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Unites States Geological Survey, Water Resources Division, Northborough, MA. list of appendices, TABLES AND FIGURES APPENDIX A DATA VALIDATION REPORT FOR 1999 MA DEP/DWM French & quinebaug river Basins MONITORING DATA (ALSO includes 1998 and 1994 FISH TOXICS MONITORING DATA) Table A2.1.1. Data Symbols and Qualifiers. Table A5.1.1. 1998-99 French & Quinebaug River Basins Censored/Qualified Hydrolab Data. Table A5.2.1. 1999 MA DEP DWM in-lake physico-chemical QA/QC field blank data. Table A5.2.2. 1999 MA DEP DWM in-lake physico-chemical QA/QC field replicate data. Table A5.2.3. 1999 MA DEP/CERO SMART Monitoring: French & Quinebaug River Basins instream physico-chemical QA/QC field blank data. Table A5.2.4. 1999 MA DEP/CERO SMART Monitoring: French & Quinebaug River Basins instream physico-chemical QA/QC field replicate data. Table A5.2.5. 1999 MA DEP DWM Cady Brook Project: in-stream physico-chemical QA/QC field blank data. Table A5.2.6. 1999 MA DEP DWM Cady Brook Project: in-stream physico-chemical QA/QC field replicate data. Table A5.2.7. 1999 MA DEP DWM Cady Brook Project: in-stream bacteriological QA/QC field blank data. Table A5.2.8. 1999 MA DEP DWM Cady Brook Project: in-stream bacteriological QA/QC field replicate data. Table A5.2.9. 1999 MA DEP DWM Cady Brook Project: in-stream phosphorus QA/QC field blank data. Table A5.2.10. 1999 MA DEP DWM Cady Brook Project: in-stream phosphorus QA/QC field replicate data. Table A5.2.11. 1999 MA DEP French & Quinebaug River Basins Censored/Qualified Discrete Water Sample Data. Table A5.4.1. 1999, 1998 and 1994 MA DEP DWM laboratory QA/QC blank data for organics in fish tissue. Table A.5.4.2. 1999, 1998 and 1994 MA DEP DWM French & Quinebaug River Basins laboratory QA/QC data for metals in fish tissue. Table A5.4.3. 1999 and 1998 MA DEP DWM laboratory QA/QC lab fortified blank data for organics in fish tissue. Table A5.4.4. 1999, 1998 and 1994 MA DEP DWM laboratory QA/QC duplicate data for organics in fish tissue. Table A5.4.5. 1999, 1998 and 1994 MA DEP DWM laboratory QA/QC lab fortified matrix and matrix spike duplicate data for organics in fish tissue. Table A6.1. 1999, 1998 and 1994 Analytical Methods APPENDIX B - 1999 MA DEP DWM French & quinebaug river Basins survey data (ALSO includes 1998 and 1994 FISH TOXICS MONITORING DATA) Table B1. 1999 MA DEP DWM French River Basin sampling matrix. Table B2. 1999 MA DEP DWM Quinebaug River Basin sampling matrix. Table B3. 1999 MA DEP DWM Cady Brook drainage area in-situ Hydrolab data. Table B4. 1999 MA DEP DWM Cady Brook drainage area, instream physico/chemical data. Table B5. 1999 MA DEP DWM Cady Brook phosphorus data. Table B6. 1999 MA DEP DWM Cady Brook bacteria data. Table B7. 1999 MA DEP DWM Cady Brook stream discharge measurements. Table B8. 1999 MA DEP/CERO SMART Monitoring French and Quinebaug River Basins in-situ Hydrolab data. Table B9. 1999 MA DEP/CERO SMART Monitoring French and Quinebaug River Basins instream physico/chemical data. Table B10. 1998 MA DEP DWM Quinebaug River Basin 97-09/104 Project on Numeric Biocriteria in-situ Hydrolab data. Table B11. 1999 MA DEP DWM aquatic macrophyte observations at selected 303d listed lakes in the French River Basin. Table B12. 1999 MA DEP DWM aquatic macrophyte observations at selected 303d listed lakes in the Quinebaug River Basin. Table B13. 1999 MA DEP DWM French & Quinebaug River Basins in-situ Hydrolab lake data. Table B14. 1999 MA DEP DWM French & Quinebaug River Basins inlake Secchi depth, alkalinity, color, total phosphorus and chlorophyll a data. Table B15. 1999 MA DEP DWM French River Basin fish toxics monitoring data for Buffumville Lake, Charlton/Oxford and Webster Lake, Webster. Table B16. 1998 MA DEP DWM fish toxics monitoring data for Texas Pond, Oxford and the Quinebaug River, Brimfield. Table B17. 1994 MA DEP OWM fish toxics monitoring data for the Hamilton Reservoir, Holland and French River (Thayers Pond - impoundment at Clara Barton Road), Oxford. Table B18. French River Basin 1994 summer lake status. Table B19. Quinebaug River Basin 1994 summer lake status. Figure B1. Locations of the 1999 MA DEP DWM Cady Brook water quality sampling stations, the 1999 MA DEP/CERO SMART water quality sampling stations and the 1998 Numeric Biocriteria sampling stations in the French & Quinebaug River Basins.. Figure B2. Locations of 1999 TMDL lake sampling stations in the French & Quinebaug River Basins. Figure B3. Locations of 1999, 1998, and 1994 MA DEP fish toxics monitoring stations in the French & Quinebaug River Basins. APPEndix c - Technical Memorandum #TM- 41/42- FRENCH & QUINEBAUG RIVER WATERSHEDS 1999 BIOLOGICAL ASSESSMENT Table 1. List of macroinvertebrate biomonitoring station locations sampled during the 1999 French & Quinebaug River watersheds survey, including station identification number, station description, and sampling date. Table 2. List of perceived problems addressed during the 1999 French & Quinebaug River watersheds biomonitoring survey. Figure 1. Location of DWM biomonitoring stations for the 1999 French & Quinebaug River watersheds survey. APPENDIX D SUMMARY OF NPDES and WMA PERMITTING INFORMATION, FRENCH & QUINEBAUG RIVER BASINS Table D1. French & Quinebaug River Basins Municipal Surface Wastewater Discharges. Table D2. French & Quinebaug River Basins Industrial Treatment Plants. Table D3. List of WMA registered and permitted average annual water withdrawals in the French and Quinebaug River Basins APPENDIX E MA DEP GRANT AND LOAN PROGRAMS APPENDIX F SUMMARY OF INSTREAM FLOW STUDIES QUINEBAUG RIVER MASSACHUSETTS AND CONNECTICUT 1999 - 2001 APPENDIX G Technical Memorandum FRENCH AND QUINEBAUG RIVERS PERIPHYTON SURVEY RESULTS 1999 Table 1. French and Quinebaug Rivers-1999 Station Numbers and Station Descriptions Table 2. French River-Cady Brook-1999 Station Locations for Periphyton Biomass Table 3. French and Quinebaug Rivers: Dominant Alga Type, % Algal Cover, % Canopy Cover 1999 Rapid Bioassessment Surveys Table 4. Cady Brook, Quinebaug River-Average Ash Free Dry Mass (g AFDM m-2 and Average Productivity (P)( mg ash-free weight/m2/day)-1999 Figure G1. Cady Brook: July and August 1999 Ash Free Dry Mass (mg/cm2) APPENDIX A DATA VALIDATION REPORT FOR 1999 MA DEP/DWM FRENCH & QUINEBAUG RIVER BASINS Assessment (ALSO includes 1998 and 1994 FISH TOXICS MONITORING DATA) PREFACE: The objective of DWMs data validation process is to ensure that the quality of monitoring data meets defined criteria for acceptability as final, usable data. This is accomplished by thoroughly reviewing and evaluating all draft data and associated field and laboratory quality control information. This report includes evaluation of all 1999 data collected in the French and Quinebaug River Basins by DWM as part of Year-2 monitoring, as well as from MA DEP/CERO programmatic monitoring (SMART) and two DWM special projects (1999 Cady Brook Project and the 1997-98 Project on Numeric Biocriteria). In addition to 1999 fish toxics data, this report also includes previously unreported 1998 and 1994 fish toxics data collected in the French & Quinebaug River Basins. This Appendix is divided into seven sections as follows: - A1. Introduction - A2. The Data Validation Process for 1999 French & Quinebaug Data - A3. 1999 QAPPs/SOPs Used in French & Quinebaug Basins Monitoring - A4. 1999 QA/QC Acceptance Criteria for French & Quinebaug Data - A5. QC-Sample Data And Validation Decisions For French & Quinebaug River Basins (1999 and 1998 Water Quality; 1999 and 1994 Fish Toxics Data) - A6. 1999 Analytical Methods and MDLs - A7. Conclusions A1. INTRODUCTION The following data were collected by MA DEP/DWM and MA DEP/CERO personnel in the French & Quinebaug River Basins, and were used in this assessment: French River Basin In situ Hydrolab readings and associated water sampling at six lakes and one tributary inlet, In situ Hydrolab readings and associated CERO/SMART monitoring at one river/stream station, Fish tissue toxics data at two lakes, and Benthic macroinvertebrates and aquatic habitat assessment at a total of seven river/stream stations. Quinebaug River Basin In situ Hydrolab readings and associated inlake sampling at five lakes and one tributary inlet, In situ Hydrolab readings and associated CERO/SMART monitoring at two river/stream stations, In situ Hydrolab readings and associated Cady Brook Project sampling at eleven river/stream stations in 1999, In situ Hydrolab readings at two river/stream stations in 1998, as part of the Project on Numeric Biocriteria, Flow measurements at nine river/stream stations, and Benthic macroinvertebrates and aquatic habitat assessment at a total of ten river/stream stations. For monitoring locations, parameters and dates, see Tables B1 and B2 in Appendix B. A2. The Data Validation Process for 1999, 1998 and 1994 French & Quinebaug Basin Data The procedures used to accept, accept with qualification or censor data were based on the draft DWM Standard Operating Procedure (SOP) for data validation (MA DEP 2002). These procedures are supplemental to separate data quality assurance activities and laboratory validation performed by the analytical laboratory, Wall Experiment Station (WES). The data validation SOP outlines specific criteria by which to evaluate data quality and acceptability. These criteria pertain to the following elements: Conformance to DWM-project and DWM-programmatic Quality Assurance Project Plans (QAPPs) and Standard Operating Procedures (SOPs) Precision (review of overall precision, including field precision and lab precision) Accuracy (review of lab quality control data regarding analysis of blind performance evaluation samples, internal check standards, blanks and matrix spike samples) Representativeness (review of field data sheets and field SOPs used to collect the data for the evidence of the potential for non-representative conditions at the time of sampling) Holding Times and Preservation (review for conformance to method holding times and preservation requirements for samples) Frequency of Field QC samples (review for conformance to standard DWM requirements for the number of field blank and split/duplicate samples taken per total number of samples taken) Contamination of Field Blanks (review of blank analyses for detectable analyte concentrations) Completeness (review of the amount of usable data in comparison to that intended to be collected) Chain-of-Custody (review of sample handling and transfer records) Data that fell outside QA/QC acceptance criteria were investigated and may have been subject to censoring or qualification. Specific symbols and qualifiers used to censor and qualify data are provided in Table A2.1.1. Completion of 1999 data validation for the French and Quinebaug data resulted in the entry of the final data into the DWM water quality database, and its use for assessment purposes. Table A2.1.1. Data Symbols and Qualifiers. Symbol/ QualifierData SourceDefinition**AllCensored or missing data--AllNo data718, 1,413, 2,760, 6,668 or 12,900 uS/cm) or turbidity (>10, 20 or 40 NTU). It can also be used for TDS and Salinity calculations based on qualified (c) conductivity data, or that the calculation was not possible due to censored conductivity data ( TDS and Salinity are calculated values and entirely based on conductivity reading). iHydrolabinaccurate readings from Hydrolab multiprobe likely; may be due to significant pre-survey calibration problems, post-survey calibration readings outside typical acceptance range for the low ionic check and for the deionized blank water check, or lack of calibration of the depth sensor prior to use.Table A2.1.1. Continued. 1999 Data Symbols and Qualifiers. Symbol/ QualifierData SourceDefinitionMHydrolabmethod not followed; one or more protocols contained in the DWM Hydrolab SOP not followed, ie. operator error (eg. less than 3 readings per station (rivers) or per depth (lakes), or instrument failure not allowing method to be implemented.sHydrolabField sheet-recorded data were used to accept data (not the data electronically recorded in the Hydrolab surveyor unit), due to operator error or equipment failure.uHydrolabunstable readings, due to lack of sufficient equilibration time prior to final readings, non-representative location, highly-variable water quality conditions, etc. ?HydrolabLight interference on Turbidity sensor (Hydrolab error message). Data is typically censored.aDiscrete samplesaccuracy as estimated at WES Lab via matrix spikes, PT sample recoveries, internal check standards and lab-fortified blanks did not meet project data quality objectives identified for program or in QAPP.bDiscrete samplesblank Contamination in lab reagant blanks and/or field blank samples (indicating possible bias high and false positives).dDiscrete samplesPrecision of field duplicates (as RPD) did not meet project data quality objectives identified for program or in QAPP.eFlow dataFlow data estimated, due to field measurement error, complication or anomaly.fDiscrete samplesfrequency of quality control duplicates did not meet data quality objectives identified for program or in QAPP.hDiscrete samplesholding time violation (usually indicating possible bias low)jDiscrete samplesestimated value; used for lab-related issues where certain lab QC criteria are not met and re-testing is not possible (as identified by the WES lab only). Also used by WES to report sample data where the sample concentration is less than the reporting limit or RDL and greater than the method detection limit or MDL (mdl< x 1mg/L, or <30% RPD for method detection limits <1mg/L. or meet more specific criteria contained in a 1999 QAPP. If the criteria are not met, the data may be censored or qualified, depending on extent of exceedance and other factors. In most cases, poor precision of field split samples reflects potential poor reproducibility for entire surveys and/or analytical batch runs, and may lead to the censoring/qualification of same. - Laboratory assessment of analytical precision and accuracy: The WES Laboratory is solely responsible for the administration of its Quality Assurance Program and Standard Operating Procedures. WES staff release discrete water sample data when their established QA/QC criteria have been met. When the following criteria cannot be met, data are qualified as estimated (using a J value) if appropriate, or no data (ND) is reported: Low Calibration Standards Checks the stability of the instruments calibration curve; analyzes the accuracy of an instruments calibration within a 5% range. Reference Standards Generally, a second source standard (a standard different from the calibration stock standard) that analyzes the method accuracy. Laboratory Reagent Blank/Method Blank (LRB) Reagent grade water (de-ionized) extracted with every sample set used to ensure that the system is free of target analytes (< MDL) and to assess potential blank contamination. Duplicate Sample Measures the precision (as Relative Percent Difference or RPD) of the analytical process. The acceptable laboratory %RPD range is typically ( 25%. Spike Sample (Laboratory Fortified Blank - LFB, Laboratory Fortified Matrix - LFM) Measures the accuracy (% Recovery) of an analytical method. The acceptable laboratory % recovery range is typically between 80 120% for LFB samples and 70 130% for LFM discrete water samples. Range of Logs (bacteria data) Acceptance limits established by WES for range of log-tranformed duplicate data. A4.3 QA/QC Objectives and Criteria for 1999, 1998 and 1994 Fish Tissue Contaminant Data Fish from lakes in the French and Quinebaug Basins were collected and processed according to the DWM 1999 Standard Operating Procedure (SOP) for fish contaminant monitoring (now CN 40.0). This SOP adheres to EPA-approved laboratory QA/QC methodologies (EPA 823-R-95-007). Laboratory data quality was assessed at WES by analyzing the following quality control samples: Laboratory Reagent Blank/Method Blank (LRB) Clean clam tissue matrix extracted with every sample set to ensure that the system is free of target analytes (< MDL) and to assess the potential for blank contamination. Laboratory Fortified Blank (LFB) Clean clam tissue matrix spiked with a low concentration of target compounds. LFB results are used to establish accuracy of systems performance. The acceptable laboratory % recovery range is typically 80 120%. Laboratory Fortified Matrix (LFM) Tissue matrix spiked with a low concentration of a target compound. LFM and LFM duplicate results are used to establish accuracy of the extraction and analytical process. The acceptable laboratory % recovery range is typically between 70 130% for metal analysis and 60 140% for PCB/Organochlorine Pesticide analysis. Quality Control Standard (QCS) A pre-spiked secondary tissue sample. QCS results are used to establish accuracy in the extraction and test methods. The acceptable laboratory % recovery range is typically between 80120%. Laboratory sample duplicates A second lab sample is taken the blended fish tissue slurry for analysis of all analytes. Used to estimate analytical precision, the acceptable laboratory relative percent difference (RPD) for lab duplicates is typically 80-120%. A4.4 QA/QC Objectives of 1999 Data for Benthic Macroinvertebrates, Aquatic Habitat and Miscellaneous Biological Monitoring (periphyton, aquatic macrophytes, phytoplankton) Macroinvertebrate sampling and processing was conducted by DWM biologists, as described in the SOP Water Quality Monitoring In Streams Using Aquatic Macroinvertebrates (now 39.0), which is based on US EPA Rapid Bioassessment Protocols (RBP III). The QAPP for 1999 biomonitoring outlined general QC steps that included: Thorough rinsing of sampling equipment between stations to prevent inter-station effects. Duplication and checking (for transcription errors) of documentation and database entries. In-house spot-checking (among two DWM biologists) of taxa identifications for accuracy. A5. QC-SAMPLE DATA AND VALIDATION DECISIONS FOR FRENCH & QUINEBAUG RIVER BASINS Data validation procedures, as now outlined in DWMs draft Data Validation SOP (MA DEP 2002; CN 56.0) were applied to in-situ Hydrolab, discrete water quality and fish tissue data for the French & Quinebaug River Basins. The 1999 Data Validation Report (MA DEP 2000a, CN 73.0) summarizing all 1999 data validation results is also available as a separate evaluation. Assessment and validation of the benthic macroinvertebrate, periphyton and habitat data collected for the French & Quinebaug River Basins is not covered here. DWM QA/QC assessment of benthic/habitat data is general in nature (ie. adherence to the SOP and QAPP, discussions with primary staff on QAPP implementation, etc.). A5.1 Hydrolab Data Validation Review of 1998 and 1999 Hydrolab data and imposition of the data acceptance criteria identified in A4.1 resulted in specific validation decisions (censored, qualified or accepted without qualification), as follows in Table A5.1.1. All other data were accepted. See the 1999 Data Validation Report (CN 73.0) appendix for the complete Hydrolab QC records (MA DEP 1999i). Table A5.1.1. 1998-99 French & Quinebaug River Basins Censored/Qualified Hydrolab Data. WatershedSurvey Date(s)OWMID #sCensored/ Qualified ParametersCensored/ QualifiedReason and/or ClarificationFrench/ Quinebaug (various sites)5/19, 6/22, 6/23, 7/27, 8/17, 8/1841-0034, 0037, 0038, 0043, 0044, 0045, 0047, 0052, 0053, 0054, 0056, 0064, 0065, 0066, 0067, 0070, 0071, 0072, 0073, 0074, 0075, 0076, 0077, 0078, 0079, 0080, 0081, 0083, 0084, 0085, 0086, 0087, 0092, 0097, 0119Depth Censor (i)Depths inaccurate (neg., 0.0) French/ Quinebaug (various sites)5/19, 6/22, 6/23, 7/27, 8/18, 9/15 41-0035, 0039, 0040, 0041, 0048, 0049, 0050, 0055, 0057, 0058, 0059, 0082, 0088, 0089, 0090, 0121, 0122, 0123, 0124, 0125, 0127Depth Qualify (i)Depths inaccurate (0.1) Table A5.1.1. Continued. 1998-99 French & Quinebaug River Basins Censored/Qualified Hydrolab Data. WatershedSurvey Date(s)OWMID #sCensored/ Qualified ParametersCensored/ QualifiedReason and/or ClarificationCady Brook6/22/9941-0038Conductivity (and TDS)Qualify (c)> calibration range (718)Cady Brook6/22/9941-0042Temp, pH and conductivity (and TDS)Qualify (u)Readings slightly unstable (still increasing or decreasing after 5 one-minute readings)Cady Brook6/22/9941-0044Temp, D.O. and % SAT Qualify (u)See above (41-0042)Conductivity (and TDS)Qualify (c)> calibration range (718)Cady Brook6/23/9941-0053Conductivity (and TDS)Qualify (c)> calibration range (718)Cady Brook6/22/9941-0064Conductivity (and TDS)Qualify (c)> calibration range (718)Cady Brook8/17/9941-0066 and 0067Conductivity (and TDS)Qualify (c)> calibration range (718)Cady Brook8/17/9941-0075Conductivity (and TDS)Qualify (c)> calibration range (718)Cady Brook8/18/9941-0083 and 0085Conductivity (and TDS)Qualify (c)> calibration range (718)Cady Brook7/27/9941-0119 through 0125D.O., temp, cond, pH, % saturation, depth and TDSAccept all field sheet Hydrolab data, and qualify all data (s)SRV3 electronic data lost due to battery failure; accept field sheet data with qualification.Gore Pond8/4/99LB-0099D.O. and %SAT at 2.5 mQualify (u)Unstable readingsTemp at 3.5 and 4.5 mQualify (u) Unstable readingsGore Pond9/1/99LB-0505D.O. and % SAT at 3.4 mQualify (u) Unstable readings Larner Pond7/28/99LB-0074D.O. and % SAT at 2.5 m depthQualify (u)Unstable readingsLarner Pond7/28/99LB-0075Temperature at 2.5 m depthQualify (u)Unstable readingsLarner Pond9/22/99LB-0373D.O. and % SAT at 2.5 and 3.0 mQualify (u) Unstable readings Pierpont Meadow Pond8/4/99LB-0098D.O., temp, cond, pH, % saturation, depth and TDS at depths 2.5 and 2.8Qualify (m) Low equilibration time: readings < one minute intervals AND only three readings per depth Temp at 2.5 mQualify (u)Unstable readingsPierpont Meadow Pond8/4/99LB-0100D.O. and % SAT at 2.5Qualify (u) Unstable readingsRochdale Pond8/5/99LB-0109D.O. and % SAT at 2.5 mQualify (u) Unstable readings Temp at 3.1mQualify (u)Unstable readingsWallis Pond8/26/99LB-0213D.O. and % SAT at 0.3 mQualify (u) Unstable readings (very low DO continuing to fall after 5 readings)Wallis Pond9/22/99LB-0368DepthQualify (i)Depth inaccurate (0.1) Table A5.1.1. Continued. 1998-99 French & Quinebaug River Basins Censored/Qualified Hydrolab Data. WatershedSurvey Date(s)OWMID #sCensored/ Qualified ParametersCensored/ QualifiedReason and/or ClarificationMill Road Pond9/29/99LB-0231D.O. and % SAT at 0.5 mQualify (u) Unstable readings Sibley Pond north7/29/99LB-0502D.O. and % SAT at 1.5 mQualify (u) Unstable readings Sibley Pond north8/25/99LB-0211Temp at 0.5 mQualify (u) Unstable readings D.O. and % SAT at 1.5 mQualify (u)Sibley Pond north8/25/99LB-0206D.O. and % SAT at 1.5 mQualify (u) Unstable readings Temp at 0.5 mQualify (u) Unstable readingsSibley Pond south7/29/99LB-0501D.O. and % SAT at 0.5 mQualify (u) Unstable readings Sibley Pond south8/25/99LB-0210D.O. and % SAT at 1.3 mQualify (u) Unstable readings  A5.2 Discrete Sample Data Validation A5.2.1 Quality Control Sample Results Field blank and field replicate sampling results for all discrete lake quality control sample data taken in 1999 are provided in Tables A.5.2.1 through Table A5.2.6. Quality control sample data are stored and maintained in the Water Quality Data (WQD) Access Database. For Tables A5.2.1 and A5.2.2 all 1999 lake quality control samples are listed; for multiple lake surveys, certain lakes may not have quality control samples. Table A5.2.1. 1999 MA DEP DWM in-lake physico-chemical QA/QC field blank data. (All units expressed in mg/L unless otherwise specified.) Date OWMID OWMID Alkalinity Color Total QA/QC (mg/L) (PCU) Phosphorus (mg/L) Field Blank Sample 08/03/99 LB-0078 BLANK <2.0 <15 <0.005 09/29/99 LB-0229 BLANK -- -- <0.005 08/05/99 LB-0105 BLANK <2.0 <15 <0.005 09/28/99 LB-0405 BLANK <2.0 <15 <0.005 08/31/99 LB-0380 BLANK <2.0 <15 <0.005 09/29/99 LB-0234 BLANK <2.0 -- -- 07/29/99 LB-0053 BLANK <1.0 <15 <0.005 08/25/99 LB-0203 BLANK <2.0 <15 <0.005 09/23/99 LB-0354 BLANK <2.0 <15 <0.005 08/04/99 LB-0096 BLANK <2.0 <15 <0.005 09/01/99 LB-0241 BLANK <2.0 <15 <0.005 10/05/99 LB-0390 BLANK <2.0 <15 <0.005 09/02/99 LB-0256 BLANK <2.0 <15 <0.005 07/28/99 LB-0065 BLANK <1.0 <15 <0.005 08/26/99 LB-0216 BLANK <2.0 <15 <0.005 09/22/99 LB-0365 BLANK <2.0 <15 <0.005 08/05/99 LB-0415 BLANK <2.0 <15 <0.005 08/12/99 LB-0187 BLANK -- -- <0.005 07/15/99 LB-0029 BLANK <2.0 <15 <0.005 08/12/99 LB-0183 BLANK -- -- <0.005 09/13/99 LB-0329 BLANK <2.0 <15 <0.005 07/27/99 LB-0041 BLANK <1.0 <15 <0.005 08/24/99 LB-0191 BLANK <2.0 <15 <0.005 09/21/99 LB-0341 BLANK <2.0 <15 <0.005 ** = Censored or missing data -- = No data MDL) and holding time violations on several occasions, resulting in censored/qualified data. REFERENCES Clesceri, L.S., A.E. Greenberg, and A.D. Eaton, (editors). 1998. Standard Methods for the Examination of Water and Wastewater 20th Edition. American Public Heath Association, Washington, D.C. MA DEP. 1999. CN 21.0 QAPP for the Cady Brook Water Quality Project. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999a. CN 22.0 QAPP for 1999 Baseline Lakes TMDL. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999b. CN 1.0 Grab Collection Techniques for DWM Water Quality Sampling, Standard Operating Procedure. October 25, 1999. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999c. CN 13.0 Fish Contaminant Monitoring Program, Quality Assurance Project Plan, 1999. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999d. CN 4.0 Hydrolab Series 3 Multiprobe, Standard Operating Procedure. September 23, 1999. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999e. CN 7.0 SOP for Benthic Macroinvertebrate Collection and Analysis. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999f. CN 40.0 SOP for Fish Collection/Preparation for Fish Tissue Analysis. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999g. CN 2.0 Apparent Color Standard Operating Procedures. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999h. CN 3.0 Chlorophyll a Standard Operating Procedures. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999i. Open File. 1999 Hydrolab QAQC. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 2000a. 1999 Data Validation Report. CN 73.0; 9/2001. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 2000b. CN 12.0. Smart Monitoring Water Quality Quality Assurance Project Plan. Massachusetts Department of Environmental Protection, Division of Watershed Management, Worcester, MA. MA DEP. 2002. Draft 2002 Data Validation SOP, February, 2002. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. APPENDIX B 1999 MA DEP DWM FRENCH & QUINEBAUG River BasinS survey data (ALSO includes 1998 and 1994 FISH TOXICS MONITORING DATA INTRODUCTION The MA DEP DWM sampled in the French & Quinebaug River Basins April through November 1999. Sampling components included macroinvertebrate and habitat quality evaluations in selected wadeable streams, fish sampling for organic and metal toxins in edible fillets, river station sampling that included in-situ Hydrolab Multiprobe Series 3 analyzer (hereafter referred to as Hydrolab) measurements, bacteria, oxygen demand, physico-chemical and nutrient sampling, baseline lake surveys that included Hydrolab measurements, secchi depth, alkalinity, color, total phosphorus, and chlorophyll a sampling as well as macrophyte identification/density at the maximum extent of growth. Each sampling component is described in the sections that follow. STREAM WATER QUALITY MONITORING Stream water quality monitoring was conducted by MA DEP DWM personel in the Quinebaug River Basin on Cady Brook in Charlton and Southbridge. The following was excerpted from CADY BROOK, QUINEBAUG RIVER 1999 WATER QUALITY AND WASTEWATER DISCHARGE DATA (Hartman 2001). The Division of Watershed Management of the Massachusetts Department of Environmental Protection conducted a survey of Cady Brook, in the Quinebaug River watershed during the summer of 1999. Sampling included instream water quality, effluent quality from the Charlton WWTF, biological monitoring of macroinvertebrates and algae, streambottom qualitative assessment, flow and time of travel. The USEPA conducted one set of sampling of the Charlton WWTF including chemical, nutrient and metals analyses. The information from these surveys are to be used to develop a wasteload allocation model utilizing QUAL2E for NPDES permitting, and for inclusion in the MA DEP biannual assessment of waters for 305b reporting purposes to the federal government. Included in this report are the sampling plan and methods for the water, wastewater discharge, macroinvertebrate, and algal sections, streambottom characterization, and time of travel. Results for the water and wastewater, stream bottom, flow and time of travel are also included in this report. The results of the macroinvertebrate and algal analyses are reported separately. As part of monitoring efforts of the Strategic Monitoring and Assessment for Riverbasin Teams (SMART) program, MA DEP/CERO SMART water quality monitoring was conducted at one station in the French River Basin drainage area (Dudley/Webster) and at two stations in the Quinebaug River Basin drainage area (Sturbridge, Massachusetts and Thompson, Connecticut). This monitoring program focuses on obtaining a snapshot of water quality in selected subwatersheds with the goals of determining existing water quality conditions, quantify loadings, calibrate models, and evaluate the water body for fishable, swimmable uses as defined in Section 305b of the Clean Water Act. baseline Lake surveys Six of the 303d listed lakes in the French River Basin (31 confirmed and 1 needing confirmation in this basin) were selected for baseline surveys. Five of the 303d listed lakes in the Quinebaug River Basin (20 confirmed in this basin) were selected for baseline surveys. Lakes were preferentially targeted for sampling based on the severity of the nutrient-related problem and the size of the lake (MA DEP 1999a). Those lakes that were listed solely for non-nutrient related issues (e.g., lakes listed for fish consumption advisories) and those with previous diagnostic/feasibility studies were not selected. Baseline surveys were conducted to provide information on the current chemical, physical and biological conditions of the lake system (i.e., in-lake and in the surrounding watershed). Each baseline lake survey included a macrophyte survey conducted once during the late summer at the peak of macrophyte growth (generally in July/August/September). The survey data are used in several ways: 1) to determine if the macrophyte growth causes nuisance conditions such that the lake would be listed or delisted on the state's 303d list for violations of water quality standards; 2) to determine if the lake meets designed uses in the 305b assessments; 3) to monitor changes in density of plant growth following implementation of a TMDL; 4) to document invasive species distributions in the state; and 5) to suggest macrophyte management options for the lake. Trophic status (an indicator of the productivity level of a lake) is based on the evaluation of data collected during baseline surveys. Parameters used to determine trophic status include; oxygen levels, chlorophyll a concentrations, total phosphorus levels, Secchi disk measurements, and macrophyte density determinations. The data are used to validate Total Maximum Daily Load (TMDL) phosphorus loading models and to document the present trophic conditions as well as assessing the status of lakes designated uses. The total phosphorus data are used to evaluate accuracy of land use loading estimates (Mattson and Isaac 1999) of total phosphorus to lakes by comparing predictions of lake concentrations based on modeling to actual measured lake concentrations. These may be used as a basis for estimation of internal loading or other unmeasured phosphorus sources. Concurrently a lake database will be developed for both 303d development and for 305b evaluation based on lakes that are on the current 303d list. The data contained in this database along with the other data collected are used in TMDL development or to monitor lakes for changes in water quality and nuisance plant growth after TMDL implementation. fish tOXICS MONITORING Fish toxics monitoring is aimed primarily at assessing human health risks associated with the consumption of freshwater fishes. The program is a cooperative effort among three MA DEP Offices/Divisions, (Watershed Management, Research and Standards, and Environmental Analysis), the Department of Fisheries and Wildlife Environmental Law Enforcement, and the Department of Public Health (DPH). Fish tissue monitoring is typically conducted to assess the concentrations of toxic contaminants in freshwater fish, identify waterbodies where those concentrations may pose a risk to human health, and identify waters where toxic contaminants may impact fish and other aquatic life. Fish tissue analysis has been restricted to edible fillets. The fish toxics monitoring was designed to screen the edible fillets of several species of fish representing different feeding guilds (i.e., bottom dwelling omnivores, top-level predators, etc.) for the presence of heavy metals (Pb, Cd, Se, Hg, As), PCBs and organochlorine pesticides. These data are then used by the Massachusetts Department of Public Health in assessing human health risks associated with the consumption of freshwater fishes. During 1994, MA DEP OWM (now MA DEP DWM) monitored two stations for toxics in fish flesh; Thayer Pond, Oxford an eight-acre impoundment of the French River was sampled in September, and Hamilton Reservoir, Oxford a 249acre waterbody located in the Quinebaug River Basin was sampled in August. During 1998, in response to Public Requests, Texas Pond, Oxford (a 27acre impoundment of the French River) was sampled during July and August and the Quinebaug River, Brimfield (upstream/west/southwest of Brimfield Road) was sampled during September. During 1999, MA DEP DWM monitored two French River Basin ponds for toxics in fish flesh as part of Massacusetts Watershed Initiative Year 2 activities. Sampling was conducted in June at Buffumville Lake, Charlton/Oxford (a 186acre waterbody) and Webster Lake, Webster (a 1,181acre waterbody). BENTHIC MACROINVERTEBRATE STUDIES Excerpted from French & Quinebaug River Watersheds 1999 Biological Assessment technical memorandum, which is attached as Appendix C of this Assessment Report. The main objectives of biomonitoring in the French & Quinebaug River watersheds were: (a) to determine the biological health of streams within the watersheds by conducting assessments based on aquatic macroinvertebrate communities; and (b) to identify impaired stream segments so that efforts can be focussed on developing NPDES permits, stormwater management, and control of other nonpoint source pollution. Specific tasks were: Conduct benthic macroinvertebrate sampling and habitat assessments at selected locations throughout the French & Quinebaug River watersheds. Based upon the macroinvertebrate data, identify river segments within the watersheds with potential or existing point/nonpoint source pollution problems; and Using the benthic macroinvertebrate data and supporting water chemistry and field/habitat data: Assess the types of water quality and/or water quantity problems that are present, and if possible, make recommendations for remedial actions. Provide macroinvertebrate data to DWMs Environmental Monitoring and Assessment Program to be used in making aquatic life use assessments required by Section 305(b) of the Federal Clean Water Act (CWA). PERIPHYTON and PHYTOPLANKTON Excerpted from FRENCH AND QUINEBAUG RIVERS - PERIPHYTON SURVEY RESULTS 1999 technical memorandum, which is attached as Appendix G of this Assessment Report. The objectives of the periphyton sampling were limited in scope since only qualitative sampling was done. The samples were collected in order to learn more about the biota in the streams and rivers, to document problem areas, to offer a means of comparing biological communities in conjunction with the macroinvertebrate and habitat information, to examine community changes and to provide a record of the taxa that are found in Massachusetts. Materials And Methods The MA DEP DWM sampling plan matrix for the French & Quinebaug River Basins is summarized in Tables B1 and B2 respectively. Table B1. 