United States
                Environmental Protection
                Agency
               Great Lakes National
               Program Office
               536 South Clark Street
               Chicago, Illinois 60605
EPA-905/4-84-001
r/EPA
                                                       C, I
Lake Erie  Intensive
Study 1978-1979

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                                               EPA-905/4-84-001
                                               January 1984
     Lake  Erie  Intensive  Study 1978-1979


                 Final  Report
                      by

              David  E. Rathke
    Lake Erie Technical  Assessment  Team
         The Ohio State  University
     Center For Lake Erie  Area  Research
               Columbus, Ohio
              Project Officer


               David Rockwell
     U.S. Environmental Protection Agency
     Region 5, library (PL42J
     77 West Jackson Boulevard, 12th tw*
     Chtea«o,IL  60604-3590

    lireat Lakes National Program Office
U.S. Environmental Protection Agency, Region  V
      536 South Clark Street, Room  958
          Chicago, Illinois  60605

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                        DISCLAIMER
     This report has completed the EPA peer and publications review
process and is approved for publication as an EPA document.  Mention
of trade names or commercial products does not constitute endorsement
or recommendation by EPA.

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                                  PREFACE

     Lake Erie has experienced several decades of accelerated eutrophication and
toxic substances  contamination.   During the latter part of the 1960s,  remedial
actions were planned and by the latter part of the 1970s, many of these plans were
at least  partially implemented.   The first signs  of  lake recovery are now being
observed through  comprehensive monitoring programs.  The intent of this report is
to summarize the methods, findings and  conclusions of the  1978-1979 Lake Erie
Intensive  Study.  The  report also contains  a set of recommendations to insure
continued improvement of the water and biotic quality of Lake Erie.

     Management information in the form of a review  of the lake's status and its
water quality trends are contained in a companion report  entitled, "Lake Erie
Water Quality 1970-1982:  A Management Assessment."  The management report
also  contains recommendations designed to ensure continued improvements in the
quality of the lake's water and biota.

     I would like to acknowledge the excellent cooperation of the many investiga-
tors  who participated in the Lake Erie Intensive Study and thank them  for their
contributions in the form of reports, data, and helpful suggestions.  Also, I would
like to thank David Rathke, Larry Cooper,  Laura Fay and Gary Arico, and the other
members  of  the  Lake Erie Technical Assessment  Team  staff for the  intensive
effort r\  preparing this report.
                          Charles E. Herdendorf, Chairman
                          Lake Erie Technical Assessment Team

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                           TABLE OF CONTENTS

Preface                                                                     i
Table of Contents                                                           iii
List of Tables                                                              vii

List of Figures                                                             xii

Acknowledgement                                                         xxii

Introduction                                                                 1

Methods                                                                     7
     Open Lake                                                             7
     Nearshore                                                             11
     Data Compatability   (Peter Richards)                                  13
                                           r
          Analysis of Split Sample Data                                      13
          Analysis of Round Robin Results                                    14
          Analysis of Data and Adjacent Stations                              15
          Synopsis                                                         17

Results                                                                    19
     Open Lake   (David Rathke, Laura Fay)                                  19
          Temperature                                                     19
          Thermal Stratification and Structure                               20
          Limnion Volumes                                                22
          Dissolved Oxygen                                                23
          Nutrients                                                        25
          Total Phosphorus                                                25
          Forms of Phosphorus                                             28
          Dissolved Inorganic Nitrogen                                      30
          Silica                                                           32
          Corrected Chlorophyll a and Particulate Organic Carbon             33
          Turbidity and Suspended Solids                                    34
          Secchi                                                          36
                                        iii

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           Principal Ions                                                    38
           Sediment Metal Analysis                                          40
           Phytoplankton                                                    44
     Nearshore Zone (Laura Fay, David Rathke)                               47
           Temperature Regime                                              48
           Nutrients                                                        49
           Total Phosphorus                                                 52
           Soluble Reactive Phosphorus                                       53
           Dissolved Inorganic Nitrogen                                       53
           Silica                                                            54
           Corrected Chlorophyll a                                           54
           Secchi                                                           55
           Dissolved Oxygen                                                 56
           Principal Ions                                                    56
           Conductivity                                                     59

Discussion                                                                  61
     Nearshore-Offshore Relationship   (Laura Fay)                           61
     Nearshore Trophic Status   (Laura Fay)                                  68
     Total Phosphorus   (David Rathke)                                      72
     Phosphorus Trends                                                     75
     Chlorophyll Trends                                                     76
     Dissolved Oxygen   (David Rathke)                                     77
     Objectives and Standards  (Larry Cooper, Audrey Rush, Bill Snyder)       84
           State of Michigan                                                 86
           State of Ohio                                                    87
               Ottawa and Lucas Counties                                   87
               Erie-Sandusky Counties                                       88
               Lorain County                                               90
               Cuyahoga County                                            91
               Lake and Ashtabula Counties                                  92
               Open Lake, State of Ohio Inclusive                            95
           Commonwealth of Pennsylvania                                    95
           State of New York                                                96
           Province of Ontario                                               97
                                        iv

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      Synopsis                                                         98
 Trace Metals   (Larry Cooper, Suzanne Messier)                          99
      Aluminum                                                       99
      Arsenic                                                         100
      Cadmium                                                       101
      Chromium                                                      102
      Copper                                                         103
      Total Iron                                                      104
      Lead                                                           105
      Manganese                                                      106
      Mercury                                                        107
      Nickel                                                          108
      Selenium                                                        109
      Vanadium                                                       110
      Zinc                                                           110
      Synopsis                                                        111
 Nearshore Water Quality Trends   (Audrey Rush)                        112
 Water Quality Trends at Cleveland, Ohio   (Peter Richards)               119
      Long Term Historical Trends                                      120
      Short Term Historical Trends                                      122
      Removing Seasonal Patterns                                      123
 Cladophora  (David Rathke, Dick Lorenz)                              127
      Lakewide Distribution                                            129
      Specific Study Sites                                              131
      Nuisance Conditions                                              133
Fish Communities   (Mark Barnes, Laura Fay, John Mizera)               135
      Background on Fish Population Changes                            136
      Effects of Cultural Stresses on Specific Fishes                      139
      Fish Stock Assessment                                            143
      Current Status and Potential Population Changes                    145
      Fish Population Response to Improving Water Quality                151
Fish Research                                                         155
      Larval Fish Entrapment                                          155

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          Distribution                                                   156
          Entrainment                                                   159
     Fish Contaminants                                                  162

Recommendations                                                       167
     Scientific Investigations                                             167
     Future Management Programs                                        169

Literature Cited                                                         171
Tables                                                            Tl -Till
Figures                                                           Fl - F163
APPENDIX A - Yearly Reach Means                                   Al - A91
APPENDIX B - River/Harbor Yearly Means                            Bl - B106
                                       vi

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                       LIST OF TABLES



 1.    EPA Cruise Schedule                                          T-l

 2.    CCIW Cruise Schedule                                         T-2

 3.    Nearshore Cruise Schedules for Lake Erie Intensive               T-3

 4.    Nearshore Reach Design                                       T-5

 5.    Precision Analysis Based on Split Samples                        T-6

 6.    Performance of  the  Lake Erie Labs  on  I3C Round-Robin
      Studies 21 through 29, Organized by Parameter                 T-l 1

 7.    Biases Suggested by Across-Boundary Comparisons  of Field
      Data                                                       T-l 5

 8.    Western  Basin Thermal  Structure Data by Cruise for 1978-
      1979                                                       T-16

 9.    Central Basin Thermal Structure Data by  Cruise for 1978-
      1979                                                       T-17

10.    Eastern Basin Thermal Structure Data by  Cruise for 1978-
      1979                                                       T-19

11.    Western  Basin  Volume  Weighted Total Phosphorus, Soluble
      Reactive Phosphorus, Tonnages and Concentrations, 1978-
      1979                                                       T-21

12.    Central  Basin Volume Weighted  Total Phosphorus, Soluble
      Reactive Phosphorus, Tonnages and Concentrations, 1978-
      1979                                                       T-23

13.    Eastern  Basin Volume Weighted  Total Phosphorus, Soluble
      Reactive Phosphorus, Tonnages and Concentrations, 1978-
      1979                                                       T-25

1<>.    Western  Basin  Volume  Weighted Nitrate  Plus  Nitrite  and
      Ammonia Tonnages and Concentrations, 1978-1979              T-27

15.    Central  Basin  Volume  Weighted Nitrate  Plus  Nitrite  and
      Ammonia Tonnages and Concentrations, 1978-1979              T-29

16.    Eastern  Basin  Volume  Weighted Nitrate  Plus  Nitrite  and
      Ammonia Tonnages and Concentrations, 1978-1979              T-31

17.    Corrected  Chlorophyll  a Volume  Weighted Tonnages  and
      Concentrations,  1978-1979                                    T-33

                                       vii

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 18.    Volume Weighted Particulate Organic Carbon, Tonnages and
       Concentration, 1978-1979                                   T-39

 19.    Mean Total Suspended Solids Concentrations (mg/1) for 1978
       (USEPA)                                                   T-43

 20.    Lake  Erie   Basin   Concentrations  of   Area  Weighted
       Transparency Measurements by Cruise                        T-44

 21.    Averaged Area Weighted Secchi Depth (m)                       37*

 22.    Lake Erie  Basin  Ratios of Area  Weighted  Transparency
       Measurements (M) by Cruise                                 T-45

 23.    Principal  Ion Concentrations  for  the  Open  Lake Cruises,
       1978-1979 (USEPA)                                         T-46

 24.    Lake Erie  1979  Sediment Survey (USEPA) Cluster  Means
       (mg/kg dry weight)                                          T-47

 25.    Sediment  Source Loading                                      44*

 26.    Seasonal  Relative Abundance of Common (>5%) Species in
       the Western Basin - 1978                                    T-48

 27.    Seasonal  Relative Abundance of Common (>5%) Species in
       the Western Basin - 1979                                    T-50

 28.    Seasonal  Relative Abundance of Common (>5%) Species in
       the Central Basin - 1978                                     T-52

 29.    Seasonal  Relative Abundance of Common (>5%) Species in
       the Central Basin - 1979                                     T-54

 30.    Seasonal  Relative Abundance of Common (>5%) Species in
       the Eastern Basin - 1978                                     T-56

 31.    Seasonal  Relative Abundance of Common (>5%) Species in
       the Eastern Basin - 1979                                     T-58

 32.    Total Mean Phytoplankton Biomass by Basin                      46*

33.    Western Basin Nearshore Nutrient Variability Between Years       51*

34.    Rationale for Monitoring Dissolved Substances                  T-59

35.    Lake Erie 1978-1979 Nearshore Principal Ion Reach Concen-
       trations (mg/1) and Statistics                                 T-62

36.    Principal  Ion Comparison of  1970  Open Lake Data (CCIW)
       with 1978-1979 Open Lake and Nearshore Data                   59*

                                       viii

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37.    Total Phosphorus and Chlorophyll  Concentrations and Basin
       Ratios for the U.S.  Nearshore, 1978-1979                       66*

38.    Nearshore and Open Lake Total Phosphorus and Chlorophyll
       Concentrations and Percent Difference by Basin, 1978-1979       67*

39.    Relationship of Total Phosphorus, Chlorophyll and Secchi          68*

40.    Comparison of Trophic Status of Lake Erie's Nearshore Zone
       Using Annual Reach Means, 1978-1979                         T-64

41.    Summary of Trophic  Status  Data  for Lake Erie Nearshore
       Waters, Summer 1972-1973                                   T-65

42.    Steinhart Water  Quality Index Values for the  Lake Erie
       1978-1979 Nearshore Reaches                                T-66

43.    Comparison of the Nearshore Composite Trophic Index and
       Steinhart's Index Using 1978-1979 Lake Erie Data               T-67

44.    Total Phosphorus Concentrations (ug/1) in  Lake Erie, 1970-
       1980                                                        73*

45.    Percentage Contribution  of Oxygen  Sinks  to  Dissolved
       Oxygen Deficit at the Time of Minimum D.O. in the Central
       Basin Hypolimnion                                            80*
                                     -2  1
46.    Central  Basin  SOD Rates (g 02m   d  ) of Several Investi-
       gators                                                      T-68

47.    Components of  Hypolimnetic  Oxygen Demand (HOD) in
       Central Lake Erie, 1979                                      T-69

48.    Lake  Erie  Central   Basin   Homogeneous  Area  Oxygen
       Depletion Rates                                             T-70

49.    Michigan Standards and I3C Objectives for Lake Erie Water
       Quality                                                     T-71

50.    Ohio Standards and  IJC Objectives for  Lake  Erie  Water
       Quality                                                     T-72

51.    Commonwealth of Pennsylvania Standards and IJC Objectives
       for Lake Erie Water Quality                                  T-73

52.    New York State Standards and I3C Objectives for Lake Erie
       Water Quality                                               T-75

53.    Ontario Provincial Objectives for Lake Erie  Water Quality       T-76

54.    Summary of Locations and Parameters Identified as Areas of
       Concern                                                    T-77

                                         ix

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55.    Neurotoxic  and   Oncogenic   Human  Health   Problems
       Associated with Chronic Exposure to Selected Trace Metals      T-81

56.    Objectives  and/or  Standards  for  Metal Concentrations  in
       Lake Erie                                                   T-82

57.    Summary of Cadmium Violations                              101*

58.    Number of Total Cadmium, Copper, Lead, Nickel,  Silver and
       Zinc Observations  Calculated  to Exceed USEPA  Published
       Criteria 1978-1979                                           T-83
59.    Summary of Chromium Violations                             103*

60.    Summary of Copper Violations                                10**

61.    Summary of Lead Violations                                  106*

62.    Summary of Mercury Observations                             107*

63.    Summary of Nickel Violations                                 108*

6*.    Summary of Selenium Violations                               109*

65.    Summary of Zinc Violations                                   111 *

66.    Total Metal Concentrations (ug/1) for Lake Erie, 1982           T-85

67.    Calculated Toxicity Units for Lake Erie, 1982                   T-86

68.    Number  Assignments,  Agencies and Locations for Stations
       Selected for Trend Analysis                                   T-87

69.    Summary of  Linear  Regression Trends of  Water  Quality
       Parameters at Selected Stations on Lake Erie                   T-89

70.    Comparison of Historical Data from Beeton (1961) with 1978
       Central Basin Nearshore Data (Heidelberg College)              T-91

71.    R-Square and T Values for Regression Analyses of Data from
       the Division  of  Water  Intakes,  Cleveland, Ohio, Before and
       After Filtering the Data to Remove Seasonal Fluctuations       T-92

72.    Comparison of Maximum Standing Crop Values from the 1979
       and 1980 Lake Erie Cladophora Surveillance Program            T-93

73.    Annotated List of Lake Erie Fish Species                       T-9<>

7*.    Current Populations Status of Major  Lake Erie Fish Species      T-96

75.    Relative Abundance of Larval Fishes Captured in the Western
       Basin of Lake Erie in 1977                                    T-99

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 76.    Relative Abundance of Larval Fishes Captured  Along the
       Ohio Shoreline of the Central Basin in 1978                    T-100

 77.    Larval Fish Entrainment Estimates for Western Basin Power
       Plants Per Year (1977)                                       T-102

 78.    Larval Fish Entrainment Estimates for Central Basin Power
       Plants Per Year (1978)                                       T-103

 79.    Comparison  of  Nearshore Volume  Weighted  Larval  Fish
       Abundance with Estimated Entrainment                       T-104

 80.    Summary of Toxic Substances from Lake Erie Fish Studies,
       1977-1980                                                  T-105

 81.    Fish Samples Collected from Lake  Erie Tributary Mouths
       Found  in Excess of IJC  and FDA  Limits  on Fish Tissue
       Concentrations, 1979                                        T-110
* Denotes those tables which appear in the text.
                                         xi

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                       LIST OF FIGURES
Figure 1.        Organizational  Structure   Responsible   for   the
                Implementation of the Lake Erie Study Plan.            F-l

Figure 2.        The Major Organizations and Participants Involved
                in the Two-Year Lake Erie Plan.                       F-2

Figure 3.        Representative  Cruise  Tract  Used by  USEPA-
                GLNPO During 1978 (taken from Cruise 7 August 29
                -Sept. 6).                                           F-3

Figure 4.        Schematic Representation of the Horizons Sampled
                in the Three Basins During the Stratified Seasons.       F-4

Figure 5.        Representative Cruise  Track Used by CCIW-NWRI
                During  1978 (taken from Cruise  103  May  29 -3une
                2).                                                 F-5

Figure 6.        Representative Cruise  Track Used by CCIW-NWRI
                During  1979 (taken from Cruise 103 May  15 -May
                18).                                                F-6

Figure 7.        Explanation of Plots Used to Display Data.              F-7

Figure 8.        Comparison of Percent 1978 Central and Eastern
                Basin Hypolimnion  Volumes  for  Each  Cruise as
                Estimated by CCIW-NWRI and USEPA-GLNPO.          F-8

Figure 9.        U.S.  Near shore  Station   Pattern   and   Reach
                Designation for 1978-1979.                            F-9

Figure 10.       Canadian  Nearshore Station Pattern  and  Reach
                Designation for 1978 and 1979.                       F-10

Figure 11.       Open Lake Seasonal Surface Temperature Pattern
                Recorded for All Three Basins in 1979.                F-l 1

Figure 12.       Open Lake Seasonal Bottom Temperature Pattern
                Recorded for the Central and Eastern Basins During
                1979.                                              F-12

Figure 13.       Seasonal Pattern of  Hypolimnion  Thickness (M) as
                Recorded in the Central and Eastern Basins of Lake
                Erie During the 1978 CCIW-NWRI Field Season.         F-13

Figure 14.       Representative Seasonal Thermal Structure for  the
                Central Basin  as Recorded by  CCIW-NWRI  at
                Station  12, 1979.                                    F-l 5

                                      xii

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 Figure 15.       Representative Seasonal Thermal Strucutre for the
                Eastern Basin  as  Recorded  by  CCIW-NWRI  at
                Station 4, 1979.                                     F-16

 Figure 16.       The   Mean   Western  Basin   Dissolved  Oxygen
                Concentrations  and  Percent Saturations for  197S
                USEPA-GLNPO.                                    F-17

 Figure 17.       The   Mean   Central  Basin   Dissolved  Oxygen
                Concentrations  and  Percent Saturations for  1978
                CCIW-NWRI.                                       F-18

 Figure 18.       The Seasonal  Hypolimnion Dissolved Oxygen (mg/1)
                Distribution Patterns for the  Central  and  Eastern
                Basins of Lake Erie During 1978.                      F-19

 Figure 19.       The   Mean   Eastern  Basin   Dissolved  Oxygen
                Concentrations  and  Percent Saturations for  1978
                (CCIW-NWRI).                                     F-21

 Figure 20.       The  Seasonal Epilimnion and Hypolimnion  Total
                Phosphorus  (ug/1) Distribution  Patterns for  the
                Central  and Eastern  Basins  of Lake Erie for  1978
                (CCIW-NWRI).                                     F-22

 Figure 21.       The   Mean   Western  Basin   Total   Phosphorus
                Concentrations for 1978 (USEPA-GLNPO).             F-24

 Figure 22.       The Mean Central Basin Epilimnion and  Hypolimnion
                Total Phosphorus Concentrations  for 1978  (CCIW-
                NWRI).                                            F-25

 Figure 23.       The Mean Eastern Basin Epilimnion and  Hypolimnion
                Total Phosphorus Concentrations  for 1978  (CCIW-
                NWRI).                                            F-26

 Figure 24.       The  Mean   Western  Basin   Total   Phosphorus
                Concentrations for 1979 (USEPA-GLNPO).             F-27

 Figure 25.       The Mean Central Basin Epilimnion and Hypolimnion
                Total Phosphorus Concentrations  for 1979  (CCIW-
                NWRI).                                            F-28

Figure 26.       The Mean Eastern Basin Epilimnion and Hypolimnion
                Total Phosphorus Concentrations  for 1978  (CCIW-
                NWRI).                                            F-29

Figure 27.       The Mean Central Basin Epilmnion and Hypolimnion
                Soluble Reactive Phosphorus  Concentrations  for
                1978 (CCIW-NWRI).                                  F-30
                                       xiii

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Figure 28.       The Mean Eastern Basin Epilmnion and Hypolimnion
                Soluble  Reactive Phosphorus  Concentrations  for
                1978 (CCIW-NWRI).                                  F-31

Figure 29.       The Mean  Western Basin Ammonia Concentrations
                for 1978 (USEPA-GLNPO).                            F-32

Figure 30.       The Seasonal Epilimnion and Hypolimnion Ammonia
                (ug/1)  Distribution  Patterns for  the  Central  and
                Eastern Basins of Lake Erie for 1978 (CCIW-NWRI).     F-33

Figure 31.       The Mean Central Basin Epilimnion and Hypolimnion
                Ammonia Concentrations for 1978 (CCIW-NWRI).       F-35

Figure 32.       The Mean Eastern Basin Epilimnion and Hypolimnion
                Ammonia Concentrations for 1978 (CCIW-NWRI).       F-36

Figure 33.       The Seasonal  Epilimnion and Hypolimnion Nitrate
                Plus Nitrite (mg/1)  Distribution  Patterns for  the
                Central  and Eastern Basins of Lake Erie for 1978
                (CCIW-NWRI).                                       F-37

Figure 34.       The  Mean  Western   Basin  Nitrate  Plus  Nitrite
                Concentrations for 1978 (USEPA-GLNPO).             F-41

Figure 35.       The Mean Central Basin Epilimnion and Hypolimnion
                Nitrate Plus Nitrite Concentrations for  1978 (CCIW-
                NWRI).                                             F-42

Figure 36.       The Mean Eastern Basin Epilimnion and Hypolimnion
                Nitrate Plus Nitrite Concentrations for  1978 (CCIW-
                NWRI).                                             F-43

Figure 37.       The Seasonal  Epilimnion   Dissolved  Silica  (ug/1)
                Distribution Patterns for  the Central  and Eastern
                Basins of Lake Erie for 1978 (CCIW-NWRI).            F-44

Figure 38.       The   Mean  Western  Basin   Dissolved   Silica
                Concentrations for 1978 (USEPA-GLNPO).             F-46

Figure 39.       The Mean Central Basin Epilimnion and Hypolimnion
                Concentrations of Dissolved Silica for 1978 (CCIW-
                NWRI).                                             F-47

Figure 40.       The Mean Eastern Basin Epilimnion and Hypolimnion
                Concentrations of Dissolved Silica for 1978 (CCIW-
                NWRI).                                             F-48

Figure 41.       The Seasonal  Epilimnion  Corrected Chlorophyll  a
                (ug/1)  Distribution  Patterns for  the Central  and
                Eastern  Basins  of  Lake  Erie for 1978 (USEPA-
                GLNPO).                                           F-49
                                        xiv

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 Figure 42.       The Seasonal Epilimnion Participate Organic Carbon
                (ug/1)  Distribution Patterns for the  Central  and
                Eastern Basins of Lake Erie for 1978 (CCIW-NWRI).     F-51

 Figure 43.       The Mean Western Basin  Corrected  Chlorophyll  a
                Concentrations for 1978 (USEPA-GLNPO).        ~    F-53

 Figure 44.       The Mean Central Basin Epilimnion and Hypolimnion
                Corrected Chlorophyll  a Concentrations for  1978
                (USEPA-GLNPO).      "                            F-54

 Figure 45.       The Mean Eastern Basin Epilimnion and Hypolimnion
                Corrected Chlorophyll  a Concentrations for  1978
                (USEPA-GLNPO).      "                            F-55

 Figure 46.       The Mean Central Basin Epilimnion and Hypolimnion
                Particulate Organic Carbon Concentrations for 1978
                (CCIW-NWRI).                                      F-56

 Figure 47.       The Mean Eastern Basin Epilimnion and Hypolimnion
                Particulate Organic Carbon Concentrations for 1978
                (CCIW-NWRI).                                      F-57

 Figure 48.       The 1978  Seasonal Mean  Distribution  Pattern of
                Total  Suspended  Solids  (mg/1)  for  Central and
                Eastern Basins of Lake Erie (USEPA-GLNPO).           F-58

 Figure 49.       The Mean Central Basin Epilimnion and Hypolimnion
                Total  Suspended  Solids Concentrations  for  1978
                (USEPA-GLNPO).                                    F-59

 Figure 50.       The Mean Eastern Basin Epilimnion and Hypolimnion
                Total  Suspended  Solids Concentrations  for  1978
                (USEPA-GLNPO).                                    F-60

 Figure 51.       The Mean Western Basin Total Suspended Solids
                Concentrations for  1978 (USEPA-GLNPO).              F-61

 Figure 52.       The Mean Western Basin Turbidity Values for  1978
                (USEPA-GLNPO).                                    F-62

 Figure 53.       The Mean Central Basin Epilimnion and Hypolimnion
                Turbidity Values for 1978 (USEPA-GLNPO).             F-63

 Figure 54.       The Mean Eastern Basin Epilimnion and Hypolimnion
                Turbidity Values for 1978 (USEPA-GLNPO).            F-64

 Figure 55A.      The Mean  Western Basin  Secchi Values  for  1978
                (USEPA-GLNPO).                                   F-65

Figure 55B.      The Mean Central and Eastern Basin Secchi Values
                for 1978 (USEPA-GLNPO).                           F-66
                                       xv

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Figure 56.      The Central and Eastern Basin Secchi Ratios Based
               Upon a Normalization of  the  1978 Western Basin
               Values.                                            F-67

Figure 57.      The   Distribution    Patterns    for    Epilimnion
               Concentrations of Principal Ions  Measured During
               June 1978 (USEPA-GLNPO).                          F-68

Figure 58.      The Mean Central Basin Epilimnion and Hypolimnion
               Chloride Concentrations for 1978 (USEPA-GLNPO).     F-70

Figure 59.      The Mean Eastern Basin Epilimnion and Hypolimnion
               Chloride Concentrations for 1978 (USEPA-GLNPO).     F-71

Figure 60.      The Mean Western Basin  Chloride Concentrations
               for 1978 (USEPA-GLNPO).                            F-72

Figure 61.      The Mean Western Basin Sulfate Concentrations for
               1978 (USEPA-GLNPO).                              F-73

Figure 62.      The Mean Central Basin Epilimnion and Hypolimnion
               Sulfate Concentrations for  1978 (USEPA-GLNPO).       F-74

Figure 63.      The Mean Eastern Basin Epilimnion and Hypolimnion
               Sulfate Concentrations for  1978 (USEPA-GLNPO).       F-75

Figure 6*.      The 1979 Distribution Patterns of Surficial Sediment
               Metal   Concentrations  in  Lake  Erie  (USEPA-
               GLNPO).                                           F-76

Figure 65A.     The Distribution Pattern  of Metal Concentrations
               Based Upon Cluster Analysis for Lake Erie Surficial
               Sediments in 1979.                                   F-80

Figure 65B.     The Major Sediment  Depositional Areas in Lake
               Erie.                                              F-80

Figure 66A.     The Distribution Pattern of Mercury Concentrations
               (mg/kg) in the Surficial Sediments of  Lake Erie
               During 1970.                                        F-81

Figure 66B.     The Distribution Pattern of Mercury Concentrations
               (mg/kg) in the Surficial Sediments of  Lake Erie
               During 1979.                                        F-81

Figure 67.      Phytoplankton Sampling Locations for  1978 and the
               Modified 1979 Collection Sites (USEPA-GLNPO).        F-82

Figure 68.      Seasonal  Fluctations  in   Western   Basin  Total
               Phytoplankton Biomass for 1978 and 1979 (USEPA-
               GLNPO).                                           F-83
                                        xvi

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Figure 69.       Seasonal    Fluctuations    in    Western    Basin
                Phytoplankton Composition, 1978 (USEPA-GLNPO).     F-8*

Figure 70.       Seasonal    Fluctuations    in    Western    Basin
                Phytoplankton Composition, 1979 (USEPA-GLNPO).     F-85

Figure 71.       Seasonal  Fluctuations  in  Central  Basin   Total
                Phytopiankton Biomass for 1978 and 1979 (USEPA-
                GLNPO).                                           F-86

Figure 72.       Seasonal  Fluctuations  in  Eastern  Basin   Total
                Phytopiankton Biomass for 1978 and 1979 (USEPA-
                GLNPO).                                           F-87

Figure 73.       Seasonal    Fluctuations    in    Central    Basin
                Phytoplankton Composition, 1978 (USEPA-GLNPO).     F-88

Figure 7k.       Seasonal    Fluctuations    in    Central    Basin
                Phytoplankton Composition, 1979 (USEPA-GLNPO).     F-89

Figure 75.       Seasonal    Fluctuations    in    Eastern    Basin
                Phytoplankton Composition, 1978 (USEPA-GLNPO).     F-90

Figure 76.       Seasonal    Fluctuations    in    Eastern    Basin
                Phytoplankton Composition, 1979 (USEPA-GLNPO).     F-91

Figure 77.       Mean  Concentrations   for  the  1978  and  1979
                Nearshore   Data  Base   Summarized   for   Each
                Designated Reach Area.                             F-92

Figure 78.       South   Shore   River  and  Harbor  Mean   Total
                Phosphorus  Concentrations  Summarized  for  1978
                and 1979.                                           F-98

Figure 79.       South  Shore River  and Harbor Mean Nitrate Plus
                Nitrite Concentrations  Summarized  for  1978 and
                1979.                                              F-99

Figure 80.       South  Shore  River  and  Harbor Mean  Ammonia
                Concentrations Summarized for 1978 and 1979.        F-100

Figure 81.       Mean  Nearshore Reach Concentrations  of   Total
                Phosphorus for 1978 and 1979.                       F-101

Figure 82.       Mean  Nearshore Reach Concentrations of Soluble
                Reactive Phosphorus for 1978 and 1979.               F-102

Figure 83.       Mean  Nearshore Reach Concentrations of Nitrate
                Plus Nitrite for 1978 and 1979.                       F-103

Figure 8
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Figure 85.       Mean Nearshore Reach Concentrations of Dissolved
                Silica for 1978 and 1979.                            F-105

Figure 86.       Mean Nearshore Reach Concentrations of Corrected
                Chlorophyll a for 1978 and 1979.                     F-106

Figure 87.       Mean  Nearshore Reach Concentrations of Secchi
                Depth for 1978 and 1979.                            F-107

Figure 88.       Mean Nearshore Reach Concentrations of Dissolved
                Oxygen for 1978 and 1979.                           F-108

Figure 89.       Mean  Nearshore  Reach  Percent  Saturation  of
                Dissolved Oxygen for  1978 and 1979.                  F-109

Figure 90.       A   Comparison   of   Lake   Erie   Principal  Ion
                Composition with that of  a Standard Bicarbonate
                Lake.                                              F-110

Figure 91.       Mean Nearshore Reach Concentrations of  Chloride
                for 1978 and 1979.                                  F-lll

Figure 92.       Mean  Nearshore  Reach  Concentrations  of Sulfate
                for 1978 and 1979.                                  F-112

Figure 93.       South  Shore  River   and   Harbor  Mean  Sulfate
                Concentrations Summarized for 1978 and  1979.        F-113

Figure 9*.       The Percent Contribution of the Individual Principal
                Ions to the Total Conductance for Each of the U.S.
                Reaches.                                          F-114

Figure 95.       Mean Nearshore Reach Chloride Concentrations and
                Conductivity Values for 1978 and 1979.               F-115

Figure 96.       Mean Total Phosphorus and Chloride Concentrations
                for Western Basin Transect 26 - Maumee Bay, 1978-
                1979.                                              F-116

Figure 97.       Mean Total Phosphorus and Chloride Concentrations
                for  Central  Basin Transect 34  - Cuyahoga River,
                1978-1979.                                         F-117

Figure 98.       Mean Total Phosphorus and Chloride Concentrations
                for  Central Basin Transect 16 - Wheatley Harbor,
                1978.                                              F-118

Figure 99.       Mean Total Phosphorus and Chloride Concentrations
                for  Central  Basin Transect 39 - Ashtabula River,
                1978-1979.                                         F-119
                                       xviii

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Figure 100.     Secchi   Depth   and  Corrected   Chlorophyll   a
               Relationship  for  the Nearshore  Reaches 1978  and
               1979.                                              F-120

Figure 101.     Annual Mean  Composite  Trophic  Index for  the
               Nearshore Reaches 1978 and 1979.                    F-121

Figure 102.     Composite Trophic  Index Numbers for the Summer
               Mean  1972-1973  and the Annual  Mean  for  1978-
               1979.                                              F-122

Figure 103.     Steinhart Water  Quality Index Numbers for  the
               Nearshore Reaches 1978 and 1979.                    F-123

Figure 104.     Western Basin  Annual  Cruise Mean Concentrations
               of Total Phosphorus for 1970-1982.                    F-124

Figure 105.     Central  and Eastern  Basin Annual  Cruise  Mean
               Concentrations of Total Phosphorus for 1970-1982.     F-125

Figure 106.     Early Summer Mean Central Basin Epilimnion Total
               Phosphorus Concentrations for 1970-1982.             F-126

Figure 107.     Western Basin  Annual  Cruise Mean Concentrations
               of Corrected Chlorophyll a for 1970-1982.             F-127

Figure 108.     Central  and Eastern  Basin Annual  Cruise  Mean
               Concentrations of Corrected Chlorophyll a for 1970-
               1982.                                 ~            F-128

Figure 109.     Relationship  Between  Yearly Total Phosphorus and
               Chlorophyll a Concentrations Corrected for Spatial
               and SeasonafEffects.                               F-129

Figure 110.     Composite Anoxic Area of the Central Basin for the
               Period from 1930 to 1982.                           F-130

Figure 111.     Schematic of  the  Components and  Processes of
               Hypolimnion Oxygen Demand.                        F-131

Figure 112.     Central Basin Hypolimnion Oxygen Depletion  Rates
               as Reported by Dobson  and Gilbertson, 1971.           F-132

Figure 113.     Central Basin Hypolimnion Oxygen Depletion  Rates
               as Reported by Charlton (1979) and Rosa and Burns
               (1981).                                             F-133

Figure 114.     Shoreline Counties  of  Ohio Utilized  in Tabulating
               Nearshore Water Quality Violations.                  F-134

Figure 115.     South  Shore  Metal  Concentrations by Season  and
               Basin for 1978 and 1979.                             F-135
                                       xix

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Figure 116.      Shoreline Locations Used to Determine Long Term
                Trends.                                            F-138

Figure 117.      Total  Phosphorus Trend  Analysis for the  Detroit
                River/Livingston Channel (Station 00002*).            F-139

Figure 118.      Total  Phosphorus Trend  Analysis for the Maumee
                River/C and O Dock.                               F-140

Figure 119.      Specific Conductance and Chloride  Trend Analysis
                for  the Cleveland  Area as  Reported by  Beeton
                (1961) and Richards (1981b).                         F-141

Figure 120.      Sulfate  and  Calcium  Trend  Analysis   for  the
                Cleveland Area as Reported by Beeton  (1961)  and
                Richards (1981b).                                   F-l*2

Figure 121.      Sodium  Plus  Potassium  Trend  Analysis  for  the
                Cleveland Area as Reported by Beeton  (1961)  and
                Richards (198 Ib).                                   F-l*3

Figure 122.      Areas  of Widespread Cladophora  Colonization as

Figure 123.
Figure 12*.
Figure 125.
Figure 126.
Figure 127.
Figure 128.
Figure 129.
Figure 130.
Figure 131.
Reported by Auer and Canale 1981.
Station Locations Used in the Cladophora Survey.
Western Basin Cladophora Standing Crop Estimates
for Stony Point, Michigan and South Bass Island,
Ohio 1979 (CLEAR).
Central - Eastern Basin Cladophora Standing Crop
Estimates for Walnut Creek, PA 1979 (Suny).
Eastern Basin Cladophora Standing Crop Estimates
for Hamburg, NY (Suny) and Rathfon Point, Ont.
(MOE) 1979.
A Comparison of the Maximum Cladophora Standing
Crops for the Five Survey Locations, 1979.
Total Commercial Landings of Herring, Whitefish,
Sauger, Blue Pike and Walleye from 1880 to 1980.
Total Commercial Landings of Yellow Perch and
Rainbow Smelt from 1890 to 1980.
Total Commercial Landings of Carp, Drum, White
Bass, Gizzard Shad, Channel Catfish and Suckers
from 1960 to 1980.
Western Basin (1977) and Central Basin (1978)
Larval Fish Sampling Stations.
F-W
F-145
F-146
F-147
F-148
F-149
F-150
F-151
F-152
F-153
                                         XX

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Figure 132.      Mean Larval Yellow Perch  Density  in the Western
                Basin During 1977.                                  F-15*

Figure 133.      Mean Larval  Yellow Perch Density  for Individual
                Western Basin Sampling Transects During 1977.        F-155

Figure 134.      Mean Larval  White Bass Density  in the  Western
                Basin During 1977.                                  F-156

Figure 135.      Mean  Larval White  Bass  Density   for Individual
                Western Basin Sampling Transects During 1977.        F-157

Figure 136.      Mean Larval Walleye Density  in the  Western Basin
                During 1977.                                       F-158

Figure 137.      Mean Larval Walleye Density for Individual Western
                Basin Sampling Transect During 1977.                 F-159

Figure 138.      Mean Larval Yellow Perch  Density  in the Central
                Basin During 1978.                                  F-160

Figure 139.      Mean Larval  Yellow Perch Density  for Individual
                Central Basin Sampling Transects During 1978.         F-161

Figure 1*0.      Mean Larval  Smelt Density in the  Central Basin
                During 1978.                                       F-162

Figure 1*1.      Mean Larval Smelt  Density for Individual Central
                Basin Sampling Transects During 1978.                F-163
                                         xxi

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                         ACKNOWLEDGEMENT
     Without the cooperation of numerous agencies and individuals during the
preparation of this report,  the task would  have been  considerably more
difficult.  In particular, I would like to thank Canada Centre for Inland Waters
scientists F. Rosa and M. Charlton for providing the 1978 and 1979 open lake
data sets and for reviewing the final draft report. I would also like to thank Y.
Hamdy and his staff at the Ontario Ministry of the Environment for supplying
the 1978 and 1979 nearshore data plus numerous supplementary documents.

     I wish to thank the  reviewers for their suggestions,  in particular, 3.
Leach (OMNR), C. Mortimer, C. Edwards and 3. Gannon (I3C), and H.   Dobson
(CCIW).

     In addition, Laura Fay, 3ohn Mizera, Gary Arico, and the CLEAR clerical
staff provided the support and expertise necessary to complete this project.

     I wish to acknowledge  the EPA-Great Lakes National Program Office
for their support of Technical Assessment Team  and the  1978 and 1979 data
sets.

     Finally, a special recognition should be given to Noel Burns (CCIW) for
his contribution to the understanding of the numerous complexities associated
with the limnology of Lake Erie.
                                       David E. Rathke
                                       Editor
                                  xxii

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                                  INTRODUCTION

      In many respects Lake Erie has one of the longest and most complete historical
 Great Lakes databases.  The first open lake surveys of the western, central and eastern
 basins were conducted during the late 1920's and into the early 1930's (Wright 1955, Fish
 1960).  Although  no other major monitoring effort was made until the Federal Water
 Pollution Control Administration (FWPCA) conducted surveys in 196* and 1968, numerous
 independent studies were undertaken.  Many of these  studies were confined to localized
 regions primarily  in  the  western and  central basins and  were  generally university
 affiliated.

      During the mid  1960s, public awareness of the eutrophic condition  of Lake Erie
 together with increased concern by the Canadian government and the Canadian and U.S.
 scientific community,  prompted the initiation of the most intensive  surveillance program
 yet to be conducted. Two programs were initiated during the 1970 field season. The first
 program consisted of  ten  surveillance  cruises spanning April through December.  This
 surveillance program, conducted by the Canada Centre for Inland Waters (CCIW), provided
 an extensive whole lake database plus a thorough analysis of lake processes.  The program
 culminated in a series of 21 articles presented in the J.  Fish Res. Board Can., Vol. 33,
 1976.   In   addition,  numerous scientific  articles were  published  further expanding
 information on lake processes.

      A second  program,  focusing  on the  central basin  hypolimnion, represented a
 combined effort of the USEPA  Cleveland Office and CCIW.  This study, "Project Hypo",
 was designed to examine the processes responsible for  the O- depletion problem annually
 encountered in the central  basin. Seven central basin surveys were conducted over a 28-
 day period from late July through the end of August during which  time numerous physical,
chemical  and  biological   parameters  associated with hypolimnion  dissolved  oxygen
depletion were measured.  This program culminated in a report, "Project Hypo" (Burns and
Ross  1972),  consisting  of nine papers each dealing with specific aspects of hypolimnion
processes. The report concluded by stating:

      "The above findings and estimates lead to one definite conclusion: Phosphorus input
      to Lake Erie must be  reduced immediately;  if this is done, a quick improvement in
      the condition  of the lake  can  be  expected; if  this is  not  done,  the  rate  of
      deterioration of the lake will be much greater than it has been in recent years."
                                         1

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      Following  the formal  scientific recognition  and  verification  of  the extensive
problems developing throughout the lake, the Canada/US Water Quality Agreement was
signed in 1972.  This agreement called for reduction in the pollutants entering the lake,
specifically phosphorus, in order to curb the increasing eutrophication-related problems.
In addition, a continuation of the 1970  Canadian surveillance effort was also agreed upon,
and  this program  began  in 1973  under the  sponsorship  of  the  USEPA—Large  Lakes
Research Station.  The western and  central basins were monitored by the Center for Lake
Erie  Area  Research—The  Ohio State University (CLEAR), and the  eastern basin  was
monitored  by  the  State University  of  New York-Buffalo (SUNY).  Reports were  issued
detailing the  1973 through  1975  open  lake studies  (Great  Lakes Laboratory  1980,
Herdendorf 1980a).  The 1973-1975 database,  together with the 1970 Canadian data set,
provided much of  the information necessary for the verification and calibration  of Lake
Erie models.   The  modeling program was developed  to further the  understanding of lake
processes and aid  in predicting responses  to  efforts designed to slow down the already
accelerated eutrophication (DiToro and Connolly 1980, Lam et al. 1983).

      The next phase of the  Lake Erie program was initiated  under the auspices of the
International Joint Commission's Water Quality Board.   An appointed  Lake Erie Work
Group was  established to  specifically  develop a long-term  study plan for  the lake.  The
Lake  Erie Work Group prepared a nine-year  surveillance plan in 1977 which was designed
to provide  an  understanding of the  overall,  long-range responses of the lake to pollution
abatement  efforts.  This  plan was  eventually incorporated as part of the Great  Lakes
International Surveillance Plan (GLISP) developed by the Surveillance Subcommittee of
the Water  Quality  Board.  The  general  objectives established  by  the Surveillance
Subcommittee for GLISP included:

      1.    To  search for,  monitor, and quantify violations of the existing agreement
           objectives (general and  specific), the I3C recommended objectives, and the
           individual jurisdictional standards, criteria and objectives.  Quantification will
           be  in terms of severity,  areal or volume  extent, frequency, duration and  will
           include sources.
      2.    To  monitor local and whole  lake  responses  to  abatement measures and to
           identify emerging problems.
      3.    To  determine the cause-effect relationship between water quality and  inputs
           in  order  to   develop  the appropriate  remedial/preventive  actions  and
           predictions of the rate and extent of local/whole lake responses to alternative
           proposals.

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      Within the context of  these  general  objectives  and considering the key  issues
specific to Lake Erie, the surveillance plan additionally focused on:

      1.    Determining the long-term trophic state of  Lake Erie and observing to what
           degree remedial measures have resulted in improvements.
      2.    Assessing the presence, distribution, and impact of toxic substances.
      3.    Providing information to  indicate  the requirements  for  and  direction of
           additional remedial programs, if necessary, to protect water uses.
      Figure 1 outlines the organizational structure responsible for the implementation of
the Lake Erie plan.

      The Lake Erie plan called for a two-year intensive study of open lake and nearshore
conditions in 1978 and 1979  to be followed by  seven  years of  open  lake  monitoring.
Planning and implementation of the two-year field program was coordinated by the Lake
Erie Work Group of the Surveillance Subcommittee.  This subcommittee served as the
Implementation Committee for the I3C Great Lakes Water Quality Board.  The Lake Erie
Work Group was charged  with the responsibility of monitoring  the progress of the field
investigations,  preparation of reports analyzing  the results of these  studies,  and the
coordination of a comprehensive assessment of the current status of Lake Erie.

      The general  objective of the Lake  Erie Intensive Study was to  provide information
for detailed assessments of  tributary, nearshore, and  open lake water quality.   The
intensive  study was designed  to identify emerging problem areas, to detect changes in
water quality on a broad geographic  basis, and to provide information necessary for trend
analyses.   This study  was to take  into consideration  the seasonal  nature of tributary
inputs, lake circulation patterns, and nearshore-offshore  gradients.  Linkages between the
various components of the study were to be explored to permit a detailed "whole lake"
water quality assessment.  In addition, information derived from this study was intended
to serve as a database against which future changes could be measured.

      The intensive program was divided into  six major categories with  the respective
responsibilities sub-divided into 33 components each of which were assumed by a specified
organization  (Figure 2).   In order to assist  the Lake Erie Work Group in meeting its
responsibilities the  Center for  Lake Erie  Area  Research  (CLEAR)   proposed that  a
Technical Assessment Team (TAT) be established.  In March 1980, TAT was established at
The Ohio State University by a grant from  the U.S. Environmental  Protection Agency,

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Great Lakes National Program Office (USEPA-GLNPO).  TAT was formed to synthesized

all data from the various contributors into  a unified, whole lake assessment.  Specific

objectives of TAT include the following:


      1.    To perform an in-depth and integrated analysis of the database for the purpose
           of a comprehensive assessment.

      2.    To assure that all pertinent baseline data resulting from United States sources
           are entered into STORET for the purpose  of  this  assessment and  future
           analysis.   Efforts would be made to achieve similar  entry of Canadian data
           into STORET.

      3.    To bring  together the individual Canadian and United States elements  of the
           intensive study to produce a timely, unified whole-lake report which will:

           a.    Determine the status of the open water and nearshore areas of Lake Erie
                in terms  of:

                (1)   Trophic level
                (2)   Toxic substance burden
                (3)   Oxygen demand

           b.    Provide baseline data  for the chemical, microbiological,  and  physical
                parameters of water quality against which future changes may be judged.

           c.    Compare the present data  with past data in order to determine how
                rapidly and in what manner the lake is changing.

           d.    Determine how these changes are related to reductions in waste loading,
                pollutant  bans, nutrient control  programs, and  pollution  abatement
                programs.

           e.    Prepare  recommendations  concerning  the scope  of  future  remedial
                programs to enhance or maintain current water quality.

      Following the  establishment of the TAT program, several data acquisitions were

necessary in order to analyze and integrate the many programs involved in the intensive
two-year  study.   Preliminary efforts to retrieve U.S. data sets through STORET were

plagued with numerous problems. Generally, the difficulty lay in the lack of completeness

of the  entered  information and/or mistakes within  the  data  sets.    These problems

significantly delayed data  analysis of both the open lake and  the nearshore.  All Canadian

data sets were acquired directly from the appropriate agency with little complication.


      In addition to the actual data, quality control  information was also requested from
each  Lake Erie Intensive participant.   I3C  round-robin studies and limited information

from  the nearshore  groups served  as the only source of quality control data.  Thus,

thorough examination of individual group data and comparisons between  groups were very

                                         4

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limited.  Due to inconsistencies within data sets and incompatability between data sets,
much of the survey information was difficult to integrate.  This  situation existed with
both open lake and nearshore data sets.

     The objective of this  report is to present the data collected over the two-year
intensive study and evaluate it in terms of our previous knowledge of Lake Erie. This aim
is not to present a model, but only to evaluate the current database and attempt to place
it in perspective with  information accrued over the last decade.   Key pieces of  missing
information will be identified and future investigations will be recommended.

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                                      Methods
Open Lake

     During  1978 and 1979 both  the  United States Environmental Protection Agency,
Great Lakes National Program Office (USEPA-GLNPO), and the Canada Centre for Inland
Waters, National Water  Research Institute (CCIW-NWRI) conducted field programs on
Lake Erie open  waters.  The U.S. program was  established as  a two-year surveillance
program  designed to provide an extensive baseline data set. The Canadian contribution
consisted of  two projects designed to examine  specific  research  problems  and were
extensive enough spatially and temporily to provide detailed data on both the central and
eastern basins.  Information as  to  sampling and analytical methods will not be discussed
here since this information is  available through  each  of  the respective agencies. Only
those methods, either field or analytical, resulting in obvious differences in the data  will
be addressed.

     The USEPA-GLNPO scheduled 18 surveys on the western, central and eastern basins
over the two-year period.  Table  1 lists the cruise dates for each survey.  The station
sampling pattern employed during the  two-year period followed a scheme established in
the early 1970's and was utilized  annually from  1973  through 1977 (Herdendorf 1980a,
Great Lakes Lab 1980).  A total of 27 eastern basin, 37 central basin and 17 western basin
stations were sampled on each cruise.  Figure 3 shows the general cruise  track employed
during  1978.  During 1979, surveys were conducted using a west to east pattern, beginning
in the western basin and  moving in a criss-crossing pattern toward Buffalo.  Each cruise
lasted  approximately 10 days; however, this varied according  to weather and  boat
maintainence problems.  Water samples were obtained using the following scheme:

     Unstratif ied Condition:         1 m
                                   mid depth
                                   1m above bottom
     Stratified Condition:           1m
                                   1m above mesolimnion
                                   1m below mesolimnion
                                   1m above bottom
     This design was modified to accomodate differences in thermal conditions (Figure

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      In  1978, temperature/depth profiles were taken using a Martek probe coupled with
 an x-y recorder.   During 1979, a Guildline bathythermograph (EBT)  was the  primary
 instrument with the Martek as the support unit.  Temperature/depth plots were taken at
 each station and were  used to  determine  sample depths.  Water samples were obtained
 with Niskin bottles positioned in tandem on a cable and closed at the appropriate depth by
 a series  of messengers.  Water samples were then transferred from the Niskin bottles to
 appropriate containers for processing.  Subsequent sample processing  varied for  each
 parameter measured; for example, soluble nutrients (i.e., soluble reactive phosphorus—
 SRP, nitrate + nitrite - N + N, ammonia - NH3) were processed on board ship and analyzed
 shortly after collection, while samples for metals analysis were stored and transported to
 a land-based laboratory.

      The second major open lake data set was collected by CCIW-NWRI in the course of
 conducting specific research programs.  The 1978 database  was collected during a project
 designed to examine hypolimnion oxygen depletion mechanisms in the central and eastern
 basins and was initiated by N. Burns and F. Rosa.  The  1979 CCIW data orginated from a
 project examining the flux of material through the water column and was initiated by M.
 Charlton.  Since  these  two data sets were collected  and analyzed by the same agency
 using identical standardized  procedures, the data was treated as one set.   The major
 differences in the two CCIW data sets lie in the intensity of station coverage and cruise
 schedules. The station plan and representative cruise tracks for  each year are shown in
 Figures 5 and 6.  The areal coverage in 1978 provides the most comprehensive database to
 date on the central and eastern basins.  The two cruise schedules differ in that the  1979
 field season begins  earlier and ends later (Table 2).  It should be remembered that  both
 these projects were designed around specific research problems and were not designed to
 be used as lake surveillance databases.

     All CCIW temperature/depth profiles were  measured with a Guildline EBT. Samples
 were  collected at  intervals  similar to  those used by USEPA-GLNPO  (Figure  f).   In
addition,  mesolimnion  samples were collected  whenever  the  mesolimnion  thickness
permitted. Water was collected using a deck-controlled Rosette sampler equipped  with
Niskin bottles and an EBT sensor.  Therefore, samples were taken at known depths and
temperatures. Once water was obtained, soluble nutrients were analyzed on board, while
samples that could be stored were processed at the land-based laboratory.

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      A potential sampling problem occurs for both single Niskin bottles and the Rosette
 configurated samplers.  These bottles may entrain and hold water when being lowered
 through  the water column.   This is most likely to happen  when samples are taken in
 narrow strata or limnions such as those  occurring in the central basin, and since the
 sample bottle only travels 3-5 meters after leaving the epilimnion, adequate flushing may
 not occur. This problem requires further investigation.

      Analysis  of both  the  CCIW  and  the USEPA-GLNPO  databases by  TAT was
 implemented  using  identical  techniques  whenever  possible  in  order  to  ensure
 compatability at  this level. The first phase of the analyses of the physical and chemical
 data involved interpretation of the individual EBT traces from  both USEPA-GLNPO and
 CCIW.  Limnion1 depth data  for 1978 CCIW data was provided by F. Rosa. From these
 temperature/depth profiles, estimates as precise as the individual traces would allow were
 made for epilimnion, mesolimnion and hypolimnion thicknesses and temperatures.

     This information was then used to create a data file containing Jimnion depths and
 temperatures  for each  station within a cruise.  During the  next phase,  each sampling
 depth was assigned a code designating the limnion from which that sample was taken.  A
 hypothetical example follows:  Station  9 (USEPA-GLNPO), located in the eastern basin,
 has a  sounding depth of  45  m.  By examining the temperature/depth  profile,  it was
 determined  that the epilimnion extended from 0 to 20 m, the  mesolimnion from 20-30 m,
 and hypolimnion from 30-45 m.  Water samples at Station 9 were taken  at  1 m, 10 m, 19
 m,  25 m, 31  m, 37  m  and 44 m.   Each one of the sample depths  was then  coded
 appropriately, i.e., 1, 10 and 19 meters = epilimnion, 25 meters = mesolimnion, and  31, 37,
 and 44 meters = hypolimnion.  During unstratified conditions, depths were simply coded
 surface, mid or bottom.
   The term limnion will be used throughout this text to refer non-specifically to one
or all thermal layers (i.e., epilimnion, mesolimnion, hypolimnion).

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     The limnion depth determinations and the sample coding files enabled two computer
programs to be utilized.  The first and most  sophisticated program  was developed
specifically  to  be used on Lake Erie data sets.  The "Survey 8"-A Budget Calculation
Program for Lake Erie developed by B. Hanson, F.  Rosa and N. Burns (1978), computes
lake-wide or basin-wide volume weighted concentrations and quantities (metric tons) for
any given parameter plus plots isopleth distribution maps of each stratified layer.  The
Survey 8 program also provides an estimate of the area and volume for each limnion. The
lake was partitioned into geographical regions based on Sly (1976), i.e., western, central
and eastern basins; thus, estimates of  limnion volumes and parameter volume  weighted
mean concentrations were available for each individual basin.

     Due to the cost and time necessary to run Survey 8's, a second program was utilized
to obtain routine  mean  concentrations.   Sort  and  means programs available  with  the
Statistical Analysis System (SAS)  package were applied  to these data sets.   Since all
station data had been coded as to basin and each sampling depth coded as  to limnion,  a
simple means program could  be utilized.  This  system provided means,  standard errors,
maximum, minimum, and sample number (n) for any parameter in the data set.  Graphical
representation of the data sets includes all the previously mentioned statistics (Figure 7).
This data was compiled for the individual  basins and limnions however,  the values were
not volume weighted. If total quantities were desired for budget purposes, the volume of
each limnion obtained  from  the Survey-8 program could be  multiplied by the mean
concentration to obtain total tonnages.

     We were confronted with a rather unique  situation, having two distinctly  different
data sets available for the two-year period. Both the CCIW and the USEPA-GLNPO data
sets were examined individually before they were compared.  Since  both station patterns
and cruise schedules were significantly different, comparison  was somewhat subjective.
The 1978 data sets were the  most complete,  consequently comparisons between agencies
were made using the 1978 database.  First, the Survey 8 program  was run in order to
compare  limnion volumes  and  thicknesses.    The  poor  quality  of  the  USEPA
temperature/depth profiles made this  comparison extremely  difficult for most of  the
surveys (Figure 8).  When comparisons could be made, differences  in individual limnion
volumes  ranged from  20 to  50 percent.   When Guildline  EBT's were  taken by both
agencies, good  agreement  existed for  limnion  volume comparisons;  however,  the
instrument was not used for all cruises and only partially  on some surveys  conducted by
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USEPA-GLNPO.  Considering the difference in quality of the temperature/depth profiles,
the CCIW data was considered to be the most accurate.

      Since the concentrations and quantities of phosphorus are of primary importance in
the evaluation of Lake Erie's current trophic status, this parameter was examined to
determine data compatability.  Volume weighted concentrations by limnion could not be
compared due to the differences in estimated limnion volumes as previously discussed;
consequently, calculated total basin tonnages were compared.  The 1978 and 1979 CCIW-
NWRI phosphorus concentrations and quantities were found to be comparable with data
sets collected since  1970.  The  1978 central basin concentration and quantities of total
phosphorus derived from the USEPA-GLNPO data sets  were 30-40 percent lower than
estimates calculated from the CCIW data.  When the 1979 data was compared for the two
organizations, total phosphorus determinations were found to be more compatible than in
the 1978 data set, however, the USEPA-GLNPO values were still found to be consistently
lower. The reason for this discrepancy is not clear; however, the analytical method used
by the two agencies was different.  Phosphorus determinations  made  by the USEPA-
GLNPO laboratories conformed to USEPA methods  for waste water analysis utilizing the
molybdate ascorbic acid technique, while  CCIW  used the molybdate stannous chloride
procedure.   Based  on  these two problem areas (volume  determinations and  total
phosphorous concentrations) it was decided  to use the CCIW data as the primary data  set
and USEPA-GLNPO data when Canadian information was  not available.

Nearshore.

      As  a segment of the two-year intensive study on Lake Erie, the nearshore zone was
monitored with the intent to provide compatable data sets throughout the nearshore and
open lake.  The nearshore study was divided among four groups:  1) northshore - Ontario
Ministry  of the Environment - OMOE;  2) western basin - U.S., CLEAR - OSU; 3) central
basin  - U.S., Heidelberg College; 4) eastern basin - U.S., GLL - SUNY.

     The entire  U.S. shoreline  was a  coordinated study sponsored  and  managed  by
USEPA-GLNPO Region  V.   The  program  was designed with the  three participants
monitoring the U.S. nearshore zone  using similar schedules,  sampling  methods, and
analytical procedures.   Four  surveys  were conducted each  year  (Table  3)  to examine
seasonal variability. The sampling pattern was designed to provide stations parallel to the
shoreline as  well  as clusters of stations perpendicular to the shore in regions of harbors
                                         11

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and river mouths (Figure 9).  During each survey the individual stations were sampled on
three consecutive days in order to estimate short-term variability.

      Analytical methods  employed by each groups were those outlined by  USEPA with
details  and/or modifications of procedures  available from each  of  the three groups
participating in the U.S.  program.   The number and position of the sampling depths at
individual stations  varied  with the  sounding  depth.   Samples were routinely taken one
meter below the surface and  one meter above the bottom.  This general  pattern was
modified for sounding depths less than 4 m when only surface samples were taken and
soundings greater than 10  m when a mid depth sample was added.

      Two significant problems developed when combining the three U.S. data sets. First,
even though uniform methodologies  were to have been followed, several  inconsistencies
were  evident.  For example, in the eastern basin the soluble nutrient chemistry was not
carried out on-board ship as was done in the  western and central basins.  Water samples to
be analyzed  for soluble  nutrients (i.e., soluble  phosphorus, ammonia and  nitrate plus
nitrite) were stored and processed at a shore-based laboratory.  Thus,  this data must be
interpreted as  only estimates  of shoreline  concentrations.   An additional interpretation
problem existed in  the central basin where  no temperature/depth profiles were taken at
the deeper stations (>10 m).  Consequently, the extent of intrusion of mesolimnion or
hypolimnion water into this zone was difficult to verify.

     The second problem  encountered while attempting to interface  the data resulted
from  the difference in  cruise  schedules  (Table 3).   During  the  spring, scheduling
differences were largely due to varying ice conditions from the western  to the eastern
basin.  During the summer and fall, however, no attempt was made to sample the various
basins within the same time frame. This added an additional variable to an already highly
variable region.

     The north shore  study conducted by the  Ontario Ministry of the  Environment
(OMOE) was designed independently  of the  U.S. near shore  study.  The sampling pattern
covered  all three basins (Figure 10) with various levels  of effort  directed at specified
areas along the shore.  The cruise schedule differed in 1978 and 1979 and also differed
from the south shore plan  (Table 3).  As with the south shore study, two distinct station
patterns were  evident:  1) stations forming a chain parallel to  the  shoreline, and 2)
                                          12

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stations forming  a chain perpendicular to  the shoreline, usually forming  a  transect
originating at a river mouth or harbor and extending into the open lake (Figure 10).