1999 MA DEP DWM French River Basin sampling matrix. WATERBODY (SEGMENT #)STATION1AprilMayJuneJulyAugustSeptemberOctoberNovemberTown Meadow Brook, outlet Sargent Pond, Leicester to inlet Dutton Pond, Leicester. (MA42-01)MB11M, PTown Meadow Brook, outlet Dutton Pond Leicester to inlet Greenville Pond, Leicester. (MA42-02)MB12M, PFrench River, outlet of Greenville Pond, Leicester to North Oxford Dam immediately upstream of Clara Barton Road, (McIntyre Road extension), Oxford. (MA42-03)FR14M, PFR15M, PRochdale Pond (MA42048) (contained within segment MA42-03)ABBBuffumville Lake (MA42005) (contained within segment MA42-09)F0079TDresser Hill Pond (MA42014)CBBBGore Pond (MA42018)ABBBBBBBunnamed tributary to Gore Pond (MA42018)DBBPierpont Meadow Pond (MA42043)ABBBWebster Lake (MA42064)F0073TFrench River, dam at North Village, Webster/Dudley to Webster/Dudley WWTP, Webster/Dudley. (MA42-05)FR11SSSM, PSSFR17M, PWallis Pond (MA42062)ABBBLarner Pond (MA42068)ABBBBBFrench River, Thompson, Connecticut. (downstream of MA42-06)FRI8M, P1 Sampling did not necessarily occur at the same exact location although that which occurred in the general vicinity of the sampling station is listed together. B Baseline lake monitoring. Can include: Hydrolab multiprobe meter (depth, pH, dissolved oxygen, conductivity, temperature, total dissolved solids, turbidity) and secchi depth, alkalinity, color, total phosphorus, and chlorophyll a. M Macroinvertebrate sampling and habitat assessment P Periphyton (habitat, algal identification, and abundance) S SMART monitoring. Can include: Hydrolab multiprobe meter (depth, pH, dissolved oxygen, conductivity, temperature, total dissolved solids, turbidity), chemistry (alkalinity, hardness, chloride, suspended solids, turbidity), and nutrients (total phosphorus, ammonia, nitrate-nitrogen, total Kjeldahl nitrogen). T Toxics in fish tissue (Cd, Pb, Hg, As, Se, % lipids, PCBs, organochlorine pesticides) Note: Fish toxics monitoring was also conducted in the French River Basin by MA DEP DWM in 1998 (Texas Pond, Oxford) and by MA DEP OWM in 1994 (Thayer Pond, Oxford). Locations are depicted in Figure B3 and data are presented in Tables B11 and B12, respectively. Table B2. 1999 MA DEP DWM Quinebaug River Basin sampling matrix. WATERBODY (SEGMENT #)STATION1AprilMayJuneJulyAugustSeptemberOctoberNovemberQuinebaug River, outlet Hamilton Reservoir, Holland, to Sturbridge WWTP, Sturbridge. (MA41-01)QR0BM, PQR00SSSM, PSSMill Road Pond (MA41032)ABBSherman Pond (MA41046)ABBQuinebaug River, Sturbridge WWTP, Sturbridge to confluence with Cady Brook, Southbridge. (MA41-02)QR01BM, PQR01CM, PQR03M, PCady Brook, outlet of Glen Echo Lake, Charlton to Charlton City WWTP, Charlton. (MA41-05)CA01QQQCA03CCCady Brook, Charlton City WWTP, Charlton to confluence with Quinebaug River, Southbridge. (MA41-06)CA04C, QQC, Q, PM, PMA0101141CCCA06AQCA06CC, QC, QC, Q, PM, PCA08CCCA10AMMCA10C, QCC, QQCA12CCCA14C, QCC, QCA16CCCQCA18CC, QC, QC, QQunnamed trib to Cady Brook no segmentSB05C, QC, QC, QSibley Pond north (MA41047)ABBBBBunnamed tributary to Sibley Pond north (MA41047)CBSibley Pond south (MA41048)ABBBQuinebaug River, confluence with Cady Brook, Southbridge to Southbridge WWTP in Southbridge. (MA41-09)QR04UM, PQuinebaug River, Thompson Connecticut. (downstream of MA41-04)QR06SSSM, PSSMorse Pond (MA41033)ABB1 Sampling did not necessarily occur at the same exact location although that which occurred in the general vicinity of the sampling station is listed together. B Baseline lake monitoring. Can include: Hydrolab multiprobe meter (depth, pH, dissolved oxygen, conductivity, temperature, total dissolved solids, turbidity) and secchi depth, alkalinity, color, total phosphorus, and chlorophyll a. C Cady Brook study. Can include: bacteria (fecal coliform), oxygen demand (BOD/CBOD), Hydrolab multiprobe meter (depth, pH, dissolved oxygen, conductivity, temperature, total dissolved solids, turbidity), chemistry (alkalinity, hardness, chloride, suspended solids, turbidity), and nutrients (total phosphorus, ammonia, nitrate-nitrogen, total Kjeldahl nitrogen). M Macroinvertebrate sampling and habitat assessment S SMART monitoring. Can include: Hydrolab multiprobe meter (depth, pH, dissolved oxygen, conductivity, temperature, total dissolved solids, turbidity) chemistry (alkalinity, hardness, chloride, suspended solids, turbidity), and nutrients (total phosphorus, ammonia, nitrate-nitrogen, total Kjeldahl nitrogen). P Periphyton (habitat, algal identification, and abundance) Q Flow measurements Note: 1. Fish toxics monitoring was also conducted in the Quinebaug River Basin by MA DEP DWM in 1998 (Quinebaug River, Brimfield) and by MA DEP OWM in 1994 (Hamilton Reservoir, Holland). Locations are depicted in Figure B3 and data are presented in Tables B11 and B12, respectively. 2. In the Quinebaug River Basin data was also collected as part of the 97-09/104 Project on Numeric Biocriteria authorized under the 104(b)(3) Wetlands and Water Quality Grant Program (see Appendix E of this report). While these two stations are not included in this matrix, the in-situ Hydrolab data are presented in Table B10 and the stations are depicted in Figure B1. STREAM WATER QUALITY MONITORING Stream water quality monitoring was conducted by MA DEP DWM personel in the Quinebaug River Basin on Cady Brook in Charlton and Southbridge, during 1999. Sampling for this study included: bacteria (fecal coliform), in situ measurements using the Hydrolab Multiprobe Series 3 analyzer (measures dissolved oxygen, water temperature, pH, depth, turbidity, and conductivity and calculates total dissolved solids and % oxygen saturation), physico-chemical variables (alkalinity, hardness, chloride, suspended solids, and turbidity), nutrient concentrations (total Kjeldahl nitrogen, ammonia, , nitrate nitrogen, and total phosphorus), and oxygen demand parameters (5-day BOD, and 5-day CBOD). Details related to the collection, handling, and processing of samples are presented in the report entitled CADY BROOK, QUINEBAUG RIVER 1999 WATER QUALITY AND WASTEWATER DISCHARGE DATA (Hartman 2001). The quality control protocol that was followed for field and equipment blank samples is described in Appendix A of this report. MA DEP/CERO SMART water quality monitoring was conducted during April, May, July, September, and November 1999 at one station in the French River Basin drainage area (Dudley/Webster) and at two stations in the Quinebaug River Basin drainage area (Sturbridge, Massachusetts and Thompson, Connecticut). Sampling at these synoptic monitoring locations included: in situ measurements using the Hydrolab Multiprobe Series 3 analyzer (measures dissolved oxygen, water temperature, pH, depth, and conductivity and calculates total dissolved solids and % oxygen saturation), physico-chemical variables (alkalinity, hardness, chloride, suspended solids, and turbidity), and nutrient concentrations (total phosphorus, nitrate nitrogen, and ammonia). MA DEP/CERO SMART stations are identified in Figure B1. Procedures used for water sampling and sample handling are described in the Grab Collection Techniques for DWM Water Quality Sampling, Standard Operating Procedure (MA DEP 1999b) and Hydrolab Series 3 Multiprobe, Standard Operating Procedure (MA DEP 1999c). SMART monitoring personel followed procedures outlined in the then draft Smart Monitoring Water Quality Quality Assurance Project Plan (MA DEP 2000). The Wall Experiment Station (WES), the Departments analytical laboratory, supplied all sample bottles and field preservatives, which were prepared according to the WES Laboratory Quality Assurance Plan and Standard Operating Procedures (MA DEP 1995). Samples were preserved in the field as necessary, transported on ice to WES on each sampling date, and analyzed according to the WES Standard Operating Procedure (SOP). The quality control protocols that were followed for all samples (field blank, field replicate, and raw water) are described in Appendix A of this report.  Figure B1. Locations of the 1999 MA DEP DWM Cady Brook water quality sampling stations, the 1999 MA DEP/CERO SMART water quality sampling stations and the 1998 Numeric Biocriteria sampling stations in the French & Quinebaug River Basins. BASELINE LAKE SURVEYS In the French River Basin, baseline lake surveys were conducted between July and October 1999 to coincide with maximum growth of aquatic vegetation, highest recreational use, and highest lake productivity. Lakes (Figure B2) were sampled three times each (monthly intervals). The deep hole in the northern quadrant of Gore Pond, Charlton and a second site in the approximate center of the southern quadrant of Gore Pond, Dudley were sampled 4-August, 1 September and 5 October 1999. Sampling of an unnamed northwestern tributary to Gore Pond, Dudley on 4-August 1999 was unsuccessful due to lack of water. This station was sampled for total phosphorous only on 5 October 1999. The deep hole of Larner Pond, Dudley was sampled 28 July, 26 August and 22 September 1999. A second site on Larner Pond (in the center of the lobe east of Wayne Avenue and Michael Lane, Dudley) was sampled for total phosphorous only 28 July 1999. The deep hole of Pierpont Meadow Pond, Dudley was sampled 4-August, 1 September and 5 October 1999. The deep hole of Rochdale Pond, Leicester was sampled 5-August, 2 September and 28 September 1999. The deep hole of Wallis Pond, Dudley was sampled 28 July, 26 August, and 22 September 1999. In the Quinebaug River Basin, baseline lake surveys were conducted between July and September 1999 to coincide with maximum growth of aquatic vegetation, highest recreational use, and highest lake productivity. Lakes were sampled three times each (monthly intervals). The deep hole of Mill Road Pond, Brimfield was sampled 3-August, 31-August, and 29 September 1999. The deep hole of Morse Pond, Southbridge was sampled 5-August, 2 September and 28 September 1999. The deep hole of Sherman Pond, Brimfield was sampled 3-August, 31-August, and 29 September 1999. The deep hole of Sibley Pond (north), Charlton was sampled on 29 July, 25 August, and 23 September 1999. A second site close to the northern inlet, Charlton was sampled for total phosphorous only on 29 July 1999. Sampling of an unnamed northern tributary to Sibley Pond (north) on 25-August 1999 was unsuccessful due to lack of water. The deep hole of Sibley Pond (south), Charlton was sampled on 29 July, 25 August, and 23 September 1999.  Figure B2. Locations of 1999 TMDL lake sampling stations in the French & Quinebaug River Basins. In situ measurements using the Hydrolab (measures dissolved oxygen, water temperature, pH, conductivity, and depth and calculates total dissolved solids and % oxygen saturation) were recorded. At deep hole stations measurements were recorded at at various depths creating profiles. In-lake (as well as unnamed tributary) samples were also collected for alkalinity, total phosphorus, apparent color, and chlorophyll a (an integrated sample). Procedures used for water sampling and sample handling are described in the Grab Collection Techniques for DWM Water Quality Sampling Standard Operating Procedure and the Hydrolab Series 3 Multiprobe Standard Operating Procedure (MA DEP 1999b and MA DEP 1999c). The Wall Experiment Station (WES), the Departments analytical laboratory, supplied all sample bottles and field preservatives, which were prepared according to the WES Laboratory Quality Assurance Plan and Standard Operating Procedures (MA DEP 1995). Samples were preserved in the field as necessary, transported on ice to WES, and analyzed according to the WES Standard Operating Procedure (SOP). The quality control protocol that was followed for field and equipment blank samples is described in Appendix A of this report. Both quality control samples (field blanks, trip blanks, and split samples) and raw water quality samples were transported on ice to WES on each sampling date; they were subsequently analyzed according to the WES SOP. Information about data quality objectives (accuracy, precision, detection limits, holding times, representativeness and comparability) is also presented in Appendix A. Apparent color and chlorophyll a were measured according to standard procedures at the MA DEP DWM office in Worcester (MA DEP 1999d and MA DEP 1999e). An aquatic macrophyte survey was conducted at each lake. The aquatic plant cover (native and non-native) and species distribution was mapped and recorded. Details on procedures used can be found in the Baseline Lake Survey Quality Assurance Project Plan (MA DEP DWM 1999a). fish tOXICS MONITORING 1999 fish toxics Fish toxics monitoring was conducted by DWM at two sites in the French River Basin in 1999 (Figure B3, Table B10). Fish were collected via gill nets and boat mounted electrofishing gear at Webster Lake (Webster) on 14 June 1999. Fish were collected using boat mounted electrofishing gear at Buffumville Lake (Charlton/Oxford) on 29 June 1999. Fish were held in an onboard livewell until an appropriate sample number was reached, at which time the fish selected were placed in an ice filled cooler and brought back to the DWM laboratory for processing. Fish were sorted by type and processed at the DWM laboratory, as composite samples comprised of tissue from three like-sized individual fish. Protocols designed to assure accuracy and prevent cross-contamination of samples were followed for collecting, processing and shipping fish (MA DEP 1999f). Lengths and weights were measured and fish were visually inspected for tumors, lesions, or other anomalies. Scale or pectoral fin spine samples were obtained from each fish to determine age. Fish were filleted (skin off) on glass cutting boards and prepared for freezing. All equipment used in the filleting process was rinsed in tap water to remove slime, scales, and other fluids such as blood, and then re-rinsed in deionized water before (and/or after) each sample. Composite samples (single fillets from three like-sized individuals of the same species) targeted for % lipids, PCBs and organochlorine pesticide analysis were wrapped together in aluminum foil. Composite samples targeted for metals analysis were placed in VWR 32-ounce high-density polyethylene (HDPE) cups with covers. Samples were tagged and frozen for subsequent delivery to the WES laboratory. Methods used at WES for metals and PCB/organochlorine pesticide analysis is provided in Appendix A of this report and additional information is available from the WES laboratory (MA DEP 1995). According to standard practice, all laboratory analytical results were forwarded to the Department of Public Health (DPH) for review. Figure B3. Locations of 1999, 1998, and 1994 MA DEP fish toxics monitoring stations in the French & Quinebaug River Basins.  1998 fish toxics In 1998, MA DEP DWM at one site in each of the French and Quinebaug River Basins conducted fish toxics monitoring (Figure B3, Table B11). Texas Pond, an impoundment of the French River in Oxford, was sampled via gill nets on both 28 July and 12 August 1998. The Quinebaug River upstream of Brimfield Road, Brimfield was sampled via gill nets on 11 September 1998. Fish were placed in an ice filled cooler and brought back to the DWM laboratory for processing. Fish were sorted by type and processed at the DWM laboratory, as composite samples comprised of tissue from two or more like-sized individual fish. Protocols designed to assure accuracy and prevent cross-contamination of samples were followed for collecting, processing and shipping fish. Lengths and weights were measured and fish were visually inspected for tumors, lesions, or other anomalies. Scale or pectoral fin spine samples were obtained from each fish to determine age. Fish were filleted (skin off) on glass cutting boards and prepared for freezing. All equipment used in the filleting process was rinsed in tap water to remove slime, scales, and other fluids such as blood, and then re-rinsed in deionized water before (and/or after) each sample. Composite samples (single fillets from two or more like-sized individuals of the same species) targeted for % lipids, PCB and organochlorine pesticide analysis were wrapped together in aluminum foil. Composite samples targeted for metals analysis were placed in VWR 32-ounce high-density polyethylene (HDPE) cups with covers. Samples were tagged and frozen for subsequent delivery to the WES laboratory. Methods used at WES for metals and PCB/organochlorine pesticide analysis is provided in Appendix A of this report and additional information is available from the WES laboratory (MA DEP 1995). According to standard practice, all laboratory analytical results were forwarded to the MDPH for review. 1994 fish toxics In August and September 1994, MA DEP OWM at two stations in the Quinebaug River Basin conducted fish toxics monitoring (Figure B3). Using boat-mounted electrofishing gear OWM staff collected fish on 30 August 1994 from Hamilton Reservoir (Holland), and on 8 September 1994 from the French River (in the impoundment at Clara Barton Road known as Thayers Pond) (Oxford). Fish selected for analysis were placed in an ice filled cooler and brought back to the OWM laboratory for processing. Data for the French River in Oxford (F0088) and the Hamilton Reservoir in Holland (F0087) is presented in Table B12. BENTHIC MACROINVERTEBRATE STUDIES A technical memorandum (Appendix C) by John Fiorentino of MA DEP DWM entitled French & Quinebaug River Watershed 1999 Biological Assessment presents details related to the collection, handling, and processing of aquatic macroinvertebrate samples (as well as the analysis results) collected from selected sites in the French & Quinebaug River Basins during August and September 1999. PERIPHYTON and PHYTOPLANKTON Periphyton was collected at ten stations in the Quinebaug River Basin (Quinebaug River at stations QR0B, QR00, QR01B, QR01C, QR03, QR04U, and QR06, and Cady Brook at stations CA04, CA04b, and CA06) and at seven stations in the French River Basin (Town Meadow Brook at stations MB11, and MB12, and the French River at stations FR14, FR15, FR11, FR17, and FR18) during the summer of 1999. Details are presented in a technical memorandum by Joan Beskenis of MA DEP DWM entitled FRENCH AND QUINEBAUG RIVERS - PERIPHYTON SURVEY RESULTS 1999 that is provided in Appendix G of this report. LAKES In the French River Basin there are 68 lakes, ponds or impoundments (the term "lakes" will hereafter be used to include all), covering 3,556 acres, that have been identified and assigned Pond and Lake Information System (PALIS) code numbers (Ackerman 1989 and MA DEP 2001). During July, August, and September 1994 OWM synoptic surveys were conducted on 44 (65%) of these lakes covering 2,203 acres (62%) of the French River Basin lake acerage. In the Quinebaug River Basin there are 51 lakes, ponds or impoundments (the term "lakes" will hereafter be used to include all), covering 2,358 acres, that have been identified and assigned Pond and Lake Information System (PALIS) code numbers (Ackerman 1989 and MA DEP 2001). During July, August, and September 1994 OWM synoptic surveys were conducted on 27 (53%) of these lakes covering 1,956 acres (83%) of the Quinebaug River Basin lake acerage. Observations, from at least one access point on each lake (multiple access points on larger lakes), were recorded on standardized field sheets during the synoptic surveys. An attempt was made to observe the entire surface area of each lake to determine the extent of areal macrophyte cover. At each sampling location, general water quality conditions, identification and abundance of aquatic and wetland macrophyte plant species, and estimates of total percent areal coverage were recorded. Macrophyte visual observations were augmented at each station by identifying plant specimens collected from the lake bottom. Specimens were retrieved utilizing a rake (a short handled, double-sided garden rake on a 50 foot line) thrown to its maximum extension in multiple directions at each station. Macrophytes collected on the rake were identified (in-situ or in the laboratory) and recorded on the field sheets. Transparency was measured where possible using a standard 20-centimeter diameter Secchi disk attached to a rope with metric calibrations. When Secchi disk measurements were not feasible, transparency was estimated as being above or below 1.2 meters. This depth is based on the MA DPH bathing beach standard (4 foot Secchi disk depth) (MA DPH 1969). Trophic status has been estimated primarily using visual observations of macrophyte cover and phytoplankton populations. Trophic status (level of nutrient enrichment) determinations and designated use impairment assessments were made on site. Occasionally, older data from more detailed diagnostic studies were utilized. A more definitive assessment of trophic status would require more extensive collection of water quality and biological data. RESULTS STREAM WATER QUALITY MONITORING Stream water quality monitoring was conducted by MA DEP DWM personel in the Quinebaug River Basin on Cady Brook in Charlton and Southbridge, during 1999. Hydrolab data were collected from eleven stations in the Cady Brook portion of the Quinebaug River Basin drainage area during the 1999 MA DEP DWM surveys. Data are provided in Table B3. Discrete physico/chemical water sampling occurred at nine stations (Tables B4 and B5) and bacteria sampling occurred at eight stations (Table B6). Stream discharge was monitored by DWM personal at nine stations in the Cady Brook portion of the Quinebaug River Basin drainage area (Table B7). Results of this survey are presented in the draft report entitled CADY BROOK, QUINEBAUG RIVER 1999 WATER QUALITY AND WASTEWATER DISCHARGE DATA (Hartman 2001). Excerpted from CADY BROOK, QUINEBAUG RIVER 1999 WATER QUALITY AND WASTEWATER DISCHARGE DATA (Hartman 2001). During the 1999 Cady Brook survey, instream water quality appeared to be affected by both the Charlton WWTF and Sibley Brook. Charlton WWTF effluent discharge controlled levels of phosphorus and nitrogen instream, although Sibley Brook contributed to the nitrogen concentrations with a lesser effect on phosphorus levels. Fecal coliform values, BOD, and turbidity were also controlled by the Charlton WWTF, and to a lesser extent, Sibley Brook also affected the levels. Nitrogen values instream appeared to be affected by both the Charlton WWTF and Sibley Brook, with the Charlton WWTF contributing the higher concentration. The increases in the levels listed above gradually decreased as the distance downstream of the plant increased. The decreases in the nutrient levels corresponded also to increases in coverage of substrate organic mats of attached algae. The stream bottom, downstream of the treatment plant, appeared to be functioning as a nutrient uptake system, similar to a trickling filter at a wastewater treatment plant. Loadings were calculated in order to compare the relative impacts on Cady Brook from both the effluent of the treatment plant and the water from Sibley Brook. Loadings of nitrate, ammonia, total phosphorus, and ortho-phosphate from Sibley Brook were negligible as compared to the loadings from the WWTF. In contrast, loadings from organic nitrogen, total suspended solids, BOD, and chlorides were comparable. Hydrolab data were collected from two stations in the Quinebaug River Basin drainage area and one station in the French River Basin during the 1999 MA DEP/CERO survey. Data are provided in Table B8. Discrete physico/chemical water sampling results are presented in Table B9. During the 1998 DWM water quality surveys, Hydrolab data were collected from two stations in the Quinebaug River Basin drainage area, part of the Lower Worcester Plateau/Eastern Connecticut Upland subecoregion, as part of the 97-09/104 Project on Numeric Biocriteria authorized under the 104(b)(3) Wetlands and Water Quality Grant Program. Data are provided in Table B10. Table B3. 1999 MA DEP DWM Cady Brook drainage area in-situ Hydrolab data. Date OWMID Time Depth Temp pH Cond @ TDS DO SAT Turbidity (24hr) (m) (C) (SU) 25 C (mg/L) (mg/L) (%) (NTU) ((S/cm) CADY BROOK (Saris: 4129125) Station: CA03, Mile Point: 5.3 Description: approximately 20 feet upstream/north of Route 20 bridge, Charlton 05/19/99 41-0034 09:45 ** i 17.4 7.1 444 284 9.1 93 -- 07/27/99 41-0120 09:26 s 0.2 s 22.7 s 7.2 s 378 s 242 s 7.7 s 89 s 1.2 s CADY BROOK (Saris: 4129125) Station: CA04, Mile Point: 5.07 Description: upstream/north of Charlton WWTP discharge, Charlton 06/22/99 41-0037 08:39 ** i 14.5 6.8 536 343 9.4 90 -- 41-0043 15:45 ** i 20.9 7.0 538 344 8.2 89 -- 06/23/99 41-0052 04:28 ** i 15.3 6.8 540 346 8.1 79 -- 08/17/99 41-0065 08:53 ** i 18.5 6.8 562 360 8.4 88 -- 41-0074 16:08 ** i 23.8 7.0 575 368 9.3 108 -- 08/18/99 41-0082 04:27 0.1 i 19.3 6.9 594 380 7.5 80 -- Pipe/Discharge to CADY BROOK (Saris: 4129125) Station: MA0101141, Mile Point: 5.06 Description: Charlton WWTP (NPDES=MA0101141) discharge pipe (CA05A sampled just before mixing with river, CA05B sampled before UV), Charlton 06/22/99 41-0064 (CA05A) 08:54 ** i 19.0 7.1 1,048 c 671 c 8.8 93 -- 08/17/99 41-0066 (CA05A) 08:34 ** i 22.5 7.1 1,115 c 714 c 8.0 91 -- CADY BROOK (Saris: 4129125) Station: CA06, Mile Point: 5.0 Description: east of Route 169 approximately 230 feet downstream/south of Charlton WWTP discharge, Charlton (near wooden footbridge) 05/19/99 41-0035 10:12 0.1 i 16.6 6.9 439 281 9.1 92 -- 06/22/99 41-0038 09:21 ** i 16.9 6.9 746 c 478 c 8.9 90 -- 41-0044 16:08 ** i 20.6 u 7.1 762 c 488 c 8.2 u 89 u -- 06/23/99 41-0053 04:57 ** i 16.4 7.0 736 c 471 c 7.3 73 -- 07/27/99 41-0121 10:04 s 0.1 is 22.6 s 7.0 s 554 s 355 s 7.6 s 85 s ** ms 08/17/99 41-0067 09:46 ** i 20.6 6.7 868 c 555 c 6.6 72 -- 41-0075 16:29 ** i 23.2 7.2 969 c 620 c 7.5 87 -- 08/18/99 41-0083 04:53 ** i 21.3 7.3 963 c 617 c 5.9 65 -- Unnamed Tributary Station: SB05, Mile Point: 0.04 Description: unnamed Cady Brook tributary draining Sibley Ponds approximately 30 feet upstream/west of Route 169 bridge, Charlton 06/22/99 41-0039 09:49 0.1 i 17.1 6.9 419 268 8.9 90 -- 41-0045 16:32 ** i 21.5 7.0 419 268 7.2 80 -- 06/23/99 41-0054 05:16 ** i 16.3 6.8 420 269 7.3 72 -- 07/27/99 41-0122 10:27 s 0.1 is 21.9 s 6.9 s 512 s 328 s 7.7 s 87 s 3.6 s 08/17/99 41-0070 10:22 ** i 19.4 6.8 555 355 8.4 90 -- 41-0076 16:43 ** i 25.2 7.0 561 359 8.6 104 -- 08/18/99 41-0084 05:13 ** i 20.0 6.9 556 356 6.3 68 -- CADY BROOK (Saris: 4129125) Station: CA08, Mile Point: 4.6 Description: east of Route 169 approximately 350 meters downstream/south of confluence with unnamed tributary draining Sibley Ponds, Charlton (in from utility pole #99) 06/23/99 41-0055 05:38 0.1 i 15.9 6.8 558 357 6.6 65 -- 08/18/99 41-0085 05:33 ** i 20.7 7.0 774 c 495 c 5.6 61 -- ** = Censored or missing data -- = No data i = inaccurate readings from Hydrolab multiprobe likely; may be due to significant pre-survey calibration problems, post-survey calibration readings outside typical acceptance range for the low ionic check and for the deionized blank water check, or lack of calibration of the depth sensor prior to use. m = method not followed; one or more protocols contained in the DWM Hydrolab SOP not followed, ie. operator error (eg. less than 3 readings per station (rivers) or per depth (lakes), or instrument failure not allowing method to be implemented. s = Field sheet recorded data were used to accept data, not data electronically recorded in the Hydrolab surveyor unit, due to operator error or equipment failure. u = unstable readings, due to lack of sufficient equilibration time prior to final readings, non-representative location, highly-variable water quality conditions, etc. See Section 4.1 for acceptance criteria. c = Greater than Conductivity calibration std. (>718, 1,413, 2,760, 6,668 or 12,900 uS/cm); also used for TDS and Salinity calculations based on qualified conductivity data, or that calculation was not possible due to censored conductivity data ( TDS and Salinity are calculated values and entirely based on conductivity reading). (See Section 4.1 for acceptance criteria.) Table B3. Continued. 1999 MA DEP DWM Cady Brook drainage area in-situ Hydrolab data. Date OWMID Time Depth Temp pH Cond @ TDS DO SAT Turbidity (24hr) (m) (C) (SU) 25 C (mg/L) (mg/L) (%) (NTU) ((S/cm) CADY BROOK (Saris: 4129125) Station: CA10, Mile Point: 3.8 Description: upstream/north at Snake Hill Road, Charlton 06/22/99 41-0040 10:20 0.1 i 14.6 7.2 530 339 9.4 91 -- 41-0047 16:57 ** i 20.2 7.2 534 342 8.2 88 -- 06/23/99 41-0056 06:00 ** i 15.4 7.1 534 342 8.6 84 -- 07/27/99 41-0123 10:49 s 0.1 is 20.7 s 7.3 s 517 s 331 s 8.3 s 92 s 2.2 s 08/17/99 41-0071 10:57 ** i 18.9 7.0 655 419 8.5 89 -- 41-0077 17:01 ** i 22.8 7.1 677 433 7.7 88 -- 08/18/99 41-0086 05:53 ** i 20.6 7.2 688 440 7.4 81 -- CADY BROOK (Saris: 4129125) Station: CA12, Mile Point: 3.3 Description: approximately 20 feet upstream/east of Route 169 bridge, Charlton (near pipeline crossing) 06/22/99 41-0048 17:23 0.1 i 21.5 7.3 537 343 8.4 93 -- 06/23/99 41-0057 06:21 0.1 i 15.5 7.0 542 347 8.2 80 -- 08/17/99 41-0078 17:17 ** i 23.6 7.3 644 412 8.6 100 -- 08/18/99 41-0087 06:10 ** i 20.9 7.1 663 425 6.9 75 -- CADY BROOK (Saris: 4129125) Station: CA14, Mile Point: 2.5 Description: first bridge crossing of Route 169 approximately 1000 meters north of Charlton/Southbridge border, Charlton 06/22/99 41-0041 10:53 0.1 i 15.6 7.2 520 333 9.5 94 -- 41-0049 17:47 0.1 i 19.4 7.2 520 333 8.2 87 -- 06/23/99 41-0058 06:40 0.1 i 15.4 7.1 526 337 8.9 87 -- 07/27/99 41-0124 11:09 s 0.1 is 21.0 s 7.4 s 483 s 309 s 8.8 s 97 s 2.4 s 08/17/99 41-0072 11:26 ** i 20.0 7.2 623 399 9.2 99 -- 41-0079 17:40 ** i 22.6 7.3 640 410 8.5 97 -- 08/18/99 41-0088 06:24 0.1 i 20.3 7.2 649 416 8.0 87 -- CADY BROOK (Saris: 4129125) Station: CA16, Mile Point: 1.7 Description: approximately 5 feet upstream/north of Brookside Drive bridge, Southbridge 06/22/99 41-0050 18:11 0.1 i 18.9 7.2 475 304 8.4 88 -- 06/23/99 41-0059 07:00 0.1 i 14.5 7.1 473 303 9.3 89 -- 07/27/99 41-0125 11:36 s 0.1 is 20.7 s 7.5 s 462 s 295 s 9.0 s 99 s 7.4 s 08/17/99 41-0080 18:09 ** i 22.3 7.2 533 341 8.3 94 -- 41-0092 11:55 ** i 19.9 7.2 526 337 9.5 102 -- 08/18/99 41-0089 06:40 0.1 i 19.4 7.2 529 339 8.3 88 -- CADY BROOK (Saris: 4129125) Station: CA18, Mile Point: 0.3 Description: off upstream/northern side of Randolph Street bridge, Southbridge 05/19/99 41-0036 10:51 0.2 15.8 7.2 316 202 10.1 99 -- 06/22/99 41-0042 11:18 0.2 16.1 u 7.4 u 404 u 259 u 9.9 98 -- 41-0051 18:34 0.2 20.1 7.3 456 292 8.4 91 -- 06/23/99 41-0060 07:24 0.2 14.9 7.1 450 288 9.3 90 -- 07/27/99 41-0119 11:59 s ** is 21.3 s 7.5 s 423 s 271 s 9.0 s 100 s 3.2 s 08/17/99 41-0073 12:26 ** i 21.6 7.4 472 302 9.6 106 -- 41-0081 18:28 ** i 23.7 7.5 474 303 8.5 99 -- 08/18/99 41-0090 06:58 0.1 i 19.8 7.1 479 306 8.4 90 -- ** = Censored or missing data -- = No data i = inaccurate readings from Hydrolab multiprobe likely; may be due to significant pre-survey calibration problems, post-survey calibration readings outside typical acceptance range for the low ionic check and for the deionized blank water check, or lack of calibration of the depth sensor prior to use. s = Field sheet recorded data were used to accept data, not data electronically recorded in the Hydrolab surveyor unit, due to operator error or equipment failure. u = unstable readings, due to lack of sufficient equilibration time prior to final readings, non-representative location, highly-variable water quality conditions, etc. See Section 4.1 for acceptance criteria. c = Greater than Conductivity calibration std. (>718, 1,413, 2,760, 6,668 or 12,900 uS/cm); also used for TDS and Salinity calculations based on qualified conductivity data, or that calculation was not possible due to censored conductivity data ( TDS and Salinity are calculated values and entirely based on conductivity reading). (See Section 4.1 for acceptance criteria.) Table B4. 1999 MA DEP DWM Cady Brook drainage area, instream physico/chemical data. All units in mg/L unless otherwise noted. OWMID OWMID Date Time Alkalinity Hardness Chloride Suspended Turbidity Total Ammonia NO3 - NO2 BOD CBOD QA/QC (24hr) Solids (NTU) Kjeldahl 5-day 5-day Nitrogen CADY BROOK (Saris: 4129125) Station: CA03, Mile Point: 5.3 Description: approximately 20 feet upstream/north of Route 20 bridge, Charlton 41-0034 05/19/99 9:45 -- -- -- -- -- 0.55 <0.02 0.06 -- -- CADY BROOK (Saris: 4129125) Station: CA04, Mile Point: 5.07 Description: upstream/north of Charlton WWTP discharge, Charlton 41-0037 06/22/99 8:39 26 54 b 130 1.2 0.85 0.21 <0.02 0.16 <2.0 j -- 41-0065 08/17/99 8:53 36 60 130 1.3 0.65 0.14 <0.02 0.05 -- <2.0 CADY BROOK (Saris: 4129125) Station: MA0101141, Mile Point: 5.06 Description: Charlton WWTP (NPDES=MA0101141) discharge pipe (CA05A sampled just before mixing with river, CA05B sampled before UV), Charlton 41-0063 (CA05B) 06/22/99 ** 41 87 b 100 -- 3.7 h 3.5 1.6 64 6.9 -- 41-0064 (CA05A) 06/22/99 8:54 51 88 b 99 -- 2.8 h 2.5 0.09 62 -- -- 41-0091 (CA05B) 08/17/99 ** 62 79 110 5.6 4.3 7.6 7.5 69 -- ** CADY BROOK (Saris: 4129125) Station: CA06, Mile Point: 5.0 Description: east of Route 169 approximately 230 feet downstream/south of Charlton WWTP discharge, Charlton (near wooden footbridge) 41-0035 05/19/99 10:12 -- -- -- -- -- 0.46 <0.02 0.17 -- -- 41-0061 41-0038 06/22/99 ** 36 67 b 120 3.0 2.6 1.3 0.03 27 3.6 j -- 41-0038 41-0061 06/22/99 9:21 36 67 b 120 4.8 2.8 1.2 0.04 27 3.9 j -- 41-0067 41-0068 08/17/99 9:46 43 73 120 3.2 2.6 1.2 0.21 36 -- 2.1 41-0068 41-0067 08/17/99 9:46 43 72 120 3.4 2.5 1.3 0.20 38 -- 2.4 Unnamed Tributary Station: SB05, Mile Point: 0.04 Description: unnamed Cady Brook tributary draining Sibley Ponds approximately 30 feet upstream/west of Route 169 bridge, Charlton 41-0039 06/22/99 9:49 19 42 b 100 1.6 2.5 0.51 0.07 1.0 2.7 j -- 41-0070 08/17/99 10:22 28 61 130 2.4 1.5 0.34 0.03 0.63 -- <2.0 ** = Censored or missing data -- = No data b = blank Contamination in lab reagent blanks and/or field blank samples (indicating possible bias high and false positives). h = holding time violation (usually indicating possible bias low) j = estimated value; used for lab-related issues where certain lab QC criteria are not met and re-testing is not possible (as identified by the WES lab only). Also used to report sample data where the sample concentration is less than the reporting limit or RDL and greater than the method detection limit or MDL (mdl< x 0.5 ** LB-0401 0.5 -- -- 0.12 -- Gore Pond (Baker Pond) (Palis: 42018) Station: A Description: deep hole in northern quadrant, Charlton 08/04/99 9:30 2.1 6.1 LB-0090 0 - 5.5 -- -- -- 35 LB-0088 0.5 7.0 29 0.018 -- LB-0089 5.5 18 170 0.10 -- 09/01/99 14:12 2.6 6.1 LB-0245 ** - ** -- -- -- 1 LB-0243 0.5 6.5 40 0.017 -- LB-0244 5.5 27 160 0.14 -- 10/05/99 12:20 3.2 6.1 LB-0396 0 - 6.0 -- -- -- <1 LB-0394 0.5 7.0 48 0.019 -- LB-0395 5.6 6.5 50 0.014 -- Station: B Description: approximate center of southern quadrant, Dudley 08/04/99 ** ** ** LB-0091 ** -- -- 0.015 -- 09/01/99 ** ** 3.1 LB-0246 0.5 6.0 40 0.018 -- 10/05/99 ** 2.9 ** LB-0399 0 - 2.5 -- -- -- **m LB-0397 0.5 7.0 50 0.018 -- LB-0398 2.5 5.5 55 0.016 -- Unnamed Tributary Station: D Description: northwest inlet of Gore Pond from downstream side of unnamed road which is southwest off of Baker Pond Road, Charlton 08/04/99 ** -- ** ------------------------- Not enough water to take sample---------------------- -- -- -- -- 10/05/99 ** -- ** LB-0400 0.5 -- -- 0.046 -- ** = Censored or missing data -- = No data b = blank Contamination in lab reagent blanks and/or field blank samples (indicating possible bias high and false positives). d = precision of field duplicates (as RPD) did not meet project data quality objectives identified for program or in QAPP; batch samples may also be affected h = holding time violation (usually indicating possible bias low) m = method SOP not followed, only partially implemented or not implemented at all, due to complications with sample matrix (e.g. sediment in sample, floc formation), lab error (e.g., cross-contamination between samples), additional steps taken by the lab to deal with matrix complications, and lost/unanalyzed samples. p = samples not preserved per SOP or analytical method requirements. Table B14. Continued. 1999 MA DEP DWM French & Quinebaug River Basins inlake Secchi depth, alkalinity, color, total phosphorus and chlorophyll a data. Date Time Secchi Station OWMID OWMID Sample Alkalinity Apparent Total Chlorophyll a (24hr) Depth Depth QA/QC Depth (mg/l) Color Phosphorus (mg/m3) (m) (m) (m) (PCU) mg/l French River Basin Larner Pond (Palis: 42068) Station: A Description: deep hole, southern end near dam, Dudley 07/28/99 11:00 1.7 3.4 11:05 1.6 LB-0071 0 - 2.9 -- -- -- 2b LB-0069 0.5 19 17d 0.028 -- LB-0070 2.9 20 70d 0.033 -- 08/26/99 ** 1.8 3.4 LB-0223 0 - 2.5 -- -- -- 8 LB-0221 ** 19 35 0.024 -- LB-0220 0.5 20 <15 0.023 -- 09/22/99 8:30 2.3 3.5 LB-0372 0 - 3.0 -- -- -- 20 LB-0370 0.5 18 38 0.024 -- LB-0371 3.0 18 32 0.022 -- Station: B Description: center of the lobe east of Wayne Avenue and Michael Lane, Dudley 07/28/99 ** ** ** LB-0072 0.5 -- -- 0.048 -- Pierpont Meadow Pond (Palis: 42043) Station: A Description: deep hole south of Charlton/Dudley border, Dudley 08/04/99 13:38 1.8 3.4 13:45 1.9 LB-0097 ** - ** -- -- -- 3 LB-0095 LB-0094 0.5 10 17 **d -- LB-0094 LB-0095 0.5 12 17 **d -- LB-0101 2.9 12 17 0.018d -- 09/01/99 10:45 1.9 2.8 LB-0242 ** - ** -- -- -- **m LB-0239 LB-0238 0.5 12 29 0.019 -- LB-0238 LB-0239 0.5 11 29 0.022 -- LB-0240 2.5 12 23 0.019 -- 10/05/99 ** 2.6 3.4 LB-0392 0 - 3.0 -- -- -- <1 LB-0389 LB-0388 0.5 11 22 0.016d -- LB-0388 LB-0389 0.5 11 23 0.027d -- LB-0391 3.0 11 24 0.019d -- Rochdale Pond (Palis: 42048) Station: A Description: deep hole in southeastern quadrant near outlet, Leicester 08/05/99 13:00 2.2 3.6 LB-0110 0 - 3.5 -- -- -- 17 LB-0106 0.5 14 60 0.035 -- LB-0114 3.1 21 85 0.10 -- 09/02/99 10:00 2.3 3.5 LB-0258 ** - ** -- -- -- 1 LB-0255 LB-0254 0.5 13 -- 0.028 -- LB-0254 LB-0255 0.5 14 46 0.028 -- LB-0257 3.0 14 46 0.037 -- 09/28/99 10:00 2.0 4.3 10:10 2.2 LB-0411 0 - 3.8 -- -- -- 1 LB-0409 0.5 11 70 0.037 -- LB-0410 3.8 10 70 0.034 -- ** = Censored or missing data -- = No data b = blank Contamination in lab reagent blanks and/or field blank samples (indicating possible bias high and false positives). d = precision of field duplicates (as RPD) did not meet project data quality objectives identified for program or in QAPP; batch samples may also be affected h = holding time violation (usually indicating possible bias low) m = method SOP not followed, only partially implemented or not implemented at all, due to complications with sample matrix (e.g. sediment in sample, floc formation), lab error (e.g., cross-contamination between samples), additional steps taken by the lab to deal with matrix complications, and lost/unanalyzed samples. Table B14. Continued. 1999 MA DEP DWM French & Quinebaug River Basins inlake Secchi depth, alkalinity, color, total phosphorus and chlorophyll a data. Date Time Secchi Station OWMID OWMID Sample Alkalinity Apparent Total Chlorophyll a (24hr) Depth Depth QA/QC Depth (mg/l) Color Phosphorus (mg/m3) (m) (m) (m) (PCU) mg/l French River Basin Wallis Pond (Palis: 42062) Station: A Description: deep hole, southern central lobe near dam, Dudley 07/28/99 9:05 >0.8 0.8 LB-0066 0 - 0.4 -- -- -- 3b LB-0063 LB-0064 0.4 20 46d 0.021 -- LB-0064 LB-0063 0.4 21 60d 0.022 -- LB-0067 0.4 19 46d 0.026 -- 08/26/99 10:30 >0.5 0.5 LB-0217 0.5 -- -- -- <1 LB-0215 LB-0214 0.5 31 31 0.028 -- LB-0214 LB-0215 0.5 30 43 0.028 -- 09/22/99 10:15 >1.0 1.0 LB-0367 ** - ** -- -- -- <1 LB-0364 LB-0363 0.5 14 60 0.025 -- LB-0363 LB-0364 0.5 12 49 0.025 -- Quinebaug River Basin Mill Road Pond (Palis: 41032) Station: A Description: deep hole, near dam at eastern end of pond, Brimfield 08/03/99 12:25 1.8 1.9 LB-0079 ** - ** -- -- -- 3 LB-0080 1.3 18 70 0.024 -- LB-0076 LB-0077 0.5 18 55 0.023 -- LB-0077 LB-0076 0.5 20 60 0.020 -- 08/31/99 12:20 >2.0 2.0 LB-0386 0 - 1.5 -- -- -- **h LB-0384 0.5 19 25 0.021 -- LB-0385 1.5 20 48 0.022 -- 09/29/99 9:51 >1.8 1.8 LB-0230 ** - ** -- -- -- 1 LB-0226 LB-0227 0.5 13 -- 0.025 -- LB-0227 LB-0226 0.5 11 -- 0.026 -- LB-0228 1.3 11 -- 0.029 -- Morse Pond (Palis: 41033) Station: A Description: deep hole near outlet at southern end, Southbridge 08/05/99 10:06 1.5 1.6 LB-0108 0 - 1.0 -- -- -- 3 LB-0104 LB-0103 0.5 15 46 0.14 -- LB-0103 LB-0104 0.5 15 50 0.12 -- 09/02/99 13:05 >1.3 1.3 LB-0262 ** - ** -- -- -- **m LB-0260 0.5 13 38 0.032 -- LB-0261 0.8 12 48 0.029 -- 09/28/99 11:40 >1.8 1.8 LB-0407 0 - 1.3 -- -- -- <1 LB-0403 LB-0404 0.5 9.0 41 0.017 -- LB-0404 LB-0403 0.5 9.0 44 0.018 -- LB-0406 1.3 9.0 38 0.020 -- ** = Censored or missing data -- = No data b = blank Contamination in lab reagent blanks and/or field blank samples (indicating possible bias high and false positives). d = precision of field duplicates (as RPD) did not meet project data quality objectives identified for program or in QAPP; batch samples may also be affected h = holding time violation (usually indicating possible bias low) m = method SOP not followed, only partially implemented or not implemented at all, due to complications with sample matrix (e.g. sediment in sample, floc formation), lab error (e.g., cross-contamination between samples), additional steps taken by the lab to deal with matrix complications, and lost/unanalyzed samples. Table B14. Continued. 1999 MA DEP DWM French & Quinebaug River Basins inlake Secchi depth, alkalinity, color, total phosphorus and chlorophyll a data. Date Time Secchi Station OWMID OWMID Sample Alkalinity Apparent Total Chlorophyll a (24hr) Depth Depth QA/QC Depth (mg/l) Color Phosphorus (mg/m3) (m) (m) (m) (PCU) mg/l Quinebaug River Basin Sherman Pond (Palis: 41046) Station: A Description: deep hole in northeast quadrant of pond, Brimfield 08/03/99 9:40 2.1 3.0 10:10 2.1 LB-0083 0 - 2.5 -- -- -- 1 LB-0082 0.5 9.0 32 0.019 -- LB-0084 2.5 10 46 0.017 -- 08/31/99 10:50 2.0 3.0 LB-0382 0 - 2.5 -- -- -- **h LB-0379 LB-0378 0.5 12 29 0.021 -- LB-0378 LB-0379 0.5 **m 38 0.022 -- LB-0381 2.5 11 29 0.028 -- 09/29/99 12:30 2.6 3.1 LB-0233 ** -- -- -- <1 LB-0232 0.5 9.0 -- 0.020 -- LB-0235 2.5 10 -- 0.022 -- Sibley Pond north basin (Palis: 41047) Station: A Description: North Basin, deep hole at southern end, Charlton 07/29/99 10:15 1.6 3.4 LB-0055 0 - 2.8 -- -- -- 64 LB-0052 LB-0051 0.5 15d 31d 0.030 -- LB-0051 LB-0052 0.5 25d 17d 0.030 -- LB-0054 2.8 31 260d 0.17 -- 08/25/99 11:20 1.2 3.0 11:25 0.9 LB-0205 0 - 2.5 -- -- -- 4 LB-0201 LB-0202 0.5 20 44d 0.050 -- LB-0202 LB-0201 0.5 19 25d 0.048 -- LB-0204 2.5 19 46d 0.12 -- 09/23/99 11:26 1.4 3.4 LB-0360 0 - 2.9 -- -- -- <1 LB-0358 0.5 15 75 0.091 -- LB-0359 2.9 19 75 0.099 -- Station: B Description: North Basin, close to inlet at northern end, Charlton 07/29/99 ** ** ** LB-0056 ** -- -- 0.035 -- Unnamed Tributary Station: C Description: approximately 50 meters up an unnamed tributary flowing into the northern end of Sibley Pond North Basin, Charlton 08/25/99 ** -- ** ------------------------- Not enough water to take sample---------------------- ** = Censored or missing data -- = No data b = blank Contamination in lab reagent blanks and/or field blank samples (indicating possible bias high and false positives). d = precision of field duplicates (as RPD) did not meet project data quality objectives identified for program or in QAPP; batch samples may also be affected h = holding time violation (usually indicating possible bias low) m = method SOP not followed, only partially implemented or not implemented at all, due to complications with sample matrix (e.g. sediment in sample, floc formation), lab error (e.g.,. cross-contamination between samples), additional steps taken by the lab to deal with matrix complications, and lost/unanalyzed samples. Table B14. Continued. 1999 MA DEP DWM French & Quinebaug River Basins inlake Secchi depth, alkalinity, color, total phosphorus and chlorophyll a data. Date Time Secchi Station OWMID OWMID Sample Alkalinity Apparent Total Chlorophyll a (24hr) Depth Depth QA/QC Depth (mg/l) Color Phosphorus (mg/m3) (m) (m) (m) (PCU) mg/l Quinebaug River Basin Sibley Pond south basin (Palis: 41048) Station: A Description: South Basin, deep hole close to center of pond, Charlton 07/29/99 11:41 0.6 ** LB-0059 0 - 1.6 -- -- -- **m LB-0057 0.5 21 48d 0.16 -- LB-0058 1.6 24 70d 0.16 -- 08/25/99 9:35 1.2 1.8 LB-0209 ** - ** -- -- -- 3 LB-0208 1.3 25 29d 0.15 -- LB-0207 0.5 25 29d 0.082 -- 09/23/99 10:00 1.0 2.1 LB-0356 0 - 1.6 -- -- -- 2 LB-0352 LB-0353 0.5 18 70 0.088 -- LB-0353 LB-0352 0.5 19 75 0.084 -- LB-0355 1.5 18 70 0.090 -- ** = Censored or missing data -- = No data b = blank Contamination in lab reagent blanks and/or field blank samples (indicating possible bias high and false positives). d = precision of field duplicates (as RPD) did not meet project data quality objectives identified for program or in QAPP; batch samples may also be affected h = holding time violation (usually indicating possible bias low) m = method SOP not followed, only partially implemented or not implemented at all, due to complications with sample matrix (e.g. sediment in sample, floc formation), lab error (e.g., cross-contamination between samples), additional steps taken by the lab to deal with matrix complications, and lost/unanalyzed samples. fish tOXICS MONITORING 1999 FISH TOXICS The results of MA DEP DWM 1999 fish toxics monitoring surveys are briefly described below for each lake sampled (MA DEP 1999h). These lakes sampled in 1999 are located in the French River basin. Buffumville Lake, Charlton/Oxford F0079 (Table B15) Samples of largemouth bass (Micropterus salmoides), yellow perch (Perca flavescens), chain pickerel (Esox niger), pumpkinseed (Lepomis gibbosus) and yellow bullhead (Ameiurus natalis) were collected from Buffumville Lake, Charlton/Oxford. The lipids content ranged between 0.06 and 0.15%. Cadmium, PCB, pesticides, and lead were not detected in the edible fillets of any sample analyzed for these analytes from Buffumville Lake. Arsenic levels ranged from non-detect <0.04 to 0.09 mg/kg wet weight. Selenium levels ranged from 0.12 to 0.27 mg/kg wet weight. Mercury in the fish tissue from Buffumville Lake ranged from 0.35 to 0.95 mg/kg wet weight. Due to elevated mercury concentrations a fish consumption advisory was issued by MDPH for Buffumville Lake, Charlton/Oxford (MDPH 2002). Webster Lake, Webster F0073 (Table B15) Samples of largemouth bass, white perch (Morone Americana), bluegill (Lepomis macrochirus), brown bullhead (Ameiurius nebulosus), and yellow perch were collected from Webster Lake, in Webster. The lipids content ranged between 0.05 and 0.30%. Cadmium, lead, PCB and arsenic were not detected in the edible fillets of any sample analyzed for these analytes from Webster Lake. Selenium levels ranged from 0.08 to 0.29 mg/kg wet weight. Mercury in the fish tissue from Webster Lake ranged from 0.14 to 0.32 mg/kg wet weight. With the exception of DDE being detected at 0.014 (g/g in a three fish composite sample, all other pesticides were not detected (see Appendix A for list of analytes and detection limits). 1998 fish toxics The results of MA DEP DWM 1998 fish toxics monitoring surveys are briefly described below for each lake sampled (MA DEP 1998). The lakes sampled in 1998 occur in both the French and Quinebaug River Basins. Texas Pond, Oxford F0058 (Table B16) Samples of largemouth bass, white perch, yellow bullhead, and white sucker, (Castomus commersoni) were collected from Texas Pond in Oxford. The lipids content ranged between 0.05 and 1.6%. Cadmium, arsenic, PCB, and lead were not detected in the edible fillets of any sample analyzed for these analytes from Texas Pond. Selenium levels ranged from 0.103 to 0.276 mg/kg wet weight. Mercury in the fish tissue from Texas Pond ranged from 0.19 to 0.77 mg/kg wet weight. The mercury data triggered a site-specific advisory against the consumption of fish from Texas Pond, North Andover (MDPH 1999). With the exception of DDE being detected at 0.014 (g/g in a three fish composite sample, all other pesticides were not detected (see Appendix A for list of analytes and detection limits). Quinebaug River, Brimfield F0057 (Table B16) Samples of largemouth bass, white sucker, yellow bullhead, bluegill and yellow perch were collected from the Quinebaug River in Brimfield (upstream/west /southwest of Brimfield Road). The lipids content ranged between 0.09 and 0.79%. Cadmium, lead, arsenic, PCB and pesticides were not detected in the edible fillets of any sample analyzed for these analytes from this section of the Quinebaug River. Selenium levels ranged from 0.22 to 0.41 mg/kg wet weight. Mercury in the fish tissue ranged from 0.32 to 0.84 mg/kg wet weight. Due to elevated mercury concentrations a fish consumption advisory was issued by MDPH for the Quinebaug River, East Brimfield Reservoir, Holland Pond, Brimfield/Holland (MDPH 1999). 1994 fish toxics The goal of the 1994 fish toxics monitoring was to screen resident fishes for PCB, organochlorine pesticides, percent lipids, and selected metals (As, Cd, Pb, Hg and Se). Where possible, fish selected for analysis represented species and sizes desired by the angling public for consumption, as well as different feeding guilds (i.e., predator, invertivore, omnivore). Survey results are presented in Table B17 (MA DEP 1994a). The waters sampled in 1994 occur in the Quinebaug River basin. Hamilton Reservoir, Holland (F0087) (Table B17) Samples of yellow bullhead, yellow perch, brown bullhead and largemouth bass were collected from the Hamilton Reservoir in Holland. The lipids content ranged between 0.15 and 1.3%. Cadmium, lead, PCBs pesticides, and arsenic were not detected in the edible fillets of any sample analyzed for these analytes from Hamilton Reservoir. Selenium levels ranged from 0.103 to 0.285 mg/kg wet weight. Mercury in the fish tissue ranged from 0.16 to 0.29 mg/kg wet weight. French River (Thayers Pond - impoundment at Clara Barton Road), Oxford (F0088) (Table B17) Samples of largemouth bass, smallmouth bass (Micropterus dolomieu), brown bullhead and yellow perch were collected from the French River (Thayers Pond - impoundment at Clara Barton Road), Oxford. The lipids content ranged between 0.15 and 0.80%. Cadmium, lead, arsenic, PCB, and pesticides were not detected in the edible fillets of any sample analyzed for these analytes from this reach of the French River. Selenium levels ranged from 0.043 to 0.125 mg/kg wet weight. Mercury in the fish tissue ranged from 0.140 to 0.480 mg/kg wet weight. BENTHIC MACROINVERTEBRATE STUDIES A technical memorandum (Appendix C) by John Fiorentino of MA DEP DWM entitled French & Quinebaug River Watersheds 1999 Biological Assessment presents the aquatic macroinvertebrate analysis results (as well as details related to sampling and processing) for samples collected from selected sites in the French & Quinebaug River Basins during August and September 1999. Table B15. 1999 MA DEP DWM French River Basin fish toxics monitoring data for Buffumville Lake, Charlton/Oxford and Webster Lake, Webster. Results, reported in wet weight, are from composite samples of fish fillets with skin off. Sample IDCollection DateSpecies1 CodeLength (cm)Weight (g)Sample ID (laboratory sample #)Cd (mg/kg)Hg (mg/kg)Pb (mg/kg)As (mg/kg)Se (mg/kg)Lipids (%)PCB ((g/g)Pesticides ((g/g)Buffumville Lake, Charlton/Oxford F0079BUF99-016/29/99LMB31.536099251 (L990228-1)BUF99-026/29/99LMB31.9400<0.020.85<0.20<0.040.180.06NDNDBUF99-036/29/99LMB31.1350BUF99-046/29/99YP22.012099252 (L990228-2)BUF99-056/29/99YP23.5160<0.020.68<0.20<0.040.270.12NDNDBUF99-066/29/99YP25.3190BUF99-076/29/99CP42.240099253 (L990228-3)BUF99-086/29/99CP37.6340<0.020.95<0.20<0.040.120.06NDNDBUF99-096/29/99CP36.0300BUF99-106/29/99P18.014099254 (L990228-4)BUF99-116/29/99P19.3140<0.020.35<0.200.090.270.06NDNDBUF99-126/29/99P17.4110BUF99-136/29/99YB28.140099255 (L990228-5)BUF99-146/29/99YB26.3300<0.020.62<0.20<0.040.130.15NDNDBUF99-156/29/99YB25.9270Webster Lake, Webster F0073WBF99-016/14/99LMB31.444099234 (L990214-1)WBF99-026/14/99LMB33.7530<0.020.32<0.20<0.040.100.05NDNDWBF99-036/14/99LMB31.6430WBF99-046/14/99WP23.521099235 (L990214-2)WBF99-056/14/99WP28.4300<0.020.22<0.20<0.040.250.12NDNDWBF99-066/14/99WP25.9240WBF99-076/14/99YP19.79099236 (L990214-3)WBF99-086/14/99YP19.590<0.020.24<0.20<0.040.190.09NDNDWBF99-096/14/99YP18.880WBF99-106/14/99B18.710099237 (L990214-4)WBF99-116/14/99B17.6100<0.020.23<0.20<0.040.290.30ND0.014*WBF99-126/14/99B18.0100WBF99-136/14/99BB31.940099238 (L990214-5)WBF99-146/14/99BB32.0420<0.020.14<0.20<0.040.080.15NDNDWBF99-156/14/99BB32.34201Speciesbluegill (B) Lepomis macrochiruslargemouth bass (LMB) Micropterus salmoidesyellow bullhead (YB) Ameiurus natalisbrown bullhead (BB) Ameiurus nebulosuspumpkinseed (P) Lepomis gibbosusyellow perch (YP) Perca flavescenschain pickerel (CP) Esox nigerwhite perch (WP) Morone americanaND = not detected or the analytical result is at or below the established detection limit (MDL). See Appendix A for MDL.* DDE (all other analytes tested were ND) NOTE: mg/kg = (g/g = ppm = mg/l Table B16. 1998 MA DEP DWM fish toxics monitoring data for Texas Pond, Oxford and the Quinebaug River, Brimfield. Results, reported in wet weight, are from composite samples of fish fillets with skin off. Sample IDCollection DateSpecies1 CodeLength (cm)Weight (g)Sample ID (laboratory sample #)Cd (mg/kg)Hg (mg/kg)Pb (mg/kg)As (mg/kg)Se (mg/kg)Lipids (%)PCB ((g/g)Pesticides ((g/g)French River BasinTexas Pond, Oxford (impoundment of the French River) F0058TPF98-17/28/98WP26.026098027 (L980522-1)TPF98-27/28/98WP24.5230<0.020.27<0.2<0.0400.2761.6ND0.014*TPF98-37/28/98WP24.6220TPF98-47/28/98WS41.676098028 (L980522-2)TPF98-57/28/98WS36.9580<0.020.19<0.2<0.0400.1360.79NDNDTPF98-67/28/98WS39.7690TPF98-88/12/98LMB37.885098029 (L980522-3)TPF98-98/12/98LMB44.01140<0.020.77<0.2<0.0400.1070.05NDNDTPF98-108/12/98LMB43.61220TPF98-118/12/98LMB41.51000TPF98-128/12/98YB26.928098030 (L980522-4)<0.020.36<0.2<0.0400.1030.20NDNDTPF98-138/12/98YB24.5200Quinebaug River BasinQuinebaug River, Brimfield (upstream/west/southwest of Brimfield Road) F0057QNRF98-19/11/98LMBa33.958098034 (L980599-1)QNRF98-29/11/98LMBa33.2530<0.020.84<0.19<0.040.260.10NDNDQNRF98-39/11/98LMBa32.9580QNRF98-49/11/98YPa22.213098035 (L980599-2)QNRF98-59/11/98YPa21.9120<0.020.82<0.19<0.040.410.19NDNDQNRF98-69/11/98YPa23.1140QNRF98-79/11/98WS39.664098036 (L980599-3)QNRF98-89/11/98WS42.1790<0.020.32<0.19<0.040.310.79NDNDQNRF98-99/11/98WS38.2600QNRF98-109/11/98YB25.220098037 (L980599-4)QNRF98-119/11/98YB22.7160<0.020.58<0.19<0.040.220.17NDNDQNRF98-129/11/98YB22.4160QNRF98-139/11/98B18.412098038 (L980599-5)QNRF98-149/11/98B17.9120<0.020.63<0.19<0.040.360.09NDNDQNRF98-159/11/98B18.31301Speciesbluegill (B) Lepomis macrochiruswhite sucker (WS) Castomus commersonia yellow grub parasite in fish fleshlargemouth bass (LMB) Micropterus salmoidesyellow bullhead (YB) Ameiurus nataliswhite perch (WP) Morone americanayellow perch (YP) Perca flavescensND = not detected or the analytical result is at or below the established detection limit (MDL). See Appendix A for MDL.* DDE (all other analytes tested were ND) NOTE: mg/kg = (g/g = ppm = mg/l Table B17. 1994 MA DEP OWM fish toxics monitoring data for the Hamilton Reservoir, Holland and French River (Thayers Pond - impoundment at Clara Barton Road), Oxford. Results, reported in wet weight, are from composite samples of fish fillets with skin off. Sample IDCollection DateSpecies1 CodeLength (cm)Weight (g)Sample ID (laboratory sample #)Cd (mg/kg)Hg (mg/kg)Pb (mg/kg)As (mg/kg)Se (mg/kg)Lipids (%)PCB ((g/g)Pesticides ((g/g)French River Basin French River (Thayers Pond, impoundment at Clara Barton Road), Oxford F0088Frf94-19/8/94LMB33.862094023 (94-4250) (94-4249)<0.200.480<1.0<0.040.125Frf94-29/8/94SMB29.53400.15NDNDFrf94-39/8/94YP27.027094024 (94-4252) (94-4251)<0.200.273<1.0<0.040.043Frf94-49/8/94YP25.22000.19NDNDFrf94-59/8/94BB25.321094025 (94-4254)Frf94-69/8/94BB24.6180Frf94-79/8/94BB25.0220<0.200.140<1.0<0.040.081Frf94-89/8/94BB23.6170(94-4253)0.80NDNDFrf94-99/8/94BB23.0140Quinebaug River Basin Hamilton Reservoir, Holland F0087HRF94-18/30/94LMB38.696094020 (94-3971)HRF94-28/30/94LMB33.6580HRF94-38/30/94LMB34.5600<0.010.29<0.03<0.0020.285HRF94-48/30/94LMB34.9670(94-3970)0.23NDNDHRF94-58/30/94LMB33.1510HRF94-68/30/94YP23.116094021 (94-3973)HRF94-78/30/94YP24.5170HRF94-88/30/94YP22.8130<0.010.22<0.03<0.0020.192HRF94-98/30/94YP20.4110(94-3972)0.15NDNDHRF94-108/30/94YP20.0100HRF94-118/30/94YB26.730094022 (94-3975)HRF94-128/30/94YB23.7210HRF94-138/30/94YB22.7190<0.010.16<0.03<0.0020.103HRF94-148/30/94BB22.7170(94-3974)1.3NDNDHRF94-158/30/94YB19.01001Speciesbrown bullhead (BB) Ameiurus nebulosusyellow bullhead (YB) Ameiurus natalislargemouth bass (LMB) Micropterus salmoidesyellow perch (YP) Perca flavescenssmallmouth bass (SMB) Micropterus dolomieuND = not detected or the analytical result is at or below the established detection limit (MDL). See Appendix A for MDL.NOTE: mg/kg = (g/g = ppm= mg/l PERIPHYTON and PHYTOPLANKTON Results from MA DEP DWMs 1999 periphyton sampling are presented in Appendix G of this report as a technical memorandum by Joan Beskenis entitled FRENCH AND QUINEBAUG RIVERS - PERIPHYTON SURVEY RESULTS 1999. LAKES Lake synoptic survey results from 1994 summer surveys in the French and Quinebaug River Basins are presented in Tables B18 and B19 respectivery (MA DEP 1994b). TABLE B18. French River Basin 1994 summer lake status. LAKEWBIDSIZE (Acres)TROPHIC STATus SURVEY OBSERVATIONS (Objectionable Conditions)Ballard Hill Pond, LeicesterMA420695eAbout 90% of the surface covered with emergent and floating vegetation Bouchard Pond, LeicesterMA420034eSlight turbidity, slight dissolved organics, 100% of surface covered with floating, emergent and submergent vegetation, likely non-native species (Mh)Buffum Pond, Charlton/ OxfordMA4200422EModerate brown turbidity, slight dissolved organics, 100% of surface dense with submergent, floating, and emergent vegetation, non-native plants (Mh, Pa)Buffumville Lake, Charlton/ OxfordMA42005186eSlight to moderate turbidity, slight dissolved organics, dense floating and emergent vegetation around much of the perimeter (about 10 acres total), non-native plants (Mh)Burncoat Pond, LeicesterMA42007122MSlight turbidity, fine organic layer covering sandy bottom, abundance of clams at beach, floating and emergent vegetation sparse, possible non-native species (M. sp.) Carbuncle Pond, OxfordMA4200811UGood clarity, floating and emergent vegetation sparse throughout Cedar Meadow Pond, LeicesterMA42009146mSlight turbidity, slight dissolved organics, inlet channel 100% covered with very dense floating vegetation (about 10 acres); remainder of pond sparse floating and emergent vegetation, non-native species (Cc, M. sp.) Dresser Hill Pond, CharltonMA420148HDense bluegreen bloom, transparency estimated at only a few inches, surface scum present on windward shore, no vegetation evident due to bloomDutton Pond, LeicesterMA420156hExcessive brown/green turbidity, algal bloom evident, transparency estimated at less than 4 ft., filamentous algae abundant on southeastern shore, floating and emergent vegetation sparse Easterbrook Pond, DudleyMA420175ENo open water observable, 100% of surface covered with very dense floating vegetation, non-native species (Ls)Gore Pond, Charlton/Dudley (Baker Pond)MA42018169EModerate turbidity (post-bloom), west and east cove areas 100% covered with very dense floating and emergent vegetation (about 10 acres), non-native species (Mh)* Indicates Class A (water supply) waterbody; all others are Class B. WBID Waterbody Identification code. Trophic State: E= Eutrophic, H= Hypereutrophic, M= Mesotrophic, U= Undetermined. Non-native Plants: Cc = Cabomba caroliniana, Ls = Lythrum salicaria, Mh = Myriophyllum heterophyllum, Pa = Phragmites australis Note: M. sp. Possible Myriophyllum heterophyllum, requires further confirmation when flowering heads are evident. TABLE B18. Continued. French River Basin 1994 summer lake status. LAKEWBIDSIZE (Acres)TROPHIC STATus SURVEY OBSERVATIONS (Objectionable Conditions)Granite Reservoir, CharltonMA42019198MGood clarity, slight dissolved organics, about 50% of the south cove (about 20 acres) covered with very dense floating vegetation, likely non-native species (Mh)Greenville Pond, LeicesterMA4202330EModerate brown turbidity, bluegreen bloom evident, sparse floating and emergent vegetation throughout, bottom likely covered with submergentsGreenville Pond (West Basin), LeicesterMA420227EGood clarity, slight dissolved organics, surface area nearly 100% covered with floating and emergent vegetation, possible non-native (M.sp.)Hayden Pond, DudleyMA4202441MModerate grey/green turbidity, evidence of bloom, sparse floating and emergent vegetation throughout Henshaw Pond*, Leicester MA4202533UGood clarity, slight organic covering on bottom and vegetation, sparse floating and emergent vegetation throughoutHudson Pond, OxfordMA4202917ECouldnt observe clarity, abundant algal growth, 75% of surface covered with very dense floating vegetation; likely remaining areas covered with very dense submergents, non-native species (Ls, Pa) Hultered Pond, CharltonMA410235HTea colored water, 100% of surface covered by floating and submergent vegetation, little open water observed, many frogs Jones Pond, Charlton/ SpencerMA4203025EBrown turbidity, moderate dissolved organics, silty coating on bottom and organic debris, about 50% of upper end of pond with very dense floating vegetation; about 25% of lower half covered (total about 15 acres)Larner Pond, DudleyMA4206825EModerate turbidity, heavy dissolved organics (coffee-colored), algal bloom likely, heavy organic deposits on submergent vegetation, northern end 50-75% dense floating vegetation; east and west margins with dense floating and emergent vegetation (about 20 acres total), non-native species (Mh)Little Nugget Lake, CharltonMA4203214MModerate dissolved organics (brown), slight silty coating to bottom sand, few patches of floating vegetation along shore, submergent vegetation apparently not dense, possible non-native species (M. sp.)Lowes Pond, OxfordMA4203444EModerate turbidity (brown), moderate dissolved organics, 75-100% of surface covered with floating vegetationLow Pond, DudleyMA420333MModerate turbidity, green/brown algal growth, no floating or emergent vegetation evident, submergents very dense on bottom, non-native species (Mh)McKinstry Pond, OxfordMA4203516EHeavy dissolved organics, southern two-thirds of pond 100% covered with floating vegetation, northern one-third sparsely coveredMerino Pond, DudleyMA4203672MModerate turbidity, green/brown algal growth, no floating or emergent vegetation evident, submergents possibly dense on bottom, possible non-native species (Mh)* Indicates Class A (water supply) waterbody; all others are Class B. WBID Waterbody Identification code. Trophic State: E= Eutrophic, H= Hypereutrophic, M= Mesotrophic, U= Undetermined. Non-native Plants: Cc = Cabomba caroliniana, Ls = Lythrum salicaria, Mh = Myriophyllum heterophyllum, Pa = Phragmites australis Note: M. sp. Possible Myriophyllum heterophyllum, requires further confirmation when flowering heads are evident. TABLE B18. Continued. French River Basin 1994 summer lake status. LAKEWBIDSIZE (Acres)TROPHIC STATus SURVEY OBSERVATIONS (Objectionable Conditions)New Pond, DudleyMA4203730MModerate turbidity, about 90% of northern end covered with submergent vegetation, northwest cove 50-75% covered with floating and submergent vegetation, cove at western end 100% covered with vegetation (total cover about 5 acres), likely non-native species (Mh)Nipmuck Pond, WebsterMA4203920mGood clarity, very low dissolved organics, clouds of filamentous algae, main body of pond with 15% floating vegetation and 100% submergents, south cove 100% covered with submergent vegetationPackard Pond, DudleyMA420406ESlight turbidity, 100% of surface area covered with floating (40%) and submergent (60%) vegetation, likely non-native species (Mh)Peter Pond, DudleyMA4204244USlight turbidity, sparse floating and emergent vegetation throughoutPierpont Meadow Pond, Charlton/DudleyMA4204390ESlight turbidity, slight blue-green bloom, southern portion of lake and western littoral zone covered with very dense floating and submergent vegetation, non-native species (Mh)Pikes Pond, CharltonMA4204432EExcessive turbidity (Secchi disk estimated < 4 ft.), water level very low, black stain on rocks around shore and outlet structure, sparse vegetation, non-native species (Ls) Putnam Pond, CharltonMA4204619MSlight turbidity, moderate dissolved organics, warning sign posted re: herbicide treatment (6/9/94), no vegetation observedRobinson Pond, OxfordMA4204798MModerate turbidity, slight dissolved organics, slight olive-green color, northern end 100% covered with floating vegetation; southern end and west cove covered 50-75% with vegetation Rochdale Pond, LeicesterMA4204841MSlight turbidity, moderate dissolved organics, 50-75% of shore with floating or emergent vegetation, no other vegetation observed, possible non-native species (M. sp.)Sargent Pond, Leicester MA4204969MGood clarity, slight dissolved organics, sparse vegetation throughout, likely non-native species (Mh)Shepherd Pond, DudleyMA4205118EWater not observable, 100% very dense emergent vegetation over surface, non-native species (Pa)Slaters Pond, OxfordMA42053107UGood clarity, slight to moderate dissolved organics, mucky rust-colored bottom, sparse vegetationSnow Pond, CharltonMA420542ESlight turbidity, moderate dissolved organics, 25% of surface covered with dense patches of floating and submergent vegetationStiles Reservoir, Spencer/ LeicesterMA42055346MSlight to moderate turbidity, slight dissolved organics, likely algal bloom (golden brown color), very dense low-growing submergents covered with filamentous algae, possible non-native species (M. sp.)Texas Pond, OxfordMA4205827HExcessive brown turbidity, algal bloom evident, marginal community of vegetation around shore, non-native species (Ls) * Indicates Class A (water supply) waterbody; all others are Class B. WBID Waterbody Identification code. Trophic State: E= Eutrophic, H= Hypereutrophic, M= Mesotrophic, U= Undetermined. Non-native Plants: Cc = Cabomba caroliniana, Ls = Lythrum salicaria, Mh = Myriophyllum heterophyllum, Pa = Phragmites australis Note: M. sp. Possible Myriophyllum heterophyllum, requires further confirmation when flowering heads are evident. TABLE B18. Continued. French River Basin 1994 summer lake status. LAKEWBIDSIZE (Acres)TROPHIC STATus SURVEY OBSERVATIONS (Objectionable Conditions)Tobins Pond, DudleyMA420609eOpen water not observable, 100% of surface covered with very dense floating and emergent vegetationWallis Pond, DudleyMA4206223EOpen water not observable, 100% of surface covered with very dense floating and emergent vegetation, possible non-native species (M. sp.)Watson Mill Pond, SpencerMA420632ESlight turbidity, heavy dissolved organics, western side of pond 100% covered with vegetation, eastern side 50% covered with vegetationWee Laddie Pond, CharltonMA420656MSlight turbidity, moderate dissolved organics, silty organic coating on bottom, sparse floating and emergent vegetation throughout* Indicates Class A (water supply) waterbody; all others are Class B. WBID Waterbody Identification code. Trophic State: E= Eutrophic, H= Hypereutrophic, M= Mesotrophic, U= Undetermined. Non-native Plants: Cc = Cabomba caroliniana, Ls = Lythrum salicaria, Mh = Myriophyllum heterophyllum, Pa = Phragmites australis Note: M. sp. Possible Myriophyllum heterophyllum, requires further confirmation when flowering heads are evident. TABLE B19. Quinebaug River Basin 1994 summer lake status. LAKEWBIDSIZE (Acres)TROPHIC STATus SURVEY OBSERVATIONS (Objectionable Conditions)Alum Pond, SturbridgeMA41001195MSlight green turbidity, good water clarity, sparse vegetation, development around entire shorelineCedar Pond, SturbridgeMA41008146eSlight dissolved organics, brown/green turbidity, algal growth on bottom and rocks, dense to very dense submergent vegetation in northern end of lake and near dam (southern end), non-native species (Mh)East Brimfield Reservoir, Brimfield/SturbridgeMA41014420ESlight turbidity, slight to heavy dissolved organics, very dense floating and emergent vegetation encroaching in cove areas in west arm of northern basin, submergent vegetation very dense where sampled, non-native species (Mh)Lake George, WalesMA4101693uSlight turbidity, slight dissolved organics, rocks coated with algae in some locations, very dense patches of floating vegetation along west shore and in cove along east side.Glen Echo Lake, CharltonMA41017112MSlight turbidity, sparse floating and emergent vegetation, heavy development around shoreline Hamilton Reservoir, Holland/ Union (CT)MA41019249MModerate brown-green turbidity, slight dissolved organic, slit and algae on bottom and rocks, very dense floating vegetation in southwest cove and coves near outlet, non-native plants (Mh, Pa) Holland Pond, HollandMA4102265MGood clarity, slight dissolved organics, slight algal and silty cover on bottom, possible non-native species (M.sp.), dense to very dense floating and emergent vegetation around perimeter over about 10% of surface Leadmine Pond, SturbridgeMA4102762MGood clarity, very little dissolved organics, a few widely scattered dense patches of floating and emergent vegetation* Indicates Class A (water supply) waterbody; all others are Class B. WBID Waterbody Identification code. Trophic State: E= Eutrophic, H= Hypereutrophic, M= Mesotrophic, U= Undetermined. Non-native Plants: Ls = Lythrum salicaria, Mh = Myriophyllum heterophyllum, Pa = Phragmites australis Note: M. sp. Possible Myriophyllum heterophyllum, requires further confirmation when flowering heads are evident. TABLE B19. Continued. Quinebaug River Basin 1994 summer lake status. LAKEWBIDSIZE (Acres)TROPHIC STATus SURVEY OBSERVATIONS (Objectionable Conditions)Little Alum Pond, Brimfield MA4102973USlight turbidity, slight dissolved organics, only sparse vegetation throughout, pond recently treated with herbicides McIntyre Pond, CharltonMA4103113EHeavy dissolved organics, 100% of surface covered with very dense floating, submergent and emergent vegetationMill Road Pond, BrimfieldMA4103215eSlight turbidity, slight dissolved organics, algal scum floating on surface, silt and green algae coating rocks, very dense floating leaf patches around shore and at upstream end covering about a third of the surface Monson Road Pond, WalesMA410594eHeavy dissolved organics, much debris on bottom, two-thirds of the surface covered by very dense floating vegetation Morse Pond, SouthbridgeMA4103345eGood clarity, slight dissolved organics, scum of watermeal and duckweed, two-thirds of the surface covered by very dense floating and submergent vegetation New Boston Road Pond, SturbridgeMA4103514MModerate brown turbidity, slight dissolved organics, moderate vegetation density, some patches of vegetation over the entire surfaceNo. 3 Reservoir*, Southbridge (Hatchet Res. No. 3)MA4103821MSlight turbidity, brown silt on bottom and plants, sparse to moderate low-growing vegetationNo. 4 Reservoir*, Southbridge (Hatchet Res. No. 4)MA4103964MSlight green turbidity, very silty (brown) and algae coating bottom and vegetation, much leaf debris on bottom, very dense low-growing vegetation, possible non-native species (M. sp.).No. 5 Reservoir*, Southbridge (Hatchet Res. No. 5)MA4104026MGood clarity, very silty on bottom and vegetation, water level very low, sparse to dense low-growing vegetation Pistol Pond, SturbridgeMA410576HBrown/green turbidity, very dense floating leaf and submergent vegetation over 100% of the surface, submergent plants often blackened at depth, non-native plants (Pa)Prindle Pond, Charlton MA4104369MSlight turbidity, rocks/sand on bottom often covered with organic and algal mats, very dense growths of vegetation in the southeastern cove and scattered throughout the littoral zoneRailroad Pond, CharltonMA410586eSlight brown turbidity, moderate dissolved organics, mucky bottom, little open water to observe, 75-100% of surface covered with floating, emergent and submergent vegetation, non-native species (Mh)Sherman Pond, BrimfieldMA4104686MSlight turbidity, slight dissolved organics, very dense floating and emergent vegetation encroaching along south, west and north shores; about 25% of surface area affected, non-native species (Mh)Sibley Pond (North Basin), CharltonMA4104721eTurbidity (brown) high at outlet (Secchi disk reading 0.8 m), moderate dissolved organics, a few patches of dense floating vegetation on eastern side of pondSibley Pond (South Basin), CharltonMA4104819HExcessive turbidity, moderate dissolved organics, filamentous algae common, a few patches of floating plants at south end * Indicates Class A (water supply) waterbody; all others are Class B. WBID Waterbody Identification code. Trophic State: E= Eutrophic, H= Hypereutrophic, M= Mesotrophic, U= Undetermined. Non-native Plants: Ls = Lythrum salicaria, Mh = Myriophyllum heterophyllum, Pa = Phragmites australis Note: M. sp. Possible Myriophyllum heterophyllum, requires further confirmation when flowering heads are evident. TABLE B19. Continued. Quinebaug River Basin 1994 summer lake status. LAKEWBIDSIZE (Acres)TROPHIC STATus SURVEY OBSERVATIONS (Objectionable Conditions)Sylvestri Pond, DudleyMA4104918eSlight turbidity, heavy dissolved organics, 90% of surface covered with very dense floating vegetation, non-native species (Ls, Mh)Walker Pond, Sturbridge MA41052103MSlight turbidity, slight dissolved organics, very dense floating vegetation at north end of pond and occasional patches down eastern shore (5-10 acres total), non-native plants (Mh) Wells Pond, SouthbridgeMA410536MModerate brown/green turbidity, much debris on floating on surface, much leaf litter on bottom, dense patches of floating vegetation at the south end (about 10% of the surface area)Wielock Pond, Dudley MA410565eExcessive brown/grey turbidity, slight dissolved organics, apparent algal bloom reducing transparency (estimated below 4 ft. Secchi disk), sparse floating vegetation throughout pond* Indicates Class A (water supply) waterbody; all others are Class B. WBID Waterbody Identification code. Trophic State: E= Eutrophic, H= Hypereutrophic, M= Mesotrophic, U= Undetermined. Non-native Plants: Ls = Lythrum salicaria, Mh = Myriophyllum heterophyllum, Pa = Phragmites australis Note: M. sp. Possible Myriophyllum heterophyllum, requires further confirmation when flowering heads are evident. REFERENCES Ackerman, M.T., 1989 April. Compilation of Lakes, Ponds, Reservoirs and Impoundments Relative to the Massachusetts Lake Classification Program. Publication: #15901-171-50-4-89-c.r. Technical Services Branch, Massachusetts Division of Water Pollution Control, Department of Environmental Quality Engineering. Westborough, MA. Hartman, E.M. 2001. Draft. 1999 Cady Brook, Quinebaug River Water Quality and Wastewater Discharge Data. Massachusetts Department of Environmental Protection, Division of Watershed Management, Worcester, MA. MA DEP. 1994a. Open File. 1994 Fish Toxics Monitoring Data in the French & Quinebaug River Basins. Massachusetts Department of Environmental Protection, Office of Watershed Management, Worcester, MA. MA DEP. 1994b. Open File. 1994 Synoptic Lake Surveys Coding Sheets. Massachusetts Department of Environmental Protection, Office of Watershed Management, Worcester, MA. MA DEP. 1998. Open File. 1998 Fish Toxics Monitoring Data in the French & Quinebaug River Basins. Massachusetts Department of Environmental Protection, Division of Watershed Management, Worcester, MA. MA DEP. 1995 January Draft. Laboratory Quality Assurance Plan and Standard Operating Procedures. Massachusetts Department of Environmental Protection, Division of Environmental Analysis. Wall Experiment Station, Lawrence, MA. MA DEP. 1999a. Baseline Lake Survey Quality Assurance Project Plan. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999b. CN 1.0 Grab Collection Techniques for DWM Water Quality Sampling, Standard Operating Procedure. October 25, 1999. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999c. CN 4.0 Hydrolab Series 3 Multiprobe, Standard Operating Procedure. September 23, 1999. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999d. CN 2.0 Apparent Color Standard Operating Procedures. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999e. CN 3.0 Chlorophyll a Standard Operating Procedures. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999f. CN 13.0. Fish Contaminant Monitoring Program, Quality Assurance Project Plan, 1999. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999g. Open File. 1999 Lake Survey Field Sheets and Macrophyte Maps. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. MA DEP. 1999h. Open File. 1999 Fish Toxics Monitoring Data in the French & Quinebaug River Basins. Massachusetts Department of Environmental Protection, Division of Watershed Management, Worcester, MA. MA DEP. 2000. CN 12.0. Smart Monitoring Water Quality Quality Assurance Project Plan. Massachusetts Department of Environmental Protection, Division of Watershed Management, Worcester, MA. MA DEP. 2001. Open File. PALIS updates. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. DPH. 1969. State Sanitary Code. Article 7, Regulation 10.2B. Massachusetts Department of Public Health. Boston, MA. MDPH. 1999. Freshwater Fish Consumption Advisory List. Massachusetts Department of Public Health. Boston, MA. MDPH. 2002 Impending Fish Consumption Advisory for Buffumville Lake. Massachusetts Department of Public Health, Bureau of Environmental Health Assessment. Boston, MA. Mattson, M. D. and R. A. Isaac. 1999. Calibration of Phosphorous Export Coefficients for Total Maximum Daily Loads of Massachusetts Lakes. Journal of Lakes and Reservoir Management 15(3): 209-219. APPENDIX C  Technical Memorandum #TM- 41/42- 2 Title: FRENCH & QUINEBAUG RIVER WatershedS 1999 Biological Assessment  EMBED MSPhotoEd.3  Perlid stonefly collected during the French & Quinebaug River watersheds biosurvey. Photo by Robert Nuzzo, MA DEP Prepared by: John Fiorentino, MA DEP/ Division of Watershed Management, Worcester, MA Date: 13 November 2001 CONTENTS Introduction 3 Methods 6 Macroinvertebrate Sampling RBPIII 6 Habitat Assessments 6 Maroinvertebrate Sample Processing and Analysis 6 Results and Discussion 8 Quinebaug River 9 French River 16 Cady Brook 20 Town Meadow Brook 24 Summary and Recommendations 26 Literature Cited 32 AppendixMacroinvertebrate taxa lists, RBPIII analyses, and Habitat evaluations 33 Tables Table 1. Macroinvertebrate biomonitoring station locations 4 Table 2. Perceived problems addressed during 1999 survey 4 INTRODUCTION Biological monitoring is a useful means of detecting anthropogenic impacts to the aquatic community. Resident biota (e.g., benthic macroinvertebrates, fish, periphyton) in a water body are natural monitors of environmental quality and can reveal the effects of episodic and cumulative pollution and habitat alteration (Barbour et al. 1995, Barbour et al. 1999). Biological surveys and assessments are the primary approaches to biomonitoring. As part of the Massachusetts Department of Environmental Protection/Division of Watershed Managements (MA DEP/DWM) 1999 French & Quinebaug River watersheds assessment, aquatic benthic macroinvertebrate biomonitoring was conducted to evaluate the biological health of various portions of the watersheds. In accordance with the Quality Assurance Project Plan for 1999 Benthic Macroinvertebrate Biomonitoring (Fiorentino 1999), a total of 17 biomonitoring stations were sampled to investigate the effects of various point source and nonpoint source stressorsboth historical and currenton the aquatic communities of the French & Quinebaug River watersheds. Some stream segments were previously unassessed by MA DEP, while historical MA DEP biomonitoring stationssampled most recently in 1994 (Szal 1999)were reevaluated to determine if water quality and habitat conditions have improved or worsened over time. In some cases (i.e., point source investigations), a site-specific sampling approach was implemented, in which the aquatic community and habitat downstream from the perceived stressor (downstream study site) were compared to an upstream reference station (control site) representative of least disturbed biological conditions in the waterbody. While the alternative to this site-specific approach is to compare the study site to a regional reference station (i.e., best attainable condition), the site-specific approach is more appropriate for an assessment of a known or suspected stressor, provided that the stations being compared share basically similar instream and riparian habitat characteristics (Barbour et al. 1999). Since both the quality and quantity of available habitat affect the structure and composition of resident biological communities, effects of such features can be minimized by sampling similar habitats at stations being compared, providing a more direct comparison of water quality conditions (Barbour et al. 1999). Sampling highly similar habitats will also reduce metric variability, attributable to factors such as current speed and substrate type. Upstream reference stations were established in Town Meadow Brook, Cady Brook, the French River, and the Quinebaug River. To provide additional information necessary for making basin-wide aquatic life use designations required by Section 305(b) of the Clean Water Act, biomonitoring stations were compared to a regional reference station as well. Use of a regional reference station is particularly useful in assessing nonpoint source (NPS) pollution, nutrient and BOD loadings, and toxic impacts at upstream control sites as well as downstream sites suspected as chemically-impacted from known point source stressors (Hughes 1989). Regional reference stations were established in the Quinebaug River watershed (QR0B) and the French River (FR14) watershed for biomonitoring stations in the Quinebaug River and French River respectively. An additional regional reference station was used in Town Meadow Brook (MB11) for investigations of Cady Brook (CA10A)a tributary with considerably less drainage area than the French and Quinebaug River watersheds. All reference stations were situated upstream from all known point sources of water pollution, and were assumed to be relatively unimpacted by nonpoint sources. Sampling locations, along with station identification numbers and dates, are noted in Table 1. Sampling locations are also shown in Figure 1. The main objectives of biomonitoring in the French & Quinebaug River watersheds were: (a) to determine the biological health of streams within the watersheds by conducting assessments based on aquatic macroinvertebrate communities; and (b) to identify impaired stream segments so that efforts can be focussed on developing NPDES permits, stormwater management, and control of other nonpoint source pollution. Specific tasks were: Conduct benthic macroinvertebrate sampling and habitat assessments at selected locations throughout the French & Quinebaug River watersheds. Based upon the macroinvertebrate data, identify river segments within the watersheds with potential or existing point/nonpoint source pollution problems; and Using the benthic macroinvertebrate data and supporting water chemistry and field/habitat data: Assess the types of water quality and/or water quantity problems that are present, and if possible, make recommendations for remedial actions. Provide macroinvertebrate data to DWMs Environmental Monitoring and Assessment Program to be used in making aquatic life use assessments required by Section 305(b) of the Federal Clean Water Act (CWA). Table 1. List of macroinvertebrate biomonitoring station locations sampled during the 1999 French & Quinebaug River watersheds survey, including station identification number, station description, and sampling date. StationSite DescriptionSampling DateQR0BQuinebaug River, 1 km upstream from Brimfield Rd., Holland, MA17 Aug 1999QR00*Quinebaug River, 80 m upstream from Holland Rd., Sturbridge, MA17 Aug 1999QR01B*Quinebaug River, 100 m downstream from Farquhar Rd., Sturbridge, MA20 Aug 1999QR01CQuinebaug River, 700 m downstream from Breakneck Brook, Sturbridge, MA17 Aug 1999QR03Quinebaug River, 135 m downstream from Mill St., Southbridge, MA17 Aug 1999QR04U*Quinebaug River, 120 m upstream from Southbridge WWTP, Southbridge, MA18 Aug 1999QR06*Quinebaug River, 500 m upstream from Rt. 197 and USGS gage, Thompson, CT18 Aug 1999FR11French River, 25 m upstream from Oxford Ave., Webster, MA19 Aug 1999FR14*French River, 160 m upstream from Rt. 56, adjacent to Mill St., Oxford, MA19 Aug 1999FR15*French River, 100 m upstream from Rt. 56, Oxford, MA19 Aug 1999FR17*French River, 120 m downstream from Hill St., Webster, MA18 Aug 1999FR18*French River, 700 m upstream from Langers Pond, Thompson, CT18 Aug 1999MB11*Town Meadow Brook, 140 m downstream from Ashworth Pond, Leicester, MA19 Aug 1999MB12*Town Meadow Brook, 15 m upstream from Pine St., Leicester, MA19 Aug 1999CA04*Cady Brook, 25 m upstream from Charlton WWTP, Charlton, MA23 Sept 1999**CA06*Cady Brook, 100 m downstream from Charlton WWTP, Charlton, MA23 Sept 1999**CA10ACady Brook, 130 m upstream from Snake Hill Rd., Charlton, MA20 Aug 1999 23 Sept 1999 * biomonitoring (RBPII) conducted by MA DEP in 1994; ** low base-flow precluded August sampling Table 2. List of perceived problems addressed during the 1999 French & Quinebaug River watersheds biomonitoring survey. Specific biomonitoring stations addressing each problem are also listed, as is the sampling methodology employed at each station. StationIssues/ProblemsSampling MethodQR00; QR01B; QR01C; QR03; MB11; MB12; QR04U; QR06; FR14; FR15; FR17; FR18; CA04; CA06; CA10AWWTP and/or industrial discharges1, 2, 3, 4RBPIII--kick samplingFR11; FR14; FR15; FR17; FR18; QR03; QR04U; QR06NPS/Urban impacts (trash, runoff, sedimentation, habitat degradation) 4, 5RBPIII--kick samplingQR03; QR06/ MB11; MB12; CA04; CA06; CA10AWater withdrawals/ Flow alteration 3, 4, 5RBPIII--kick samplingQR00; QR01B; QR01C; QR03; QR04U; QR06; FR14; FR15; FR11Impoundment effects 4RBPIII--kick samplingFR18Sediment contamination 5RBPIII--kick samplingQR06; FR18Nutrients 1, 2, 6 1 (MA DEP 1990); 2 (MA DEQE 1989); 3 (Hartman 2001); 4 (Szal 1999); 5 (T. Mounce, MA MA DEP/CERO, Personal Communication); 6 (MA DEP 1998)    Figure 1. Location of DWM biomonitoring stations for the 1999 French & Quinebaug River watersheds survey. METHODS Macroinvertebrate Sampling - RBPIII The macroinvertebrate sampling and processing procedures employed during the 1999 French & Quinebaug River watersheds biomonitoring survey are described in the standard operating procedures (Nuzzo 1999), and are based on US EPA Rapid Bioassessment Protocols (RBPs) for wadeable streams and rivers (Barbour et al. 1999). Sampling was conducted by DWM biologists throughout a 100 m reach, in riffle/run areas with fast currents and cobble/gravel substratesgenerally the most productive habitats, supporting the most diverse communities in the stream system. Ten kicks in squares approximately 0.46 m x 0.46 m were composited for a total sample area of about 2 m2. Samples were labeled and preserved in the field with denatured 95% ethanol, then brought to the MA DEP/DWM lab for further processing. Habitat Assessments An evaluation of physical and biological habitat quality is critical to any assessment of ecological integrity (Karr et al. 1986; Barbour et al. 1999). Habitat assessment supports understanding of the relationship between physical habitat quality and biological conditions, identifies obvious constraints on the attainable potential of a site, assists in the selection of appropriate sampling stations, and provides basic information for interpreting biosurvey results (US EPA 1995). Before leaving the sample reach during the 1999 biosurveys, habitat qualities were scored using a modification of the evaluation procedure in Barbour et al. (1999). The matrix used to assess habitat quality is based on key physical characteristics of the water body and the immediate riverfront area. Most parameters evaluated are instream physical attributes often related to overall land use and are potential sources of limitation to the aquatic biota (Barbour et al. 1999). The ten habitat parameters are as follows: instream cover, epifaunal substrate, embeddedness, sediment deposition, channel alteration, velocity/depth combinations, channel flow status, right and left (when facing downstream) bank vegetative protection, right and left bank stability, right and left bank riparian vegetative zone width. Habitat parameters are scored, totaled, and compared to a regional reference station and/or a site-specific control (upstream reference) station to provide a final habitat ranking. Macroinvertebrate Sample Processing And Analysis Macroinvertebrate sample processing entailed distributing whole samples in pans, selecting grids within the pans at random, and sorting specimens from the other materials in the sample until approximately 100 organisms (10%) were extracted. Specimens were identified to genus or species as allowed by available keys, specimen condition, and specimen maturity. Taxonomic data were analyzed using a modification of Rapid Bioassessment Protocol III (RBP III) metrics and scores (Barbour et al. 1999). Based on the taxonomy, various community, population, and functional parameters, or metrics, were calculated which allow measurement of important aspects of the biological integrity of the community. This integrated approach provides more assurance of a valid assessment because a variety of biological parameters are evaluated. Deficiency of any one metric should not invalidate the entire approach (Barbour et al. 1999). Metric values for each station were scored based on comparability to the reference station, and scores were totaled. The percent comparability of total metric scores for each study site to those for a selected least-impacted reference station yields an impairment score for each site. RBP III analysis separates sites into four categories: non-impacted, slightly impacted, moderately impacted, and severely impacted. Impacts to the benthic community may be indicated by the absence of generally pollution-sensitive macroinvertebrate taxa such as Ephemeroptera, Plecoptera, and Trichoptera (EPT); dominance of a particular taxon, especially the pollution-tolerant Chironomidae and Oligochaeta taxa; low Taxa Richness; or shifts in community composition relative to the reference station (Barbour et al. 1999). Those biological metrics calculated and used in the analysis of French & Quinebaug River watersheds macroinvertebrate data are listed and defined below [For a more detailed description of metrics used to evaluate benthos data see Barbour et al. (1999)]: Taxa Richnessa measure based on the number of taxa present. The lowest possible taxonomic level is assumed to be genus or species. EPT Indexa count of the number of genera/species from the orders Ephemeroptera (mayflies), Plecoptera (stoneflies), and Trichoptera (caddisflies). As a group these are considered three of the more sensitive aquatic insect orders. Therefore, the greater the contribution to total richness from these three orders, the healthier the community. Biotic IndexBased on the Hilsenhoff Biotic Index (HBI), this is an index designed to produce a numerical value to indicate the level of organic pollution (Hilsenhoff 1982). Organisms have been assigned a value ranging from zero to ten based on their tolerance to organic pollution. A value of zero indicates the taxon is highly intolerant of pollution and is likely to be found only in pollution-free waters. A value of ten indicates the taxon is tolerant of pollution and may be found in highly polluted waters. The number of organisms and the individually assigned values are used in a mathematical formula that describes the degree of organic pollution at the study site. The formula for calculating HBI is: HBI= ( xiti n where xi = number of individuals within a taxon ti = tolerance value of a taxon n = total number of organisms in the sample Ratio of EPT and Chironomidae AbundanceThe EPT and Chironomidae abundance ratio uses relative abundance of these indicator groups as a measure of community balance. Skewed populations having a disproportionate number of the generally tolerant Chironomidae (midges) relative to the more sensitive insect groups may indicate environmental stress. Percent Contribution Dominant Taxonis the percent contribution of the numerically dominant taxon (genus or species) to the total numbers of organisms. A community dominated by few species indicates environmental stress. Conversely, more balance among species indicates a healthier community. Ratio of Scraper and Filtering Collector Functional Feeding GroupsThis ratio reflects the community food base. The proportion of the two feeding groups is important because predominance of a particular feeding type may indicate an unbalanced community responding to an overabundance of a particular food source (Barbour et al. 1999). Scrapers predominate when diatoms are the dominant food resource, and decrease in abundance when filamentous algae and mosses prevail. Filtering collectors thrive where filamentous algae and mosses are prevalent and where fine particulate organic matter (FPOM) levels are high. Community Similarityis a comparison of a study site community to a reference site community. Similarity is often based on indices that compare community composition. Most Community Similarity indices stress richness and/or richness and abundance. Generally speaking, communities with comparable habitat will become more dissimilar as stress increases. In the case of the French & Quinebaug River watersheds bioassessment, an index of macroinvertebrate community composition was calculated based on similarity (i.e., affinity) to the reference community, expressed as percent composition of the following organism groups: Oligochaeta, Ephemeroptera, Plecoptera, Coleoptera, Trichoptera, Chironomidae, and Other. The reference site affinity (RSA) metric is calculated as: 100 (( ( x 0.5) where ( is the difference between the reference percentage and the sample percentage for each taxonomic grouping. RSA percentages convert to RBPIII scores as follows: <35% receives 0 points; 2 points in the range from 35 to 49%; 4 points for 50 to 64%; and 6 points for (65%. RESULTS AND DISCUSSION The macroinvertebrate and habitat data collected at each sampling station during the 1999 biosurveys are attached as an Appendix. Included in the taxa list (Table A1) are total organism counts, and the functional feeding group (FG) and tolerance value (TV) of each taxon. Summary tables of the RBP III data analyses of the 1999 benthos data, including biological metric calculations, metric scores, and impairment designations, are included in the Appendix as well. Table A2 is the summary table for all Quinebaug River stations using QR0B as the Quinebaug River watershed reference station. Table A3 summarizes results of site-specific investigations in the Quinebaug River using QR00 and QR04U as upstream controls. Table A4 is the summary table for all French River stations using FR14 as the French River watershed reference station. Table A5 summarizes results of site-specific investigations in the French River using FR14 and FR17 as the upstream control sites. Table A6 summarizes results of site-specific investigations in Cady Brook using CA04 as the upstream control station. The August-sampled Cady Brook station CA10A was also compared to a regional reference station (MB11), shown in Table A7. Metric values for the CA10A benthos assemblage sampled in September are included in Table A7 as well; however, these metrics are not scored. Table A8 summarizes results of site-specific investigations in Town Meadow Brook using MB11 as the upstream control station. Habitat assessment scores for all stations are also included in the data analyses summary tables, while a more detailed summary of habitat parameters is found in Table A9. The 1999 biomonitoring data for the French & Quinebaug River watersheds generally indicate various degrees of nonpoint source-related problems at most of the stations examined. Urban runoff, habitat degradation, and other forms of nonpoint source pollution compromise water quality and biological integrity throughout the watersheds. In addition, the productive and impounded nature of much of the watersheds appears to shape benthic community structure and function at many of the biomonitoring stations sampled. Point source investigations found that municipal wastewater treatment facilities slightly impact aquatic life at some of the downstream study sites in the Quinebaug River and Cady Brook; though, not in Town Meadow Brook and the French River. Improvements in water quality were evident at some of the stations historically monitored by MA DEP, as reflected in the aquatic communities found there during the 1999 biosurveys. French & Quinebaug River Watersheds The Quinebaug River basin covers 744 square miles in south central Massachusetts, eastern Connecticut, and northwestern Rhode Island. The Quinebaug River flows 76 miles from its source in Mashpaug Pond in Union, Connecticut to its confluence with the Shetucket River in Norwich, Connecticut, forming the Thames River. Of the Quinebaugs 76 miles, 28 lie in Massachusetts and drain an area of 148 square miles. Major tributaries are Cady Brook in Massachusetts and the French, Five Mile, Moosup, and Pachaug rivers in Connecticut. Of these, the French River is the largest, extending 26 miles from its source in Greenville Pond, Leicester, Massachusetts to the confluence with the Quinebaug River in Thompson, Connecticut. From its source in Mashpaug Pond, the Quinebaug River flows a short distance to Hamilton Reservoir, which lies on the Connecticut-Massachusetts state line. Leaving this reservoir in Holland, Massachusetts, the river flows north to Sturbridge, where it passes through Old Sturbridge Village. Upon leaving Sturbridge, the river turns southeast to Southbridge, where it is joined by Cady Brook, Dresser Hill Brook, and Lebanon Brook, and flows on through Dudley to recross the state line. After the French River enters in Thompson, Connecticut, the Quinebaug flows generally south through Putnam, Danielson, and Plainfield to its confluence with the Shetucket River in Norwich. This confluence forms the Thames River which continues south to Long Island Sound. The Sturbridge and Southbridge wastewater treatment plants discharge their effluent to the Quinebaug River in Massachusetts. Additional wastes are discharged to Cady Brook in Charlton by the towns treatment plant. The U.S. Geological Survey maintains three streamflow gaging stations on the Quinebaug River, two of which are located just downstream from the East Brimfield and Westville dams. The East Brimfield gage receives flow from an area 67.5 square miles, while the Westville gage measures a drainage area of 99.1 square miles. The French River basin totals 132 square miles, 93 of which lie within the Commonwealth. The French River is a major tributary of the Quinebaug River and extends 26 miles from its source in Greenville Pond, Leicester, to its confluence with the Quinebaug River in Thompson, Connecticut. From its headwaters at Sargent Pond, Leicester (this portion, known as Town Meadow Brook, extends from Sargent Pond to Greenville Pond), the French River flows generally south throughout its length through Oxford, Dudley, and Webster to Thompson, Connecticut. Webster Lake, one of the largest natural lakes in the state, drains to the French River via Mill Brook in Webster. Other tributaries discharging to the French River are generally small and include Burncoat, Bartons, and Grindstone brooks in Leicester; the Little River in Oxford; Potash Brook in Webster; and Backwater and Sunset Hill brooks in Thompson, Connecticut. The Leicester, Oxford-Rochdale, and Dudley-Webster wastewater treatment plants discharge their effluent to the French River. The U.S. Geological Survey maintains two streamflow gaging stations on the French River. One gage, located in downtown Webster, measures flow from an area of 85.3 square miles. A second gage, located at the Hodges Village Army Corps Dam, records drainage from an area of 31.0 square miles. Quinebaug River QR0BQuinebaug River, upstream from East Brimfield Rd., Holland, MA. Sampling conducted 17 August 1999. Habitat The partially (50%) shaded QR0B sampling reach meandered through an area of dense maple-dominated (Acer rubrum) woodland. The stream was approximately 2-3 m wide, with a depth of about 0.20 m in the riffle areas and 0.40 m in the deepest pool areas. An abundance of rocky substratesespecially boulder, cobble, and pebbleprovided excellent epifaunal riffle habitat for macroinvertebrates. Fish habitat was also considered excellent, with snags, boulder, and overhanging vegetation providing a good mix of stable cover. Riparian/bank habitat parameters scored wellbanks were well-vegetated with grasses and herbaceous (false nettle, Bohmeria cylindrica; cardinal flower, Lobelia cardinalis; purple loosestrife, Lythrum salicaria) vegetation. Bank stability was excellent, and the riparian vegetative zone extended undisturbed from both banks. Affecting the QR0B habitat evaluation most negatively was the low base-flow, which resulted in exposed riffle substrates and a lack of deep pool areas. QR0B received a composite habitat score of 162/200, which was high relative to most biomonitoring stations sampled during the 1999 French & Quinebaug River watersheds survey (Table A9). This was the designated reference station for all Quinebaug River biomonitoring stations by virtue of its habitat evaluation, presumed good water quality, and minimal upstream/nearstream land use impacts (i.e., absence of point source inputs, lack of channelization, minimal development or agricultural activity nearby, undisturbed and well-vegetated riparian zone, minimal nonpoint source pollution inputs). Benthos This portion of the Quinebaug River watershed was characterized by a macroinvertebrate assemblage indicating a healthy aquatic community, with most of the metric values indicative of clean water and least-impacted conditions (Table A2). In particular, those attributes that measure components of community structure (i.e., Taxa Richness, Biotic Index, EPT Index)which display the lowest inherent variability among the RBP metrics used (Resh 1988)scored well, further corroborating the designation as a reference station. An extremely low Biotic Index (3.77the lowest of all the French & Quinebaug River watersheds biomonitoring stations) and high Scraper/Filterer metric value (1.28) relative to other biomonitoring stations in the Quinebaug River indicated the dominance of pollution-sensitive taxa among the QR0B benthos assemblage, and good overall trophic balance. Only the Percent Dominant Taxon metric performed poorly; however, this was the result of high densities of the mayfly, Stenonema sp.a fairly intolerant taxon that requires generally high quality, well-oxygenated waters. QR0B received a total metric score of 36 (Table A2). QR00Quinebaug River, upstream from Holland Rd., Sturbridge, MA. Sampling conducted 17 August 1999. Habitat The QR00 sampling reach began approximately 80 m upstream from Holland Road, in a forested and relatively undeveloped portion of the upper Quinebaug River watershed. The reach was 6-8 m wide, with well-developed riffle areas of varying depths (0.20-0.50 m) and pools up to 0.75 m deep. An abundance of large rocky substrates provided macroinvertebrates with excellent epifaunal habitat, while snags and other submerged woody debris provided excellent fish cover throughout the reach. Riparian and bank habitat parameters scored wellbanks were stabilized with large boulders and well-vegetated with grasses and herbaceous (cardinal flower, Lobelia cardinalis; Joe-Pye weed, Eupatorium sp.) growth. Riparian zone width was unlimited in this maple-dominated (Acer spp.) setting. Nonpoint source pollution was not observed in the immediate area adjacent to the sampling reach; however, instream deposits of fine organic matter and slight turbidity hinted at potential water quality effectspossibly the result of numerous large impoundment(s) located immediately upstream. QR00 received a habitat assessment score of 188/200one of the highest habitat evaluations received by a biomonitoring station in the 1999 French & Quinebaug River watersheds survey (Table A9). Benthos The QR00 benthos assemblage received a total metric score of 34, representing 94% comparability to reference conditions at QR0B and placing the benthos in the non-impacted category for biological condition (Table A2). This station was more comparable to the reference station than any other of the Quinebaug River study stations, with most metrics performing as good as, or better than, those for the least impacted conditions at QR0B (Table A2). Only the Scraper/Filterer metric performed poorly (score=2), probably the result of upstream impoundments. East Brimfield Lake, in particular, is currently on the Massachusetts Section 303(d) List of Waters due to noxious aquatic plants (MA DEP 1999). Productive conditions in that waterbody may account for the delivery of FPOM to downstream communities such as QR00. Indeed, filter-feeding taxa dominated the QR00 benthos assemblage (Table A1). This biological assessment differed from results of the 1994 biosurvey conducted here, when the benthos assemblage was found to be moderately impacted relative to reference conditions (Szal 1999). It should be noted, however, that the 1994 bioassessment of QR00 was based on a different reference station location, and only family-level taxonomy. Nevertheless, total Taxa Richness, EPT richness, and Biotic Indexat least at the family levelall improved here since the 1994 survey, suggesting possible improvements in biological integrity and water quality. The healthy aquatic community observed at QR00, coupled with its excellent instream and riparian habitat quality, corroborate its use as an upstream control station for DWMs site-specific investigations of point source discharges (i.e., Sturbridge and Southbridge WWTPs) in the Quinebaug River. QR01BQuinebaug River, downstream from Farquhar Road, Sturbridge, MA. Sampling conducted 20 August 1999. Habitat The QR01B sampling reach began approximately 100 m downstream from Farquhar Road, ending at a large pool immediately downstream of the road crossing. Due to the somewhat limited riffle areas, the sampling reach was slightly less than the 100 m called for in the standard operating procedures (Nuzzo 1999). Riffle habitat (0.10-0.25 m), though restricted to the middle portion of the reach, contained an abundance of cobble substrates and offered excellent habitat for macroinvertebrates. Fish habitat was also good, with deep (0.50-0.75 m) pools and submerged woody debris providing ample cover. Riparian and bank habitat parameters were less than optimalbank vegetative growth along the west bank in particular suffered from anthropogenic disruption (i.e., footpaths). The lack of bank vegetation probably exacerbated the erosional effects observed along both banks. Riparian vegetative zone width was minimal along both banks, although a thin vegetative buffer existed between the east bank and an adjacent horse farm/hay field. Where vegetative clearing had not occurred, shrubs (riverbank grape, Vitis riparia; elderberry, Sambucus canadensis) and herbaceous (jewelweed, Impatiens capensis; Joe-Pye weed, Eupatorium sp; purple loosetrife, Lythrum salicaria; goldenrod, Salidago sp.) growth dominated the riparian zone. Aquatic vegetative cover and algal growth were dense, covering 60% and 50% of the open-canopied reach respectively. Much of the instream vegetation consisted of rooted emergent (burreed, Sparganium sp.; arrow arum, Peltandra virginica) and submergent (water starwort, Callitriche sp.; milfoil, Myriophyllum sp.) forms. Mosses, attached to rocky substrates, were also quite common. Filamentous algae were observed on cobble substrates in both pool and riffles areas; green algal mats were common in riffles. Slight instream turbidity was observed. QR01B received a total habitat assessment score of 157/200 (Table A9). Various NPS-related habitat degradation affected the habitat assessment scoremost notably, instream sedimentation (especially deposition of sand and FPOM) and riparian disturbances (adjacent horse farm and hayfield, foot traffic along banks). While the Farquhar Road crossing might be responsible for some of the sediment inputs to this reach, it should be mentioned that sand/gravel operations exist along both Hamant and Hobbs brookstributaries that discharge to the Quinebaug River just upstream from QR01Band the Quinebaug River itself in the vicinity of Route 86. This station was the designated Quinebaug River reference station during MA DEPs 1994 biomonitoring survey in the French & Quinebaug River watersheds. However, MA DEP/DWM personnel deemed it inappropriate as a reference condition for the 1999 biosurvey due primarily to the observed instream and riparian habitat degradation noted above, and potential water quality impacts relating to the upstream WWTP (Sturbridge). Benthos Compared to the Quinebaug River watershed reference station (QR0B), the QR01B benthos assemblage received a total metric score of 28, representing 78% comparability to least impacted conditions in the watershed and resulting in a slightly impacted bioassessment (Table A2). Both the EPT/Chironomidae and Scraper/Filterer metrics performed poorly (score=2)the result of numerous filter-feeders and chironomids in the QR01B assemblage (Table A1). Compared to the upstream reference station at QR00, the QR01B benthos assemblage received a total metric score of 36, representing 90% comparability to the reference condition and placing the community in the non-impacted category for biological condition (Table A3). Richness metric (i.e., Taxa Richness, EPT Index) values were actually higher than those for the reference station (Table A3). In fact, Taxa Richness was higher here (29) than at any other biomonitoring station in the 1999 French & Quinebaug River watersheds survey. Thus, the water quality effects (i.e., impoundment effects such as abundant FPOM) apparently reflected in the upstream reference stations benthos assemblage appear to affect QR01B community structure and function in a similar manner. The high-scoring Community Similarity metric corroborates this. Based on comparisons to both the watershed reference station and the upstream reference station, then, it appears that community structure and function at QR01B is influenced more by water quality effects resulting from upstream impoundments [as with East Brimfield Lake, Cedar Pondlocated just upstream from QR01Bis also on the 303(d) list for noxious aquatic plants (MA DEP 1999)] and/or habitat quality impacts rather than suspected point-source related perturbations from the Sturbridge WWTP. Discharge effects should not be completely ruled out in this portion of the Quinebaug River, however, as the considerable macrophyte and algal growth observed at QR01B coupled with the slightly turbid instream conditions suggest water quality may in fact be degraded here. It is difficult to determine if biological integrity has improved or worsened at QR01B since the last biomonitoring survey conducted here by MA DEP. Because this was the reference station during the 1994 biosurveys, it did not receive an impairment designation. However, slight increases in family-level total Taxa Richness (16) and EPT richness (8) were documented here since the 1994 bioassessment. This may be a sign of improved biological quality or simply a result of temporal variability. Habitat degradationespecially sediment deposition and riparian disturbancescontinues to be a problem here, however, and probably threatens biological potential the most. QR01CQuinebaug River, downstream from Breakneck Brook, Sturbridge, MA. Sampling conducted 17 August 1999. Habitat The QR01C sampling reach began almost 700 m downstream from the Breakneck Brook confluence and flowed adjacent to Old Mashapaug Road in a predominantly forested secton of Sturbridge. Fairly deep (0.30 m) riffles, containing an abundance of boulder and cobble/pebble substrates, provided excellent epifaunal habitat for macroinvertebrates. Fish habitat was also rated excellent, with deep (0.50-0.75 m) pools and runs containing a mix of snags, submerged logs, and boulder. The stream was approximately 10-15 m wide and only about 25% shaded. Aquatic vegetation covered approximately 10-15% of the sampling reach, with rooted submergent forms of water starwort (Callitriche sp.) and milfoil (Myriophyllum sp.) the dominant species. Algae coverage was slightly less extensive and comprised filamentous growth on rocky