      Although major  differences  existed between the  four  data sets,  the  techniques
employed to summarize and analyze the data were as uniform as  possible.   The entire
nearshore  region  was  subdivided  into homogeneous  sections referred to as "reaches"
(Figure 9 and 10,  Table 4). A total of 20 reaches were designated along  the  entire lake
shore.   Areas that  presented  unique conditions   (i.e., exceptionally  high  nutrient
concentration) such as  the  Maumee River  Bay  at  Toledo,  Ohio  were designated as
individual reaches. This approach was taken  in order to avoid areas having significantly
large point sources from heavily influencing mean  concentration calculations of  adjacent
regions not subject to strong localized effects.  Mean and median reach concentrations
were calculated for each cruise and year; however,  only yearly  values will  be presented in
this report.  In addition, selected transects perpendicular to the shore were examined in
order to define the sharp concentration gradient occurring within 5 km of the nearshore
zone.  Individual stations located in harbors and/or river mouths were examined to obtain
yearly mean concentrations in regions considered to be problem areas.  In  the three types
of geographical divisions, all station  values measured were averaged. In other words, all
surface and bottom values measured over the consecutive 3-day period were averaged in
order to obtain a  mean for an individual station. The individual station values were then
averaged for an entire reach area to yield a reach mean.

Data Compatability

      When attempting  to  summarize the data collected by the agencies  involved in the
two-year program, data compatability  became  an extremely important consideration.
Consequently, an assessment of data  compatability was undertaken  in order to determine
if the major data sets could be used as one unit.  Each of the participating U.S.  agencies
was contractually  obligated to carry out a quality control (QC) program and evaluate their
own program as an internal control on the reliability  of their  individual databases.  The
Canadian agencies also have similar programs  providing internal QC information.  Thus, as
much of the individual QC data that was available was  utilized in the analysis.

      Analysis of Split Sample Data.  An estimate of  precision can be generated from the
standard deviation of differences between values  obtained in  duplicate analyses of the
same sample. During the Lake Erie study, agencies split a designated number  of samples
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at  the  time of  collection.   These  "splits"  were processed  and analyzed  as separate
samples,  thus  the precision estimate encompasses  all aspects  of the collection  and
analysis processes.

      The  mean  and standard  deviation of  the differences  were  calculated  for each
parameter.  Any differences greater than  three times  the standard deviation were
excluded, and  a  new mean  and standard deviation were calculated.   This  process  was
repeated until  no additional  values were  excluded, or until five percent of the data  had
been  excluded.  The mean  of  the differences in this final data set,  divided by 1.128,
provides an  estimate  of the standard  deviation associated  with  an  analysis  for  the
parameter examined. (This standard deviation applies to the analytical  result,  not to the
difference between a pair of  analyses.) (IJC, Data Quality Work Group 1980.)

      The procedure for iterative exclusion of large differences was adopted because 1) it
could be  done automatically by computer;  2) it was an  objective process; and, 3) it
produces a precision estimate based on  most of the data (at least 95 percent) but  not
inflated by the abnormal situation when  the  system was, in the broadest sense, out of
control.

      The results of the split analysis are presented in Table 5.  In general, these results
suggest that differences in precision between  groups were not  significant; thus, precision
was not a factor in combining the  data sets.   While the precision associated  with a
particular  parameter varies  from year  to  year  and  from agency to  agency, even  the
largest  standard deviations were not large in context of the concentrations involved (i.e.,
the relative standard deviations  are generally quite small, on the order of one percent or
less).  The exceptions were encountered with the metal parameters, many  of which were
at levels close to detection limits. Here the limited data available suggests that precision
was often not good enough to permit any but the most coarse-scale data analysis.

      Analysis of  Round Robin Results.  The Data Quality Board of the International 3oint
Commission provided a continuing series of  round-robin studies in  which samples were
sent to  participating labs for analysis.   Each study involved analysis of several (usually
related) parameters covering a broad  range of concentrations.  Many of  the samples were
of natural waters, or natural waters spiked to increase concentrations.  The results were
evaluated in reference to the  range of values  reported  by  the participants  with  the
assumption that the median value reported is the best estimate of the true value for that
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 sample.  This  assumption may be questionable for some analyses,  particularly when
 concentrations  were very close to detection limits, resulting in one or two laboratories
 doing accurate  work but being flagged for poor performance because the majority of the
 laboratories skewed the  mean upward.   Generally this  approach served to  identify
 laboratories that are erratic or biased in their performance. All laboratories involved in
 the Lake Erie study participated in the round-robin series to some extent.

      Results of  the I3C studies involving  Lake Erie  Intensive  Study  participants
 conducted shortly before and during the Lake Erie study were evaluated for indications of
 bias and erratic performance.  The data includes multiple analyses, usually as part of two
 or  three separate  round-robin  studies, involving  29 parameters. In general, the results
 show that substantial biases between laboratories are common, that erratic results  are
 common, and that  good performance  on one round-robin  study does  not  predict good
 performance on the next study involving the same parameters or visa versa.   Several
 laboratories,  mostly  Canadian,  had consistently  good performances for almost  all
 parameters, but most laboratories exhibited poor performance  at least occasionally on
 some parameters.

      These results suggest that combining data from different agencies is unwise, at least
 without careful  scrutiny of the data compatibility. It is important to consider such results
 in context with  the purposes for which the data is to be utilized.  The results of the round-
 robins evaluated are presented in Table 6.

      Analysis of Data and Adjacent Stations.  Since the purpose  of combining data sets is
 to answer questions concerning the lake as a whole, it could be argued that the  ultimate
 data compatibility test lies in the  data itself, that is, the comparison of values at stations
 along the boundaries at which the  different agencies interfaced.   One could consider the
 data compatable if differences  across boundaries  were not large in comparison with day-
 to-day differences found at each station, or in comparison with  some other measures of
 small scale internal variability.

      This approach was  examined by choosing pairs of stations which interfaced agency
boundaries and comparing the data obtained at stations  over the three  successive days'
sampling. If the two triads of data overlapped, the data  were judged to be similar. This
judgement was made for each date and level sampled at two or more pairs of  stations.
The results  were tabulated as  the number of observations judged the same, the number
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judged high in laboratory  1 relative to  laboratory 2, and  the number judged low  in
laboratory 1 relative to laboratory 2.

     The approach was weakened by the spatial and temporal separation of the stations.
Some "nearest" station pairs across  boundaries were 6 km apart, while others were at the
same location within navigational accuracy. Some sampling intervals involved overlap  of
sampling dates, while others involved intervals of up to 10 days between sampling by the
two laboratories. Arbitrarily, any comparisons involving sampling time separations greater
than 10 days were not used in the analysis. Allowance was made for expectable seasonal
changes such as changing temperatures and dissolved oxygen concentrations in the spring.
Bottom samples  showing indications of  hypolimnion  water samples were  not included
unless all samples in that comparison seemed to be hypolimnion in origin.

     An additional problem  encountered involved the difference in sampling routine  used
in the nearshore  study versus the  open lake program.   The  nearshore stations were
sampled three days in succession,  while the open lake stations were sampled only once per
cruise.  Thus, comparisons between two agencies working in the nearshore zone involve six
data points, comparisons between nearshore and open  lake agencies  involve  four, and
comparisons between two open lake agencies  involve only two data points. Where more
data points  are involved in the comparison, the likelihood of reaching a no-difference
judgement was greater. Indeed,  when only two  data points are involved, the values will
usually  be different.   Since the final  assessment is usually  based on  10 to 20  such
judgements, and only parameters  which showed consistent divergent behavior were judged
to contain a between-laboratory  bias, this difference in data density  is probably not a
serious problem.  The results of these comparisons are shown in Table 7.

     In general, data compatibility is not seriously affected by precision except for metal
parameters  where  water concentrations were at very  low levels.  However, between-
laboratory biases are  commonly significant  compared to  the  temporal  and spatial
variability.  The question of data compatibility is a relative one, and judgements about the
compatibility of the data  must ultimately be  made in the context of specific research
questions to which the  data  is applied.   However, the implication of  the analyses
presented here is that it is not safe to assume that data gathered by different agencies,  or
even by the same agency in different years, is compatible.

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      During USEPA-GLNPO cruise five  1978  an intercomparison study with OMOE was
 undertaken.  On July 23 water samples were collected at seven stations (29, 30, 31,78, 32,
 33, and  3*, Figure 3)  from Ashtabula, Ohio to the Canadian shore.   USEPA sampled at
 each location  with replicate  collections split between three groups, USEPA-GLNPO,
 OMOE Toronto,  and OMOE  London.  Several  parameters were analyzed, however,  only
 total phosphorus  will be discussed in this text. Preliminary analysis of the data stated:

      -   data ranged from 2 to 28 ug/1
      -   All labs reported to the nearest 1 ug/1
      -   London/EPA correlation was excellent with a scattered range of 4 4 ug/1, London
         being higher by 1 ug/1
      -   although on the average  Toronto  data agrees with the  other two labs results
         below 8 ug/1 tend to be high by an average of about 5 ug/1.

      All laboratories employed similar methodologies  for the total  phosphorus  analysis
 using the ascorbic acid procedure with persulfate digestion.

      Due to the lack of replication  this data set does not lend itself to rigorous statistical
 treatment, therefore, the results do not  provide the information  necessary to critically
 resolve differences between the labs involved in the study.  However, it was necessary to
 statistically  resolve some information from the comparison.  The Wilcoxon signed rank
 test was used to compare the medians of two data sets, i.e. USEPA  vs Toronto and USEPA
 vs London, since  the distribution of the data was not known.  Values from all stations and
 all depths were pooled for the  analysis.  The results of the nonparametric test indicated
 the  USEPA-GLNPO  results  were significantly  lower  than Toronto (a = 0.02)  and
 significantly lower than London (a = 0.01).  No comparison can be made with the  CCIW
 data set since  the cruise interval  and sample locations  were not compatable with  this
 study.

     Synopsis.  Data compatibility becomes  an important issue when attempting to
 assess such a complex  database.  Therefore, any program designed to involve  numerous
 agencies must have this consideration.  Detailed planning of the project must incorporate
 a QC  program not only for the individual  participants,  but also provide  for comparisons
 between  participants. Precedent for field intercomparison studies has been established by
Robertson et al. (197*) and Feder and Zapotosky (1978).  This type of study is difficult,
but it serves a very valuable and obvious function. Prior to the initiation of the 1978 field
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season, CCIW (organized by N. Burns) attempted to coordinate such an effort by bringing
all the participating groups together to discuss the above mentioned problems.  However,
little was done to follow through with this effort by the U.S. participants. Consequently,
the problem of data compatibility remains one of the major nemeses of these large multi-
agency programs.
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                                      RESULTS

      The results are divided into two sections, OPEN LAKE and NEARSHORE.  Within
each section the major  parameters are presented,  providing an adequate database was
available.  Frequently, both the open lake 1978 and 1979 field season data were available,
however,  due  to  the year-to-year similarity  in  distribution patterns and seasonal
concentrations, only the most representative and complete data set was utilized.  This
policy was adopted to reduce the volume of the document as well  as to eliminate the
redundancy resulting from  providing a detailed description of each parameter for the two
field seasons.  The CCIW-NWRI 197S data set was considered the primary  open lake
database since the  basin coverage  was extensive and the quality of  the analysis was
considered to be  superior.  In contrast, the nearshore was found to be considerably more
variable than the open lake, consequently, two year summaries  were used to present the
nearshore database.

Open Lake

      Temperature.  The Lake Erie seasonal surface temperature cycle follows a similar
pattern annually. A comparison of surface temperature contours from 1970 through 1979
indicates differences only in the rate of spring warming  and fall  cooling with minor
deviations  in contour patterns resulting from short-term meteorological episodes.  The
1979 surface temperatures for the three basins are shown in Figure 11 and represent a
typical annual cycle.

      The western basin is generally ice-covered by  early January with ice formation  on
the central and eastern basins by late January. Depending on the severity of the winter,
ice is present in all three basins until late March.  The western basin is first to lose ice
cover, followed  by the central  and  eastern  basins  in a  west to  east succession.
Frequently, float ice remains in the eastern basin through late  April, resulting in delays
for surveillance cruises.

     The surface waters of the  entire lake continue to warm through the spring into the
late summer. The shallow western basin is the first to warm, frequently reaching 10°C  by
mid-May and remaining 2-4 C warmer than the central and eastern basin epilimnion until
late July or early August. During late August the surface temperatures of all three basins
are nearly  uniform, having reached a maximum of 20-25°C. With the onset of fall, the
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western basin  begins cooling and continues cooling  more  rapidly than the  central and
eastern basins.  Not until late December or early January does  the entire lake become
nearly uniform in temperature.

      Unlike the consistency of  surface or  epilimnion  temperatures, the  hypolimnion
waters may show significant temperature variation  from year  to year.   The  bottom
temperatures in unstratified regions, i.e. western  basin and nearshore regions, seldom
differ from surface  temperatures.  However, by late summer in the stratified regions  of
the central and eastern basin hypolimnion temperatures can  be 10-20°C colder than the
overlying epilimnion water.  Through the  stratified  season  hypolimnion waters of the
central basin increase  from 5 to 10°C.  The  warming of the central basin  hypolimnion
varies from year to year depending upon the  initial hypolimnion temperature, thickness
and  climatic  conditions through  the stratified  period.    Eastern  basin  hypolimnion
temperatures do not increase at the  same rate as the central basin (Figure  12).  In the
deepest portions of  the eastern basin, hypolimnion  temperatures may only increase 2°C
through the stratified period.  In addition  year to differences in eastern basin  hypolimnion
temperatures are less variable than in the central basin.

      Thermal Stratification and Structure.  In contrast to the  western basin, both the
central and eastern  basins stratify during the summer months.  The thermal structure  of
the central basin is of particular importance due  to the  recurring  anoxic  condition
associated with the hypolimnion during the late summer months. Since any western basin
thermal structure is  short in duration and the eastern basin hypolimnion remains thick and
well oxygenated throughout the stratified season, much of this text will specifically deal
with the problematic central basin.

      As mentioned,  the western basin does not stratify in the conventional manner  as do
the other two basins.  Due to its shallow nature, the western  basin remains isothermal
throughout  most of  the  summer months.   Generally, two  mechanisms  can lead to a
stratified condition or a strong thermal gradient (Bartish  1984).  First a period of warm,
calm  weather may lead to the formation of a thermal gradient which in turn inhibits
mixing of bottom waters with the warmer overlying water.  Second, central basin water
(mesolimnion/hypolimnion) can be entrained into the western basin during seiche activity.
This central basin water mass is cooler and denser than western basin water, resulting in a
"stratified"  water column.   Regardless  of how thermal  structure  is established in the
western basin, it only remains stable  until wind velocities increase  sufficiently to cause
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the entire water column to mix.  Generally, complete mixing occurs within a few days of
the onset of the "stratified" water column.

     Stratification in the central basin is considerably more consistent and stable than in
the western basin. The first indication of stable stratification is evident in late May.  The
initial  thickness  and  temperature  of the  hypolimnion are  dependent  on the  spring
meteorological conditions; thus,  the physical structure  of  the  hypolimnion is somewhat
different each year.  Figure 13 presents the 1978 central basin hypolimnion thickness
contours for each cruise. The central basin stratified period lasts approximately 100 days
with fall turnover generally occurring by mid September.  The seasonal changes in thermal
structure typifying the mid-central basin in 1979 are presented in Figure If.

     The eastern basin is the deepest of the three basins,  having a hypolimnion which is
thicker and colder  than that found in the central basin.   The  hypolimnion temperature
generally does not exceed 6°C  and the dissolved oxygen remains closer to saturation
(> 60%) throughout the  summer.  The eastern basin hypolimnion assumes a conical shape
following the  basin topography.   The  thickest portion  of  the  hypoiimnion  located
approximately 13 km east of Long Point is in  excess of 25 m (Figure 13). The 1979 annual
thermal structure for this region is presented in Figure 15.

     The average hypolimnion thickness of  the eastern basin is generally twice that of
the central basin and the mesolimnion is from 3 to 5 times thicker. The thickness of  the
mesolimnion was  found  to be an  important factor in the interaction between the central
basin hypolimnion and  the eastern  basin  mesolimnion.   Boyce  et al. (1980) found that
eastern basin  mesolimnion water could be transported  into the eastern  portion of  the
central basin.   This intermittent event, induced by specialized meteorological conditions,
results in a reverse flow (east to west) over the Pennsylvania ridge, representing a major
interaction between the basins.  This eastern basin entrainment can significantly  re-
oxygenate the  eastern  portion  of the central  basin; thus, the  event is an  extremely
important consideration when budget calculations are made for either basin.

     From May 1979 through June 1980, as part of the two-year intensive  study, an array
of more than 29  current meters was positioned throughout the three basins in order to
obtain  detailed information on current directions and speeds as well as thermal structure
(Saylor and Miller 1983). This report has only recently been  issued. The reader  is urged to
                                         21

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review this study for  further information on the physical characteristics of the  three
basins.

      Limnion Volumes.  Accurate measurements  of temperature (±0.1 °C) versus  depth
(+0.25m) at each sampling station are a basic requirement for Great Lakes research.
Bathythermograph traces, such as those shown in Figures 14  and 15, provide  an accurate
record of sounding depth and thermal structure, critical for  both physical and chemical
data  analysis.   Generally, sampling  regimes are based  on  thermal structure,  thus it
becomes necessary to have accurate temperature/depth  profiles in order to determine
appropriate sampling depths in and around the thermocline.  Since the thermal structure
not only varies from  cruise to cruise but from station to station, profiles must be taken as
a routine measurement.

      Once the detailed thermal  structure has been defined, basin-wide limnion depths,
volumes  and areas  can  be calculated.   This  provides  the necessary information to
calculate  volume and  area weighted  concentrations as well as total quantities  (metric
tons)  for any parameter.  These  values are subsequently  used  for basin-wide and whole
lake budget calculations.  Thus, it is necessary to obtain  the most  accurate  volume
estimates possible in order to make year-to-year comparisons meaningful.  This becomes
particularly critical  for central basin hypoJimnion dissolved  oxygen and nutrient models
since  small volume differences can significantly influence the  analysis.

      Western  basin  limnion volume estimates (USEPA-GLNPO) for  1978 and 1979  are
presented in Table 8.  It is noteworthy that in June and July of 1978 a thermal gradient
was recorded but was  not encountered in 1979.  The 1978 data indicated  a thin layer of
colder bottom  water  in the eastern portion of  the  basin.   As previously discussed,
stratified conditions  may develop  several times during the summer, but lasting only  a few
days.  The fact  that stratification was not documented  in 1979  only indicates that  the
thermal condition was not encountered during the cruises and not that it did not exist
sometime during the  summer.

     The  two-year (1978-1979) limnion volumes and thickness for the central and eastern
basins (CCIW-NWRI) are presented in Tables 9 and 10.  The data indicates a somewhat
thicker hypolimnion in  both basins during 1978. This is particularly evident during the late
spring in the central  basin.  The initial spring hypolimnion  thickness in 1978 was over 2 m
greater (30%)  than that found  in  1979 resulting in a thicker  hypolimnion  throughout  the
                                         22

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 1978 stratified season.  A similar thickness relationship existed in the eastern basin during
 both 1978 and 1979.

      The  central  basin epilimnion frequently  comprises over 60% of the total water
 volume and during the late summer  may exceed 80%.  On  the other  hand, the  eastern
 basin  epilimnion rarely exceeds  60% of  the  total basin volume with the hypolimnion
 generally comprising 10-25%.   As previously pointed out, the mesolimnion in the  eastern
 basin  is significantly thicker  than the mesolimnion of the central  basin.   Eastern basin
 mesolimnion frequently accounts for  30% or more of  the total volume while the  central
 basin mesolimnion usually accounts for only 10% of the total volume.

      The  1978 and 1979  thermal  structure  data typify  the  year-to-year  variation
 encountered in the  three basins  of Lake Erie.  Thus, in order to calculate year-to-year
 nutrient budgets, verify predictive models  or conduct trend  analysis,  thermal  structure
 data is vitally important.

      Dissolved Oxygen (P.O.). Dissolved oxygen has been a major environmental concern
 associated with the eutrophication of Lake Erie since the early 1950s.  The focus of ©2
 depletion problems has been on the bottom waters of the western and central basins, while
 the eastern basin Oj concentrations  have  remained above critical levels throughout the
 current period of record.

      The recurring  problems of low D.O. concentrations at the sediment-water interface
 are directly related to thermal stratification in  both the central and western basins.  The
 circumstances leading to 0- depletion in the western basin are as complicated and varied
 as the situation encountered in the central basin. In either situation the bottom waters do
 not freely  exchange with the  O- saturated (90%) overlying water mass; thus the  limited
 supply of hypolimnion O_ is depleted.

      All recorded  instances  of  major  O2 depletion in the western basin have been
 associated  to some degree with the  formation  of a thermal gradient  (Britt 1955, Carr
 1962, Bartish 198*, Wright 1955, Hartley and Potos 1971). Due to the high oxygen demand
 rate in the western basin (Davis et al. 1981), anoxic conditions may develop in only a few
 days following stratification.  For example, if a thermal gradient formed 2 meters above
 the bottom with an initial O- concentration of 5  mg/1, it would take between 3 and 4 days
for anoxic conditions to develop.  When anoxia occurs, both the flora and fauna within the
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region become stressed.  In addition, soiubie  nutrients are released into the overlying
waters, further stimulating algal growth.  Since anoxic conditions develop intermittently
over the summer, there is little documentation of the frequency or extent of the problem.

      The  1978  western  basin data  (USEPA-GLNPO)  shows  the  average  surface
concentrations of D.O. (Figure 16).  At no time during the field seasons did the average
D.O. drop below 7 mg/1 in the surface waters, and no critically low values were evident
for samples taken 1 m from the bottom.  Only during the late  June survey were small
pockets of stratified waters encountered with limited O2 depletion west and north of the
Bass Island region.  This is not to imply that critical oxygen levels at the sediment water
interface  were not  reached other times during the summer of 1978; however, since the
conditions leading to low bottom D.O. were  largely a  function of meteorological events,
episodes of low D.O. could be easily missed during a 3-week cruise interval.

      The dissolved  oxygen database discussed for the central  and eastern basins  was
supplied by the CCIW-NWRI 1978 hypolimnion study.   Due to the intense station pattern
and number  of surveys  during the stratified period,  this database provided the most
thorough examination of hypolimnion O« yet undertaken in the stratified basins. The 1978
thermal  structure,   hypolimnion thickness  and temperature represented near  average
seasonal conditions.

      Like the western basin, central basin  surface waters remained close  to the 100%
saturation level throughout the field season with spring values frequently exceeding 100%
due   to   phytoplankton  photosynthetic  O2  production   (Figure  17).     Hypolimnion
concentrations, immediately following the formation of the thermocline, are very similar
to epilimnion values.  During  the stratified period, exchange with the highly oxygenated
epilimnion waters (90%)  is greatly inhibited by the thermoclinej  thus the quantity of O2
present in the hypolimnion at the formation of the thermocline is a critical factor
controlling the quantity of O2 remaining at the end of the  stratified period.  Through the
summer months hypolimnion O2 values continually decreased, reaching concentrations
below 4 mg/1 by mid-August. The areal O2 distribution throughout the hypolimnion is not
uniform (Figure 18).  Concentrations in  the western  portion of the  central basin and
particularly in the Sandusky sub-basin reflect the influence of the nutrient and plankton
input  from the western basin and Sandusky Bay.  A distinct southwest to northeast and
west to east gradient of increasing O2 concentrations is evident throughout most of the
stratified season (Figure 18).  This  is most clearly seen in  the contour of the late August
                                         24

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 survey.  By early September much of the basin was anoxic (< 1 mg/1) and remained anoxic
 through the  duration of the stratified  period.  Once turnover occurs, the water column
 becomes isothermal and homogenous relative to O2 concentration, returning to levels near
 100%  saturation.   The central  basin  oxygen budget  is  more  complicated  than this
 explanation and will be dealt with in greater detail later  in this report.

      The eastern basin epilimnion D.O. concentration remains near 100% throughout the
 summer months, and during  the spring diatom pulse, values increased to greater than
 140%.  Unlike the central  basin, the eastern basin is not subject to periods of anoxia.
 Hypolimnion mean oxygen concentrations remain above 6 mg/1 throughout the stratified
 period (Figure 19).

      Nutrients.  The lakewide distribution pattern of the major nutrients remains similar
 from year to year.   The individual  basin  nutrient distribution patterns most frequently
 presented  reflect the circulation patterns within the individual  basins  under normal or
 moderate wind  conditions.   This "normal" pattern  can  be altered under  extreme wind
 stress, i.e. severe storms.  However, moderate conditions account for the majority of the
 nutrient distribution  patterns seen in contours and generally  reflect the water transport
 model describing major circulation  patterns developed  by  T.J. Simons  at CCIW (Simons
 1976).

      The following sections will illustrate the distribution patterns of the major nutrients
 using the 1978-1979 CCIW data.  This data set provides the most extensive coverage of
 the central and eastern basins.  Unfortunately,  the western basin was not sampled during
 either CCIW  research program; thus, the western basin USEPA-GLNPO data was utilized.
 Graphs  of  1978 and 1979 mean basin concentrations for the epilimnion and hypolimnion
 will  be  presented whenever the data is available.   Tables  presenting the limnion
 concentrations and tonnages of several parameters will also be included. Only a detailed
 description of the total phosphorus distributions will be presented  due to the similarity of
 high and low concentration  regions for  most nutrients  making additional description
 redundant.

     Total Phosphorus (TP).  The seasonal horizontal  epilimnion concentrations  of TP
 show several unique  distribution  patterns.  First, a distinct concentration gradient is
evident in  the transition region between the western basin and central  basin.  The same
gradient is  also  evident  between the  central and  eastern  basins;  however, the
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concentration  difference is considerably less.  Th's basin-to-basin gradient leads to a
general  west to east trend  of  decreasing concentration.   Since the major sources of
nutrient loading to the lake ( >50%) enter  the western basin and the natural lake flow is
from west to east (Detroit River to Buffalo River), the gradient evident in  many of the
contours presented in this report  and  in similar reports follows a  seemingly  logical
pattern.

      This description of the TP distribution pattern represents a simplified explanation of
the normal horizontal gradients; it  must be re-emphasized that the circulation patterns
examined and discussed by  Simons, Boyce,  Bennett, Saylor and others represent a complex
combination  of many physical variables, i.e.  temperature  gradients, thermal structure,
wind fields,  currents, etc., and  together influence the overall distribution of chemicals
within the lake.    In-depth physical process research is critical to the understanding of
the dispersion of pollutants in the three basins.  This point is made clear by examining TP
dispersion or  contour patterns in the central  basin.   As  previously  discussed,  the
transitions between basins are characterized by  north-south contours representing the
gradient structure, but within the central basin contours are east to west paralleling the
south shore.  TP concentrations  are highest along the south shore with values frequently
double those  found at the center of the lake. These high south shore concentrations result
from two sources;  first, western basin  water with high nutrient  concentrations remain
confined to the south shore region as the water mass enters the central basin through the
passage  south of the island region,  and second, point source loading from urban centers
along the entire shoreline, i.e. Cleveland.  The predominant flow  in the nearshore region
is west to east, but currents do carry the high nutrient Iadened water into the  basin to mix
and disperse  with the open lake. Mixing the nearshore waters into the  open lake is a
complex dispersal process  resulting in unique transition patterns (Figure 20).   Central
basin south shore contours  show a variable cruise-to-cruise pattern shifting in  a north-
south  and  east-west  configuration  depending  on  meteorologically  induced  current
patterns. Thus, the better  our understanding of the hydrodynamic flow structure of the
lake,  in  particular the interface of  the open lake  with the  nearshore region, the greater
our understanding of the effect pollutants will have on the lake ecosystem.

      In contrast to  the western  basin and  the south shore of the central basin, the north
shore of  the central  basin and  the entire eastern basin are not  subject to extensive
problems resulting from external point source loading.  Due to erosion of the clay bluffs
lining the north shore of the  central basin, nearly 13,500 metric  tons  of  phosphorus are
                                          26

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 added to the lake annually (Williams et al. 1976).  The major phosphorus contribution of
 this non-point source is in the form of apatite phosphorus which has a very low solubility
 and is not biologically available (Williams et al. 1980); consequently apatite phosphorus is
 not a significant source of available phosphorus and is not included in loading calculations.
 The populace along the north shore areas is confined to small communities and farmland
 with little or no industrial development.  Therefore, when examining the contour maps of
 the northern shore,  localized effects (point sources) and shoreline contributions (non-point
 sources) are  not prevalent  features.   One exception, the Grand  River located  in  the
 eastern  basin is the largest single point  source  of nutrient loading to the entire north
 shore.  As with all tributary sources of loading,  the most dramatic effects can be seen
 during the spring when nutrient concentrations and water flows are highest.

      An area of future concern  is the newly-forming industrial and  urban  complex
 developing in the eastern basin at Nanticoke, Ontario.  Due to the care taken with  the
 initial planning of this complex, minimal impact has been noted in the area; however, this
 region must be  monitored routinely. To date, numerous reports have been issued  by  the
 Ontario  Ministry of the Environment  (OMOE).  The reader can obtain further detailed
 information by contacting OMOE.

     The  seasonal  changes in  TP  concentration tend to  follow a  yearly pattern
 characteristic of the individual basin (Figures 21-26; Tables 11-13). The 1978 western
 basin data (USEPA-GLNPO) is too sparse for any meaningful interpretation (Figure 21);
 however, the  1979  data  presents a more typical  seasonal pattern  (Figure 2*).  Highest
 concentrations are encountered during the early  spring months, February through April,
 resulting from a combination of peak external and internal loading  events.  The external
 load is  high  due to both agricultural runoff and  the increase  in  sediment-phosphorus
 transport of the instream bed load.   This source of western basin loading has been
 characterized and quantified by Logan (1978), Logan et al (1979),  Verhoff et al. (1978),
 and DePinto et al. (1981). Internal  loading is also  a major source of TP to the basin since
 spring  is frequently characterized by high winds  and storms  which readily resuspend
 settled material in the shallow western basin.  Consequently, the western basin spring TP
 values are frequently over 50 ug/1  in the open basin and in 1979 the  mean western basin
 concentration exceeded  100  ug/1.    Through   the  remainder  of  the  summer,  TP
 concentrations generally  decrease, although sharp increases in concentration can occur
during the mid-summer months as a result of an  occasional storm  or periods  of anoxia.
The duration of  mid-summer sharp  concentration  increases is usually a few days.  During
                                         27

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the fall,  concentrations again  increase as a result of  increased  tributary loading and
resuspension.

      A somewhat similar seasonal pattern is  evident in the central basin, best seen in the
1979 CCIW database (Figure 22 and 25).  The highest TP concentration of the field season
generally occurs during the unstratified periods of the spring and fall.  This is because the
central basin is subject to internal and external loading, influences similar to those the
western basin experiences.  In addition, the transport of nutrient rich western basin water
into the central basin contributes to the concentrations characteristic of these periods.
Since the central basin stratifies from approximately late  May  through early September,
resuspension of the settled material does not contribute to the internal loading of the
epilimnion within the stratified  regions.  Increasing hypolimnion  concentrations of TP can
originate from  three  sources:   first,  from  decaying plankton  settling through the
thermocline into the hypolimnion, and second, from anoxic release of sediment-bound P in
the later weeks of stratification (late August until turnover  in mid-September).  Thirdly,
peaks of  TP occur in the hypolimnion resulting  from the resuspension  of the loosely-
floculated material at the sediment water interface. This occurs during very active storm
periods when seiche and internal wave activity induce accelerated hypolimnion current
velocities (Ivey and  Boyce 1982).   If the hypolimnion  is sampled before this material
resettles, hypolimnion concentrations will be significantly elevated.

      The eastern basin is least influenced by either  spring loadings or resuspension  of
bottom materials;  thus,  the concentrations in  this  basin  do not  show  the extreme
fluctuations encountered in the central and western basins (Figure 23 and 26).  Seasonal
concentrations indicate a pattern similar to that described  for the central basin with, the
highest values found  in the spring followed by  a  continual decline  through the stratified
period.  A small increase is evident following turnover;  however, concentrations did not
reach spring levels or approach central basin fall concentrations.

      Forms of  Phosphorus.  In addition  to  routine measurements of total phosphorus,
three additional forms were also measured.  The terminology used to delineate the forms
unfortunately is not uniform throughout the literature; however, the forms measured are
method specific and  consequently  separation is not difficult.   The  standards  forms
measured and synonymy are:
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      1.       Soluble Reactive P (SRP) =  Dissolved Ortho P
      2.       Total Filtered P (TFP)  = Total Dissolved P

      An additional form which can be measured directly or be obtained by difference is
 Participate P (PP):

                        TP - TFP =  Particulate Phosphorus (PP).

      These  four  forms of Phosphorus, TP,  TFP,  SRP  and PP,  constitute the  normal
 fractions  determined  during  surveillance studies.   It  should  be mentioned that  an
 additional form can be determined by difference:

                    TFP - SRP  = Soluble Organic Phosphorus (SOP)

      This fraction  is composed of high molecular weight organic compounds.  These
 various  forms of phosphorus  are all  associated with conceptual compartments which
 interact within the  lake ecosystem.  Details as to phosphorus cycling and turnover rates
 for the various components in the phosphorus pool  can be found in a series of papers by
 Lean (1973),  Lean and Nalewajko (1976), and Lean and Pick (1981).

      The largest  contributing  fraction to total phosphorus is the PP fraction, comprising
 from 50-70%  of  the total.   Particulate  phosphorus  follows  distribution and seasonal
 patterns similar to  those of total phosphorus.  PP concentrations are highest during the
 spring and fall unstratified periods when resuspension is greatest.  It also is evident  that
 PP concentrations follow a decreasing  concentration gradient from west to east.  During
 periods  of high plankton production, i.e. western basin mid-summer and nearshore regions
 throughout the year, the PP fraction is also increased.  Consequently, this fraction serves
 a dual role as a source and as a sink for  available phosphorus.

      Soluble reactive  phosphorus is  the most commonly measured fraction other than
 total  phosphorus.    This fraction  represents a  measure  of  the biologically "readily
 available"  phosphorus;   thus  concentrations  of this  nutrient  generally  remain  low
 throughout the active  growing season.   Western  basin  summer mean concentrations
fluctuated from 3  to 12 ug/1 with values rarely dropping below 1 ug/1. During peak spring
loading or periods of anoxia, concentrations may exceed 10 ug/1 in the open basin.
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      Epilimnion SRP concentrations in the central and eastern basins generally remained
below 2  ug/1 through the stratified period (Figures 27 and 28; Tables 11-13).  It is  not
uncommon for values in the mid lake to drop below detection limits (< 0.5 ug/1) from  the
end of July through much of  August.   Hypolimnion concentrations increased throughout
the stratified season in both basins: however, a much greater increase was evident in  the
central basin.  As in the western basin, seasonal soluble reactive concentrations  peak in
the spring as a result of both external and internal loading and increase again in the late
fall when storm-induced resuspension is common.

      Numerous difficulties have been recognized in measuring concentrations of SRP.
Frequently  concentrations  are found  to be  near  or  below  detection  limits  making
quantification of this phosphorus form difficult.  The analytical problems associated with
measuring SRP have been discussed in a series of papers by Tarapchak and Rubitschun
(1981), Tarapchak et al. (1982a, 1982b).

      Dissolved Inorganic Nitrogen. Dissolved  inorganic nitrogen is  composed of  three
fractions, all of which may be important nutrients for plankton growth:  (1) ammonia, (2)
nitrate plus nitrite and, (3) dissolved nitrogen (Nj).  Dissolved nitrogen was not measured
in any of these studies and will not be discussed in this text. Generally, the concentration
and quantity of nitrate plus nitrite in the lake is nearly ten times that of ammonia while
loading of nitrate plus nitrite is roughly 3.5 times ammonia loading.

      The distribution  pattern  and  seasonal  cycle shown by the two parameters reflect
both biological and chemical (redox) influences.  Western basin ammonia  concentrations
are generally  * to 5  times higher than  those in  the  other  basins  (Figure 29).  High
concentrations (100 ug/1) are found in the region of the Ohio tributaries and frequently in
the bottom waters of  the open basin  during  the summer.  As with soluble reactive
phosphorus, ammonia concentrations frequently showed extreme fluctuations during  the
summer  months.  The highest basinwide concentrations occurred during the spring when
tributary loading was the greatest (Table 14-16).

      The 1978 ammonia distribution  maps of the central and  eastern basins include one
map  representing  seasonal  epilimnion contours  (September)  and  a full season   of
hypolimnion  contours  (Figure  30).  In both  basins the epilimnion concentrations  of
ammonia remain below 10 ug/1 from May  to September with only small areas  of higher
concentrations found  along  the south shore  (Figure 30).   These  pockets of  higher
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 concentrations reflect external loading which can be attributed to urban and agricultural
 sources. The remainder of the lake is relatively uniform in concentration.

      Central  basin  hypolimnion concentrations  increase  during  the beginning  of  the
 summer with  highest  concentrations found  along the southern shoreline.  Hypolimnion
 concentrations peak by the end of the stratified season (Figure 31) as a result of plankton
 decomposition and ammonia regeneration  from  the sediments  in  regions  where  the
 hypolimnion has become anoxic.

      A similar seasonal pattern of  hypolimnion ammonia concentrations is encountered in
 the eastern basin with the peak occurring early in the summer (Figure 32). The eastern
 basin does not show another increase in the later period of stratification primarily due to
 the presence of oxic conditions throughout the hypolimnion.  In addition, the release of
 ammonia from the decomposition of plankton is not as quantitatively important to the
 hypolimnion of the eastern basin as it is in the shallower, more productive central basin.

      The lake-wide distribution of nitrate plus nitrite is very similar to that described for
 total phosphorus (Figure 33).  This similarity is expected since  the principal external
 loading sources of these two nutrients are similar.  Concentrations in the central basin
 reflect the loading influence from  the south shore and western  basin.  This pattern is
 clearly evident up through August in both epilimnion and hypolimnion waters.  The shore
 influence is evident in the eastern basin only during early June after which concentrations
 are fairly uniform.

      Seasonally, epilimnion  nitrate plus nitrite concentrations indicate a rapid decline
 from  peak  spring  values into  mid-summer  when concentration  becomes  more stable
 (Tables  14-16).    This yearly  cycle  is  most  evident  in  the  western basin  where
 concentrations decline by over a factor of three (Figure 34). Similar trends can be seen in
 the central and eastern basins but to a lesser degree (factor of 2) (Figure 35 and 36). The
hypolimnion concentrations in both  basins increase into the stratified season.  As anoxic
conditions  develop  in  the central basin hypolimnion and reducing conditions prevail,
nitrate plus nitrite concentrations begin to decline.   This pattern is not  evident in the
eastern basin since oxic conditions prevail throughout the stratified period.  During the
late  fall, the concentration  again increases  in both basins due to a slight  increase  in
loading.
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      Silica.   The seasonal cycle of dissolved reactive silica (DRS) is influenced by a
combination of external  and internal loading plus biological processes within the lake.
The effect of external loading is most evident during the early spring in the western basin
when mean concentrations can easily exceed 1.0 mg/1 and may reach over 5.0 mg/1 in the
nearshore  region (Figures 37 and 38).   Vernal point source influences  are also evident
along the southern shore of the central basin and the north shore of the eastern basin near
the  Grand River, Ontario.  By early summer, surface concentrations  in the central and
eastern basins have declined to seasonal lows and remain below 200 ug/1 in  the open lake
throughout  most of  the  summer (Figures 39 and  40).   Western basin concentrations
remained higher than the remainder of  the lake and continued  to fluctuate through the
summer months.

      Hypolimnion concentrations in the central and eastern basins  increase through the
summer reaching peak values by late summer-early fall just prior to  turnover.  Bottom
concentrations in the central basin  reach values greater than twice  those encountered in
the eastern basin largely  resulting from regeneration of silica during  periods of anoxia.
Once turnover has taken place the concentration  of silica in the surface waters again
increases due to the mixing of hypolimnion waters into the water  column plus a small
increase in external loading during the late fall.

      Following  spring loading events, the silica cycle (primarily in the central and eastern
basins) is largely controlled by biological activities,  namely  diatom  metabolism and
subsequent dissolution of  the  frustules.  Shelske and Stoermer  (1972) have shown that
phytoplankton   species  composition  and  community  structure  are  governed  by
silica/phosphorus concentrations in Lake Michigan.  Although undocumented, silica is
likely to play an equally important role in the  phytoplankton community structure in Lake
Erie.  The silica concentrations decrease in the central and eastern basins during the
spring until epilimnion silica becomes growth-retarding.  During the summer months much
of  the  silica  previously  complexed as  diatom  frustules  goes into  solution in  the
hypolimnion  to  be  recycled  following  turn-over increasing  silica  concentrations
sufficiently to support the fall diatom pulse.  Nriagu (1978) presents a detailed budget for
silica in  Lake Erie.   He  concludes  that regeneration of silica from  sediments greatly
exceeds annual external loading and that most of the biogenic silica is redissolved  in the
water column or at  the sediment-water interface.  Little of the diatom bound silica is
actually lost to the  sediments. It is apparent that the internal recycling together with
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external loading of silica provides sufficient  silica to maintain the diatom community,
which comprises 80% of the total phytoplankton (Munawar and Munawar 1976).

      Corrected  Chlorophyll  a  and Particulate Organic  Carbon.  Both  corrected
chlorophyll a (CCHLA) and particulate organic carbon (POC) were measured during the
two years. CCIW and  USEPA/GLNPO measured chlorophyll while only CCIW collected
data for POC.  The USEPA/GLNPO chlorophyll a values will be presented for 1978 due to
the longer EPA field season.

      The information  derived from these two parameters is somewhat compatible since
both  are  used  as  an  indirect measure of biomass.  Unlike  CCHLA, which  indirectly
measures only the phytoplankton, POC measures all particulate organic carbon present in
the water column.  The POC  consists of  the  carbon  associated with the phytoplankton
community as well as all the remaining members of the plankton community (i.e. bacteria
and zooplankton). More importantly, POC also encompasses the detrital carbon which may
contribute up to 90%  of the total POC measured. Therefore, any correlation between
POC and CCHLA/phytoplankton biomass may not necessarily be very useful.

      Similar lake-wide distribution  and seasonal  patterns  in the surface waters were
evident for both parameters.  Contour maps (Figures 41 and  42) indicate a distribution
pattern like that previously described for TP.  In general, a west to east decrease in
concentration can be observed throughout the field season with highest concentrations
found in the western basin and along the south shore of the central basin.  Only during the
first cruise did  the Grand River, Ontario in the eastern basin indicate a strong influence
relative to these two parameters.

     The concentration and total quantities of POC and CCHLA are presented in Tables
17 and 18 for each cruise and year. The western basin  CCHLA concentrations (Figure 43)
show  a unimodal seasonal pattern  with the highest concentrations found during the late
summer when phytoplankton biomass values are at their peak.  Epilimnion CCHLA and
POC concentrations (Figures 44-47) indicate similar-seasonal patterns in both the central
and eastern basins.  High spring values  result from  the vernal diatom pulse  plus  the
resuspension of detrital carbon from the sediments and tributary inputs.  Concentrations
decreased by late spring and  remained low  through  mid-summer.  The early to mid
stratified period presents  the  lowest  concentration of  particulate  material in  the
epilimnion as shown by  low phytoplankton biomass,  low CCHLA and POC  concentrations,
                                         33

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 and high transparencies.  By mid-August, concentrations begin to increase in both basins
 but are highest in the central basin.  During the fall, values continue to increase with
 conditions generally comparable to those of the spring.

      The central basin hypolimnion  CCHLA  concentrations were higher than epilimnion
 values  through the  early  summer  due to  the settling  of  the  spring  phytoplankton
 community; however, by late August limnion  concentations again became similar. In the
 deeper  eastern basin CCHLA hypolimnion concentrations were consistently lower than the
 epilimnion values reflecting the  decomposition taking  place in the water  column as the
 phytoplankton community settles into the  hypolimnion. POC concentrations reflect this
 difference between the two basins  even more clearly.  Central basin hypolimnion POC
 concentrations are nearly  always greater than  epilimnion concentrations  due to  the
 settling plankton  and detrital material during the early  summer  (Figures 46  and 47).
 Eastern basin hypolimnion POC concentrations exceeded epilimnion values only during this
 early summer  period, while during  the remainder of  the year epilimnion values were
 greatest.  This may be attributed to microbial decomposition of detrital  carbon in  the
 epilimnion and mesolimnion as the carbon settles through the water column.

      Turbidity and Suspended Solids.  Transparency measurements comprise one of  the
 longest  single historical data records for the  lake.  Since water clarity can be related to
 water quality  this information can be used for trophic assessments and long-term trend
 analysis. Water clarity is inversely  proportional to the quantity of particulate  material
 suspended  in  the  water  column.   Turbidity  results  from the presence  of suspended
 particulate material which is a combination of suspended organic and inorganic particles.
 The total quantity of particulate material found in the water column is measured when
 total suspended solids (TSS) determinations are made.   TSS  determinations are frequently
 further  fractionated into volatile  solids  (VS), the organic fraction and fixed  residual solids
 (FRS) the  inorganic fraction, providing additional information as to the  nature of  the
 particulate material.

      The composition of the particulate matter varies  seasonally and from basin to basin
 as well as within each basin.  For example, particulate material found near  the mouths of
 rivers (i.e., Maumee) or in embayments (i.e.,  Sandusky  Bay) consists largely of inorganic
material.  Normally, clays make up the largest percentage of inorganic matter originating
either from river  drainage  or  resuspension  of  previously settled material.   Organic
material, i.e. plankton biomass and detritus (autochthonous and allochthonous in origin),
                                          34

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combine to make up the remaining portion of the suspended particulate matter. The 1978
mean TSS distribution pattern presented in Figure 48 and cruise means presented in Table
19  characterize  the general distribution of suspended material throughout  the three
basins.   The highest TSS concentrations  occur in  the western basin from  Maumee Bay
along the south shore to Sandusky Bay in the central basin.  Similarly, the central and
eastern basins have the highest values along  the shores (both north and south), while open
lake regions show the lowest concentrations.  This pattern is similar to the 1970 turbidity
contours presented by Burns (1976b).

      The seasonal cycle of TSS reflects the influence of inorganic and organic particulate
matter  on water clarity in the three  basins.  This is most  evident  in the central and
eastern basins (Figures  49 and 50) during unstratified  periods when both VS and FRS
material are present in high concentrations.  Due to the violent nature of the fall storms,
the quantity of TSS is highest during the late fall.  In the stratified months,  the spring
plankton and inorganic suspended material settle  reducing the TSS values to minimum
yearly concentrations in the surface waters.  This is  accompanied  by a concentration
increase in the hypolimnion.  The  western basin is  susceptible to resuspension during the
entire year  (primarily spring and  fall)  (Figure 51),  and  receives large loads of inorganic
clays from agricultural drainage; thus, the inorganic fraction remains high throughout the
year. Western basin TSS values are usually double those of the central and eastern basins
with peak fall concentrations up to four  times  the  concentration measured in the other
two basins.

      The percent composition of  VS  and FRS also shows seasonal and basin differences.
During  1981 a  western  and central basin study was conducted in order  to examine the
inorganic and organic makeup of TSS (Fay et al. 1983).  Central basin epilimnion values
ranged  from 80% organic/20%  inorganic in the summer months to 17% organic/83%
inorganic during the fall. In contrast, western basin values ranged from 45% organic/55%
inorganic during  the early summer to 10%  organic/90% inorganic  in  the fall,  clearly
showing  the stronger  influence  of  inorganic material in  this  basin.    Burns  (1976)
determined a relationship  between turbidity and suspended inorganic material (SIM) for
April 1970:

                      SIM (gm-3) = 0.92 x Turbidity (3.T.U.) + .02

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      This equation was  then applied to a  transport model used to calculate  sediment
 movements  between  basins.   Considering  the ratio of  inorganic/organic suspended
 material  changes  with season  and basins, an  entire  seasonal  comparison  would  be
 necessary in order to most effectively utilize the transport model.

      The seasonal  turbidity cycle for each of the individual basins is presented in Figures
 52, 53, and 54. The 1979 data was chosen because early spring (April) data is  available
 which represents an important time period for suspended particulates.  Naturally, this is
 not true for areas with ice cover (i.e. western basin) between January and mid-March.  In
 fact, periods of maximum clarity are probably reached during ice cover.  In the late fall
 through early spring, when ice is not present, strong  winds together  with high  tributary
 loadings provide the necessary condition to reduce water clarity to minimum values.  This
 is evident in both the western and central basins in  1979.  Due  to persistent ice cover in
 the eastern basin, no data was obtained from this basin in April.  Western basin  turbidity
 values decrease by a factor of four from spring to early summer.  This improvement is a
 direct result of reduced tributary inputs of particulate matter  from the Ohio watersheds
 and a lessening of  the stronger wind events. Western basin summer  values  fluctuate in
 response  to storm activity  and phytoplankton development  but  generally  turbidity
 decreases into  mid-summer and again increases by late August through September due to
 peak  phytoplankton biomass  development.   Minimum turbidity occurs in late June and
 early July in  both the central and eastern basins with  a slight increase evident  by
 September, also due to increased phytoplankton  biomass. The fall is again similar to the
 spring with increased storm activity resulting in an increase in turbidity.

      Secchi.  Secchi transparency provides the simplest and most frequently employed
 technique for the measurement of water clarity.   Although  the technique is a simple one,
 there are many sources of variability  aside from natural patchiness of  the water, for
 example,  the whiteness of  the disc, the altitude of the sun,  the reflection from the water
 surface and the height of the observer  above the water. However, when  compared  with
 other parameters such as nutrient chemistry, secchi is probably the longest continuously
recorded  data base having the least number  of methodology changes.  For this reason, as
 well as its usefulness as a trophic status indicator (Gregor  and Rast 1979) and historical
 trend analysis, the secchi disc data was evaluated.

      The 1978  and 1979 secchi data  was analyzed in a manner compatible with previous
 Lake  Erie studies.  Individual station secchi values were area-weighted (Table 20) utilizing
                                          36

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the grid pattern established for the 1973-1975 Lake Erie study (Zapotosky 1980).  As
expected, the western basin consistently had  the lowest  water clarity  with  a 2-year
average secchi depth of 1.81 m (Figure 55a).   The averages for the central and eastern
basins were 4.32 m and 4.64 m respectively (Figure 55b, Table 20).

      Seasonally, the western basin secchi values can be subject to extreme fluctuation
due to the shallow nature of the basin. In general the peak secchi values occur during late
July to early August.  This was most evident during  1979 with historical data indicating
the same trend (Zapotosky 1980). The central and eastern basins show peak secchi values
from  late June through mid-July with both basins having nearly equivalent values.  The
intensity of the spring and fall  storms is the principal factor governing the water clarity
during the unstratified period.  An additional factor clearly evident during late August
through late September is the development of increased phytoplankton biomass.  This can
be seen by the increase in corrected chlorophyll a and is most evident in the central basin,
when secchi values are reduced at the end of summer. Table 21 shows the area weighted
secchi for  1974-75 and 1978-79.  Due to incomplete data, only the western and central
basin data is presented. The central basin values do not indicate any difference  over the
time  period; however, the western basin averages indicate an increase of over .5 m.  If
this represents an actual trend,  this could have important ramifications for the basin.

      By normalizing all western basin cruise averages to a value of  1 and multiplying this
factor by the central and eastern cruise means, basin ratios were calculated to illustrate
spatial differences  (Table 22,  Figure 56). The  results  clearly illustrate  the difference
between the turbid and productive western basin and the other deeper but less productive
basins.  The central and eastern basin area weighted secchi  values are greater  than the
western basin values by nearly 100 percent for  the two years period.

                                  TABLE 21
               AVERAGED AREA WEIGHTED SECCHI DEPTH (m)

                              WB          CB          EB
1974
1975
1978
1979
1.3
0.9
1.9
1.7
4.4
4.0
4.6
3.9
__
_
4.7
4.5
     Applying the trophic classification established  by Dobson et al. (1974)  for yearly
                                          37

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mean secchi data,  the  western basin would be classified as eutrophic  (0-3 m) and the
central and eastern basins as mesotrophic (3-6 m). The problem with such indices is that
they can indicate any of the three major trophic categories depending upon which portion
of the seasonal data is utilized.  For example, if one were to utilize the  maximum secchi
readings  found in July (7 m) it would indicate an oligotrophic condition for the open lake
portion of the central  basin  for  a  one month period each year.  This  is obviously  a
misleading measure as would be the use of early spring or late fall values when the water
is more turbid. Therefore the use of such indices should only be made with knowledge of
the full year's data set.

      Principal Ions.  The principal  ions  routinely examined  are  those  which make the
greatest  contribution to ionic salinity of the water body.  The total ionic strength of a
lake is generally measured as conductivity, and in bicarbonate lakes conductivity has been
shown to have a  proportional relationship with the concentrations of the principal ions
(Hutchinson  1957).    Several Lake Erie  studies  have measured the principal  ion
concentrations throughout the lake, while conductivity is routinely measured during most
all surveillance programs (Kramer 1961, Weiler and Chawla 1968,  Don 1972).  During the
intensive two-year study, conductivity, chloride (Cl) and sulfate (SO.) were measured on
every cruise during  1978 and  calcium (Ca), magnesium (Mg), sodium (Na) and potassium
(K) were measured during one summer cruise.  Due to the spatial and seasonal uniformity
of these  principal ions  only the  June 1978 surface concentrations will be presented as
contour distribution maps (Figure 57).

      Conductivity remains uniform throughout the open lake with  no extreme seasonal or
spatial fluctuations  evident. Station means for the two-year study indicate a west-to-east
increase  from 240 umhos/cm near  the mouth of the Detroit River to 300 umhos/cm in the
eastern basin.  The  low  values found near the Detroit River would  be expected since this
water mass originates from Lake Huron which has conductivity values ranging from 190-
200 umhos.  The highest concentrations found  in the open waters of western basin (280
umhos/cm) were found near the mouth of  the Maumee River and the Monroe power plant.
The highest central basin values occurred near Cleveland with a mean of 31* umhos/cm,
exceeding the IJC 1978 objective of 308  umhos/cm.

      The individual species contributing to  total conductivity can be classified into two
categories: first,  the principal ions which are considered to be conservative, that is, only
show  very minor changes in concentration resulting  from biotic interaction, Cl, Mg, Na
                                         38

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and K.  For example, Cl is frequently the conservative ion used in hydrodynamic model
calibration. The second category includes the remaining major species, Ca, SO^ and CO^,
which can show significant fluctuations resulting from metabolic processes induced by the
lake biota and therefore are not considered conservative.

      Of  the  four  conservative  ions,  Cl  concentrations are  the  most  important
quantitatively contributing over 12% of the conductivity.  Chloride concentrations range
from 10-21 mg/1 with a mean value of 20.0 mg/1.  The lowest concentrations are found in
the western basin in  the region of the Detroit River mouth.  The highest concentrations
occur in the central basin near the Cleveland-Fairport region and extend into the entire
eastern basin.  Of the total external chloride loading to the central basin, 80% enters via
the Grand River at Fairport, Ohio.  As would be expected,  the chloride concentrations
show only minor seasonal fluctuations at all limnion depths in both the central and eastern
basins (Figures 58 and 59),  while western basin concentrations show a distinct decrease
from May through November (Figure 60).

      Magnesium,   sodium  and  potassium  combined  contribute  only 10%  of  the
conductance.   Distributions of these ions reveal no distinct or related pattern  either
vertically or horizontally.  No seasonal fluctuations were evident as would be expected
since  biological utilization of  these ions is minimal.   Similar seasonal  results  were
confirmed from contour  maps of  Na  and K  presented by  Burns  et  al.  (1976c).  An
indication of south shore  loading of Na near Cleveland was evident during  1970 but was
not seen in the 1978 data.

      The  non-conservative ions SO., Ca and  CO-  are  known to show changes in
concentration both with  depth and through the season; however, no major fluctuations
were  evident for these three ions. Sulf ate concentrations in the surface waters contribute
approximately  15  percent of  the  conductivity.   Concentrations indicated only small
horizontal variations (median range 18-30 mg/1) and minimal seasonal changes (Figures 61-
63; Table 23).  Concentrations in the central  and eastern  basins during 1978  indicated
almost no change throughout the field season in any of the limnions while western basin
concentrations  indicated some fluctuations showing  a  peak during  August.  One  might
expect to see a significant seasonal change in  hypolimnion  sulfate concentrations of the
central basin.  During the  late summer when reducing conditions are  often prevalent, SO.
is  reduced  to  H.S; thus  a concentration decrease  is expected (Burns  and Ross 1972)
however no concentration change was found in 1978.  Lowest concentrations were found
                                          39

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near the Detroit River and highest values were evident near industrial centers.  Three
areas of high concentrations were noted:  (1) near the Monroe power plant, western basin;
(2) Lorain and Cleveland, central basin; and (3) the north  and east end  of the eastern
basin.  All three areas of high concentrations are the result of industrial emissions from
fossil fuel power plants and heavy industry. As with the previous ions, calcium does not
indicate any unusual pattern of distribution.  Lowest concentrations are found near the
Detroit River mouth  and  near  Cleveland,  with  the  remainder of  the  lake  showing
concentrations from 33-*0 mg/1.  Calcium is an important component of the conductivity,
comprising from 15 to 20 percent.

     Alkalinity was measured routinely throughout the three basins of the lake during the
intensive program.  Alkalinity values expressed as mg/1 CaCo^ equivalents provide a
measure  of  CO.  forms (carbonate-bicarbonate-carbonic  acid  buffering system) in the
lake.  Normally alkalinity values ranged from 85 to 105 mg/1  with little spatial difference
evident between  the  basins.   Highest  values were  generally  recorded in the  more
productive regions of the lake, i.e., the western basin, Sandusky Bay and the south shore
of the central basin. Phenolphthalein alkalinities were not uncommon in these productive
regions indicating pH values greater than 8.*.  Seasonally alkalinity values were somewhat
higher during  the  more productive months.  The carbonate  ion was the most  significant
ionic species, contributing over 50% to the conductivity in the open lake.

     The precipitation of CaCO- has been reported by USEPA-GLNPO in the western
basin of Lake  Erie.  The phenomenon  known as "whiting"  has been documented  in other
Great Lakes, i.e.,  Lake Ontario,  but as yet no studies have  confirmed  the event in Lake
Erie (Jerome, personal communication).

     Sediment Metal Analysis.  During the 3une cruise of 1979, USEPA-GLNPO obtained
sediment samples  at each of the survey stations where suitable substrate made coring
possible.   The top 10  cm of each core  was homogenized and  analyzed  for 19  metal
elements:    silver,  aluminum, boron, barium,  beryllium, cadmium, cobalt,   chromium,
copper,  iron,  mercury,  manganese, molybdenum, nickel,  lead, tin, titanium, vanadium,
zinc.  The remaining section of the core below 10 cm was analyzed as a second sediment
layer however, due to  the  incomplete and inconsistent  nature of the data it will not be
included. Due to detection limit problems, boron, beryllium and tin will not be reported.
                                         40

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      Concentrations reported by USEPA-GLNPO are expressed as mg kg-1  dry weight
except as noted. Contour maps were prepared to show the distribution of the elements in
the open lake sediments (Figure 64).  Statistical  analysis of the data was limited by the
nature of the survey, i.e.,  only one core per  station was taken.  In addition, data was
unavailable at 11  stations (3, 4, 8, 11, 23, 34, 40, 50, 51, 82 and 85).  In some cases, the
values reported were .known to be higher than actual values; these data were not included
in the mapping or data analysis.  The distribution of each element is briefly discussed
below.

      Aluminum is a major  constituent of the  natural sediment found in all three basins.
Since clays are a predominant component of the sediments, particularly in  the fine grain
depositional regions, and aluminum (primarily as illite) is a primary constituent of the clay
minerals, its distribution is largely ubiquitous.  Highest concentrations were found in the
major depositional regions.

      Titanium is  closely related  to  aluminum as a component of the sediments and is
probably associated with illite (Kemp et al.  1976).  As with aluminum it is  ubiquitous in
distribution with the highest  open lake concentrations found in the depositional  zone of
the eastern basin.

      Iron and manganese  both occur at high  concentrations in the sediments with iron
being one of  the  most abundant  elements  found  in the open lake sediments.   Highest
concentrations were found in the major depositional areas. Kemp et al.  1976 reports both
these elements to  be vertically mobile in the sediments with highest concentrations found
at the sediment water  interface.   In the western and central basins where  the sediment
water  interface is subject to anoxic  conditions, both iron and  manganese are known  to
migrate from  the sediments into the overlying waters.

     Cobalt concentrations were  fairly uniform throughout the lake with  higher values
encountered in the major depositional zones.

     Nickel and zinc both show distributional patterns of high concentrations near known
loading sources.   Highest  values  were primarily  found  in the  western portion  of the
western basin and along the south shore of the central basin.  Kemp et al.   (1976) states
that the major increase  in concentration has likely  occurred since 1950.
                                           41

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      Molybdenum showed somewhat higher values in the major depositional zones of the
central and eastern basins.

      Cadium,  chromium, lead and  copper  constitute four  of the five major metal
contaminants in  the lake.  All four indicate similar distribution patterns showing  the
highest open lake concentrations in the western basin and within major depositional areas
in the central and eastern basins.  Nearshore areas of high concentrations were found in
the western portion of the western basin and along the south shore of the central basin.

      Silver was  found in low concentrations throughout the lake.  Only  in the western
basin adjacent to the Detroit River and in the eastern portion of the central basin were
concentrations reported above detection limits.

      Barium and vanadium both indicate a rather ubiquitous distribution with the highest
open lake values occurring in the major depositional areas of the basins.