substrates and green algal mats on some sediments. Riparian vegetation was dominated by treesmost notably ash (Fraxinus americana) and red maple (Acer rubrum); however, shrub growthespecially riverbank grape (Vitis riparia) and dogwood (Cornus sp.)were observed along the stream margins as well. Hydrophyllic grasses and ferns (Osmunda regalis) were also common along the margins and in the understory. Riparian/bank habitat parameters scored well, although NPS inputs (sediment inputs/road runoff) originating from the adjacent road resulted in erosion along the south bank and localized impacts (slight instream deposition) to the bottom of the sampling reach. Slight turbidity was observed in the water column and deposits of fine organic matter were seen in some of the slower portions of the reach. QR01C received a composite habitat assessment score of 190/200the highest received by a biomonitoring station during the 1999 French & Quinebaug River watersheds survey (Table A9). Habitat here was highly comparable to the upstream reference station QR00, and slightly less comparable to the Quinebaug River watershed reference station (QR0B) (Table A9). Benthos Despite the high quality epifaunal habitat here, the QR01C benthos assemblage received a total metric score of 26, representing 72% comparability to the QR0B reference station and resulting in an assessment of slightly impacted for biological condition (Table A2). The Scraper/Filterer metric value (0.14) affected the total metric score most negativelythe result of high densities of filter-feeding mayflies (Isonychia sp.), hydropsychid caddisflies (Hydropsyche morosa gr.), and fingernail clams (Pisidium sp.) (Table A1). The biological assessment of QR01C faired better when the assemblage was compared to the upstream reference station, QR00 (Table A3). A total metric score of 32 was 80% comparable to the upstream controla percent value that is intermediate to the slightly and non-impacted biological condition categories. Taxa Richness was actually higher at QR01C than at the QR00 control site; Biotic Index and Community Similarity metrics also scored well (score=6) relative to reference conditions upstream. Results of the bioassessment for QR01C are not unlike those for QR01Bmacroinvertebrate community structure and function are more comparable to the upstream reference station in the Quinebaug River than at the QR0B reference station. The effects of organic enrichment at QR01Cevidenced by high densities of filter-feeders, a displacement of scrapers, and instream deposits of FPOMmay simply be a result of the productive, impounded nature of the Quinebaug River watershed rather than the upstream wastewater discharge. QR03Quinebaug River, downstream from Mill Street, Southbridge, MA. Sampling conducted 17 August 1999. Habitat The QR03 sampling reach began approximately 135 m downstream from Mill Street, in a highly industrialized and channelized (a stone wall has replaced the north bank) portion of the Quinebaug River. The minimally (5%) shaded reach was approximately 6 m wide, with depth ranging from 0.30-0.40 m in riffle/run areas and up to 0.50 m deep in the pools. Swift current velocity, coupled with an abundance of cobble and pebble substrates offered excellent epifaunal habitat for macroinvertebrates. It should be noted, however, that low base-flow (channel only about half-full) resulted in much exposed epifaunal substrate. While the Channel Flow Status habitat parameter received the lowest score (6) of any of the Quinebaug River stations, it is difficult to determine whether or not this is the result of upstream water withdrawalsa perceived threat to this portion of the river. Fish habitat was less than optimal due to limited cover. In fact, instream trash (metal, plastic, glass) provided most of the stable fish habitat. The riparian zone was minimally vegetated along the north bank save for some hydrophyllic grasses, providing no buffer from an adjacent parking lot and mill building. Along the steep south bank, silver maple (Acer saccharinum), red maple (Acer rubrum), and slippery elm (Ulmus rubra) trees provided a thin riparian buffer from the adjacent road. Serious bank erosion has resulted in numerous bare spots along this bank, and a large pile of trash was observed near the top of the reach. The narrow vegetative buffer along both banks, coupled with the close proximity of adjacent industrial/commercial activity, increases the potential for nonpoint source pollution inputs to the QR03 reach. Large deposits of sand were observed throughout the upper portion of the sampling reachorigins of instream sedimentation are unknown; however, erosion along the steep south bank, adjacent parking lots, and stormdrains entering the stream at multiple points are potential sources. Slightly turbid instream conditions were observed. QR03 received a total habitat assessment score of 128/200 (Table A9). This was the lowest habitat score received by a biomonitoring station during the 1999 French & Quinebaug River watersheds survey Instream deposits of fine organic (FPOM) and inorganic (sand) matter may threaten habitat quality and biological potential here more than anything else. These fine materials can be deleterious because they can reduce light penetrationand consequently plant growth (instream aquatic vegetation and periphyton cover were minimal at QR03 despite the open-canopied nature of the reach), smother hard surfaces, and fill interstices within the substrate (Wiederholm 1984). Resident biota at QR03, then, may be subsequently affected by obstructions to food collection or respiration caused by fine deposits of organic/inorganic matter. Benthos Despite the poor habitat evaluation at QR03, the benthos assemblage received a total metric score (32) that was 89% comparable to the reference conditions of QR0B, resulting in a non-impacted assessment of biological condition (Table A2). Metric values for total richness (27) and EPT richness (11) were actually higher than those for QR0B, and a Percent Dominant Taxon metric value of 18% indicated better community balance here than at the reference station. Metrics for the QR03 benthos assemblage also scored surprisingly well when compared to the upstream reference station in the Quinebaug River. A total metric score of 34 represented 85% comparability to QR00, again placing the community in the non-impacted category for biological condition (Table A3). Four of the seven metrics calculatedincluding Taxa Richness and EPT Indexperformed as well as, or better than, those for the upstream reference station. QR04UQuinebaug River, north of Route 131, upstream from Southbridge WWTP discharge, Southbridge, MA. Sampling conducted 18 August 1999. Habitat The QR04U sampling reach began approximately 120 m upstream from the Southbridge WWTP discharge, in a heavily commercialized portion of the watershed. The wide (20 m) and mostly open (<5% shaded) reach was dominated by riffle areas of varying depth (0.20-0.30 m) and occasional deep (0.40-1.0 m) pools. Cobble, pebble, and gravel substrates offered excellent epifaunal habitat for macroinveftebrates; however, the small size of the rocky substrates and a lack of additional stable cover provided fish with only marginal habitat. Aquatic vegetative coverage was substantial, with mosses and rooted submergent macrophytes (milfoil, Myriophyllum sp.; pondweed, Potamogeton sp.) covering 70% of the reach. Algal growth was fairly minimal, consisting mainly of matted green forms. Both stream banks were stable, with good vegetative cover in the form of grasses and herbaceous growth (jewelweed, Impatiens capensis; riverbank grape, Vitis riparia; goldenrod, Salidago sp.; purple loosestrife, Lythrum salicaria). Riparian vegetation has been impacted by human activities a great deal herea shopping strip mall and parking lot (with storm drains) adjacent to the south bank offered numerous potential NPS inputs in the form of runoff. A parking lot associated with the WWTP facility encroached on the north bank, with active excavation and construction activities compounding the threat of NPS pollution impacts. The narrow riparian buffer that did exist along both sides of the river consisted mainly of willow (Salix sp.), sumac (Rhus sp.), birch (Betula sp.), and white pine (Pinus strobus). Slight turbidity was observed in the water column, and deposits of fine organic particulates covered substrates in 40% of the reach. Instream deposits of FPOM were documented here during the 1994 biosurvey and habitat evaluation as well (Szal 1999). QR04U received a total habitat assessment score of 153/200 (Table A9). Benthos Despite habitat comparable (94%) to the Quinebaug River watershed reference condition, the QR04U benthos assemblage received a total metric score of only 24, representing 67% comparability to the reference station at QR0B and resulting in a slightly impacted bioassessment (Table A2). The dominance of the community by the filter-feeding Hydropsychidae indicates an unbalanced community responding to an overabundance of fine particulate organic matter (FPOM) in the water column. Significant deposits of FPOM were also observed on much of the instream substrates. That the assemblage is dominated by filter-feeders is not surprising, as the impounded nature (and associated wetlands) of much of the Quinebaug River no doubt results in a constant source of suspended FPOM; however, the high densities represented by the hydropsychids are somewhat disconcerting and indicative of the effects of moderate enrichment. Typically, in lentic systems such as the upstream impoundments, the primary source of organic matter is autochthonous (produced within the system), with secondary inputs of allochthonous (transported into the system from someplace else) materials from shoreline and/or wetland vegetation as well as fluvial inputs (Wetzel 1975, Merritt et al. 1984). Phytoplankton productionand to a lesser extent, littoral vascular plant productionand associated dissolved organic matter (DOM), are the primary sources of autochthonous matter (Wetzel 1975). It is the physical-chemical flocculation (nonbiological) of this DOM and/or other biological processes that leads to the formation of FPOM, the primary nutrition resource utilized by filter-feeders (Wetzel 1975). While FPOM production in lotic systems is primarily a result of the processing of Coarse Particulate Organic Matter (CPOM) contributed by aquatic shredders, the high concentration of FPOM in stream systems immediately below pond and reservoir outlets has mainly lentic origins. If these lentic systems are subjected to increasingly eutrophic conditions the resulting effects of enrichment (i.e., increased algal, plant, and DOM production) can be seen not only in the lentic fauna, but also in the lotic aquatic communities immediately downstream. The enrichment effects (e.g., dominance of filter-feeders, displacement of scrapers) reflected in the QR04U benthic community are probably most directly related to the productive nature of various upstream portions of the Quinebaug River. Productivity of upstream impoundments may also be exacerbated by stormwater and other forms of urban runoff in the vicinity of downtown Southbridge, as well as suspected nutrient loads originating from Cady Brook which enters the Quinebaug River just upstream from QR04U. Highly productive waterbodies upstream, as well as various nonpoint source-related nutrient/organic loadings to the Quinebaug River, appear most responsible for biological impairment and suspect water quality at QR04U. In addition, instream deposits of fine organic (FPOM) materials threaten habitat quality and biological potential here as well. Despite the slightly impacted assessment resulting from the 1999 biosurvey at QR04U, biological integrity appears to have improved here since the 1994 MA DEP biosurvey. Results of the 1994 biomonitoring efforts at QR04U found the community to be moderately impacted based on family-level taxonomy, with biological impairment possibly attributed to the American Optical discharge and dam located just upstream (Szal 1999). The company has since discontinued the discharging of treated effluent to the Quinebaug River (P. Hogan MA DEP/DWM, personal communication 2001). Like the 1999 benthos assemblage collected here, the 1994 community was dominated (31%) by filter-feeding hydropsychids. Interestingly, chironomidsgenerally tolerant of organic pollutantswere a major component of the assemblage sampled in 1994; however, midges were poorly represented in the 1999 benthos sample. Family-level richnessfor both total taxa and EPT richnesswas considerably higher in the 1999 macroinvertebrate sample (17 and 7) than in the 1994 sample (11 and 4), which, coupled with the decline in chironomid densities, is somewhat encouraging and perhaps indicative of improved water quality and biological conditions in this portion of the Quinebaug River. QR06Quinebaug River, upstream from Route 197 and USGS gage, Thompson, CT. Sampling conducted 18 August 1999. Habitat The QR06 sampling reach began approximately 500 m upstream from Route 197 in a densely forested area of mostly oaks (Quercus spp.), ash (Fraxinus americana), and willow (Salix sp.). Approximately 15 m wide, the mostly (75%) shaded riffle-dominated reach offered excellent epifaunal habitat in the form of cobble/pebble substrates subjected to varying velocity-depth regimes. Depth ranged from 0.30 m in the riffle/runs to 0.40 m in the somewhat limited pool areas. Snags provided most of the stable, albeit, less than optimal fish cover. Aquatic vegetation coverage was considerably less here than at QR04U, consisting mainly of mosses and occasional patches of waterweed (Elodea sp.). Algal coverage was more extensivefilamentous forms were common in the pool areas while thin layers of periphyton were observed on cobble substrates in riffles. Riparian and bank habitat parameters scored very well here. Banks were stable and well-vegetated with grasses, moss, and elderberry (Sambucus canadensis) shrubs. The riparian zone was undisturbed and extensive, with herbaceous (Joe-Pye weed, Eupatorium sp.; jewelweed, Impatiens capensis; goldenrod, Salidago sp.; purple loosestrife, Lythrum salicaria) and shrub (riverbank grape, Vitis riparia) growth along both banks giving way to hardwood trees with a fern understory. Nonpoint source pollution inputs to this portion of the Quinebaug River were not evident; however, slight turbidity was observed in the water column. QR06 received a total habitat assessment score of 173/200 (Table A9). Benthos When compared to the Quinebaug River watershed reference station (QR0B), QR06 received a total metric score of 28, representing 78% comparability to reference conditions and placing the aquatic community in the slightly impacted category for biological condition (Table A2). As with many of the Quinebaug River study stations, filter-feeding organisms dominated the assemblage here, leading to a low-scoring Scraper/Filterer metric (score=0). Much like the benthos sample collected here in 1994, hydropsychid caddisflies were the numerically dominant taxon, comprising more than half of the sample (Table A1). However, other metric values were encouragingmost notably Taxa Richness and EPT Index, which were some of the highest values received by a biomonitoring station in the French & Quinebaug River watersheds survey (Tables A2-A8). At the family level, these richness metrics (17 and 10 for total Taxa Richness and EPT richness respectively) were considerably higher than those (9 and 7 for total Taxa Richness and EPT richness respectively) seen in the benthos assemblage collected during the 1994 bioassessment. When compared to the upstream control station QR04U, the QR06 benthic community received a total metric score of 42, indicating high (>100%) comparability to the reference condition. Several metrics at QR06including Taxa Richness, EPT Index, Biotic Index, and Percent Dominant Taxonperformed better than for the QR04U assemblage, resulting in a non-impacted bioassessment (Table A3). However, the impairment detected at QR04U (slightly impacted when compared to the Quinebaug River watershed reference station) may hinder its effectiveness as a control station and undermine somewhat the utility of these upstream/downstream comparisons. That said, it would appear from the bioassessments of QR06 that the Southbridge WWTP may have less effect on biological integrity at QR06 than other anthropogenic perturbations farther upstreammost notably, NPS pollution inputs associated with urban runoff, and the numerous dams and productive impoundments (though it is possible that productivity in the impoundments immediately upstream from QR06 is exacerbated by the Southbridge WWTP discharge). In addition, a rather lengthy portion of the Quinebaug River upstream from QR06 is on the 303(d) list for nutrients (MA DEP 1999). A combination of these and other unknown water quality stressors may be most responsible for the signs (dense algal coverage, a preponderance of filter-feeders) of slight organic enrichment evident in the QR06 sampling reach. French River FR14French River, upstream from Route 56, near Mill Street, Oxford, MA. Sampling conducted 19 August 1999. Habitat The FR14 sampling reach began approximately 160 m upstream from the Route 56 bridge, and was situated adjacent to Mill Street in the Rochdale section of Oxford. A hardwood/evergreen forest comprised of maple (Acer rubrum), ash, (Fraxinus americana) birch (Betula sp.), and hemlock (Tsuga canadensis) provided a closed canopy throughout the reach. Stream width was approximately 4 m, with a depth of 0.10-0.20 m in the riffle/runs and 0.20 m in the deepest pool areas. Historical mill activity upstream appears to have altered channel morphology in this portion of the French River. Riffle areas were comprised of an abundance of rocky substrates; however, the shallow (channel <50% full) nature of the reach resulted in somewhat limited epifaunal habitat. Fish habitat was also less than optimal due to lack of depth in pools and an absence of stable cover, although numerous dace were observed during kick sampling. Instream aquatic vegetation and algae were virtually absent, save for minimal amounts of moss on some of the rock substrates. Riparian/bank structure was generally good, with well-vegetated banks giving way to a wide riparian zone of mainly trees and occasional ferns in the understory and along the flood plain. Some bank erosion was observed, especially along the west bank near the top of the reach. Nonpoint source pollution inputs mainly originated from Mill Street, where the dumping of trash appears to be an ongoing practice and threatens riparian/instream habitat quality. FR14 received a total habitat assessment score of 131/200 (Table A9). FR14 served as the reference station for all biomonitoring stations in the French River during the 1999 survey. Despite evidence of habitat degradation, as well as the presence of upstream impoundments, it was still thought to represent least-impacted conditions in the French River. Its location in the relatively undeveloped upper portion of the watershed, and upstream from all point source discharges to the French River, corroborate this designation. This station was also the reference station during MA DEPs 1994 bioassessment of the French River, with comparisons made to stations downstream from the Oxford-Rochdale and Webster-Dudley WWTPs (Szal 1999). Benthos Taxa Richness and EPT Index values of 21 and 11 (Table A4)both higher than at the Quinebaug River reference station (QR0B)would appear to indicate generally good water quality and biological integrity in this portion of the French River. It is unclear how biological health here compares to conditions during the 1994 biosurvey. Though richness metric values were higher than those for the 1994 assemblage, community structure and function in the 1999 sample was more skewed toward a filter-feeder-based assemblage. Both Percent Dominant Taxon and Scraper/Filterer metrics performed better in 1994 than 1999. This was mainly the result of a high density (36) of the filter-feeding clam Pisidium sp. in 1999 (Table A1). Only five pisidiids were observed in the 1994 benthos sample (Szal 1999). Productive conditions documented by MA DEP (1999) in upstream impoundments probably play a major role in shaping community structure and function at FR14. In particular, 303(d)-listed Stiles Reservoir and Greenville Pond (noxious aquatic plants), and Rochdale Pond (nutrients, organic enrichment) probably contribute significant FPOM loads to downstream lotic communities such as FR14. FR15French River, upstream from Route 56, Oxford, MA. Sampling conducted 19 August 1999. Habitat The FR15 sampling reach began approximately 100 m upstream from Route 56, in the North Oxford Village section of Oxford. This highly channelized (both banks were rip-rapped) portion of the river was approximately 2 m wide, with a depth of only about 0.10-0.20 m. Riffle areasthough common and consisting of ample rocky substrateswere extremely shallow, resulting in macroinvertebrate habitat that was marginal at best. Fish habitat was also limited due to the low base-flow (channel less than half full) here, with inadequate cover and a lack of stable habitat. Thin layers of periphyton and filamentous forms of green algae covered much of the available substrate; The mostly open (reach 10% shaded) canopy was conducive to light penetration and algal growth. Riparian and bank structure parameters scored well. Banks were well-stabilized due to the presence of boulder rip-rap along the base of both banks. Upper portions of the banks were vegetated with a mix of riverbank grape (Vitis riparia) and herbaceous growth (jewelweed, Impatiens capensis; Joe-Pye weed, Eupatorium sp; purple loosetrife, Lythrum salicaria). A wide riparian zone, consisting mainly of hardwood trees (ash, Fraxinus americana; birch, Betula sp.; willow, Salix sp.), extended from both banks. Riparian disturbances were minimal along most of the sampling reach; however, a house near the top of the reach offered potential NPS inputs in the form of backyard trash- dumping. FR15 received a total habitat assessment score of 136/200, which was slightly higher than the evaluation received at the reference station (Table A9). Low base-flow here is clearly affecting instream habitat most negatively. Benthos The FR15 benthos assemblage received a total metric score of 32, representing 84% comparability to the French River reference station (FR14). The resulting assessment for biological condition was non-impacted. Virtually all metrics outperformed those for the reference stationmost notably, Taxa Richness, EPT Index, and Biotic Index (Table A4). And while EPT/Chironomidae and Community Similarity metrics scored poorly (scores=0 and 2 respectively), this was mainly the result of an assemblage much less dominated by filter-feeding hydropsychid caddisflies than at the reference station. Other signs of improved trophic balance were evidentPercent Dominant Taxon was only 19% (score=6) and the Scraper/Filterer metric value was higher than for the FR14 assemblage (Table A4). The displacement of filter-feeders such as caddisflies with algal scrapers observed at FR14 is consistent with biological conditions observed here during the 1994 biosurvey. In 1994, filter-collectors were about 50% more abundant in the reference station (FR14) sample than the test (FR15) sample, and the Scraper/Filterer ratio for the test station sample was about five times that for the reference station samplesuggesting that higher concentrations of suspended organic matter existed at the reference station than at FR15 (Szal 1999). Of greater significance may be results of the community composition metrics. Taxa Richness and EPT Index metrics performed poorly during the 1994 benthos evaluation, contributing to the moderately impacted bioassessment (Szal 1999). That these metrics outperformed those for the reference station during the 1999 bioassessmentand also were higher than the 1994 valuesmay be indicative of improved water quality and biological integrity here since the 1994 survey. FR11French River, upstream from Oxford Ave., Webster, MA. Sampling conducted 19 August 1999. Habitat The FR11 sampling reach began immediately upstream from the Oxford Avenue bridge and adjacent to a USGS gaging station, and ended just downstream from a railroad crossing in downtown Webster. Stream width in this minimally (5%) shaded reach ranged from about 2-6 m, with an average depth of 0.30 m in the riffles and up to 0.75 in the deepest pool areas. Channelization, mainly in the form of the railroad bridge abutment and a concrete wall along the south bank, and rip-rap along both banks near the Oxford Ave. crossing, has resulted in altered channel morphology in this portion of the river. Rocky substrates (cobble and pebble) subjected to varying flow regimes provided excellent epifaunal habitat for macroinvertebrates. Fish habitat was also optimal, with boulder, snags, and submerged logs providing stable cover in riffle and pool areas. Dense beds of water milfoil (Myriophyllum sp.), covering about 70% of the reach, provided additional microhabitat for fish. Algal cover was also extensive, with filamentous green forms and mats covering rock and vegetative substrates in approximately 60% of the reach. Bank vegetation was good along the north bank, though slightly disrupted along the south bank in the vicinity of a residential property. Trash deposits were noted in the backyard of this house as well. Both stream banks were fairly stable, with some infrequent small areas of erosion along the north bank. An adjacent parking lot along the north bank and the house near the south bank resulted in riparian vegetative disturbancessumac (Rhus sp.) and Japanese knotweed (Polygonum cuspidatum) were a common component of the vegetative buffer. Other riparian vegetation consisted of shrubs (riverbank grape, Vitis riparia; elderberry, Sambucus canadensis), herbaceous growth (jewelweed, Impatiens capensis), and a few trees (maple, Acer rubrum; ash, Fraxinus americana). The various impervious surfaces nearby and the adjacent backyard offered numerous NPS pollution inputsmost notably sand and trashto this portion of the river. Other sources may also contribute to the moderate sediment deposits and associated substrate embeddedness observed throughout the FR11 sampling reachnumerous nearstream sand/gravel operations exist in this portion (i.e., between Oxford and Webster centers) of the French River. Benthos The benthos assemblage at FR11 received a total metric score of 36, which represented 95% comparability to the reference station. Despite slight reductions in total taxa and EPT richness compared to the reference community, the FR11 benthos was found to be non-impacted (Table A4). The macroinvertebrate community here was dominated (>60%) by filter-feeding hydropsychids to the extent that the resulting biological assessment should be interpreted with caution. From a structural and functional standpoint, this is clearly an imbalanced community responding to an abundance of FPOM in the water column. Numerous weed-choked impoundments (e.g., Lowes, Robinson, Nipmuck, and McKinstry ponds) (MA DEP 1999), as well as the massive Webster Lake which discharges immediately upstream from FR11 via Mill Brook, probably collectively contribute to the dense FPOM food resource in this portion of the French River and the resulting macroinvertebrate assemblage found at FR11. FR17French River, upstream from Hill Street, Webster, MA. Sampling conducted 18 August 1999. Habitat The FR17 sampling reach began approximately 120 m downstream from Hill Street and about 1 km downstream from FR11. Despite the close proximity to downtown Webster, land-use in the immediate area was predominantly forest, providing a closed canopy (reach 98% shaded) throughout the reach. The stream was approximately 9 m wide, with depths of 0.20-0.40 m in the riffle/run areas and 0.40 m in the pools. Rocky substrates and good current velocity provided macroinvertebrates with generally excellent habitat, although instream deposits of sand and FPOM compromised epifaunal substrate quality in some areas. Fish habitat was less than optimal due to the somewhat limited stable cover. Instream vegetative coverage was extensive (50% of reach), especially with rooted submergent taxa such as milfoil (Myriophyllum sp.), water starwort (Callitriche sp.), and pondweed (Potamogeton sp.). Algal growth was also quite densefilamentous and matted green algae were observed in the riffle and pool areas of 50% of the reach. Both banks were well-vegetated, and bank stability was excellent along the west bank. Serious bank erosion and undercutting were observed along most of the east bank, however. Riparian vegetative zone width was extensive along both sides of the reach, with herbaceous (jewelweed, Impatiens capensis; ferns) and shrub (riverbank grape, Vitis riparia; elderberry, Sambucus canadensis; Japanese knotweed, Polygonum cuspidatum) growth giving away to a hardwood-dominated forest of mainly oak (Quercus sp.), elm (Ulmus rubra), maple (Acer spp.), and birch (Betula sp.). Petroleum odors detected near the top of the reach and slight turbidity in the water column indicated suspect water quality. Sand and FPOM deposits threaten habitat quality throughout the reach. FR17 received a total habitat assessment score of 151/200 (Table A9). Benthos The benthos sample taken at FR17 received a total metric score of 32, representing 100% comparability to the least disturbed conditions at FR14 (Table A4). Metric values for richness and Biotic Index were virtually the same as for the reference station, and while the filter-feeding hydropsychids continue to dominate the assemblage and lead to point reductions (score=2) for the Percent Dominant Taxon metric, their densities were not as high as at the FR11 station just upstream. In fact, trophic structure at FR17 appears more balanced than in the community observed here in 1994, when net-spinning caddisflies were hyperdominant and contributed to a moderately impacted bioassessment (Szal 1999). Community composition at FR17 also seems to have improved considerably since the 1994 biosuvey, with increases in both total Taxa Richness (from 8 in 1994 to 14 in 1999) and EPT Index (from 4 in 1994 to 7 in 1999) at the family level. Analysis of metrics for the FR17 benthos assemblage resulted in a bioassessment of non-impacted. However, the extensive macrophyte and algae cover, FPOM deposits, and preponderance of filter-feeders at FR17 continue to suggest some level of organic enrichment in this portion of the French River. FR17 was also used as an upstream control station in an attempt to bracket the discharge effects of the Webster-Dudley WWTP on the downstream biological community at FR18. That it received a non-impacted designation for biological condition corroborates its use as an upstream reference station for site-specific investigations. FR18French River, upstream from Langers Pond, Thompson, CT. Sampling conducted 18 August 1999. Habitat The FR18 sampling reach was approximately 700 m downstream from Perryville Road near the Massachusetts-Connecticut border. The Webster-Dudley WWTP discharge was located about 1.5 km upstream. Surrounding land-use in this relatively undeveloped portion of the watershed was virtually 100% hardwood forest, providing a mostly (>60%) shaded sampling reach. Stream substrates in the 10 m wide reach were dominated by boulders and large cobble, offering good epifaunal habitat for macroinvertebrates in well-developed riffle (0.30-0.40 m deep) areas. Fish habitat was excellentin addition to massive boulders, submerged woody material and deep (0.50 m) pools offered much stable cover. Aquatic vegetation covered almost one third of the reach, with rooted submergent (waterweed, Elodea sp.; pondweed, Potamogeton sp.) and free-floating (Lemna sp.) macrophytes common. Algae were fairly abundant (25% cover) as well, mainly comprised of a filamentous green alga and thin films of periphyton on rocky substrates. Bank and riparian habitat parameters scored well. Both stream banks were well-vegetated with riverbank grape (Vitis riparia) and herbaceous (jewelweed, Impatiens capensis; royal fern, Osmunda regalis; sensitive fern, Onoclea sensibilis) growth. Stability was provided by large boulders and tree roots. The riparian zone along both sides of the reach was wide and undisturbeddominated by hardwood (oak, Quercus sp.; ash, Fraxinus americana) trees and a mountain laurel (Kalmia latifolia) understory. A railroad crossing just upstream from the reach, and nearby sand/gravel operations were potential sources of NPS pollution. In addition, a considerable amount of trash (tires, plastics, metal tanks) was observed in the sampling reach. Slight turbidity was observed in the water column, and an odor of treated sewage was detected here as well. FR18 received a total habitat assessment score of 174/200the highest evaluation received by a French River biomonitoring station during the 1999 survey (Table A9). Benthos When compared to the FR14 reference station, FR18 received a total metric score (36) that was 95% comparable to the least-impacted conditions in the French River (Table A4). Most metric values scored as well as those for the reference assemblage, resulting in a non-impacted bioassessment. Only the Percent Dominant Taxon metric performed poorly, the result of a hyperdominance of Hydropsychidae and indicative of an overabundance of the FPOM food resource in this portion of the French River. In fact, filter-feeding hydropsychids were twice as abundant at FR18 in 1999 than during the 1994 biosurvey. Other metrics, however, suggest improvements in community composition at FR18 since the 1994 surveymost notably family-level Taxa Richness and EPT Index metric values which have improved from 11 and 4 respectively in 1994 to 14 and 7 in 1999. When compared to the upstream reference station, FR17, the FR18 benthos assemblage received a total metric score of 30, representing 94% comparability to upstream reference conditions and again placing the community in the non-impacted category for biological condition (Table A5). Results of upstream/downstream community comparisons, then, suggest that water quality conditions (especially those relating to impoundment effects and/or urban runoff associated with downtown Webster) upstream from the Webster-Dudley WWTP discharge, rather than the discharge itself, probably most-influence biological integrity at FR18. Tributaries - Cady Brook Since the 1994 biomonitoring surveys at Cady Brook, a Phase 1 facility upgrade of the Charlton WWTP has been completed, with operation beginning in 1997. However, subsequent problems have arisen at the facility in connection with the recent tie-in of the Massachusetts Turnpike Authoritys Eastbound Facility discharge, which sends heavy weekend BOD, nutrient, and suspended solid loads to the Charlton WWTP. The turnpike facility is also responsible for suspect water quality documented by MA DEP in Sibley Brooka tributary to Cady Brook (Hartman 2001). In addition, the town of Charlton has requested an increased discharge flow in order to accommodate both new construction as well as existing point source dischargers in the area (Bay Path Vocational High School, Masonic Rest and Nursing Home). The additional connections are expected to increase loadings at the Charlton WWTP facility to over ten times present day average daily loadings to a maximum of 450,000 gpd (Hartman 2001). Potentially exacerbating impacts from the increased effluent discharge is the flow regulation of the outlet structure at Glen Echo Lake. The headwaters of Cady Brook, Glen Echo Lake is used extensively for recreational purposes and water flow from the lake is eliminated during the summer months to maintain a high surface water level for boating. Thus, the Cady Brook system becomes an effluent-dominated system during the summer months, with minimal waste assimilative capacity. Indeed, DWM was unable to conduct biomonitoring at Cady Brook stations CA04 and CA06 during the scheduled August biosurvey due to low base-flowthe proposed sampling reach upstream from the Charlton WWTP discharge contained only isolated pools of standing water. As a result, the biosurvey here was postponed until the end of September, when sufficient volume and current velocity allowed for the application of DWMs RBP-based sampling methodologies. DWM also conducted water quality monitoring in concert with the biomonitoring efforts at Cady Brook. Information gathered from the water quality survey will be utilized to develop an updated wasteload allocation model for the Charlton WWTP, as well as in the assessment of water quality conditions in the French & Quinebaug River watersheds. Biomonitoring data collected during the 1999 survey will allow MA DEP to assess the impacts of a known anthropogenic pollution source (i.e., Charlton WWTP), to provide comparative biological data to evaluate stations historically sampled by MA DEP in an attempt to determine changes which may have taken place since the 1997 treatment plant upgrade, to evaluate additional locations to determine the extent of impacts downstream, and provide information on the effects of unknown or potential nonpoint source pollution inputs. CA04Cady Brook, upstream from Charlton WWTP, Charlton, MA. Sampling conducted 23 September 1999 (low base-flow precluded sampling in August). Habitat The CA04 sampling reach began approximately 25 m upstream from the Charlton WWTP discharge. Land-use in this portion of Cady Brook was predominantly forest and the WWTP property (mowed grass). The reach was minimally (20%) shaded. Base-flow had improved here since the failed August sampling attemptcobble and pebble dominated substrates provided ample, albeit shallow (0.20 m), riffle habitat for macroinvertebrates. Fish habitat remained quite limited, primarily due to shallow pools (0.30 m) and minimal cover. Occasional patches of moss and filamentous green algae were present, yet minimal. Both banks were well-vegetated with dense shrub (riverbank grape, Vitis riparia; sumac, Rhus sp.; elderberry, Sambucus canadensis; rose, Rosa sp.) and herbaceous (goldenrod, Salidago sp.; Joe-Pye weed, Eupatorium sp.) growth along the margins of the stream. Bank stability was generally good, save for a few small areas of erosion along the east bank near the WWTP outfall pipe. Riparian disruption was observed along both banks, but was most severe near the east bank due to the close proximity of the treatment facilitys property and associated lawn, failing silt screens, and stone walls. In addition to the shrub and herbaceous growth mentioned above, riparian vegetation consisted of maple (Acer spp.), birch (Betula sp.), and white pine (Pinus strobus). CA04 received a total habitat assessment score of 148/200 (Table A9). This was the designated upstream reference station for comparisons to biomonitoring stations downstream from the Charlton WWTP discharge. Benthos Despite a Biotic Index suggesting a generally pollution sensitive assemblage at CA04, the EPT Index was only 3 (Table A6). It is possible that the periodic low base-flowsand the subsequent elimination of productive epifaunal habitatmay contribute to the reduction in EPT taxa at CA04, as many of these organisms are particularly susceptible to substrate exposure and stranding (Minshall 1984). In terms of trophic structure, the scraper-based benthos assemblage observed at CA04 in 1999 was similar to the assemblage sampled by MA DEP in 1994, when elmid beetles were the numerically dominant taxon (Szal 1999). However, dramatic reductions in both family-level total Taxa Richness and EPT richness were observed in the 1999 benthic community compared to the 1994 sample. The reason for the discrepancy in community composition between the two surveys is unknown; however, it is possible that the upstream flow alteration (i.e., flow regulation at the Glen Echo Lake outlet structure) and resulting reduced summer base-flowsexacerbated by a near-record dry summerobserved here during the 1999 survey were not a factor in 1994. That water quality monitoring conducted here by DWM in 1999 found generally good water quality suggests that more than likely it is flow-related instream habitat constraints rather than water quality constraints that limit biological potential at CA04. CA06Cady Brook, downstream from Charlton WWTP, Charlton, MA. Sampling conducted 23 September 1999. Habitat The CA06 sampling reach began downstream from a small wooden footbridge and approximately 100 m downstream from the Charlton WWTP discharge. Like the CA04 reach, CA06 was minimally (15%) shaded. Most of the kicks were made downstream from the footbridge and adjacent to a now-defunct diner (Dee-Dees); however, two were made immediately downstream from the discharge outfall. Base-flow here (channel only half-full) did not seem markedly different than at the CA04 sampling reach. Stream width was approximately 2 m, with depths of about 0.10-0.20 m in the riffle/runs and up to 0.30 m in the pool areas. Much like at CA04, cobble and pebble-dominated substrates offered good epifaunal habitat for macroinvertebrates, while fish habitat suffered due to shallow water and lack of stable cover. Algae cover here was more extensive than at CA04, consisting mainly of a filamentous green alga and covering a quarter of the reach. Stream banksthough fairly well-vegetated with grasses, shrubs (elderberry, Sambucus canadensis; Japanese knotweed, Polygonum cuspidatum; sumac, Rhus sp.; riverbank grape, Vitis riparia), and herbaceous (goldenrod, Salidago sp.; Joe-Pye weed, Eupatorium sp.) growthwere somewhat unstable, especially along the west bank just upstream from the footbridge. An extensive golf driving-range lawn and large piles of sand disrupted riparian vegetative growth along the east bank, while the minimally buffered parking lot associated with Dee-Dees offered potential NPS inputs along the west bank. The riparian buffer improved somewhat towards the top half of the reach, with red maple (Acer rubrum), oak (Quercus sp.), birch (Betula sp.), ash (Fraxinus americana), and white pine (Pinus strobus) recorded. Instream deposits of sand and fine organic matter were observed throughout the sampling reach, and a slight odor of treated sewage was detected during sampling. CA06 received a total habitat assessment score of 117/200 (Table A9). Instream habitat parameters most reliant on base-flow, along with riparian disturbances, affected the evaluation most negatively. Benthos When compared to CA04, the CA06 benthos assemblage received a total metric score of 22, representing 55% comparability to upstream reference conditions and resulting in a slightly-impacted bioassessment (Table A6). Low scoring (score=0) values for the Scraper/Filterer and Percent Dominant Taxon metrics, as well as reduced similarity to the reference community (Community Similarity: 51%), clearly indicate a shift in benthic community function below the Charlton WWTP discharge. The relatively pollution sensitive scrapers that dominated the CA04 assemblage have been almost completely displaced here by more tolerant filter-feeding taxa (e.g., hydropsychid caddisflies comprise two-thirds of the sample), indicating that effluent-related FPOM has replaced periphyton as the primary food resource in this portion of Cady Brook. In addition, the presence of only two EPT taxa suggests low levels of dissolved oxygen often associated with increased organic enrichment. Indeed, DWM documented a decrease in percent saturation from 80% at CA04 to 61% at CA06 during the August water quality survey (Hartman 2001). Other water quality analytes recorded by DWM here during the August survey corroborate the effluent-related water quality effects reflected in the resident biota at CA04. Most dramatic were the high levels of total phosphorus (>0.60 mg/l), ammonia (>0.20 mg/l), nitrate-nitrogen (37 mg/l), and organic nitrogen (1.09 mg/l) (Hartman 2001)further evidence that the Charlton WWTP discharge contributes significant organic nutrient loads to this portion of Cady Brook. Despite the slightly-impacted status of the CA06 macroinvertebrate community, biological integrity has probably improved here since the 1994 biomonitoring survey, when tubificid wormsconsidered highly tolerant of conventional organic pollutionwere hyperdominant and contributed to a moderately-impacted bioassessment that was attributed to discharge effects (Szal 1999). In the 1999 benthos sample tubificid worms were virtually absent, replaced by somewhat less tolerant forms of filter feeding hydropsychids as the predominant taxon. These apparent changes in community structure are probably attributable to improved effluent quality resulting from the 1997 discharge upgrades at the Charlton WWTP. CA10ACady Brook, upstream from Snake Hill Road, Charlton, MA. Sampling conducted 20 August and 23 September 1999. Habitat The CA10A sampling reach began 130 m upstream from Snake Hill Road and approximately 1.50 km downstream from Sibley Brooks confluence with Cady Brook. Land-use in the vicinity of the reach was predominantly forest (shading 98% of the reach), with a few nearby residences. The discharge contributions from upstream tributaries resulted in a reach that was wider (5 m) and deeper (0.20-0.30 m in riffle/runs; 0.40 m in pools) than CA04 and CA06 during the September biosurveys. Rocky substrates comprised of mainly cobble/pebble with some boulder provided excellent epifaunal habitat for macroinvertebrates in the well-developed riffle areas. Fish habitat was also optimal, with a good mix of boulder and submerged woody material offering stable cover. Instream vegetation was scarce, and algal cover was not nearly as extensive as at the upstream stations. Banks were well-vegetated with ferns and mosses, and boulders provided good stability along the west bank. Bank stability suffered somewhat along the east bank, where tree clearing associated with nearby power lines resulted in erosional areas at the top of the reach. Trash piles were observed in the backyard of an adjacent residence; however, riparian vegetation (oak, Quercus sp.; birch, Betula sp.; hemlock, Tsuga canadensis; white pine, Pinus strobus; red maple, Acer rubrum) offered an adequate buffer between the stream and dumping activities. The riparian zone along the east bank was less extensive, due to the close proximity of the power lines and associated clearing. Occasional deposits of sandmore substantial in August than during the September biosurveywere observed in the sampling reach, apparently originating from a small tributary entering near the top of the reach and receiving the runoff from the adjacent road (Route 169). Other sources (e.g., via Sibley Brook) of sediment inputs may exist as well. CA10A received a total habitat assessment score of 131/200 during the August biosurvey (Table A9). During the September biosurvey, it received a total habitat assessment score of 155/200, which was the highest habitat evaluation received by a Cady Brook biomonitoring station during the 1999 survey (Table A9). Increases in base-flow contributed to better epifaunal habitat and an overall higher habitat evaluation at CA10A during the September biosurvey. Benthos The CA10A (September sample) benthos assemblage received a total metric score of 40, which was identical (100% comparable) to that received by the upstream reference station, CA04 (Table A6). Five of the seven metrics calculated outperformed those for the reference station, contributing to the non-impacted bioassessment. Compared to the reference station in Town Meadow Brook (MB11), CA10A (August benthos sample) was again highly comparable (95%) to least-impacted conditions, receiving a total metric score of 40 and a non-impacted assessment for biological condition (Table A7). Regardless of which reference condition is used, then, it appears that the enrichment effects observed farther upstream at CA06 have diminished this far downstream from the Charlton WWTP discharge. Despite habitat differences between the August and September biosurveys at CA10A, metric values were comparable for both macroinvertebrate assemblages and community similarity was high (79%) (Table A7). Differences in base-flow and related habitat parameters, in particular, were probably too minimal to result in significant temporal variability in metric performance. Sibley Brook discharge contributions are probably instrumental in the maintaining of instream base-flows adequate for support of a healthy aquatic community here. It is likely that improvements in both habitat and water quality are jointly responsible for the apparent recovery of biological integrity at CA10A as reflected in the resident benthos found here during the August and September biosurveys. Indeed, water quality monitoring by MA DEP at Snake Hill Road indicated improved levels of dissolved oxygen, and nutrient levels comparable to those recorded at CA04 (upstream from Charlton WWTP) (Hartman 2001). Other parameters (e.g., conductivity, BOD, suspended solids) indicated improved water quality as well (Hartman 2001). And discharge contributions from upstream tributariesmost notably, Sibley Brooknot only increase the assimilative capacity in this portion of Cady Brook, but also provide improved instream habitat for macroinvertebrates (and fish) as a result of increased base-flow. Interestingly, suspect water quality (elevated bacteria, BOD, and turbidity) originating from Sibley Brook was documented by MA DEP during the 1999 water quality survey (Hartman 2001); however, these effects apparently were not reflected in the CA10A aquatic community (although instream turbidity was observed at CA10A). Tributaries - Town Meadow Brook A second-order tributary to the French River, Town Meadow Brook originates in Sargent Pond, flowing in a generally southerly direction before reaching Greenville Pondthe source water for the French River. Land-use in the Town Meadow Brook subwatershed is mainly forest, with some light residential development along the Route 56 corridor of Leicester. The Leicester WWTP, located just downstream from Route 9, is the perceived major anthropogenic stressor to the Town Meadow Brook system. MB11Town Meadow Brook, upstream from Leicester WWTP, downstream from Ashworth Pond, Leicester, MA. Sampling conducted 19 August 1999. Habitat The MB11 sampling reach began approximately 140 m downstream from Ashworth Pond and immediately upstream from the Leicester WWTP discharge. Surrounding land-use was predominantly forest, with the exception being the WWTP facility property near the bottom of the reach and a house near the top of the reach. Both of these properties, however, were well-buffered from the stream. Instream substrates were dominated by cobble/pebble; however, the naturally shallow nature of this small (1-2 m wide; riffle/runs 0.10-0.20 m deep) stream resulted in less than optimal epifaunal habitat. Aquatic mosses covered half of the reach and provided additional microhabitat for macroinvertebrates. Instream algal growth was fairly minimalperhaps the result of a mainly closed (95% shaded) canopy along the sampling reach. Fish habitat was also suboptimalpools were very shallow (<0.30 m) and the woody materials (submerged logs, snags) that normally provide good fish cover were mostly exposed and unavailable to fish. Riparian and bank parameters scored well. Banks were well-vegetated with ferns, mosses, shrubs (riverbank grape, Vitis riparia; rose, Rosa sp.), and herbaceous (Joe-Pye weed, Eupatorium sp.; poison ivy, Rhus radicans); purple loosestrife, Lythrum salicaria; jewelweed, Impatiens capensis) growth. Boulders, mosses, and root masses provided good bank stability. Riparian vegetation, consisting mainly of hardwood trees (oak, Quercus sp.; ash, Fraxinus sp.; maple, Acer rubrum) and white pine (Pinus strobus), was extensive and undisturbed along both sides of the stream. There were no signs of NPS pollution inputs to the MB11 sampling reach, although an upstream road crossing (Route 9) is a potential source. MB11 received a total habitat assessment score of 163/200 (Table A9). This station was designated the upstream reference station in an attempt to discern the effectsif anyof the Leicester WWTP discharge on the downstream biota at MB12. Benthos The MB11 benthos assemblage showed good trophic balance, with virtually all major functional feeding groups well represented (Table A1). Filter-feeding hydropsychids, though abundant, were not hyperdominant as they were during the 1994 biosurvey conducted near here. Overall community structure was good, with a number of pollution-sensitive taxa present, good Taxa Richness, and no dominant taxon at the genus/species level (Table A8). In fact, Taxa Richness and EPT Index metric values were more than twice that documented during the 1994 bioassessment (Szal 1999). MB12Town Meadow Brook, downstream from Leicester WWTP, upstream from Pine Street, Leicester, MA. Sampling conducted 19 August 1999. Habitat The mostly (80%) shaded sampling reach began approximately 15 m upstream from the Pine Street crossing and ended just downstream from a small, wooden footbridge. Much like the upstream reach at MB11, MB12 was only about 1-2 m wide with shallow riffle/run and pool areas only about 0.10 m and 0.20 m deep respectively. Despite the abundance of cobble and boulder substrates, the low base-flow (channel only half-full) provided very limited epifaunal habitat for macroinvertebrates. Fish habitat was only slightly better, with some boulder and snags providing stable cover. Shrubs (riverbank grape, Vitis riparia; elderberry, Sambucus canadensis) and herbaceous growth (ferns; jewelweed, Impatiens capensis) provided good bank vegetation along the west bank. This vegetation, interspersed with large boulders, provided good stability along this bank as well, although some small areas of erosion were observed near the top of the reach. A dense hardwood-evergreen forest provided an undisturbed riparian zone along the west bank, with oak (Quercus sp.), ash (Fraxinus americana), white pine (Pinus strobus), and hemlock (Tsuga canadensis) common. Bank and riparian habitat parameters were considerably more degraded along the east bank, mainly due to the close proximity of several houses with mimimally buffered backyards. A few of the properties adjacent to the reach offered potential NPS pollution inputs in the form of yard waste and lawn runoff. The bank instability and erosion observed along this bank was probably exacerbated by the clearing of vegetation and dumping of yard waste (leaves, grass clippings, branches), and the few trees present provided only a minimal vegetative buffer from these activities. Probably most detrimental to this portion of Town Meadow Brook is the dumping of trash behind a house at the bottom of the reach, where enormous amounts of car parts, scrap metal, and other debris are piled near the stream. There is virtually no riparian buffer here, and a stone wall that helps to prevent refuse from entering the stream is currently in a state of gradual collapse. MB12 received a total habitat assessment score of 116/200. This was easily the lowest habitat score received by a biomonitoring station in the entire 1999 French & Quinebaug River watersheds survey (Table A9). Benthos Despite the degraded riparian habitat, and potential impacts from the WWTP discharge, the MB12 benthos received a total metric score of 42the same score received by MB11 (Table A8). Outperforming the upstream reference station for virtually every metric, the resulting bioassessment was non-impacted. Richness metrics (Taxa Richness, EPT Index) were not only higher than at the upstream reference station, but also higher than those recorded here during the 1994 biosurvey (Szal 1999). In addition, two species (Acroneuria sp.; Paragnetina sp.) of Plecopteragenerally considered to be the most pollution sensitive insect order and rarely associated with effluent-receiving surface waterswere recorded in the 1999 benthos sample (Table A1). Based on the resulting bioassessment here, then, it would appear that habitat degradationmost notably NPS inputs and other riparian disruption along the east bankmay pose a greater threat to biological potential at MB12 than discharge-related water quality effects. SUMMARY/ RECOMMENDATIONS Quinebaug River QR0B Benthos: Reference condition for watershed Habitat: Reference condition for watershed Despite slight impoundment effects resulting from its location downstream from Hamilton Reservoir, the QR0B benthic community was thought to represent the best attainable conditions in the watershed with respect to biological integrity, habitat quality, and water quality. Biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004, especially if it is to serve as the reference station. Fish population sampling, which has not historically been performed by MA DEP in this watershed, should accompany the macroinvertebrate sampling effort. QR00 Benthos: Non-impacted compared to watershed reference; Upstream reference condition Habitat: >100% comparable to watershed reference; Upstream reference condition Despite the non-impacted bioassessment received here, the effects of productive upstream impoundments were seen in the benthos assemblage (dominance of filter-feeders) and habitat in the form of instream FPOM deposits. Nevertheless, total Taxa Richness, EPT richness, and Biotic Indexat least at the family levelall improved here since the 1994 MA DEP biosurvey, suggesting possible improvements in biological integrity and water quality. Biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004, especially if it is to serve as an upstream reference station. Fish population sampling should accompany the macroinvertebrate sampling effort. QR01B Benthos: Slightly impacted compared to watershed reference; Non-impacted compared to upstream reference Habitat: 97% comparable to watershed reference; 84% comparable to upstream reference Based on comparisons to both the watershed reference station (QR00) and the upstream reference station (QR0B), it appears that benthic community structure and function at QR01B is influenced more by water quality effects resulting from upstream impoundments and/or habitat quality impacts rather than suspected point-source related perturbations from the Sturbridge WWTP. Nonpoint source pollution compromises both habitat potential and biological health at QR01B. Sediment deposition, probably originating from multiple sources (upstream sand/gravel operations, road runoff, eroding banks), and riparian disruption along both banks of the reach affect habitat quality most negatively. In addition, the restoration of a more adequate vegetative buffer along the sampling reach would help alleviate the effects of some of these NPS inputs. To continue to monitor the quality of the Sturbridge WWTP effluent and any effects it may have on downstream aquatic communities, biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004. Fish population sampling should accompany the macroinvertebrate sampling effort. QR01C Benthos: Slightly impacted compared to watershed reference; Slightly/Non-impacted compared to upstream reference Habitat: >100% comparable to watershed reference; >100% comparable to upstream reference The effects of organic enrichment at QR01Cevidenced by high densities of filter-feeders and displacement of scrapersmay simply be a result of the productive, impounded nature of the Quinebaug River watershed rather than the upstream wastewater discharge. Instream deposits of FPOM observed in the QR01C sampling reach may threaten biological potential the most. These fine materials can be deleterious because they can reduce light penetration (and consequently plant growth), smother hard surfaces, and fill interstices within the substrate (Wiederholm 1984). QR03 Benthos: Non-impacted compared to watershed reference; Non-impacted compared to upstream reference Habitat: 79% comparable to watershed reference; 68% compared to upstream reference Depite the non-impacted bioassessment received by the QR03 macroinvertebrate community, serious habitat degradation continues to threaten biological integrity in this portion of the Quinebaug River. The greatest threat to the resident benthic community at QR03 may be instream sedimentation. Sand and other fine sediments drastically reduce macroinvertebrate microhabitat by filling the interstitial spaces of epifaunal substrates. In addition, the filling of pools with sediment reduces fish cover and may be detrimental to fish egg incubation and survival. While it may be difficult to eliminate or isolate some sources of sedimentation and other forms of urban runoff (stormwater, road/parking lot runoff, riparian disturbances) that threaten habitat and biological quality at QR03, streambank stabilization and restoration of an adequate riparian buffer may help to alleviate the effects of some nonpoint source inputs to this portion of the river. In addition to sediments, much anthropogenic debris exists throughout the sampling reach, further compromising habitat and threatening water quality here. A stream clean-up effort would greatly improve the aesthetic nature of this segment of the Quinebaug River. It is unclear whether upstream water withdrawals are directly responsible for the low base-flow observed at QR03 during the 1999 biosurvey. Additional water quantity information, including a flow duration curve, should be developed for this stream to better assess the relationship between biological integrity and streamflow. Biomonitoring is recommended during the next MA DEP French & Quinebaug River watersheds survey in 2004, particularly if measures are taken before then to address the habitat constraints (e.g., sedimentation, trash) documented here. Fish population sampling should accompany the macroinvertebrate sampling effort. QR04U Benthos: Slightly impacted compared to watershed reference; Upstream reference condition Habitat: 94% comparable to watershed reference Highly productive waterbodies upstream, as well as various nonpoint source-related nutrient/organic loadings to the Quinebaug River, appear most responsible for biological impairment and suspect water quality at QR04U. In addition, instream deposits of fine organic (FPOM) materials threaten habitat quality and biological potential here. Despite the slightly impacted assessment here, however, it is possible that biological integrity has improved since the 1994 MA DEP biosurvey. The removal of the American Optical wastewater discharge has probably contributed to these improvements. BMPs (e.g., silt screen fences, haybales) may help to alleviate potential impacts from nearstream excavation and construction activities associated with the Southbridge WWTP property. Biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004, especially if QR04U is to be used again as an upstream reference station. Fish population sampling should accompany the macroinvertebrate sampling effort. QR06 Benthos: Slightly impacted compared to watershed reference; Non-impacted compared to upstream reference Habitat: >100% comparable to watershed reference; >100% comparable to upstream reference The excellent habitat evaluations relative to both reference stations suggest that water quality rather than habitat quality is most limiting to biological potential in this portion of the Quinebaug River. It would appear from the bioassessments of QR06 that the Southbridge WWTP may have less effect on biological integrity at QR06 than other anthropogenic perturbations farther upstreammost notably NPS pollution inputs associated with urban runoff, and the numerous dams and productive impoundments (though it is possible that productivity in the impoundments immediately upstream from QR06 is exacerbated by the Southbridge WWTP discharge). To continue to monitor the quality of the Southbridge WWTP effluent and any effects it may have on downstream aquatic communities, biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004. Fish population sampling should accompany the macroinvertebrate sampling effort. French River FR14 Benthos: Reference condition for watershed Habitat: Reference condition for watershed Despite FPOM loads originating from productive upstream impoundments, FR14 was thought to represent the least impacted conditions in the French River watershed in terms of habitat quality and the benthic assemblage found there. The dumping of trash in the vicinity of Mill Street along the FR14 sampling reach should be strongly discouraged. A stream clean-up effort to address the deposits of trash currently found there should be encouraged. Biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004, especially if FR14 is to be used again as the French River reference condition. Fish population sampling should accompany the macroinvertebrate sampling effort. FR15 Benthos: Non-impacted compared to watershed/upstream (same) reference Habitat: >100% comparable to watershed/upstream (same) reference Despite the non-impacted bioassessment relative to the reference station (FR14), the extremely low (channel only 25% full of water) base-flow observed here poses a threat to both instream habitat quality and biological potential. While periodic low base-flow at FR15 may be naturally occurring (i.e., there are no known water withdrawals in this watershed), an investigation of water release practices in Texas Pond may be warranted. In addition, the nearstream dumping of trash that is occurring in the backyard of an adjacent residence should be addressed through outreach. To continue to monitor the quality of the Oxford-Rochdale WWTP effluent and any effects it may have on downstream aquatic communities, biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004. Fish population sampling should accompany the macroinvertebrate sampling effort. FR11 Benthos: Non-impacted compared to watershed reference Habitat: >100% comparable to watershed reference Despite the non-impacted bioassessment here, the FR11 benthos assemblage showed signs of community imbalance. Numerous weed-choked impoundments (e.g., Lowes, Robinson, Nipmuck, and McKinstry ponds) (MA DEP 1999), as well as the expansive Webster Lake which discharges immediately upstream from FR11 via Mill Brook, probably collectively contribute to the dense FPOM food resource in this portion of the French River and the resulting (i.e., filter-feeding dominating) macroinvertebrate assemblage found at FR11. In addition to the vast impervious surfaces adjacent to the FR11 sampling reach, other sources may also contribute to the substantial sediment deposits and associated substrate embeddedness observed throughout the FR11 sampling reach. Numerous nearstream sand/gravel operations exist in this portion (i.e., between Oxford and Webster centers) of the French Riversite visits to determine the extent that these facilities may contribute sediment loads to the French River is suggested. A stream clean-up effort would address the instream deposits of trash observed during the biosurvey and greatly improve the aesthetic nature of this segment of the French River. In addition, the nearstream dumping of trash that is occurring in the backyard of an adjacent residence should be addressed through outreach. Biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004, especially if the habitat degradation noted above is addressed through remediation and/or outreach efforts. Fish population sampling should accompany the macroinvertebrate sampling effort. FR17 Benthos: Non-impacted compared to watershed reference; Upstream reference condition Habitat: >100% comparable to watershed reference; Upstream reference condition Macroinvertebrate community structure and function appear to have improved considerably here since the 1994 biomonitoring survey, though, sand and FPOM deposits threaten habitat quality throughout the FR17 sampling reach. The urbanized nature of this portion of the French River watershed may make it difficult to locate or isolate origins of sedimentationvarious sources of urban runoff in the vicinity of downtown Webster are probably most responsible. Biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004. FR17 should again serve as the upstream reference station for study sites downstream from the Webster-Dudley WWTP. Fish population sampling should accompany the macroinvertebrate sampling effort. FR18 Benthos: Non-impacted compared to watershed reference; Non-impacted compared to upstream reference Habitat: >100% comparable to watershed reference; >100% comparable to upstream reference Results of upstream/downstream community comparisons suggest that water quality conditions upstream (especially those relating to impoundment effects and/or urban runoff associated with downtown Webster) from the Webster-Dudley WWTP discharge rather than the discharge itself probably most-influence biological integrity at FR18. Sand deposition and trash threaten habitat potential at FR18. Origins of trash are unknown, while sand inputs may originate from upstream sand/gravel operations in the western portion of Dudleypossibly warranting site visits to these facilities. Several habitat parameters scored poorly as a result of low base-flowit is unclear whether flow reductions are naturally occurring or a result of the pumping station located just upstream from FR18 in the Perryville section of town. To continue to monitor the quality of the Webster-Dudley WWTP effluent and any effects it may have on downstream aquatic communities, biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004. Fish population sampling should accompany the macroinvertebrate sampling effort. Cady Brook CA04 Benthos: Upstream reference condition Habitat: Upstream reference condition That water quality monitoring conducted here by DWM in 1999 found generally good water quality suggests that more than likely it is flow-related instream habitat constraints, rather than water quality constraints, that limit biological potential at CA04. Efforts to minimize impacts to biological communities within this segment of Cady Brook should be pursued through flow-related operational BMPs by the town of Charlton. It is imperative that minimum base-flows be maintained here to support aquatic life. The complete closure of the Glen Echo Lake outlet structure during summer months is ill-advised, as it will not only impact a potentially viable benthic and fish community at CA04, but also affect the assimilative capacity of Cady Brook downstream from the Charlton WWTP. Biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004. Fish population sampling should accompany the macroinvertebrate sampling effort. CA06 Benthos: Slightly impacted compared to upstream reference Habitat: 79% comparable to upstream reference Biological integrity may have improved here since the 1994 biosurveypossibly a result of upgrades to the Chalton WWTP discharge in 1997. However, the effects of organic enrichment and nutrient loadings in this portion of Cady Brook continue to influence benthic community structure and function. Water quality analytes recorded by DWM here during a 1999 August survey corroborate the discharge-related water quality effects reflected in the resident biota at CA04. Low base-flowpresumably resulting from flow regulation at Glen Echo Lake and probably exacerbated by a near-record dry summerresulted in somewhat impaired instream habitat quality here during the biosurvey. Permitting authorities should also recognize that the available instream dilution in this portion of Cady Brook will be greatly reduced if summer closure of the Glen Echo Lake outlet structure continues. Riparian disruption (sand piles, adjacent parking lot), bank erosion, and an adjacent golf course all offer potential NPS pollution inputs to the CA06 sampling reach. Trash removal, streambank stabilization, and restoration of an adequate riparian buffer would lessen potential impacts to habitat and biological quality in this portion of Cady Brook. To continue to monitor the quality of the Charlton WWTP effluent and any effects discharge increases may have on downstream aquatic communities, biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004. Fish population sampling should accompany the macroinvertebrate sampling effort. CA10A Benthos: Non-impacted (September benthos sample) compared to upstream reference; Non-impacted (August benthos sample) compared to Town Meadow Brook reference Habitat: >100% comparable to upstream reference; 95% comparable to Town Meadow Brook reference It is likely that improvements in both habitat and water quality are jointly responsible for the apparent recovery of biological integrity at CA10A as reflected in the resident benthos found here. It appears that the enrichment effects observed farther upstream at CA06 have diminished this far downstream from the Charlton WWTP discharge. Sand deposition impacts instream habitat quality here. Origins of sediment inputs should be investigated. Potential sources are Route 169 runoff and inputs entering Cady Brook from Sibley Brookwhich receives runoff from the Massachusetts Turnpike and its service facilities. Sibley Brook may also be the source of observed turbidity at CA10A, as this tributary to Cady Brook drains Sibley Pond which is on the 303(d) list for turbidity (MA DEP 1999). To continue to monitor the quality of the Charlton WWTP effluent and any effects discharge increases may have on downstream aquatic communities, biomonitoring is recommended here during the next MA DEP French & Quinebaug River watersheds survey in 2004. Fish population sampling should accompany the macroinvertebrate sampling effort. Town Meadow Brook MB11 Benthos: Upstream reference condition for Town Meadow Brook; Reference condition for CA10A (August benthos sample) Habitat: Upstream reference condition for Town Meadow Brook; Reference condition for CA10A (August habitat) A diverse benthos assemblage with well-balanced trophic structure indicated good biological health in this portion of Town Meadow Brook. In addition, the high quality instream and riparian habitat observed at MB11 corroborates its status as a reference station. MB12 Benthos: Non-impacted compared to upstream reference Habitat: 71% comparable to upstream reference Habitat degradationmost notably NPS inputs and other riparian disruption along the east bankprobably poses a greater threat to biological potential at MB12 than discharge-related water quality effects. Outreach efforts are recommended to educate abutting landowners on how improper yard waste and trash disposal can impact aquatic life in their own back yard, as well as the importance of maintaining a riparian buffer zone. In addition, local clean-up efforts to remove instream trash and debris should be encouraged. LITERATURE CITED Barbour, M. T., J. B. Stribling, and J. R. Carr. 1995. The multimetric approach for establishing biocriteria and measuring biological condition. pp. 63-80. in W. S. Davis and T. P. Simon (eds.). Biological Assessment and Criteria: Tools for Water Resource Planning and Decision Making. Lewis Publishers, Boca Raton, FL. 415 p. Barbour, M. T., J. Gerritsen, B. D. Snyder, and J. B. Stribling. 