      A cluster analysis  was used to group similar sediment types together based on the
concentrations of the 9 elements for  which a complete  data set was available.  The
analysis was dominated by Al  and Fe,  the most abundant metals of the lake sediments.
Except for Cluster No. 1 (Figure 65a and Table 24), the groups show a general ordered
increase in mean concentrations of the elements. However, Cluster No. 1 includes Station
1, having high concentrations of five elements in conjunction with relatively low levels of
Al and Fe. Data from Station  1 does not conform to any information  previously reported
for this area (Thomas and Mudroch 1979).  Since there are no  point sources which would
lead  to extensive  metal deposition  in this area and  contamination  from  shipping is
unlikely, it is expected that this data is incorrect.  The USEPA-GLNPO was  not  able to
provide any additional information as to the validity of the data at this station.

      The areas of the lake corresponding to  Cluster No. 4 (highest mean concentrations)
are located in the central and eastern basins.  Also high  concentrations  (Cluster No. 3)
•were found in  the middle portion of the western basin and in  the central and  eastern
basins.  Moderate levels (Cluster No.  2) are located in parts of all  three basins.  Low
concentrations of Al and Fe (Cluster No.   1) were found in  the northeast  part  of  the
central basin and at Station 1.
                                         42

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      Figures 65a and 65b show the sediment depositional pattern determined for Lake
Erie and the results of the cluster  analysis plotted as a contour map.   The light areas
represent depositional zones of fine-grained silt, clay particles and organic matter located
in the deepest areas of the central and eastern basins.  In general,  the depositional zones
correspond to the areas of highest  element concentrations.  In addition, the large non-
depositional area in the northeastern part of the central basin  corresponds with the low
concentration area evident from the  cluster analysis.

      The mercury concentrations in the surface sediments of Lake Erie have decreased
markedly in the past 10 years.  Sediment cores taken at the.mbuth of the Detroit River in
1970  (Thomas and Jaquet 1976) yielded surface concentrations over 2000 mg/kg (Figure
66a),  decreasing exponentially  with  depth to background concentrations of less than 100
mg/kg.  High surface values were attributed to waste discharges from chlor-alkali  plants
which operated on  the  Detroit   and  St.   Clair Rivers  between  1950  and  1970.
Contamination from the Detroit River appears to have spread throughout the western and
most  of the central basin. Localized high concentrations in the eastern basin seem to be
related to local point sources. Samples taken during the Intensive Study, nearly ten years
after  the plants ceased operation, indicate that recent deposits have covered the  highly
contaminated sediment.   A thin layer of new  material  having mercury concentrations
approaching background  levels is now evident (Figure 66b).  In a like  fashion,  mercury
levels in Lake St. Clair walleyes have declined  from 2 ug/g in  1970 to 0.5 ug/g in 1980.
The rapid environmental response subsequent to the cessation of point source discharges
can be attributed to flushing of the  St. Clair -Detroit River system and the high load of
suspended sediment delivered to western Lake Erie covering the contaminated sediments.

      In addition to the data just discussed, work by Thomas et al. (1976), Kemp  et al.
(1974, 1976) and Nriagu et al. (1979) have characterized the sediments of all three  basins
as well as estimated sedimentation rates and fluxes of elements to the sediments.  Using
an intensive sampling pattern (275 sites) and a detailed analysis of the surf icial sediments,
Thomas et al. (1976) characterized the sediment texture and, utilizing grain size analysis,
defined  energy  regimes  at  the sediment water  interface.   In  further work on the
sediments, Kemp  et  al.  (1976) attempted  to trace the cultural  impact on  Lake Erie
through the concentrations of various elements found in  10 cores distributed throughout
the three basins.  After grouping the  elements examined into six categories (conservative,
enriched,  nutrient, carbonate, mobile and miscellaneous elements), each element within
its  category  was  examined and characterized  relative  to  recent  cultural  changes
                                          43

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influencing the lake.  In particular, the enriched elements (Hg, Pb, Zn, Cd and Cu) were

found to have increased to high concentrations above  the Ambrosia horizon.   This was
attributed to anthropogenic loading especially since 1950.  Most recently, Nriagu et al.
(1979) examined the record of heavy metal contamination using cores taken from all three
basins.  Profiles of Cd, Cu, Pb and Zn were determined in order to evaluate loadings of
metals  to  the  lake.   Using Pb dating techniques, sedimentation  rates  and  fluxes  of
elements were calculated  for each of the basins plus a mass balance was determined for
the lake.  An inventory of the sources and sinks for Cd, Cu, Pb and Zn is presented in
Table 25.
                                     TABLE 25
                              Sediment Source Loading
                              (From Nriagu et al. 1979)

                              Flux Rate, x 10  kg yr-1

            Source             Cadmium      Copper     Lead     Zinc

  Detroit River (import from          —        16*0      630     5220
     Upper Lakes)
  Tributaries, U.S.A.                  ~         100       52      271
  Tributaries, Ontario                 —          31       19      1*0
  Sewage discharges                 5.5         **8      283      759
  Dredged spoils                     4.2          42       56      175
  Atmospheric inputs                  39         206      6*5      903
  Shoreline erosion                  7.9         190      221       308

  TOTAL, all sources                  -        2*77     1906     7776

  Export, Niagara River and           —        1320      660     **00
     Welland Canal

  Retained in sediments               —        1157     12*6     3376

     It is evident that the major sources  of loading are from atmospheric inputs, sewage

discharges and, most importantly, the Detroit River.  The Detroit River contributed 66%

of the  Cu load, 32% Pb and 67% Zn while sewage and atmospheric sources contributed

26%, *9% and 22% respectively.  Over *0% of the metal loading is retained in the lake

and in  the case of Pb, 65% is sedimented in the basin.   It is evident that the most

important point source of contamination to the lake is from the Detroit River; thus this

must be considered the principal target for open lake loading reductions.


     Phytoplankton.  Before the  1978 -  1979 open lake program, a  phytoplankton

population study which incorporated all three basins had only been conducted once during

                                        44

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the last decade.   Munawar and  Munawar (1976) reported phytoplankton  community
structure in the three basins for seven cruises from April through December 1970. As
part  of the  1978 - 1979  Intensive  Study,  phytoplankton species  composition  and
community structure were examined in order to detect any changes that would reflect on
water quality (DeVault and Rockwell 1981).  During 1978, samples were collected at each
station  using the same sampling pattern utilized for chemical analysis (Figure 67) while a
reduced sampling pattern was followed during 1979. Sample analysis employed a modified
Utermohl technique with cell number and biomass estimates derived for each count.

     Western basin biomass indicated a somewhat similar pattern during the first  half of
both  field  seasons.    The  initial diatom  peak was  not encountered  either year;
consequently, spring and early summer biomass values were low.  As the western basin
warmed in the late spring and early summer, a rapid biomass increase continued through
mid-summer. In 1978, biomass showed  a decline into the fall, while in  1979 fall biomass
remained  high  with peak values occurring in November  (Figure  68).   These extreme
oscillations  are  characteristic of  the  western basin,  particularly if blue-green bloom
conditions  are  encountered, as  was the case in  1979.   In  general, the western basin
phytoplankton biomass is dominated by diatoms in the spring and co-dominated by diatoms
and blue-greens  through the summer and fall (Figures 69 and 70).  This pattern is  similar
each year with  only the intensity of  these fluctuations varying,  as was also shown by
Munawar and Munawar (1976).

     The  central  and eastern basins  showed  a somewhat similar biomass pattern and
species  composition during  both years (Figures 71 and  72).   The diatoms  and  greens
represented the major contributors to the phytoplankton community throughout the season
(Figures 73-76).  Initial spring biomass is generally high relative to the summer  months
due to diatom populations found in both  basins.  Through mid-summer, values remained
low with a gradual biomass increase toward mid-August  and September resulting  from
increasing populations of  the green algae.  Following  turnover in the central basin and
later into  the fall  in the eastern basin, diatoms again became dominant members of the
community.

     The relative  abundance of the taxa contributing greater than 5 percent to the total
biomass by basin and year is presented in Tables 26-31. In addition, each taxa considered
to be indicative of eutrophic conditions  is  indicated.  The taxa comprising the  species
most commonly encountered in the western  basin represent diatoms, blue-greens, greens
                                          45

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and cryptomonads while in the central and eastern basins blue-greens do not represent the
influence found in the western basin. Diatoms are the most important group throughout
the lake in terms of total biomass with greens having the next greatest contribution. No
one taxa or group characterizes any single basin; instead, most any of the taxa listed were
found to be ubiquitous throughout the three basins.

     Biomass distribution indicate a west-to-east decrease in standing crop with higher
concentrations found along  the  U.S. shore  of all basins.  Comparison between  the two
years indicated  somewhat higher concentrations occurring in 1979,  particularly in the
western basin (Table  32).  Very little change was evident in the eastern basin, while the
central basin increase can be attributed to  an increased diatom biomass during  the late
fall cruise of 1979.  The western basin increase was also due to a diatom pulse during the
same fall cruise in  addition  to a large population of blue-greens  in early August through
September.    Both  the fall pulse  of  diatoms  and  August population of blue-greens
contribute  significantly  to   year-to-year variation,  particularly considering the long
interval between surveys.

                                  TABLE  32
                Total Mean Basin Phytoplankton Biomass by Basin
                         Western           Central           Eastern
        1978             4.0 g/m3        1.8 g/m3         1.2  g/m3
        1979             9.4 g/m3        3.4 g/m3         0.9  g/m3
                                         46

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Nearshore Zone

     The nearshore segment of the Lake Erie intensive study 1978-1979 was the resultant
effort of four groups, each responsible for individual segments of the nearshore region,
i.e. western basin (U.S. - CLEAR), central basin (U.S. - Heidelberg College), eastern basin
(U.S., GLL - SUNY) and the entire north shore (Canada - OMOE).  A more complete
description of the nearshore program is presented in the Methods section.

     The combining of the nearshore data sets was not confluent; however, in  order to
present a comprehensive view of the nearshore region the data was  pooled and  mean
values were  determined  for the  two-year study period.  Figure 77  presents the  mean
concentrations of several parameters for each  of the individual reaches. The figures are
ordered by basin and shoreline, i.e. north shore of the eastern basin (reaches 1-*)  followed
by central basin north shore (reaches 5-7) and so on. A more complete yearly summary of
the data is presented in  Appendix A, presenting a list of  primary parameters for each
reach together  with median,  mean,  maxima,  minima,  standard  error, and number of
samples (n).

     "Nearshore" is  an ambiguous term also referred to as the  littoral zone (an interface
zone between the  drainage basin and the open water  of the lake) (Wetzei 1975).  The
expanse of this  region in relation to the open water  (pelagic  zone)  varies among lakes
depending on geomorphology and sedimentation rates.  Wetzei states that most of the
world's lakes are relatively shallow and areally  small with the littoral zone constituting a
major portion of the lake basin. The littoral zone generally is a  major  contributor to total
lake productivity with submerged macrophytes responsible  for much of the production.
This does not represent the situation observed in Lake Erie.  Submerged aquatics were not
observed at  any of  the  shore stations; however,  primary  productivity was indeed high
compared with the open lake due to profuse populations of phytoplankton.  For example,
corrected chlorophyll a values frequently used as  an  indication of  primary production,
reached a maximum of 209 ug/1 in the nearshore area of Sandusky Bay.

     Many authors have attempted to define Lake Erie's nearshore  zone  (Cooper  1978,
Gregor  and Ongly  1978, Gregor  and Rast  1979,  Herdendorf 1980b,  Richards 198la,
Rukavina and St.  Jacques 1971)  but  no  one  has  been able  to establish the  physical
boundaries  or determine  objective criteria for  nearshore waters.  To establish definite
                                         47

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boundaries for the nearshore, one must establish the criteria to be utilized.  Several of the
above-mentioned authors have suggested the following criteria:

      1.    Physical description
           a.   depth contour
           b.   distance from shore
      2.    Chemical
           a.   high mean concentrations
           b.   steep inshore-offshore chemical gradients
      3.    Dynamics
           a.   high energy sediment deposition
           b.   high variability mixing zone

      Indeed the nearshore zone is highly variable, and one can sample an inshore-offshore
transect on one day and find uniform concentrations throughout while on the following day
concentrations at inshore stations can be 10 to 100 times greater than at a corresponding
offshore station.  The resultant problem  is to find criteria that can be used independently
of short- and long-term variability, i.e. daily vs.  seasonal fluctuations.  The demarcation
of this zone and the interface with the open lake will be presented in the Discussion.

      Temperature  Regime.  Thermal stratification in the nearshore area is ephemeral,
most commonly occurring in the central  and eastern basins.   Stratification was not
observed in  the nearshore region west  of Sandusky Bay during this study.   Since the
western portion of Lake Erie is shallow and does not form a permanent thermal  structure,
the likelihood of any thermal structure in the  nearshore would be very remote.  The
occurrence of a thermal regime in the nearshore of the central and/or eastern basin is
also not  frequently encountered.  The nearshore region can be  characterized as a high-
energy mixing zone due to breaking waves and accompanying orbital  velocities of the
water mass beyond the breakers.  Thus  any thermal structure encountered in this zone
would be expected to last only a few days, depending upon meteorological conditions.  The
mechanisms  involved in the  formation  of a thermocline  or  thermal gradient in the
nearshore zone are similar to those previously discussed for  the  open  waters of the
western  basin.  Essentially  two conditions could  result in the formation of thermal
structure. First and probably the least stable condition occurs during several warm, calm
days when  a thermal gradient develops.   The thermal gradient persists until wind stress
induces sufficient vertical  mixing to destroy any gradient. The second condition occurs
                                          48

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 during periods of strong wind events and seiche activity resulting in a temporary tilting of
 the hypolimnion in both the central and eastern basins. This tilting can result in transport
 of hypolimnion  and/or  mesolimnion water into the shore region of either basin and, as
 previously mentioned,  this water mass  may also  move  into the western basin.   Most
 frequently this tilting of the hypolimnion effects the southwest corner of the central basin
 known as the Sandusky sub-basin. Water depth in this region is less than 15 m and by late
 summer permanent  thermal stratification no longer exists. However, during periods of
 seiche activity central basin bottom waters may move into the sub-basin for short periods
 of time.  For  example,  during a summer nearshore cruise in 1979, stratification was found
 near Huron, Ohio.  Stations in the region were sampled on three consecutive days, with
 stratification  encountered at the Huron station on  the first and third days but not on the
 second.  During the  second day, thermal structure was encountered approximately 0.5 km
 northeast of the original location. This type of hypolimnion/mesolimnion water transport
 is not unusual for the shore  regions of the central  basin.  Similar recordings of thermal
 structure movement were  also made at Cleveland, Ohio, Erie, Pennsylvania, and Dunkirk,
 New York.

     A second type of  thermal event, potentially important to the nearshore region and
 known as "thermal bar," has been described for the  Great  Lakes (Rodgers 1966). Thermal
 bar formation occurs during the spring when nearshore and tributary water-temperatures
 are 4 C and greater. A 4°C interface between the nearshore waters and the colder open
 lake water mass forms, resulting in a somewhat impermeable barrier to mixing of the two
 water masses.  The most  notable effect in Lake  Erie is to inhibit the mixing of the
 tributary water with the open lake; for example, the turbid, warmer water of the Maumee
 River is confined to the south shoreline of the western basin during  the presence of  a
 thermal bar.   This  phenomenon was  observed  during  the spring cruise of 1979.  The
 thermal bar was not observed in the south shore region of the central and eastern basins
 due to the lateness of the spring cruises (late May, early June)  and north shore coverage
 was not sufficient to document this event.  Wetzel (1975)  hypothesized that thermal bars
 probably occur in all lakes; however,  the duration of their effect may be only transitory.
 Due to  the shallowness of Lake Erie compared  with the  other Great Lakes, the spring
 warming period is rather rapid resulting in a short time frame when the thermal bar could
 have an important lakewide effect.

     Nutrients.  When  examining the  nearshore data collected during the  two intensive
years three sources of variability were considered:  (1) spatial or regional differences, (2)
                                         49

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seasonal differences, and (3) year-to-year differences.  Each of the nutrient parameters
are influenced to various degrees by these three sources  of variability.  After preliminary
analysis  of  the data the entire nearshore of the lake was geographically divided into
sections referred to as "reaches." The sectioning of the nearshore was designed to reduce
spatial variability.  For example, the spatial variability in total phosphorus concentrations
one finds along the U.S. shoreline of the western  basin is considerably greater than that
found along  the  Canadian shoreline of  the  central  basin.  Consequently, areas of the
greatest variability with respect to concentrations, or regions having uniquely high or low
values were segregated. These regions are represented  by  reaches 2 (Port Maitland), 11
(Maumee  Bay), 13 (Sandusky Bay),  16 (Cleveland), and 19 (Erie Harbor).  Each of  these
locations  represents  an area  of high  concentrations and loading compared with the
adjoining  reaches.  By separating these regions,  some  of  the  major effects of spatial
variability were removed.

     Neither the seasonal nor yearly  variability   was stringently  dealt  with in the
framework of this report.  Appendix A  presents standard error, and maximum/minimum
values for each year providing  information on the yearly differences, however seasonal
values were not presented.   For  each of the five major nutrient parameters,  total
phosphorus (TP),  soluble reactive phosphorus (SRP), nitrate plus nitrite (N+N), ammonia
(NHA and dissolved reactive silica (DRS), seasonal variability  proved to be greater than
year-to-year variability. The exception was TP where seasonal vs. yearly variations were
similar.

     When examining  the western basin nearshore mean nutrient concentrations for year
to year vs. seasonal fluctuations, several points become  obvious  (Table 33).  First, if the
seasonal high and low concentrations are compared it can be seen that over a 75% change
in concentration occurred between cruise mean values for  all parameters with the
exception of TP.  For example, 1978 spring western basin nearshore concentrations of SRP
were 36.2 ug/1  while fall values were 6.8 ug/1 indicating an  81% change through the field
season.  Second, if yearly means for 1978 and  1979 are compared, it is apparent that the
difference is considerably less than that found within a single season.
                                         50

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                                 TABLE 33
   WESTERN BASIN NEARSHORE NUTRIENT VARIABILITY BETWEEN YEARS
                                   (ug/1)
                           TP      SRP      N+N        3      SRS
   1978
   Mean concentration      130        16       785       86      1388
   Difference between       **%      81%      95%      86%     89%
   seasonal max. and
   min.
1979
Mean concentration
Difference between
seasonal max. and
min.

88
38%



9
76%



1148
9*%



92
81%



1128
75%


   Difference between       35%     «8%      27%       6%     23%
   years

     It is  important to remember that the western  basin represents the extreme in
seasonal  variation  not  only evident from  the percent  change but  also the actual
differences  in  concentrations.    For  example,  1978  eastern  basin  cruise  mean
concentrations of TP ranged from 38 to 2* ug/1 (37% difference) while the western basin
values ranged from 185 to 10
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nutrients.  At seven western basin tributaries mean concentrations of TP, N + N and NHj
illustrate the localized effect of these point sources (Figure 78-80).  The cruise mean
concentrations of TP at offshore locations (open western basin) ranged from 14 to 40 ug/1
for the two-year period except for an extremely high concentration encountered in spring
of 1979 (102 ug/1).  In contrast the cruise mean nearshore concentrations (western basin)
of TP  ranged from 70 to 185 ug/1 over the two year period.  In almost all cases, highest
nearshore and open  lake concentrations occurred  during the spring coinciding  with  peak
loading  from  all  tributaries.    As  evident  by Figures  81-85  the  two-year  mean
concentrations in the nearshore region around the western basin tributaries were as high
or usually  higher than peak spring open water values, further illustrating the year-round
localized effect of these smaller tributary inputs. This same relationship between high
localized concentrations and tributaries is also evident in the central and eastern basins.

     As previously discussed, these numerous tributaries contribute  greater than 40% to
the total loading (Great Lakes Water Quality Board 1983); however, their influence within
the mixing zone of the lake is very dramatic. They produce both esthetically unpleasant
conditions,  i.e.  turbidity,  and  greatly  enhance  the  eutrophication of  the nearshore.
Frequently, in conjunction with high  nutrient loading, the input of contaminants is also
significant.  In nearly all  such regions, elevated concentrations of heavy metals and
organics have been measured.  Since the nearshore portion  of the lake represents the
maximum-use area  both recreationally  and  for municipal and industrial purposes, the
pollution of the region is particularly important.

     Total Phosphorus.  Total  phosphorus  will  serve as an  exemplar for  the  reach
distribution of the major nutrient parameters. Since phosphorus concentrations provide a
good indication of external loading from both agricultural  and municipal sources, the high
and  low reach  concentrations  of TP  are  generally  indicative of the other nutrient
parameters.  From Figure 81 it is evident that the highest concentrations of TP are found
in the  western basin and the south shore of the central basin.  Only two other reaches
indicate  exceptionally high  values, both in  the eastern basin, reaches 2 (Port  Maitland),
site of the input of the Grand River, Ontario, and 19 (Erie, PA Harbor). The entire north
shore of  Lake Erie and the south shore of the eastern basin, with the exception  of the two
previously  mentioned reaches, have concentrations below 30 ug/1 for the two-year mean.
Maumee Bay and Sandusky Bay maintained the highest values (160 ug/1) both receiving the
major  percentage  of phosphorus loading from agricultural sources; however, the city of
Toledo is also a significant  contributor to the Maumee Bay phosphorus load. Since much
                                          52

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of the Maumee River flow remains confined to the south shore portion of the basin, the
reach  immediately east (12) is also  influenced by  the  high values originating from the
Maumee. The  central basin south shore concentrations  primarily reflect municipal point
sources, i.e. Cleveland (16) and Faiport (17).

     Soluble  Reactive  Phosphorus.  SRP reach  means similarly  reflect point  source
contributions  along both  the northern  and southern  shorelines.    High values were
encountered  at  reaches 2 (Port  Maitland)  and 11  (Maumee Bay) with intermediate
concentrations found near Leamington  (8) and along the southern shore of the western
basin  and the central  basin west of  Cleveland (Figure 82).  High SRP  values were
anticipated in Erie PA Harbor due to the high TP values but were not observed.  This may
have been due to  a methodology  problem discussed previously  and/or rapid biological
uptake of soluble phosphorus in the eutrophic bay.

     Dissolved Inorganic Nitrogen.  Nitrate plus  nitrite  and ammonia concentrations
were found to be highest in the western basin and along  the southern shore of the central
basin (Figures  83 and 84).  As with  total phosphorus, ammonia and N+N originate both
from agricultural and municipal  sources; however, the primary source of both forms of
nitrogen during the spring is from agricultural drainage. Point sources proved to be the
most important  in terms  of localized effects,  particularly  in  Maumee Bay  and the
Cleveland area, where the highest values of the nearshore region were recorded.

     Seasonal  concentrations of ammonia are  considerably more stable than those of
nitrate plus nitrite along the entire U.S. shoreline. For example, at select stations in the
western  basin where variability is  the  greatest, ammonia concentrations changed from
spring  peak values to seasonal lows by  approximately  500%  while nitrate  plus  nitrite
values  showed  a  seasonal change in  concentration of over 15 fold (1500%).  The most
dramatic example of seasonal fluctuations for an entire reach is found in the Maumee Bay
(reach  11) where 1979  spring  concentrations of  NH^  were greater  than 350  ug/1 and
nitrate plus nitrite exceeded 4,700  ug/1 while fall mean  values were 90 ug/1 and 800 ug/1
respectively.    The very large reduction in nitrate plus nitrite results from  reduced
tributary concentration and flow. Since agricultural runoff is the  principal source of this
form of dissolved nitrogen during the  spring,  such  a  drop would be expected.  Loading of
ammonia,  on   the  other hand,  represents  more of a  combination  of  two  sources,
agricultural and municipal.   Following  the spring loadings of ammonia,  concentrations
remain relatively  high due to the constant input from municipal  sewage treatment plants.
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      Silica.   Dissolved  reactive silica  (DRS)  concentrations indicate  shoreline  and
 seasonal distribution characteristics similar to those previously described for nitrate plus
 nitrite (Figure 85). Sources of loading do differ; external loading of silica enters the lake
 only  through  land drainage, or agricultural runoff and through internal  loading such as
 dissolution of particulate silica and DRS found in interstitial waters.  Points of highest
 concentations are reaches 11 (Maumee Bay) and 13 (Sandusky Bay).  Both areas are subject
 to  extensive  loading of sediments  from  agricultural  drainage and continual bottom
 resuspension.

      Corrected Chlorophyll a.  Classical definitions of the  nearshore region or littoral
 zone  allude to a  region of high primary production.  Frequently this region is heavily
 populated with macrophytes and attached epiphytes. However, macrophyte populations
 are not plentiful along the shorelines of Lake Erie; being present only in isolated marsh
 areas such as Long  Point Bay.   Consequently, only phytoplankton and  Cladophora  are
 responsible for  the  high production  evident  along the shores as reflected by CCHLA
 concentrations.  The more eutrophic reaches are clearly  evident throughout the U.S. shore
 of the western basin (reaches 10 through 1*) and Erie PA Harbor (reach 19), with  the most
 abundant algal growth found at reach 13, Sandusky Bay (Figure 86).  The two-year mean
 CCHLA was 60 ug/1  with maximum values of over 200 ug/1 occurring in the upper regions
 of the bay near the Sandusky River mouth.  Erie Harbor  represents the only region of high
 CCHLA values  outside  the  western basin reflecting high  nutrient input and limited
 exchange with the open lake.

      Only in  the western basin did any significant change  in  the mean concentration
 occur throughout the season.  The cruise-to-cruise mean concentrations over the two-year
 period did not change more than 2 ug/1 in the central or eastern  basins, while  in  the
 western basin  cruise means doubled from the spring cruise to  early summer and remained
 high into  the  fall.  It is important to notice that a doubling of CCHLA values in  the
 western basin is greatly more significant than  an equivalent increase in the other two
basins.

      In all three  basins, nearshore zone concentrations were greater than the offshore
values.  In the western basin,  nearshore concentrations were  usually 100 percent greater
than  those from the open basin.  The central basin nearshore concentrations were only
40% greater while eastern basin nearshore concentrations varied from 20  to 75% greater
than the open lake values.  Eastern basin nearshore mean values were never greater than 6
                                          54

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ug/1 at any time  during the  two years,  thus the inshore-offshore differences of actual
concentration were small (1 ug/1-2 ug/1).

      Seasonally, the highest concentrations  occurred during September for all basins
which is similar to the pattern found in the open portion of the lake (Figures 44 and 45).
The northern nearshore zone was not sampled with the same intensity as the south shore,
thus it is difficult  to interpret this data.

      Secchi.  Water clarity provides an  indirect measure of water quality incorporating
several parameters.  As discussed in the open lake section, secchi, turbidity, CCHLA and
particulate  organic  carbon all show a relationship to water  clarity.  Decreased secchi
depth for the nearshore region is significantly affected by two factors:  first, resuspension
of the sediments due to wave action, and second, tributary inputs.  The resuspension of
bottom material adds turbidity to the nearshore region during increased wave  activity
with  the intensity  determining the degree of  resuspension.   During  moderate wave
conditions this effect is minimal, influencing only the area inside 0.5 km  in most  regions;
however, during severe storm activity the effect can be evident  several kilometers from
shore.  During the late fall and early spring, resuspension influences the entire water
column throughout all three basins.

      The second  significant influence on water  clarity originates from tributary flow.
Other than the Detroit River, most of the tributaries entering the lake have secchi values
less than .25 m, turbidity values  of 100 NTU and total suspended solids of greater than 40
mg/1.  Therefore the mixing zone represents  a highly turbid region  compared with the
open lake.

      In  addition to  these factors, the inshore zone  also may contain a high density of
phytoplankton further decreasing water clarity. This  is particularly true  in Sandusky Bay
where blue-green populations  may frequently reach bloom conditions.    In general,
however, phytoplankton are not the major form of particulate material responsible for the
reduced transparency encountered in the nearshore region.

      It is evident that the clarity of  water improves once removed from the  western
basin influence (Figure 87). Nearly the entire north shore and the eastern basin maintain
mean secchi values greater than  2 m.  Much of the central basin south shore values  were
two to three times greater than western basin values.
                                          55

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      Dissolved Oxygen.  Low dissolved oxygen values in the nearshore region of any basin
were not a frequent occurrence (Figure 88).  Based on the International Joint Commission
objective of 6 mg/1, only an average of 5% of all values reported from the U.S. nearshore
were below the  objective level.   Many  of  the  low D.O.  values were associated with
temporary thermal stratification particularly in  the central basin.  For example,  nearly
40% of the low D.O. values recorded in the  central basin in 1978 occurred in the Huron,
Ohio area.   As  previously   discussed  due  to  the  pendulum-like  mobility of  the
mesolimnion/hypolimnion water of  the central basin moving into the Sandusky sub-basin,
D.O. values as low as 0.1 mg/1 were encountered.  Low values were also found adjacent to
a dredge spoil  construction site near the Detroit River, at an open lake dredge disposal
area near  Conneaut and at the mouths of the Maumee, Huron, Cuyahoga and Buffalo
Rivers. Low D.O.  values were noted along the north shore  in 3 of the 9 reaches (1  - Port
Colborne, 6 - Port Stanley, and 7 -  Wheatley) at  least once  over  the two-year period. A
complete violation listing was  not available for the north shore.

      The seasonal fluctuations in  dissolved  oxygen concentrations  encountered in the
nearshore zone can mainly be attributed to changes  in solubilities  resulting  from the
annual lake temperature cycle. Based on 100% saturation, D.O.  concentrations could
range from 14 mg/1 during periods of cold water to 8.5 mg/1 in the warmest months.  The
mean values during this study range from 81  to 99.9% saturation with the concentration
means ranging from 7.5 mg/1  to 10 mg/1.   Only three reaches indicate saturations below
90% (Figure 89):  reaches 6 (Port Stanley 82.2), 9 (Colchester 81.1) and 14 (Sandusky Bay
88.6), none of which indicate any specific problem in terms of an entire reach.

      Principal  Ions.  The  principal   ions  (chloride,  sulfate,  bicarbonate  calcium,
magnesium, sodium, and potassium) are all natural constituents of Lake Erie water as a
result of interactions  between  bedrock  and groundwater (weathering,  leaching  and
erosion).   These  constituents  of Lake Erie  chemistry historically  have been  used as
indicators of long-term changes in  water quality (Beeton 1961).  Thus a more  detailed
explanation of their distribution is pertinent.

      The full complement of ion parameters was  measured during the nearshore  study,
not  because the  nearshore area was expected to have chronic  or toxic  concentrations
(Table 34), but to establish an extensive seasonal and spatial data base for further use in
trend analysis.   Due to the conservative properties  of ions, they lend  themselves to
                                         56

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 analysis of long-term changes in the lake resulting from external inputs, i.e. changes in
 chloride concentrations originating from municipal sources.

      Using the south shore central basin nearshore  data, Richards (1981a) determined
 that this section of the lake was very similar to the standard bicarbonate lake described
 by Hutchinson (1957) with the exception of chloride and potassium (Figure 90).  Lake Erie
 chloride concentrations are two times higher than those found in other bicarbonate lakes.
 In contrast,  potassium  concentrations  were found to be only  40% of concentrations
 normally encountered.  This general uniformity between lakes due  to the  principles of
 geochemistry also implies uniformity within a lake.  This has  been documented by several
 investigations on  Lake  Erie  (Kramer  1964,  Don  1972) with the exception  of certain
 harbors.   The  Canada  Centre  for Inland  Waters (Don  1972) has  stated  that it is
 unnecessary to measure offshore Lake Erie principal ion concentrations because they  can
 be estimated from conductance values  in conjunction with conductance factors for  the
 individual  ions.   To  test  this assumption,  the data base  utilized  consisted  of all  the
 principal ion  data collected  during the two-year  period  (4 cruises/year)  at over  250
 nearshore stations.  The  full compliment of ion data was available  for the south shore
 reaches  only  (Table 35),  while only chloride and alkalinity were recorded for the north
 shore reaches (1-9). Data for ions is available as annual reach means in Appendix A,  and
 annual river/harbor means in Appendix B.

     Chloride reach means ranged from 17.8 to 27.5 mg/1 (n=20).  The reaches having the
 highest means are located along  the south  shore:   Maumee (27.5), Cleveland  (26.3),
 Fairport (25.4)  and Sandusky  Bay  (24.4) (Figure 91).   Two north shore  reaches  also
 exhibited noticeably higher concentrations:  Colchester (23.3) and  Port Maitland (23.2
 mg/1).  Many of  these high values are due to loadings of chloride from tributaries entering
 the lake within the designated reach. Of all the rivers that  were monitored (n=22),  the
four that demonstrated the highest concentration of chloride and subsequent loading were
located along the south shore:

                   Grand River, Ohio              67.5 mg/1
                   Cuyahoga River, Ohio           55.6 mg/1
                   Rocky River, Ohio              49.7 mg/1
                   Ashtabula River, Ohio           40.3 mg/1
                                         57

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      Large quantities of chloride (x = 2270 mg/1) have been reported for stations in the
Grand River, Ohio since 1950.  The high concentrations resulted from two sources:  soda
ash production by the Diamond Shamrock Company which utilized the brine from salt
wells adjacent to the river and from the mining of salt by the Morton Salt Company. The
Diamond Shamrock Company closed  their chromate plant in January of 1972 and the
remainder  of their facilities in 1976,  while the Morton Salt Company is still in operation.
A USEPA in-house memo discussing the chloride problem associated with the Grand River
indicated another possible chloride source,  Mentor  Marsh (USEPA  197*).   Herdendorf
(1982) stated that the marsh's chloride source resulted from leaching of brine from land
fill wastes buried within the  marsh.  Data from the open lake intensive study also shows
that the Cleveland-Fairport area has some of the highest chloride concentrations found in
the offshore regions.

      Sulfate reach means ranged from 25.8 - 95.8 mg/1 (n=ll) with the highest values
found in the upper portion of Sandusky Bay (Figure 92). All the stations in this area had
means greater than  100  mg/1.   Most  likely the source  of these high sulfates can be
attributed  to leaching from the United States Gypsum Company mines (Figure 93).  High
sulfate concentrations were also observed in the Maumee reach (x = 45.4 mg/1).  Sulfate
concentrations observed for the open lake portion of the intensive study ranged from 18.2
to 30.3 mg/1, with the maximum concentrations adjacent to areas where fossil- fuel power
plants are located.

      Kohlraush's Law states  that the conductivity of a neutral salt in a dilute solution is
the sum of 2 values,  one of which depends upon the cation (positive ions) and the other
upon  the anion  (negative ions);  in other words, each ion contributes a definite amount to
the total conductance of the electrolyte. Although  the concentration of an ion may vary
between samples, the amount of conductance resulting from one milligram of this ion is
consistent.  This constant is known as the conductance  factor.  The  American  Public
Health Association (1974) presented conductance factors for principal ions. The Canada
Centre for Inland Waters  (1972) presented monthly conductance  factors (adjusted for
temperature) for the principal ions. Utilizing these factors and the cruise means of the  7
major ions, specific  conductance  was  calculated.   The difference between  calculated
conductance and the  measured  specific conductance was less than 3% for the 1970  open
lake data set.  When this technique was applied to south shore reach data, the  differences
ranged from 6 to 10%. Since the  larger differences between the measured and calculated
conductances were consistent,  the possibility of analytical error was dismissed.  The
                                         58

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explanation of the  differences remains unknown, but there may be some indication that
the offshore conductance factors are not appropriate for the nearshore zone.

      The conductance factor technique is not meant to calculate conductance but merely
to  test  the possibility of  back calculating  in  order to  estimate  the individual ion
concentrations once the conductance is known.  In addition, it is necessary to know the
percent contribution each of the ions makes to the conductance before the concentrations
can be estimated:

                                  TABLE 36
                                  Open Lake            Nearshore
                                  CCIW 1970            1978-1979
         Bicarbonate                 51.0%               44.9%
         Chloride                     11.0%               10.9%
         Sulfate                      11.0%               16.6%
         Sodium                       5.0%                5.6%
         Potassium                    1.0%                0.9%
         Magnesium                   3.0%                4.2%
         Calcium                     17.0%               16.9%
      The percent contribution of each component is very similar between data reported
during the  1970 open lake  and the 1978-1979 nearshore studies with the exception of
bicarbonate and sulfates. Ionic percent contributions for all the south shore reaches are
presented in Figure 94.  The major difference in ionic composition occurs in reach 13
(Sandusky Bay) as a result of high sulfate concentrations.  When comparing actual ionic
concentrations (Table 36) and variability (% standard error) for the 2 main lake data sets
(1970 and  1978,  1979) and the nearshore  1978-1979,  it  is evident  that the greatest
variability  existed for the nearshore region.  The large variability of sulfate (18%) is due
to the high concentrations in the Sandusky  and Maumee Bays (Figure 94).  The  second
most  variable ion was potassium, which  is not suprising being the most active of the
metals (Table 36).

      Conductivity.   The International  Joint Commission  established  a total  dissolved
solids (TDS) objective of 200 mg/1 in the 1978 Water  Quality Agreement.  Due to the
lengthy time involved in the TDS measurement, an alternative method was employed for
the TDS determination during the two-year study.  Since  there is  a linear relationship
between conductivity and TDS, a conversion factor of 0.62 was employed to indirectly
calculate TDS (Fraser 1978).  The DC has  established a conductivity objective  of  308
umhos/cm (Great Lakes Water Quality Board 1974).  Five of the 20 nearshore reaches had
                                        59

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means greater than 308 umhos (Figure 95):  Port Maitland, Maumee Bay, Sandusky Bay,
Cleveland and Fairport.  All five of these reaches represent highly industrialized or
urbanized areas.    The four  south shore  reaches have been  repeatedly  mentioned
throughout this report for their high concentrations, Sandusky Bay for its extremely high
sulfate (x = 95.8 mg/1) and chloride (x = 24.4  mg/1) concentrations and  Cleveland and
Fairport  for their high chloride concentrations (26.3 and 25.4 mg/1 respectively).  It was
not surprising that  the  Maumee Bay reach had the second highest specific  conductance
since it  had  the highest chloride values (27.5  mg/1)  and  the second highest  sulfate
concentrations (45.4 mg/1)

     All five  reaches that exceeded the IJC objective level of 308 umhos/cm were among
the 7 highest reaches (out of 20) in chloride concentrations, and three of them (Maumee
Bay, Sandusky Bay  and  Cleveland) were the  top three ranking in sulfate concentrations.
Although the relationships between conductivity and chloride is not a strong one, there
are some similarities (Figure 95).
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                                     DISCUSSION

      In the results section of this report, the present status of individual parameters for
the OPEN LAKE and the NEARSHORE were documented. It is also necessary to examine
these individual  parameters in relation to the system  as a whole rather  than isolated
regions.   The Discussion will examine the relationship between the two regions and will
provide detailed information on several specific topics.

Nearshore-Offshore Relationships

      The  nearshore-offshore  region  is  a  transitional  zone  physically, , chemically,
biologically and sedimentilogically.  Unfortunately, the intensive study program  data sets
were not designed to examine the interface between the open lake and the nearshore.
One of the problems in defining either region is knowing which characteristics can be used
to delineate the two.  In order to help understand this  transitional zone, an effort was
made to define or at least characterize what constitutes the nearshore.  After review of
the nearshore literature and query of several Great Lakes investigators, it became evident
that no one definition or set of criteria was possible.

      A general definition might be:  The nearshore zone is an artificially bounded unit
that exhibits different  processes  than those observed  in  the more centrally located
portions  of the lake.  A more specific definition can be determined once  the processes
considered important are delineated.  The nearshore  area is  defined differently  by
physical,  chemical, biological and sediment  lake specialists,  each utilizing  different
parameters  resulting in definitions unique  to the specific  discipline.   To examine the
variety of nearshore definitions the  following list was assembled from literature and
personal communication with Great Lakes limnologists:

                                 Physical Limnology

      1.    The zone between  the  zero depth contour and  the point at which the long
           waves  are effectively  reflected.  This distance is different  depending  on
           whether we are dealing with surface seiches or internal seiches (Boyce 1982).
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2.   The zone contained between the edge of the lake and the  bottom contour
     whose depth equals the  mean  depth of the lake (WBlc = 7.4,  CBx"=18.5,
     EB jf = 24.3, whole lake x = 18.5) (Boyce 1982).

3.   The zone where the vertically integrated flow is downwind (Bennett 197it).

4.   The zone which  can be defined during  stratified conditions by the Rossby
     radius of deformation for internal waves.  The internal Rossby radius is 2 km
     for the  central basin of Lake Erie (Boyce  1982). (This definition would not be
     applicable to the western basin.)

5.   The zone that demonstrates low frequency  shore parallel motions.  In the
     offshore zone,  the spectral peak at the local intertial period becomes more
     pronounced  and the  current vector  tends toward  clockwise rotation (Murthy
     and Dunbar 1981).

6.   The distance between the shore and the point at which the offshore component
     of the anisotropic viscosity is maximum (Boyce 1982).

7.   The coastal boundary layer (CBL) is composed of two distinct  layers, an inner
     frictional boundary layer (FBL) and an outer intertial boundary layer (IBL)
     (Murthy and Dunbar  1981).  Although the calculation of these boundary layers
     has not  yet been completed for Lake Erie, Boyce (1982) feels that the FBL is
     about 1 km wide.  "An effluent discharged well within  this zone would mix
     relatively slowly with the waters of the open lake."

8.   The hydrodynamic boundary layer between the open lake and the shore with
     variable width up to 10 km (Coakley 1982).
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                                  Geology

 1.    The  zone defined by the wave  base depth (one-half the wave length of the
      prevailing waves). The wave base for the western basin has been calculated as
      19.5 m, thus classifying all the western basin a nearshore area (Coakley 1982).

 2.    The  zone defined by the break in slope  between the shore face and the lake
      bottom.  This boundary most closely approximates the point where  wave and
      current deposition (nearshore) processes change to gravity settling (offshore).
      Using  this definition,  the nearshore  zone would  be narrow  but  of more
      irregular width around the lake (Coakley 1982).

 3.    The  zone between the shore and the  maximum depth at which sand occurs.
      This maximum depth varies across the  north shore of Lake Erie from 10-18 m
      (Rukavina and St. Jacques 1971).

 4.    "Newly formed  organic  material  is  resuspended  and  redeposited  more
      frequently at nearshore locations (9 meters depth and 2 km from shore) than
      offshore  locations (40  meters depth and 16 km from shore).  Both  enhanced
      mineralization and particle sorting as a result of wind induced turbulence lead
      to the low content of  organic material in  nearshore  sediments  and  are
      responsible for POC/PON concentration differences.   This emphasizes  the
      crucial importance of  nearshore resuspension for  the  overall metabolism of
      Lake Erie." (Bloesch 1982).

 5.    "In the nearshore, wave action provides most of the erosional energy and part
      of the  transportive energy; such activities may be separated into processes
      associated with longshore drift and inshore-offshore migration.  Lack of sands
      in most deep water sediments indicate that onshore-offshore processes  are
      limited in extent and only rarely provide an escape from what is essentially a
      closed system in the nearshore" (Sly and Thomas 197*).

6.    "The  nearshore  zone  is the zone of  a lake adjacent to the shoreline where
      sediments are transported and sorted by waves" (Rossman and Seibel 1977).
      The inshore zone ( <18  m) has moderately sorted fine sands (mean phi = 2.08).
                                     63

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The  intermediate zone  (18-27  m) contains poorly sorted fine sands (mean
phi = 2.92) and the offshore zone ( >27 m) is composed of poorly sorted coarse
silts (mean phi = *.!*)• "If the wave period is known the nearshore zone of any
region of shoreline can be defined" (Rossman and Seibel 1977).
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                                  General Limnology

      1.    The zone separated from the open waters by  virtue of its relatively shallow
           depth, high nutrient concentration, dynamic mixing, and high variability due to
           input  loading and hydraulic characteristics.  The physical expanse of the zone
           varies considerably resulting from changes in wind intensity and duration and
           from  the natural variation in shoreline and bottom morphology (Gregor and
           Rast 1979).

      2.    At the outer edge of the nearshore zone, more than 90% of the transition from
           watershed to lake water has occurred in the central basin (Richards 198la).
           However, Richards does not suggest a specific width for this zone.

      Following  sediment  analysis of  all  the  Great  Lakes  nearshore areas  (shore
regions  <18.3 meters), Chesters and Delfino (1978) found them all to be non-depositional
in nature.   Inside the 18.3 m  contour,  sediments are temporarily deposited  only  to  be
eventually transported by currents and storm  activity.   The  western basin does not
conform to this concept since  the  input loadings to the basin are  in  excess of sediment
exported to the central basin (Thomas et al. 1976). The mean sediment grain size found in
the western basin is smaller  than that found in other  lakes and is  composed primarily  of
clay and not the more conventional nearshore sandy sediments. Thus, the inclusion of the
entire western basin into the nearshore zone as was done by Gregor and Rast (1979) may
not be appropriate.

      For purposes  of this report,  the nearshore will be  considered  the zone extending
from the shoreline to 7 km into the open lake.  Considering the wide variation in what is
considered to  be  "nearshore," careful attention must be  given to the criteria when future
sampling schemes are designed. This would greatly enhance the  database and possibly
broaden the application. Future research and monitoring efforts, particularly in the shore
and harbor regions, need to consider the zone where pollutants begin to mix with the open
lake in order to aid in determining the fate of the various pollutants in  the ecosystem.

      One sampling scheme used in the nearshore  study  was helpful in examining the
transitional zone.   In each  basin,  several transects perpendicular  to  the shore were
monitored. This data indicated that the differences encountered along each transect from
shore to open lake varied depending on the location around the lake. For example, the
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western  and central basin  transects along the U.S. shoreline indicated a  substantial
nutrient concentration decrease from the shore to the open lake (Figures 96 and 97). The
change was most distinct in areas of exceptionally high concentration such as Maumee
Bay and Sandusky Bay.  As would be expected,  the greatest differences were associated
with tributary mouths where flows were relatively low and concentrations high. This was
true to some  extent for all  rivers except the  Detroit  where  the volume is  great but
concentrations are low.  Inshore areas with nominal concentrations such as those  found
along most of the Canadian shoreline and along the U.S. eastern basin indicated little if
any gradient into the adjacent off-shore zone (Figures 98  and 99).

     The two-year  mean  concentrations and  basin ratios of  total  phosphorus and
corrected chlorophyll a calculated for the three U.S. portions of the nearshore and basin
ratios are presented in Table 37.

                                    TABLE 37
           TOTAL PHOSPHORUS AND CHLOROPHYLL CONCENTRATIONS
             AND BASIN RATIOS FOR THE U.S. NEARSHORE, 1978-1979
TPug/1
(Basin ratio)
CChla ug/1
(Basin ratio)
Western
Basin
110.0
(1.0)
25.8
(1.0)
Central
Basin
40.0
(0.36)
6.6
(0.25)
Eastern
Basin
25.0
(0.23)
4.0
(0.16)
     Mean nearshore concentrations of  total phosphorus for the central and eastern
basins were less than 40% of the western basin mean, while chlorophyll concentrations
were less than 25%. Not only were there significant differences in concentration between
basins but also between the nearshore and offshore concentrations within each basin.
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                                     TABLE 38
         NEARSHORE (NS) AND OPEN LAKE (OL) TOTAL PHOSPHORUS AND
     CHLOROPHYLL CONCENTRATIONS AND PERCENT DIFFERENCE BY BASIN
                                     1978-1979
                  Western Basin       Central Basin        Eastern Basin
                   NS      OL         NS      OL         NS      OL
   TPug/1        110.0     37.0       40.0    14.5       25.0      12.5
                       34%                 36%                50%
   CCHLAug/1    25.8     12.4        6.6     4.8       4.0       2.6
                       48%                 73%                65%
     Table  38 presents the  near shore  vs.  open lake  mean  concentrations  of  total
phosphorus and chlorophyll a found in each basin. In nearly every comparison there is over
a 50% difference in concentrations between  the  regions.  Seasonally, the differences
between nearshore and offshore concentrations is the least in the spring when loading to
the lake is highest.  It should be noted that  the actual concentration differences between
the two regions are greatest in the western basin and least in the eastern basin.  The load
to the eastern basin south shore from tributaries is very  small compared  to the western
basin, thus the eastern basin nearshore values are more comparable to the open lake.

     The horizontal transport and subsequent mixing of nearshore or tributary water
masses with the  open lake yields a unique distribution pattern in each basin.  In  many
instances, the open lake circulation pattern (Simons  1976), together  with  a  transport
model  (Lam and Simons 1976)  are adequate to predict the fate of pollutants entering  the
lake.   The  application  of the  model is particularly pertinent  to the Detroit River
influence.  For example, the distribution  of mercury  from the Detroit River through  the
lake follows the  major  circulation pattern shown by Simons  (1976).   This movement
resulted  in accumulations in the depositional areas of the central and  eastern basins
(Thomas and Jaquet 1976).  Equally important is the distribution of nutrients  and toxic
substances in and around  harbors and tributaries in  the  nearshore.  Both the localized
effects and the  eventual  mixing  with  the  open lake  are important  considerations.
Presently, models do exist to describe the mixing of river  pollutants with the lake waters.
For example, Sheng and Lick (1976) and Shook et al.  (1975) examined the distribution of
water in and around Cleveland Harbor. Numerous  other models have been developed  for
river/harbor interactions with  the open waters of many bodies of water.  Understanding
dispersal patterns in and around the numerous smaller tributaries, i.e. Raisin, Maumee,
Sandusky, Black, Huron, Cuyahoga and Grand  Rivers, is  important because  of  the high
                                          67

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nutrient and toxic substance concentrations found in these regions (Figures 78-80).  Since
cities in and around each of these tributaries utilize  the lake for drinking water as well as
for recreational purposes,  an understanding of the localized dispersion pattern is critically
important.

Nearshore Trophic Status

     The  localized effects of  pollutants  along  the nearshore zone are evident when
trophic indices are applied to the region.  Reviews of the numerous trophic classifications
and trophic indices have  been prepared  by Rawson (1956), Zafar (1959), Dobson et al.
(197(0, Rast and Lee (1978), Gregor and Rast (1979), Maloney (1979), and Steinhart et al.
(1981).  Of the many classification systems, two indices have been specifically designed
for Great  Lakes nearshore regions. Steinhart et  al. (1981) developed a multi-parameter
index utilizing toxic organic and inorganic  compounds plus standard nutrient parameters.
A  simpler index,  the Composite Trophic Index  (CTI) was developed  by Gregor and Rast
(1979) utilizing only three parameters: total phosphorus, chlorophyll a and secchi depth.
Total phosphorus  was chosen because of its relationship with primary production, and is
generally considered to be the limiting nutrient controlling production (Gregor and Rast
1979).  Chlorophyll is used as an estimate of biomass and production, while secchi depth is
inversely related  to biomass and is an estimator of water clarity. The Composite Trophic
Index was applied to each reach of the Lake Erie nearshore.

     Gregor  and Rast verified  three  different  relationships  (A,B,C)  between total
phosphorus, chlorophyll and secchi depth  during  their analysis of 1972 and 1973 Great
Lakes nearshore data (Table 39).

                                     TABLE 39
       RELATIONSHIP OF TOTAL PHOSPHORUS, CHLOROPHYLL AND SECCHI
                      (TAKEN FROM GREGOR AND RAST, 1979)
Relationship             Characterization
     A                  High Chlorophylls (2.0-20 ug/1) and small  secchi depths (0.8-
                        3.3m)
     B                  Low chlorophylls (0.3-1.5 ug/1) and large secchi depths (4.6-9.2)
     C                  High inorganic turbidity (0.92-4.6 m secchi) and  intermediate
                        chlorophyll values (0.5-4.0 ug/1)
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      Before using the CTI to determine the trophic status of the nearshore region it was
 necessary to characterize each  of  the designated reaches.   This was accomplished by
 plotting 2.3/secchi depth versus chlorophyll a concentrations. In 18 of the 20 reaches, an
 A type relationship was found, while reach 8 (Leamington) was considered a B region and
 reach 9 (Colchester), a C region (Figure 100).

      Utilizing the total phosphorus,  chlorophyll a and secchi two-year reach means, a CTI
 value was calculated using the appropriate equations for the specified relationship:
       CTIA   =  (3JT  "  3*8*)  *   ^-67Chla)  +  (0.31 TP)
                       l
       CTIB   =  (iig!  -  0.556) +   (1.67 Chi a)  +  (0.31 TP)
                                   3

       CTIr   =  ££i  .  0.409)  +   (1.67 Chi a)  +  (0.31 TP)
          ^*        jLJ                         "*
      The Lake Erie nearshore CTI results for the individual reaches are presented in
Table 40 and Figure 101 and are contrasted with the results reported by Gregor and Rast
(1979) (Table 41). The greater the CTI value the poorer the water quality. The maximum
CTI  calculated  in  1972-1973 was  16.2  in  the  western basin  north shore  region
corresponding to reach  8.  The current study calculated  a CTI of 10.7 for this region
(Figure 102).  This does not necessarily indicate  improved water quality since 1973 but
likely reflects the difference in sampling schedules for the databases utilized.  Gregor and
Rast  used only summer data, since only limited information was  available for spring and
fall.  In contrast, the data utilized for the 1978-1979 analysis included the spring, summer
and fall with the exception of some north shore reaches.  An additional difference in the
results  may be  attributed to  selection of  the  individual shoreline  segments used to
represent reaches.  Gregor and Rast (1979) selected reaches prior to any analysis of the
data primarily  using the location  of tributary inputs, while the selection of reaches for
this analysis was based on the preliminary results of the nearshore data sets.  Another
important difference resulted from Gregor and Rast (1979) classifying the entire western
basin  as nearshore area, versus the 7 km zone selected for the 1978-1979 analysis.
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      The result of the 1972-1973 trophic analysis for Gregor and Rast's regions resulted
in  8 oligotrophic/mesotrophic,  9  mesotrophic,  1  eutrophic/mesotrophic and only  3
eutrophic areas (Table 41) with twelve areas having insufficient data for analysis (Figure
102).

      For the two-year intensive study,  each of  the 20 reaches was assigned a trophic
status (Table 40) based on the associated  CTI value established by Gregor and Rast (1979)
(Table 41).  Of the 20 reaches, 10 were considered eutrophic, 2 eutrophic/mesotrophic, 7
mesotrophic and 1 oligotrophic/mesotrophic.  The north shore of Lake Erie was generally
mesotrophic with  the exception  of  reach 2  (Port MaitlandO which was determined to be
eutrophic.  This reach is significantly affected by the Grand River, Ontario, previously
noted for high nutrient loadings.  The reaches of the west and southwest shoreline of the
western basin, the reaches of  the south  shore central basin, and the Erie, Pennsylvania
Harbor  reach of the south shore eastern basin were all eutrophic.  The  maximum CTI
values were located along the U.S. portion of the western basin.  Sandusky Bay (reach 13)
had the highest value (81.1) followed by Maumee Bay (56.4) both noted for their eutrophic
condition.

      Steinhart et al. (1981) critiqued Gregor and Rast's (1979) index concluding that the
linear regressions determined  for total  phosphorus  and secchi were not successful in
explaining the actual data.   However,  analysis  of recent  Lake Erie nearshore  data
indicated  a good fit along the Group A  line although it was necessary to extrapolate the
line to accommodate some of the high chlorophyll areas ( >20 ug/1).

      The water quality  index  developed  by Steinhart et al.  (1981) was  applied to the
nearshore reach data  for comparison with the Gregor and Rast (1979) CTI.  The Steinhart
index is based on 5 groups of water quality parameters: (1) biological — fecal coliforms
and  chlorophyll  a;  (2)  chemical — total  phosphorus,  conductance and  chlorides; (3)
physical — suspended  solids,  aesthetic  status;  (4)  inorganic contaminants — arsenic,
cadmium, lead, mercury and nickel;  and (5) toxic organic compounds — toxaphene, PCBs,
phenols and chloroform.

      A  detailed description of the calculated method is available in Steinhart's text, An
Environmental Quality Index for  Nearshore Waters of the Great Lakes (1981); therefore,
only the methods  directly related to this study will be discussed.  Index values were
calculated using yearly reach means for all specified parameters except aesthetic status
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and the toxic inorganic group.  In the case of aesthetic status, the maximum value was
applied in  each case due to the spotty  nature of the data.   With the inorganic  toxic
compounds a different approach  was necessary  since the data  were frequently reported
only as present or absent.  For  these cases,  if the ratio of  data reported above the
detection limit to the number below the detection limit was  greater than 1, the parameter
was said to be in violation of the established cutoff point.

     Parameter  data in  the  physical,  chemical  and  biological groups  were  fairly
complete.   Inorganic toxic data for the reaches along the U.S. shoreline  were mostly
complete, but organic toxic data was sparse.  Of the organic compounds Steinhart chose
to use, the CLEAR and Heidelberg data sets contained only one compound, PCBs; the
SUNY  set also contained phenol data. Samples from the entire Canadian shoreline did not
include toxics data; therefore the Canadian index values are based only on the first four
groups of data.

     The index values calculated for the individual reaches are shown in Figure 103 and
Table  42.  Index  values  can range from 0-100 with 100 representing ideal  Great Lakes
conditions and 0 representing the worst possible conditions.  Index values prefixed with an
asterisk (*) indicate the index value is based on an incomplete  data set.  A subscript
indicates  which  mean   parameter  group concentration was  below  the  cutoff  point
considered  to be polluted or unpolluted as defined by Steinhart (p - physical, c - chemical,
b - biological, and t - toxics).

     Examination of calculated  index values  shows that  the  poorest  Lake Erie water
quality was found in the Sandusky Bay area in both 1978 (25.28),  and 1979 (29.22).  The
best water in the lake was generally found along the Canadian  shoreline. In both years,
reach 2 was the only Canadian reach that had an index value below 60, 54.15 in 1978 and
56.53 in 1979.  Along the southern shoreline the index values were lowest in the western
basin and generally  increased eastward, excluding Sandusky Bay.

     Although the water  along  the Canadian shoreline  is  perhaps the  best  quality
nearshore water in the lake, one must be careful when using these index values. No toxic
data was used in the calculation  of the index values for these reaches, whereas all other
index values included some toxic input.  Although weights were  applied proportionally
when using incomplete data sets, these index values have fewer chances of losing points.
This situation is particularly extreme in the case of toxics where an "all or nothing"
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situation exists. For example, when one examines the U.S. index values, it is evident that
every index in 1979, excluding those for  reach 19, had at least one  toxic in violation.
Thus, all index  values  along the  southern  shoreline  were  penalized for  high  toxic
concentrations,  but the  values along the  Canadian  shoreline  had  no chance to be
penalized.

     A comparison of  the two trophic  index procedures indicates good  agreement
between the results for the nearshore reaches.  With the Composite Trophic Index, low
values indicate good water quality while low values in the Steinhart index represent poor
water quality.  Due to the inverse numbering scheme of  these two indices, a uniform
ranking (1-20) was utilized to compare the  success of both systems in determining trophic
status.  Table 43 shows the CTI and Steinhart Trophic values and lists the trophic rank for
each reach. When  the two  rankings were summed (Sum of Ranks) and  the sum re-ranked
(Rank of Sums), a combined index resulted providing the same general  picture previously
discussed: the best  water quality (low rank) exists along the north shore and in the eastern
basin; the poorest water (high rank) exists  in the western and central basin south shores.
Discrepancies in trophic  rank occurred at four reaches:  7 (Wheatley), 14  (Huron), 18
(Conneaut) and 20 (Dunkirk). This was attributed to incomplete data particularly with the
toxic group.

Total Phosphorus

     The accelerated eutrophication of Lake Erie has  been attributed to increasing
concentrations  of  phosphorus  over  the  last  century.    Unfortunately,  the  historical
database necessary to substantiate the change in phosphorus concentrations is very weak.
In fact, the most reliable data sets available span only the  years 1970  to present.  Table
44 presents the mean total phosphorus concentrations for the three basins since 1970.
                                          72

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                                 TABLE 44
        TOTAL PHOSPHORUS CONCENTRATIONS (ug/1) IN LAKE ERIE
                                 1970-1980
                                                  BASIN
                                WESTERN       CENTRAL       EASTERN
   YEAR                        x      sd        x      sd       x"    sd
   1970    (CCIW)             44.6    9.6     20.5     7.8     17.5   7.0
   1973    (CLEAR/GLL)       34.7   11.9     18.5     6.2     31.1  22.6
   1974    (CLEAR/GLL)       35.1    8.8     16.8     2.7     20.8   6.9
   1975    (CLEAR/GLL)       42.3    8.6     20.3     6.8     27.6   9.2
   1976    (CLEAR)            44.9   15.0     22.6     5.2
   1977    (CLEAR)            40.7    1.9     24.1     8.1     18.3   4.1
   1978    (CCIW)                             14.2     1.2     13.9   2.5
   1979    (CCIW/GLNPO)      33.9   24.8     14.2     2.9     12.1   3.2
   1980    (CLEAR)            28.8    6.6     13.7     6.9

     The problem  with such presentations is the lack of information concerning cruise
schedules, number  of samples taken or sampling pattern.  Any one of these variables has
the potential to significantly influence the database.  For  example,  if  the  sampling
schedule consisted only of information taken during the unstratified season, one would
expect considerably higher concentrations with much greater year-to-year variability.
Lake Erie, as compared to the other  Great Lakes, is very susceptible to internal loading
from  storm-induced  resuspension during the unstratified seasons,  therefore  a  rather
unrepresentative data set would  be developed.  Conversely, values  obtained only during
the unstratified season may be low due  to settling and low loadings during the summer
months. Considering the  year-to-year variation in cruise schedules,  mean concentrations
of total phosphorus may not necessarily  depict any trend if  the data is  not subjected to
more sophisticated statistical treatment.