1999. Rapid Bioassessment Protocols for Use in Streams and Rivers: Periphyton, Benthic Macroinvertebrates, and Fish. Second Edition. EPA 841-B-99-002. Office of Water, US Environmental Protection Agency, Washington, DC. 151 p. + appendices Fiorentino, J.F. 1999. CN 7.0 Quality Assurance Project Plan for 1999 Benthic Macroinvertebrate Biomonitoring. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. 24 p. Hartman, Elaine M. 2001. Cady Brook, Quinebaug River 1999 Water Quality and Wastewater Discharge Data. Massachusetts Department of Environmental Protection, Division of Watershed Management. Report No. 42-AB-4. Worcester, MA. 47 p. Hilsenhoff, W. L. 1982. Using a Biotic Index to Evaluate Water Quality in Streams. Technical Bulletin No. 132. Department of Natural Resources, Madison, WI. Hughes, R. M. 1989. Ecoregional Biological Criteria. Water Quality Standards for 21st Century. 147-151. Karr, J. R., K. D. Fausch, P. L. Angermeier, P. R. Yant, and I. J. Schlosser. 1986. Assessing Biological Integrity in Running Waters: A Method and Its Rationale. Special Publication 5. Illinois Natural History Survey. Champaign, IL. 28 p. MA DEP. 1990. 1989 Lower Quinebaug River. Water Quality Data, Wastewater Discharge Data, and Water Quality Analysis. Department of Environmental Protection. Division of Water Pollution Control. Westborough, MA. 45 p. MA DEP. 1999. Massachusetts Section 303(d) List of Waters 1998. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. 129 p. MA DEQE. 1988. French River Basin 1987. Water Quality Data, Wastewater Discharge Data, and Water Quality Analysis. Department of Environmental Quality Engineering. Division of Water Pollution Control. Westborough, MA. 79 p. Merritt, R. W., K. W. Cummins, and T. M. Burton. 1984. The role of aquatic insects in the processing and cycling of nutrients. pp. 134-163. in V. H. Resh and D. M. Rosenberg (eds.). The Ecology of Aquatic Insects. Praeger Publishers, New York, NY. 625 p. Minshall, G. W. 1984. Aquatic insect-substratum relationships. pp. 358-400 in V. H. Resh and D. M. Rosenberg (eds.). The Ecology of Aquatic Insects. Praeger Publishers, New York, NY. 625 p. Nuzzo, R. 1999. Standard Operating Procedures (Working Draft): Water Quality Monitoring in Streams Using Aquatic Macroinvertebrates. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. 8 p. Resh, V. H. 1988. Variability, accuracy, and taxonomic costs of rapid bioassessment approaches in benthic biomonitoring. Presented at the 36th annual North American Benthological Society meeting at Tuscaloosa, Alabama, 17-20 May 1988. Szal, Gerald M. 1999. 1994 French and Quinebaug Macroinvertebrate Survey. Massachusetts Department of Environmental Protection, Division of Watershed Management. Worcester, MA. 22 p. + appendix. US EPA. 1995. Generic Quality Assurance Project Plan Guidance for Programs Using Community Level Biological Assessment in Wadeable Streams and Rivers. U.S. Environmental Protection Agency, Office of Water. 71 p. Wetzel, R. G. 1975. Limnology. W. B. Saunders Co., Philadelphia, PA. 743 p. Wiederholm, T. 1984. Responses of aquatic insects to environmental pollution. pp. 508-557. in V. H. Resh and D. M. Rosenberg (eds.). The Ecology of Aquatic Insects. Praeger Publishers, New York, NY. 625 p. APPENDIX Macroinvertebrate taxa list, RBPIII analyses, and Habitat evaluations Table A1. Species-level taxa list and counts, functional feeding groups (FG), and tolerance values (TV) for macroinvertebrates collected from stream sites during the French & Quinebaug River watersheds survey between 17 August and 23 September 1999. Refer to Table 1 for a complete listing and description of sampling stations. Taxon FG1TV2CA04CA06 CA10A3CA10A4FR11FR14FR15FR17FR18MB11MB12QR00QR01BQR01CQR03QR04UQR06QR0BHydrobiidaeSC822Amnicola limosaSC542Valvata piscinalisSC82Ferrissia sp.SC6611Physa sp.GC9231PlanorbidaeSC612Gyraulus sp.SC87Gyraulus parvusSC82Helisoma sp.SC62Pisidium sp.FC63236233458121432LumbricinaGC81Nais communisGC81Pristinella osborniGC101Tubificidae IWBGC1012Eclipidrilus sp.GC51Lumbriculus variegatusGC51231112ErpobdellidaePR811Caecidotea communisGC81Crangonyx sp.GC61Hyalella aztecaGC81HydrachnidiaPR61113211BaetidaeGC411313131Acentrella sp.SC41Baetis (2 cerci) sp.GC6191122Baetis (3 cerci) sp.GC62123Baetidae (2 cerci)GC62331271Baetidae (3 cerci)GC61421221EphemerellidaeGC1212Ephemerella sp.GC11Eurylophella sp.GC22132Serratella sp.GC2881HeptageniidaeSC441733Epeorus sp.SC012Stenonema sp.SC341891414344445Isonychia sp.GC222181251416LeptophlebiidaeGC213Tricorythodes sp.GC411CalopterygidaePR51Hetaerina sp.PR62CoenagrionidaePR91Argia sp.PR6121PerlidaePR11Acroneuria sp.PR011Paragnetina sp.PR11131131Corydalus sp.PR43112Nigronia sp.PR0121152Micrasema sp.SH22Glossosoma sp.SC032Protoptila sp.SC11HydropsychidaeFC42Cheumatopsyche sp.FC514498114832851859332176Hydropsyche sp.FC432319933Hydropsyche betteni gr.FC63112735737434231927212Hydropsyche morosa gr.FC6523651612966201Macrostemum zebratumFC32231912441114HydroptilidaeGC41Hydroptila sp.GC613Leucotrichia sp.SC6112Ochrotrichia sp.GC411Lepidostoma sp.SH11Oecetis sp.PR55121Apatania sp.SC33154Pycnopsyche sp.SH41Chimarra sp.FC41817513411191083101932Neureclipsis sp.FC711Psychomyia sp.GC21Neophylax sp.SC311Microcylloepus pusillusGC311Optioservus sp.SC4113Optioservus ovalisSC41Optioservus trivittatusSC42Oulimnius latiusculusSC410111Stenelmis sp.SC52573312211711221Stenelmis crenataSC551Ectopria sp.SC511Psephenus herrickiSC4123171621Dicrotendipes sp.GC84Micropsectra polita gr.GC75Microtendipes pedellus gr.FC69121311Microtendipes rydalensis gr.FC62Polypedilum sp.SH611Polypedilum avicepsSH411Polypedilum fallaxSH61Polypedilum flavumSH61221145111Polypedilum trigonumSH61Stenochironomus sp.GC51Micropsectra dives gr.GC73Micropsectra/Tanytarsus sp.FC71Rheotanytarsus sp.FC611Rheotanytarsus distinctissimus gr.FC6121Rheotanytarsus exiguus gr.FC61222941562117Stempellinella sp.GC21Sublettea coffmaniFC4111Tanytarsus sp.FC611712Diamesa sp.GC52216Pagastia sp.GC1153Cardiocladius sp.PR521Cricotopus sp.SH71Cricotopus annulatorSH72Cricotopus bicinctusGC71111Cricotopus vierriensisSH711Cricotopus/Orthocladius sp.GC711Eukiefferiella devonica gr.GC41Nanocladius sp.GC711Orthocladius sp.GC6434Parametriocnemus sp.GC56191Paraphaenocladius sp.GC41Synorthocladius sp.GC61Thienemanniella sp.GC61Tvetenia bavarica gr.GC5221Tvetenia vitracies gr.GC513212Ablabesmyia sp.PR81Conchapelopia sp.PR613652Nilotanypus sp.PR611Pentaneura sp.PR611Thienemannimyia sp.PR65Chelifera sp.PR61Hemerodromia sp.PR63144121SimuliidaeFC62Simulium sp.FC5211Antocha sp.GC3131Dicranota sp.PR31Tipula sp.SH611Total10192105101981021149510210810710295961031001021071 Functional Feeding Group (FG) lists the primary feeding habit of each species and follows the abbreviations: SH-Shredder; GC-Gathering Collector; FC-Filtering Collector; SC-Scraper; PR-Predator. 2 Tolerance Value (TV) is an assigned value used in the calculation of the Biotic Index. Tolerance values range from 0 for organisms very intolerant of organic wastes to 10 for organisms very tolerant. 3 Sampled 20 August 1999 4 Sampled 23 September 1999  Table A2. Summary of RBP III data analysis for macroinvertebrate communities sampled in the Quinebaug River between 17 and 18 August 1999 during the French & Quinebaug River watersheds survey. Shown are the calculated metric values, metric scores (in italics) based on comparability to the reference station (QR0B), and the corresponding assessment designation for each biomonitoring station. STATION #  QR0B QR00 QR01B QR01C QR03 QR04U QR06 STREAM QuinebaugRiver Quinebaug RiverQuinebaug RiverQuinebaug RiverQuinebaug RiverQuinebaug RiverQuinebaug River HABITAT SCORE  162 188 157 190 128 153 173 TAXA RICHNESS  16 6 15 6 29 6 23 6 27 6 24 6 26 6 BIOTIC INDEX  3.77 6 4.32 6 4.57 4 4.98 4 5.16 4 5.10 4 4.82 4 EPT INDEX 9 6 10 6  12 6 9 6 11 6 10 6 16 6 EPT/ CHIRONOMIDAE 11.25 6 15.40 6 4.29 2 5.82 4 3.05 2 5.77 4 5.50 2 SCRAPERS/ FILTERERS 1.28 6 0.25 2 0.28 2 0.14 0 0.50 4 0.13 0 0.17 0 % DOMINANT TAXON 42% 0 23% 4 20% 4 30% 2 18% 6 32% 2 20% 6 COMMUNITY SIMILARITY 100% 6 63% 4 62% 4 60% 4 57% 4 49% 2 53% 4 TOTAL METRIC SCORE 36 34 28 26 32 24 28 % COMPARABILITY TO REFERENCE  100% 94% 78% 72% 89% 67% 78%BIOLOGICAL CONDITION -DEGREE IMPAIRMENT REFERENCE NON-IMPACTED SLIGHTLY IMPACTED SLIGHTLY IMPACTED NON-IMPACTED SLIGHTLY IMPACTED SLIGHTLY IMPACTED Table A3. Summary of RBP III data analysis for macroinvertebrate communities sampled in the Quinebaug River between 17 and 18 August 1999 during the French & Quinebaug River watersheds survey. Shown are the calculated metric values, metric scores (in italics) based on comparability to the upstream reference station, and the corresponding assessment designation for each biomonitoring station. Stations QR00 and QR01B/QR01C/QR03 bracket the Sturbridge WWTP; Stations QR04U and QR06 bracket the Southbridge WWTP. STATION #  QR00 QR01B QR01c QR03 QR04U QR06 STREAM Quinebaug River Quinebaug RiverQuinebaug RiverQuinebaug RiverQuinebaug RiverQuinebaug River HABITAT SCORE  188 157 190 128 153 173 TAXA RICHNESS  15 6 29 6 23 6 27 6 24 6 26 6 BIOTIC INDEX  4.32 6 4.57 6 4.98 6 5.16 4 5.10 6 4.82 6 EPT INDEX  10 6 12 6 9 4 11 6 10 6 16 6 EPT/CHIRONOMIDAE  15.40 6 4.29 2 5.82 2 3.05 0 5.77 6 5.50 6 SCRAPERS/ FILTERERS 0.25 6 0.28 6 0.14 6 0.50 6 0.13 6 0.17 6 % DOMINANT TAXON 23% 4 20% 4 30% 2 18% 6 32% 2 20% 6 COMMUNITY SIMILARITY 100% 6 82% 6 81% 6 80% 6 100% 6 95% 6 TOTAL METRIC SCORE 40 36 32 34 38 42 % COMPARABILITY TO REFERENCE 100% 90% 80% 85% 100% >100%BIOLOGICAL CONDITION -DEGREE IMPAIRMENT REFERENCE NON- IMPACTED SLIGHTLY/ NON-IMPACTED NON- IMPACTED REFERENCE NON- IMPACTED Table A4. Summary of RBP III data analysis for macroinvertebrate communities sampled in the French River between 18 and 19 August 1999 during the French & Quinebaug River watersheds survey. Shown are the calculated metric values, metric scores (in italics) based on comparability to the reference station (FR14), and the corresponding assessment designation for each biomonitoring station. STATION #  FR14 FR15 FR11 FR17 FR18 STREAM  French River French River French River French River French River HABITAT SCORE  131 136 142 151 174 TAXA RICHNESS  21 6 28 6 17 6 19 6 18 6 BIOTIC INDEX  4.97 6 4.78 6 5.04 6 4.99 6 5.45 6 EPT INDEX  11 6 13 6 9 4 11 6 10  6 EPT/CHIRONOMIDAE  18.33 6 1.15 0 84.00 6 Null*  42.00 6 SCRAPERS/FILTERERS  0.14 6 2.05 6 0.12 6 0.37 6 0.48 6 % DOMINANT TAXON  35% 2 19% 6 36% 2 39% 2 42% 0 COMMUNITY SIMILARITY  100% 6 42% 2 68% 6 67% 6 71% 6 TOTAL METRIC SCORE  38 32 36 32 36 % COMPARABILITY TO REFERENCE STATION 100% 84% 95% 100% 95% BIOLOGICAL CONDITION -DEGREE IMPAIRMENT REFERENCE NON- IMPACTED NON- IMPACTED NON- IMPACTED NON- IMPACTED *due to a null value this metric has been eliminated from the FR17 analysis Table A5. Summary of RBP III data analysis for macroinvertebrate communities sampled in the French River between 18 and 19 August 1999 during the French & Quinebaug River watersheds survey. Shown are the calculated metric values, metric scores (in italics) based on comparability to the upstream reference station, and the corresponding assessment designation for each biomonitoring station. Stations FR14 and FR15 bracket the Oxford-Rochdale WWTP; Stations FR17 and FR18 bracket the Webster-Dudley WWTP. STATION #  FR14 FR15 FR17 FR18 STREAM  French River French River French River French River HABITAT SCORE  131 136 151 174 TAXA RICHNESS  21 6 28 6 19 6 18 6 BIOTIC INDEX  4.97 6 4.78 6 4.99 6 5.45 6 EPT INDEX  11 6 13 6 11 6 10  6 EPT/CHIRONOMIDAE  18.33 6 1.15 0 Null*  42.00  SCRAPERS/FILTERERS  0.14 6 2.05 6 0.37 6 0.48 6 % DOMINANT TAXON  35% 2 19% 6 39% 2 42% 0 COMMUNITY SIMILARITY  100% 6 42% 2 100% 6 92% 6 TOTAL METRIC SCORE  38 32 32 30 % COMPARABILITY TO REFERENCE STATION 100% 84% 100% 94% BIOLOGICAL CONDITION -DEGREE IMPAIRMENT REFERENCE NON- IMPACTED REFERENCE NON- IMPACTED *due to a null value this metric has been eliminated from the FR17 analysis Table A6. Summary of RBP III data analysis for macroinvertebrate communities sampled in Cady Brook on 23 September 1999 during the French & Quinebaug River watersheds survey. Shown are the calculated metric values, metric scores (in italics) based on comparability to the upstream reference station (CA04), and the corresponding assessment designation for the test stations (CA06; CA10A). Stations CA04, CA06, and CA10A bracket the Charlton WWTP. STATION #  CA04 CA06 CA10A STREAM  Cady Brook Cady Brook Cady Brook HABITAT SCORE  148 117 155 TAXA RICHNESS  17 6 16 6 20 6 BIOTIC INDEX  4.98 6 5.55 6 4.09  6 EPT INDEX  3 6 2 0 8 6 EPT/CHIRONOMIDAE  1.25 6 5.45 6 2.54 6 SCRAPERS/FILTERERS  1.36 6 0.19 0 0.71 6 % DOMINANT TAXON  25% 4 53% 0 17% 6 COMMUNITY SIMILARITY  100% 6 51% 4 57% 4 TOTAL METRIC SCORE  40 22 40 % COMPARABILITY TO REFERENCE STATION 100% 55% 100% BIOLOGICAL CONDITION -DEGREE IMPAIRMENT REFERENCE SLIGHTLY IMPACTED NON- IMPACTED Table A7. Summary of RBP III data analysis for the macroinvertebrate community sampled in Cady Brook on 20 August 1999 during the French & Quinebaug River watersheds survey. Shown are the calculated metric values, metric scores (in italics) based on comparability to the regional reference station (MB11), and the corresponding assessment designation for the test station. To illustrate temporal variability of metrics between the August and September biosurveys, metric values for the September CA10A benthos are shown in parentheses; however, these metrics have not been scored. STATION #  MB11 CA10A STREAM Town Meadow Brook Cady Brook HABITAT SCORE  163 131 TAXA RICHNESS  23 6 23 (20) 6 BIOTIC INDEX  4.84 6 4.09 (4.09) 6 EPT INDEX  6 6 11 (8) 6 EPT/CHIRONOMIDAE  1.09 6 1.32 (2.54) 6 SCRAPERS/FILTERERS  0.04 6 0.44 (0.71) 6 % DOMINANT TAXON  18% 6 21% (17%) 4 COMMUNITY SIMILARITY  100% 6 87% (79%*) 6 TOTAL METRIC SCORE  42 40 % COMPARABILITY TO REFERENCE STATION 100% 95% BIOLOGICAL CONDITION -DEGREE IMPAIRMENT REFERENCE NON- IMPACTED *resulting similarity when the August CA10A assemblage is compared to the September CA10A assemblage Table A8. Summary of RBP III data analysis for macroinvertebrate communities sampled in Town Meadow Brook on 19 August 1999 during the French & Quinebaug River watersheds survey. Shown are the calculated metric values, metric scores (in italics) based on comparability to the upstream reference station (MB11), and the corresponding assessment designation for the test station (MB12). Stations MB11 and MB12 bracket the Leicester WWTP. STATION #  MB11 MB12 STREAM Town Meadow BrookTown Meadow Brook HABITAT SCORE  163 116 TAXA RICHNESS  23 6 25 6 BIOTIC INDEX  4.84 6 4.89 6 EPT INDEX  6 6 9  6 EPT/CHIRONOMIDAE  1.09 6 1.82 6 SCRAPERS/FILTERERS  0.04 6 0.39 6 % DOMINANT TAXON  18% 6 17% 6 COMMUNITY SIMILARITY  100% 6 79% 6 TOTAL METRIC SCORE  42  42 % COMPARABILITY TO REFERENCE STATION 100% 100% BIOLOGICAL CONDITION -DEGREE IMPAIRMENT REFERENCE NON- IMPACTED Table A9. Habitat assessment summary for macroinvertebrate biomonitoring stations sampled during the 1999 French & Quinebaug River watersheds survey. For parameters #1-7, scores ranging from 16-20 = optimal; 11-15 = suboptimal; 6-10 = marginal; 0-5 = poor. For parameters #8-10, scores ranging from 9-10 = optimal; 6-8 = suboptimal; 3-5 = marginal; 0-2 = poor. Refer to Table 1 for a complete listing and description of sampling stations. STATIONQR0BQR00QR01BQR01CQR03QR04UQR06FR11FR14FR15FR17FR18MB11MB12CA04CA06CA10A August/ Sept. HABITAT PARAMETERS Instream substrates/cover and channel morphology (Range is 0-20) INSTREAM COVER 17 20 18 20 13 10 15 16 7 6 12 20 11 11 10 6 15/16 EPIFAUNAL SUBSTRATE 19 20 18 20 18 20 20 18 10 10 18 16 11 10 18 17 17/19 EMBEDDEDNESS  17 18 18 19 16 10 17 12 18 17 9 13 16 15 15 15 8/ 15 CHANNEL ALTERATION 15 15 15 17 12 19 20 12 11 11 20 20 20 10 17 18 18/20 SEDIMENT DEPOSITION 15 19 11 19 7 14 17 12 18 19 12 13 18 16 17 11 8/ 13VELOCITY- DEPTH COMBINATIONS 11 20 17 20 13 15 9 16 7 7 13 15 9 8 10 10 9/ 10 CHANNEL FLOW STATUS 10 16 17 18 8 17 16 8 7 6 14 18 19 7 15 8 9/ 15 HABITAT PARAMETERS Riparian and bank structure (Range is 0-10 for each bank)BANK VEGETATIVE PROTECTION 10 19 10 10 10 5 10 9 7 10 10 10 10 10 8 10 9 10 10 10 10 10 10 10 10 10 3 10 10 10 9 8 9/9 9/9 BANK STABILITY  10 10 10 10 7 6 10 10 7 10 10 10 10 9 9 8 7 8 10 10 3 10 9 10 10 10 7 7 7 10 7 4 8/8 4/6RIPARIAN VEGETATIVE ZONE WIDTH 10 8 10 10 7 8 10 8 1 6 4 4 10 10 5 8 10 9 10 10 10 10 10 10 10 9 2 10 4 5 3 1 9/6 8/9 TOTAL SCORE 162 188 157 190 128 153 173 142 131 136 151 174 163 116 148 117 131/155 APPENDIX D SUMMARY OF NPDES and WMA PERMITTING INFORMATION, FRENCH & QUINEBAUG RIVER BASINS Table D1. French & Quinebaug River Basins Municipal Surface Wastewater Discharges. All of these facilities are advanced wastewater treatment plants that require phosphorus removal between the months of April and October (total phosphorus monthly average limits of 1.0 mg/L). PermiteeNPDES #IssuanceFlow (MGD)Dilution Factor*Special Conditions/ notesReceiving Water (segment)Charlton WWTP, CharltonMA010114119960.321.25:1seeking to increase flow to 0.45 MG, see note belowCady Brook (MA41-06)Leicester Water Supply, LeicesterMA010179619960.352.6:1see note belowunnamed tributary of Town Meadow Brook (MA42-02)Oxford Rochdale Sewer, RochdaleMA010017019960.55.9:1see note belowFrench River (MA42-03)Southbridge WWTP, SouthbridgeMA010090120003.773.17:1Up to 2.5 MGD of effluent to Millenium Power Plant in Charlton, IPP*** required, see note belowQuinebaug River (MA41-03)Sturbridge WPCF, SturbridgeMA010042120020.756.9:1New permit includes a requirement for a phosphorus loading, evaluation and reduction programQuinebaug River (MA41-02)Webster/Dudley WWTP, WebsterMA010043920006.02.7:1Dechlorination, waste load allocation model to be re-run, IPP requried French River (MA42-06)Dilution factor * = Qe +Qr/Qe where Qe is the average monthly effluent flow and Qr is the estimated 7Q10 of receiving stream IPP** = industrial pretreatment program Note: permit includes a requirement for a phosphorus loading, evaluation and reduction program as described below: Within twelve months of the issuance of the permit, the permittee shall implement a phosphorus monitoring program and complete a loading analysis sufficient to characterize loadings into the facility as well as loadings to the Quinebaug River; the evaluation shall be such that variations in loadings can be determined with a high degree of confidence; the results of this analysis should be submitted to the permit authorities within three months of the completion of the study. Within twenty-four months of the issuance of the permit, the permittee shall develop an optimization plan to provide maximum removal of phosphorus with the current facility with possible alterations to treatment techniques (e.g. multiple dosing points for metal salt injections), and shall develop a program to minimize influent phosphorus loads. The plan should be submitted to the regulatory agencies within three months of completion and implemented during the remaining time period of the permit. Table D2. French & Quinebaug River Basins industrial NPDES wastewater discharge facilities. PermiteeNPDES #IssuanceFlow (MGD)Types of DischargeReceiving Water (segment)American Optical Corp., SouthbridgeMA00033611990Note: Facility decommissioned 2001/2002Quinbaug River (MA41-03)American Optical Cogeneration, Southbridge MA0033677 12/09/94Note: Facility decommissioned 2001/2002Quinebaug River (MA41-09)American Polymers, Oxford*MA002905019990.8CCW and NCCWLittle River (MA42-09)Bay Path Reg. Voc. High School, CharltonMA002639519930.0036 lagoon overflow, facility is to be tied-into Charlton WWTPUnnamed Swamp (see information in MA41-06)Mass Turnpike Service Station, Charlton- Area 6WMA00223571996Note: facility recently decommissioned, no longer discharges to pond, will be tied into Charlton WWTPPikes Pond (MA42044)Sturbridge Isle Realty, SturbridgeMA00298581994EPA recently determined no permit is required for this facilityHamant PondHyde Manufacturing Company, Southbridge*MA000165119740.07Cooling water (CWW or NCCW?)Cohassee Brook - a trib to Quinbaug River (MA41-09)Masonic Home Inc., CharltonMA002517819960.022 has agreement with the Charlton WWTP to tie in 0.03 MGD but would like increase to 0.1 MGD Unnamed trib to Quinebuag River (MA41-03)Mass Turnpike Auth. SA5E, CharltonMA00229511994Note: facility recently tied into Charlton WWTP, no longer discharges to pondSibley Pond [South Basin] (MA41048)Worcester Tool and Stamping, RochdaleMA00021511989Note: facility no longer discharges, permit is inactiveFrench River (MA42-03)Lucent Technologies, SturbridgeMAG2500032000NCCW - facility installed a closed-loop cooling system in July 2001Unnamed trib to Hobbs Brook (see MA41-02)Bethlehem Steel Corp., WebsterMA0034924Application for NPDES permit; is an emergency exclusion for petroleum cleanupMass Turnpike Serv. Station, CharltonMA0036757Application for NPDES permit; is an emergency exclusion for petroleum cleanupExxon Serv. Station #3-5943, CharltonMA0036757Application for NPDES permit; is an emergency exclusion for petroleum cleanupBrimfield Sunoco-Gas station, BrimfieldMA0032352Application for NPDES permit; is an emergency exclusion for petroleum cleanup*permit will be reissued in 2002 CCW = contact cooling water NCCW = non-contact cooling water Table D3. List of WMA registered and permitted average annual water withdrawals in the French and Quinebaug River Basins (LeVangie, D. 2001. Water Management Act Database. Massachusetts Department of Environmental Protection, Bureau of Resource Protection, Database Manager. Boston, MA.). PermitRegistrationPWSIDSystem NameRegistered Volume (MGD)20 Year Permitted Volume (MGD)SourceG or SWell/Source NameWithdrawal Location (segment)Quinebaug River Basin9P220927801Millennium Power Partners, L.P.2.5Millenium-SW1Southbridge (MA41-09)209278012278000Southbridge Water Department20278-04SSCohasset BrookSouthbridge (MA41-09)209278012278000Southbridge Water Department20278-03SSHatchet BrookSouthbridge (MA41-02)209278012278000Southbridge Water Department20278-02SSHatchet Brook Reservoir 4Southbridge (MA41-02)209278012278000Southbridge Water Department20278-01SSHatchet Brook Reservoir 3Southbridge (MA41-02)20927802American Optical Corporation7.950SQuinebaug River*Southbridge (MA41-09)9P220928701209287012287000Sturbridge Water Department0.690.43287-01GGWell #1Sturbridge (MA41-01)9P220928701209287012287000Sturbridge Water Department0.690.43287-02GWell #2Sturbridge (MA41-01)9P220928701209287012287000Sturbridge Water Department0.690.43287-03GWell #3Sturbridge (MA41-01)French River Basin9P2100800121008001208000Dudley Water Department1.030.122080000-05GGWell #5Dudley (MA42-06)9P2100800121008001208000Dudley Water Department1.030.122080000-04GWell #4Dudley (MA42-05)9P2100800121008001208000Dudley Water Department1.030.122080000-03GGWell #3Dudley (MA42-05)9P2100800121008001208000Dudley Water Department1.030.122080000-01GGWell #1Dudley (MA42-05)9P2100800121008001208000Dudley Water Department1.030.122080000-06GGNew Boston Rd. WellDudley (MA42-05)210151012151001Cherry Valley & Rochdale Water Dis0.270151A01SSHenshaw PondLeicester (MA42-03)210226012226000Mass American Water Co.- Oxford0.780226-01GGWell #1 North Main StreetOxford (MA42-11)210226012226000Mass American Water Co.- Oxford0.780226-03GGWell #3 Nelson StreetOxford (MA42-04)210226012226000Mass American Water Co.- Oxford0.780226-02GGWell #2 North Main StreetOxford (MA42-11)21031602Cranston Print Works - Webster Div.0.80SWebster LakeWebster (MA42-10)Table D3. Continued. List of WMA registered and permitted average annual water withdrawals in the French and Quinebaug River Basins (LeVangie, D. 2001. Water Management Act Database. Massachusetts Department of Environmental Protection, Bureau of Resource Protection, Database Manager. Boston, MA.). PermitRegistrationPWSIDSystem NameRegistered Volume (MGD)20 Year Permitted Volume (MGD)SourceG or SWell/Source NameWithdrawal Location (segment)210316032316000Webster DPW-Water Division1.340316-03GGStation #3Webster (MA42-10)210316032316000Webster DPW-Water Division1.340Station #2Webster (MA42-10)210316032316000Webster DPW-Water Division1.340Pumping Station #1Webster (MA42-10)G ground water, S surface water * American Optical Corporation WMA registration states 2 surface water intakes from the Quinebaug River actual withdrawal locations not documented. APPENDIX E - MA DEP GRANT AND LOAN PROGRAMS Excerpted from MA DEP/DWM World Wide Web site  HYPERLINK http://www.state.ma.us/dep/brp/wm/wmpubs.htm#other http://www.state.ma.us/dep/brp/wm/wmpubs.htm#other. Grant and Loan Programs - Opportunities for Watershed Planning and Implementation and projects specific to the French & Quinebaug River Basins. Specific project reports can be found at MA DEPs web site  HYPERLINK "http://www.state.ma.us/dep/brp/wm/wmpubs.htm#nps" http://www.state.ma.us/dep/brp/wm/wmpubs.htm#nps. 104(b)(3) WETLANDS AND WATER QUALITY GRANT PROGRAM This Grant Program is authorized under Wetlands and Clean Water Act Section 104(b)(3) of the federal Clean Water Act. The Water Quality proposals received by MA DEP under this National Environmental Performance Partnership Agreement (NEPPA) with the U.S. Environmental Protection Agency is a results oriented approach that will focus attention on environmental protection goals and the efforts to achieve them. The goals of the NEPPA are to: 1) achieve clean air, 2) achieve clean water, 3) protect wetlands, 4) reduce waste generation, and 5) clean up waste sites. 97-09/104 Project on Numeric Biocriteria. This proposal is designed to address two issues relating to the current Biocriteria Pilot Study; specifically, to evaluate subecoregion difference in stream biota, if any, and formulate the biological indicators (fish and macroinvertebrates) that are essential to assess conditions and monitor changes in streams. Study expects to establish reference streams in 5 of the 13 Massachusetts Ecological Subregions. The study streams are located in the Connecticut, Westfield, Chicopee, Millers and Quinebaug River Basins. Numeric Biocriteria sampling in the Quinebaug River Basin. Subecoregion = Lower Worcester Plateau/Eastern Connecticut Upland: Candidate Reference StreamStationBenthic MacroinvertebrateFish Population In-situ Hydrolab( MeasurementsDelphi BrookLW03DEL14 September 199816 September 199816 September 1998Browns BrookLW02BRN14 September 199816 September 199816 September 1998MA DEP DWM. 2001. Open file. Massachusetts Department of Environmental Protection, Division of Watershed Management, Worcester, MA. 319 NONPOINT SOURCE GRANT PROGRAM This grant program is authorized under Section 319 of the CWA for implementation projects that address the prevention, control, and abatement of nonpoint source (NPS) pollution. In order to be considered eligible for funding projects must: implement measures that address the prevention, control, and abatement of NPS pollution; target the major source(s) of nonpoint source pollution within a watershed/subwatershed; have a 40 percent non-federal match of the total project cost (match funds must meet the same eligibility criteria as the federal funds); contain an appropriate method for evaluating the project results; address activities that are identified in the Massachusetts NPS Management Program Plan. 01-22/319 Stormwater Management Plan at the Millyard Marketplace. Impervious parking area around the Millyard Marketplace, which is adjacent to the Quinebaug River, causes flash flooding during storm events. In addition, stormwater runoff from the parking lot contributes non-point source pollution directly into the River. This project focuses on implementing BMPs that will abate the flash flooding at the Marketplace. SOURCE WATER AND TECHNICAL ASSISTANCE/LAND MANAGEMENT GRANT PROGRAM The Source Water Protection Technical Assistance/Land Management Grant Program provides funds to third party technical assistance organizations that assist public water suppliers in protecting local and regional ground and surface drinking water supplies. 99-01/SWT Cherry Valley and Rochdale Source Water Protection Project. This project will design BMPs to mitigate untreated stormwater runoff identified in the Districtss 1997 Non-Point Source Pollution Evaluation and in their Source Water protection Plan. The proposed BMPs will increase runoff detention time to allow for the removal of silts and other materials through settling before release into Henshaw Pond, an important source of drinking water for the district. The proposed structures will include submerged intakes to reduce contaminants. WELLHEAD PROTECTION GRANT PROGRAM The Wellhead Protection Grant Program provides funds to assist public water suppliers in addressing wellhead protection through local projects and education. 99-22/WHP Dudley Wellhead Protection Project. This project will install seven wells for monitoring MTBE and VOCs for the Town of Dudley. Two of the Towns three drinking water wells, providing approximately 65% of the systems water, are threatened by groundwater contamination. Sampling at these wells in 1999 indicted low levels of VOCs at the wells and within the Zone I areas. The Town intends to conduct further field investigations, water quality analysis, and computer modeling to determine the possible extent of the contamination. APPENDIX F SUMMARY OF INSTREAM FLOW STUDIES QUINEBAUG RIVER MASSACHUSETTS AND CONNECTICUT 1999 2001 (Abele 2002) In March 1997 EPA New England, after consultation with Connecticut MA DEP and Millennium Power Partners, identified mitigation measures necessary to ensure compliance of the Millennium Power project in Charlton MA with Connecticuts water quality standards. Phase I of the mitigation measures will develop an implementation plan that best serves the needs of the aquatic resources of the Quinebaug River and the aquatic and recreational needs of the East Brimfield Reservoir. Phase I work is divided into two areas: 1) a modeling area, and 2) a mitigation area. The modeling area will be limited to the Quinebaug River watershed upstream of the confluence of the Quinebaug and French Rivers. The mitigation area will include the entire Quinebaug River watershed downstream to the Thames River. For the modeling area, a mathematical watershed hydrology model is being developed to incorporate hydraulic characteristics of the mainstem Quinebaug River, and its tributaries. The model will include hydrological characteristics and operating procedures of storage and water transfer areas within the study area. The various instream flow studies will be used to assess the effects of differing instream flow regimes on representative obligate stream species and life stages. Upon completion of hydrologic modeling, target biological states, and constraints and environmental benefits of water management options will be identified. Subsequently in Phase II EPA, in conjunction with the Management Team, will identify mitigation measures (see Tasks 4A and 4B; e.g., instream flow augmentation, sediment management, passage barrier removal) that are implementable (prudent and feasible). Mitigation measures developed for implementation by the Management Team in Phase II will be prioritized with the following hierarchy: 1) instream flow restoration; 2) instream flow enhancement; 3) habitat and fish passage restoration; 4) habitat restoration; 5) and habitat or fish passage enhancement. Three million dollars is available over ten years for Phase II mitigation measures. OVERVIEW OF MAJOR STUDY TASKS The Scope of Work for Phase I was developed and approved by members of the Management Team in the Fall of 1999. This year Task 3 (Riverine Habitat Studies) was modified to add mesohabitat studies to previously approved instream flow studies. TASK 1. Watershed Hydrology Modeling and Systems Operations/Optimization Modeling The watershed hydrology model will be used to evaluate: (A) the unaffected, unregulated daily stream flow data at locations of interest, and (B) the hydraulic characteristics and operating procedures of various storage and water transfers within the watershed to generate affected or regulated daily stream flow data at the same locations of interest. The Upper Quinebaug has a number of diversions and impoundments. Understanding the role and operation of these is key. Hence, a comprehensive search through local library and corporate records is being used to identify historic withdrawals and diversions, estimate how much water was consumed by evaporative processes and where water was discharged following use. Historically important impoundments are being located , estimates made of the total and active storage capacity of each impoundment, and relationships developed of lake/reservoir stage-surface area, outlet structure stage-discharge relationships and that systems historic operating rules. By statistically analyzing/sampling and then comparing the data sets for each stream flow scenario, the Management Team will be able to predict where, how and to what degree development and construction/operation of the various reservoirs and other water diversions impacted or possibly enhanced the natural stream flow regime of the Quinebaug River. Another component of the model will be employed to allow the Management Team to explore alternative management and operations policies at the various impoundments/diversions located in the watershed, which could support the enhancement and possible restoration of, identified impacted aquatic habitat areas. TASK 2. Assemble Baseline Biological and Habitat Setting Information for the Mitigation Area Historical documents or accounts related to flows, water quality, water usage,fisheries and wildlife and riparian vegetation are being compiled. Information on the current status of habitats, fish, invertebrate, and protected species in the mitigation area will be assembled, and deficiencies identified in the current data that would impede other tasks and enhancement planning. All of this information will be summarized in digital map form. This summer researchers from Cornell, with data and guidance from MA Division of Fisheries and Wildlife, MA DEP and CT DEP, completed the report, Defining a Target Fish Community for Planning and Evaluating Enhancement of the Quinebaug River in Massachusetts and Connecticut. The report covers efforts to develop a model fish community to serve as a target for river enhancements and serve as an endpoint for evaluating program progress. The report is consistent with Clean Water Act goals to restore and maintain the physical, chemical and biological integrity of the Nations Waters. A method is proposed which defines a community of fish that is appropriate for a natural river in southern New England by specifying common members, the balance of abundances, species organization and biological attributes. The target community is combined with a similarity measurement to assess the extent that a sampled community is comparable to that of a natural habitat. TASK 3. Riverine Habitat Modeling At representative river sites within the modeling area researchers are modeling (mesohabitat and IFIM frameworks) physical habitat features and fish community-habitat relationships will be defined to allow the benefits of altered flow regimes and/or physical habitat restoration and enhancement measures to be assessed in both key habitat and key species units. The information will provide a means to justify (anticipated species benefits) and design (flow volumes and timing) flow regimes and/ or physical habitat restoration and enhancement measures which provide biological and water quality enhancement throughout the mitigation area. This year a physical habitat model is being constructed for the reach of the river between the East Brimfield and Thompson Dams based on 4 mesohabitat mapping surveys spanning 0.3-1.0 cfs/mi2 flow. In addition the Ware River was selected as a reference river and surveys were repeated there at a single flow to define desired/ reference mesohabitat template. Next years field work will be used to construct a micro-habitat simulation model (IFIM analysis) following contemporary methods for at least 4 selected sites along the Quinebaug River. The model will be built in a contemporary simulation package using multivariate statistics and topographic sampling. It will be parameterized with field data spanning 0.3-1.0 cfs/mi2 flow. The PHABSIM model can be established on sub-set of cross-sections. To support the mesohabitat scale analyses, a series of habitats, including each mesohabitat type, will be sampled for all fish occupants. The results will be used to define mesohabitat suitability criteria for fish support. Mesohabitat sampling will be conducted with mobile electrofishing equipment and all collected species will be recorded. With the resulting data, whole-river estimates of usable habitat area and habitat quality can be generated for single species, assemblages, and the whole river fish community. TASK 4. Select and Specify Restoration/ Enhancement Options The fourth part of Phase I will synthesize the information gathered in Tasks 1, 2 and 3 to perform a multi-objective systems operation/optimization analysis. In this task, these recommendations would be developed for detailed technical evaluation and implementation in Phase II. The feasibility of restoring or enhancing instream flow and related habitat values will be investigated. A systems analysis study will provide the Management Team with specific, alternative recommendations to achieve instream flow management goals while preserving ecological and recreational resources of upstream impoundments by simulating the operation of various impoundments as a system. A list of feasible and promising flow enhancements and physical habitat restoration and enhancement measures will be developed throughout the mitigation area. Flow enhancements could include: increased low flows, stabilized fluctuations, and possibly others. Other simultaneous objectives might also include maintaining stream flow rates and depth characteristics and wetlands hydrology at target locations, maintaining recreational lake levels and existing registered and permitted withdrawals for public and industrial water supply. Physical habitat restoration and enhancement could include: dam removal, fish passage improvements, channel restructuring, sediment control, retention structure modifications. With each option, the area of habitats to be gained and the fish and invertebrate community to be increased would be calculated. Associated environmental and socioeconomic benefits and impacts of any proposed modifications would be analyzed. TASK 5. Final Products Task 5 is the preparation of a final implementation plan to make improvements to the Quinebaug River to restore or enhance aquatic resources. The plan will provide supporting documents/modeling results used to develop the implementation plan, summarize the findings and present recommendations and impacts to aquatic and recreational resources from various recommendations. Reference Abele, Ralph. (Abele.Ralph@epamail.epa.gov). 