     Another  important   factor  in  the  phosphorus picture  for  Lake  Erie is the
quantification of phosphorus loading to the lake.  External  loading  has  been a topic of
major concern since the late 1960s. The first loading estimates were primarily concerned
with the Detroit River, since it contributed greater than 60% of the total  load. It became
evident during the  early 1970s that the lower flow but high concentration tributaries also
required an  indepth treatment.  The quantification  of  the load to Lake  Erie via the
Detroit River proved to be a difficult task. First, a good cross-sectional  sampling pattern
was necessary and  the resulting measured concentrations  had to be flow-weighted.  Once
the Detroit River  portion of the total loading  was estimated, loadings from the smaller
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tributaries had to be determined.  This mainly meant monitoring the rivers from Detroit
to Cleveiand which drain agricultural lands.

     Two major complimentary programs were implemented in order to evaluate loadings
to Lake Erie. First, the Pollution from Land Use Activities Reference  Group (PLUARG)
(IJC 1980) was designed to study land use around all the Great Lakes  and to determine
types of land use activities which resulted in pollution.  PLUARG estimated that from 1/3
to 1/2  of the phosphorus loading to the lakes was associated with land use, and in the case
of Lake  Erie,  crop land drainage  was  the major contributor.   Second,  a Lake  Erie
Wastewater Management Study (LEWMS) was established in  1973.  Three phases of the
project provided detailed information on  phosphorus loading, land use practices and their
effect  on loading culminating  in the development of a management strategy to reduce
diffuse loadings (U.S. Army Corps of Engineers 1982).

     The actual annual loading estimates developed by these two groups as well as others
are not always in agreement  (Fraser  and Wilson 1982).   DeToro and  Connolly (1980)
present loading data via the Detroit River, showing the variation in loading estimates, and
provide a  description of  the  various  methods employed to estimate  the loadings.
Dissimilar  loading  estimates exist  even  in  the most current studies; however,  the
differences have been reduced.  Accurate measurement of diffuse sources, as a result of
LEWMS,  together with somewhat  standard estimates of upper Great  Lakes water and
atmospheric loading  have reduced the variability. For example, the LEWMS estimate for
total 1980 loading to  Lake Erie was  16,455  mt/yr  while  the I3C estimate was  14,855
mt/yr.

     A target  load  of  11,000  mt/yr has been determined to  be sufficient (DiToro and
Connolly 1980) to reduce the anoxia in the central basin by up to 90%.  In order to achieve
the 11,000 mt/yr  target, the diffuse load must be reduced together with total compliance
to the  1 mg/1 discharge from municipal treatment plants. The  proposed management plan
developed by LEWMS calls for improved agricultural practices  to be instigated throughout
the drainage basin in order to reduce the diffuse load.  The problem of  excessive diffuse
or agricultural  loads results from erosion or runoff during storm events or in particular
during  the spring thaw.  It is proposed that agricultural practices  be modified so as to
utilize  no-till or modified till practices  in order to reduce runoff. This potential reduction
in loading together with  reduced municipal contributions should make the 11,000  m  tons
attainable.   Models  used to predict the lake response  to the 11,000  m tons  indicate
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 oxygenated  conditions  can  be maintained (>1.0 mg/1  D.O.) in  the  central  basin
 hypolimnion throughout the stratified period.  The reduction in TP  loading will limit the
 biomass produced and subsequently decomposed in the bottom waters of the central basin.
 The eastern half  of the central basin  is most  likely the first region to demonstrate the
 improved condition.  Areas of the  western basin  and Sandusky  sub-basin where  organic
 carbon production is likely to remain high for several years following reduced loading, will
 likely continue to periodically go anoxic for some time.

 Phosphorus Trends

      The 1970-1982 total phosphorus concentrations for each of the basins are presented
 in Figures 104 and 105.  The values plotted represent  an annual mean  of the individual
 cruise means for  the entire basin.  For example, the data point for 1970 western basin
 (Figure 104) is the mean concentration of the ten  cruise means calculated for that year.
 A simple regression analysis was applied to each of the three basin data  sets. All three
 basins showed a  decreasing trend in  total phosphorus over the  twelve  year  period.
 Phosphorus concentrations indicate  a decrease  of nearly 0.5 ug/1 per year.  This analysis
 does not take into account either seasonal or spatial variability, thus these results should
 not be considered  conclusive.

      In  order to  reduce seasonal variability, total phosphorus concentrations from the
 central basin epilimnion during early  stratification (mid-June  through  mid-July)  were
 plotted (Figure 106).  The early period of stratification was chosen to reduce variability
 resulting from resuspension, also loading is generally approaching a  seasonal low,  further
 reducing external  influences.  In addition, phytoplankton biomass is  very low at this  time
 following the spring diatom pulse.   The total phosphorus resulting from the early spring
 internal  and external loading processes has largely settled either as organic plankton or
 inorganic clay bound phosphorus.  Even  this selective treatment to  reduce variability in
 the data does not adequately improve the data so as to conclusively resolve a trend.

     Recently,  other  attempts have  been  made  to see  if   Lake  Erie phosphorus
 concentrations have been affected by efforts to reduce  external loading. Kasprzyk (1983)
analyzed the 1974-1980 phosphorus and chlorophyll  databases.  Data were partitioned into
spring and fall in order to reduce  seasonal variability, and geographically sectioned to
 reduce spatial effects.   Total phosphorus showed no clearly detectable trend using this
approach.
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     In a significantly more sophisticated approach, El-Shaarawi (1983) examined several
parameters in the Lake Erie database for long term trends.  Available data from 1968-
1981 was utilized.  The data were not seasonally partitioned, however, each of the basins
was  examined separately.  A  model  was developed to  adjust  for seasonal and spatial
variability and applied to the data set.  Results indicate  a decreasing  trend for total
phosphorus in all three basins. Total  phosphorus has decreased  substantially since 1971,
with the western basin showing the greatest decrease, followed by the central and eastern
basins, respectively.

     From these results it is evident that Lake Erie  is  beginning  to  respond to the
reduction in loading.  In the next ten years it will become evident if the effort to reduce
phosphorus inputs to the lake has had a significant  effect on curbing the accelerated
eutrophication.

Chlorophyll Trends

     The 1970-1982 corrected chlorophyll a concentrations for each of the  basins are
presented in Figures 107 and 108. A simple regression analysis was applied to each data
set to  detect if any change in concentration was evident over  the thirteen year period.
All three basins indicated a decrease, with the western and central showing approximately
0.3 ug/1 per  year decrease and the eastern basin a 0.6 ug/1 per year decrease. As was
mentioned with the analysis of the  total phosphorus data, these results should not be
considered conclusive.

     Kasprzyk (1983)  reported a decreasing chlorophyll  trend for the fall in  the central
and eastern basins, while no trend was evident in the spring in either basin.  No trend was
evident during either period in the western basin. El-Shaarawi (1983) indicated a similar
trend, reporting decreasing concentrations of chlorophyll in the central and eastern basins
and a non-significant increasing trend for the western basin.

     Since the program to reduce the phosphorus  loading to Lake Erie was based on the
assumption that decreases in lake concentrations of phosphorus  would result in decreases
of phytoplankton  biomass,  the relationship between  total  phosphorus and  chlorophyll
trends  was examined (El-Shaarawi 1983).  Figure 109 presents chlorophyll values corrected
for seasonal  and  spatial variabilities  plotted against  corrected total  phosphorus values.
The relationship was fitted with a straight line:
                                            76

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                                  y= 1.6 + 0.20617«x

 where x is the concentration of phosphorus and y is chlorophyll.  The average 1971 and
 1980 seasonally and spatially corrected concentrations are shown, indicating the response
 of the phytoplankton biomass (chlorophyll) to decreasing phosphorus concentrations.

 Dissolved Oxygen

      Low concentrations of dissolved oxygen in the bottom waters have been considered a
 key issue in the eutrophication of Lake Erie for more  than three decades.  The seriousness
 of the oxygen problem was not fully recognized until the early 1950s when a severe period
 of anoxia resulted in the eradication of massive populations of the benthic mayfly nymphs
 (Hexagenia) in the western basin (Britt 1955).   Since  1950, numerous accounts of oxygen
 depleted bottom waters have been documented for both the western and central basins.
 The major focus in  terms of dissolved oxygen  monitoring efforts has been on the central
 basin hypolimnion.  Even though western  basin bottom waters are subject to recurrent
 episodes of anoxia during the summer months, such events are too intermittent to monitor
 using  a conventional survey  schedule.    Since  the central  basin  remains  stratified
 throughout the  summer  and  is  characterized  by  a progressive  decline  in oxygen
 concentration through the stratified season, changes in hypolimnion oxygen concentrations
 have  been considered the best  indicator of response to programs  designed  to curb the
 accelerated eutrophication of the lake.

      The  most  obvious  effect concerning anoxic  conditions  at  the  sediment water
 interface or in  the  hypolimnion is the resultant elimination of aerobic  organisms.  For
 example,  an attempt to document the  changes in 0- concentration in the central  basin
 hypolimnion using fossil remains of ostracods  has shown a species  shift  which has been
 attributed to periodically low dissolved oxygen concentrations (Delorme 1982).  Similar
 biological effects on fish and invertebrates have also been noted by other investigators.
 In addition to effects on  the biota, anoxia serves as a mechanism for significant internal
 loading of soluble phosphorus, ammonia, dissolved  silica and numerous metallic species
 (Svanks and Rathke 1980).   Internal loading, particularly of phosphorus, provides an
 additional nutrient source to further stimulate the eutrophication of the basin.

     Anoxia (defined as  concentrations of 0-<0.5  mg/1)  was first  documented in the
central basin in 1959 (Beeton 1963) and has since been reported to have gone anoxic each
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year surveyed.  This does not imply that anoxic conditions did not exist prior to 1959 but
sufficient survey documentation  is not available.  For example, during  the  1929 study
(Fish 1960) the lowest dissolved oxygen recorded was *.*  mg/1  during mid-August at a
station *2 km northwest of Cleveland.  Since the following survey was not conducted until
after turnover, any anoxia that might have developed late in the stratified period would
not have been detected.  In  1930, Wright (1955) measured oxygen values of < 0.8 mg/1 just
north of Marblehead, Ohio.  This area is  the border between  the  western  and central
basins; thus, it cannot be interpreted as indicative of the open waters of the central basin.
In fact, this region, referred to as the Sandusky sub-basin located in  the southwest corner
of the central basin is shallow (mean depth 12-13 m) and  generally considered the most
eutrophic open water area of the basin.  It is very likely this was the first central basin
region to suffer extensive oxygen depletion problems since it has a very thin hypolimnion
(< 2 m) and receives a high organic loading from the western  basin and Sandusky Bay.
Recurring  anoxia may  develop  in this region  after  destratification if central basin
hypolimnion waters move back into the area, i.e. during seiche activity.

      The total  areal extent of anoxia in  the open  lake portion of the basin has been
examined since first documentation in 1959 (Figure  110).  The total area represents the
composite anoxic area recorded during the  entire stratified season? therefore, it does not
indicate  the extent of  stratification at any one point in time.  For  example,  if the
Sandusky sub-basin was anoxic in  mid-summer and destratified by late summer, remaining
oxygenated, it was included in the total estimated  area.   The cumulative areal extent
reported is entirely dependent on the timing of cruise schedules, and estimates are likely
to  be conservative  since conditions may change  rapidly  during  later   stages  of
stratification.

      The processes involved  in  the  depletion of oxygen from the hypolimnion  (HOD)
center around the decomposition of organic matter in the water  column (WOD) and at the
sediment-water  interface (SOD) (Figure 111). In  addition, many reduced metallic species
also contribute to the oxygen depletion as chemical oxygen demand (COD).

      The oxygen  demand  in  the water   column  (WOD)  is  mainly a result  of the
decomposition of dying planktonic organisms (primarily phytoplankton) and respiration of
living planktonic organisms, including bacteria, referred to as biochemical oxygen demand
(BOD).   The accumulation of plankton biomass  and detrital carbon in the  hypolimnion
water column results from settling of organic material originally located in the euphotic
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zone or epilimnion.  In addition to the BOD, COD may periodically contribute to the O2
depletion in the water column, particularly following severe storm activity.  Turbulent
conditions in the hypolimnion result in the resuspension of the upper, floculant sediment
layer, resuspending both  organic and inorganic material. The COD becomes even more
significant after anoxic conditions have been established when reduced chemical species
(i.e., Fe, S, and Mn) are released into the overlying waters acting as an additional sink for
oxygen.

     The sediment oxygen demand (SOD) portion of the HOD is also a combination of
BOD and COD.  The seasonal accumulation of organic material not totally decomposed in
the water column eventually exerts an oxygen demand at the sediment water interface.
In addition, the benthic  community  primarily made up of  Oligochaete and Chironomid
populations, consumes O- through respiration.  COD exerted at the interface between the
oxygenated  sediment surface and anoxic  lower sediments certainly is more significant
than the COD in the water column.

     It should be noted that a third factor has been proposed as an additional contribution
to the HOD.   DiToro and Connolly (1980), in an attempt to model  the  O2 depletion
process,  have proposed  that the deep sediments also  exert a significant  O2 demand;
however, there is as yet no experimental SOD data that has verified this theory.

     The percent of the total demand exerted by  the individual processes just discussed
has been studied intensively, but, as yet, remains unsolved.  Certainly all the components
mentioned make up the major portion of the HOD;  however, factors such as temperature,
light penetration and hypolimnion thickness influence  the  O2 depletion rate of each
individual process.

     The DiToro model proposed that 60% of the HOD is due to WOD while the remaining
40% was attributed to SOD (Table 45).  Using a somewhat different approach, Burns and
Ross (1972) concluded that 88% of the depleted O2 resulted from bacterial decomposition
of sedimented algae (BOD) and 12% resulted from oxidation of reduced metallic species
(COD).  These two  estimates are not comparable since they do not encompass the same
factors  or combination  of  factors  accounting  for O2 depletion.   As yet,  a strict
quantification of the processes leading to depletion has not been adequately devised.
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                                    TABLE 45
 PERCENTAGE CONTRIBUTION OF OXYGEN SINKS TO DISSOLVED OXYGEN DEFICIT
       AT THE TIME OF MINIMUM D.O. IN THE CENTRAL BASIN HYPOLIMN1ON
                          (From DiToro and Connolly 1980)
                  Oxygen Sink                    Percent Contribution
                                                  1970         1975
        Deep Sediment Oxygen Demand              28.7         22.8
        Surface Sediment Oxygen Demand            11.5          8.2
        Organic Carbon Oxidation                   42.5         46.9
        Phytoplankton Respiration                  17.3         22.1

     In-situ  attempts  to measure  WOD  and  SOD have  had only limited success.
Measurements of SOD  were first made on Lake Erie during Project Hypo (Lucas and
Thomas 1972, Blanton and Winklhofer 1972).  Also, in 1978 and 1979, three studies were
undertaken to measure SOD rates in the central basin (Davis et al. 1981, Snodgrass and
Fay  1980, Lasenby 1979).  The techniques employed by  all of the above investigators
utilized an in-situ chamber positioned on the  sediments,  except Lasenby  (1979) who
measured  rates  using  cores  manipulated under  laboratory  conditions.    Table  46
summarizes the calculated rates.

     WOD measurements have not been made as frequently as SOD measurements, and
some of the studies have not as yet been published due to  problems in interpreting the
data.  The   methodologies employed  to  measure  uptake  rates are  prone to various
analytical problems,  making interpretation of the  data  difficult.  Davis et al. (1981)
reported WOD values measured at two locations in  the central basin during  1979 (Table
47).  Note that  the  percent contribution  of WOD  to the  HOD increases  through the
summer stratified period, due to the increase  in phytoplankton biomass and POC found in
the water  column during late August.   The  shift  from 80% SOD in June to 76% WOD by
August is  indicative of  the quantity of organic material accumulated in the hypolimnion
water column. This shift is not  reflected in  DiToro's model.

     In attempting to  quantify the depletion rate in the central basin, a discrepancy
between the rates calculated from the  combined in-situ measurements of SOD and WOD
and  the  more conventional method  of  calculating the  rates via  changes in D.O.
concentration measured on consecutive  surveys (cruise interval technique) is evident. The
in-situ  rate (SOD + WOD = HOD) is a direct measurement of the two oxygen consuming
processes  and does not account for any physical processes which might influence the
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introduction or elimination of oxygen in the hypolimnion through the stratified period.
The mean HOD rate for the central basin measured by in-situ techniques was 0.36 g 02
m"3d~  or 10.8 mg O2 1" mo"  assuming an average hypolimnion thickness of *.35 meters
(Davis et al. 1981).  This indicates that if the central basin  hypolimnion were a closed
system, the oxygen would  be depleted within a few weeks.   If these measurements  are
representative of  the  actual rates, the  oxygen  supplied to the hypolimnion via outside
sources is sufficient to prevent the more immediate and severe O2 depletion resulting
from  the combined WOD and SOD.  The cruise interval technique measures the oxygen
concentrations  in  the  hypolimnion over several cruise intervals throughout the stratified
period. The depletion  rate is calculated as the difference between the O2 concentrations
between successive  cruises, thus providing  information as to the net quantity of  O2
depleted for a specific period of time. As a net measure of the oxygen lost this procedure
alone  does  not  allow for  quantification of  physical processes  affecting oxygen
concentrations over the interval.  Thus, both  procedures lack the sophistication necessary
to determine the true oxygen consumption rate.

      Dissolved oxygen has been one of the key issues in evaluating the eutrophication
problem in Lake Erie;  consequently, methods had to be developed  to measure rates  and
examine historical data in hopes of determining if the lake has changed over the period of
record. The first attempt to examine historical data was in conjunction with the 1970
Hypo Project.  Dobson and Gilbertson (1972) used a simple cruise to cruise difference in
O2 concentrations averaged over the stratified season in  order to determine a rate  for
each  historical data set.  They estimated an increase in depletion rates from 0.05 g 0-
   3-1                        -31
m   day   in 1929 to  0.11  g 02 m   day  in 1970.  Data from sixteen studies spanning
this time frame were plotted  and a trend line was drawn over the time period (Figure
112).  The data indicated an annual increasing 0« demand rate  from 1950 to 1970 of 0.075
    -3   -1  -1
g m   mo   yr   or a 3% per year increase.

      Following the completion of the Hypo Project, it became evident  that accurate
determinations of depletion rates required a significantly  more sophisticated treatment of
the data if future trends were to be documented.   It was evident that oxygen transfer
across the  mesolimnion by exchange must be taken  into account if  oxygen depletion
calculations of  an accuracy of + 3% were achieved (Burns 1976).  The data from Project
Hypo  and the surveillance program accumulated during the CCIW 1970 monitoring effort
provided adequate information to develop  a model  to  account  for  internal physical
processes affecting  hypolimnion  O2 concentrations.   It was found  that during  the
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stratified period the central basin hypolimnion is subject to several processes which alter
its volume  and/or 
-------
studies were designed to further investigate the variability within the individual basins
due  to  sampling locations, hypolimnion  depth,  temperature, mesolimnion/hypolimnion
exchange and transport of water between the eastern and central basins. It was necessary
to resolve these questions before adequate corrections or modifications could be made to
historical data sets.  The study was designed to provide a complete compliment of data to
be used in conjunction  with the Mesolimnion Exchange Model and aid in determining a
homogeneous area within each basin.  These areas  were then used in conjunction  with
historical  data sets, first  to calculate a rate using only stations within these areas,
followed by corrections to reduce variability resulting from year-to-year differences in
temperature and hypolimnion thickness.

     Two important physical processes were studied, resulting in a better understanding
of how  these processes can affect the  depletion  rate.   First,  Ivey  and Boyce (1982)
examined  the vertical  mixing  of the mesolimnion  into the hypolimnion  in the central
basin.  It  was determined that downward entrainment accounted for  approximately 10-
20% of  the O2 consumed in August 1979.  This varies  from  year to  year depending on
meteorological conditions; however, it must be accounted for  in order to  obtain  an
accurate measure of the actual consumption rate.

     Second, Boyce et  al. (1980) studied  the  movement  of  eastern  basin mesoiimnion
water into the central basin hypolimnion across the Pennsylvania  ridge. During 1977, two
major transfers of water from the eastern basin  mesolimnion into  the central basin
hypolimnion occurred.  The second of the two occurrences was considered most important
to the oxygen regime of the central basin.  During early August, 7 km  of water passed
from the eastern basin  mesolimnion into  the central basin hypolimnion.  This  additional
volume  was equivalent  to 17% of the total hypolimnion volume  at that time, but more
significantly the new water mass transported oxygenated water into the oxygen depleted
central  basin hypolimnion.   This event raised the mean central  basin O2 concentration
between 0.5 and  1.0 mg/1, or an equivalent  of  5-10 days'  worth of observed oxygen
demand. However, it was calculated that this newly transferred water mass influenced
only the eastern third of the basin leaving the western two-thirds relatively unaffected.

     With this additional insight into lake processes, the Mesolimnion Exchange model
could then be applied to the 1977 and  1978 data sets to account for exchange processes
affecting  the  rate (Rosa and  Burns 1981). After  applying the  Exchange Model to the
stations within the homogeneous area, two additional corrections were applied. First, it
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was necessary to adjust for the year to year variation in hypolimnion temperatures. Since
changes in temperature primarily affect biological reaction rates, a QJQ coefficient was
used to compensate for the year to year temperature  variation.  Second, hypolimnion
thickness was adjusted to the mean of 4.7 m when profile information was available (1961
to present).  The results of each step-by-step adjustment to the data sets are presented in
Table 48 and illustrated in Figure 113 (Rosa and Burns  1981).  The resultant historical
depletion rate was determined to be 0.035 mg l^mo   yr   from 1929 to 1980.

     In a recent report, El-Shaarawi (1983) presented a statistical  model developed for
dissolved oxygen concentrations in the central basin of Lake Erie.  Two major conclusions
were reported.  First, the central basin oxygen depletion rate has increased from 1967 to
1979 and  second, the increase  in depletion rate was due  to an  increase in phosphorus
levels.

     We have seen definite indications  of eutrophication effects on the lake such as the
eradication of the mayfly and a substantial decrease in many cold water dependent fish
populations.  Lake Erie central and western basins are exceptionally shallow compared
with water  depths of  the  other Great Lakes; thus,  natural  eutrophication  plays an
important role in the changes measured  in the lake.  However, cultural stress primarily as
phosphorus loading should not be underestimated as  a major  factor in  accelerating the
natural eutrophication process.

Objectives and Standards

     Environmental measurements  have been  made each year since  1973 to assess
compliance with the general and specific objectives of the 1972 and, subsequently,  1978
Water  Quality  Agreements.   These measurements have been  used  to  evaluate the
effectiveness of remedial programs and to anticipate the changing trends in water quality.
Responsible agencies  within state, provincial, federal-Canada and federal-United States
governments contribute information and recommendations at three levels: site-specific,
lakewide and system wide (Great Lakes Water Quality Board 1981).

     The Water Quality Board (e.g. 1979, 1980) reported on "problem areas" until 1981. A
problem area was any locality where agreement objectives and/or standards of the  local
jurisdiction were exceeded  or  desired water  quality objectives could  not  be  attained.
Starting with its 1981 Report, the Water Quality Board initiated a process to establish
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"areas of concern" based on environmental measurements of sediment, biota and water.
Although the process is recognized as containing a subjective element, the importance of
this procedure lies in its application of uniform criteria across jurisdictional boundaries.

      This section applies the "area of concern" criteria to water quality data collected
during the 1978-1979 intensive study period of the Great Lakes International Surveillance
Program (GLISP) on Lake Erie.  The  criteria were  applied in a uniform  manner to all
water quality data collected during the study period and recorded in STORET.

      Data for water quality analysis was retrieved using the STORET standards program.
The original databases were collected from tributary studies or connecting channels, i.e.,
Detroit River, intensive nearshore and open lake surveillance programs, municipal water
intake plants and other miscellaneous  sources.  The individual data sets were analyzed to
determine violations or identify  problem areas as defined by  the  International Joint
Commission (I3C) Water Quality Objectives and  by the respective  state or provincial
water quality standards.

      The  Water  Quality Board  has noted  (1981)  that whenever  an Agreement  or
jurisdictional value  is exceeded,  there  is a  potential  or  real threat  to  public  health,
impairment of water use or deleterious  impact on the human health  or aquatic life. To
aid the environmental management plans within each jurisdiction, Agreement objectives
and jurisdictional standards are compared and reported in individual discussions.

      Recurring violations were recorded for conductivity, pH and iron.  These parameters
made up a major portion of the violations at many stations, particularly in and around the
tributaries and the nearshore  region of all three basins.  In general, neither conductivity
or pH violations were considered to be a  result of effluents entering the lake from either
municipal  or  industrial  sources.   The principal ion  concentrations for  Lake Erie,
particularly chloride and bicarbonate are naturally greater than those found in the other
Great Lakes resulting in higher conductivity values.  One exception was the Grand River,
Ohio  where chloride loading  from industrial sources is very high (70  mg/1) resulting in
conductivity values of 500 umhos/cm.  Similarly, mean pH values for the lake are in the
order of 8.0 and on  occasion  may exceed 9.0 primarily in biologically productive regions.
Neither pH or conductivity values  recorded in the lake  posed any health problem to the
populace utilizing the lake or to the biota.
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      The other major violator was iron and as with pH and conductivity is naturally high
in concentration.  Highest concentrations were  generally found in and around tributaries
during the peak spring loading period.  Some  contribution is made by the heavy industry
around the lake which can be  an important localized source. Iron poses no health dangers
to the lake community  and any  problems are  aesthetic in  nature,  resulting from the
precipitation of iron hydroxide.  None of these three parameters will be further discussed
in this section, and the  reader can assume frequent violations for  all three parameters
throughout the lake.

      State of  Michigan.  A total of  21 parameters were retrieved  for analysis of water
quality in the  water governed  by the state of  Michigan (Table 49). Of the 21 parameters
retrieved, only fluoride, arsenic, selenium, and un-ionized ammonia values did not exceed
IJC or state limits during the two-year study period.

      Phenolic compounds were recorded in concentrations exceeding the  objective at one
tributary monitoring station, two water  intakes and at 35 of 36 stations located along the
Detroit River. Heavy industry, largely steel production, effluents  entering the Detroit
River and its  tributaries are the principal sources of contamination.  Too  few samples
were  collected at near shore or open  lake stations for evaluation of phenolic compounds.
Phenols represent a substantial violation in the connecting channel and contributed to the
designation of the region as a problem area (GLWQB 1980).

      Fecal coliform bacteria  counts  from samples collected in the connecting channel
and the nearshore zone  frequently exceeded the 200 organisms/100  ml standard for  total
body contact with the water (swimming).  The sources of fecal contamination,  principally
the Detroit Sewage Treatment Plant, contributed to the designation of the Detroit River
as a problem area (GLWQB 1980).  Fecal coliform data taken over the two-year period
indicated the Detroit River and nearshore waters south of Detroit  (Herdendorf and Fay
1981)  represent a significant problem area.

      In  addition,  a number of the  trace  metal  parameters   retrieved  revealed
concentrations  exceeding standards.  Cadmium, copper and  mercury values  exceeded
standards at several tributary, water intake, connecting channel, nearshore and open lake
stations.
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      State of Ohio.  Lake Erie water quality  data were compared with water  quality
 objectives  set  forth  by  the IJC  and  the standards  established by  the Ohio  EPA
 respectively.   Maximum and minimum  criteria values  for  IJC  objectives and  Ohio
 standards are listed in Table 50.  Since Ohio waters comprise a dominant portion of the
 southern half  of Lake Erie and receive a majority of the lake's agricultural and industrial
 inputs, a  summary of the number and extent of observations exceeding  criteria  in Ohio
 waters as a unit would not  usefully  delineate water quality problem areas.  For the
 purposes of this report, exceptions to  the criteria limits  were examined and summarized
 by county jurisdiction (Figure 11(0. Sampling stations within each county were  divided
 into three categories: tributary monitors, nearshore surveillance stations and water intake
 monitoring stations, while open lake data was not sectioned into the county boundaries.

      Ottawa  and Lucas Counties.  Violations for  this region, located in the westernmost
 section of Ohio waters, include water quality monitoring  stations located in the Maumee
 River near Waterville; water supply intakes for  Marblehead, Port Clinton, the Bass Island
 area,  Catawba, and Toledo;  and the nearshore  surveillance stations centered  around
 Toledo and Port Clinton.  Data from only one tributary, the Maumee River, was retrieved
 for this section of Ohio  waters although  other  tributary  data was available.  Violations
 occurring in the Maumee River include those reported for cadmium, manganese, copper,
 lead, mercury, zinc and  phosphorus.  Of  these  parameters, cadmium  and copper values
 exceeded  the established criteria most frequently. Cadmium values ranged from 1.0-13.0
 ug/1; however, data for  this  metal is  suspect, due to the  consistent reporting  of the
 detection limit value, i.e. 5 ug/1. Since  the detection limit exceeds the violation limit,
 false conclusions concerning cadmium  violations were inevitable.  Data  for manganese,
 copper, iron, zinc, lead and mercury indicate that  these metals may constitute a problem
 in the Maumee River.

      Fourteen nearshore stations were sampled  in the vicinity of Toledo and Maumee Bay
 in Lucas County.  Violations occurred  consistently for phosphorus, cadmium, chromium,
 copper, nickel, zinc, manganese and fecal coliform  bacteria.  Phosphorus values were in
 violation at nearly every station sampled in the Toledo area, but represent only 4% of the
 total number  of samples taken.   The  highest values arise  during sampling intervals
coinciding  with high runoff  periods  from the  Maumee  drainage basin.    Of  these
 parameters,  cadmium  values  violated  standards   most  frequently.    Heavy  metal
contamination appears to be rather severe in the Toledo area.  Nearly 100% of cadmium
records, 75% of the copper observations and 50%  of zinc, nickel and manganese samples
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violate standards.  The severity of these violations indicates that the Toledo area may be
identified as an area of concern.

     Nearshore surveillance stations located in Ottawa County waters include 14 stations
sampled in the  vicinity of Port Clinton.  Violations were most often found for cadmium,
copper, nickel  and zinc.  Occasional  violations were  reported  for dissolved oxygen,
chromium, selenium, manganese, mercury and fecal coliform bacteria. Due to the number
                              «,
of parameters found in violation and the severity of violations reported, the Port Cinton
area may be regarded as an area of concern.

     Water intake data for this section of Ohio waters was rather limited.  Intake data
from  Marblehead, Port Clinton,  Put-in-Bay,  Catawba,  Oregon and Toledo all  showed
violations of cadmium and copper values. Fecal colif orm bacteria violations appeared at
the Port Clinton and Oregon intakes only, while zinc violations were found at the Put-in-
Bay, Catawba  and Oregon intakes,  and lead violations occurred only at the Catawba
intake.  Violations of phosphorus, nickel, selenium  and phenols  occurred at the Oregon
intake only.  It appears that while not a great percentage of violations was detected at
any one intake, the data from the  Oregon water  intake contained violations  of  more
parameters and at higher percentages.

     Erie  and  Sandusky Counties.  Included  in  this region of Ohio waters are  three
tributaries, nearshore  stations  in  Sandusky  Bay  and along the southern  shore, and
municipal water intakes for the cities of Vermilion, Huron, Sandusky and Milan.

     Of the three tributaries sampled (Sandusky,  Huron and Vermilion Rivers), violations
occurred most frequently and involved more parameters at  sampling stations in the
Sandusky River.  Copper  concentrations violated IJC objectives (Ohio does not have  a
copper standard)  more often than any other parameter measured  in the Sandusky River.
The mean concentration of copper in the Sandusky River was 32.82 ug/1, well below levels
reported to cause adverse effects to humans.  The frequency, extent and magnitude of
copper violations has contributed to the designation of the Sandusky River as a problem
area (GLWQB 1980).

     Measurements of other parameters which frequently resulted in violations included
cadmium, phosphorus and lead. Cadmium data must be viewed with skepticism in that it
was reported  by OEPA  at  a  constant concentration  of 5.0  ug/1 (detection  limit).
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Phosphorus measurments in excess of criteria do not appear often at the Sandusky River
sampling stations, with a total of nine violations from 26 samples, or 35 percent.

      Dissolved oxygen, total phosphorus, copper and cadmium were the only parameters
which were  found to  exceed DC  objectives  or  Ohio standards in the  Huron River.
Phosphorus values exceeded objectives in 103 out of 579 total samples (17.8 percent) in
the Huron  River, but the sample mean (336 ug/1) was below the state standard of 1.0 mg/1,
but close to the IJC objective of 500 ug/1. It is interesting to note that the percentage of
phosphorus violations in the Huron River was similar to that found in the Sandusky River
even though the principal sources were different (municipal and agricultural respectively).

      Copper  and cadmium violations  occurred infrequently, but  the concentrations
reported were consistently indicative of  detection limits and were  above the upper limit
of the established criteria. Violations of this nature could not be adequately assessed.
Violations  of dissolved oxygen involved 6 of 12 samples ranging from 2.0 to 5.3 mg/1 with
the sample mean (x = 5.07  mg/1) below the standard of 6.00 mg/1.  Thus, dissolved oxygen
may be a problem in the Huron River and contributed to its designation as a problem area
(GLWQB 1980).

      Violations in the Vermilion River were limited to copper, cadmium and zinc. Copper
and cadmium values were  suspect due to reasons previously noted for  the  Huron River.
Only two samples were analyzed for zinc, both of which exceeded standards. One of the
samples was in violation of standards by more than an order of magnitude.  Sample size
for zinc violations  was  too  limited to  adequately  assess the  extent or  source  of
contamination.

      Nearshore surveillance stations situated in Erie and Sandusky counties included six
stations located within Sandusky Bay and fifteen stations located along a southern shore
region extending  from  the Sandusky water  intake to Old Woman's Creek.   Cadmium,
copper, nickel and zinc measurements exceeded standards for at least 50% of all samples
taken at each station within Sandusky Bay.  Although an infrequent number  of violations
occur for fecal coliform bacteria, at least one sample exceeded standards at  every station
in Sandusky Bay.   Given  the  frequency of heavy  metal  violations coupled  with  high
conductivity and fecal coliform bacteria values, the Sandusky Bay area is one of concern.
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     The fifteen  stations located along the southern shore from  the  Sandusky water
intake to Old Woman's Creek contained a substantial number of heavy metal violations.
Every  cadmium value recorded was in  excess  of  standards.  Copper,  nickel and  zinc
averaged approximately a 50% violation rate with at least one sample from each station
having at least one heavy metal in  excess of standards.  The dissolved  oxygen standard
was exceeded on occasion reflecting water quality problems in this area of the nearshore
zone.

     Water supply intakes for Kelleys Island, Milan, Vermilion, Huron and Sandusky were
sampled  too infrequently to adequately  describe any water  quality problems.  Cadmium
criteria were violated whenever samples were measured; however,  these measurements
were suspect due to a constant record of 5 ug/1.  Zinc is the only other parameter which
frequently  exceeded standards at all sites,  with a  mean  concentration at all intakes in
Erie County of 67.0 ug/1, well above the maximum criterion limit of 30.0  ug/1 and may be
reason for concern.

     Lorain County.  Data from the two tributaries monitored  in  Lorain County were
retrieved for analysis, the Black River  and  the  Vermilion River.  The Black River was
intensively sampled by the USGS and OEPA.  Both agencies  reported numerous violations
for many parameters including (in order of frequency and magnitude): cadmium,  copper,
phosphorus, phenols,  fecal coliform bacteria,  dissolved  oxygen,  nickel,  manganese,
nitrate-nitrogen and cyanide. Due to the large number of parameters for  which violations
were  reported and  the  large  percentages  of violations which  occurred  for  most
parameters, the Black River has been designated a problem area in Lake Erie (GLWQB
1980).

     The Vermilion River  did not contain the magnitude  or severity of violations which
were reported for the Black River.  Phenols and fecal coliform bacteria were the  only
parameters  which violated standards or objectives  in sufficient numbers  to warrant
concern.  Records in excess of criteria for copper, cadmium and nickel were  suspect due
to the consistency of the values  reported. Other parameters such as phosphorus, nitrate-
nitrogen, chromium, lead and zinc infrequently exceeded standards.

     Nearshore surveillance stations sampled for this  region included 19 stations near
Lorain, Ohio.  Trace metal concentrations in excess of criteria were severe, especially
cadmium, copper and  zinc, with frequent violations for nickel and manganese.  Total
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 mercury concentrations in excess of criteria were infrequent.  In addition to trace metal
 violations, dissolved oxygen standards were frequently violated.  A substantial number of
 objectives were frequently  exceeded in  the  nearshore  area  surrounding Lorain;  thus,
 considering the magnitude and number of violations in the vicinity of Lorain, this region is
 considered an area of concern.

      Water intake data for this section of Ohio waters was scarce.  Copper and cadmium
 violations were inconclusive due to the consistent reporting of detection limits.  Only two
 other  parameters were  found to violate standards: lead at  Avon (one  sample  was
 collected), and fecal coliforms at Lorain.

      Cuyahoga County.  Data from the four tributaries monitored in Cuyahoga County
 (the Cuyahoga River, Euclid Creek, the Rocky River and Big Creek near Cleveland) were
 retrieved from STORET for comparison with KJC and Ohio water quality standards.  Of
 these four tributaries, records from the Cuyahoga River included the greatest number of
 parameters violating the  I3C Objectives and OEPA Standards.  Copper, nickel, zinc and
 phenols exceeded standards wherever sampled; however, the data for copper  and nickel
 are suspect since the majority of the concentrations were reproted as 30 ug/1 and 100
 ug/1, respectively.  It was assumed that these  values represent the detection limits and
 were retrieved as violations.   Zinc and  phenol concentrations appear  reasonable and
 represent a real problem in the Cuyahoga River.   Other parameters  which  frequently
 violated standards include cadmium, lead, fecal coliform bacteria,  total phosphorus and
 dissolved oxygen,  and  occasionally   selenium,  chromium,  ammonia,  nitrogen  and
 manganese.  The magnitude and frequency of violations of the many different criteria
 indicate the Cuyahoga River is an area of concern.

     Euclid Creek ranks  second to Cuyahoga River  in total  number of violations and
 number of  parameters violated  in Cuyahoga County.   Parameters  most  frequently
 violating standards include cadmium,  lead,  nickel, copper, phenol and fecal coliform
 bacteria.  Detection limit problems previously noted for copper and nickel were evident,
 and in addition, cadmium values were suspect due to a constant reported concentration of
 5.0 ug/1. Phosphorus and  zinc violated standards/objectives infrequently; however, fecal
coliform bacteria and phenols exceeded criteria routinely.  Thus, Euclid Creek represents
a potential area of concern.
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      The concentrations of trace metals in the  Rocky  River exceeded  standards  or
objectives more frequently than the other tributaries in Cuyahoga County with 100%  of
the  manganese  concentrations exceeding the criteria, followed by  copper (76%),  lead
(29%), phosphorus (24%), zinc (22%) and cadmium (12%). This tributary was  monitored  by
the U.S. Geological Survey; USGS records did not  contain consistent concentrations for
copper and cadmium as did stations monitored by OEPA. These  violations resulted in the
designation of the Rocky River as a problem area (GLWQB 1980).

      Although concentrations of ten parameters were found to exceed criteria at Big
Creek near Cleveland, an insufficient number of samples (N    =7) were collected during
the period of record to adequately identify this tributary as an area of  concern.

      Near shore surveillance stations sampled in this region of Ohio included 33 sites
extending from east of the Rocky River to west of Euclid, Ohio. The majority of sampling
stations were located in the vicinity of  Cleveland. Cadmium and copper  records most
frequently exceeded criteria (50-100%) with violations occuring  at every station.  Other
trace metals which frequently exceeded criteria  include lead (21%), nickel (31%) and zinc
(40%) with manganese and mercury concentrations  only occasionally  exceeding criteria.
Dissolved oxygen records occasionally exceeded the limits in the  nearshore zone, with
approximately 10.5% of the total number  of records falling below the  standard. Although
the percentage of  violations at each station was low, violations occur at every nearshore
station and  were at times severe.  Frequent dissolved oxygen violations coupled with
numerous trace metals violations  served to identify  this reach as a problem area (GLWQB
1980).

      Water  intakes in Cuyahoga County  include those for Cleveland-Baldwin, Cleveland-
Crown, Cleveiand-Divison, Cleveland-Nottingham, East Cleveland and Lakewood.  Only
copper and cadmium  values were available from these locations  and were reported  at
detection limits; thus assessment of these areas was not feasible.  Sample size at water
intake monitoring  stations in Cuyahoga County  was too small to discern if the area  of
concern designation was warranted.

     Lake and Ash tabula Counties. Station data retrieved from STORET for comparison
with water quality criteria from  this portion  of Ohio's Lake Erie  waters included four
tributaries: the Ashtabula River, Conneaut Creek, the Grand River and the Chagrin River.
Nine surveillance stations near  Conneaut, 19 stations near Fairport and 18 stations near
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 Ashtabula were used for the nearshore  analysis.   Water intake monitoring data was
 retrieved  for intakes serving  the  cities  of Madison,  Mentor,  Painesville,  Geneva,
 Ashtabula and Conneaut.

      Of the tributary monitoring data retrieved, criteria were exceeded most frequently
 at stations located  in the  Grand River  at or near  Painesville.   Violations occurred
 consistently at  different  locations in the  lower portion of  the Grand River for cadmium
 and copper, with standards exceeded 100% of the time.  Cadmium and copper violations
 were suspect, since  constant concentrations .of 5.0 ug/1 for cadmium and 30.0 ug/1 for
 copper were reported. Other parameters which frequently exceeded criteria in the Grand
 River included dissolved oxygen,  lead, nickel, zinc, manganese, phenols and fecal coliform
 bacteria.  Phosphorus values exceeding criteria  occurred  rather  infrequently, although
 they were occasionally present  (5 violations from 42 samples, or approximately  12%).
 Mercury values  exceeded the standard in 1 out of S samples (12.5%). Due to the large
 number of violations per  sample coupled  with the wide variety of parameters that
 exceeded criteria, the Grand River is considered an area of concern.

      Parameters with concentrations in excess of standards or objectives in the Chagrin
 River included copper, cadmium, nickel,  phenols and fecal  coliform bacteria.  Again,
 copper  and cadmium values were highly suspect.  Nickel  appears to be suspect at this
 location for similar  reasons; violations (>25 ug/1) occur 100%  of the time with all
 reported concentrations constant at  100 ug/1. Values reported for phenols exceed criteria
 in every record from  the Chagrin River. Point sources of phenols should be monitored in
 order to  locate  point sources and  subsequently reduce these inputs.  Fecal coliform
 bacteria densities were excessive in the Chagrin River, with  71% of the  total samples
 exceeding  Ohio  standards.   Municipal waste should be monitored to reveal sources of
 heavy contamination. Phosphorus, lead, manganese and zinc values also exceeded criteria
 on occasion.  The total number of violations was insufficient to warrant designating the
 river as an area of concern.

      Measurements recorded from stations in the Ashtabula River include violations of
limits for the following parameters  (in order of frequency):  copper, phenols, cadmium,
lead, phosphorus and dissolved oxygen.  Copper and  cadmium could not adequately be
assessed for reasons previously discussed.  Phenols exceeded  the standards 100% of the
time with a sample mean  (5.3 ug/1) well above the 1.0 ug/1 limit.  Lead values exceeded
criteria relatively frequently (approximately 20%) while the remaining parameters (i.e.,
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phosphorus and dissolved  oxygen) seldom  exceeded  the criteria.   The  number  and
frequency of violations resulted in the designation of  the Ashtabula River as a problem
area(GLWQB 1980).

     Samples were collected at  19 nearshore surveillance stations near Fairport, Ohio.
Measurements exceeding trace metal criteria occurred most frequently with cadmium,
copper, lead,  nickel  and zinc observations violating  standards  at  every station.  In
addition, measurements of mercury and manganese concentrations occasionally exceeded
criteria.

     The results of  the  data retrieved  from the  18 nearshore stations located near
Ashtabula, Ohio were similar to the results of the analysis from the nearshore Fairport
region.  Trace  metal violations appeared  most frequently, with cadmium, copper, nickel
and zinc.  Less frequent violations occurred for manganese, mercury and lead, while
dissolved oxygen measurements exceeded lower criteria limits only on occasion.

     Data from 9  nearshore stations in  the  vicinity  of  Conneaut were examined,
indicating  cadmium,  copper  and  nickel  concentrations were  the  only  trace metal
parameters that exceeded criteria at all 9 stations.  Copper  and nickel measurements in
excess  of criteria  occurred  12.5-25.0%  of  the  time, and  may  be  indicative of
contamination  near  Conneaut.    Other  parameters  which  exceeded  criteria  rather
infrequently include dissolved oxygen, fluoride, fecal coliform bacteria, selenium, cyanide
and phenols.  Although the number of violations per sample total was not significant,  the
parameters did exceed  criteria at most of the 9 stations sampled. Given  the frequency
and severity of trace metals violations  near Fairport, Ashtabula and Conneaut, these
three locations may be areas of concern for nearshore waters.

     Water intakes  for  the cities of  Mentor,  Painesville,  Madison, Ashtabula   and
Conneaut were also  examined for records in excess  of  I3C or State of  Ohio criteria.
Parameters measured at the Mentor and Ashtabula  intakes  exceeded standards  and
objectives more often than other locations.  Cadmium, copper and nickel could not be
adequately assessed due  to  data reporting problems.  At  Conneaut, 100% of phenol
samples were in violation, while phosphate violations were only 9%. Mentor water supply
records in excess of criteria  included those for phosphate (99%), fecal coliform bacteria
(8%) and dissolved oxygen (2%).  The remaining intakes examined were found to violate
only copper and cadmium criteria.
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      Open Lake, State of Ohio Inclusive.  Data from 50 open lake stations were retrieved
from STORET. Measurements in excess of criteria were noted for at least 1 parameter at
each of the 50 stations.  Twenty two of the open lake stations were sampled by Canada
Centre for Inland Waters (CCIW).  Dissolved oxygen violations were noted consistently at
the 22 CCIW stations located in Ohio waters. Dissolved oxygen measurements below the
minimum criteria occurred more frequently than any other parameter measured at the
other  28 sampling locations.  Oxygen concentrations below  6.0  mg/1 in Ohio  waters
reflected oxygen depletion in the central basin hypolimnion during the summer months.

      Dissolved mercury violations were found at  9 of 28 stations, ranging from 0.3 to 1.0
ug/1. Although relatively few stations were involved, violations appear often enough in
open lake waters to consider  this potentially toxic substance as a possible cause for
concern.  Of the remaining parameters sampled, only  measurements of trace  metals
including cadmium,  mercury, nickel, copper, zinc, chromium  and lead exceeded water
quality criteria.  Cadmium values require  further interpretation due to the consistent
reporting of a 1.0 ug/1  value.  This value may  represent the detection limit  used in
analysis;  thus  the  violations  reported  are not  necessarily  reflective  of   actual
concentrations.  The number of violations per sample total at each station was rather low.
Thus, these metals do not necessarily represent  significant or substantial water quality
impacts in the Ohio open lake portion of Lake Erie.

      Commonwealth of  Pennsylvania.  A  total  of 42 parameters  (Table 51)  were
compared  with  I3C  objective  values  and Pennsylvania Department  of  Environment
Resources (PDER) standards.  Comparisons  were  made using observations recorded from
70  stations composed of  water intake,  tributary,  nearshore and open lake stations.
Observations exceeding objective  and/or standard limits were noted for  22 of the 42
parameters  retrieved with a maximum  number of eight parameters exceeding limits  at
any one station.

      Dissolved oxygen values below the objective/standard were recorded at nearly half
of the stations sampled  over the  two-year interval.   Low  dissolved oxygen  records  in
Presque Isle Bay (Erie Harbor) contributed  to the designation  of this area as a problem
area (GLWQB  1980). During the winter months of 1977-1978, low dissolved oxygen levels
in the bay  resulted in a  massive  winter  kill of gizzard shad (Dorosoma  cepedianum)
(Wellington 1980).  In addition, low dissolved oxygen levels in hypolimnetic waters of the
open lake resulted in violations of the IJC  objective at open lake and nearshore stations.
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 The intrusion  of hypblimnetic waters  into  the  nearshore zone  was indicated by the
 occurrence of dissolved oxygen violations recorded for only a portion of a profile at any
 given station.

      Records  of  fecal  coliform  bacteria  in  excess of  the  PDER  limit  of  200
 organisms/100  mis were noted at  1*  tributary and nearshore stations.   Fecal  coliform
 violations contributed to Presque Isle Bay being designated a problem area (GLWQB 1980)
 An intensive beach sampling  program recorded exceptionally  high  bacterial counts at
 Presque Isle State Park and in Erie Harbor during  the late summer months (Wellington
 1980).  The completion  of additional  sewage treatment facilities should alleviate  this
 problem.  The  remaining violations were principally trace  metal concentrations with no
 apparent pattern of occurrences.  As a result, trace metal violations were considered
 technical in nature and require no remedial action.

     State of New York.  A  total of  22 parameters were  retrieved and  compared with
 IJC  water quality  objectives  and  New  York State water  quality standards (Table  52).
 Observations exceeding  one  or  more  objective/standard  were noted at  42  sampling
 stations in the New York State waters of Lake  Erie.  Values in  excess  of limits were
 recorded at tributaries,  connecting channels  (Niagara River), nearshore  and open lake
 stations. Over the two year interval, no more than  8 parameters were noted with one or
 more violations at any one station.

     Low  dissolved oxygen  values (< 6.0 mg/1)  recorded  at nearshore  and  open lake
 stations were the most frequently noted violations. Low values were recorded at 10 of 16
 open lake stations and 18 of 19 nearshore stations in the Barcelona-Dunkirk-Silver Creek
 reach of the New York shoreline. Low dissolved oxygen values in the nearshore primarily
 resulted from intrusion  of hypolimnetic/mesolimnetic  waters  into the nearshore zone
during the  stratified season.  This  was evident from profile data recorded at nearshore
stations.

     The remaining parameters exceeding objectives/standards in New York waters of
the lake were confined to the trace metals.  Cadmium, copper, nickel and zinc values
were  the most common of  the  trace metal violations.   KJC objective  limits were
considerably lower than New York  State standards (Table 52); as a result, the violations
noted were primarily violations of  I3C objectives  rather than state standards.  Although
not frequent, violations of  the I3C  objective for  total  nickel  and total zinc were
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 consistent throughout the New York waters.  The relatively high values recorded for the
 nickel  and zinc parameters  may  reflect the  nature  of the bedrock  substrate in the
 tributaries of this portion of  the lake. The trace metal violations are probably technical
 in nature, although the matter requires clarification.

      Province of Ontario.  For the purpose of evaluating Canadian water quality, 26
 parameters were screened from a total of  181 stations.  Ninety-eight  were nearshore
 surveillance stations and 83 were open lake stations.  Nearshore collections were made by
 the Ontario Ministry of the Environment (OMOE); open lake collections were made by
 CCIW (48 stations) and USEPA-GLNPO (35 stations). Parameters used for the evaluation
 were the water quality objectives set forth by the Ontario Ministry of  the Environment
 (Table 53). Of the 26 parameters entered, 11 exceeded objectives at one or more stations.
 The total phosphorus criterion was most commonly  exceeded, followed  by  5 phenol
 violations and  7 trace metals (zinc,  cadmium, silver, barium, beryllium, lead, chromium
 and nickel) with zinc being the most common.  It should be noted that not all stations
 were sampled  equally.   Nearshore stations recorded  in STORET (OMOE, 98 stations)
 contained data for  total phosphorus and phenols, while one  set  of  open lake stations
 (USEPA-GLNPO, 35 stations) contained  data  for total phosphorus, and 8 trace metals
 while the CCIW data set contained only total phosphorus data.

      Total phosphorus exceeded the objective at a total of 155 stations; 86 nearshore and
 69  open lake stations, with 23% of  observations in  violation.  The range of individual
 violations was 21-215 ug/1, with most violations occurring within +10 ug/1 of the objective.
 The mean of all total phosphorus sample-means was  16.3 ug/1 (S.D. = + 6 ug/1), which is
 close to  the  objective  of 20 ug/1.  The seasonally  of the phosphorus  violations is
 indicative of fluctuating seasonal inputs, and the ubiquity of  violations is indicative of
 cultural eutrophication in Lake Erie.

     Five phenol records  in excess of criteria occurred in the nearshore area ranging
 from 1.4 to 3.0 ug/1. Of all samples tested for phenol (63 observations at 5 stations), four
 stations showed single violations and one station showed 2 (9.5% of total observations in
 excess).   The  mean of  sample  means was  1.03 ug/1,  which marginally exceeded  the
objective phenol concentration limit.

     Trace metal data was collected by the USEPA, Region V (USEPA-GLNPO) during an
open lake cruise in  July  1979. Zinc was the most common trace metal exceeding limits
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with 40.6% of observations in violation (30 stations) having a violation range of 9-52 ug/1.
Cadmium and  silver were  the next most common trace metal  violations.   Cadmium
violations occurred  at 22  stations with  values  ranging from 1-50.*  ug/1  and silver
violations occurred at  19 stations ranging from 1-36.0 ug/1 (both with 28% of observations
in excess).

     Beryllium concentrations exceeded the criterion in one sample at each of 7 stations.
Six stations had concentrations in  excess of  50.2 ug/1.  The remaining violation had a
concentration of  17.0 ug/1 and occurred the previous year.   When  considering  the
similarity of the concentrations in excess of observations at the six  stations, in  addition to
their close temporal and  spatial proximity, it would seem an indicator of an ephemeral
point-source of beryllium. Four lead violations ranging from 21 to  69 ug/1 were observed.
Two chromium violations (138 and  156 ug/1) and  one nickel violation (87 ug/1) were also
recorded.

     Synopsis.  Discrepancies  were noted  between sample  means, sample  medians,
violation  ranges and parameter objectives casting doubt on the validity of the sample
means retrieved  from the  STORET  system.   For this reason,  ranges  for objective
violations were given main consideration.  Trace metal data were sparse  enough to cause
difficulties in making any statement regarding water quality.

     Table  54 provides a summary  of the violation section of the Lake Erie report.  It is
evident that the river/harbor areas as well as much  of the U.S. shoreline of the western
and central basins represent the majority of the serious problem areas in the lake.  This is
particularly critical  considering this region constitutes the primary use area of the lake,
thus having  the greatest impact on  the populous living in this vicinity. Considering most
of the municipalities around the lake use lake water as a source of drinking water and, to
a lesser  extent, for  food processing, contamination represents an  important concern.  In
addition,  there  are  aesthetic  implications which are important;  however, they are not
health related.   It is evident that our  database  is definitely  weak  and  sometimes
nonexistent as in the case of many municipal water  treatment plants. From  a potential
human  health related  aspect,  toxic  substance investigations  need  to be  strongly
emphasized with well-designed and managed programs in order to properly  evaluate lake-
wide problems as well  as localized conditions.
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 Trace Metals

      Due  to the importance  of  metal contaminants, a special segment is presented
 examining trace metal concentrations in Lake Erie.  In compliance with the International
 Surveillance Plan, trace metal  analyses  were conducted on water samples collected
 throughout Lake Erie during  1978 and  1979.  Eight different agencies  participated in
 monitoring the following related  areas: tributaries, point sources, connecting channels,
 water intakes and nearshore zones. Water samples were collected and analyzed for one or
 more of the following  elements:  aluminum, arsenic, cadmium, chromium, copper,  iron,
 lead, manganese, mercury, nickel,  selenium, silver, vanadium and zinc.

      The  results  of  the trace metal data are summarized in this report.   Figure 115
 summarizes the Intensive Nearshore portion of the Surveillance Program.   The figure
 presents data collected along a defined segment of  the nearshore zone, presented as
 quarterly means over the two-year study interval.  The presentation of standard errors of
 the  means allows preliminary analysis  of  statistically significant differences between
 quarterly mean values (Richardson 1980).  The source of  the data presented  herein was
 calculated using the statistical means procedures available through the STORET system.

      Total iron values  were available for  ten  of  the 1*  lake segments making iron the
 metal with the largest single Lake Erie database in the STORET system.  Total iron was
 reported under two different STORET parameters as total iron (code no. 01045) and total
 icon as Fe (code no. 7*010).  The second largest metal database in the system is that for
 total mercury.  Sufficient total mercury  data was available to allow  presentation  of
 quarterly mean values for six nearshore segments of the lake. Data for the remaining
 trace metals are available for  four regions of the U.S. nearshore zone only.  For the open
 lake portion of the program, samples were collected and analyzed for trace metals in 3une
 of 1978.  Due to technical problems with this database, it  must be considered of marginal
 value (Elly 1982).

     Reports of raw data were received from Michigan, Pennsylvania and New York state
authorities.  Discussions of trace metal data in the lake were not  received from  any
agencies participating in the Lake Erie Intensive Study.

     Aluminum.  There are no applicable water quality or drinking water standards for
aluminum nor is there an objective status in the Great Lakes Water Quality agreement of
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1978.  Aluminum data collected by the nearshore survey is relatively complete.  Figure
115 lists data summarized for  the U.S. nearshore reaches.  Total aluminum values are
rather high throughout the U.S. nearshore zone with the highest concentrations recorded
during the second quarter of both years and with 1978 values greater than  1979  values.
Mean nearshore concentrations from the western  basin and western portion of the  central
basin were higher than those recorded from the eastern portion of the Lake (Figure 115).

      Arsenic.  Arsenic (technically a non-metal) is  quite widely  distributed in  natural
waters occurring at levels of 5 ug/1  or more in  approximately  5  percent of the  waters
tested (Sawyer and McCarty 1978).  The toxicity of arsenic depends on acclimation.  To
unacclimated individuals, it is quite toxic while acclimated individuals can consume daily
doses of arsenic which would  be lethal to naive persons. Effects of arsenic on human
health are summarized in Table 55.  Arsenic in certain forms  is  suspected of being
oncogenic (tumor  forming).   For  this reason, the standards and objectives  have been
devised for arsenic in Lake Erie waters (Table 56.)

      Summarized  quarterly statistics for  total  arsenic concentrations measured during
the intensive U.S. nearshore  survey are depicted in Figure 115.  Several problems were
evident with the data set.  Data was either not collected or not entered into the STORET
system for the eastern basin in 1978  nor the eastern portion of the central basin during
the third and fourth quarters of 1978. In addition, 1979 eastern basin values are recorded
as a constant 2 ug/1, indicating  detection limit problems.  Western basin data must also be
regarded with skepticism due to  the low number  of stations  sampled.   In general,
nearshore arsenic  concentrations were well below standards and objectives and do not
pose any deleterious threats to Lake Erie aquatic  life.

      Estimates of  arsenic loadings  revealed that  the Detroit  River  was  the major
contributor to Lake Erie during the intensive survey.  Relatively  large loading estimates
were also calculated for the Maumee River, the Sandusky River, the Rocky River, the
Black River, the Cuyahoga River,  the Grand River, the Ashtabula River and Conneaut
Creek.

      Linear  trend  analysis was conducted  for  areas where  greater than five years of
surveillance data was available.  Methodology for trend analysis was the same  used by
Rush and Cooper (1981). Of the areas where sufficient data existed, decreasing trends for
total arsenic were found in the Maumee and Cuyahoga Rivers.
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      Cadmium.  Cadmium is used extensively in the manufacture of batteries, paints and
 plastics.  It is also used in iron plating and corrosion prevention with plating operations
 contributing the most cadmium to the water.  At low levels of exposure over prolonged
 periods it can cause high blood pressure, sterility among  males,  and kidney damage
 (Sawyer and McCarty 1978) (Table 55).  Due to the toxicity of this metal, standards and
 objectives were devised for cadmium concentrations (Table 56).

      Quarterly statistical summaries of total cadmium concentrations in  the nearshore
 zone of Lake Erie are listed in Figure 115.  In general, nearshore mean concentrations for
 1978 data exceed those for 1979, and quarterly mean values calculated from the nearshore
 portion of the west  central basin were higher than mean values  from other nearshore
 segments of the lake.  Mean values were generally below most jurisdictional standards,
 yet exceeded both DC and OMOE objectives.

      Individual cadmium measurements in  excess  of  standards and/or objectives were
 widespread.  A majority of the  violations occurring  in Ohio  waters were  due to the
 relatively low concentration established as a water quality standard in that jurisdiction.
 Violations of objectives and standards  in respective jurisdictions are as follows (data are
 reported as the number of stations in which at least one violation was reported):

                                     TABLE 57
                       SUMMARY OF CADMIUM VIOLATIONS
Jurisdiction
Ohio
Pennsylvania
New York
Michigan
Ontario
Total No.
of
Stations
2*9
57
38
73
35
Nearshore
Stations
1*7
22
9
27
N/A
Main Lake
Stations
15
0
6
1
22
Tributary
Stations
27
5
0
2
N/A
Intake
Stations
40
0
N/A
2
N/A
Connecting
Channel
Stations
1
1
     The majority of violations occur in the nearshore zone in all jurisdictions.

     The Detroit  River  was the major  source  of cadmium input into the lake.  Other
significant contributors included the Maumee, Sandusky, Black, Cuyahoga, Grand, Rocky,
and the Chagrin Rivers.
                                          101

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      Of the  stations where  adequate data existed, decreasing trends were found for
 cadmium values at  Sandusky water supply intake and for the  Cuyahoga River  at
 Independence.  Nearshore, tributary and water supply intake databases were screened to
 determine if any existing values exceeded  USEPA published  criteria (Federal Register,
 Vol. 45, No. 231, Friday, November 28, 1980) for freshwater biota. Values exceeding the
 criteria were noted only for  the hardness-related metal criteria (Table 58).  Hardness
 data, per se, were not collected during the intensive nearshore survey and, as a result,
 violations were summarized only for tributary  and water intake  stations.   Cadmium
 records exceeding criteria were relatively numerous and represent a source of concern.

      Chromium. In the aquatic  environment, chromium exists primarily in the form of
 chromate.   Only minor amounts are actually left in  solution due  to  precipitation  of
 hydrolyzed trivalent forms as hydroxide (Sawyer  and McCarty 1978).  Chromium is used
 extensively  in industry to make  alloys, refractories, catalysts  and chromate  salts.
 Chromate  poisoning  causes  skin disorders  and  liver  damage, and  is  believed  to  be
 carcinogenic (Table 55).  The standards and objectives  instituted are presented in Table
 56.

      A quarterly statistical summary of total chromium data in the nearshore zone is
 presented in Figure 115. Mean quarterly concentrations in the nearshore segments of the
 western  basin and  western portion of  the  central basin were the highest mean  values
 calculated.  In addition, 1978 mean concentrations exceeded those calculated for 1979 in
 all segments of the  U.S. nearshore study area.

      A summary of water intake data indicated inadequacies  due to the reporting of the
detection limit used by the Ohio Environmental  Protection Agency  (OEPA) and by the
Pennsylvania  Department  of Environmental  Resources  (PDER).    These  agencies
consistently reported values of 30 ug/1 and 10 ug/1, respectively.

      Chromium values in excess of standards and/or objectives were infrequent.  These
exceptions are summarized by the number of stations where at least one sample  record
exceeded criteria in each of the jurisdictions:
                                         102

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                                     TABLE 59
                       SUMMARY OF CHROMIUM VIOLATIONS
Jurisdiction
Ohio
Pennsylvania
New York
Michigan
Ontario
Total No.
of
Stations
2*9
57
38
73
35
Nearshore
Stations
30
0
0
6
N/A
Main Lake
Stations
4
0
2
0
0
Tributary
Stations
7
0
0
0
N/A
Intake
Stations
1
0
N/A
0
N/A
Connecting
Channel
Stations
N/A
N/A
0
0
N/A
      The Detroit  River was the  major contributor of  chromium with  substantial
chromium loadings occurring in the Sandusky, Maumee, Grand, Black and Rocky Rivers.

      Linear trend  analysis  of chromium data indicated a  significant increase in the
Maumee River from 1974 to 1980, while no change was noted in the Sandusky or Cuyahoga
Rivers for the same period of record.

      Copper.  Standards imposed on copper concentrations in Lake Erie serve to protect
aquatic life. Concentrations above 1.0 mg/1 may pose aesthetic taste problems in drinking
water supplies; however, there is no evidence to indicate that copper is detrimental to the
public health at levels which are aesthetically unacceptable.  In surface waters,  copper is
toxic to aquatic vascular plants, phytoplankton and some fish at concentrations near 1.0
mg/1 (Sawyer and McCarty 1978).  Standards and  objectives have been imposed on  Lake
Erie waters by the agencies involved (Table 56.)

      Quarterly statistical summaries for  total copper  are depicted in Figure 115.  With
the exception of third and fourth quarter mean values for the eastern central basin,  1978
values were higher than those collected in 1979.

     In general, 1978 loading values were higher  than  1979 values, especially those data
collected by state  agencies.   Major inputs of copper  originated from  the  following
tributaries: the Detroit River, the  Maumee River, the Sandusky River, the Rocky River,
the Cuyahoga River, the Grand River, the Black River, the Chagrin River and Conneaut
Creek.
                                         103

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      Copper concentrations in excess of objectives and/or standards occurred frequently
 in the nearshore zone, while relatively few stations at the remaining sites exhibited one or
 more violations.   The following table lists the number of stations in each jurisdiction in
 which at least one sample collected exceeded limits:

                                     TABLE 60
                         SUMMARY OF COPPER VIOLATIONS
3urisdiction
Ohio
Pennsylvania
New York
Michigan
Ontario
Total No.
of
Stations
2*9
57
38
73
35
Nearshore
Stations
1*2
2*
12
26
N/A
Main Lake
Stations
6
3
2
2
0
Tributary
Stations
26
1
1
2
N/A
Intake
Stations
*3
1
0
2
N/A
Connecting
Channel
Stations

__
1
5
N/A
      The  majority  of violations  occurred in  the nearshore  zone.   However,  this
observation may be misleading since the nearshore zone was the most intensively sampled
of the five station types.  No significant increasing or decreasing trend resulted from the
linear regression analysis at any location from  197* to 1981.  Nearshore,  tributary and
water supply intake databases were screened  to  determine  if  any existing records
exceeded USEPA published criteria for freshwater aquatic life.  Copper records exceeding
criteria were relatively numerous and represent a potential source of concern.

      Total Iron.  Iron in the water can be detrimental to aquatic life, but seems to do no
harm to humans.  However, water containing iron  can become turbid and  unacceptable
from an aesthetic point of view. In addition, iron interferes with laundering operations,
leaves objectionable  stains on plumbing fixtures,  and causes problems in distribution
systems  by  supporting growth of iron bacteria  (Sawyer and McCarty 1978).  For these
reasons, authorities have set standards for maximum allowable levels of iron in unf iltered
samples of water.  Standards which apply to waters sampled according to the Surveillance
Plan are presented in Table 56.
     The I3C and OMOE objective, and the State of New York standard for total iron is
300 ug/1.  This objective was exceeded at 7 of 38 water intakes.  The true frequency of
violation of the objective  is impossible to  ascertain due to the infrequent sampling of
total iron data at intakes.  Total iron data reported for River Mile 3.9  on the Detroit
                                         104

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River consistenly approached or exceeded the 300 ug/1 objective.  Tributary streams in
Pennsylvania occasionally exceeded the objective as well.

     Quarterly means of total iron in the nearshore zone of Lake Erie were highest in the
western basin and lowest in the eastern basin.  In the western basin, values consistently
exceed  the IJC and OMOE objective.  In the central basin, quarterly mean values were
highest for the segment extending between Marblehead and Cleveland, Ohio, with the IJC
objective exceeded by 5 of the 6  quarterly means.  Quarterly mean values exceeded the
objective in the eastern basin only once during the second quarter of 1978 in the segment
extending from Port Maitland, Ontario, to Buffalo, New York (Figure 115). No seasonal or
temporal pattern was apparent in quarterly mean values.   Although total iron values often
exceed  the ICJ objective of 300 ug/1, these violations are technical in nature and reflect
the natural state of water in  Lake Erie rather than a substantial violation or  significant
problem requiring remedial action.

     Lead.   Water  quality monitoring of  lead concentrations in  surface  waters is
extremely critical in order to maintain safe  levels for  drinking water  standards.  Lead
poisoning  has been recognized for many years and has been identified as a cause of brain
and kidney damage (Table 55). The standards and objectives for total lead are given in
Table 56.

     Summarized quarterly mean values calculated for  the four nearshore segments of
the U.S. shore are listed in Figure  115.  With the exception of the fourth quarter western-
central  basin reach,  1978 mean concentrations were higher than 1979 values.  In addition,
concentrations calculated for the eastern portion of  the central basin and the  eastern
basin nearshore segment were  higher than other portions of the  nearshore zone.

     Lead measurements in excess of water quality criteria were infrequent, the majority
of which occurred in the nearshore zone.  A summary of surveillance stations in which at
least one sample exceeded standards or objectives is listed below:
                                        105

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                                     TABLE 61
                          SUMMARY OF LEAD VIOLATIONS


Jurisdiction
Ohio
Pennsylvania
New York
Michigan
Ontario
Total No.
of
Stations
2*9
57
38
73
35

Nearshore
Stations
36
1
0
7
N/A

Main Lake
Stations
3
0
1
0


Tributary
Stations
22
0
6
1
N/A

Intake
Stations
3
0
N/A
0
N/A
Connecting
Channel
Stations

__
1
1
N/A
      The total  number of observations at each location is too limited to allow any
assessment.   The consistent reporting  of a 5.0  ug/1 value  indicates detection limit
problems, but this value is well below standards or objectives.

      The major  contributions of  lead originate from the  Detroit, Maumee, Sandusky,
Black, Rocky, and Cuyahoga  Rivers.  In general, 1979 values are greater than those for
1978.

      Sufficient data to linearly  regress data points through time were recorded at three
locations.   A significant decreasing trend was calculated for  data collected at the
Sandusky  Water Supply Intake.  Stations located in  the  Maumee and  Cuyahoga  Rivers
showed no significant change  during the period of record.  Nearshore, tributary and water
supply intake databases were screened  to  determine if  any existing records exceeded
USEPA published criteria for freshwater aquatic life.  Only trend analysis calculations
were performed for data from tributaries and water intakes (Table 58).

      Manganese.  Limits  on  manganese concentrations in  surface waters are imposed
primarily  for aesthetic reasons for drinking purposes. Concentrations  less that 20 ug/1
represent  minimal risk in aquatic environments  (Sawyer and McCarty 1978).  Only Ohio
and Pennsylvania have imposed manganese standards;  50.0 ug/1 for Ohio waters and 1,000
ug/1 for Pennsylvania (Table  56).   There are no other objectives or standards for this
parameter.  Potential  health problems  associated with chronic or massive exposure to
manganese are summarized in Table 55.
     Statistical summaries of  quarterly  mean  values calculated for four nearshore
segments of the U.S. shore are presented in Figure 115.  With the exception of eastern
                                         106

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basin mean values, 1979 values were generally higher than those in  1978.  Of the four
nearshore  segments,  the western central  basin  mean  concentrations  generally were
highest with manganese concentrations ranging from 0.00 ug/1 to 28* ug/1.

     Tributary loading estimates indicate that during 1978 and 1979, the Detroit River,
the Maumee River and the Rocky River served as major contributors of total manganese.

     Significant  increasing trends were discerned at two  locations, the Sandusky  and
Niagara Rivers.  A significant decreasing trend was calculated for data from the Erie,
Pennsylvania water supply intake. No significant increasing or decreasing  trends were
noted in calculations performed on data from the remaining sites.

     Mercury.  High levels of mercury in water could be detrimental to aquatic life, and
if consumed by humans,  large amounts  of  mercury would  endanger  their lives (OMOE
1978) (Table 55).   The IJC objective  for  dissolved mercury is 0.2 ug/1, making levels of
mercury in Lake Erie water of interest.  Although samples for dissolved mercury analyses
were not collected, analyses were conducted for total mercury in the water from samples
at 253 stations during the two-year interval 1978-1979.   The results of analyses are
summarized below in Table 62.

                                     TABLE 62
                     SUMMARY OF MERCURY OBSERVATIONS
  Number           Mean          Standard      Maximum      Minimum
  OBS               (ug/1)          Error          Value          Value

  1309              0.196          0.119          6.080          0.000

     The results  of the Intensive Nearshore Survey are summarized as quarterly means
for defined segments of the nearshore zone in Figure 115.  Generally, the quarterly means
for total mercury were below, or near, the IJC objective of 0.2 ug/1 for dissolved mercury.
The exception was in the Detroit River segment where mean concentrations exceeded 0.3
ug/1 during the  third quarter of both years.   These values were not significantly different
from the western basin open lake mean concentrations determined from samples taken in
3une 1978.  In addition, relatively high mean values were reported for the fourth quarter
of 1979 for the  segment extending between Port Maitland and Buffalo.
                                        107

-------
      Since total mercury values seldom exceed the IJC standards of 0.2 ug/1 in water,
this was interpreted to mean that mercury in the water column has not been identified as
a subject of concern during the intensive study period.

      Nickel.  Nickel is used extensively in electroplating and occurs in  the rinse waters
from  these operations, constituting the major avenue by which the salt of this metal gains
access to the aquatic environment.  Nickel is suspected of being oncogenic and for this
reason standards and objectives have been formulated (Tables 55 and 56).

      Nickel  concentrations  in  excess of  criteria occurred rather  frequently  in the
nearshore zone but were seldom found elsewhere in Lake Erie.  Table 63 lists the total
number of stations in each water where at least one sample exceeds limits.

                                     TABLE 63
                        SUMMARY OF NICKEL VIOLATIONS
Jurisdiction
Ohio
Pennsylvania
New York
Michigan
Ontario
Total No.
of
Stations
2*9
57
38
73
35
Nearshore
Stations
127
24
18
22
N/A
Main Lake
Stations
7
1
2
0
1
Tributary
Stations
15
2
0
0
N/A
Intake
Stations
5
0
N/A
0
N/A
Connecting
Channel
Stations
0
1
N/A
     Figure 115 lists quarterly statistical summaries of  intensive nearshore survey  data
from  the  U.S.  shore of  Lake Erie.   With  the  exception of  second quarter mean
concentrations in the eastern-central basin and second quarter mean concentrations in the
eastern basin, quarterly means were higher in 1978 than those  in 1979.  Except for the
samples reported by  Ohio EPA,  most of the  values lie within the limits imposed by
respective  jurisdictions.  The Ohio EPA data set reported all total nickel values as 100.0
ug/1, indicating the reporting of the detection limit.

     Loading  data for this metal  was rather scarce; only two stations were sampled by
the USGS in 1978; none in  1979. State agencies sampled two stations in 1978, while ten
were sampled in 1979.  Major tributary sources of total  nickel include the Rocky and
Cuyahoga Rivers in 1978 and the Black River, the Cuyahoga River, the Chagrin River and
the Grand River in 1979.
                                         108

-------
     Insufficient data existed to perform linear trend analysis at any location throughout
the lake.  Tributary and water intake data  screened for exceptions to USEPA published
criteria revealed no records in excess of criteria.  These observations (i.e., no trends or
violations) reflect a scarcity of data necessary for proper assessment of Lake Erie water
quality.  However, the frequency of nearshore records in excess of jurisdictional criteria
and IJC objectives indicates a potential source of concern (Table 58).

     Selenium.  Selenium  occurs  in natural waters in  very limited areas of the United
States.  Its major use is in  the manufacture  of electrical components: photoelectric  cells
and  rectifiers.  Selenium  has been  implicated as oncogenic  but  existing evidence is
limited.  The standards and objectives formulated for this metal are presented in Table
56.

     Measurements of  total selenium in excess of criteria occurred very rarely.  The
number of stations where at least one sample exceeded standards and/or objectives are
listed below:

                                     TABLE 6*
                        SUMMARY OF SELENIUM VIOLATIONS
Jurisdiction
Ohio
Pennsylvania
New York
Michigan
Ontario
Total No.
of
Stations
2*9
57
38
73
35
Nearshore
Stations
4
1
0
0
N/A
Main Lake
Stations
0
0
0
0
0
Tributary
Stations
1
0
0
0
N/A
Intake
Stations
3
0
N/A
0
N/A
Connecting
Channel
Stations
N/A
N/A
0
0
N/A
     A summary of quarterly mean values calculated for four nearshore segments of the
U.S. shore are listed in Figure 115.  Quarterly mean concentrations for 1978 were larger
than 1979 values for every quarter and nearshore  segment.  Mean 1979 eastern basin
concentrations were  based  on consistent records of  2.0  ug/1,  indicating a  possible
instrument limitation problem.  Data from municipal intakes were also of limited value
since all concentrations recorded at some intakes were either 5.0 ug/1 or 10.0  ug/L

     Loading data for total selenium was scarce, especially at stations sampled  by state
agencies.   The Detroit River, Maumee River and Cuyahoga River were large contributors
                                         109

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of selenium in 1978.  In 1979, the Grand River, Ohio and Cattaraugus Creek, New York
were calculated to contribute large amounts of selenium.

      Sufficient data were collected only at the Maumee River station near Waterville, to
conduct trend analysis.  A  significant  decreasing  trend was calculated for the period
extending from January 1974 to October  1980.

      Vanadium.  There are no applicable water quality  or drinking water standards for
vanadium nor is there an objective stated by the Great Lakes Water Quality Agreement of
1978.

      Vanadium  data  collected  for intensive nearshore  purposes is  summarized by
nearshore segment in Figure 115. For the most part, quarterly 1978 mean concentrations
were higher than 1979 values.  Data were not reported for the third or fourth quarters in
1979 in the western-central basin nearshore segment. In addition, third and fourth quarter
data from the western-central and eastern-central basin  segments and the entire eastern
basin portion were consistently reported as 5.0 ug/1.  Thus, the data set was of limited use
in assessing Lake Erie water quality in terms of total vanadium concentrations.

      Due to the extreme scarcity of vanadium data, it was not possible  to calculate
loading estimates or linear trend analyses.

      Zinc.  The toxicity  of zinc is very low.  Zinc  salts gain access to  the  aquatic
environment  through  mining,  electroplating  and corrosion  of galvanized pipes.   Water
quality standards and objectives are developed primarily for taste considerations.  The
standards and objectives have been formulated for Lake Erie waters (Table 56).

      Measurements of total zinc concentrations in excess of criteria occur frequently and
were most evident in the intensive  nearshore surveillance data.  The  following table
summarizes the  number of stations where at least one sample exceeded limits during the
1978-1979 intensive surveillance period:
                                         110

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                                      TABLE 65
                          SUMMARY OF ZINC VIOLATIONS
Jurisdiction
Ohio
Pennsylvania
New York
Michigan
Ontario
Total No.
of
Stations
2*9
57
38
73
35
Nearshore
Stations
1*6
21
11
26
N/A
Main Lake
Stations
5
0
1
0
30
Tributary
Stations
19
5
0
3
N/A
Connecting
Intake Channel
Stations Stations
11
0
N/A
1
N/A
N/A
N/A
1
3
N/A
      Quarterly mean values of intensive nearshore total zinc data calculated for each of
 four segments of the U.S. shore are listed in Figure 115.  In the eastern-central basin and
 the entire eastern basin portion,  1979  mean concentrations were  generally higher than
 1978  mean values. In the western-central basin, 1978 nearshore means were higher than
 1979 values.

      The western-central basin nearshore was the segment with the highest calculated
 values. Along the U.S. shoreline, zinc values in the nearshore study area ranged from 0.00
 ug/1 to 1726.50 ug/1.

      During  both years of the intensive survey, major inputs of zinc originated from the
 Detroit River, the River Raisin, the Maumee River, the Sandusky River, the Cuyahoga
 River, the Grand River in Ohio, the Rocky River, the Chagrin River, Conneaut Creek and
 Cattaraugus Creek.

     Of the  five stations where sufficient data existed for trend analysis, none showed a
 change through time for the period of record (approximately 1974 to 1980). Tributary and
 water  intake data screened for exceptions to USEPA published criteria revealed a very
 limited number of exceptions to this criteria (Table 58).
     Synopsis.  In spite of what is indicated by this section, trace metal data for Lake
Erie are not complete or very reliable.   Numerous serious problems exist with  the
database making any comprehensive picture of trace metal contamination still subject to
further examination at the surveillance level.  For example, the entire open lake data
collected during 1978-1979 intensive study provides no information that can be used for a
                                          111

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long-term database.  Consequently, this facet needs to be re-examined.  Several data
sources reported values only at detection limits; thus, much of this information is of only
limited value.  Copper, for example, has a violation level of 5 ug/1 while the detection
limit  frequently reported was 30 ug/1; consequently, little  can be discerned from this
information.  In addition, very little, if any, data is available on internal/external quality
control, making interpretation of results  a problem.  In addition to laboratory problems,
the actual sampling patterns and sampling schedules employed by the various studies were
by no means  optimal for data interpretation.   Thus,  the entire trace  metal contaminant
program on Lake Erie needs to be re-evaluated in  order to establish a reliable database.
Careful attention needs to be placed on the station pattern,  sample plan, methodologies
employed, and what metals are important enough to be considered in the program.

     In a recent  report, Rossman (19S3)  presented metals data for the western, central
and eastern basins.  The report contains information on open lake concentrations of total,
dissolved and particulate fractions  of 27 trace metals.   Table 66  presents the total
concentrations for the three  basins. In addition, the historical database is presented and
summarized with comments as to the  quality of the  database.  In  order to estimate the
potential toxicity of the mixture of trace metals analyzed, a ratio of the concentrations
of each metal (M.) to its respective IJC objective concentration (0.) was calculated.  The
sum of the individual ratios should not exceed  1.0 if all concentrations are at safe levels.
The results presented in Table 67 indicate that open lake concentrations  of  metals may
pose a problem to the biota.  In particular, selenium was found to exceed objective levels.
The Rossmann (1983) report  together  with a  manuscript by Lum and Leslie (1983) have
advanced the open lake trace metal database significantly.   Future  programs involving
trace metal analysis in Lake Erie should take these documents into consideration.

Nearshore Water Quality Trends

     Improvements  or changes in water quality  resulting from remedial measures are
most likely to first appear in nearshore regions rather than in the open lake. This section
deals with analyses of water quality in the nearshore zone of Lake Erie in an attempt to
assess changes or trends which may have occurred in the last decade.

     Trend analysis of long-term databases has recently attracted the attention of many
Great  Lakes research groups.   Two major problems have arisen in  attempting to analyze
large databases through time: first, a satisfactory definition of what exactly constitutes a
                                          112

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 "trend;" secondly,  and more importantly,  developing  an adequate  method of  removing
 large variations in raw data resulting from seasonally and climatic conditions such as
 storm events.   Such  variation could mask a trend that really exists, or, conversely,  it
 could indicate a trend where none actually exists.

      In 1978,  the IOC defined "trend" as  a linear regression  equation having a slope
 significantly different than zero  as determined by a  t-test.   Recently,  the Data
 Management and Interpretation Work Group (Richardson 19SO) recommended the  following
 definition for a trend in Lake Erie water quality:

      "To relieve any ambiguity  and to provide a uniform methodology of testing for
      trends we propose an operational definition of a trend which narrows it to  a change
      at a constant rate, that  is,  trend will be understood as simple linear trend.  Trend
      can thus be assessed by regressing the characteristic of interest upon time:

                                    v = bo + blx + e

      where bQ is the characteristic of interest and x is time; coefficient b. is tested for
      statistical significance and e = error."

      If analysis indicates presence of a trend, the work group expanded this definition
 somewhat and suggested further analysis of second and  third order coefficients of time to
 determine if the rate of change is  itself changing.

      Previous  investigations of trend analysis  on  Lake Erie date back to Beeton (1965)
 whose work can be found cited in almost every paper  dealing with changes in Lake Erie.
 Beeton seems to have collected the only database for long-term trend analysis dating back
 to the  turn of  the century.   Since the database used by Beeton has  not as  yet been
 reassembled and examined in as rigorous a manner as may be necessary to discern a trend,
 the results he presented should  not be considered absolute.

     In 1978, the I3C published an analysis of trends of nearshore water quality data
 throughout the  Great Lakes, 1967-1973  (Gregor and  Ongley 1978).  In this study,  the
 authors adopted an aggregation procedure for each of  1*0 nearshore geographic regions.
The regions were chosen a priori in an attempt to homogenize the effects of limnological
processes while retaining  large data populations within each subset  in order to enhance
                                          113

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statistical significance.  The  aggregation  procedure involves separating  the data into
three time frames and analyzing each by season (spring, summer and fall) and by depth
(surface and subsurface).  The authors' summary of water quality trends indicates that the
following parameters have generally decreased through  time in Lake Erie: conductivity,
total phosphorus, chloride, chlorophyll a, secchi depth and total coliforms; total nitrogen
and oxygen saturation have increased.

     Richards (1981b)  employed a third method of analyzing long-term databases.  This
procedure involved  removing seasonal variation  by averaging monthly residuals of  all
years and subtracting this average from  the linear model.  This analysis was performed
with the assumption that  the seasonal effect remains constant for each  year.  Using data
collected at the City of Cleveland's Water Supply Intake Division over a period of record
extending from 1969-1979, Richard's regression analysis with seasonal filtering indicated a
significant decrease in total phosphorus,  soluble reactive phosphorus, ammonia-nitrogen,
specific conductance, and chlorides.  No significant trends were found to exist for nitrate
plus nitrite, soluble reactive silica, alkalinity, pH or sulfate.

     The following  analysis is  a first-order attempt to discern which parameters are
significantly  changing  in the  nearshore region  of the  lake  by applying  the Data
Management and Work Group's  recommendation.  Eleven locations consisting of twenty
stations comprised the present data set. A general, all-parameter (chemical and physical)
retrieval  from STORET was reviewed to ascertain which stations showed the greatest
sampling frequency, the longest time period for analysis, and contained parameters most
conducive for evaluating water quality status. Stations chosen for analysis are depicted in
Figure  116. Agencies which sampled  the stations, station descriptions  and locations are
listed in Table 68, with station type defined as tributaries and water intake systems.

     A total of 22 parameters were chosen to represent general water quality conditions
in Lake Erie.  Physical  and chemical parameters such as turbidity, conductivity, residue,
and total  dissolved solids  may indicate changes resulting  from sediment  loading; chloride,
which  is  considered a  conservative  parameter, may indicate sources  of increased  or
decreased chemical  loading and accumulation; while pH and alkalinity  are reflective of
acid-base conditions and buffering capacities.  Dissolved oxygen and biochemical oxygen
demand were chosen to  reflect changes in biologically oxidizable organic  matter.
                                          114

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     The nutrient parameters consist of various forms of nitrogenous and phosphorus
compounds.  Of these two groups, trend analysis of phosphorus compounds may be
considered more  important since  phosphorus has  been  identified  as an  important
contributor to eutrophication and its loading rates have been of primary concern in recent
years.

     Statistical analysis of the data consisted of testing a linear regression equation by
use of a t-test or F-test (P < .05)  in order to determine if the slope  of the line  was
significantly different than zero. On all but two of the data sets reviewed,1 raw data was
plotted against time for all parameters using a STORET REG procedure.  If the t-value of
the slope was greater than the corresponding tabular "t" value for n-1 degrees of freedom,
a slope significantly different than zero was indicated (Nie et al. 1975).

     The databases used from  the C and O Dock and Davis-Besse locations were not
obtained from STORET.  Raw data was entered on tape and an SAS (79.5) General Linear
Models (GLM)  procedure was run  on monthly means to  test for significant  trends.
Significance of slope was determined using an  F-test (P<.05).  Linearity of trend  was
attempted by  plotting  residuals of the regression line for parameters found to have
significant trends in the C and O Dock and Davis-Besse databases. A relatively straight
band of residuals may be  indicative of an actual linear trend during the period of record
(Draper and Smith 1966).

     A summary of linear regression trends for each parameter and station analyzed can
be found in Table 69.  For example, trend analysis at tributary station  1 (STORET code
820011) on the U.S. shore of the Detroit River indicated a decreasing trend in alkalinity,
dissolved oxygen, conductivity,  turbidity,  total dissolved  solids, residue, biochemical
oxygen demand, ammonia plus ammonium, total Kjeldahl nitrogen, total organic carbon,
total  phosphorus,  ortho-phosphorus, phenols,  iron  and  chloride.  No  trends could be
detected by this analysis for silica, organic nitrogen, nitrate plus nitrite, or total and
fecal  coliforms.   The  analysis  indicated  no  parameter  at this  site was  increasing
significantly through time. Thus, a general increase in the quality of water can be said to
be occurring.

     The database for the Cuyahoga River presented a situation requiring a combination
of station  values.  The Cuyahoga River near  the  river mouth was sampled at three
different locations, but all within close proximity of each other. One station was sampled
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 between 1963-1974 while the other two were sampled from 1974-1981. For the purposes
 of this discussion, the stations are considered to be in the same locale and are reported
 for  the two  time periods.   From 1963-1974,  increases were found to occur  for pH,
 alkalinity and iron, while decreases were noted for conductivity and nitrate plus nitrite.
 No significant trend was noted for total phosphorus, total coliforms or chlorides. In the
 1974-1981  time frame, alkalinity continued to increase, while iron, total  phosphorus and
 chloride did not change. Nitrate plus nitrite, pH, conductivity and total  coliforms  were
 not sampled after 1974.  Total organic carbon was the only parameter sampled from 1974-
 1981 and  not the 1963-1974 time period which  showed  a significant  increase.   The
 remaining parameters did not change significantly through time.

      Each  of the four water intake systems was also  evaluated for changing water
 quality. Monroe, Michigan water intake data showed only an increasing trend in phenols;
 all  other parameters of interest were either  not  present  in the data set or showed no
 significant change.  Although the data set was limited, the  analyses of existing nutrient
 and  principal ion parameters lead to an initial conclusion that water quality at this site
 may not have changed significantly over the period of record (1967-1979).

      Analysis of Sandusky  water intake  data  indicated a  significant  increase  in
 temperature,  conductivity,  residue, nitrates and total organic carbon.  No change was
 detected for  dissolved oxygen,  turbidity,  NH-+NH., total  Kjeldahl  nitrogen,  total
 phosphorus, fecal coliforms  or  chlorides.    Decreasing trends  were  observed in  the
 regression  analysis for pH,  alkalinity and  ortho-phosphorus data.   Conclusions  derived
 from this analysis of Sandusky water intake data must be regarded with skepticism since
 the  period  of record is one of the shortest presented (1974-1980).   The possibility of
 detecting a true trend in this database is dubious at best.

      Analysis of data collected from the City of Cleveland's Crown water intake (located
 approximately 4 km offshore) (Figure 116) indicated significant  increases in  temperature,
 alkalinity, total organic carbon and fecal coliforms, as well as significant decreases in pH
 and  turbidity.  No  significant trend was evident in  dissolved  oxygen,  conductivity,
 nitrates, NH-+NH., total phosphorus or chloride. Thus, the water quality at this location
does not appear to be  changing  over the period  of record, 1974-1980.   The database
retrieved from the Erie, PA water  intake revealed a gap from mid-1976 to early 1978.
Analyses performed showed a significant decrease in pH,  alkalinity, total and  fecal
coliforms, iron and chloride values.  No significant trends were evident for temperature or
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 total phosphorus values. The only parameters for which the analyses indicate an increase
 through time were dissolved oxygen and turbidity.

      The tributaries or connecting channel  stations revealed different  responses over
 time.  Total  phosphorus analyses indicated a decreasing trend throughout most  of  the
 stations in the western basin, including all three station locations in the Detroit River,  the
 C and O Dock and the Maumee River at Waterville.  Davis-Besse, Sandusky, Crown, Erie,
 and the Cuyahoga River showed no significant total phosphorus trends.  Analyses of ortho-
 phosphorus data revealed a decreasing trend in the Detroit River and  at Sandusky, while
 Niagara  River,  just  downstream from  the Black  Rock Canal, indicated  a  significant
 increase.

      Organic nitrogen was unchanging at all sites with the exceptions  of the Buffalo and
 the Niagara Rivers where a decreasing trend was noted and the Cuyahoga River where a
 significant increase was found.  Of the  remaining nitrogen compounds, nitrate increased
 at three locations (Toledo, Sandusky  and Buffalo Rivers) and decreased at  the C  and O
 Dock. NH.+NH. decreased wherever a trend was  observed (U.S. shore and Livingstone
 Channel in the  Detroit River, Maumee  River  at Waterville, and Buffalo River).  Total
 Kjeldahl nitrogen was  decreasing at the U.S. shore and  Livingstone Channel (Detroit
 River) and Buffalo River and increasing in the Cuyahoga River.  Analyses of nitrate plus
 nitrite data  indicated  a significant  increasing  trend  at  Davis-Besse  and  a  significant
 decreasing trend in the Cuyahoga River.  Silica was the only parameter  sampled which
 indicated no significant increasing or decreasing trend at any location.

      Figures 117 and US are representative of STORET retrieval plots and  are shown to
 illustrate  various problems  encountered in this analysis of trends.  Total phosphorus
 (Figure 117) at the  Livingstone Channel station clearly  shows a  narrowing variation
 through time; values plotted from 1978 to 1981 show less variability than previous years.
 This phenomenon is possibly due to refinement of analytical technique and/or sampling
 stations.  Figure 118 depicts monthly mean total phosphorus plotted from  1970 through
 1979 at the C and O Dock  (mouth of  the Maumee River).  Visual inspection of total
phosphorus data at  this site  reveals that concentrations may have remained stable until
 1975  and  then declined.   The extreme  variation  present  in the  1974 portion  of  the
phosphorus data could have influenced the regression line.  If the variability in the early
portions of these data sets is due to factors other than random error (i.e., inadequate
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 sampling and/or analytical technique) the significant trends resulting from the analyses of
 these data sets reported herein may not be accurately assessing changes in water quality.

      Lastly, it was evident that in most cases r2 values were rather low, i.e. Figure 117,
 2
 r =0.27 for total phosphorus at the Livingstone Channel site.  This suggests that not much
 of the variability  may be explained by time. An exception to low r2 values was found in
 cyanide  trends, however.  These high values  were not indicative of actual cyanide
 phenomena.   Inspection  of  the STORET plots revealed that the  detection limit was
 probably lowered during the period of record.

      Variability in the data sets is the leading analytic problem. If the variance about
 the  regression line is  greater than the  estimated population variance  (s )  then  the
 postulated model  suffers lack of fit.  Several methods for  determining lack of  fit are
 outlined by Draper and Smith (1966) and should be pursued in  order to test the validity of
 the regression model.

      One of the most obvious methods for removing much of the variability in the data
 set is to filter  the seasonal  component.  The authors  have  attempted  to separate the
 months into seasons and regress the seasons on years.  This procedure  proved  ineffective
 as most parameters showed increases in trends in some seasons and  decreases in  others,
 thus making overall trends more difficult to ascertain.

      Another method to remove seasonal variability involves  averaging monthly  residuals
 and subtracting the average from the regression equation (Richards 1981b).  Although the
 results of Richards' paper indicate very little improvement in significance levels or r
 values for data taken from the Cleveland municipal  water intake, averaging residuals may
 prove effective in increasing r  and significance levels for data sets presented here.

      Perhaps the  most effective method is to describe the seasonal variability of each
parameter by a polynomial and subtract this equation from the linear regression equation.
This could be effective in removing the seasonal component of the variability.

     Finally, when trends are adequately described  according to variability and linearity,
further investigation  is necessary to  discern  probable  causes for  each  parameter
exhibiting significant change.   Loading and flow data of major  tributaries,  as well  as
water  level data, may  be incorporated to  illustrate any correlations which may exist
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between trends and general physical and  limnological phenomena.   Trends may also be
correlated against one another to see if perhaps a trend in one parameter is accounted for
by a trend in another.

Water Quality Trends at Cleveland. Ohio

      During 1978 and 1979, the nearshore zone of Lake Erie was sampled intensively as
part of  the  monitoring and  surveillance program for the Great Lakes (Herdendorf  1978).
The Heidelberg College Water Quality Laboratory (HCWQL) was responsible for sampling
in the nearshore zone of the central basin  between Vermilion, Ohio  and Ashtabula, Ohio.
Sampling  was  carried out at 89 stations (Figure 9).  Each station was sampled on three
successive days during four  cruises each year.  At most stations, samples  were collected
one meter below the surface and one meter above the bottom.

      One major purpose of this nearshore study was  to identify  historical  trends,
especially among parameters that may have changed  in concentration  due to human
impact on Lake Erie.  This section addresses that purpose at two levels: comparisons with
a long-term but often sketchy database extending back to 1900, and comparisons with a
much more detailed but localized database for one station from 1968  to 1979.

      The attempt to identify historical trends is  often  frustrated by the  scarcity and
inadequate quality of historical data. Changes in methods of analysis affect the data in
ways which are  hard to identify.  The methods of  analysis themselves are often not
specified.   Even  when  the methods  are  specified,  and are  known  to  be  bias-free
analytically, the  possibility  of  biases  due to  different working  ranges and  other
laboratory-level differences is  very  real,  but  usually difficult to  evaluate.  For the
nearshore zone, data is scarce even in comparison to the data set for the open lake. Much
of the data found in the literature prior to 1950 consists of average  values, and often the
locations  where the data were obtained are not adequately specified. Also, the nearshore
zone  is much  more variable spatially  and  temporally  than is the open lake, making
historical trends more difficult to detect.

      For  all of these reasons,  historical analysis  is  a difficult endeavor,  especially in
nearshore waters. Even statistically significant  changes must be carefully scrutinized to
see if they  are reasonable  in limnological context or if they are better  interpreted as
artifacts of problems in the data set.  The point must be made at  the outset, however,
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 that statistical trend analysis can show only a significant change in the numbers in a data
 set  as  a function of  time.   Identification  of a historical trend  in  Lake Erie involves
 substantial interpretation of the results of the statistical procedure.

      Long-Term Historical Trends.  One of  the most important historical trend studies
 was that of  Beeton (1961  and 1965, Beeton  and Chandler 1963).  The importance of this
 study lies in its  time span (1902  to  1960) and its concern with chemical parameters of
 general importance:  total  dissolved solids,  calcium,  sodium, potassium,  sulfate and
 chloride. The concentrations of these parameters are great enough that  one  can have at
 least cautious confidence that measurements in  the early 1900s were not drastically
 inaccurate.

      The data used by Beeton (1961 and 1965) came from a variety of sources: public
 water intakes, fisheries studies,  early  research  efforts,  and a  few early studies  of
 pollution in Lake Erie.  The data  set includes values from  all three basins of Lake Erie,
 and  from nearshore  regions and open lake waters.  Since gradients in concentration are
 known to exist from onshore to offshore, and from basin to basin, the data  set contains
 sources of systematic  difference other than the historical trends.  However,  the changes
 in most of the parameters over time are large compared to  the magnitude of these spatial
 gradients, and the mix of data from different areas is reasonably random with respect to
 time.  Thus, spatial factors may serve to obscure historical trends by increasing overall
 variance, but they probably do not  bias the trends in an important way.

     Beeton does not list the data sources shown in his figures, and much of it is from
 sources that are not readily available.   Data has  been  taken  from  Beeton's figures  as
 precisely as possible; his data is reproduced  in Figures 119-121. Since many of the data
 "points" in Beeton's graphs are actually averages, the distortion of the data due to reading
 the  graphs is probably small compared  to the  distortion  (loss of variance) introduced
 initially by the averaging process. It would  be  preferable to begin with the raw data;
 however, to date it has not been possible to reassemble the data set from  the sources that
 Beeton used.

     Also shown  in Figures 119-121 are the 1978 and 1979 means and  standard deviations
for data collected at the 15 HCWQL  stations farthest from shore.  These stations were
chosen as most compatible with Beeton's sources. In general, the HCWQL  values are quite
comparable to the values reported by Beeton (1965) from  the late 1950s; indeed, they
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 seem to be lower than Beeton's 1950s data in the case of calcium and chloride. Within the
 limitations of the data, it appears that for most parameters the lake is not deteriorating
 at the rate which typified the first half of the century.

      In order to test this conclusion,  regression lines were fitted to Beeton's data for
 each parameter. The slopes of the regression lines were tested for significance using a t-
 test.  The regression equations were  then used  to  extrapolate  Beeton's  data  to best
 estimates for 1979.  A standard error of the estimate was also calculated for a sample
 size comparable to the HCWQL database for each  parameter (Sokol and Rohlf 1969), and
 these were compared with the HCWQL data using a modified two-tailed t-test, adjusted
 for unequal variances. Table 70 summarizes  the results of this procedure.  The statistical
 procedure reveals that all  of Beeton's parameters increased significantly  (p< .01) from
 1900 to 1960. It also shows that, for all parameters except sodium plus potassium, values
 in 1978-1979 fall significantly below the  values extrapolated from the historical data.  In
 some cases, there probably has been an absolute decline in concentration since i960.  In
 others, especially sulf ate and conductivity,  there  may only be a lessening in the rate of
 increase.  However, had the analysis been done on the original data, the variance would
 have been greater, and thus the statistical significance of some of the results would have
 been reduced, perhaps even below the standard acceptable  limit of p <.05.

      The  decrease  in specific conductance,  while  highly significant  statistically,  is
 strongly dependent on the conversion factor used to convert Beeton's data, expressed  as
 total dissolved solids, to  specific conductance.  The analysis was done using a conversion
 factor of:

                           Specific Conductance  = TDS/.62

 recommended by Fraser (1978). The analysis was redone with a conversion factor of .65
 which has been  used elsewhere on Lake Erie.  This second analysis yielded no significant
 deviation of HCWI^L data  from the  trend of  Beeton's data.   Analysis of specific
 conductance and total dissolved solids data from the Division Water Intake for the City of
 Cleveland, measured  between 1968  and 1975 by the USEPA (Westlake) and the  City  of
 Cleveland lab at Whiskey Island, produced a ratio  of 0.66. This ratio is not significantly
different from the value of 0.65 discussed above, but is higher (p <.05) than the value  of
0.62 used  initially.  However, the rather poor correlation between  the two parameters
(r  <.15) makes  the data of questionable value in establishing the "true" ratio.  There  is,
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 at present, no adequate way to be certain which ratio is correct. Until a definitive study
 of this relationship is made, the long-term history of specific conductance  cannot be
 assessed with certainty.

      Short-Term Historical Trends.  Because Beeton's data set ends about 1960, a more
 recent data set was sought to help evaluate the changes in the 20  years falling between
 Beeton's data and the Lake Erie nearshore study.  The best source of information was the
 records from the Division Water Intake for the City of Cleveland, which include data on
 alkalinity, specific conductance,  pH,  total  phosphorus,  soluble  reactive phosphorus,
 ammonia, nitrate plus nitrite, chloride and sulfate, obtained between 1968 and 1973 by the
 USEPA office now in Westlake, and between 197* and 1977 by the Water Quality lab of
 the City of Cleveland, formerly located at Whiskey Island.

      The data set  used for this study is less than ideal because it was produced by three
 different laboratories,  using  different working  ranges and  in some  cases different
 analytical techniques.  In addition, the USEPA analyses were of samples from the water as
 it entered the purification plant, while the other samples were of lake water at the site of
 the water intake.  Thus, the EPA samples were of bottom water modified  by  passage
 through  the intake pipe.   By comparison,  the  City of  Cleveland  samples were mostly
 surface water, and  the HCWQL samples were both surface and bottom waters.  Because of
 the composite nature of the data set, various techniques were  used to  evaluate possible
 biases or inadequacies in the data.  The results of this scrutiny and of the earlier analysis
 are presented below.

      The data  for each  parameter  was subjected to regression  analysis  to  detect
 statistically significant linear trends.  Initial analysis  used all data in raw  form,  but
 subsequent analyses involved various modifications of the data, as described below.

      Tests of  the  regression line slopes  for significant  deviation  from  0  (no  trend)
 indicated no  trend  for alkalinity or specific  conductance, but  a significant increase in
nitrate plus nitrite (p <.001) and sulfate  (p<.001),  and  a highly significant decrease in
chloride  (p<.001) in the last  decade at this station (Richards  1981b).  Total  phosphorus
showed  no significant change, but soluble reactive phosphorus decreased  significantly,
even  though  the period  of record was shorter (1974-1979).  The  SRP data  contains  a
number of suspiciously high values early in the record, and when these were removed the
trend disappeared.
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      Removing Seasonal  Patterns.  Many, if not  all,  of the  parameters  studied for
historical  trends  also  undergo  concentration fluctuations  as  a  result  of  seasonal
fluctuations in supply and, in some cases, as a result of biological activity. The seasonal
changes are most pronounced in the nutrients, the extreme case being nitrate plus nitrite,
which declines sharply in late summer, with less than 20% of those found in early spring.

      These seasonal fluctuations tend to mask longer-term historical trends because they
increase the overall variance of the data set.  Typically, their effect is  to decrease the
achieved statistical significance in  a test of  the regression line slope.   Since  seasonal
fluctuations are a different phenomenon than the one being examined, it would be helpful
if these fluctuations could be removed from the data.  This can be done in the following
way.  Assume  that the seasonal effect is constant from year to year, and is not linked to
the long-term  historical pattern.  If  this is so, the data can be fit  by a  function of the
form:

                                   y =  mx + s(x) + b

where s(x) is a  periodic function (perhaps a very irregular one) of period one year.

      Under this assumption,  the procedure  is  as follows.  A  standard regression  is
performed  on the data, in effect ignoring the periodic component. Since it is assumed to
repeat exactly each year, it does not change  the  regression equation except to increase
the components of variance  associated with it.  The regression equation  is then used to
calculate the  values of y (the concentration)  predicted for the given values of x (time),
and the predicted y values are subtracted from the actual values.  In statistical terms, the
residuals are calculated.

     The  residuals are then grouped  together  by some  sub-interval  period  of  the
postulated  period function.  The grouping interval should be small enough to capture the
essence  of the  periodic  changes,   yet  large enough  to  contain  enough  data to  be
statistically useful. Some compromise is often necessary.  In this  study, data was grouped
by month,  which gave at least 30 data points in a month, with very few exceptions.  This
grouping gathered January data for all years in one group, February data for all years in
another group,  etc. The average of the  residuals in each of these groups is calculated. If
there is no seasonal effect in a data set, the residuals reflect only  random error, and these
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averages should all be very close to zero. Thus, any non-zero group average may be taken
as an estimate of the seasonal effect for that interval of time.

     These estimates of the seasonal effect are then subtracted from the raw data, and
the regression is recalculated.   The result should be a regression equation which is very
similar to the one calculated from the raw data, but it  should have a higher associated r-
square, or, alternatively, a t-test comparing the slope  with zero should achieve a higher
level of significance.

     Application of the above  procedure to the Division Water Intake data set produced
the results summarized in Table 71.   Examination shows that  most parameters  showed
improvement in the resolution of their historical trends, as measured by increases in the t
value.  The greatest increases  were among the nutrients, where  seasonally  is typically
most pronounced. In a few cases, the t value  decreased.  This is to be expected where
there was little seasonally, due to the error component of the seasonal effect estimate .
There was in most cases no  change in the achieved significance level of the  slope
regression  line.   Most of the  parameters for which  this  was true either  showed no
significant change,  and the improvement brought about by removing seasonally was not
sufficient to give  significance at p<.05,  or  they already showed highly  significant
historical change (p  <.001) and  the computer program did not give significance levels less
than .001.  In one  important instance, seasonal filtering produced  a  significant trend.
Total phosphorus did not show a significant trend before filtering, but showed a decreasing
trend significant at p <.05 after filtering.

     Because the procedure assumes that the seasonal patterns were constant during the
period of record,  monthly averages were plotted for each year to verify the validity of the
assumption. While the averages fluctuated considerably from year to year, no systematic
change was seen in any of the parameters.

     In general,  the seasonal filtering process tended to improve resolution of historical
changes, but not  sufficiently to have a great impact  on the conclusions of this study.  It
appears that factors other than predictable seasonal changes dominate the  variance  of
this  data set.  These  factors  may include laboratory accuracy  and precision,  and the
effects of fluctuating currents, which  may alternately expose the sampling site to waters
of more  nearshore  or more offshore  character. The following paragraphs highlight the
results of the seasonal filtering technique.
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      The total phosphorus data showed no significant change in concentration during the
 period of record; however, after seasonal filtering, a downward trend was indicated. Due
 to problems resulting from high detection limits and the various analytical  methodologies
 the indicated decreasing total phosphorus concentrations require future data in order to
 make a more definitive statement.

      SRP showed a significant decrease with time which improves upon seasonal filtering.
 Due  to  similar detection limit problems,  as previously discussed, this trend remains
 questionable.

      Nitrate plus nitrite indicates a highly significant increase in concentration over the
 period of record showing an even greater significance upon seasonal filtering.  Most of the
 increasing values were found in the last three years with little trend evident prior to 1978.

      No trend was evident for alkalinity; however, a slight decline was noted for the last
 five years.

      pH indicates a statistically significant but not visibly obvious increase with seasonal
 filtering improving the analysis.  The net apparent change over  11 years is approximately
 0.1 pH units.  Considering the difference in sampling and instrumentation, this cannot be
 considered a significant trend limnologically.

      Specific conductance showed a non-linear pattern.   Problems with the initial nine
 years of data make this analysis questionable.

      Chloride  data indicated the most  visually obvious (decreasing) trend with seasonal
 filtering only improving the trend slightly.

      Sulfate has a highly significant increasing  trend over the period of record with
 seasonal filtering not improving this trend.

      Analysis  of   the long-term  historical data  of Beeton   documented statistically
significant increases in all parameters.  By comparison, data from  the Cleveland area in
 1978-1979 is comparable to or lower than Beeton's data for  1960, indicating a decline in
the rate of increase for most parameters, and an actual decline in concentration for some.
The  only  exception  was  specific  conductance,  for which  the analysis was uncertain
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because  the  proper conversion  factor  between total  dissolved  solids  and  specific
conductance is not known at this time.  Analysis of historical data  from the Cleveland
Water  Intake Division suggests that the concentration of chloride has declined over the
period  of  time 1968-1979, and that sulfate has increased in the same time.  Both trends
were reasonably linear, and were highly significant statistically.

     Some parameters in the short-term data set showed no significant linear trend (e.g.
specific conductance),  and  others showed trends that  were significant  but data  was
decidedly  non-linear (e.g., nitrate plus nitrite). In some cases, the trends indicated may
be partly  a result of laboratory bias  (phosphorus forms) or sampling of different  water
masses (surface vs. bottom, e.g., pH) rather than historical change.  These  parameters
require further study to establish adequate historical trend information.

     Decade-long historical trends were  often comparable in magnitude to the annual
scatter in the  data, or even  to the difference between surface  and  bottom  water
concentrations.   Biases  between  labs  or between years within a lab,  or differences in
values  obtained with different analytical methodologies, may be sufficient to mask  subtle
historical  trends, or to create "trends" which reflect the history of analytical methodology
and bias rather than reflect the history of the body of water under study.  The attempt to
recognize subtle historical trends, which may nonetheless be of  great  interest to the
public, requires data of  the best quality.  Wherever  possible, the database should be the
work of one lab using one set of  methodologies and a carefully designed  quality control
program to  guarantee the comparability of data  from day to  day,  month to  month, and
year to year.  At the very least, frequent participation in "round-robin" exercises (such as
that carried  out  the the International  Joint  Commission)  is necessary  by  all  labs
contributing  to a historical database.  The results of these round-robin studies must be
made  part  of  the  laboratory quality control  program,  and  used to  adjust  biases, if
compatible data sets are to  be  generated.  These results should also be considered in the
historical  analysis, since  they may suggest biases that were not corrected,  and that might
not otherwise be apparent.

     Finally, the researcher who conducts  the historical analysis should seek as much
background  information  as possible related to quality  control,  and  should assume that
biases  will  exist in  many  data sets.  In the matter of historical analysis,  scientific
skepticism must extend to the data itself.

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 Cladophora

      Prior  to the  1950s,  the abundance of the  filamentous  green alga Cladophora
 glomerata (L.) Kutz had not presented significant enough problems in the  Great Lakes to
 attract widespread attention.  The earliest comprehensive Lake Erie study was reported
 by Taft and Kishler (1973) documenting the history of Cladophora in the western basin as
 well as seasonal abundance and biomass development from 1965 through 1971.  The study
 specifically examined Cladophora populations in and around the South Bass Island region
 of the western basin.  This  study  was stimulated more by academic interest  than as a
 result of Cladophora being considered a  nuisance problem.   However,  with  increased
 nutrient  loading and recreational use of the lakes, Cladophora became an ever-growing
 topic of concern.

      In  response to renewed ecological awareness  in  the Great Lakes  region and  the
 recognition  of Cladophora  as a potential symptom  of  pollution-related problems, a
 workshop was sponsored by the International Joint  Commission's Research  Advisory Board
 Standing  Committee on  Eutrophication  in order  to  bring  together scientists  most
 knowledgeable of Cladophora.  The proceedings from the workshop (Cladophora  in  the
 Great Lakes, ed. H. Shear and D. Konasewich J975) reviewed the current knowledge and
 discussed the future research needs concerning  Cladophora.  The  workshop members
 defined seven specific areas  in which further research  on Cladophora was necessary in
 order to  manage the problem effectively and be able  to measure whether or not  efforts to
control Cladophora were to be effective:

     I.   Growth requirements, physiology and life history.
     2.   Nutritional factors limiting growth.
     3.   Measurements of present distribution, biomass and production.
     4.   Measurement and prediction of responses.
     5.   Significance of Cladophora in the ecology of the lake.
     6.   Mechanical, biological and chemical control.
     7.   Socio-economic impact on lake activities and uses.
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     Each of the seven topics was described in greater detail within the text.  In addition,

nine general conclusions  were stated,  several of which were similar to the previously

listed research concerns:

      1.   The limnologists participating in the workshop concluded that Cladophora was
          the most important manifestation of eutrophication in  Lake Ontario and a
          major symptom in Lakes Erie, Michigan and Huron.

     2.   Cladophora could  be  used as a  general  barometer of lake  condition if its
          distribution, biomass and production could  be measured quantitatively.

     3.   Several  important measuring techniques are  available but have not yet been
          broadly  tested  and used,  i.e.  remote sensing for distribution and assays of
          nutritional status of Cladophora.

     4.   The role of Cladophora in the general ecology of the lake is  little known and
          should be included in a biological mapping of major components of the Great
          Lakes biota.

     5.   The objectives for fishery production for each  lake should be established as
          Cladophora is  believed to  play  a major role in determining  fish  species
          composition and production.

     6.   Two basic  types  of in-lake studies are recommended—a detailed continuing
          investigation  of water chemistry, physical  and  biological  conditions from
          within a limited growth bed in each lake,  and synoptic surveys from a number
          of stations in each lake to obtain comparative nutritional information, data on
          associated  faunal  populations, and accumulation of heavy  metals, pesticides
          and radioactivity.

      7.   As an alternative to control, the development of economic uses for Cladophora
          offers the potential of changing a liability  to an asset.

      8.   A  measurement of the socio-economic impact of Cladophora on the Great
          Lakes should be made by specialists in this area of endeavor.

      9.   To  direct  future  Cladophora  studies and coordinate activities  of various
          research and funding agencies, a task group should be established and operate
          under the aegis of the I3C.

      In  response to this  workshop and  subsequent  smaller  Cladophora workshops, the

Great Lakes International Surveillance Plan included  a program designed  to address some

of the issues outlined in the 1975 workshop.  Three objectives were declared:

      1.   To  determine  the growth  rate, density  and  distribution  of Cladophora  at
           selective sites in Lake  Erie for trends;

      2.   To  determine  the relationship(s) between environmental  contaminants and
           Cladophora growth; and,

      3.   To establish a  systematic database.

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      In order to ensure complete coverage of Lake Erie, USEPA-GLNPO and Ontario
 Ministry of the  Environment (MOE)  jointly cooperated  in the  program.  Sites were
 selected in each of the 3 basins; studies were conducted in the western basin by CLEAR-
 OSU, central  and eastern  basins U.S. shoreline by GLL-SUNY and eastern basin north
 shore by Ontario MOE.  The central basin  site was actually positioned at the  transition
 between the central  and eastern basin and will be considered an eastern basin site  in this
 report.  Simultaneous sampling programs were established over the 1979 field season with
 similar methodologies employed  by each of the groups.  Details concerning each of these
 studies can be found in  Volume 8, No. 1, 1982, of the Journal of  Great Lakes Research
 (Millner et al., Lorenz and Herdendorf, and Neil and Jackson). This issue of the journal is
 devoted exclusively  to  studies  involving  the ecology of  filamentous  algae (primarily
 Cladophora) in the  Great Lakes.   For further insight into  Cladophora  ecology and
 modeling,  the reader should take note of the 7-paper series on Lake Huron presented  in
 the same issue.

      Lakewide Distribution.  The Lake Erie Cladophora  study examined seasonal growth
 patterns and  biomass estimates  as  they  related to physical and chemical  (nutrient)
 factors. In addition, the area! distribution of Cladophora throughout the three basins has
 been reviewed by Auer and  Canale (1981).  In this report  areas of widespread Cladophora
 occurrence were delineated (Figure 122).

      As an additional  segment  of the western basin study, an attempt  was made to
 determine  the extent to which Cladophora  colonized the western basin (Lorenz and
 Herdendorf 1982). From June 27-29, 1981, data on the nearshore region and  shoreline
 structures  including reefs, shoals, and submerged shorelines was  obtained throughout the
 basin (Figure  123).   Cladophora standing  crop, bio-volume,  filament length, maximum
 depth of growth,  photosynthetically  active radiation (PAR)  profiles, Secchi depth and
 temperature data were also collected  at each site.

      Although Cladophora is present "throughout the western basin" its total areal extent
is not great.  Verber (1957) reported  that only 3% of the bottom of the western basin is
composed  of  bedrock some of  which  occurs at  depths not  capable  of  supporting
Cladophora due to light limitations.  A significant portion of the littoral region along the
Michigan, Ohio and Canadian shorelines does not provide suitable substrate to support this
alga.   The largest extent of bedrock suitable for colonization is  located in the Island

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region where exposed bedrock is found along the shorelines of most of the islands as well
as isolated tops of the major reefs.

      The western basin survey  reported Cladophora on the vast majority of all suitable
substrate in the western basin  including rocky shorelines, submerged  shoreline shelves,
reefs and man-made structures such as concrete, stone, wood and metal breakwalls, buoys
and ships.  Occasionally Cladophora was completely absent from substrates, as was the
case  on  the metal navigational buoys at Middle Ground Shoal and Pelee Point.  These
buoys were exclusively  colonized  by Ulothrix zonata.  Bangia  atropurpurea was also
frequently observed in the splash zone throughout the basin. Bangia is a recent invader
into the  Great Lakes, first reported in Lake Erie in 1969 (Kishler and Taft  1970), and is
now established in the splash zone throughout the lake.

      The depth to which Cladophora was found on the island shelves and reefs varied with
location.  Maximum colonization depth was generally greater the further north the site
was located, corresponding to greater Secchi transparencies and smaller light extinction
coefficients (K).  Depth distribution of Cladophora was greatest on the isolated reef areas
located offshore.
                                           2
      Standing crop varied from 10-229 g/m  dry  weight (DW).  Middle Ground Shoal
standing  crop  was  patchy and concentrated in the cracks of the bedrock,  possibly the
result of scouring action of sand moving across the shoal.  The largest DW standing crop
                                       2
collected was from Kelleys Island (229 g/m  ); this site also had the lowest in percent AFW
(ash free weight).  The percent AFW was  greatest  (62-78%) in the areas located in the
northwest region of the western basin where algal filaments appeared healthier (a bright
green color) and were more firmly attached than filaments found in other areas.

      A detailed account of Cladophora distribution is not available for the central basin.
Only  one station west of Erie, Pennsylvania was sampled near the western boundary of the
eastern basin;  consequently, no  information can be extrapolated for the entire basin.   In
general,  the north shore of the central basin is lined with steep erodable clay bluffs with
limited rubble/sand beach areas.  This unstable substrate is not suitable for any extensive
development of Cladophora.  The south shore is somewhat similar in topography  although
some areas are  more advantageous for limited Cladophora development with the most
noticeable Cladophora  colonization  associated  with  man-made structures  such   as
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 breakwalls.   These structures  almost without  exception support prolific Cladophora
 growth.

      The eastern basin studies also do not provide information pertaining to the extent of
 basin-wide Cladophora colonization.  In general, the south shore substrate characteristics
 are similar  to  those in  the  central  basin in that expanses of colonizable  bedrock are
 unavailable for extensive development of  Cladophora beds. In contrast, the north shore
 does provide a bedrock substrate similar to the western basin island region.  In particular,
 the area from Port Maitland to Fort Erie, Ontario supports  extensive Cladophora beds.  In
 addition,  Cladophora  populations are prevalent throughout  the  basin  wherever  the
 appropriate man-made substrate is available.

      Specific Study Sites.  The Lake Erie Cladophora studies provided information as to
 the seasonal growth pattern and biomass accumulations for  the specific areas studied. At
 each of the study sites, a bimodal season  pattern of biomass accumulation was observed
 (Figures 124-126).  The magnitude of  the bimodal  peaks varied with sampling depth and
 from site to site; however, the general pattern was evident. The maximum standing crop
 recorded at each of the study  areas is presented in Figure 127 and Table 72.

      The Walnut Creek,  Pennsylvania site, located at the central-eastern basin border,
 supported the smallest standing crop, with slightly larger standing crops  measured at
 Hamburg, New York and  Stony Point,  Michigan in 1979 and 1980, and South Bass in 1979.
 Rathfon Point, Ontario (eastern basin) clearly supported the largest maximum standing
 crop of 980 g/m  DW (Figure  127).  In  comparison, standing  crops reported for Lake Huron
 at Harbor Beach, Michigan were 200-300 g/m2 DW range (Canale and Auer 1982), and in
 Lake Ontario maximum standing crops  have reached 1062 g/m DW (Neil 1975).