2002. Summary of the Quinebaug River Flow Studies. U.S. EPA. E-mail to Theresa Beaudoin at Massachusetts Department of Environmental Protection dated 4 February 2002. APPENDIX G Technical Memorandum FRENCH AND QUINEBAUG RIVERS - PERIPHYTON SURVEY RESULTS 1999 By Joan Beskenis MA DEP Division of Watershed Management February 2002 Table of Contents FRENCH AND QUINEBAUG RIVERS-PERIPHYTON SURVEY RESULTS 1999 Page INTRODUCTION G 3 MATERIALS AND METHODS G 3 Periphyton Identifications and Relative Abundance G 3 Periphyton Biomass G 4 RESULTS G 5 Quinebaug River: Algal Identification and Abundance G 6 Quinebaug River: Cady Brook-Algal Identification and Abundance G 7 French River: Algal Identification and Abundance G 7 Quinebaug River: Cady Brook-Algal Biomass G 8 DISCUSSION G 9 Algal Identification and Abundance G 9 REFERENCES CITED G11 APPENDIX A G12 FRENCH AND QUINEBAUG RIVERS-PERIPHYTON SURVEY RESULTS 1999 INTRODUCTION During the summer of 1999, MA DEP personnel collected periphyton samples from stations in the French and Quinebaug River Basins. The objectives of the periphyton sampling were limited in scope since only qualitative sampling was done. The samples were collected in order to learn more about the biota in the streams and rivers, to document problem areas, to offer a means of comparing biological communities in conjunction with the macroinvertebrate and habitat information, to examine community changes and to provide a record of the taxa that are found in Massachusetts. The sampling was conducted as part of the macroinvertebrate/habitat assessment. Samples were typically collected in the riffle zone and were usually from scrapes of one substrate type. Because the sampling design was established for the quantitative, macroinvertebrate investigations, time and personnel constraints meant that the sampling location could not easily be adjusted to meet the needs of the periphyton sampling. If the sampling was done to specifically meet the periphyton objectives, then weighted samples would be collected. Samples would be collected at various habitats-not just in riffles-in proportion to its presence in the reach. The sampling stations included did not all have open canopies and the flow regime was typically limited to the riffle zone, occasionally pools were also sampled. Also, the area included in the algal scrapes is not standardized. The samples collected indicate the presence of particular genera in one habitat. MATERIALS and METHODS Periphyton Identifications and Relative Abundance Periphyton data were gathered along with the macroinvertebrate and habitat data using methods described in Barbour, M. T. (1999). Sampling was done by John Fiorentino or Robert Nuzzo and consisted of randomly scraping rocks and cobble substrates, typically within the riffle area, with a knife and collecting the material in a labeled glass vial. The samples are transported to the lab MA DEP-DWM-Worcester without refrigeration, but once at the lab they are refrigerated until identifications are completed. The vial was shaken to get a uniform sample before subsampling. If filamentous algae comprised most of the sample they were removed first, identified separately and then the remainder of the sample was examined. An Olympus BH2 compound microscope with Nomarski optics was used for the identifications. Slides were typically examined under 200 power. A modified method for periphyton analysis developed by L. Bahls (1993) was used. The scheme developed by Bahls for determining abundance is as follows: R (rare) fewer than one cell per field of view at 200x, on the average; C (common) at least one, but fewer than five cells per field of view; VC (very common) between 5 and 25 cells per field; A (abundant) more than 25 cells per field, but countable; VA (very abundant) number of cells per field too numerous to count. This determination of abundance provides a relative approximation of the phyla that contribute the most to the biomass in the riffle or pool habitats. Information obtained from the algal identifications and relative abundance is combined with information obtained in the habitat assessment, in particular, canopy cover and percent algal cover. Where potential problem areas are found based upon percent algal cover and abundance , these locations are noted. The information can possibly be used by assessment personnel in determination of whether or not the uses of the rivers are impaired, in particular, aesthetics and aquatic life. Table 1 lists the stations that were included in this study and descriptions of their locations. The data is included in Appendix A. Table 1: French and Quinebaug Rivers-1999 Station Numbers and Station DescriptionsQuinebaug RiverQR0BTributary to Quinebaug River, upstream from East Brimfield Rd., Holland, MAQR00Upstream from Holland Rd., Sturbridge, MAQR01BDownstream from Farquhar Rd., SturbridgeQR01CDownstream from Breakneck Brook, Sturbridge, MAQR03Downstream from Mill St., SouthbridgeQR04U120 m upstream from Southbridge WWTP, Southbridge, MAQR06Upstream from Route 197, Quinebaug, CTCA04Cady Brook, 25 m upstream from Charlton WWTP, Charlton, MACA04bCady Brook, approximately 20 m below the Charlton WWTPCA06Cady Brook, 100 m downstream from Charlton WWTP, Charlton, MA French RiverMB11Town Meadow Brook, upstream from Leicester WWTP, Leicester, MA MB12Town Meadow Brook, upstream from Pine St., Leicester, MAFR14Upstream from Route 56, adjacent to Mill St., Oxford, MAFR15Upstream from Route 56, Oxford, MAFR11Upstream from Oxford Ave., Webster, MAFR17Downstream from Hill St., Webster, MA FR18Upstream from Langers Pond, Thompson, CT Periphyton Biomass Additional work was done at Cady Brook, a tributary to the Quinebaug River to learn more about algal production especially below the Charlton Wastewater Treatment Plant. Artificial substrates were deployed and analyzed in the laboratory by Joan Beskenis with the assistance of seasonal personnel Mathew Klansek and Brian Connors. Glass slides were deployed for a period of approximately three weeks in stream. The slides were held vertically in a wooden tray which was attached to a cinder block with nylon twine. The periphyton samplers were deployed in water of at least 0.25 m depth. Samplers were placed in comparable light regimes. When the samplers were retrieved they were removed from the cinder blocks and placed in plastic bags and kept in an iced cooler for transport back to the Worcester offices of MA DEP. The two outside slides from the periphyton samplers were discarded. Four slides from each container were air dried. After air drying the slides were brought to the Wall Experiment Station in Lawrence for the analysis of ash-free mass. Ash-free analysis examines the accumulation rate of organic matter from periphyton, as well as filamentous bacteria, attached protozoa, rotifers (APHA, 1992). Detrital material and captured planktonic material may also be on the slides. Three slides were used as replicates and were scraped using a razor blade into pre-cleaned and pre-weighed china crucibles. The last slide was kept as an archive sample. The crucibles were dried to a constant weight at 105 (C for 1 hour in a drying oven, allowed to cool to room temperature in the dessicator then weighed. A few drops of water were added to the crucibles and ignited at 500 (C for 1 hour. The ash residue was re-wetted with deionized water and again dried to a constant weight at 105 (C. The final weight was then recorded. This information gives you ashfree dry mass (AFDM). Productivity was calculated as: P= mg ash-free weight/slide tA P=net productivity, mg ash-free weight/m2/day t=exposure time, days, and A=area of a slide, m2. The initial sampling was performed in July; the samplers were re-deployed at some of the same locations in August. This re-deployment was to determine net production by examining the gain in ash-free dry mass. Unfortunately, the lack of precipitation and manipulation of a dam upstream led to reduced stream flow during the exposure periods and contributed to exposed substrates. This resulted in loss of data so the net gain in production cannot be calculated for those stations. However, data from Cady Brook can be compared to other streams and rivers that have been sampled in the same way. Also, the AFDM values can be compared to those in the scale described in Biggs 1996, Barbour 1999. These data are included in Table 4. Table 2 lists stations Included in the biomass (weight/area) study. Table 2: French River-Cady Brook-1999 Station Locations for Periphyton BiomassStation numberStation DescriptionMonth sampledCA03Upstream Route 20, CharltonJulyCA04Approximately 25 m upstream of the Charlton WWTP, CharltonAugustCA04bApproximately 20 m downstream of the Charlton WWTP, CharltonJulyCA06Approximately 100 m downstream from Charlton WWTP, CharltonJuly, AugustCA10uUpstream Snake Hill Rd., CharltonAugustCA16Upstream Brookside Rd., SouthbridgeAugust RESULTS Following are some comments regarding the periphyton communities identified from riffle sampling at stations along the French and Quinebaug Rivers. Table 3 contains canopy cover, percent algal cover and dominant algal types for stations in these two basins. Appendix A is a list of the taxa that were found at the different stations and a listing of abundance. Table 3: French and Quinebaug Rivers: Dominant Alga Type, % Algal Cover, % Canopy Cover 1999 Rapid Bioassessment SurveysQuinebaug RiverFrench RiverStationDominant alga% algal cover% canopy coverStationDominant alga% algal cover% canopy coverQR0BGreen550MB11Blue-Green10100QR00Blue-green570MB12Green1100QR01BGolden brown5050FR14Diatoms/ greens1100QR01CGreens/ diatoms1025FR15Green9010QR03Diatoms515FR11Green600QR04UBlue-green500FR17Green5060QR06Green2580FR18Green2560CA04Diatoms1020CA06Green2515 Quinebaug River: Algal Identifications and Abundance Only two stations in the Quinebaug River basin, of the ones that were sampled, have more than 40% algal cover (table 3) and three in the French River system. This information combined with the type of algae that is dominant (Appendix A) is used to determine if an area is organically enriched and if nuisance aquatic growth is present. Algal cover greater than 40% and composed of macroalgae-usually green filamentous is described as excessive algal growth Biggs (1996) and Barbour (1999). This usually results from elevated nutrient loading, but is also determined by flow regime, grazing pressure and amount of available sunlight. The following stations in the Quinebaug River have elevated alga growth that could threaten use of the segment for aesthetic enjoyment and aquatic life: ( QR01B is located downstream from Farquhar Rd., Sturbridge and is located below the Sturbridge WWTP. The Quinebaug River is approximately 10 m wide at this point and has some potential nonpoint sources including road crossings and possibly from the adjacent horse farm/hayfield. The open canopy and well developed riffle area had algal mats comprised of Phormidium sp. and the diatom Melosira varians (Appendix A). The percent cover was 50%. In the surrounding pools, there were long filaments of the green alga Spirogyra. This station is cited because of high percent algal cover, open canopy and the known point source of nutrients. ( QR04U is located upstream from the Southbridge WWTP, Southbridge in a reach with an open canopy. The riparian landuse is approximately 20 % forested at the top of the reach but 40 % commercial in the lower part of the reach as well as 40 % devoted to the WWTP parking lots and buildings. It was estimated that the algal coverage within the reach was 50 %. The algae included in the riffle on the rock substrate was almost entirely Phormidium sp. although another blue-green algae (cyanobacteria) was also common, Oscillatoria sp. These species of blue-green algae are not macroalgae, and do not develop the biomass of nuisance forms of filamentous algae. The station is cited because of the high percentage of algal cover, the potential sources of non-point source pollution in the vicinity and the open canopy that could provide the necessary sunlight for rapidly growing algal species. Quinebaug River: Cady Brook-Algal Identifications and Abundance Station CA04, above the Charlton WWTP discharge pipe, is located in a stretch of Cady Brook that has a fairly open canopy with approximately 20% canopy cover. Algal coverage within this reach was relatively sparse at approximately 10% (Appendix A). The noted potential sources of nonpoint source pollution are the Charlton WWTP lawn and a road crossing just above the end of the reach. A diatom floc was prevalent in this reach with Melosira sp.and Cymbella sp. being the most abundant genera (Appendix A). One comment on the data sheets is that there were a lot more diatoms present at this station than downstream of the WWTP. The algal community was possibly limited by the wide variations in flow that were observed at Cady Brook, in general. The August 3, 1999 samples at CA04b were collected right below the Charlton WWTP discharge pipe. One was from a sunny, riffle location and the other from a shady, riffle location. The riffles were very shallow, approximately 2.5 cm deep. The sunny riffle was dominated by diatoms, in particular, Cymbella sp. and Navicula sp. The sunny riffle had no algal genera that were present in abundant numbers. They were not abundant in the brown floc that covered the substrates. The green algae present in the upstream samples were no longer present in the riffle samples even in the sunny locations. It was anticipated that the combination of sun and increased nutrients from the WWTP could have led to algal blooms in this area. The algal community at Cady Brook (CA06) 100 m below the Charlton WWTP, Charlton was sampled on August 3 and September 23. The reach is behind the closed Dee Dees Restaurant and is located just down stream of the Charlton Wastewater Treatment Plant. It also receives runoff from non point sources which contribute nutrients and solids to Cady Brook. These include a golf driving range and a parking lot. Algal coverage on September 23 was estimated as covering 25% of the bottom within the sample reach. The substrates, whether in sun or shade, had a brown floc of diatoms present. The riffles under the open canopy had long filaments of the green alga Spirogyra sp. (Appendix A). The riffles were most productive if they were found below the small wooden bridge, in the middle of the reach, and along the banks by the driving range. The sunny riffles above the small wooden bridge had very abundant Spirogyra sp. as well as the floc forming Melosira varians. French River: Algal Identifications and Abundance At the French River basin there were three stations that should be closely observed. ( FR15 is located upstream from Route 56 Oxford on the French River and has an open canopy. Algal cover was described as 90%. There were not many sources of nonpoint source pollution, although some trash dumped along the right bank. Other sources outside of the reach are possibly contributing nutrients since the algal community is very abundant. Both an algal floc of the blue-green cyanobacteria Coelosphaerium sp. (Appendix A) and filamentous algae (Spirogyra sp.) are present. The large extent of the bottom that is covered by algae indicates organic enrichment (Barbour 1999). The invertebrate and fish communities may also be affected by this growth. As break down of the algae contributes organic matter interstitial spaces will clog, this alters what can live in these spaces. ( FR11 is located upstream from Oxford Ave., Webster is a section of the river with an open canopy. The surrounding land use is mixed with 25 % forest, 25 % residential and 50 % commercial. There are potential sources of nonpoint source pollution including: road crossings, a parking lot and yard trash. Algae covered approximately 60 % of the reach with both filamentous forms and algal mats present. The centric diatom Melosira sp. (Appendix A) was very abundant in the algal mat as were the blue-green cyanobacteria: Oscillatoria sp.and Coelosphaerium sp. In the pools, Spirogyra sp.was very abundant. As indicated by the types and percent cover of the algae, this reach of the river may be considered to be aesthetically degraded (Biggs 1996) (Barbour 1999). Also, the amount of organic matter present as live algal biomass may destroy the habitat for interstitial organisms as it breaks down as well as altering the amount of dissolved oxygen that is present. The percent algal coverage of 60% indicates that this area is receiving organic enrichment (Barbour 1999) and this can lead to loss of uses for this waterbody. ( FR17 is located upstream from Hill Rd., Webster and was sampled on August 18, 1999. Aquatic vegetation provided approximately 50 % coverage within the reach and the algae also covered about 50 % within the reach (Appendix A). Some of the algae were present in mats, some on plants and some on the rock substrates. Most abundant was the filamentous green Tetraspora cylindricum that also had abundant epiphytic pennate diatoms. The presence of oil slicks and oily sediments along the margin at the top of the reach may affect the algal community. The centric diatom Melosira sp, is often found in areas of organic enrichment, but it was found only in low densities, other factors, like disturbance, may be suppressing growth. The 50% algal coverage of filamentous greens indicates a location that is organically enriched (Barbour et al 1999). Quinebaug River: Cady Brook Algal Biomass Ash-free dry mass (AFDM) provides a measure of bacteria, fungi, small fauna and detritus in the samples (Barbour et al 1999). The values for AFDM (g AFDM m-2) measured in July 1999 at stations along Cady Brook ranged from 0.03 g AFDM m-2, CA03, n=1 above Rte 20, CA03 to 5.84 g AFDM m-2 at CA06, n=3. The August samples ranged from a high of 2.21 g AFDM m-2 mass to a low of 0.21 g AFDM m-2 upstream of the Charlton Wastewater Treatment Plant. August samples were all based on n=3. Some stations only have one data point in July because of interrupted exposure periods due to falling water levels as well as some laboratory problems.  EMBED Excel.Chart.8 \s  The productivity results and ash-free dry mass results are listed in Table 4. The productivity and ash-free dry mass in Cady Brook is low above the Charlton WWTP, increases immediately below it at CA04b to P= 113.6, 2.61 g AFDM m-2 and continues to increase even more 100 m below the discharge (CA06) to 5.84 g AFDM m-2 ), P=253.9. Productivity dropped by CA10 to 0.56 g AFDM m-2 (AFDM), P=60.2. This is higher than above the Charlton WWTP, indicating some likely influence from the discharge but a significant drop from CA04b. Table 4: Cady Brook, Quinebaug River-Average Ash Free Dry Mass (g AFDM m-2 and Average Productivity (P)( mg ash-free weight/m2/day)-1999 Station number LocationAFDM P CA03Upstream Route 20, Charlton0.031.2CA04Approximately 20 m upstream of the Charlton WWTP, Charlton0.216.9 CA04bApproximately 20 m downstream of the Charlton WWTP, Charlton2.61 113.6 CA06 Approximately 100 m downstream from Charlton WWTP, Charlton5.84 253.9  CA10Upstream Snake Hill Rd., Charlton0.56 60.2 CA16 Upstream Brookside Rd., Southbridge0.13  4.3Other Comparative River LocationsCharles River, below Watertown Dam, Watertown8.39399.6Charles River, Trout Brook@Haven St.Dover0.6625.3North Coastal Basin, Porter River@Rte 62, Danvers5.43.39 DISCUSSION Algal Identifications and Abundance Examination of the percent algal cover as well as the dominant alga type provides some information on where areas of concern are for aesthetic impairment and degradation of the substrates. At the Quinebaug River, percent cover ranged from 5 to 50 %. The two stations with the elevated value i.e., QR01B with the golden brown- Melosira varians and QR04U which was dominated by the blue-green Phormidium sp. Neither of these genera are considered to be nuisance algae which are macroalgal green aglae, so it is not considered that they are threatening the aesthetics of the river system. However, both the Melosira varians and the Phormidium genera are typically found in organically enriched areas (Palmer, 1962). At the French River the percent cover ranged from 1-90%. It appears that based on the algal coverage estimated at the two river systems, the French River appears to be the one that is more organically enriched and may have some areas of the river where aquatic uses are threatened. FR11 with 60 % green algal cover, FR15 with 90 % green algal cover and at FR17 with 50 % green algal cover. At the Quinebaug River, there were no stations recorded as having percentages greater than 40 % green macroalgal cover. Biggs (1996) and Barbour (1999) both use 40 % as the maximum seasonal cover by filamentous algae. Growth in excess of that may affect the recreational usage of streams. However, the biomass that they list as comparable to 40% cover i.e. 50 g AFDM m-2 is significantly higher then is found at these stations (values of 5 g AFDM m-2 and less). It is not believed at this time that benthic habitats have been compromised by the 40% or greater macroalgal cover. But, increases in algal cover and AFDM in the future may have a deleterious effect on the habitats and aesthetics of these areas. The calculation of AFDM provides a way of obtaining information on the amount of organic matter present at a location. The use of artificial substrates has some benefits since the period of deployment is uniform as well as the predation and nutrient concentrations that the slides are exposed to. The negative aspects include the possibility of loss by vandalism, storm or, as was true this summer, drop in water levels which exposed the slides to the air and ruining them for further use. Given the drought conditions during the summer of 1999 some of the data were lost because the slides were exposed with water levels falling rapidly, also in the case of Cady Brook, manipulation of an upstream dam made the stream particularly vulnerable to flow fluctuations. Many factors can affect the development of the algal community and biomass. Chlorophyll a or AFDM can be four to five times higher at open sites than at sites with full tree canopy development. This is particularly true when the grazing pressure is low. Alternatively, when grazing pressure is high biomass may not be correlated with light (Lowe et al., 1986). When a regression was run for the dependent parameter % algal cover with % canopy cover the F value was significant (F=0.0406) and R2 was 0.266. Benthic algal production and the community is also affected by shading from well-developed streamside vegetation (Hill, 1996). Competition for limiting nutrients is important in deciding algal communities, however, stress can also be important. Algae with stature (complex growth forms like the filamentous algae) do better in high resource areas, but those that are tightly attached, even prostrate growth forms do best where disturbance is frequent and scouring also occurs with regularity. Some areas of the Quinebaug River-Cady Brook, particularly above and immediately below the Charlton WWTP discharge, had low productivity and most of the algal production was single celled diatoms. Both above and below the WWTP, water levels dropped so much over a brief period of 24 hours that artificial substrates were unuseable. Disturbance like this was common during the summer of 1999. Some algae can survive on the moist substrates, but others dessicate or lack sufficient nutrients to grow. The algae that were present were predominantly found as a floc of diatoms (Melosira sp.) on the substrates. When rain did occur, Cady Brook appeared to be very flashy which contributes to scouring and loss of some algal species, personal observation J. Beskenis. Lack of light also creates disturbance and may also be contributing to the dominance at most locations within Cady Brook by diatoms. Figure 33 indicates that production was the highest in July and that the peak for both sample periods was CA06 which is located below the Charlton Wastewater Treatment Plant approximately 100 m downstream. Stations located above the WWTP like CA03 and CA04 have average values of 0.03, 0.21 g AFDM m-2, respectively. These values in the Biggs, 1996 scheme for New Zealand streams would be in the unenriched, forested category with a median of <1.5 g AFDM m-2 and the CA06 station values represented in July by the average value of 5.84 g AFDM m-2 would be in the moderately enriched category represented by a median of 4.8 g AFDM m-2 , August production had dropped off for some reason, perhaps stress, to an average of 2.21 g AFDM m-2 . In comparison, a highly nutrient enriched station at the Charles River, below the Watertown Dam in Watertown had an AFDM value of 8.39 g AFDM m-2 in August 1997. Another river which is nutrient enriched is the Porter River at Route 62 in Danvers, North Coastal Basin. This had an AFDW value of 5.42 g AFDM m-2 in August 1997. In contrast, Trout Brook at Haven Street also in the Charles River basin but is not nutrient rich had a AFDM value of 0.65 g AFDM m-2. All of these values were obtained from artificial substrates. REFERENCES CITED American Public Health Assoc. 1992. Standard Methods for the Examination of Water and Wastewater-18 th edition 1992.. American Public Health Assoc. Washington, D. C. Bahls, L. L. 1993. Periphyton Bioassessment Methods for Montana Streams. Water Quality Bureau, Dept. of Health and Environmental Sciences. Helena, Montana. Barbour, M., Gerritsen, J, Synder, B. D. and J. B. Stribling. 1999. Rapid Bioassessment Protocols for Use in Streams and Wadeable Rivers: Periphyton, Benthic Macroinvertebrates and Fish, 2nd edition. EPA 841-B-99-002. U.S. Environmental Protection Agency, Office of Water, Washington, D.C. Biggs, B. J. F. 1996. Patterns of benthic algae in streams. IN Algal Ecology: Freshwater Benthic Ecosystems. R. J. Stevenson, M. Bothwell, and R. L. Lowe. Pp 31-55. Academic Press, San Diego, California. Borchardt, M. A., 1996. Nutrients. IN: Algal Ecology: Freshwater Benthic Ecosystems. Edit. R.J. Stevenson, M. L. Bothwell. R. L. Lowe. Academic Press. New York. Hill, W. 1996. Effects of light. IN: Algal Ecology: Freshwater Benthic Ecosystems. Edit R. J. Stevenson. Academic Press. San Diego.121-148. Lowe, R. L., Golladay, S. W. and Webster, J. R.. 1986. Periphyton response to nutrient manipulation in streams draining clearcut and forested watersheds. J. North Am Benthol. Soc. 5, 221-229. Palmer, C. M. 1962. Algae in Water Supplies. US Dept. of Health, Education and Welfare. Washington D. C. 88 p. Appendix A: PERIPHYTON-FRENCH AND QUINEBAUG RIVERS 1999 Habitat, Algal Identification and Abundance HabitatFamilyGenusAbundanceQUINEBAUG RIVERQR 0B17 Aug. 1999cobble/riffleChlorophyceaeSpirogyravery abundantupstream from East Brimfield Rd., HollandBacillariophyceaeSynedrarareQR0017 Aug. 1999algal matsCyanophyceaeLyngbyarareupstream from Holland Rd., SturbridgeCyanophyceaeOscillatoriacommonFlexibactervery abundantBacillariophyceaeCymbellarareQR01B 20 Aug. 1999cobble, poolChlorophyceaeSpirogyraabundantFarquhar Rd., Sturbridge RhizocloniumrareBacillariophyceaeMelosira varianscommonQR01B20 Aug. 1999cobble, riffle (mat and filamentous)CyanophyceaePhormidiumabundantdownstream from Farquhar Rd., SturbridgeBacillariophyceaeMelosiracommonChrysophyceaeUI chainsvery abundantQR 01Cdwnstream Breakneck Brk, Sturbridge17 Aug. 1999mats on sediment, riffleChlorophyceaeTetrasporacommonBacillariophyceaeMelosira varianscommonQR 01C17 Aug.1999cobble/riffleBacillariophyceaeMelosira variansraredownstream from Breakneck Rd., SturbridgeChlorophyceaeSpirogyrarareQR0317 Aug. 1999cobble/riffleChlorophyceaeMougeotiararedwnstream from Mill St., SouthbridgeSpirogyrarareBacillariophyceaeCymbellararenaviculoidsabundant Appendix A: Continued. PERIPHYTON-FRENCH AND QUINEBAUG RIVERS 1999 Habitat, Algal Identification and Abundance  HabitatFamilyGenusAbundanceQuinebaug R.-QR04U18 Aug. 1999cobble, riffleCyanophyceaePhormidiumvery abundantupstream from Southbridge WWTPOscillatoriacommonQR0618 Aug. 1999cobble, riffle/runBacillariophyceaeMelosira granulat v. angustissima forma spiralis O. Mullrareupstream from Rte 197, Quinebaug, CTChlorophyceaeUI coccoid, crustose, parenchymatouscommonlong chains of filamentous bacteriarareQR0618 Aug. 1999cobble, pool ChlorophyceaeSpirogyravery abundantupstream from Rte 197UlothrixabundantOedogoniumrareBacillariophyceaeMelosiracommonCady Brook-CA0423 Sept. 1999riffle/cobbleBacillariophyceaeMelosiraabundantapprox. 25 m upstream from Charlton WWTPCymbellaabundantTabellariarareNavicularareFragilariarareChlorophyceaeSpirogyraabundantGloeocystisrarePeniumrareRhizocloniumrareCADY BROOK-CA04b03 Aug. 1999shade, riffle BacillariophyceaeCymbellacommonapprox. 20 m below the Charlton WWTPGyrosigmararecommonCyanophyceaeLyngbyacommonChlorophyceaeMougeotiacommon Appendix A: Continued. PERIPHYTON-FRENCH AND QUINEBAUG RIVERS 1999 Habitat, Algal Identification and Abundance  HabitatFamilyGenusAbundanceCADY BROOK-CA06 3 Aug. 1999sunny, riffleBacillariophyceaeMelosira variansvery abundantapprox.100 m below the Charlton WWTPCymbellavery commonPinnulariarareChlorophyceaeSpirogyravery abundantCADY BROOK-CA06 3 Aug. 1999shady, runBacillariophyceaeCymbellacommonapprox.100 m below the Charlton WWTPMelosiracommonCyanophyceaeLyngbyarareChlorophyceaeUlothrixrareVorticellacommonCADY BROOK-CA06 23 Sept. 1999riffle/cobbleChlorophyceaeSpirogyravery abundantapprox.100 m below the Charlton WWTPStigeocloniumrareUlothrixrareBacillariophyceaeMelosira variansrareFRENCH RIVERFR14-upstream from Rte 56, Oxford (adjacent to Mill St.)19 Aug. 1999pool/cobbleChlorophyceaeMougeotiaabundantBacillariophyceaeFragilariaabundantMelosirarareFR 15 upstream from Rte 56, Oxford19 Aug. 1999cobble/riffle/poolChlorophyceaeSpirogyravery abundantCyanophyceaeCoelosphaeriumabundantFR1118 Aug. 1999cobble, poolChlorophyceaeSpirogyravery abundantupstream from Oxford Ave., WebsterMougeotiarareTetrasporacommonBacillariophyceaeSynedrarareCymbellarareMelosirarare Appendix A: Continued. PERIPHYTON-FRENCH AND QUINEBAUG RIVERS 1999 Habitat, Algal Identification and Abundance  HabitatFamilyGenusAbundanceFR1119 Aug. 1999riffleBacillariophyceaeMelosiravery abundantupstream from Oxford Ave., WebsterSynedracommonFragilariacommon FR1119 Aug. 1999algal matBacillariophyceaeMelosiravery abundantupstream from Oxford Ave., WebsterCyanophyceaeOscillatoriavery abundantCoelosphaeriumcommonupstream from Hill St., WebsterUlothrixrareui pennate diatomscommonMelosirarareCyanophyceaeOscillatoriacommonFR 1718 Aug. 1999cobble/riffle/matChlorophyceaeSpirogyravery abundantupstream from Hill St.., WebsterBacillariophyceaeMelosiraabundantSynedracommonFragilariacommonGomphonemarareCymbellarareCocconeisrareFR18-Upstream from Langers Pond, Thompson, Connecticut 18-Aug-99pool, riffleChlorophyceaeHydrodictyonvery abundantTetrasporacommonTown Meadow Brook, MB11 upstream from Leicester WWTP, Leicester19 Aug. 1999cobble/riffleCyanophyceaeLyngbya versicolorabundantTown Meadow Brook-MB12 upstream from Pine St., Leicester19 Aug. 1999cobble/riffleChlorophyceaeSpirogyravery abundantScenedesmusvery abundantSynedravery common See EPA letter dated March 5, 1998 to the Army Corps of Engineers concerning the Millennium Power project. The Management Team in the original permit condition consists of Millennium Power Partners, EPA, Massachusetts MA DEP, Connecticut MA DEP, US Fish and Wildlife Service and the US Army Corps of Engineers. Subsequently, the Massachusetts Division of Fisheries and Wildlife was added to the team. Membership on the team does not in any way preclude state and federal agencies from complying with their obligations under applicable state and federal laws, regulations or policies. Membership on the Management Team does not compel agencies to expend funds which they would not otherwise expend. French & Quinebaug River Watershed 2001 Water Quality Assessment Report  PAGE \* MERGEFORMAT 126 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watershed 2001 Water Quality Assessment Report  PAGE \* MERGEFORMAT 133 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix A A PAGE 3 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix A A PAGE 1 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix A A PAGE 19 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix A A PAGE 15 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix A A PAGE 29 42/41wqar.doc DWM CN 51.0 PAGE  French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B PAGE 8 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B PAGE 1 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B PAGE 35 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B PAGE 17 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B PAGE 23 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B PAGE 44 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B PAGE 39 42/41wqar.doc DWM CN 51.0 PAGE  French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix C C PAGE 30 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix C C PAGE 1 42/41wqar.doc DWM CN 51.0 PAGE  French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix C C PAGE 45 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Basins 2001 Water Quality Assessment Report Appendix F E PAGE 1 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix D D PAGE 2 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix E E PAGE 2 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix F F PAGE 3 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix F F PAGE 1 42/41wqar.doc DWM CN 51.0 PAGE 1 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix G G PAGE 11 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix G G PAGE 1 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix G G15 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix G G13 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix G G14 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix G G13 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix G G12 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix D D4 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix D D3 42/41wqar.doc DWM CN 51.0 Table 1. (continued) French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix C C37 42/41wqar.doc DWM CN 51.0 Table 1. (continued) French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix C C36 42/41wqar.doc DWM CN 51.0 Table 1. (continued) French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix C C35 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix C C34 42/41wqar.doc DWM CN 51.0 French River Watershed Quinebaug River Watershed  French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B38 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B37 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B36 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B22 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B16 42/41wqar.doc DWM CN 51.0 French & Quinebaug River Watersheds 2001 Water Quality Assessment Report Appendix B B15 42/41wqar.doc DWM CN 51.0    French & Quinebaug 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