     The  western  and eastern basins presented  somewhat different growth  limiting
 conditions.  In the western basin ambient levels of nutrients, in particular phosphorus, are
 sufficient so that a nutrient limiting condition is not  created (Lorenz  1981).  Light was
 determined to be the limiting  factor inhibiting more extensive Cladophora development in
 the western basin.   The greatest depth of growth was attained during the spring pulse,
 from late  May to late June. At Stony  Point, Cladophora generally did not colonize below
 2 m, and at South Bass Island the alga extended to approximately 3 m.  Cladophora at
 other locations in the western basin was observed as deep as 7 m.  When the variation in
depth of colonization at the different  sites was compared with  light data it was evident
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 that light attenuation was influencing the extent of vertical growth.  Temperature and
 nutrient availability at the deeper depths (3 m) was not appreciably different than at the
 shallower depths.

      The  results  from routine monitoring, laboratory experiments, and surveys of the
 western basin all support the theory that Cladophora in western Lake Erie is light-limited
 at PAR levels below approximately 50 uE/m  sec. The depth at which light attenuates to
 50 uE/nrr sec in the western basin varies from less than 2 m to over 7 m.  This agrees with
 a similar concurrent laboratory study utilizing a Lake Huron isolate of Cladophora which
                                                 ^
 reported the  minimum PAR value to be  35 uE/m  (Auer  1982).   The increase in the
 turbidity of western Lake Erie over the past century that has contributed to the decline of
 aquatic vascular plants (Stuckey  1971)  may also have decreased the total colonizable
 substrate available to Cladophora. If in the future the turbidity of the basin decreases in
 response  to  decreased sediment  loadings  and total phosphorus  concentrations remain
 above 50 ug/1 in  the nearshore regions, the quantity of Cladophora is likely to increase
 due to a greater vertical distribution.

      It is evident that the Cladophora  growth along the Canadian  shore in the eastern
 basin presents the greatest problem due  both to the quantity of  biomass produced and to
 the extent of public shoreline made undesirable. Three factors were considered to be
 important  on governing the  extent  of  Cladophora development in  the  eastern  basin
 providing the  appropriate  substrate is present: nutrients (phosphorus), light (turbidity) and
 temperature.

     At all three  eastern basin sites, nutrients (phosphorus) appeared to be the controlling
 factor of the abundance of Cladophora biomass.  Millner et al. (1982) point out that Secchi
 disk  depth generally  exceeded station depth; thus,  light was not considered a critical
 factor in the basin. Tissue nutrients were  found  to be at or below critical levels during
 the summer  months  indicating possible near-limiting conditions.  At  the north  shore
location an experiment was conducted to test if phosphorus additions into an experimental
site would further stimulate growth (Neil and Jackson  1982). Cladophora standing  crop
did in  fact increase in  response to the additions  of  phosphorus,  indicating  a phosphorus
dependent condition.  It was concluded that Cladophora biomass could be expected to be
reduced if local phosphorus concentrations are reduced.
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     Temperature seemed to influence Cladophora populations similarly in both basins.
The  combined effects of light and temperature have been extensively investigated  by
Graham et al. (1982).  In general, Cladophora standing crop continues to increase as the
temperature increases to 20°C (July).  At this point, the photosynthetic/respiration (P/R)
ratio is  less  than  1  leading to senescense,  tissue nutrient decline and subsequent
detachment of the filaments results.  In the  fall as temperature  and light intensities
decline, the P/R ratio is again greater than  1 and the second peak of the bimodal seasonal
development begins to appear.

     Nuisance Conditions.  Frequently contained in  the literature is a series of similar
statements describing  the serious nuisance effects resulting from Cladophora populations
(Surveillance Subcommittee 1981, Shear and Konasewich 1975, and Millner  et al. 1982).
For example, the Great Lakes International Surveillance Plan states:

     (1)    The  odor  and water discoloration  caused  by  windrows  of   decomposing
           Cladophora that accumulate on beaches can force the closing of recreational
           areas.
     (2)    Floating masses of algae foul the nets of commercial fishermen in Lake Erie.
     (3)    Tastes  and odors  in drinking water have also been attributed to  decomposing
           masses of Cladophora.
     (4)    Indications are that the abundance of Cladophora and other attached algae has
           increased significantly over the past 50 years.
     These statements do not represent the situation in Lake Erie. In fact, the last three
do not seem to be based on  any factual information; commercial fishermen experience
minimal problems  as a result  of Cladophora; for the most part, water intake systems are
generally  elevated off  the  bottom  and located approximately  2  km  offshore, and
consequently,  Cladophora would  rarely interfere with intakes or cause taste  and  odor
problems; and finally, there  is no real documentation that  would  enable  one to state
whether there has  been a quantitative change in the standing crop of Cladophora over the
last  50 years in Lake Erie.   Cladophora  can and does  accumulate along  shorelines
becoming  odiferous  as it decomposes; thus, only  the first statement has  any validity
concerning the Lake Erie Cladophora community.  The significance of Cladophora  on a
lake-wide distribution basis is certainly over-exaggerated and primarily presents problems
to beaches and shorefrontage in localized areas.  The problem of washed-up  algae and
aquatic plants is common to most every marine coastal beach in North America.  The
approach taken is to routinely remove the accumulated biomass.
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     The nuisance problems attributed to Cladophora in the Great Lakes result from an
over-abundance  of  nutrients, in this  case primarily phosphorus.   This  is particularly
evident by the extensive standing crops in regions of point sources.  The  most effective
way to reduce the levels  of Cladophora to  "natural concentrations" is  to  reduce the
loading of phosphorus to the lake as shown by Auer (19S2) in Lake Huron. This results in a
positive response both  in the nearshore and offshore regions.  Concerning the original
objectives of  the Surveillance Plan, two components remain unaddressed.  First, little
information is available as to the relationship(s)  between environmental contaminants
such as  heavy metal and organic compounds and  Cladophora growth.  Second, a more
complete basin-wide  database has to  be established in  order to  adequately evaluate
phosphorus control programs.   Having data from five select study sites provides only a
very limited insight into the Cladophora community of the whole lake.
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Fish Communities

      Fish communities of Lake Erie and their habitats have undergone significant changes
over the past 150 years in response to a series of cultural stresses.  These have included
intensive,  selective commercial exploitation of several fish  stocks, increased nutrient
loading, siltation due to watershed and shore erosion, invasion or introduction of exotic
fish species,  and loss of important  stream  and marsh habitats  due to diking,  filling,
damming,  channelization,  siltation, and industrial pollution.  The history and causes of
these changes have been extensively reviewed and discussed, particularly during the last
20 years.  Much of the discussion regarding causes is and  must remain speculative due to a
lack of intensive  limnological and fish population data  during the times when the  most
significant changes were occurring and to  incomparability  of  such  data as a result of
changing techniques in limnological measurement and fish stock assessment.

      In  general,  the cultural stresses listed above  resulted in  drastic  declines  or
extirpations of several endemic commercially and recreationally abundant  valuable fish
species and the proliferation of a few exotic or adaptable native species with significantly
less commercial or recreational value.  Declines of certain species were first noticed as
early as the  1880s, and some ultimately ineffective attempts were made  to  stop or
reverse the declines by supplemental stocking and regulation. However, during the 1950s
a series of major fish population collapses and extirpations occurred and radically altered
the composition of  both the Lake Erie fish community and the nature of  the fisheries
exploiting it.  Moreover, the deterioration of water quality in the lake accelerated due to
population and industrial expansion after World War II lead to fishery population declines.
Nationwide trends of a similar nature attracted increasing public attention and eventually
resulted in state and national legislation aimed at maintaining environmental quality and
managing  natural  resources.   In Lake Erie,  measures  to regulate  commercial and
recreational fisheries and to reduce cultural  nutrient loading, siltation, industrial pollution
and habitat loss were introduced during the 1960s and 1970s.
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     The purpose of this section is to provide a current assessment of fish stocks, fish
community  composition, and fisheries in  Lake Erie  with respect to  their actual or
potential responses to improving water quality.

     Background on Fish Population Changes.  Approximately 138 species of fishes have
been recorded from Lake Erie and its tributary waters.  At least 40 are or have been of
significant commercial, recreational or forage value (Table 73). Nineteen of these species
have been of major significance in commercial landings  since commercial fishing began in
Lake Erie over 150 years ago.  Lake Erie supports a greater diversity and higher biomass
of fish per unit area than any of the other Great Lakes. This has been attributed to the
southernmost position of the lake, its relatively warm,  shallow, nutrient-rich waters, and
its  variety of aquatic habitats  (Trautman  1957, 1981; Van Meter and Trautman 1970;
Hartman 1973).

     Commercial fish production in Lake Erie has been high throughout the history of the
fishery, averaging approximately  19  million kg/yr and ranging  from  approximately 11
million kg/yr to 75 million kg/yr since 1915. Annual commercial fish production in Lake
Erie has often surpassed total production in the other four Great  Lakes combined and has
seldom comprised less than one-third of total Great Lakes production.  An extensive and
valuable  recreational fishery has developed largely since  1949 and continues to expand,
competing with the commercial fishing  industry for several  fish stocks (Regier et al.
1969; Applegate and Van Meter 1970; Hartman 1973; Baldwin et al. 1979).

     In spite of the traditionally high level of commercial fish production in Lake Erie,
significant qualitative changes in the fish communities of the lake have occurred over the
last 150  years as a result of  exploitation and environmental changes.  The following
review of fish population changes and their causes is based largely on the accounts and
data of Regier et al. (1969), Applegate and Van Meter (1970), Regier and Hartman (1973),
and Baldwin et al. (1979) unless otherwise noted.

     The intensive settlement, agriculturalization and urbanization of the Lake Erie basin
by  European-descended  Americans and  Canadians began around 1815.   Native, pre-
settlement  fish  communities  in the  lake  were  characterized by  a  much  greater
predominance  of coldwater and coolwater  species, including lake sturgeon,  lake trout,
lake whitefish, lake herring, northern pike, muskellunge,  yellow perch, walleye,  sauger,
and blue  pike (Table 73). Many native warmwater species, including white bass,  suckers,
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ictalurids, and centrarchids, were also apparently more abundant than at present whereas
other warmwater species such as gizzard  shad and freshwater  drum  may  have been
significantly less abundant (Trautman 1957 and 1977; Hartman 1973; Regier and Hartman
1973).

      Regular commercial fishing in  Lake Erie began around 1815. By 1930, fishing had
become an important industry using seines, drag nets, weirs, trotlines, spears, and hook-
and-line.  Most fishing was concentrated in nearshore areas along the U.S. shore.  Around
1850, large, stationary pound nets were introduced in the western basin and gill nets were
introduced in the eastern basin.  This gear  made offshore, deepwater fishing a feasible
enterprise.  These efficient harvest techniques, in conjunction with improved preservation
methods and  transportation  systems made fishing more profitable (Regier et al.  1969;
Applegate and Van Meter 1970).

      A precise description of species and quantities of  fish harvested between 1815 and
1870 is not possible due to the  sparse catch records kept during  those years.  Based on
available  records,  muskellunge, northern pike,  largemouth and  smallmouth  bass, lake
sturgeon,  yellow perch and white bass were among the first species to attain commercial
importance,  especially in the  seine fisheries of bays  and rivers.   Lake herring, lake
whitefish  and lake trout became commercially important around the mid-1800s as gill nets
and pound nets made offshore harvest of these  species more  efficient.  Lake trout had
already declined significantly in abundance by 1870 (Regier et al. 1969; Applegate and Van
Meter 1970).

     By the early  1870s  pound nets, gill nets, fyke nets and trap nets were in use on a
large  scale in Lake Erie, predominantly in U.S. waters. The Ohio fishery was preeminent
during this period.  The Canadian pound net  fishery,  which concentrated on lake herring,
began to increase significantly after 1880, marking the beginning of increased activity by
the Canadian fishery, which had previously lagged far behind the U.S. (Regier et al. 1969;
Applegate and Van Meter  1970).

     Improved but  still  fragmentary catch  records  between 1870 and 1900  indicated
generally  stable lakewide harvest.  Lake  herring and lake whitefish stocks supported an
intensive,  high-profit commercial fishery, but landings of these  species peaked during
these  years and lower-value "coarse fish" such as sauger,  walleye, yellow perch, blue pike,
channel catfish and white bass increased in commercial importance. Perceived decreases
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in abundance  of  lake whitefish  and  lake  herring led  to  attempts  at governmental
regulation,  management, artificial propogation and stocking, however,  these  attempts
were complicated by  jurisdictional divisions.   The only  significant  loss to the fishery
during this  period was the lake sturgeon (Regier et al. 1969; Applegate and Van Meter
1970).

      Steam, gasoline  and diesel-powered fishing vessels replaced sailing vessels on Lake
Erie after  1899, and  the  introduction of the  steam gill  net lifter increased handling
efficiency.  The use of pound nets declined after 1920 due to the increasing efficiency and
portability of gill nets and trap nets, and pound nets were no longer in significant use
after 1936 (Regier et al. 1969; Applegate and Van Meter 1970).

      Good  commercial fishery statistics were available after  1900.   Lakewide  fish
landings declined steadily  during  the period  1914-29, due largely to a major decline in
abundance of lake herring.  The lake herring fishery collapsed around 1925.  Commercial
harvest  of  northern pike  and muskellunge  declined after  1915 (Regier  et  al.  1969;
Applegate and Van Meter 1970).

      By  1930, the  principal commercial  fishing method  consisted  of gill netting
throughout  the eastern  and central basins and shore seining and  trap netting  in  the
western  basin.  Lakewide commercial fish production leveled off between 1930 and  1950
with no new losses to  the fishery, although species already declining continued  to do so.
However, these declines were offset by increased landings  of walleye,  blue pike,  lake
whitefish and white bass. This period marked the end of the high-profit fisheries based on
high-value  coldwater  stocks,  but  fishing  effort  remained  relatively  stable  lakewide
(Regier et al. 1969; Applegate and  Van Meter 1970).

     Two major changes in fishing technology occurred in the 1950s. First, by 1952 nylon
nets had replaced twine as the material used in manufacturing gill nets.  The new nylon
gill nets could be fished continuously and were two to three times more efficient than the
conventional twine nets. Second, trawling for  smelt was introduced in 1958 and became  a
major  portion of the  Canadian fishing industry (Regier et al. 1969; Applegate and  Van
Meter 1970).

     In  the  early 1950s a period of great instability in the fisheries began.  Lakewide
commercial fish landings increased between 1951 and 1960 due largely to use of nylon gill
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nets and intensified  fishing effort, primarily  for smelt, in Canada.   Canadian landings
superseded  U.S.  landings as the abundance of the  higher-value species (lake  whitefish,
sauger and blue pike) on which the U.S. depended declined. Landings of whitefish, sauger
and blue pike  had fluctuated cyclically around  relatively stable averages between 1915
and 1950, but these fisheries declined steadily  and significantly during the 1950s and had
all collapsed by 1960.  By the 1960s the composition of  commercial  fish landings from
Lake Erie had changed considerably.  Canadian fisheries depended  almost entirely on
intensive production of yellow perch, walleye and smelt, whereas U.S. fisheries depended
largely on yellow perch and walleye as "cash species," with supplemental  income derived
from lower  value species (channel catfish, white bass, carp, suckers and freshwater drum).
Although stocks of  the  latter  species  were  substantial, landings were  variable and
governed by seasonal demand and marketability (Regier et al.  1969; Applegate and Van
Meter  1970).

     Effects  of Cultural Stress on Fish Populations. Natural  and culturally induced
environmental changes in Lake Erie have been widely reviewed and analyzed (Arnold 1969;
Beeton 1961, 1963, 1965; Carr 1962; Carr and Hiltunen 1965; Davis 196*; Hartman 1973;
Trautman 1957;  Verduin  196^,  1969).  Highlights based largely on Hartman (1973) and
Regier and Hartman (1973) of the major environmental changes as they affected the lake's
fish populations are as follows.

     Regier and Hartman (1973) conceded that short-term and long-term natural stresses
such as storm surges, seiches, cyclic water level fluctuations and  temperature changes
could have marked, even  persistent effects on the Lake Erie ecosystem, but they argued
that no natural stress during the last 200  years could have had more profound, long-term,
direct  effects on the lake's fish populations than any one of a series of cultural stresses
introduced after  1815.  Natural stresses were probably not primary causes of any  major,
long-term changes in fish populations, although the synergistic effects of natural stresses
in conjunction with cultural stresses probably contributed to changes (Regier and Hartman
1973).

     The original vegetative cover of  the Lake Erie drainage basin consisted of dense
upland  and swamp forest, interspersed with grasslands, and  an extensive marsh system
bordering the western end of the lake. Because of the dense vegetative cover, soil erosion
was limited and  runoff waters entering  the lake  were generally low in dissolved and
suspended solids. Tributary and lake waters were clear, their  bottoms largely free of silt,
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and aquatic vegetation was abundant.  Most of the forest and grassland was cleared for
agricultural by 1870, and most of the marshes were filled and diked by 1900.  Loss of the
original vegetative land cover and subsequent increased runoff, poor  erosion control and
inadequate soil management resulted in increased turbidity and silt deposition in the lake
and its tributaries.  The extensive loss of wetlands, aquatic vegetation, and clean rock,
sand and gravel bottoms  constituted a significant loss of spawning,  nursery  and adult
habitats for many fish species, especially salmonids,  esocids and percids (Trautman 1957,
1977; Hartman 1973; Regier and Hartman 1973).

     After  1815, hundreds of mill dams were constructed on tributaries of Lake Erie and
during the present century many larger dams were built for purposes of water supply and
flood control.   Many  tributaries were  dredged  and  channelized for navigation  and
agricultural drainage. Dikes were constructed around marshes at first  to protect adjacent
farmland and  later to preserve the remaining marshes as waterfowl hunting areas.  Dams
and dikes contributed to the decline or extirpation of many fish populations by making
essential  marsh   and  tributary  spawning  areas  inaccessible,  whereas  dredging  and
channelization resulted  in increased siltation  and habitat loss  in  many areas still
accessible (Trautman 1957, 1977; Hartman 1973; Regier and Hartman 1973).

     Accelerated nutrient loading, or cultural eutrophication, became a significant stress
on Lake Erie's fish populations over the  last 50-60  years.  Cultural  eutrophication  was
marked by significant increases in all major ions, including apparent three-fold increases
in nitrogen  and phosphorus.  Nutrient loading  has been greatest in  the western  basin,
decreasing eastward through the central and eastern basins. Increased nutrient loading
resulted in increased production of phytoplankton and zooplankton, increased biomass and
deposition of  decaying organic material  on the bottom,  which  subsequently  increased
sediment oxygen demand (Beeton 1965; Hartman 1973; Regier and Hartman 1973).

     The principal effect of cultural eutrophication  on fish populations was the gradual
restriction of  suitable  spawning,  resting, and  feeding habitats.   For example,  due to
oxygen depletion of the colder hypolimnetic central basin waters, the cool and cold water
species inhabiting this region during the summer months were forced to find alternative
habitats. As a consequence, several detrimental effects on certain species were probable,
i.e.,  decreases in the stocks of sensitive populations, increases in  year-class strength
variability and increases in population mobility, with all factors rendering the affected
fish  populations more vulnerable to other stresses such as commercial exploitation.Fish
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 populations  in  the  western and eastern basins were less  strongly affected  by oxygen
 depletion  because the former is too shallow to thermally stratify for long periods and
 because the latter is subject to |ess nutrient loading and deep enough to contain a large
 dissolved  oxygen reserve  when thermally  stratified.   Changes  in  the composition of
 benthic invertebrate populations caused by siltation and oxygen stress may also have
 negatively affected certain fish populations by decreasing the availability of forage items
 such as mayflies and amphipods (Beeton 1965; Hartman 1973; Regier and Hart man 1973).

      The  long-term effects on Lake Erie  fish populations  of toxic pollutants, including
 persistent biocides, metals, other inorganic and  organic compounds delivered to the lake
 via  agricultural runoff or industrial discharge, are  poorly understood.  Although such
 pollutants have been detected in fish and their negative human health impacts recognized,
 long-term impacts  on growth, reproduction and  mortality to  the fish require  further
 research.  Regier and Hartman (1973) expected such effects to be  small in relation to the
 other cultural stresses discussed.

      Eurasion carp and goldfish were widely introduced for pond culture beginning in the
 1870s.  Escapes and deliberate introductions into tributaries resulted in the establishment
 of these species in the lake.   The increasingly  turbid, nutrient-rich condition of the
 nearshore regions favored their proliferation. The direct competitive effects of carp and
 goldfish on native fish populations are not known, although their herbivorous,  bottom-
 rooting habits may have had some negative  effects on coastal marshes  (Trautman 1957;
 Hartman 1973).

      The sea lamprey, first  reported in Lake  Erie  in  1921, invaded  the lake via the
 Welland Canal.  Lamprey never became as numerous  in Lake Erie as in  the upper Great
 Lakes and have apparently had little  effect  on native fish populations.  The  relative
 scarcity of the lamprey in Lake Erie has been attributed to a lack of suitable spawning
 tributaries and preferred salmonid prey. The alewife,  another marine invader entering via
 the Welland  Canal,  was first reported  in the lake in 1931.  It  also never became  as
 numerous in Lake Erie as in the upper Great Lakes and has had apparently little effect on
native fish populations.  The failure of  this species to become well established  in Lake
Erie has been attributed  to  an abundance of predators and possible susceptibility  to
coldwater stress (Dymond 1932; Van Meter and Trautman 1970; Hartman 1973).
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      Various non-native salmonids have  been stocked in Lake Erie since 1870, but no
significant  naturally  reproducing  populations  became  established.   At present only
steelhead, coho and Chinook salmon are stocked annually and exist in significant numbers.
The effects of these three species on  native  fish populations  are poorly understood
although they are known to prey extensively on the abundant emerald shiners and rainbow
smelt (Hartman 1973; Parsons 1973).

      Rainbow smelt were first reported in Lake Erie during the 1930s, having evidently
originated from a single introduction in the Lake Michigan basin in  1912, and have become
increasingly abundant  in the central and eastern basins since the 1950s.  Their abundance
has been  attributed to greatly reduced competitive and predatory pressure during the
1940s and 1950s (Van  Oosten 1936; Van Meter and Trautman 1970; Regier and Hartman
1973). Regier et al. (1969) hypothesized that predatory stress exerted by abundant smelt
on  young native  salmonids and  percids  was  a  significant factor  in  the decline or
extirpation of these populations.

      White  perch were first reported in Lake Erie in 1953, having apparently invaded the
lake via the Welland Canal.  This species did not become widely established in the lake
until the late 1970s (Busch et al. 1977; Barnes and Reutter 1981; Isbell 1981).  The effects
of increasing populations of white perch on  native fish  populations have yet  to  be
assessed.

      The combined effects of exploitation  and  environmental  changes in  Lake Erie
resulted in major changes in several commercial and recreational fish populations.  In
addition,  many fish populations which have not been  exploited  have also directly or
indirectly responded to these factors and have exhibited long-term increases or decreases.
Changes  in  commercial fish populations have  been largely documented by continuous
monitoring of commercial landings since  1915 and have  been summarized by Trautman
(1957, 1981),  Regier  et al. (1969), Applegate and Van  Meter (1970), Hartman (1973),
Regier and  Hartman (1973),  and Baldwin  et al.  (1979).  Reliable, quantitative data on
changes  in  populations of  other species, including some of significant  recreational
importance, are largely lacking. Documentation of these changes is primarily found in the
results of qualitative or semi-qualitative ichthyological surveys, most of which have been
summarized by Trautman  (1957, 1977, 1981) and Van Meter and Trautman (1970).  Table
74 summarizes the changes in individual populations based  on these sources.
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      A number of unexploited fish species in Lake Erie have also  exhibited declines in
abundance,  largely in response to long-term habitat losses and environmental changes
(Table 73).   Among the species suffering  drastic declines  or extirpation  were wetland-
dependent species such as spotted gar, pugnose shiner, pugnose minnow, blackchin shiner,
blacknose shiner, lake chubsucker,  tadpole  madtom, banded  killifish and Iowa darter.
Tributary spawners, deep coldwater spawners and generally silt-intolerant species such as
longjaw cisco, mooneye, silver chub, longnose dace, eastern sand darter, channel darter,
river darter,  spoonhead sculpin and fourhorn sculpin were also subject  to declines or
extirpations (Trautman 1957, 1981; Van Meter and Trautman 1970).

      Fish Stock Assessment.  Fish stock assessment is "a collective term connoting a
group of  serially related nonexclusive functions - observation, description, analysis and
prediction - focused specifically on the  integrity, character, measurement, performance
and  projection of fish resources" (Kutkuhn  1979).  In practice, fish stock assessment can
use  a full  range  of  fish  and  fishery  data inputs,  parameter  estimates,  functional
relationships and analytical outputs. The principal fish stock assessment programs which
have or are currently  operating in Lake Erie follow.  These are the principal sources of
long-term, relatively uniform and consistent data concerning fish population abundance on
which any analysis of long-term trends in Lake Erie fish populations must be based.

      Annual  lakewide landing data  collected  in  a roughly uniform manner  was not
available  until around 1910 (Applegate and Van Meter  1970).  By the 1930s,  a uniform
system for collection  and analysis of commercial fishery statistics was in  use throughout
the U.S and Canadian  waters of Lake Erie.  The basis of this system was  the division of
the  lake  into statistical  districts and the submission of monthly catch  reports  by
commercial fishermen listing types and amount of gear used, time fished, locations fished
and catch of each species (Hile 1962). With certain statistical refinements, this system is
still  in use today. For  heavily exploited fish stocks commercial production is considered a
reliable  indicator  of  abundance.   Commercial  landing  statistics  are  less  useful in
determining abundance of fish with low  market values because the landed catch of such
species is related more to dockside price and seasonal marketability rather than the size
of the stock available for exploitation.

      During drastic fishery changes of the  1950s, the need for more predictive capability
in managing the fisheries than could be achieved  by  monitoring  commercial  landings
became apparent.   Consequently,  fishery biologists  in the U.S.   and  Canada began
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 sampling both landed and throwaway commercial catches at docksides and  on vessels.
 Data generated included sample age, size, and sex distribution, food habitats, maturity,
 and fecundity, of imporant commercial and recreational species.  Analyses of these data
 increased  the ability of fishery management agencies  to estimate future year-class
 strengths, recruitment, growth rates, mortality rates, and stock size of important species.
 This  provided the  information necessary  to  maintain or  increase  exploitable stocks by
 imposing size and catch limits or by regulating the types of gear used or areas fished.

      Index sampling of  fish  populations  was  a  logical  and necessary addition to the
 collection and analysis of commercial fishery  statistics.   Index sampling in Lake Erie
 consists of long-term collections by state,  provincial or  federal  fishery biologists at
 selected sites and  times of year  using comparable effort and techniques from year-to-
 year.  Index sampling is similar to biological sampling of commercial catches in the types
 of data acquired and kinds of analyses possible. However, index sampling gear,  sites and
 timing can be selected to maximize catches of target species and age groups, particularly
 the low-value species, young-of-the-year,  and small forage fishes often not included in
 commercial catches. This program was necessary to maintain uninterrupted time-series
 data, and to sample populations during critical life-stages  not represented in commercial
 catches. Two types of long-term  index sampling programs have been in operation in Lake
 Erie during the last 20 years.

      Stock-specific index sampling is oriented toward predicting future performance on a
 stock-wide basis important recreational, commercial, or forage species.  The purpose of
 the program  is to conserve the stocks by regulating  the  size and characteristics of the
 catch  over a  period of time and  evaluating the  effectiveness  of past and  current
 management  strategies.  Techniques primarily involve trawling, fyke netting and gill
netting at selected index stations with data collected  on relative abundance of young-of-
the-year fishes, age, size,  and sex distribution,  food habits, maturity  and fecundity.
Target  species are  primarily the heavily  exploited yellow perch,  walleye,  white bass,
channel  catfish and smallmouth bass,  but the relative  abundance of all  lower-value
commercial, recreational and forage species are generally recorded.  Index sampling has
been  largely  standardized and  integrated  over jurisdictional areas via the Great Lakes
Fishery Commission so that  stocks ranging over several such areas can be managed as
units.
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      Site-specific index sampling on  a long-term basis has generally been related to
 environmental  impact   assessment,  specifically  impacts  of  thermal  discharges,
 impingement and entrainment of adult and larval fishes by water intakes.  Most Lake Erie
 electrical  power  companies with  generating  facilities  in the  U.S. have  conducted
 programs.  In general, such surveys employ a variety of sampling methods and the types of
 data collected include seasonal abundance and distribution of fish species at control and
 test sites in the vicinity of the plant,  size distribution,  food habits and numbers of  fish
 impinged or entrained by the intake.   Although these  studies are not oriented toward
 stock-wide  assessment  as previously  discussed,  they have  provided  useful,  long-term
 corollary data  which can be of some value in  analyzing  fish populations in general
 (Reutter et al. 1980; Hamley 1981).

      During the  1960s  and  1970s  exploitation of certain  Lake Erie fish populations,
 notably walleye, yellow  perch, freshwater drum,  smallmouth  bass, white bass and channel
 catfish, by  recreational  fisheries increased  significantly and approached the intensity of
 commercial exploitation. It thus became necessary for fish stock assessment programs to
 record recreational extractions.  Sporadic creel censuses, or collection and analysis of
 recreational fishing statistics,  were conducted  during  the  1950s  and 1960s.   Regular,
 annual creel censuses consist of boat counts at access points, direct contact interviews
 with boat and  shore anglers,  biological sampling of catches, and submission of  monthly
 reports by  licensed  charter  boat operators  and sport fish processors.   Quantitative
 information provided by  these methods includes angler harvest by species, success rates,
 amount and distribution of angling effort,  and  biological characteristics (age and size
 distribution) of catches.

     Current  Status and Potential  Population Changes.  The potential impacts on fish
 populations  from  improving  Great Lakes water quality as  a result of restoration  and
 enhancement programs instituted since 1970 were reviewed  and  discussed by Sullivan et
 al. (1981).  The most significant impact of these  in terms of  effects on fish communities
 are phosphorus (and dissolved oxygen regimes) and sediment loads.

     Nutrient  loading from point sources is expected  to  decrease significantly in  the
 Great Lakes in the next  20 years primarily as a result of  treatment of municipal effluents
(Sullivan et  al.  1981).  Little change in  total  phosphorus loading from non-point sources is
anticipated. Phosphorus  loading in Lake Erie decreased from approximately 24,000 metric
tons in 1970 to  15,000 metric tons in 1980 (Sullivan et al. 1981).
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     Phosphorus load reductions could result in decreased plankton production, followed
by  decreased production of  planktivorous  species  such as alewife,  gizzard shad and
rainbow smelt and  of salmonid  and  percid predators.  On the other hand, reductions in
phytoplankton production could improve water transparency and favor the growth  of
submersed macrophytes which could  provide valuable cover and spawning habitat to many
fish species  (Sullivan et  al. 1981).   The most obvious  benefit to fish communities  of
phosphorus load reductions would be decreased organic decomposition and increased
availability of dissolved oxygen. In  oxygen-stressed  areas like the central basin of Lake
Erie, this could  be  of crucial  importance.  Availability of summer habitat for coolwater
and coldwater species like lake herring, lake  whitefish, lake trout, rainbow smelt, alewife,
yellow perch and walleye could be increased (Sullivan et al. 1981).

     In general, nutrient  loading is directly related  to primary and secondary production,
and ultimately fish  production (Ryder 1981).  Theoretically, phosphorus load reductions to
the Great Lakes could result in  decreased fish production and decreased yield to fisheries
(Sullivan et al. 1981). Based on  a model  by Lee and  Jones (1979), if planned reductions in
phosphorus loading  occur  between 1990 and 2000, fish yield  could  decrease 5, 10, and 25
percent in the eastern,  central  and  western  basins  of Lake Erie,  respectively; however,
this is highly speculative.

     Such models  cannot  account  for secondary,  selective effects  of nutrient  load
increases or  reductions  on individual species, populations or assemblages in complex fish
communities such as occur in  the Great  Lakes.  In eutrophic Lake Erie, greatly increased
cultural   nutrient   loading  was  accompanied  by   increased  plankton  biomass  and
deterioration of dissolved oxygen regimes.   This  resulted, in  combination with over-
exploitation, in yield declines  of  the  most desirable and  profitable  coolwater and
coldwater species, notably lake herring, lake  whitefish, lake trout and blue pike. Although
the total biomass of fish in Lake Erie may have increased, this is more likely reflected in
increased stocks of tolerant, warmwater  species such as gizzard shad, carp and freshwater
drum.  Anticipated  nutrient load reductions may indeed result in decreased fish biomass,
particularly  these  tolerant,  warmwater species.  Such  decreases may be  balanced  by
increases in more valuable coolwater and coldwater  species such as lake whitefish, lake
trout, rainbow smelt, walleye and yellow perch.  Precise effects are difficult to predict.
In the oligotrophic upper Great Lakes, where cultural nutrient  loading has been relatively
light and  has had minimal impact on offshore hypolimnetic oxygen regimes, it has been
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 speculated that nutrient load reductions might result  in  some  decrease in salmonid
 production (Sullivan et al. 1981).

      Reductions in sediment  loading could have beneficial effects on fish communities
 and fisheries  throughout the  Great Lakes,  particularly  in  harbors and  embayments.
 Loading reductions could result  in restoration  of  clean  sand, gravel and  rock  bottoms
 needed as spawning substrates  by many species, notably salmonids and percids.  Decreased
 amounts  of suspended sediments  could result in greater water clarity, thereby favoring
 the growth of submersed macrophytes.  This could benefit a number of  species using
 submersed macrophyte beds as spawning and nursery areas.  A  negative side effect of
 sediment loading reduction might be an increase  in many toxic or  persistent contaminants
 in the water column, since many such contaminants tend to sorb to particulate matter and
 be deposited on the bottom.   A decrease of particulates might  increase the amount of
 time toxics remain in the water  column thereby increasing exposure to  fishes.  On the
 other hand, sorption on particulate matter is the  transport mechanism by which many such
 contaminants enter a  lake, so  that decreased sediment  loading might be accompanied by
 decreased contaminant loading (Sullivan et al.  1981).

      The  elimination  of  contaminants from industrial discharges and agricultural runoff
 will certainly  have beneficial local effects, particularly in harbors,   tributaries  and
 embayments,  by reducing fish mortality and restoring habitat  quality.   The lakewide
 effects of reductions in dissolved solids and persistent contaminants are difficult to assess
 because the  effects of these  substances on fish growth,  health  and survival are poorly
 understood.  In general, effects  of contaminant reductions on fish communities will
 probably be much less significant than the effects of reductions in nutrient loading  and
 sediment input.

     Following the series of major fish population declines, extirpations  and community
changes in Lake Erie  during the 1950s, a period of relative  stability ensued  during  the
 1960s and  1970s. No major losses to the fishery occurred. Stock sizes, distributions and
commercial landings exhibited  no  apparent fluctuations  or trends on a scale comparable
with previous years. Deterioration of water quality in the lake during the 1950s and 1960s
was severe, and major water quality restoration and  enhancement  efforts began in  the
 1970s.  To assess the actual effects of the resulting water quality improvements on fish
populations, one must analyze the status and trends in those populations during the period
1970-1980  against the  background  of  their status and trends during the period 1960-1970.
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The following results are based on data from the Great Lakes Fishery Commission (1971,
1973, 197*, 1975, 1976, 1978, 1980, 1981) unless otherwise noted.

      Lakewide commercial landings of all species from Lake Erie during the period 1970-
1980 averaged approximately 20 million kg/yr and ranged from 16 million kg in 1976 to 23
million kg in 1980. This average was consistent with the  long-term average of 19 million
kg/yr (since 1915), and the variability was quite low compared to the long-term  range of
11-75 million kg/yr (since  1915).  The estimated average weights of major species during
the period were:  rainbow smelt (8  million  kg/yr), yellow perch (6 million kg/yr),  white
bass (1.5 million kg/yr), carp (1 million kg/yr), freshwater  drum (0.5 million kg/yr), gizzard
shad (0.* million kg/yr), walleye (0.2  million  kg/yr) and channel catfish (0.2 million kg/yr).
No other species had mean annual lakewide landings that  exceeded 0.2 million  kg/yr
(Baldwin et al.  1979; Great Lakes Fishery Commission 1980, 1981).

      Recreational  fishing pressure  during  the period 1970-1980  was concentrated on
walleye,  yellow perch, channel catfish, white bass, freshwater drum and smallmouth bass.
Recreational fishery statistics were not available on a regular basis until 1975 so a
thorough long-term analysis of recreational harvest trends is not possible.  During 1980 in
Ohio  waters  alone approximately 3.5  million kg of fish  were harvested by recreational
fishermen.  This comprised approximately 16 percent of the lakewide commercial harvest
that year and 109  percent of the Ohio commercial harvest,  illustrating  the current
significance of recreational extractions as a  factor affecting the lake's fish populations.

      After a general decline during the 1950s, walleye stocks remained relatively  low
through the 1960s. In 1970, Ontario, Ohio and  Michigan  closed  the commercial walleye
fishery in the western basin because  high  concentrations  of mercury  were  detected in
walleyes.  This  moratorium  remained  in  effect  through  1975.   Ohio and  Michigan
subsequently  banned commercial  walleye fishing but it continued in Ontario, Pennsylvania
and New York waters. A series of consistently strong year classes occurred almost every
year  after  1970.   Moreover,  during the  moratorium  an international catch  quota
management  plan under the auspices of  the  Great Lakes Fishery  Commission was
developed for western basin walleye stocks (Hartman 1980). By 1975, walleye stocks were
thought to  be at their highest level since  the  mid-1950s and approaching the  carrying
capacity of the  basin (Figure  128).  There also appeared  to be a  significant expansion of
western basin populations into the central basin.
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      Stocks and commercial landing  of yellow perch were high during the 1950s and
 1960s.  Between 1970 and 1974 a series of poor hatches and weak year-classes occurred.
 This  resulted  in  drastically declining  stocks reflecting  in  reduced  commercial and
 recreational landings from 1971 to 1976. Michigan, Ohio and Ontario, under the auspices
 of the Great Lakes Fishery Commission,  established a Yellow Perch Technical Committee
 to develop  information required for increasing brood stock  size via minimum size limits
 and  catch  quotas (Hartman  1980).   Tactics for accomplishing this  are still under
 discussion.  Good to excellent hatches and year-classes in 1975, 1977 and 1979 resulted in
 a reversal of the decline. By 1980, yellow perch stocks had  increased to near 1971 levels
 but were still considered dangerously low (Figure 129).

      Rainbow  smelt stocks  and  commercial  landings in Lake Erie increased steadily
 during the 1950s and remained relatively stable through the  1960s and early 1970s (Figure
 129).  There has been evidence of short-term stock size variability due to variable  year-
 class strengths and mass adult mortality. Potential causes of this mortality  are spawning
 stress,  oxygen stress in the  central basin, the  widespread sporidian  parasite  Gluea
 hertwigi,  or a  combination of the three.  Nevertheless, long-term smelt production has
 remained  high and commercial landings increased substantially after 1975.  This increase
 was  attributed to a shift in  Canadian summer fishing pressure from  the  depleted yellow
 perch stocks to smelt due to increasing Japanese market demand (Baldwin et ai. 1979).

      Both lake sturgeon and  muskellunge were severely depleted by over-exploitation and
 habitat loss to  the point of near-extirpation by the 1950s (Hartman 1973).  Both species,
 as indicated by their occasional presence in  commercial and index sampling catches, are
 still  present in the lake in limited numbers and there is no indication of a significant
 change in  their status since 1960.

      Northern  pike landings, after a significant decline  from over one million kg/yr  in
 1914, averaged 28,000 kg/yr during the period 1920-1956.  In  1957, commercial fishing for
 pike   was  banned  in Ohio and Michigan  waters.   Subsequent  landings, predominantly
Canadian, averaged only 900 kg/yr until 1973, after which they steadily increased through
 1980, averaging approximately  11,000 kg/yr (Baldwin et al. 1979; Great Lakes Fishery
Commission 1980,  1981).

      An effort to re-establish sauger was  made  by  the Ohio  Department of Natural
Resources.  Fry and  finger lings were stocked in upper Sandusky Bay  in  1974,  1975 and
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1976.  Survival was good  and growth  excellent, with successful natural  reproduction
documented. Future plantings  were proposed, but the natural expansion of the stock and
its interactions with walleye are not certain (Rawson and Scholl 1978).

     The principal native coldwater species of Lake Erie,  lake trout,  lake  herring, lake
whitefish and burbot, have all been commercially extinct in the lake  since  the  1950s
(Hartman 1973).   The latter  three,  as evidenced  by their occasional occurrence  in
commercial landings and index  sampling  catches, are still present in limited  numbers, but
there is no evidence of significant increases in stock  sizes.  Commercial  landings of lake
whitefish have increased from an average of approximately 750 kg/yr during  1970-1976 to
an average of approximately  2,000 kg/yr during 1977-1980.   The recent  short-term
increase  in  landings cannot be  considered  highly significant, and it is not certain that it
indicates increased stock size.

     Lake trout restoration efforts began by stocking in  Pennsylvania  waters in  197*.
Since 1978 the New York State Department of Environmental Conservation  and the U.S.
Fish and Wildlife Service have cooperated annually in an effort  to  re-establish a viable
population by stocking in the  eastern basin.  Although it is too early  to  evaluate the
success of the program, survival has been good and growth excellent.

     Stocks and commercial  landings  of the  principal  commercial and  recreational
warmwater  species in Lake Erie,  namely  gizzard shad, carp, suckers,  channel catfish,
bullheads,  white  bass and  freshwater  drum,  appeared  to  remain  relatively  stable
throughout the 1960s and 1970s (Figure  130).  Except for channel catfish, none of  these
species  exhibited  signs  of over-exploitation  or  response  to  environmental stress.
Commercial landings  of  channel  catfish  declined  steadily from 1960  to  1980 and  an
apparent decline in stocks was  documented.  The cause of this decline  was thought  to  be
poor year-class strength and over-exploitation of younger, mature females. Length limits
on commercially caught catfish in Ohio waters were increased to protect this segment of
the stock during the late  1970s.

     Although  cyclic fluctuations in  individual  populations  occurred, abundance  of
principal Lake Erie forage species,  including spottail shiner, emerald shiner, trout-perch,
and young-of-the-year alewife and gizzard shad, generally remained stable throughout the
period 1960-1980.  By 1980, an apparent general decline in all these populations was  noted
in index  sampling catches and attributed to an over-abundance of predators, primarily
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 walleye.  The U.S. Fish and Wildlife Service in 1979 began a study of forage abundance
 and predator-prey relationships in Lake Erie (Great Lakes Fishery Commission 1981).

      Pink salmon (Oncorhynchus gorbuscha) were first reported in both U.S. and Canadian
 waters of Lake Erie in 1979.  This Pacific species was first introduced into Lake Superior
 in 1956 and has now extended its range throughout the Great Lakes.  In the upper Great
 Lakes it reproduces naturally and has established self-sustaining populations.  Successful
                                                                     I
 reproduction in Lake Erie has not yet been documented (Emery 1981).

      Although the sea lamprey and white perch invaded Lake Erie in the 1920s and 1950s,
 respectively, significant changes in the status of each occurred in the 1970s.  Several U.S.
 and Canadian tributaries were classed as "low producers" of lamprey ammocoetes, with
 Big Creek in Ontario considered the major source of lamprey  recruitment to the lake.
 Surveys documented significantly increased production of ammocoetes in Conneaut Creek,
 Ohio, during 1977, followed by increased  spawning runs  and production in  Big Creek  and
 Young Creek,  Ontario,  and Cattaraugus  Creek, New  York, during  1978-1980.   These
 increases were attributed to improving water quality in the streams (Great Lakes Fishery
 Commission 1978, 1980, 1981).

      Abundance  and distribution of  the white  perch  increased suddenly and dramatically
 in Lake Erie during the late 1970s, particularly in the western basin.  This species has now
 become commercially and recreationally significant.  The cause of the sudden population
 expansion  and  its  potential impact  on  other fish  populations  remains  unclear  and is
 currently being investigated (Schaeffer 1981).

      Fish Population Response to Improving Water Quality. Although changes in  status
 have been documented for several Lake Erie fish populations during the period 1970-1980,
 it is difficult to specifically relate these  changes to  documented improvements in water
 quality during the same period.  First, as pointed out by Kutkuhn (1979), "analytical  and
 assessment capabilities have not yet advanced to the point where the relative contribution
 of pollution abatement to the recovery and improvement  of Great Lakes fishery resources
 can be quantitatively (and reliably) discriminated."  In  Lake Erie other factors such as
 tighter regulation  of fisheries,  more effective  and comprehensive fish management
 programs, artifical replenishment of stocks, regulation of fish losses due to impingement
and entrainment  at large volume water intakes, and increasingly closer  evaluation  and
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 modification of habitat-altering construction activities have all probably contributed to
 the recovery and expansion of certain populations.

      Second, Lake Erie fish populations for which an extensive amount of biological data
 is  available  are those economically important  populations which are most intensively
 exploited and  managed.   The relative  contribution of improving water quality to the
 recovery or  expansion of such species  as walleye, yellow perch and rainbow smelt is
 difficult  to  segregate from  the contributions  of  management, regulatory and habitat
 protection programs.  Populations of lake sturgeon, lake herring, lake whitefish, northern
 pike, muskellunge and burbot suffered  major  historical  declines in abundance and have
 remained at  low levels of abundance due  in part to water quality deterioration.  These
 species are  not intensively exploited  or  managed  at  present and any  recovery from
 depleted status might be construed as due  to improving water quality.  However,  because
 these potential indicator species are of relatively minor economic importance at  present,
 they are  not intensively  monitored  in stock assessment  programs.  The  biological data
 necessary to  detect and evaluate any recovery is  not available.

     Third, the life  cycles of the  majority of  economically important  Lake Erie fish
 species currently monitored range from five to ten years.  Important indicator species like
 lake sturgeon and lake trout live  as long as 30 years. Even assuming, quite liberally, that
 significant water quality improvements began in  the mid-1970s, the ensuing five years are
 scarcely an adequate time base for analyses of trends in  stocks in which the majority of
 individuals have not completed a single  life cycle.  A longer time, on  the order of 10-20
 years, is necessary to make such analyses.

     Four recent cases of fish  population recovery and expansion may be related  to
 improving water quality in Lake Erie. Of these, increased production and expansion of sea
 lamprey populations  in certain tributaries is  the only sufficiently documented  case in
 which improved water quality is probably a major cause.  The expansion of western basin
 walleye stocks  into the central basin is often cited as an indication of improving dissolved
 oxygen  regimes.  There is no documentation of  expansion into the hypolimnetic region,
and it  appears  to be  confined  to the nearshore epilimnetic area where oxygen depletion
has not  been a problem.  The  expansion is  more likely due  to population pressure.
However, reduction of the degree and extent of dissolved oxygen depletion in the central
basin may be important in the restoration  of a large endemic walleye population in  the
basin.  Finally, commercial landings of  lake whitefish and northern pike  have increased
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markedly in the last several years. However, sufficient data is not available to determine
whether these increases are due to  expanding stocks or to increased availability and
fishing pressure in certain areas.  For instance, increased fishing pressure on smelt in the
central basin may  have resulted in greater incidental catches  of whitefish,  which are
probably sympatric with smelt during all or part of the year.

      In general, improving water quality in Lake Erie might result in a shift  of trophic
status toward improved trophic status.  It can be conjectured that in the  long-term this
would result in the re-emergence of  a fish community approximating the composition of
the original  pre-settlement community.   While individual populations of  coolwater and
coldwater species might indeed expand, it is doubtful that the pre-settlement community
can be re-established.  Certain native species have been  irrecoverably extirpated.  If
habitat alterations such as dammed and channelized  tributaries and diked marshes persist,
improving water quality alone will not result in major recoveries of certain tributary and
marsh-spawning stocks.  Large populations of exotic species such as rainbow smelt, carp
and white perch have occupied niches which may have once been occupied by depleted
native stocks.  For instance,  to what  extent the  large smelt populations will affect the
recovery of lake herring or lake whitefish, which occupied similar niches, is difficult to
predict. Predatory interactions between populations of exotic species and depleted native
species may affect recovery of the latter. Smelt predation on young-of-the-year walleye
and blue pike has already been hypothesized as  a factor in the decline of these two native
species (Regier et al.   1969).   Finally,  commercial and recreational  extractions and
management programs will continue to affect the fish community as a whole.  To a large
extent, the structure of Lake Erie's fish community in the future will depend on a public
perception of what structure would be  most economically advantageous.
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Fish Research

      Larval Fish Entrainment.  Although  not  part  of the intensive program, a  brief
summary of a study designed to examine the distribution of larval fish and the effect of
power plant entrainment on larval fishes in western and central Lake Erie (Cooper et al.
1981) is considered to be appropriate. By examining larval fish distributions, considerable
insight can be gained as to potential effects of construction, industrial water use and new
sources  of  pollution  on fish  populations.   Consideration of  the  impacts upon  major
spawning and nursery areas when locating  new industry and dredging operations can  only
benefit fish populations.

      Icthyoplankton samples were collected at ten transects (three stations perpendicular
to the shoreline)  along the Michigan and Ohio shorelines of the Western basin in 1977 and
at nine transects along the Ohio shoreline of the central basin in 1978.  Additional samples
were collected in 1978 immediately adjacent to six power plant  intake structures. Figure
131  gives station locations for the western and central basin studies.  Samples  were
collected every ten days beginning in May and ending in mid-August.  All samples  were
collected during the period from one hour after sundown to one hour before sunrise using a
75 cm diameter 550 micron oceanographic  plankton net with an attached calibrated flow
meter.  The net  was towed obliquely through the water column behind a small boat  at a
constant speed between four and five knots for  four  minutes.   Each  larval fish  was
identified to the  lowest taxon possible and  its developmental stage, as described by Hubbs
(1943), was  noted.  Several species which are morphologically similar during their early
development could not be efficiently separated.  Gizzard shad (Dorsoma cepedianum) and
alewife (Alosa pseudoharengus) were grouped together as gizzard shad.  Carp (Cyprinus
carpio), goldfish (Carassius auratus) and their hybrids were similarly grouped and reported
as carp.  White bass (Morone chrysops) and white perch (Morone americana) were reported
as white bass.   Black  crappies (Pomoxis  nigromaculatus) and  white crappies (Pomoxis
annulius) were reported  as crappies, Pomoxis spp., and all sunfish specimens were reported
as sunfish,  Lepomis  spp.   References found  useful  in  the  identification  procedures
included:  Fish (1932),  Norden  (1961a), Mansuiti and  Hardy (1967),  Nelson  (1968)  and
Nelson and Cole (1975).

      The number of ichthyoplankton captured in each sample was converted to larvae per
100 m .  Four replicate samples at each  station  were then averaged  to give  a mean
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station  larvae concentration.   Entrapment  estimates  for  each  power  plant  were
calculated by multiplying the average larvae concentration at the station closest to the
power plant intake by the average! pumping rate for that plant per day.

      Distribution;  Twenty taxa of larval fishes were collected in the nearshore of the
western basin in 1977.  Sixteen species  were  identified,  representing ten families and
comprising  99.90%  of the catch.   Ten species,  gizzard  shad, yellow  perch (Perca
flavescens), emerald shiners (Notropis antherinoides),  white bass, carp, freshwater drufn
(Aplodinotus grunniens), log  perch (Percina caprodes), walleye  (Stizostedion vitreum
vitreum).  rainbow smelt (Osmerus mordax), and spottail shiners (Notropis hudsonis) were
captured in numbers great enough to be considered  abundant (i.e., mean density >.1/100
m3).  Four species, gizzard shad, yellow perch,  emerald shiners and  white  bass made up
over 97%  of the catch. Gizzard shad alone accounted for 83% of the total catch with the
remaining ten taxa represented by a few or often a single specimen. Table  75 lists the
average density for each taxon for the entire study area.

      In addition, larval whitefish  and sauger, although rare, were captured.   Both
whitefish  and sauger were abundant and commercially fished prior to the 1950s; however,
populations of these  two  species have  been  reduced consequently  they were  rarely
captured.   Subsequently, stocking programs have been initiated to re-establish the native
sauger population; thus, the capture of larval sauger indicates  these efforts  may have
been successful.  The capture  of  whitefish larvae indicates a small population  of whitefish
still uses spawning sites in the western basin.

      Of the twenty taxa collected in the western basin, yellow  perch, white bass and
walleye (henceforth referred to as "valuable species") have  the highest  commercial and
sport interest. A detailed description of the spatial and temporal distributions of these
"valuable  species" will follow.

      Yellow perch, the second  most abundant  larval species  captured in the western
basin, had a basin-wide mean  density of 21.31 larvae  per  100 m  in 1977.  Larvae were
first captured  on April  20  and were collected  during every sampling effort thereafter,
reaching a maximum density of 87 per 100 m3 on May 2. Figure 132 shows the temporal
distribution of yellow  perch larvae in the western basin in 1977  and Figure 133 displays
the yearly mean yellow perch density at each station.

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      Friedman's rank  sum  test  (Hollander and Wolfe  1973) was used  to  determine
 differences between inshore and offshore densities and differences between transects.
 However, no significant differences were found. The only significant differences occurred
 (a = .05) between the transects where the densities were highest, transects M2 and OH3,
 and transects M5  and  M3 where the densities  were lowest.  Transects  M2 and OH3
 accounted for 31  and  23 percent of the total  yellow  perch catch,  respectively.  The
 maximum density of yellow  perch larvae sampled was 665  larvae per 100  nrr at station
 M2/1 on May  1.

      The fourth most abundant species captured  in the western basin in 1977, white bass,
 had a basin-wide mean density of 7.85 larvae per 100 m3.  Figure 134 displays mean white
 bass densities for each  sampling date. White bass were first captured on May 22 and were
 collected during every  sampling effort thereafter with maximum densities  reaching 29.5
 larvae per 100 m  on June 13.  Figure 135 shows the mean density of white bass larvae
 captured at each station for the entire study period.  Significantly more white bass larvae
 were captured in Maumee Bay  than along the Michigan or Ohio shorelines.  Friedman's
 rank sum test (a =  .05)  indicated the lowest densities of white bass larvae were captured
 along  transects OH3 and M5 while  no significant differences were detected between
 inshore and  offshore concentrations (a =.05).  The maximum density of  white bass
 sampled was 283.3 larvae per 100 m  on June 4 at station MB 1/1.

      With a basin-wide mean density of 0.99 larvae per 100 m , walleye were the ninth
 most abundant larval species captured in the western basin.  Larval walleye  were the first
 larval species captured in this study, first collected on April  20, and were seen only during
 the  next three  collection periods  (Figure 136).   Samples  collected  indicated  larval
 densities were highest on May 1 with an average  basin density of 4.6 larvae per  100 m3.
 Figure 137  displays the spatial distribution of walleye larvae in the  study area.  The
 Kruskal-Wallis test indicated (ot= .05) that more  larval walleye were captured along the
 Ohio shoreline than in Maumee Bay or along the Michigan shoreline. The highest densities
 of walleye larvae were captured along transects OH3 (43% of the total walleye catch) and
OH2 (32% of  the total  catch) with the maximum density of  38 per 100 m  captured at
station OH3/1 on May 2.   The lowest densities were found along transects M3 and M5.
The  walleye  larvae, however, were almost exclusively found along the Ohio  shoreline,
particularly in the  Locust Point area (Davis-Besse  Power Plant).  This area along  the
shoreline has many offshore shallow rocky shoals ideal for walleye spawning habitat.
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     The majority of white bass captured in the western  basin were  probably spawned
over sandy dredge spoil islands on both sides of the Toledo navigation channel or near the
Ottawa River in North Maumee Bay.   The high yellow perch densities probably  were
spawned near the shallow sandy shoreline along Woodtick peninsula.  Densities of yellow
perch larvae were higher off Otter Creek, Michigan (transect M2) than anywhere else in
the study area.

     Twenty-eight taxa of larval  fishes were  collected in the  nearshore  zone  of the
central basin in  1978.  Twenty-two species were identified representing fourteen families
comprising 98.98% of the total catch (Table 76). Nine species, emerald shiner, gizzard
shad, spottail shiner, freshwater drum,  rainbow smelt,  carp, yellow perch, trout perch
(Percopsis  omiscomaycus) and log  perch were captured in  numbers great enough to be
considered abundant (i.e., mean density  >.10 per 100 m ).   Johnny darters  (Etheostoma
nigrum) and  mottled  sculpins (Cottus bairdi) had average mean densities of .84 and .50
larvae per  100 m  respectively, but since the capture was limited  to a few stations these
species were not considered to be abundant in the central basin in 1978.  Table 76 lists the
mean densities  for the entire sampling period and  the percentage of the total catch
represented by each taxon for the central basin as a whole.

     The bulk of the  catch was made up of Cyprinidae with emerald and spottail  shiners
contributing 32% and  16% of the  total catch. Species of  commercial and/or sport interest
captured were rainbow smelt, carp, white bass,  yellow perch, sauger and walleye.  The
capture of walleye and sauger larvae was limited to only a few specimens at a small
number of  locations.  Only yellow perch and rainbow smelt will be discussed since these
two taxa represent the major portion of the commercial/sport/ valued species.

     Yellow perch, the seventh most abundant species captured in the central basin, had
a mean basin-wide density of 1.25 larvae per 100 m  and were first captured on May 11
and subsequently on every sampling effort thereafter.  Figure 138 shows the temporal
distribution of yellow perch  larvae and Figure 139 represents the spatial distribution of
yellow perch larvae in the central basin  study area.  Friedman's rank sum test indicated
significantly  more larvae were captured at stations immediately adjacent to the shoreline
(77 percent) than at either the intermediate or offshore stations.  Ohio transects 8, 9 and
10 accounted for 59% of the total yellow perch larvae  captured. Collections indicated
yellow perch larvae densities were highest on 3une 19 (100 larvae  per 100 m ) at  station
OH9/1  and had a mean density of 6.2 larvae per 100 m .
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      Yellow perch larvae were found to be concentrated in the eastern third of the study
area. This area has very limited quantities of clean sand and gravel and even less aquatic
vegetation (requirements for yellow perch spawning habitat). Yellow perch therefore may
be using harbor breakwalls and sand accumulated on the leeward side of these structures
as spawning habitat.

      Rainbow  smelt were the fifth most abundant larval species captured, with a mean
basin density of 3.4 larvae per 100 m .  Smelt larvae were first captured on May 20 and
during every sampling effort thereafter.  Samples collected indicated smelt densities were
highest on July 5  with an  average  density of  14.6  larvae  per  100  m .  Figure 1*0
graphically represents  smelt densities  throughout  the sampling period.  Seventy-two
percent of all smelt larvae were captured at the stations farthest from the shoreline. The
majority of smelt  were captured west of Cleveland with 68.3% of the catch coming from
transects Ohio  1-4. Maximum density of smelt larvae was 100.1 larvae per 100 m  on 3uly
5. Figure  141 is the representation of mean smelt densities at each station.  Past studies
indicate that no rainbow smelt spawning activity had been reported west of Cleveland.
Historically it  has been believed that any smelt  larvae found in this area were probably
spawned in the Pelee Island-Pelee Point area and were carried to the south shore area by
the dominant surface currents (MacCallum and  Regier 1969). The  fact that 72% of all
smelt larvae were captured  well offshore and that  over 98% of the smelt  larvae were
developed beyond the pro-larval stage indicates the majority of the smelt may have been
carried into the study area by these currents.
                                 Q
Entrainment.  A total  of 4.87 x  10  larvae were estimated to have been entrained at the
four power stations along  the shoreline of the western basin  in 1977.   Detroit Edison's
                                        q
Monroe Plant accounted for 61% (2.87 x 10  larvae) of  the total, Toledo Edison's Bayshore
Plant accounted for 27.3%,  Consumer's Power's Whitting Plant 11.3% and the Toledo
Edison-operated Davis-Besse Plant 0.3% of the total.

     Gizzard shad was the most abundant species entrained comprising 90.5% of the total
number of  larvae entrained (summed over all four plants).  Carp larvae were the second
most abundant, accounting for 4.48%  of  the total entrained and yellow perch were third
with 2.15% of the  total.  Entrainment estimates were  highest at the Monroe plant where
        9
2.97 x 10   larvae  were estimated to have been  entrained (60.9% of  the  total  basin
entrainment).   The lowest  number  entrained  was  at  the  Davis-Besse  plant  where
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 1.58 x 10'  larvae were estimated  to have been entrained.  Table 77 lists the number of
 each species entrained at each power plant.

      Although the Monroe power  plant entrained two times more larvae than any other
 power plant, 98.2% of the total entrainment was made up of gizzard shad (91.0%) and carp
 (7.2%).  "Valuable species" accounted for only 1.1% of total entrainment at Monroe.  In
 contrast, the  much smaller Toledo Edison Bayshore plant entrained  far more larvae of
 "valuable species."  The Bayshore plant was  responsible  for 48.2% of all  yellow  perch
 larvae entrained, 1.6 times that of the Monroe facility, 67.7% of the white bass, 15 times
 more than Monroe, and 66.3% of the walleye entrained, with no walleye calculated to
 have been entrained at Monroe. If one would consider the location of the power plant in
 relationship to spawning and nursery areas, entrainment of valuable species, particularly
 walleye  and yellow perch, would  be expected to be  high  at  Davis-Besse.   However,
 comparatively few larvae were entrained here:  6.2% of the total number of walleye, 2.1%
 of the yellow perch, and .03% of the white bass.  This can be attributed to the fact that
 the  Davis-Besse plant has a  small water demand compared to the other three plants
 because it utilizes a cooling tower.

     Entrainment estimates were  calculated for six power plants along the Ohio portion
 of the central basin: Avon Lake, Edgewater, Lake Shore, Eastlake, Ash tabula A & B and
                                                                      o
 Ashtabula C Plants (Table 78).  Calculations indicate a total of 2.52 x 10  larvae were
 entrained at the six power stations along the shoreline in 1978.  Entrainment losses were
 highest at the Ashtabula A & B plant where 7.61 x 10  larvae, representing 30.8%  of all
 central basin entrainment, occurred. The Eastlake plant ranked second with 21.4%, third
 was  Ashtabula C plant (20.3%), fourth the Avon Lake plant (14.6%), fifth Lake  Shore
 (6.4%) and  the Edgewater plant entrained the fewest larval fishes with 4.7% of the total
 number entrained.

     The power plants in the central basin, unlike those in the western basin, have their
cooling water intakes behind man-made structures.  Although these man-made structures
are designed to reduce the accumulation of storm-driven debris in the canal; they may
also  reduce larval entrainment. Entrainment of larval fishes  in the central basin appears
to be more dependent upon location of the power plant than to the amount of water used
by the plant.
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      Emerald  shiners were calculated to  be the  most abundant species entrained,
accounting for 37.2%  of  the total entrapment in the basin.  Gizzard  shad (25.0%) and
rainbow smelt (13.0%) ranked second and third.  Table 78 lists the number of each taxon
estimated to have been entrained at each power plant.

      Densities of yellow perch larvae were higest along the transects east of Cleveland.
The Ashtabula A  & B plant and the Ashtabula C plant, the easternmost power plants in the
study area, accounted for 54.22% of the total number of yellow perch entrained (36.96%
at  A &  B and 17.26% at the C plant).  Yellow perch  entrainment was lowest at the
Edgewater plant where 4.83 x 10  larvae were estimated to have been entrained (1.05% of
total central basin yellow perch entrainment).

      Larval  smelt entrainment was highest  at the Eastlake plant where 2.19 x 10  smelt
larvae (68.7% of  total smelt entrainment) were estimated to have been entrained.  It  is
hypothesized that this plant entrained  such a high  percentage of smelt  because of the
design of the protective breakwall.  At this plant the breakwall is  open  to  the west to
minimize inflow  of  warm  water and debris from the Chagrin River.  All other power
plants are located inside harbors or have their intakes  open and to the east.  If one
assumes  smelt larvae are spawned in the Point Pelee area and are carried into the study
area by  the  dominant currents, smelt larvae would be carried directly into the  water
intake.

     In an effort to determine  the effects  of entrainment upon larval fish  populations,
the total number of larval fish estimated to have  been  entrained  was compared  to  a
volume-weighted  estimate  of  nearshore larval  fish abundance.    Table 79 gives the
percentage of  the  volume-weighted estimate  of nearshore  larvae  abundance  for the
valuable  species  that were entrained.   One cannot assume, however, that yellow perch
populations in the western basin are almost  eight percent lower than they  would be  if
power plants  were not present.

     The number of larval fish entrained by a power plant is largely determined by two
factors:  (1) the location of the power plant or more specifically the location of its water
intake structure, and (2) the amount of cooling water pumped from the lake. Entrainment
losses are therefore lower at  power plants  which are built in an area not utilized as
spawning or  nursery  areas or in which measures have been taken to minimize lake water
usage.
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      Fish Contaminants.  The second current research effort deals with the assessment
of toxic substances found in the fish of Lake Erie. Since Lake Erie is heavily exploited by
sport and commercial fisheries,  it is imperative that the toxic burden  of  the fish be
known.  Surveys of organochlorine contaminant concentrations in Lake Erie  fishes have
not  been extensive and  have been  largely limited to  samples from  the  open  lake.
Moreover,  uptake rates of  such  contaminants have  primarily been investigated under
laboratory rather than field conditions.

      In order to determine some watershed sources of organochlorine contaminants in
Lake Erie,  Burby et al.  (1980)  determined  concentrations  of  27  major  contaminants
(aldrin, a-BHC, b-BHC, y-BHC, chlordane, o,p'-DDT, p,p'-DDT,  o,p'-DDD,  pp'DDD, o,p'-
DDE, p,p'-DOE,  dieldrin, o-endosulfon, b-endosulfon,  endrin,   heptachlor,  heptachlor
epoxide,  hexachlorobenzene, 2, 4-D, methoxychlor, mirex, arochlors 1016, 1254 and  1260,
total PCBs, toxaphene  and trifluralin) in whole  fish samples from  11 Lake Erie tributary
mouths  (River Raisin, Maumee River, Toussaint River,  Sandusky  River, Black River,
Cuyahoga River,  Chagrin River, Grand River, Ash tabula  River,  Walnut  Creek  and
Cattaraugus  Creek).   Twelve  common species of recreational,  commercial or forage
importance,  gizzard shad (Dorosoma cepedianum), rainbow  smelt (Osmerus  mordax),
northern  pike (Esox lucius), carp (Cyprinus carpia), emerald shiner (Notropis atherinoides),
channel catfish (Ictalurus punctatus), brown bullhead (Ictalurus nebulosus),  white bass
(Morone  chrysops), yellow perch (Perca flavescens)  and  freshwater drum (Aplodinotus
grunniens) were tested.  Age groups within each species were tested separately.  In order
to make field determinations of uptake rates, hatchery-raised young-of-the-year bluegill
(Lepomis macrochirus) and channel catfish were held  in  the mouths of  the  Maumee,
Cuyahoga and Ashtabula Rivers for six weeks during summer, 1980. Fish were  removed
and tested  for the 27 contaminants at the end of  the  holding period in  1979,  whereas
weekly sub-samples were removed and tested during the 1980 holding period.

      Of the 27 contaminants tested, ct-endosulfan, b-endosulfan, and toxaphene were not
detected  in any of the samples from the tributary mouths.  Arochlors  1016, 1254, 1260 and
total  PCBs  exceeded  1.0 ppm in fish samples from the Raisin,  Maumee, Toussaint,
Sandusky, Black, Cuyahoga and Chagrin Rivers and a concentration of yBHC in excess of
1.0 ppm  was found  in the  Ashtabula River.   All other  contaminants  were  found in
concentrations less than 1.0 ppm.  Significant differences were found in concentrations of
contaminants in fish of the same species and age groups  from different tributaries.  In
particular, total PCB concentrations exhibited large differences among same age groups
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 of white bass, carp and spottail shiners in different tributaries. One Age Group IV channel
 catfish from  the Sandusky River and  one Age Group IX channel catfish from the Black
 River contained concentrations of DDT and metabolites in excess of I3C limits. The same
 channel catfish contained total PCBs and mirex concentrations in excess of FDA and IJC
 limits, respectively Age  Group IV carp, Age Group I spottail  shiner, and Age Group II
 brown bullhead  from the River Raisin  also contained total PCBs concentrations in excess
 of FDA limits.  Gizzard shad,  carp, spottail shiner,  emerald shiner,  white bass  and
 freshwater drum representing a number of age groups in the Raisin, Maumee, Sandusky,
 Black, Cuyahoga, Chagrin, Grand and Ashtabula Rivers contained mirex concentrations in
 excess of IJC limits.

      Yellow  perch  recovered from the Maumee River at the conclusion  of the  1979
 uptake rate experiment showed  a slight  increase in  concentration  of 7 contaminants.
 White perch  recovered from  the Cuyahoga River indicated  a  slight  increase of  15
 contaminants.  Two  of the contaminants, hexachlorobenzene and trifluralin, increased
 markedly.   In the channel catfish recovered from the Cuyahoga River, 10 contaminants
 increased  slightly.   Again, hexachlorobenzene and  trifluralin increased markedly.  No
 living channel catfish were recovered from the Maumee River. No uptake of  the majority
 of the 27 contaminants was observed during the 1980 experiment.  Only p,p'-DDD, p,p'-
 DDE,  dieldrin,  heptachlor  epoxide,  2,*-D,  trifluralin and arochlor  125*  exhibited
 increases,  generally  at low concentrations, in either bluegill or channel catfish from the
 Maumee, Cuyahoga and Ashtabula river mouths.

      Clark et al. (1982) reported results of comprehensive organochlorine and mercury
 analyses of coho salmon (Oncorhynchus kisutch) in each of the Great Lakes. Analysis by a
 single laboratory produced a set of tissue residue data on over 30 pesticides and industrial
 chemicals  including those currently in use in  the  Great Lakes and those whose use  has
 been  banned  or severely  restricted.   The  data  also demonstrated  the extent  of
 accumulation for compounds currently applied to control  various pests in the Great Lakes
 Basin.   Coho  salmon  from   Lake  Superior  contained only  trace amounts or  low
 concentrations of most contaminants.  Lake Erie coho contained low levels of a number of
 pesticides  and industrial compounds with  relatively higher residue levels in coho from
 Lake Huron and  Lake Michigan. The highest residue levels for a number of compounds
were found in coho from Lake Ontario, but this may reflect a faster growth rate for fish
in that lake and not  present a true picture of the  relative  magnitude of contaminant
inputs.  Because of their open water habitat preferences, contaminant concentrations in
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coho salmon demonstrate whole lake contaminant problems rather than point-source or
nearshore conditions.   The data  reported generally  agreed with  recent findings  from
individual state contaminant monitoring programs, although the problems with varying
analytical and sampling techniques precluded direct comparisons.  Current tissue residue
levels were usually less  than historical levels for PCBs, DDTs  and mercury, indicating
some decreases in these contaminants have occurred since the 1960s and early 1970s.
Only residue levels of mirex in coho collected from Lake Ontario exceeded the Food and
Drug action level of 0.1 ug/g.

      The differences in study design of  toxics in fish far  outweight  the  similarities
making it evident  that standardization of techniques should be resolved before any future
studies are initiated. A summarization of recent studies (Table 80) shows the  variation in
study areas sampled, tissue types analyzed (whole body vs. fillet),  fish  species utilized,
parameters analyzed, and the application of data correction methods for recoveries.  The
few  guidelines concerning toxic  substances in fish established by  the Federal  Drug
Administration refer only to edible portions (fillets) yet studies on whole bodied fish have
been undertaken (Table 81) with no certainty as to how the data collected would apply to
these guidelines.  The scientific  evidence  points to the fact that organochlorines are
concentrated in fatty portions of fishes,  very  little of  which  is associated  with fillets
(Reinert 1969; Hamelink et al. 1971).  If one wishes to examine the potential toxic burden
to humans it is best to measure concentrations in  edible portions only; however, if  total
bio-accumulation  in fishes is the  desired  information  the  measure of  whole  fishes or
possibly just the fatty portions is appropriate.

      With the number of utilized industrial chemicals increasing, and with their potential
health effects  singularly or synergistically uncertain,  we are forced to begin a more
realistic approach  to a toxic program.

      The following list presents suggestions compiled from the authors of the most recent
Lake Erie toxics programs in order to aid in the coordination of future programs.

      1.   To optimize the dollars spent on analysis an attempt should be made to select
          tributaries which appear to be sites of organochlorine  contamination based on
          the  recent survey  information  (i.e., Ashtabula, Raisin, Maumee and  Sandusky
          Rivers).
      2.   Select only parameters that result in health problems.
      3.   Limit collections to a few species.
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4.   Standardization in templing design and methodology.
     a.    Whole body versus fillets
     b.    Definition of whole body should be established

     c.    Total  PCBs (the sum of arochlors 1260,  1254, 1248 and 1242) should be
           reported to comply with the Federal Drug Administration  guidelines as
           well as the individual components.

     d.    Reported data  should  not be corrected  for  recoveries;  however, the
           recovery  data must be presented along with  additional quality control
           information.

     e.    Most importantly, the  extraction and analytical procedures need to be,
           agreed upon.
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166

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                                RECOMMENDATIONS

      The recommendations that have ensued during the preparation of this document are
classified  in  two categories:   (1) scientific investigations and  (2) future management
programs.   Further  studies on  Lake Erie  should  involve  a  thorough analysis of past
programs and a firm committment  to  future programs.  New programs must be more
efficient in  design  in  order  to acquire  information  pertinent to  the goals  of  the
investigation.  In addition, more attention must be paid  to information already available
pertaining to the scientific problem being addressed.

Scientific Investigations

1.    The U.S. alone has accumulated a preponderance of historical data collected from
      the turn of  the century  until present.   Many of the questions we  are being
      confronted with today cannot  be  answered without the  proper evaluation of past
      data  records.   The subjects that  need to  be examined  in  light of historical  data
      include both biological and chemical parameters. For example, the issue of changes
      in the biota of the lake, specifically phytoplankton  and benthic communities, needs
      to  be thoroughly appraised in this  manner. This type of  approach is also  applicable
      to chemical parameters such as phosphorus, nitrogen and ions.

2.    In  conjunction  with the  previous  recommendation, an in-depth evaluation  of  the
      statistical techniques applicable to trend analysis needs to be examined in order to
      adequately evalute historical  data.   This  is  a  complex problem dealing with
      numerous sources of variability, i.e.,  changes  in sampling  locations and  methods,
      missing data,  and natural variability within a  field season and between years.  If we
      are to utilize  this valuable historical  resource,  proper  consideration   to  these
      problems must  be given,  resulting  in a valuable contribution to the analysis of  the
      entire Great Lakes database. Statistical evaluation of historic data sets would be
      useful in planning future programs.

3.    The continuation of the open lake monitoring program is required by international
      agreement and must be maintained in order to evaluate the  response of the lake to
      remedial programs.  The major effort should be concentrated  on the western and
      central basins with  a reduced  effort  maintained on the eastern basin.   Primary
                                          167

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      consideration should center around total phosphorus, nitrate plus nitrite, chlorophyll,
      phytoplankton and benthic organisms.  This effort  requires survey data pre-  and
      post-stratification as well as data throughout the stratified period. This will ensure
      adequate information for modeling efforts as well as nutrient budget calculations.
      The current program should be stringently reviewed in light of present and future
      priorities in order to avoid problems of incomplete and/or inadequate data sets.

4.    The nearshore region primarily along the U.S.  coast of  the  western and central
      basins needs special consideration. Site and parameter specific  studies should be
      implemented in many of the nearshore regions to evaluate contaminants known or
      suspected to be important within a region.  Each of  the site specific studies should
      involve a pilot study to evaluate current data records, to inventory potential or
      anticipated contaminants, to scientifically  determine optimal sampling schedules
      and locations and to define objectives for the study.  Careful consideration of these
      points must be made in order to follow contaminant loads into the lake and follow
      their interaction with the open lake and biota.

5.    Databases on heavy metals and organic contamination are extremely weak and need
      to  be updated and  upgraded.   This is particularly  important in the western and
      central basins of the open lake and at localized nearshore regions suspected to be
      problem areas.  In many cases, the information is either incomplete or not existent.
      Also, recommended methods and detection limits need  to be upgraded  to reflect
      current technology.  Accessability and usability  of the STORET  system  should be
      improved:
      a.    Reorganization of STORET codes
      b.    Addition of codes for pesticide parameters
      c.    Correction of data already in system
      d.    Simplification of user's manual

6.    Biological indicators should be better  utilized to examine contaminant loadings and
      subsequent effects.  It is recommended that benthic  and  Cladophora populations be
      examined for this purpose.  Due to the sedentary nature of these  organisms, and
      their reduced variability to exposure, they could provide a better indication of biotic
      levels of contamination than transient fish populations.  For example, benthic and
      Cladophora  populations located at or near point sources or transects extending from
                                          168

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      such sources may prove to be an effective monitor of contaminant loads as mixing
      with the open lake occurs.

 Future Management Programs

      The second group of recommendations is put forward in hopes that future programs
 on the lake will be more  effective and  efficient.   They  specifically are designed  to
 upgrade the management of future programs.

 1.    The I3C should assume a  dominant role in the prioritizing and coordination of the
      studies to be  undertaken.  This requires overseeing a project from inception  to
      completion in  order to ensure that programs are implemented in accordance  with
      the original study plan.  This  is particularly important for quality  control programs
      and statistical  analysis of the  data.

 2.    The overseeing I3C committee should consist of U.S. and Canadian  managers and
      scientific staff who are currently active in lake research. This is to ensure a proper
      balance and perspective of studies at  both planning and implementation phases.

 3.    A stronger effort needs to be applied to the active cooperation of scientists  from
      both U.S. and Canadian research institutions.  Not since "Project Hypo" in 1970 have
      the U.S. and Canada formally been involved at a research level concerning problems
      on Lake Erie.

4.    Future studies should  be  more focused  on site-specific  and parameter-specific
      objectives.  This will allow the research effort  to be  more thorough and allow an
      intensive  effort if deemed necessary. In addition, it is more likely that the  project
      will be brought to completion with a thorough analysis of the data and a complete
      manuscript.

5.    The  open  lake annual  surveillance/monitoring  program should  be combined  with
      specific research efforts in order to take better  advantage of the  current database
      and sampling program. Since the major expense in supporting a whole lake program
      originates  from  boat  and  field staff expenditures, a combined effort  is  both
      economical and utilizes current facilities and expertise. Future programs should be
                                          169

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designed with this consideration in mind as such combined efforts generally lead to a
better surveillance/monitoring program.
                                     170

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Lam, D.C.L. and T.J. Simons.  1976.   Numerical computations  of advective and diffusive
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Lasenby, D.C.  1979.  Determinations of sediment and water uptake rates for oxygen in
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Lean, D.R.  1973. Phosphorus dynamics in lake water.  Science. 179:678-680.

Lean, D.R.  and  C. Nalewajko.   1976.  Phosphate   exchange and  organic phosphorus
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Lean, D.R.S. and F.R. Pick.  1981. Photosynthetic response of lake plankton to nutrient
      enrichment: a test for nutrient limitation. Limnol. and Oceanogr. 26(6): 1001-1019.

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      Oceanic and Atmospheric Administration, Ann Arbor, MI.

                                         177

-------
 Logan,  T.3.   1978.  Maumee River basin pilot watershed study.   PLUARG Task C.
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 Lorenz, R.C.  1981. The  ecology of Cladophora glomerata in western Lake Erie.  MS
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                                         178

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Neil, 3.H.  and M.B. Jackson.  1982.  Monitoring Cladophora growth conditions and the
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                                          179

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                                         180

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                                         181

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                                         182

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                                         183

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                               TABLE 1
                        EPA CRUISE SCHEDULE
Year
Cruise
  No.
Julian
 Date
Calendar
 Date
1978
  1
  2
  3
  4
  5
  6
  7
  8
  9
 10
              no cruise
138-147       May 18-May 27
156-166       June 5- June 15
174-182       June 23-Juiy 1
200-210       July 19-July 29
220-228       August 8-August 16
241-249       August 29-September 6
276-285       October  3-October 12
297-305       October  24-November 1
314-323       November 10-November 19
1979
 Wl
 W2
 W3
 2
 3
 4
 5
 6
 7
 8
 9
 10
016-018       January 16-January 18
058-060       February 27-March 1
086-088       March 27-March 29
107-110       April 17-April 20
135-146       May 15-May 26
163-172       June 12-June 21
192-200       July 11-July 19
212-216       July 31-August 4
235-247       August 23-September 4
254-264       September 11-September 21
275-287       October 2-October 14
311-320       November 7-November 16
                                T-l

-------
                                TABLE 2
                        CCIW CRUISE SCHEDULE
Year
Cruise
  No.
Julian
 Date
  Calendar
    Date
1978
             103
             104
             106
             108
             110
             111
             114
              149-157
              170-175
              194-199
              212-216
              231-235
              256-262
              273-277
              May 29-June 2
              June 19-June 24
              July 13-July 18
              July 31-August 4
              August 19-August 23
              September 13-September 19
              September 30-October 4
1979
 101
 103
 104
 106
 109
 112
 114
 116
114-116
135-138
161-165
184-187
204-208
235-237
267-271
289-291
April 24-April 26
May 15-May 18
June 10-June 14
July 3-July 6
July 23-July 27
August 23-August 25
September 24-September 28
October 16-October 18
                                 T-2

-------
                                 TABLE 3

         NEARSHORE CRUISE SCHEDULES FOR LAKE ERIE INTENSIVE
                     (3ULIAN DATES/JULIAN MID POINT)
               U.S.
            Western Basin
                         U.S.
                       Central Basin
                        U.S.
                      Eastern Basin
Cruise 2


Cruise 3


Cruise 4
Apr 14 - Apr 29
104-119/112

3un 26 - Jul 12
177-193/185

Aug23-Sepll
235-254/245

Oct 3 - Oct 17
276-290/283
May 18 - Jun 2
138-153/146

Jun 15 - Jun 29
166-180/173

Aug28-Sepll
240-254/247

Oct 8 - Oct 22
281-295/288
May 24 - 3un 17
144-168/156

Jun 21 - Jul 13
172-194/183

Aug 14 - Sep 1
226-244/235

Sep 14 - Oct 5
262-278/270
             Canadian
            Western Basin
                        Canadian
                       Central Basin
                       Canadian
                      Eastern Basin
1978

Cruise 1


Cruise 2


Cruise 3
Apr 16 - Apr 29
106-119/113

Aug 17 - Aug 23
229-235/232

Oct 12 - Oct 20
285-293/289
May 1 - May 24
121-144/133

Aug 26 - Sep 5
238-248/244

Oct 23 - Nov 3
296-307/302
May 22 - May 30
142-150/146

Aug 18 - Aug 29
230-241/236

Nov 1 - Nov 6
305-310/308
                                      T-3

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                TABLE 3 CONTINUED

NEARSHORE CRUISE SCHEDULES FOR LAKE ERIE INTENSIVE
          (JULIAN DATES/JULIAN MID POINT)

1979
Cruise 1
Cruise 2
Cruise 3
Cruise 4

1979
Cruise 1
Cruise 2
Cruise 3
Cruise 4
Cruise 5
Cruise 6
Cruise 7
U.S.
Western Basin
Mar 29 - Apr 15
088-105/097
Jul 25 - Aug 5
206-217/212
Sep 9 - Sep 23
252-266/259
Oct 9 - Oct 23
282-296/289
Canadian
Western Basin
Apr 17 - Apr 19
107-109/108
May 18 - May 30
138-150/144
Jul 4 - Jul 9
185-190/187
Aug 9 - Aug 19
219-231/226
Sep 23 - Sep 25
266-268/267
Oct 14 - Oct 16
287-289/288
Nov 22 - Nov 24
U.S.
Central Basin
Apr 11- Apr 25
101-115/108
Jul 1 1 - Jul 25
192-206/199
Aug 18 - Sep 1
230-244/237
Oct 2 - Oct 18
275-291/283
Canadian
Central Basin
Apr 20 - Apr 23
110-113/111
Aug 20 - Aug 23
232-235/233
Oct 28 - Nov 3
301-307/303




U.S.
Eastern Basin
May 15 - Jun 1
134-152/143
Jul 2 - Jul 18
183-199/191
Aug 20 - Sep 6
232-249/241
Oct 1 - Oct 31
274-304/289
Canadian
Eastern Basin
Apr 27 - May 16
117-136/126
Jun 16 - Jun 28
167-179/172
Jul 19 - Aug 5
200-217/209
Aug 27 - Sep 15
239-258/249
Sep 29 - Oct 19
272-292/282
Nov 5 - Nov 19
309-232/316

   326-328/327
                        T-4

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                           TABLE 4

                 NEARSHORE REACH DESIGN
No.
              Name
                         Description
 1
 2
 3
 it
 5
 6
 7
 8
 9
10
11
12
13
14
15
16
17
18
19
20
Colborne
Port Maitland
Nanticoke
Long Point Bay
Port Burwell
Port Stanley
Wheatley
Leamington
Colchester
Monroe
Maumee Bay
Locust Point
Sandusky Bay
Huron
Lorain
Cleveland
Fair port
Conneaut
Erie Harbor
Dunkirk
                                 Port Maitland to Buffalo
                                 Port Maitland
                                 Nanticoke to Port Maitland
                                 Long Point to Nanticoke
                                 Port Burwell to Long Point
                                 Rondeau to Port Burwell
                                 Point Pelee to Rondeau
                                 Kingsville to Point Pelee
                                 Amherstburg to Kingsville
                                 Detroit River to Maumee Bay
                                 Maumee Bay
                                 Cedar Point to Marblehead
                                 Sandusky Bay
                                 Sandusky Sub Basin
                                 Huron to Rocky River
                                 Rocky River to Euclid
                                 Euclid to Ashtabula
                                 Conneaut to Erie Harbor
                                 Erie Harbor
                                 Erie to Buffalo
                               T-5

-------
                                                      TABLE 5

                                    PRECISION ANALYSIS, BASED ON SPLIT SAMPLES
                                     Units for concentration are mg/1 except as noted.

                                WBNS: Western Basin Nearshore, CBNS: Central Basin Nearshore,
                                EBNS: Eastern Basin Nearshore, CNS: Canadian Nearshore,
                                USOL U.S. Open Lake, COL: Canadian Open Lake

                                                        1978
I
CT>
        Parameter
                                WBNS
    Estimated Standard Deviation
CBNS          EBNS          CNS
USOL
COL
Temperature
PH
Conductance
Alkalinity
Dissolved Oxygen
Turbidity
Chlorophyll a
Pheophytin
Tot. Sol. Phos.
Total Phosphorus
Sol. React. Phos.
Tot. Kjeldahl N
Ammonia N
Nitrate + Nitrite
Dis. React. Silica
Chloride
Fluoride
Sulfate
Calcium
Magnesium
Sodium
Potassium
.20
.058
7.1
1.26
.17
.54
.0034
ND
.0006
.001
.0005
.011
.0012
.008
.014
.11
.0172
.32
NA
NA
NA
NA
.11
.024
2.84
.68
.10
.20
.0006
.0003
.0015
.0022
.0005
.073
.007
.006
.022
.48
.0008
.95
1.56
.17
.23
.11
••• •
.089
10.0
3.0
	
.66
	
	
	
.011
.004
.097
.011
.04
.38
.53
.075
1.2
2.0
.40
.83
.23
0.0
.023
.75
.31
.07
.12
.0004
.0005
	
.0015
.0002
.041
.002
.002
.003
.12
	
.36
	
	
	
	
•MBW—
	
	
.30
	
	
	
	
	
.0003
.001
	
.0004
.003
.005
.12


.18
.05
	
.1
.04

-------
                                       TABLE 5 CONTINUED

                          PRECISION ANALYSIS, BASED ON SPLIT SAMPLES
                            Units for concentration are mg/1 except as noted.

                                               1978
Parameter
                       WBNS
    Estimated Standard Deviation
CBNS         EBNS          CNS
USOL
COL
Total Metals (in ug/1)
Aluminum
Cadmium
Chromium
Copper
Iron
Lead
Manganese
Nickel
Vanadium
Silver
Zinc
Arsenic
Mercury
Selenium
Dissolved Metals (in ug/1)
Aluminum
Cadmium
Chromium
Copper
Iron
Lead
Manganese
Nickel
Vanadium
Zinc
Silver

63.**
1.40
16.57
8.05
78.39
1.38
11.1*
18.12
1.50
0.19
6.21
0.75
0.05
9.26

26.63
0.11
0.07
0.73
3.41
0.88
0.50
0.45
2.7*
7.*6
0.02

282
2.*
7.2
8.1
21
17.*
3.*
5.8
39

77
.71
.13
.28

77
0.0
8.9
2.5
2.9
17
.2
3.6
*8
5.1


I
*_•»•» *
	 	 .1
	 	 . 1
	 	 ^2
89 	 .5
____ ____ .3
	 	 .1
	 	 .5
	 	 . 1

	 	 .3
	 	 	
^l^ 	
____ ____ ____


	 	 	
	 	 	


	 	 m2
	 	 	
	 	 	
	 	 	
	 	 	
	 	 	


-------
                                              TABLE 5 CONTINUED

                                 PRECISION ANALYSIS, BASED ON SPLIT SAMPLES
                                   Units for concentration are mg/1 except as noted.

                                                     1979
00
       Parameter
                              WBNS
    Estimated Standard Deviation
CBNS         EBNS         CNS
USOL
COL
Temperature
pH
Conductance
Alkalinity
Dissolved Oxygen
Turbidity
Chlorophyll a
Pheophytin
Tot. Sol. Phos.
Total Phosphorus
Sol. React. Phos.
Tot. Kjeldahl N.
Ammonia N
Nitrate + Nitrite
Dis. React. Silica
Chloride
Sulfate
Calcium
Magnesium
Sodium
Potassium
Total Metals (in UR/!)=
Aluminum
Cadmium
.03
.078
3.07
2.15
.14
1.38
.0030
ND
ND
.0010
.0004
.039
.0017
.0040
.010
ND
ND
6.66
7.27
0.11
0.01



0
.012
.68
.68
.00
.11
.0003
.00016
.0014
.0018
.0003
.122
.005
.0034
.026
.17
.55
.38
.12
.12
.03

18.2
.55
_
.089
10.0
3.0
	
.66
	
	
	
.011
.004
.097
.011
.04
.38
.53
1.2
2.0
.40
.83
.23

---_
	
.006
.02
.464
.26
.13
.12
.0003
.00012
____
.0024
.0004
	
.0015
.0026
.0064
.13
____

.....
___
	

......
— —
_
	
— —
.30
	
___
_ -

. ...
.0003
.001
----
.0004
.003
.005
.12
.18
.05
____
.1
.04

1
.1

-------
                                       TABLE 5 CONTINUED

                           PRECISION ANALYSIS, BASED ON SPLIT SAMPLES
                            Units for concentration are mg/1 except as noted.

                                               1979
Parameter                                Estimated Standard Deviation
                       WBNS          CBNS          EBNS          CNS           USOL         COL
Chromium
Copper
Iron
Lead
Manganese
Nickel
Vanadium
Zinc
Arsenic
Mercury
Selenium
Silver
Dissolved Metals (in ue/1)
Aluminum
Cadmium
Chromium
Copper
Iron
Lead
Manganese
Nickel
Vanadium
Zinc
g.O 	 	 .1
4.4 	 	 \2
29.7 89 ™ .5

4.9 	 	 [i
3.7 	 	 \5
6.7 	 	 .1
7.4 	 	 .3
.05 	 	 	
.06 	 	 	
0.0 	 	 	
.321 	 	 	

4.8 	 	 	
.10 	 	 	
1.7 	 	 	
4.3 	 	 	
8.7 	 	 .2

2.6 	 	 	
2,7 — •..— .... ....
2.1 	 	 	
5.9 	 	 	

-------
                                            TABLE 5 CONTINUED
a.   Data as published  in  MOE Data  Quality  Summary 1975, but appropriate to their  Lake Erie work, according
     to Don King.  Data is the 95  within run precision, and  may be expected to be higher than  data generated
     for this paper by a factor of about 2.7
b.   Data screened in  advance by  the  agency for large differences between values.   This has probably led to
     lower  standard deviations for some parameters,  but it  is  not  possible  to  say  which  parameters have  been
     affected.

c.   Precision data as  supplied  by the  agency.   Method based  on analytical  or  reagent blanks.   This method
     will  tend to give smaller standard deviations than the method used by TAT.

d.   Metals data for the western basin is combined for 1978 and 1979.

-------
                                      TABLE 6

PERFORMANCE OF THE LAKE ERIE LABS ON 13C ROUND-ROBIN STUDIES 21 THROUGH 29,
                            ORGANIZED BY PARAMETER

               Region codes:
                WBNS:  Western Basin Nearshore, CBNS: Central Basin Nearshore,
                EBNS: Eastern Basin Nearshore, CNS: Canadian Nearshore,
                USOL: U.S. Open Lake, COL: Canadian Open Lake

               Key to symbols used in chart:
                ok:  performance showed no serious deficiencies,
                ERR: performance erratic: some analyses high and others low,
                B-H: performance suggests high bias relative to other labs,
                B-L: performance suggests low bias relative to other labs.
                Labs that did not participate, or did not analyze enough
                samples to permit evaluation, have a blank entered for that
                parameter.
Parameter
PH


Conductance

Alkalinity


Dissolved Oxygen
Suspended Solids
Chlorophyll a
Pheophytin
Study
Number
21
22
27
21
27
21
22
27
No studies
No studies
No studies
No studies
WBNS CBNS

ok
ERR B-H

ERR B-H

B-L
B-H




Lake Erie
EBNS
ok
ERR
ok
ok
B-L
ok

ok




Region
CNS
ok
B-H
B-H
ok

ok
ok
ok




USOL
ok
ok
ERR
ok
B-H
ok
ok
ok




COL
ok
ok
ok
ok

ok
ok
B-L





-------
                                         TABLE 6 CONTINUED

              PERFORMANCE OF THE LAKE ERIE LABS ON I3C ROUND-ROBIN STUDIES 21 THROUGH 29,
                                      ORGANIZED BY PARAMETER
ro
Parameter
Tot. Sol. Phos.
Total Phosphorus


Sol. React. Phos.
Tot. Kjeldahl N.

Ammonia N
Nitrate+Nitrite

Dis. React. Silica


Tot. Org. Carbon

Chloride

Fluoride
Sulfate

Calcium

Magnesium

Sodium

Study
Number WBNS
No studies
24 ERR
27
28
No studies
22
27
27 ok
22 B-L
27 ok
22 B-H
25 ok
27 B-L
21
27
22
27
27
22
27
22
27
22
27
22
27
CBNS

ok
ok
ok


ERR
B-H

ERR
B-H
B-H
B-H

B-H
ok
ok

B-L
ok

ok

B-L

ERR
Lake Erie
EBNS


B-H
ERR


ok
B-L
B-H
ok

ERR
B-H
ok
B-H

ok




ok

ok
ERR
ERR
Region
CNS

ok



ok
ok

B-L
ok
ok



B-H
ok
ok

B-H

ok
ok
ok
ok
ok
ok
USOL

ok
B-L
ok

B-L
B-H
B-H
B-H
ok
ERR
ok
ok

ok
ok
ok
ok
ok
ok
ok
ok
ok
ok
B-H
B-H
COL


ok
B-L

ok
ok
ok
B-H
ok
B-L
ok
ok

ok
ok
ok

ok
ok
ok
ok
ok
ok
ok
ok

-------
                                           TABLE 6 CONTINUED


               PERFORMANCE OF THE LAKE ERIE LABS ON I3C ROUND-ROBIN STUDIES 21 THROUGH 29,
                                        ORGANIZED BY PARAMETER
I
I—'
CO
Parameter
Potassium

Total Metals:
Aluminum

Cadmium

Chromium

Copper

Iron

Lead

Manganese

Nickel

Vanadium

Zinc

Arsenic

Study
Number
22
27

21
23
21
23
21
23
21
23
21
23
21
23
21
23
21
23
21
23
21
23
21
26
WBNS CBNS

ERR


B-H

ok

B-H

ERR

B-H

B-H

B-H

B-H

B-L

ERR


Lake Erie
EBNS
B-L
B-L



ok
B-H

ERR

ERR
ok
B-L

ERR
ok
ERR
ok
ERR


ok
ok

ERR
Region
CNS
B-L
ok

ok

ERR
ok
ok
ok
ok
ERR
ok
ok
ok
ok
ok
ok
ok
ok
B-L
ok
ok
ok
ok
ok
USOL
ERR
ERR

ok
ok
ok
ok
ok
B-H
ERR
B-H
ok
B-H
ok
B-H
B-L
B-H
B-L
B-L
B-L
B-H
ok
B-L
ok
ERR
COL
ok
ok

ok
ok
ok
ok
ok
B-L
ok
ok
ok
ok
ok
ok
ok
ok
ok
B-L
ok
ok
ok
ERR

ok

-------
                                        TABLE 6 CONTINUED

          PERFORMANCE OF THE LAKE ERIE LABS ON I3C ROUND-ROBIN STUDIES 21 THROUGH 29,
                                     ORGANIZED BY PARAMETER
                        Study                              Lake Erie Region
Parameter               Number     WBNS       CBNS       EBNS       CNS        USOL      COL


Selenium                 Inadequate data
Mercury                 No studies
Silver                   No studies
Dissolved Metals:          No study for any dissolved metals except major ions

-------
                                  TABLE 7

  BIASES SUGGESTED BY ACROSS-BOUNDARY COMPARISONS OF FIELD DATA
     Although comparisons are made  pair-wise, the final determination of who is
biased can only be made when all pair-wise comparisons have been made.  For now, the
following information is offered.

     1.   Comparisons between USEPA-GLNPO and CLEAR

         EPA data for  conductance and pheophytin are consistently higher  than
         CLEAR data for these parameters.

         EPA Total Soluble Phosphorus is consistently lower than CLEAR data.

         EPA Total Phosphorus, Soluble Reactive  Phosphorus, and TKN tend to be
         lower, but these patterns are less clear-cut than the above.

         There is a considerable amount of  missing data for many parameters, with
         much of the missing data being USEPA-GLNPO.

     2.   Comparisons between Heidelberg College and CLEAR

         HC has higher specific conductance, lower Total Phosphorus, Total  Soluble
         Phosphorus, and turbidity than CLEAR. The last three differences are only
         apparent at the station at the outer edge of  the near shore zone, because
         they are  not pronounced enough to overcome  the great scatter in the very
         nearshore data.

         HC tends to have higher TKN, nitrate plus nitrite, DO, and Secchi depth
         values. These tendencies are less clear-cut than the ones above.

         The day-to-day  variability in the data is considerable, and no dates of
         sampling by the two agencies were closer than 1 week. These facts make
         bias discrimination rather hazy.

     3.   Comparisons between USEPA-GLNPO and Heidelberg College

         EPA Alkalinity is higher both years about 60% of the time.  It is never
         lower.

         In  1979, 4 of 6 USEPA-GLNPO pH  values are higher  (see below), and 4 of 6
         USEPA-GLNPO Nitrate plus Nitrite values are higher (but the other 2 are
         lower).

         In  1978, 8 of 14  USEPA-GLNPO pH values are lower, as are 4 of 4 Total
         Phosphorus, and 3 of 4 Total  Soluble Phosphorus. Five of  10 EPA chloride
         values are higher.

         Much of the USEPA-GLNPO data is missing.
                                         T-15

-------
                    TABLE 8

WESTERN BASIN THERMAL STRUCTURE DATA BY CRUISE
                 FOR 1978-1979
DATE
1978/USEPA
5/18-5/27
6/5-6/15
6/23-7/1
7/19-7/29
8/8-8/16
8/29-9/6
10/3-10/12
10/24-11/1
11/10-11/19
1979/USEPA
4/17-4/20
5/15-5/26
6/12-6/21
7/11-7/19
7/31-8/4
8/23-9/4
9/11-9/21
10/2-10/14
11/7-11/16
LIMNION

total
total
epi
meso
hypo
total
epi
meso
hypo
total
total
total
total
total
total

total
total
total
total
total
total
total
total
total
VOLUME
km3

25.1
25.1
22.4
2.6
0.1
25.1
23.7
0.7
0.0
24.4
24.3
24.1
23.9
23.8
23.9

24.8
25.0
24.8
25.0
25.1
25.1
24.8
24.4
24.2
THICKNESS
(m)

8.3
8.1
7.3
2.5
0.6
7.7
1.4
0.0
7.9
7.8
7.7
7.7
7.7

8.1
8.1
8.1
8.1
8.2
8.2
8.1
8.0
7.9
PERCENT
OF TOTAL T
VOLUME

100
100
89.2
10.4
0.4
100
97.1
2.9
0.0
100
100
100
100
100
100

100
100
100
100
100
100
100
100
100
EMPERATURE

16.4
17.5
21.4
21.0
N
23.4
22.8
N
24.3
23.5
17.7
10.8
8.0

5.5
12.8
19.4
21.8
23.6
21.3
21.4
18.5
8.2
                        T-16

-------
                   TABLE 9

CENTRAL BASIN THERMAL STRUCTURE DATA BY CRUISE
                 FOR 1978-1979
DATE
1978/CCIW
5/29-6/2



6/19-6/24



7/13-7/18



7/31-8/4



8/19-8/23



9/13-9/19



9/30-10/4



LIMNION

epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
VOLUME
(km3)

93.8
101.2
121.9
316.9
179.5
69.9
65.9
315.3
191.6
59.4
61.0
312.0
213.1
41.5
53.5
308.1
220.7
37.5
53.8
312.0
266.9
18.2
24.7
309.8
280.3
16.4
12.1
308.8
THICKNESS
(m)

5.7
6.6
8.6

10.9
4.5
4.7

11.7
4.0
4.8

13.2
2.9
4.4

13.5
2.6
4.1

16.3
1.8
3.4

17.1
1.8
2.7

PERCENT
OF TOTAL
VOLUME

29.6
31.9
38.5
100.0
56.9
22.2
20.9
100.0
61.4
19.0
19.6
100.0
69.1
13.5
17.4
100.0
70.7
12.0
17.3
100.0
86.1
5.9
8.0
100.0
90.8
5.3
3.9
100.0
TEMPERATURE

15.39
10.60
7.04

16.80
12.23
7.70

20.85
14.27
8.76

22.00
13.18
9.41

22.92
13.76
9.85

20.37
14.12
10.75

18.53
14.63
10.72

                       T-17

-------
                          TABLE 9 CONTINUED

         CENTRAL BASIN THERMAL STRUCTURE DATA BY CRUISE
                            FOR 1978-1979
DATE
1979/CCIW
4/24-4/26
5/15-5/18

6/10-6/14

7/3-7/6

7/23-7/27

8/23-8/25

9/20-9/28

LIMNION

total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
VOLUME
(km3)

313.7
190.7
56.1
68.6
315.4
266.2
21.7
27.4
315.3
247.7
28.9
37.7
314.3
162.8
125.9
26.6
315.3
266.7
27.8
20.9
315.4
309.4
3.1
1.2
313.7
THICKNESS
(m)

19.2
11.7
4.0
6.0
16.3
1.9
3.0
15.2
2.4
4.3
10.0
8.1
2.9
16.3
2.5
2.5
18.9
1.3
2.9
PERCENT
OF TOTAL
VOLUME

100.0
60.5
17.8
21.7
100.0
84.4
6.9
8.7
100.0
78.8
9.2
12.0
100.0
51.6
39.9
8.5
100.0
84.6
8.8
6.6
100.0
98.6
1.0
0.4
100.0
TEMPERATURE

3.83
8.83
6.73
5.03
12.87
11.11
8.83
16.51
13.87
10.00
22.36
16.07
9.66
20.40
17.75
11.70
18.57
17.77
16.60
10/16-10/18     total
312.0
19.1
100.0
10.21
                                   T-18

-------
                         TABLE 10



EASTERN BASIN THERMAL STRUCTURE DATA BY CRUISE FOR 1978-1979
DATE
1978/CCIW
5/29-6/2



6/19-6/24



7/13-7/18



7/31-8/4



8/19-8/23



9/13-9/19



9/30-10/4



LIMNION

epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
VOLUME
(km3)

15.6
92.6
52.8
161.0
67.6
42.0
50.7
160.3
68.7
44.6
45.9
159.2
82.5
35.3
41.5
159.3
94.6
29.1
35.6
159.3
105.8
16.8
34.1
156.7
109.4
17.6
31.2
158.2
THICKNESS
(m)

2.6
15.8
13.3

11.5
8.7
14.0

11.6
9.1
12.1

14.0
8.0
12.3

16.0
7.2
11.3

18.1
4.8
12.1

18.5
5.4
12.4

PERCENT
OF TOTAL
VOLUME

9.7
57.5
32.8
100.0
42.2
26.2
31.6
100.0
43.2
28.0
28.8
100.0
51.8
22.6
25.6
100.0
59.4
18.2
22.4
100.0
67.5
10.7
21.8
100.0
69.2
11.1
19.7
100.0
TEMPERATURE
(°C)

16.63
6.73
4.15

14.89
9.00
4.85

20.18
10.98
5.35

21.42
10.63
5.07

22.36
11.40
5.74

19.66
11.85
5.67

18.00
10.34
5.89

                             T-19

-------
                    TABLE 10 CONTINUED



EASTERN BASIN THERMAL STRUCTURE DATA BY CRUISE FOR 1978-1979
DATE
1979/CCIW
4/24-4/26
5/15-5/18



6/10-6/14



7/3-7/6



7/23-7/27



8/23-8/25



9/24-9/28



10/16-10/18



LIMNION

total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
VOLUME
(km3)

159.8
158.1
1.2
1.1
160.4
28.4
71.9
60.1
160.4
73.9
56.9
29.6
160.4
43.6
91.3
25.5
160.4
91.8
50.9
17.7
160.4
122.6
20.2
16.9
159.7
139.9
14.3
5.0
159.2
THICKNESS
(m)

27.1
26.8
3.4
5.6

4.8
12.8
15.0

12.5
12.6
11.5

7.4
17.1
10.5

15.6
12.1
9.6

20.8
7.4
9.0

23.7
8.1
7.1

PERCENT
OF TOTAL
VOLUME

100.0
98.5
.8
.7
100.0
17.7
44.8
37.5
100.0
46.1
35.5
18.4
100.0
27.2
56.9
15.9
100.0
57.2
31.7
11.1
100.0
76.8
12.6
10.6
100.0
88.0
9.0
3.0
100.0
TEMPERATURE
(°C)

1.79
4.15
6.57
4.30

13.30
9.04
4.84

16.23
10.49
5.33

23.26
14.08
5.32

20.40
12.22
5.53

18.33
14.21
6.88

13.62
10.64
6.14

                              T-20

-------
                    TABLE 11

WESTERN BASIN VOLUME WEIGHTED TOTAL PHOSPHORUS,
          SOLUBLE REACTIVE PHOSPHORUS
     TONNAGES AND CONCENTRATIONS, 1978-1979
DATE
1978/USEPA
5/18-5/27
6/5-6/15
6/23-7/1
7/19-7/29
8/8-8/16
8/29-9/6
10/3-10/12
10/24-11/1
11/10-11/19
LIMNION

total
total
epi
meso
hypo
total
epi
meso
hypo
total
total
total
total
total
total
TOTAL PHOSPHORUS
METRIC CONC.
TONS (ug/1)

367.72
588.34
663.26
83.64
ND
746.90
ND
ND
ND
ND
ND
ND
ND
ND
536.32

14.65
23.44
29.61
32.17
ND
29.88
ND
ND
ND
ND
ND
ND
ND
22.44
REACTIVE
METRIC
TONS

19.08
86.60
79.74
20.37
ND
100.10
206.66
6.17
ND
212.83
43.98
51.33
163.24
45.22
70.98
PHOSPHORUS
CONC.
(ug/1)

.76
3.45
3.56
7.83
ND
4.00
8.72
8.81
ND
8.79
1.81
2.13
6.83
1.90
2.97
                        T-21

-------
              TABLE 11 CONTINUED

WESTERN BASIN VOLUME WEIGHTED TOTAL PHOSPHORUS,
         SOLUBLE REACTIVE PHOSPHORUS
     TONNAGES AND CONCENTRATIONS, 1978-1979
DATE
1979/USEPA
HI 17-4/20
5/15-5/26
6/12-6/21
7/11-7/19
7/31-8/4
8/23-9/4
9/11-9/21
10/2-10/14
11/7-11/16
LIMNION

total
total
total
total
total
total
total
total
total
TOTAL PHOSPHORUS
METRIC CONC.
TONS (ug/1)

2537.78
504.50
649.51
468.75
664.65
882.52
992.00
746.40
795.21

102.33
20.18
26.19
18.75
26.48
35.16
40.00
30.59
32.86
REACTIVE
METRIC
TONS

171.37
64.00
ND
55.75
51.96
45.43
62.00
50.51
50.34
PHOSPHORUS
CONC.
(ug/1)

6.91
2.56
ND
2.23
2.07
1.81
2.50
2.07
2.08
                       T-22

-------
                        TABLE 12

CENTRAL BASIN VOLUME WEIGHTED TOTAL PHOSPHORUS, SOLUBLE
             REACTIVE PHOSPHORUS, TONNAGES
              AND CONCENTRATION, 1978-1979
DATE
LIMNION
TOTAL
PHOSPHORUS
METRIC CONC.
TONS (ug/1)
REACTIVE
PHOSPHORUS
METRIC CONC.
TONS (ug/1)
1978 (CCIW)
5/29-6/2



6/19-6/2*



7/13-7/18



7/31-8/4



8/19-8/23



9/13-9/19



9/30-10/4



epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
1245.2
1479.6
1754.5
4479.3
1975.9
913.5
904.4
3793.8
2281.8
915.3
1146.1
4343.2
ND
ND
ND
ND
2847.5
686.9
1095.6
4630.0
3752.2
304.6
412.6
4469.4
4254.5
331.9
257.7
4844.1
13.3
14.6
14.4
14.1
11.0
13.0
13.7
12.0
11.9
15.3
18.8
13.9
ND
ND
ND
ND
12.8
18.3
20.3
14.8
14.2
16.7
16.6
14.4
15.1
20.2
21.3
15.7
89.2
96.2
133.8
319.2
168.5
81.2
70.4
320.1
201.1
63.8
74.3
339.2
239.6
55.1
82.9
377.6
288.3
67.9
113.1
469.3
639.2
53.4
81.5
774.1
607.8
95.6
130.4
833.8
0.95
0.95
1.09
1.01
0.94
1.16
1.07
1.02
1.05
1.07
1.22
1.09
1.12
1.29
1.52
1.21
1.31
1.81
2.10
1.50
2.38
3.02
3.32
2.50
2.17
5.83
10.78
2.70
                           T-23

-------
                       TABLE 12 CONTINUED

    CENTRAL BASIN VOLUME WEIGHTED TOTAL PHOSPHORUS, SOLUBLE
   REACTIVE PHOSPHORUS, TONNAGES AND CONCENTRATION, 1978-1979
DATE
1979/CCIW
4/24-4/26
5/15-5/18



6/10-6/1*



7/3-7/6



7/23-7/27



8/23-8/25



9/24-9/28



LIMNION

total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
TOTAL
PHOSPHORUS
METRIC CONC.
TONS (ug/1)

5776.5
2759.7
803.1
973.7
4536.5
3351.8
341.2
416.4
4109.4
2618.2
447.3
778.3
3843.8
1684.8
1540.9
428.1
3653.8
2827.5
379.4
295.7
3502.6
4436.2
30.7
22.6
4489.5

18.41
14.47
14.31
14.20
14.38
12.59
15.69
15.21
13.03
10.54
15.39
20.54
12.23
10.35
12.24
16.08
11.59
10.66
13.85
15.29
11.10
14.34
9.84
18.68
14.31
REACTIVE
PHOSPHORUS
METRIC CONC.
TONS (ug/1)

1002.9
313.4
84.0
104.3
501.7
260.1
25.5
37.4
323.0
393.9
86.6
226.8
707.3
103.5
97.6
26.3
227.4
196.6
42.5
58.9
298.0
704.7
4.2
3.4
712.3

3.19
1.64
1.51
1.52
1.59
0.98
1.17
1.37
1.02
1.58
2.98
5.98
2.25
0.64
0.77
0.99
0.72
0.74
1.53
2.83
0.94
2.28
1.35
2.80
2.27
10/16-10/18  total
5827.0
18.67
2536.5
8.12
                                T-24

-------
                        TABLE 13

EASTERN BASIN VOLUME WEIGHTED TOTAL PHOSPHORUS, SOLUBLE
             REACTIVE PHOSPHORUS, TONNAGES
              AND CONCENTRATION, 1978-1979
DATE
LIMNION
TOTAL
PHOSPHORUS
METRIC CONC.
TONS (ug/1)
REACTIVE
PHOSPHORUS
METRIC CONC.
TONS (ug/1)
1978 (CCIW)
5/29-6/2



6/19-6/24



7/13-7/18



7/30-8/4



8/19-8/23



9/13-9/19



9/30-10/4



epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
234.4
1578.2
840.5
2653.1
998.4
571.6
726.3
2296.3
863.5
635.9
744.7
2244.1
ND
ND
ND
ND
1177.5
384.3
527.9
2089.7
1110.0
166.7
347.7
1624.4
1103.7
159.6
302.1
1565.4
15.1
17.0
15.9
16.5
14.7
13.6
14.3
14.3
12.5
14.2
16.2
14.1
ND
ND
ND
ND
12.4
13.2
14.8
13.1
10.5
9.9
10.2
10.4
10.1
9.0
9.7
9.9
21.3
171.4
227.5
420.2
106.5
42.9
113.8
263.2
97.4
62.3
92.5
252.2
87.5
42.9
75.6
206.0
175.3
46.7
83.5
305.5
168.4
31.1
97.8
297.3
128.7
23.7
56.5
208.9
1.37
1.85
4.30
2.61
1.57
1.02
2.24
1.64
1.42
1.39
2.01
1.58
1.06
1.21
1.82
1.29
1.85
1.61
2.35
1.92
1.57
1.87
2.80
1.90
1.18
1.34
1.81
1.32
                            T-25

-------
                    TABLE 13 CONTINUED

 EASTERN BASIN VOLUME WEIGHTED TOTAL PHOSPHORUS, SOLUBLE
REACTIVE PHOSPHORUS, TONNAGES AND CONCENTRATION, 1978-1979
DATE
LIMNION
TOTAL
PHOSPHORUS
METRIC CONC.
TONS (ug/1)
REACTIVE
PHOSPHORUS
METRIC CONC.
TONS (ug/1)
1979 (CHARLTON)
4/24-4/26
5/15-5/18



6/10-6/1*



7/3-7/6



7/23-7/27



8/23-8/25



9/24-9/28



10/16-10/18



total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
2720.9
2554.2
16.4
17.0
2587.6
354.9
1148.5
674.2
2177.6
881.4
638.4
330.2
1850.0
477.0
924.6
334.1
1735.7
887.6
476.3
192.1
1556.0
1027.9
168.3
147.2
1343.4
1255.9
188.8
54.6
1499.3
17.02
16.16
13.39
15.52
16.13
12.51
15.96
11.23
13.58
11.92
11.22
11.15
11.53
10.94
10.13
13.10
10.82
9.70
9.44
11.13
9.70
8.38
8.32
8.66
8.41
8.97
13.21
10.93
9.42
829.3
315.2
1.8
1.6
318.6
35.0
74.7
145.1
254.8
113.2
107.9
75.6
296.7
41.8
80.0
50.8
172.6
67.6
62.1
47.5
177.2
213.4
36.2
43.6
293.2
428.2
49.1
18.8
496.1
5.19
1.99
1.49
1.50
1.99
1.23
1.04
2.42
1.59
1.80
1.89
2.55
1.85
0.96
0.88
1.99
1.08
0.74
1.22
2.69
1.10
1.74
1.79
2.57
1.84
3.06
3.40
3.77
3.12
                             T-26

-------
                      TABLE 1*

 WESTERN BASIN VOLUME WEIGHTED NITRATE PLUS NITRITE
AND AMMONIA TONNAGES AND CONCENTRATIONS, 1978-1979
DATE
1978/USEPA
5/18-5/27
6/5-6/15
6/23-7/1
7/19-7/29
8/8-8/16
8/29-9/6
10/3-10/12
10/2
-------
                TABLE 14 CONTINUED

 WESTERN BASIN VOLUME WEIGHTED NITRATE PLUS NITRITE
AND AMMONIA TONNAGES AND CONCENTRATIONS, 1978-1979
DATE
1979/USEPA
4/17-4/20
5/15-5/26
6/12-6/21
7/11-7/19
7/31-8/4
8/23-9/4
9/11-9/21
10/2-10/14
11/7-11/16
LIMNION

total
total
total
total
total
total
total
total
total
NITRATE
METRIC
TONS

19780.23
19708.25
ND
8193.50
10814.59
6486.09
2378.07
2430.97
3543.61
+ NITRITE
CONG.
(ug/1)

797.59
788.33
ND
327.74
430.86
258.41
95.89
99.63
146.43
AMMONIA
METRIC CONC.
TONS (ug/1)

3332.13
666.75
ND
1065.25
785.88
ND
523.03
741.52
653.40

134.36
26.67
ND
42.61
31.31
ND
21.09
30.39
27.00
                         T-28

-------
                     TABLE 15

CENTRAL BASIN VOLUME WEIGHTED NITRATE PLUS NITRITE
    AND AMMONIA TONNAGES AND CONCENTRATIONS,
                     1978-1979
DATE
1978/CCIW
5/29-6/2
6/19-6/24
7/13-7/18
7/31-8/4
8/19-8/23
9/13-9/19
9/30-10/4
LIMNION

epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
NITRATE
METRIC
TONS

26086.7
24232.3
25311.3
75630.3
39347.9
16317.4
14511.5
70176.8
42036.4
12393.1
12139.1
66568.6
33661.5
7629.9
11111.5
52402.9
24643.8
6805.4
10820.4
42269.6
24969.4
2659.8
6142.7
33771.9
23339.2
1647.7
2130.2
27117.1
PLUS NITRITE
CONC.
(ug/1)

278.04
239.39
207.58
238.66
219.19
233.27
220.25
222.57
219.48
208.34
198.99
213.36
156.67
179.77
202.85
167.96
111.63
181.53
201.07
135.48
93.09
150.69
250.32
109.01
83.30
100.50
176.00
87.80
AMMONIA
METRIC
TONS

458.6
474.4
1637.6
2570.6
1274.9
1051.9
1091.0
3417.8
1296.9
973.7
1339.5
3610.1
591.5
450.4
789.2
1831.1
803.5
972.8
1525.9
3302.2
3087.1
398.7
456.7
3942.5
2950.7
525.7
473.6
3950.0
CONC.
(ug/1)

4.89
4.69
13.43
8.11
7.10
15.04
16.56
10.84
6.77
16.37
21.96
11.57
2.75
10.61
14.41
5.86
3.64
25.95
28.36
10.58
11.51
22.59
18.61
12.73
10.53
32.06
39.14
12.79
                         T-29

-------
                        TABLE 15 CONTINUED

        CENTRAL BASIN VOLUME WEIGHTED NITRATE PLUS NITRITE
            AND AMMONIA TONNAGES AND CONCENTRATIONS,
                              1978-1979
DATE
1979/CCIW
4/24-4/26
5/15-5/18
6/10-6/14
7/3-7/6
7/23-7/27
8/23-8/25
9/24-9/28
LIMNION

total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
NITRATE
METRIC
TONS

51081.0
24071.9
8258.4
11602.9
43933.2
31613.8
3347.9
4537.6
39499.3
33843.8
4859.2
8068.6
46771.6
12679.7
16725.4
6698.1
36103.2
28872.8
6412.1
5479.6
40764.5
21294.3
110.9
68.9
21474.1
PLUS NITRITE
CONG.
(ug/1)

162.83
126.24
147.20
169.25
139.29
118.75
153.99
165.69
125.28
136.25
167.25
212.89
148.81
77.86
132.88
251.61
114.50
108.27
230.59
262.71
129.25
68.83
35.49
56.85
68.45
AMMONIA
METRIC
TONS

3277.8
611.9
142.6
550.8
1305.3
4280.6
534.5
917.8
5732.9
2753.6
985.2
1733.6
5472.4
987.9
1591.9
686.6
3266.4
2539.1
662.5
517.4
3719.0
9506.0
70.1
130.5
9706.6
CONC.
(ug/1)

10.45
3.21
2.54
8.03
4.14
16.08
24.59
33.51
18.18
11.09
33.91
45.74
17.41
6.07
12.65
25.79
10.36
9.52
23.82
24.80
11.79
30.73
22.45
107.64
30.94
10/16-10/18   total
23526.7
75.39
7057.5
22.61
                                  T-30

-------
                    TABLE 16

EASTERN BASIN VOLUME WEIGHTED NITRATE PLUS NITRITE
   AND AMMONIA, TONNAGES AND CONCENTRATIONS,
                    1978-1979
DATE
CCIW/1979
5/29-6/2



6/19-6/24



7/13-7/18



7/31-8/4



8/19-8/23



9/13-9/19



9/30-10/4



LIMNION

epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
NITRATE
METRIC
TONS

2823.3
21797.8
12763.5
37384.6
13182.8
7739.6
12302.2
33224.6
10000.9
8434.5
11205.3
29640.7
7546.3
6585.8
11216.3
25348.4
7600.7
7138.6
10788.3
25527.6
9797.7
3706.2
10955.9
24459.8
10811.2
4253.4
10222.0
25286.6
PLUS NITRITE
CONC.
(ug/1)

181.47
235.38
241.49
232.20
194.90
184.13
242.67
207.26
145.58
189.99
244.10
186.19
91.51
186.53
270.51
159.12
80.36
245.50
303.39
160.25
91.44
222.98
314.16
156.09
98.9
241.1
328.0
159.8
AMMONIA
METRIC
TONS

40.9
593.4
500.5
1134.8
541.9
559.8
1052.4
2154.1
530.4
1438.6
1274.6
3243.6
753.8
903.0
478.9
1400.1
1006.5
157.5
106.8
1270.8
881.9
91.7
140.1
1113.7
613.3
82.6
99.7
795.6
CONC.
(ug/1)

2.63
6.41
9.47
7.05
8.01
13.32
20.76
13.44
7.70
32.24
27.77
20.37
9.14
25.58
11.55
8.79
10.64
5.42
3.00
7.98
8.24
5.52
4.03
•7.11
5.61
4.68
3.19
5.03
                        T-31

-------
               TABLE 16 CONTINUED

EASTERN BASIN VOLUME WEIGHTED NITRATE PLUS NITRITE
   AND AMMONIA, TONNAGES AND CONCENTRATIONS,
                    1978-1979
DATE
CCIW/1979
4/24-4/26
5/15-5/18
6/10-6/14
7/3-7/6
7/23-7/27
8/23-8/25
9/24-9/28
10/16-10/18
LIMNION

total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
NITRATE
METRIC
TONS

33655.0
32354.6
238.0
243.6
23836.2
2759.8
10562.2
13369.6
26691.6
10480.4
11119.1
6739.3
28338.8
4776.8
12621.2
5653.4
23051.4
10369.9
11811.5
4879.5
27060.9
11546.0
3519.8
4338.2
19404.0
15272.1
2310.3
1117.3
18699.7
PLUS NITRITE
CONC.
(ug/1)

210.58
204.65
194.91
223.25
204.71
97.28
146.74
222.61
166.41
141.79
195.49
227.53
176.68
109.55
138.23
221.70
143.71
112.93
232.04
276.06
168.71
94.18
173.97
255.33
121.50
109.13
161.63
223.74
117.46
AMMONIA
METRIC
TONS

1269.5
363.2
1.2
1.1
365.5
150.9
404.4
877.7
1433.0
817.9
1262.9
557.4
2638.2
170.9
1567.5
55.4
1793.8
560.9
243.4
52.9
857.2
717.4
196.9
72.3
986.6
1393.9
99.1
20.9
1513.9
CONC.
(ug/1)

7.94
2.29
1.00
1.00
2.28
5.32
5.62
14.61
8.93
11.07
22.20
18.82
16.45
3.92
17.17
2.17
11.18
6.11
4.78
2.99
5.34
5.85
9.74
4.25
6.18
9.96
6.93
4.18
9.51
                         T-32

-------
                     TABLE 17

CORRECTED CHLOROPHYLL a VOLUME WEIGHTED TONNAGES
           AND CONCENTRATIONS, 1978-1979
DATE

1978/USEPA
5/18-5/27
6/5-6/25
61 23-7 l\
7/19-7/29
8/8-8/16
8/29-9/6
10/3-10/12
10/24-11/1
11/10-11/19
LIMNION
WESTERN

total
total
epi
meso
hypo
total
epi
meso
hypo
total
total
total
total
total
total
CORRECTED
METRIC
TONS
BASIN

261.5*
174.95
340.70
12.51
ND
353.21
352.89
3.30
ND
356.19
455.87
377.89
233.98
316.30
239.00
CHLOROPHYLL a
CONC.
(ug/I)


10.42
6.97
15.21
4.81
ND
14.07
14.89
4.7
ND
14.60
18.76
15.68
9.79
13.29
10.00
                         T-33

-------
                TABLE 17 CONTINUED

CORRECTED CHLOROPHYLL a VOLUME WEIGHTED TONNAGES
           AND CONCENTRATIONS, 1978-1979
DATE

1979/USEPA
4/17-4/20
5/15-5/26
6/12-6/21
7/11-7/19
7/31-8/4
8/23-9/4
9/11-9/21
10/2-10/14
11/7-11/16
LIMNION
WESTERN

total
total
total
total
total
total
total
total
total
CORRECTED
METRIC
TONS
BASIN

109.86
265.50
ND
209.00
454.81
ND
455.58
316.22
279.51
CHLOROPHYLL a
CONC.
(ug/1)


4.43
10.62
ND
18.36
18.12
ND
18.37
12.96
11.55
                         T-34

-------
                TABLE 17 CONTINUED

CORRECTED CHLOROPHYLL a VOLUME WEIGHTED TONNAGES
           AND CONCENTRATIONS, 1978-1979
DATE

1978/USEPA
5/18-5/27
6/5-6/15
6/23-7/1
7/19-7/29
8/8-8/16
8/29-9/6
10/3-10/12
10/24-11/1
11/10-11/19
LIMNION
CENTRAL

total
total
epi
hypo
meso
total
epi
hypo
meso
total
epi
hypo
meso
total
epi
hypo
meso
total
total
total
total
CORRECTED
METRIC
TONS
BASIN

2720.16
1334.90
319.73
398.80
333.80
1052.33
346.14
433.30
323.30
1102.64
805.29
292.57
387.31
1485.17
779.57
271.52
238.18
1289.27
2254.31
2479.74
1917.06
CHLOROPHYLL a
CONC.
(ug/1)


8.61
4.37
2.46
5.00
3.17
3.34
2.92
4.32
3.47
3.53
4.68
4.20
5.56
4.77
3.86
5.26
4.20
4.16
7.30
8.03
6.40
                        T-35

-------
                TABLE 17 CONTINUED

CORRECTED CHLOROPHYLL a VOLUME WEIGHTED TONNAGES
           AND CONCENTRATIONS, 1978-1979
DATE

1979/USEPA
4/17-4/20
5/15-5/26
6/12-6/21
7/11-7/19
7/31-8/4
8/23-9/4
8/11-9/21
10/2-10/14
11/7-11/16
LIMNION
CENTRAL

total
epi
hypo
meso
total
total
epi
hypo
meso
total
epi
hypo
meso
total
total
epi
hypo
meso
total
total
total
CORRECTED
METRIC
TONS
BASIN

1776.40
962.59
303.22
193.42
1459.23
ND
822.21
100.43
74.01
996.65
1499.05
306.12
196.17
2001.34
ND
1964.95
65.22
66.13
2096.30
1871.30
2548.77
CHLOROPHYLL a
CONC.
(ug/1)


5.67
4.97
3.88
4.47
4.63
ND
3.53
2.04
2.31
3.17
6.84
4.67
6.47
6.35
ND
7.20
2.78
3.92
6.69
6.17
8.45
                         T-36

-------
                TABLE 17 CONTINUED

CORRECTED CHLOROPHYLL a VOLUME WEIGHTED TONNAGES
           AND CONCENTRATIONS, 1978-1979
DATE

1978
(USEPA)
5/18-5/27
6/5-6/15
6/23-7/1
7/19-7/29
8/8-8/16
8/29-9/6
10/3-10/12
10/24-11/1
11/10-11/19
LIMNION
EASTERN

total
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total

total
total
CORRECTED
METRIC
TONS
BASIN

860.7
660.7
102.2
152.5
146.9
401.6
210.6
71.8
116.3
398.7
178.3
52.9
44.5
275.7
197.0
49.9
38.3
285.2
ND
580.8
592.8
CHLOROPHYLL a
CONC.
(ug/1)


5.35
4.12
2.10
3.54
2.14
2.51
3.30
1.72
2.16
2.51
2.08
1.81
1.01
1.74
2.32
1.92
0.81
1.81
ND
3.67
3.75
                        T-37

-------
                 TABLE 17 CONTINUED

CORRECTED CHLOROPHYLL a VOLUME WEIGHTED TONNAGES
            AND CONCENTRATIONS, 1978-1979
DATE

1979
(USEPA)
5/15-5/26



6/12-6/21
7/11-7/19



7/31-8/4
8/23-9/4
9/11-9/21



10/2-10/14



LIMNION
EASTERN


epi
meso
hypo
total

epi
meso
hypo
total
ND
ND
epi
meso
hypo
total
epi
meso
hypo
total
CORRECTED
METRIC
TONS
BASIN


408.0
34.8
64.5
507.3
ND
167.0
20.2
38.2
225.4
ND
ND
312.0
46.5
43.1
401.6
333.6
26.1
22.0
381.7
CHLOROPHYLL a
CONC.
(ug/1)



3.22
3.89
2.60
3.17
ND
1.92
0.86
0.79
1.41
ND
ND
2.86
2.53
1.34
2.52
2.59
2.01
1.28
2.40
11/7-11/16
total
621.4
3.92
                           T-38

-------
                  TABLE 18

VOLUME WEIGHTED PARTICULATE ORGANIC CARBON,
    TONNAGES AND CONCENTRATION, 1978-1979
DATE
LIMNION
PARTICULATE
METRIC
TONS
ORGANIC CARB
CONC.
(ug/1)
CENTRAL BASIN
1978 (CCIW)
5/29-6/2
6/19-6/2*
7/13-7/18
7/31-8/4
8/19-8/23
9/13-9/19
9/30-10/4

epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total

49803.6
57213.0
57659.2
164675.6
59731.0
27818.0
30941.0
118490.0
72655.0
29300.3
37590.0
139545.3
91604.6
19649.1
26749.4
138003.1
113789.0
22807.2
31018.4
167614.6
152463.0
9901.1
13918.0
176281.1
158873.0
8669.8
3708.1
171250.9

530.9
565.2
472.9
519.6
332.7
397.7
469.6
375.8
379.2
492.6
616.2
447.3
426.4
462.9
488.3
442.3
515.4
608.4
576.4
537.2
568.4
560.9
567.2
569.0
566.8
528.8
306.4
554.6
                     T-39

-------
                    TABLE 18 CONTINUED

     VOLUME WEIGHTED PARTICULATE ORGANIC CARBON,
         TONNAGES AND CONCENTRATION, 1978-1979
                            PARTICULATE ORGANIC CARBON
DATE
LIMNION
METRIC
 TONS
 CONC.
(ug/1)
                       CENTRAL BASIN

1979/CCIW

4/24-4/26         total        113980.0        363.3

5/15-5/18         epi           98151.0        514.7
                 meso         26768.0        477.1
                 hypo         26392.0        384.9
                 total        151311.0        479.7

6/10-6/14         epi          112707.0        423.4
                 meso         9258.0        425.8
                 hypo         10665.0        389.4
                 total        132630.0        420.7

7/3-7/6           epi           63669.0        256.3
                 meso         9287.0        319.7
                 hypo         11522.0        304.0
                 total         84478.0        268.8

7/23-7/27         epi           42114.0        258.6
                 meso         34426.0        273.5
                 hypo         8171.0        306.9
                 total         84711.0        268.7

8/23-8/25         epi          100720.0        377.7
                 meso         9029.0        324.7
                 hypo         7456.0        357.5
                 total        117205.0        371.6

9/24-9/28         epi          121733.0        393.5
                 meso          898.0         287.6
                 hypo          489.0         403.5
                 total        123120.0        392.5

10/16-10/18       total        107459.0        344.3
                              T-40

-------
             TABLE 18 CONTINUED

VOLUME WEIGHTED PARTICULATE ORGANIC CARBON,
    TONNAGES AND CONCENTRATION, 1978-1979
DATE

1978 (CCIW)
5/29-6/2
6/19-6/24
7/13-7/18
7/30-8/4
8/19-8/23
9/13-9/19
9/30-10/4
PARTICULATE
LIMNION METRIC
TONS


epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
EASTERN BASIN

8616.6
49100.4
14486.5
72203.5
33517.9
18321.5
17920.7
69760.1
23619.1
14515.1
16284.3
54418.5
35681.6
12036.0
12456.8
60174.4
45918.7
10284.0
10973.6
67176.3
47794.1
6269.5
8874.5
62938.1
44755.8
5243.1
7472.9
57471.8
ORGANIC CARB
CONC.
(ug/1)


553.8
530.2
274.1
448.5
495.6
435.9
353.5
435.2
343.9
323.8
356.2
341.8
432.7
340.9
300.4
377.7
485.5
353.7
308.6
421.7
446.1
377.2
254.5
401.6
409.3
297.2
239.8
363.3
                      T-41

-------
                    TABLE 18 CONTINUED

     VOLUME WEIGHTED PARTICULATE ORGANIC CARBON,
         TONNAGES AND CONCENTRATION, 1978-1979
                           PARTICULATE ORGANIC CARBON
DATE
LIMNION
METRIC
 TONS
 CONC.
(ug/1)
1979 (CHARLTON)
                 total
                       EASTERN BASIN
              33995.0
5/15-5/18
6/10-6/14
7/3-7/6
7/23-7/27
8/23-8/25
9/24-9/28
10/16-10/18
epi
meso
hypo
total
14639.0
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
epi
meso
hypo
total
39818.0
330.7
225.3
40374.0
516.0
40712.0
14589.0
69940.0
15860.0
11405.0
6215.0
33480.0
13359.0
19959.0
4842.0
38160.0
25036.0
8819.8
2491.0
36346.8
32605.0
4881.0
3162.0
40648.0
39593.0
3329.0
861.0
33783.0
               212.7

               251.9
               270.8
               205.6
               251.7
                            565.6
                            242.9
                            436.0

                            214.6
                            200.5
                            209.8
                            208.7

                            306.4
                            218.6
                            189.9
                            237.9

                            272.6
                            173.3
                            140.9
                            226.6

                            265.9
                            241.2
                            186.1
                            254.5

                            211.5
                            232.9
                            172.4
                            212.2
                              T-42

-------
                    TABLE 19

MEAN TOTAL SUSPENDED SOLIDS CONCENTRATIONS (mg/1)
                 for 1978 (USEPA)
YEAR/CRUISE LIMNION
1978 2
3
4
5
6
7
8
9
10
epi
epi
hypo
epi
hypo
epi
hypo
epi
hypo
epi
hypo
epi
hypo
epi
hypo
epi
WB
4.05
8.77
7.63
9.36
ND
6.09
ND
7.16
ND
9.52
ND
19.31
ND
8.87
ND
23.16
BASIN
CB
2.42
1.39
1.74
1.36
1.61
1.05
2.10
1.46
2.48
2.50
2.23
5.32
ND
5.35
ND
4.82
EB
1.74
1.44
1.93
1.03
1.81
1.33
2.35
1.08
2.56
2.20
2.82
4.60
2.78
4.47
3.89
3.87
                        T-43

-------
                  TABLE 20

LAKE ERIE BASIN CONCENTRATIONS OF AREA WEIGHTED
     TRANSPARENCY MEASUREMENTS BY CRUISE
Date Year
1978
5/18-5/27
6/5-6/15
6/23-7/1
7/19-7/29
8/8-8/16
8/29-9/6
10/3-10/12
10/24-11/1
11/10-11/19
mean of means n=9
1979
4/17-4/20
5/15-5/26
6/12-6/21
7/11-7/19
7/31-8/4
8/23-9/4
9/11-9/21
10/2-10/14
11/7-11/16
mean of means n=9
Cruise
No.
1
2
3
4
5
6
7
8
9
10

1
2
3
4
5
6
7
8
9
10

Area-Weighted Transparency,
Secchi Disk (m)
Western Central Eastern
N.A.
2.50
2.02
2.00
2.06
2.68
1.94
1.58
2.08
0.65
1.95 .58
N.A.
0.67
1.81
1.44
3.03
2.38
1.91
1.29
1.59
0.96
1.68
N.A.
3.87
4.31
4.22
6.93
6.60
5.16
4.31
2.93
3.42
4.64 1.36
N.A.
1.28
2.82
3.49
5.80
5.78
N.A.
3.92
3.50
5.03
3.95
N.A.
3.96
4.22
6.87
5.95
7.03
4.65
3.20
3.63
3.16
4.74 1.51
N.A.
N.A.
3.16
3.07
6.91
N.A.
N.A.
5.82
4.26
3.67
4.48
                       T-44

-------
               TABLE 22

 LAKE ERIE BASIN RATIOS OF AREA WEIGHTED
TRANSPARENCY MEASUREMENTS (M) BY CRUISE
Date

5/18-5/27
6/5-6/15
6/23-7/1
7/19-7/29
8/8-8/16
8/29-9/6
10/3-10/12
10/24-11/1
11/10-11/19

4/17-4/20
5/15-5/26
6/12-6/21
7/11-7/19
7/31-8/4
8/23-9/4
9/11-9/21
10/2-10/14
11/7-11/16
Cruise
Year No.
1978 1
2
3
4
5
6
7
8
9
10
1979 1
2
3
4
5
6
7
8
9
10
Western
N.A.
1.00
1.00
1.00
1.00
1.00
1.00
1.00
1.00
1.00
N.A.
1.00
1.00
1.00
1.00
1.00
1.00
1.00
1.00
1.00
Central
N.A.
1.55
2.13
2.11
3.36
2.46
2.66
2.73
1.41
5.26
N.A.
1.91
1.56
2.42
1.91
2.43
N.A.
3.04
2.20
5.24
Eastern
N.A.
1.58
2.09
3.44
2.89
2.62
2.40
2.03
1.75
4.86
N.A.
N.A.
1.75
2.13
2.28
N.A.
N.A.
4.51
2.68
3.82
                   T-45

-------
                                                    TABLE 23


                    PRINCIPAL ION CONCENTRATIONS FOR THE OPEN LAKE CRUISES 1978-1979 (USEPA)
      Year
I
Ji>
CT>
Cruise
WB
CB
EB
WB
CB
EB
WB
CB
EB

1978








1979









1978
1979

2
3
4
5
6
7
S
9
10
2
3
4
5
6
7
8
9
10

4
5

19.0
17.4
17.2
16.2
16.4
17.0
14.9
14.4
12.8
24.0
17.9
	
	
15.3
15.9
13.0
13.9
12.6

10.0
7.8
Chloride
20.2
20.2
20.0
20.0
20.2
20.5
19.9
20.2
20.2
20.0
19.5
	
19.4
18.6
	
18.8
18.0
16.9
Sodium
9.6
9.6

20.9
20.8
20.9
20.6
21.5
21.1
19.9
20.8
20.5
_»__
20.5
	
	
	
	
19.7
19.6
19.4

10.0
9.1

22.4
21.6
22.1
20.7
25.2
18.3
19.9
	
18.9
23.7
29.5
	
	
20.1
	
__ __
19.9
19.3

8.7
7.4
Sulfate
23.8
23.3
23.0
22.8
23.8
24.4
22.8
	
23.6
23.7
23.9
-___
21.5
22.8
	
23.3
22.7
22.5
Magpesium
7.6
7.2

24.6
24.5
24.6
23.8
24.6
	
23.4
____
25.5
_.._»
25.8
__—
	
	
	
24.2
25.3
24.2

7.3
7.5

91.0
94.4
90.0
91.3
88.4
88.6
85.6
85.1
85.0
87.8
89.3
87.8
89.2
87.0
88.7
86.8
86.1
86.5

36.2
31.9
Bicarbonate
94.8
93.1
93.3
93.6
93.6
93.0
94.0
93.3
93.7
91.8
93.6
91.0
90.7
91.3
	
94.2
92.4
92.1
Calcium
35.9
33.8

94.8
94.5
93.3
94.8
96.2
94.1
94.6
96.2
96.2
«_»
94.2
94.3
92.8
	
____
96.2
96.1
95.6

34.4
34.1

-------
              TABLE 24
LAKE ERIE 1979 SEDIMENT SURVEY (USERA)
   CLUSTER MEANS (mg/kg dry weight)
CLUSTER
NO. AL
1
2
3
4
10,391
10,113
15,303
22,556
BA
65
54
83
121
CR
44
39
46
48
CU
25
26
34
36
FE
14,091
21,125
28,970
38,778
MN
639
498
601
762
HG
0.01
0.03
0.04
0.03
TI
287
111
123
173
VA
40
28
35
49
                T-47

-------
                                  TABLE 26

        SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                        IN THE WESTERN BASIN 1978
CRUISE
May 18-25
June 6-15
June 23-July 2
July 19-29
August 8-16
August 29-September 6
SPECIES
Melosira spp.
Tabellaria fenestrata
Closterium lunula
Unidentified pennate diatom

Cryptomonas erosa
Cryptomonas ovata
Tabellaria fenestrata
Cosmarium spp.
Unidentified non-green flagellate
Rhodomonas minuta

Cryptomonas ovata
Cryptomonas erosa
Mougeotia spp.
Ceratium hinrundinella*
Aphanizomenon flos-aquae*

Ceratium hinrundinella*
Cosmarium sp.
Aphanizomenon flos-aquae*
Cryptomonas erosa
Cryptomonas ovata

Aphanizomenon flos-aquae*
Coscinodiscus rothii*
Melosira spp.

Cosinodiscus rothii*
Aphanizomenon flos-aquae
Melosira spp.
Stephanodiscus niagarae
Oscillatoria spp.*
Anabaena spp.*
  %OF
  TOTAL
BIOVOLUME
  16.28
  15.11
   7.57

  32.74
  12.63
   9.20
   7.16
   6.11
   5.41

  14.57
  12.89
  12.84
  10.03
   7.30

  53.79
  11.99
   7.99
   7.11
   6.07

  49.50
  14.38
  11.88

  28.62
  14.13
  11.58
   9.28
   6.58
   5.14
                                       T-48

-------
                        TABLE 26 CONTINUED

       SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                      IN THE WESTERN BASIN 1978
CRUISE
October 3-12

October 24-November 1
November 7-16


SPECIES
Oscillatoria sp*
Melosira spp.
Coscinodiscus rothii*
Anabaena spp.*
Stephanodiscus niagarae*
Pediastrum simplex*
Oscillatoria spp.*
Melosira spp.
Anabaena spp.*
Mougeotia spp.
Oscillatoria spp.*
Melosira spp.
Coscinodiscus rothii*
Mougeotia spp.
Tabellaria fenestrata
Dinobryon spp.
%OF
TOTAL
BIOVOLUME
18.60
17.82
12.32
6.85
6.40
6.16
31.04
16.40
8.32
5.68
26.73
15.04
6.42
5.88
5.73
5.06
*Eutrophic species
                                 T-49

-------
                                  TABLE 27
        SEASONAL RELATIVE ABUNDANCE OF COMMON (-5%) SPECIES
                        IN THE WESTERN BASIN - 1979
CRUISE
SPECIES
  %OF
  TOTAL
BIOVOLUME
March 27-29
April 17-20
May 15-26

July 11-19
July 31-August 4
Fragilaria spp.
Tabellaria fenestrata
Stephanodiscus niagarae*
Meloslra spp.
Stephanodiscus binderana
unidentified centric diatom
unidentified non-green flagellate
Diatoma tenue var. elongatum*
Asterionella formosa
Fragilaria crotonensis

Melosira spp.
Diatoma tenue var. elonatum*
Stephanodiscus binderana*
Tabellaria fenestrata
Stephanodiscus niagarae*

No data

Aphanizomenon flos-aquae*
Ceratium hirundinella*
Cryptomonas erosa
Coscinodiscus rothii*
Cryptomonas ovata

Aphanizomenon flos-aquae*
Coscinodiscus rothii*
Anabaena spp.*
Melosira spp.
Anabaena spiroides*
  17.02
   9.71
   9.59
   8.51
   7.92
   7.54
   6.90
   6.00
   5.77
   5.01

  29.54
  15.49
  14.18
   7.49
   6.24
  18.43
  16.82
  11.57
   6.70
   6.14

  23.10
  19.48
   9.95
   8.18
   7.49
                                      T-50

-------
                           TABLE 27 CONTINUED

        SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                        IN THE WESTERN BASIN - 1979
CRUISE
SPECIES
  %OF
  TOTAL
BIOVOLUME
September 11-21
October 4-
November 7-16
Meloslra spp.
Stephanodiscus niagarae*
Coscinodiscus rothii*
Aphanizomenon flos-aquae*
Anabaena spiroides*
Anabaena spp.*

Stephanodiscus niagarae*
Melosira spp.
Aphanizomenon flos-aquae*
Gryosigma spp.
Pediastrum simplex*
Stephanodiscus binderana*

Melosira spp.
Stephanodiscus binderana*
Stephanodiscus niagarae*
Aphanizomenon flos-aquae*
Diatoma tenue var. elongatum*
  16.71
  12.54
  12.21
  10.93
   7.66
   6.38

  22.73
  12.93
  11.96
   8.10
   5.32
   5.13

  38.45
  17.82
  14.59
   6.01
   5.07
*Eutrophic species
                                      T-51

-------
                                  TABLE 28


        SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                        IN THE CENTRAL BASIN - 1978
CRUISE
SPECIES
  %OF
  TOTAL
BIOVOLUME
May 18-25
June 6-15
June 23-July 2
July 19-29
August 8-16
Asterionella formosa
Melosira spp.
Fragilaria crotonensis
Stephanodiscus niagarae*
Stephanodiscus binderana*

Unidentified non-green flagellate
Unidentified pennate diatom
Rhodomonas minuta
Tabellaria fenestrata
Cryptomonas erosa
Fragilaria crotonensis

Fragilaria crotonensis
Cryptomonas erosa
Unidentified non-green flagellate
Stephanodiscus niagarae*
Rhodomonas minuta
Cryptomonas ovata
Tabellaria fenestrata

Ceratium hirundinella*
Aphanizomenon flos-aquae*
Stephanodiscus niagarae*
Cosmarium spp.

Ceratium hirundinella*
Aphanizomenon flos-aquae*
Oedogonium spp.
Unidentified coccoid green
Scenedesmus bijuga*
  31.92
  18.08
   6.44
   6.40
   6.39

  27.95
  13.06
   9.48
   8.70
   8.54
   7.25

  15.72
  11.42
  12.21
   9.64
   8.37
   7.32
   6.77

  29.34
   8.00
   7.59
   5.10

  21.93
  13.30
   9.61
   5.49
   5.13
                                       T-52

-------
                           TABLE 28 CONTINUED

        SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                       IN THE CENTRAL BASIN - 1978
CRUISE
SPECIES
  %OF
  TOTAL
BIOVOLUME
August 29-September 6
October 3-13
October 24-November 1
November 7-16
Oocystis borgei*
Aphanizomenon flos-aque*
Unidentified coccoid green
Scenedesmus bijuga*
Oocystis spp.
Oocystis pusilla

Stephanodiscus niagarae*
Cryptomonas erosa
Aphanizomenon flos-aque*
Unidentified pennate diatom
Oocystis borgei*
Oocystis spp.

Cryptomonas erosa
Oscillatoria spp.*
Cryptomonas ovata
Oocystis borgei*
Stephanodiscus niagarae*
Unidentified coccoid green

Cryptomonas erosa
Cryptomona ovata
Oscillator ia spp.*
Stephanodiscus niagarae*
  17.68
  11.53
   8.79
   8.79
   7.60
   5.75

  12.53
   6.56
   5.81
   5.71
   5.60
   5.22

  13.85
  11.44
   9.74
   7.80
   6.55
   5.53

  17.10
  12.21
  11.79
   6.22
*Eutrophic species
                                      T-53

-------
                                  TABLE 29
        SEASONAL RELATIVE ABUNDANCE OF COMMON (-5%) SPECIES
                        IN THE CENTRAL BASIN - 1979
CRUISE
SPECIES
  %OF
  TOTAL
BIOVOLUME
March 27-29
April 17-20

May 15-26
July 11-19
3uly 31-August
September 11-21
Stephanodiscus niagarae*
Fragilaria spp.
Stephanodiscus binderana*
Unidentified centric diatom
Gryrosigma spp.

No data

Stephanodiscus niagarae*
Melosira spp.
Tabellaria fenestrata
Diatoma tenue var. elongatum*
Rhodomonas minuta
Unidentified non-green flagellate
Fragilaria crotonensis

Ceratium hirundinella*
Coelastrum reticulatum
Staurastrum paradoxium*
Cryptomonas erosa
Rhodomonas minuta
Oocystis borgei*

Represents  only the western portion
 of the basin
Ceratium hirundinella*
Aphanizomenon flos-aque*
Fragilaria crotonensis
Coscinodiscus rothii*

Stephanodiscus niagarae*
Aphanizomenon flos-aque*
Pediastrum  simplex*
Ceratium hirundinella*
  36.03
  10.81
   8.89
   7.59
   7.32
  15.55
  12.29
  11.26
  10.65
  10.47
   7.09
   5.99

  28.53
  14.67
   7.21
   5.81
   5.53
   5.08
  25.30
  22.98
  19.28
   8.19

  28.05
   8.36
   7.39
   7.28
                                       T-54

-------
                          TABLE 29 CONTINUED

        SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                      IN THE CENTRAL BASIN - 1979
                                                                %OF
                                                                TOTAL
CRUISE                 SPECIES                               BIOVOLUME
October 4-10             Stephanodiscus niagarae*                   30.63
                        Melosira spp.                             18.40
                        Aphanizomenon flos-aquae*                  8.23

November 7-16           Melosira spp.                             41.76
                        Stephanodiscus niagarae*                   29.97
                        Stephanodiscus binder ana*                  14.69
*Eutrophic species
                                    T-55

-------
                                  TABLE 30
        SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                        IN THE EASTERN BASIN - 1978
CRUISE
SPECIES
  %OF
  TOTAL
BIOVOLUME
May 18-25
June 6-15
June 23-July 2
July 19-29
August 8-16
August 29-September 6
Stephanodiscus binderana*
Asterionella Formosa
Melosira spp.
Stephanodiscus niagarae*
Fragilaria crotonensis

Unidentified pennate diatom
Cryptomonas erosa
Tabellaria fenestrata
Closterium  lunula

Cryptomonas erosa
Fragilaria crotonensis
Rhodomonus minuta
Unidentified flagellate
Asterionella formosa
Tabellaria fenestrata

Anabaena flos-aquae*
Oocystis borgei*
Ceratium hirundinella*
Staurastrum paradoxum
Cryptomonas ovata

Scenedesmus bijuga*
Oocystis borgei*
Ceratium hirundinella*
Unidentified coccoid green

Oocystis borgei*
Oocystis sp.*
Scenedesmus bijuga*
Unidentified coccoid green
  20.45
  17.8
   9.6
   9.6
   9.2

  15.7
  14.0
  11.5
   5.3

  16.4
  14.4
  11.7
  11.2
   9.8
   6.6

  18.7
  17.0
  13.0
   7.4
   5.1

  28.4
  15.1
   8.3
   5.5

  24.9
  16.7
  11.1
   8.0
                                       T-56

-------
                           TABLE 30 CONTINUED

        SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                       IN THE EASTERN BASIN - 1978
CRUISE
SPECIES
  %OF
  TOTAL
BIOVOLUME
October 3-12
October 24-November 1
November 7-16
Oocystis borgei*
Oocystis sp.
Tabellaria fenestrata
Staurastrum paradoxum*
Unidentified coccoid green
Unidentified pennate diatom

Tabellaria fenestrata
Stephanodiscus niagarae*
Cryptomonos erosa
Oocystis borgei*
Cryptomonas ovata
Staurastrum paradoxum*

Cryptomonas erosa
Tabellaria fenestrata
Staurastrum paradoxum*
Cryptomonas ovata
Cosmarium sp.
  13.9
  11.1
  10.*
  8.6
  6.3
  5.8

  21.9
  14.7
  13.3
  7.2
  7.0
  5.1

  18.1
  15.2
  12.8
  10.6
  5.2
*Eutrophic species
                                     T-57

-------
                            TABLE 31
       SEASONAL RELATIVE ABUNDANCE OF COMMON (»5%) SPECIES
                    IN THE EASTERN BASIN - 1979
CRUISE
March 27-29
AprU 17-20
May 15-26
July 11-19


July 31-August 4
September 11-12
October 4-10

November 7-16
SPECIES
Stephanodiscus niagarae*
Unidentified centric diatom
No data
No data
Oocystis borgei*
Ceratium hirundinella*
Rhodomonas minuta
Fragilaria crotonensis
Cryptonoma erosa
No data
Ceratium hirundinella*
Staurastrum paradoxum*
Oocystis spp.
Cosmarium spp.
Coelastrum microporum*
Stephanodiscus niagarae*
Ceratium hirundinella*
Microcystis aeruginosa
Staurastrum paradoxum*
Stephanodiscus niagarae*
Cryptomonas erosa
%OF
TOTAL
BIOVOLUME
78.33
8.17


19.31
17.49
11.06
7.30
5.70

27.78
10.02
8.72
7.50
6.78
35.73
10.54
10.49
5.02
66.87
5.24
*Eutrophic species
                                T-58

-------
                                        TABLE 34

                 RATIONALE FOR MONITORING DISSOLVED SUBSTANCES*
 Parameter
    Sources
   Harmful/Beneficial Effects
TDS
Carbonates, bicarbonates,
chlorides, sulfates,
phosphates, nitrates of
calcium, sodium, magnesium,
potassium, iron and manganese
Concentrations  exceeding 500 mg/1
are  reported  to  be unpalatable,
not capable  of quenching  thirst,
having possible laxative  action on
new  users,  causing foam  in   boilers,
interfering with clearness, color or  taste
of a finished food or beverage  product,
accelerating      corrosion,      causing
hindrance to crop production and  most
importantly influencing  the  toxicity of
heavy metals and  organic compounds to
fish and other aquatic life.
Conductivity
Chlorides
Sulfate
Major ionic species present
in the water
Widely used in water treatment,
deicing highways, agricultural
salts, human and animal sewage
and industrial effluents
(paper works, galvanizing
plants, water softening, oil
wells and petroleum refineries)
Leachings from gypsum and
abandoned coal mines, as
well as numerous industrial
wastes (tanneries, sulfate-
pulp mills, textile mills, etc.)
At  higher  concentrations  can be
harmful to  living organisms due to the
increase  in  osmotic  pressure, causing
water  to  be drawn from  the gills and
other delicate external organs, resulting
in cell damage or death.

In drinking water may be injurious to
people  suffering  from  heart  or
kidney diseases.   The USPHS drinking
water  standards  of 1962 recommended
that chloride levels not exceed 250
mg/1.  Appear to exert a significant
effect on the rate of corrosion of  steel
(45  mg/1), aluminum  (5-300  mg/1) and
stainless steel (10.0 mg/1).

Appear to increase corrosiveness of
water  on  concrete.  Less  toxic to
plants than chloride.
                                           T-59

-------
                                  TABLE 34 CONTINUED

                RATIONALE FOR MONITORING DISSOLVED SUBSTANCES*
Parameter
    Sources
   Harmful/Beneficial Effects
Sodium
Very common element of the
earth's crust (2.83%).
Leached from the soils or
from industrial wastes
May be harmful to people with cardio-
vascular, renal  and  circulatory
diseases at levels of approximately
200 mg/1.
Magnesium
Potassium
Calcium
Very common element of the
earth's crust (2.1%).  Also
a constituent of light alloys,
used frequently for
metallurgy and in the
manufacturing of electrical
and optical apparatus

Constitutes 2.4% of the
earth's crust, is extremely
soluble and one of the
most active metals
Among the most commonly
encountered substances in
water. Originates from
the earth's crust, soil
leachates, sewage, and
industrial wastes
At  high  concentrations, Mg has a
laxative  effect  but  it  has  such
an  unpleasant  taste that people
would  stop  drinking  it before
it reached toxic levels.
If  the  total  concentration  of
potassium   and  sodium  exceeds
50  mg/1  there  may  be  foaming
in    boilers.      Critical   levels   of
potassium must  be  5-10  times higher
than  the   sodium  critical  level  for
people    with    heart    and    renal
problems.    Potassium  on  the  other
hand   is  more   toxic   to  fish   and
shellfish  than  calcium,   magnesium
and sodium.

High  concentrations  of Ca  are
associated with  low  incidence of
heart attacks, inhibits corrosion of
cast iron and steel and is desirable
in  irrigation water,  essential for
normal  plant  growth and  reduces  the
toxicity  of   lead,  zinc  and  aluminum
to fish.   Ca  in  excess can  result in
formation of body,  kidney  or bladder
stones,    be   a   disadvantage   for
washing,  bathing,   laundrying,  form
incrustations   on    cooking   utensils
and    water   heaters,   result   in
precipitation   and   curds   when  using
soaps,      and      upset       certain
fermentation processes.
                                           T-60

-------
                                  TABLE 3* CONTINUED

                 RATIONALE FOR MONITORING DISSOLVED SUBSTANCES*
Parameter
    Sources
   Harmful/Beneficial Effects
Alkalinity
pH
Alkalinity is caused by
the presence of carbonates,
bicarbonates, hydroxides
and to a lesser extent by
berates, silicates,
phosphates and organic
substances. The alkalinity
of water can be increased by
the addition of municipal
sewage and many industrial
wastes

Hydrogen ions, industrial
acid and alkaline wastes.
Alkalinity  in  itself  is  not  con-
sidered harmful to humans but it is
generally associated  with high  pH
values,  hardness   and  excessive
solids, ail  of  which  may be dele-
terious.  High alkalinities are not
desired in the production of food and
beverages and may be detrimental for
irrigation water.  It is desirable to
have  high  alkalinities to inhibit
corrosion.

pH of  the water  affects taste (sour
 3.9),    corrosivity    (dissolves    lead
pH    8.0),    efficiency    of    chlor-
ination,   (diminishes   with   increasing
pH,   advantageous  if  pH   7),   and
efficiency   of    treatment   processes
such   as  coagulation  and   industrial
applications.        PH    controls   the
degree   of   dissociation   of    many
substances (ammonia,  etc.)  and  since
undissociated       compounds      are
frequently  more  toxic  than the  ionic
forms, pH may be  important in  areas
with effluents of toxic materials.
*From McKee and Wolf, 1974
                                           T-61

-------
ro
                                                  TABLE 35



            LAKE ERIE 1978-1979 NEARSHORE PRINCIPLE ION REACH CONCENTRATIONS (mg/1) AND STATISTICS
Reach
number/name
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
11.
12.
13.
14.
15.
16.
17.
18.
19.
20.
X
SD
SE
%SE
n
Colborne
Port Maitland
Nanticoke
Long Point Bay
Port Burwell
Port Stanley
Wheatley
Leamington
Colchester
Monroe
Maumee
Locust Point
Sandusky Bay
Huron
Lorain
Cleveland
Fairport
Conneaut
Erie Harbor
Dunkirk
21.48
2.88
0.64
3.0
20
Cl
19.9
23.2
20.1
20.0
19.8
18.9
18.4
21.4
23.3
18.6
27.5
17.8
24.4
19.6
18.9
26.3
25.4
20.7
24.6
20.8
35.51
20.74
6.25
17.61
11
so,


29.4
45.4
28.2
95.8
27.8
29.0
30.1
26.0
25.8
26.4
26.7
97.06
10.55
2.36
2.43
20
Alk
106.2
118.9
109.6
113.5
113.7
105.1
99.6
89.5
89.0
88.4
101.5
92.3
95.4
86.8
88.9
89.7
87.9
87.0
89.5
88.7
11.41
2.60
0.78
6.87
11
Na


11.3
15.9
9.9
12.3
10.6
10.3
15.4
13.5
8.7
9.6
8.0
9.04
1.77
0.53
5.86
11
Mg


8.9
12.3
8.63
12.8
7.9
8.0
8.3
7.8
8.2
8.2
8.4
1.68
0.41
0.12
7.14
11
K


1.0
2.1
1.2
2.1
1.1
1.6
2.0
1.6
2.0
2.0
1.8
34.96
6.89
2.07
5.95
11
Ca


33.5
38.9
33.0
51.3
32.9
36.5
37.8
37.9
27.0
27.4
28.4
310
40
9
2.9
20
Cond pH
umhos/cm
299
359
303
304
286
285
282
278
281
282
387
296
436
286
304
328
314
294
303
293





8.3
8.2
8.2
8.2
8.5
8.3
8.2
8.0
7.9
8.5
8.5
8.4
8.6
8.3
8.3
8.2
8.4
8.4
8.4
8.4






-------
                       TABLE 36

PRINCIPAL ION COMPARISON OF 1970 OPEN LAKE DATA (CCIW) WITH
         1978-1979 OPEN LAKE AND NEARSHORE DATA

K Mg
Ca
Na
so,
HCO3
Cl
1970 ANNUAL MEANS
X
SD
SE
%SE
N
X
SD
SE
%SE
N
1.28 7.59
0.09 0.20
0.03 0.08
2.6 1.0
7 7
7.63



NA 2
37.19
0.94
0.36
1.0
7
11.82
0.25
0.09
0.8
7
24.01
0.61
0.23
1.0
7
111.56
1.68
0.63
0.6
7
1978-1979 STUDY MEANS
34.4 9.37 23.25



2
1978-1979 MEAN OF STUDY
X
SD
SE
%SE
N
1.68 9.04
0.41 1.77
0.12 0.53
7.14 5.86
11 11
34.96
6.89
2.07
5.95
11



2
NEARSHORE
11.41
2.60
0.78
6.87
11
1.34
0.42
1.8
10
REACH
35.51
20.74
6.25
17.61
11



NA
MEANS
97.06
10.55
2.36
2.43
20
23.60
0.61
0.23
1.0
7
18.84
1.38
0.36
1.9
15

21.48
2.88
0.64
3.0
20
                           T-63

-------
                                TABLE 40

    COMPARISON OF TROPHIC STATUS OF LAKE ERIE'S NEARSHORE ZONE
                 USING ANNUAL REACH MEANS, 1978-1979
REACH GROUP* SECCHI
NO. (m)
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
A
A
A
A
A
A
A
B
C
A
A
A
A
A
A
A
A
A
A
A
3.2
2.0
2.2
2.7
2.8
1.6
2.1
1.0
0.7
0.7
0.5
0.7
0.3
1.1
1.9
2.3
2.1
2.8
1.7
2.7
CHLa
ug/1
2.4
5.0
2.2
2.0
2.8
4.2
6.6
6.0
2.9
27.3
36.1
18.4
61.7
13.1
6.9
6.8
6.8
4.0
19.5
4.0
TP
ug/1
12.3
51.3
14.7
12.7
18.2
18.8
22.2
27.5
24.6
100.7
179.6
97.1
158.3
77.9
55.7
54.7
40.3
23.6
64.2
23.6
CTI**
4.3
11.6
5.8
4.7
5.6
8.9
9.2
10.7
7.8
37.9
56.4
32.6
81.1
22.2
13.3
12.3
11.2
6.8
21.8
6.9
TROPHIC
STATUS***
O/M
E
M
M
M
M
E/M
E/M
M
E
E
E
E
E
E
E
E
M
E
M
*A  High chlorophyll a and low secchi depth
B Low chlorophyll a and high secchi depth
C High inorganic turbidity

**Composite Trophic Index (Gregor and Rast 1979)

***E = Eutrophic
  E/M = Eutrophic/Mesotrophic
  M = Mesotrophic
  O/M = Oligotrophic/Mesotrophic
  O = Oligotrophic
                                   T-64

-------
                                TABLE 41

 SUMMARY OF TROPHIC STATUS DATA FOR LAKE ERIE NEARSHORE WATERS,
                           SUMMER 1972-1973*
REACH GROUP* *SECCHI
NO. (m)
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
31
32
33
A
A
A
A
A
A
A
C
C
C
C
C
C
A
A
A
A
A
A
C
-
A
_
_
_
_
_
_
_
_
-
_
—
3.7
3.6
4.0
3.0
3.5
4.0
3.9
2.9
2.7
2.3
1.6
1.6
1.1
2.6
2.8
2.9
2.0
1.4
1.8
1.4
_
2.0
_
_
-
_
_
_
_
_
_
_
—
CHLa
ug/1
2.3
2.4
2.6
3.7
2.2
2.0
1.9
1.7
1.7
2.3
2.2
3.3
3.6
3.4
3.9
4.8
5.6
10.3
7.2
2.8
-
7.5
_
_
_
_
_
_
_
_
-
-
—
TP
ug/1
18
23
19
34
17
20
21
15
17
21
19
28
24
19
20
19
32
48
42
34
-
42
60
30
40-100
30
INSF
INSF
INSF
INSF
INSF
INSF
23
CTI***
4.5
5.1
4.5
7.5
4.5
4.3
4.4
3.2
3.6
4.5
4.7
6.3
6.9
6.2
6.3
6.6
9.9
16.2
12.3
6.8
-
11.9
-
-
-
-
-
-
-
-
-
-
—
TROPHIC
STATUS****
O/M
M
O/M
M
O/M
O/M
O/M
O/M
O/M
O/M
M
M
M
M
M
M
E/M
E
E
M

E











*Taken from Gregor and Rast, 1979

**A High chlorophyll a and low secchi depth
 B  Low chlorophyll a and high secchi depth
 C  High inorganic turbidity

***Composite Trophic Index
(Gregor and Rast 1979)
****£ = Eutrophic
  E/M = Eutrophic/Mesotrophic
  M = Mesotrophic
  O/M = Oligotrophic/Mesotrophic
  O = Oligotrophic

INSF = Insufficient Data
                                    T-65

-------
                                TABLE 42

      STEINHART WATER QUALITY INDEX VALUES FOR THE LAKE ERIE
                      1978-1979 NEARSHORE REACHES
Reach
1
2
3
4

5
6
7
8
9
10
11
12
13
15
16
17
18

19
20

1978
*69.24
*5iUV,
*67.80 L l
*69.38

*65.95
*64.84
*69.23
*61.11
*63.67*
1
31. SO-* _
1B2 3
34.66/-> D a T
2F2B2 2
.3 !..?£ — DDT
1112
25.28c1p1B1T^
48.95 12 2 3
C1B2 2
*2'* CjT
40.57- o T
C2 1 4
44.43PV1/
114
^•08BCT,
1 1 u
41.08- T
VkrfT I^O
46.83- T
^r4
1979
*67.56
*56.53
*67.03
*69.47p
i
N.D.
N.D.
*6°'56ci
*62.48C
ND
36.61- p R
38 55 1!
51.27- p2
29 22
C1P2B
^'^P.C.B
*57.58C1 Tx
*55.95 l 2
12
' P C T
*58'97C?T
2 1
^2
*70.44f: T
^11











1T3
1T2
1T2
2T3
1T3
2




B = Biological (fecal conforms and chlorophyll a)
C = Chemical (chloride and total phosphorus)
T = Toxics (inorganic and organic)
*incomplete data set (either B, C, P or T missing)
                                    T-66

-------
                              TABLE 43

    COMPARISON OF THE NEARSHORE COMPOSITE TROPHIC INDEX (CTI)
         AND STEINHART'S INDEX USING 1978-1979 LAKE ERIE DATA
Reach
// Name
1
2
3
>4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
Colborne
Maitland
Nanticoke
Long Pt. Bay
Pt. Burwell
Pt. Stanley
Wheatley
Leamington
Colchester
Monroe
Maumee Bay
Locust Point
Sandusky Bay
Huron
Lorain
Cleveland
Fairport
Conneaut
Erie
Dunkirk
1978-1979
CTI* Rank
4.3
11.6
5.8
4.7
5.6
8.9
9.2
10.7
7.8
37.9
56.4
32.6
81.1
22.2
13.3
12.3
11.2
6.8
21.8
6.9
1
12
4
2
3
8
9
10
7
18
19
17
20
16
14
13
11
5
15
6
1978
Steinhart
69.24*
54.14*
67.80*
69.38*
65.95*
64.84*
69.23*
61.11*
63.67*
31.80
34.66
31.52
25.28
48.95
42.46
40.57
44.43
44.08
41.08
46.83
Rank
2
9
4
1
5
6
3
8
7
18
17
19
20
10
14
16
12
13
15
11
Sum of
Ranks
3
21
8
3
8
14
12
18
14
36
36
36
40
26
28
29
23
18
30
17
Rank of
Sums
1
11
3
1
3
6
5
9
7
17
17
17
20
13
14
15
12
9
16
8
*Gregor and Rast's Composite Trophic Index (1979)
                                  T-67

-------
                                                     TABLE H6




                       CENTRAL BASIN SOD RATES (g C^m'V1) OF SEVERAL INVESTIGATORS




                                            (Taken from Davis et al. 1981)
Data Source
June
July
                                                                              August
Sept.
_,    Davis et al. (1981)



«>    Lucas & Thomas (1971)



      Blanton <5c Winklhofer (1972)




      Snodgrass <5c Fay (1979)



      Lasenby(1979)
                                                    1.45   0.55
                                .45 (1.601)
                               mean summer rate of 0.35



                               0.44
                                         0.94  0.43



                                         0.43



                                         0.32








                                         0.27
                                         0.48   0.24



                                         1.3
                                         0.32
 A June mean value of 1.6 g O,,m~ d~  was reported by Lucas and Thomas in which they included several observations when



the sediments within the chamber were slightly to moderately resuspended.

-------
vo
                                                   TABLE 47



                  COMPONENTS OF HYPOLIMNETIC OXYGEN DEMAND (HOD) IN CENTRAL LAKE ERIE - 1979



                                           (Taken from Davis et al. 1981)


Cruise Month Station
Al
1 3UNE
A2
Al
2 JULY
A2
Al
3 AUG.
A2

Hypo
Thick.
2.5m

4.5m
6.2m

3.5m
5.5m

3.8m

SOD
(Areal)*
1.28

1.56
1.19

0.82
0.56

0.38

WOD
(Areal)


0.36
0.43

0.42
1.10

1.22

SOD
(Vol.)**
0.51

0.35
0.19

0.23
0.10

0.10

WOD
(Vol.)


0.08
0.07

0.12
0.20

0.32

HOD
(Vol.)


0.43
0.26

0.35
0.30

0.42
SOD
%
HOD


81
73

66
33

24
WOD
%
HOD


19
27

34
67

76
      * Areal Rate: g m  day"



      **Volumetric Rate: mg/l/day

-------
                              TABLE 48

LAKE ERIE CENTRAL BASIN HOMOGENEOUS AREA OXYGEN DEPLETION RATES
                         (Taken from Rosa 1982)
YEAR
                  RATES
                      (gm m
              S+V
"3 mo'1)
 S+V+Q
  FINAL
S+V+Q+THKS
1929
1949
1950
1951
1961
1962
1963
1969
1970
1974
1975
1977
1978
1980
2.1
2.6
2.4
2.4
3.2
2.9
3.2
2.7
3.0
3.9
2.4
3.2
3.1
2.9
2.3
2.7
2.7
2.6
3.8
3.9
3.7
3.5
3.5
4.8
2.9
4.1
3.3
3.7
2.1
2.4
2.9
2.8
3.1
4.0
3.6
3.4
3.6
4.2
3.3
3.7
3.7
3.3
2.1
2.4
2.9
2.8
2.9
3.5
3.5
3.1
3.4
4.1
3.5
3.6
3.7
3.5
     S:     Simple Rate.

    S+V:     Simple, corrected for Vertical Mixing.

   S+V+Q:   Simple, corrected for Vertical Mixing, and adjusted to 10°C using Qiri
            2.0.                                                        1U
S+V+Q+THKS:
              Simple,  corrected for Vertical  Mixing, adjusted  to
10"C, and Standardized to a mean thickness of 4.15 m.
                                    T-70

-------
                                  TABLE 49

                 MICHIGAN STANDARDS AND IJC OBJECTIVES
                       FOR LAKE ERIE WATER QUALITY
    Parameter
 IJC
Objective
Michigan
Standards
Dissolved O2 (mg/1)
pH (std. unite)
Dissolved solids (mg/1)
Specific conductance
 (umhos/cm)
Fluoride (ug/1)
Chloride (mg/1)
Cadmium - total (ug/1)
Chromium - total (ug/1)
Copper - total (ug/1)
Iron - total (ug/1)
Lead - total (ug/1)
Nickel - total (ug/1)
Arsenic - total (ug/1)
Mercury - total (ug/1)
Mercury - dissolved (ug/1)
Selenium - total (ug/1)
Phenols (ug/1)
PCB's (ug/1)
Zinc - total (ug/1)
Ammonia - total (ug/1)
Fecal Coliform (ho./100 ml)
Cyanide (ug/1)
6.00*
6.50-9.00**
200
308.0

1200

0.200
50
5
300.0
25
25
50

0.200
10.00
1.00
0.100 - fish, wet weight
30
500 (NH3)
6.00*
6.70-8.50**
 502
 122
100

300,2
 30^

100?
 502
                            200'
                            5
 Monthly average
2
 Proposed

 Total body contact

*Minimum

**Permissible range
                                       T-71

-------
                        TABLE 50
OHIO STANDARDS AND IJC OBJECTIVES FOR LAKE ERIE WATER QUALITY
PARAMETER
Dissolved O7
PH
Conductivity
Phosphorus
Fluoride
Cadmium
Chromium
Copper
Iron
Lead
Nickel
Arsenic
Mercury
Selenium
Phenols
Zinc
NH,-NH,
} 1}
Manganese
Cyanide
Fecal Coliform
PCB's
IJC OBJECTIVE
MINIMUM MAXIMUM
6.00
6.50
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
9.00
308.00
0.500
1.20
0.200
50.00
5.00
300.00
25.00
25.00
50.00
0.200
10.00
1.00
30.00
xxxx
xxxx
xxxx
xxxx
xxxx
0.100
OHIO STANDARD
MINIMUM MAXIMUM
6.00
6.50
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
xxxx
9.00
320.0
1.00
1.80
1.200
50.00
xxxx
1000.00
30.00
25.00
50.00
.200
10.00
1.00
30.00
6.500
100.00
50.00
.0250
200.00
xxxx
                             T-72

-------
                                  TABLE 51

          COMMONWEALTH OF PENNSYLVANIA AND IJC OBJECTIVES
                STANDARDS FOR LAKE ERIE WATER QUALITY
    Parameter
 IJC
Objective
Pennsylvania
Alkalinity-total (mg/1)
Ammonia (mg/1)
Arsenic (mg/1)
Fecal Coliforms (no/100 ml)
Total Coliforms (no/100 ml)
Cadmium (mg/1)
Chromium-total (mg/1)
Copper-total (mg/1)
Cyanide (mg/1)
Dissolved Oxygen (mg/1)
Fluoride (mg/1)
Hardness
Iron-total (mg/1)
Iron-dissolved (mg/1)
Lead-total (mg/1)
Manganese-total (mg/1)
Nickel-total (mg/1)
Nitrite+Nitrate
 (mg/1 - nitrogen)
pH (std. units)
Phenolics (mg/1)
Selenium (mg/1)
Sulfate
Specific Conductance
 (umhos at 25°C)
Total dissolved solids (mg/1)
Zinc (mg/1)
Aldrin/dieldrin (ug/1)
Chlordane (ug/1)
DDT+metabolites (ug/1)
Endrin (ug/1)
0.020 (NH,)
0.050    *
0.002
0.050
0.005

6.0*
1.200

0.300

0.025

0.025
6.5-9.0**
0.001
0.010
308
200
0.030
0.001
0.300 (mg/kg-fish,
wet wgt.)
0.060
0.003
1 ug/g -
fish, wet wgt.
0.002
0.3 ug/g -
fish, wet wgt.
20*
0.500
0.050
200%
1000^
0.010 (96 RLC 50)
0.05 (hexavalent)
0.1 (96 RLC 50)
0.005 (HCN+CN")
6.0*
2.0
150 (monthly mean)
0.300
0.30
0.050
1.0
0.01 (96 RLC  50)

10.0
6.5-9.0**
0.001
0.010
250.0

3400
200^

0.001
0.3 (mg/kg-fish,
wet wgt.)
0.060
0.003
1 ug/g-
fish, wet wgt.
0.002
0.3 ug/g -
fish, wet wgt.
                                       T-73

-------
                             TABLE 51 CONTINUED

          COMMONWEALTH OF PENNSYLVANIA AND I3C OBJECTIVES
                 STANDARDS FOR LAKE ERIE WATER QUALITY
                                   IJC
 Parameter                        Objective             Pennsylvania
 Heptachlor (ug/1)                  0.001                 0.001
                                  0.300 ug/g-fish,       0.300 ug/g-fish,
                                  wet wgt.             wet wgt.
 Lindane (ug/1)                     0.010                 0.010
                                  0.300 ug/g -          0.300 ug/g -
                                  fish, wet wgt.         fish, wet wgt.
 Methoxychlor (ug/1)                0.0*0                 0.0*0
 Toxaphene (ug/1)                  0.008                 0.008
 Phthalic Acid Esters (ug/1)
  dibutyl-                         4.0                   4.0
  di (2-ethyl hexyl)-                0.6                   0.6
  other phthalates                 0.2                   0.2
 Polychlorinated Diphenyls
  (PCBs)                          0.001                 0.001
                                  0.1 ug/g -             0.1 ug/g -
                                  fish, wet wgt.         fish, wet wgt.
 Mercury-total (mg/1)               0.005 -
                                  fish, wet wgt.
 Mercury-dissolved (mg/1)           0.002


  Commonwealth of Pennsylvania Public Law 1987.  Title 25. Rules and
  Regulations.  Part I.  Dept. of Environmental Resources.  Article II.
  Water Resources. Chapter 93. Water Quality Standards.

  Geometric mean taken over not more than a thirty-day period.

  Average annual average based on representative lake-wide sampling.

 *Minimum

**Permissible range
                                        T-74

-------
                                 TABLE 52

             NEW YORK STATE STANDARDS AND I3C OBJECTIVES
                      FOR LAKE ERIE WATER QUALITY
       Parameter
Fecal coliform bacteria (no/100 m)
Total coliform bacteria (no/100 ml)
Dissolved oxygen (mg/1)
Total dissolved solids (mg/1)
Specific conductance (umhos/cm)
pH (std. units)
Iron, as Fe (mg/1)
Ammonia or ammonium
 compounds (mg/1)
                                         DC
                                       Objective
                                                1
                                        6.0*
                                        200
                                        308
                                        6.5-9.0**
                                        0.3
                                        0.020 (NHJ
                                        0.500 (NhK) -
                                        water supply
New York .State
 Standard
1
 Great Lakes Water Quality Agreement of 1978.
                                                          2003
Cyanide (mg/l-CN)
Ferrocyanide (mg/1-
Ferricyanide Fe(CN)6)
Cadmium total (ug/1)
Copper-total (ug/1)
Zinc-total (ug/1)
Arsenic-total (ug/1)
Chromium-total (ug/1)
Lead-total (ug/1)
Mercury-dissolved (ug/1)
Mercury-total (ug/1)

Nickel-total (ug/1)
Selenium-total (ug/1)
Fluoride-total (ug/1)
Phenolic compounds (ug/1)



0.2
5.0
30.0
50.0
50.0
25.0
0.2
0.5 - fish,
wet wgt.
25
10
1200
1.0
6.0*
200

6.7-8.5**
0.3
2.0, at pH   8.0
                                                          0.100

                                                          0.400
                                                          300.0
                                                          200.0
                                                          300.0
 Environmental Conservation Law  15-0313,17-0301.  Part 702.1
Class A - Special (International Boundary Waters).
 Geometric mean of not less than five samples taken over not more than
 a 30-day period.

*Minimum

**Permissible range
                                      T-75

-------
                        TABLE 53

ONTARIO PROVINCIAL OBJECTIVES FOR LAKE ERIE WATER QUALITY
PARAMETER
UNIT
 OBJECTIVE
MIN.       MAX.
Chlorine - tot resd
Cyanide = CN - tot
pH
Phenols - total
Phosphorus - total
Beta - total
Radium 226 - dissolved
Arsenic = As - total
Beryllium = Be - total
Cadmium = Cd - total
Chromium = Cr - total
Copper
Iron = Fe - total
Lead = Pt> - total

Nickel = Ni - total
Selenium = Se - total
Mercury = Hg - Dissolved
Silver = Ag - total
Zinc = Zn - total
Endrin
Lindane - whole sample
Toxaphene
Parathion - whole sample
Aldrin
Dieldrin
,mg/l
mg/1
s.u.
ug/1
mg/1
pc/1
pc/1
ug/1
ug/1
ug/1
ug/1
ug/1
ug/1
ug/1

ug/1
ug/1
ug/1
ug/1
ug/1
tot ug/1
ug/1
tot ug/1
ug/1
tot ug/1
tot ug/1
XXX
XXX
6.50
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX

XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
.005
.005
8.50
1.0
0.020
1000
3.0
100.0
11.0
0.20
100.0
5.0
5.0
(25.0)
20.0
25.0
100.0
10.0
0.10
0.30
0.30
0.01
0.01
0.008
0.001
0.001
                         T-76

-------
                                                   TABLE 54

                 SUMMARY OF LOCATIONS AND PARAMETERS IDENTIFIED AS AREAS OF CONCERN
Local
Parameter
Status
Michigan
   Detroit River
Ohio
   Ottawa and Lucas Counties
      Tributaries
          Maumee River
      Nearshore Zone
      Water Intakes
         Marblehead
         Port Clinton
         Put-in-Bay
         Catawba
         Oregon

         Toledo

   Erie and Sandusky Counties
      Tributaries
         Sandusky River
         Huron River
         Vermilion River
Fe, Cu, Cd, Hg, phenolic compounds, pH,
specific conductance, fecal coliforms
Cd, Cu, Fe, Pb, Hg, Zn, Mn, P, pH,
specific conductance

Cd, Cr, Cu, Fe, Ni, Zn, Mn, P, pH,
specific conductance, fecal coliforms
Cd, Cu
Cd, Cu, fecal coliform
Cd, Cu, Zn
Cd, Cu, Zn, Pb
Cd, Cu, Ni, Se, phenolic compounds, P,
fecal coliform
Cd, Cu
Cu , Cd*, Pb, Fe, P, specific conductance
Cu*, Cd*, DO, TP, specific conductance
Cu*, Cd*, Zn
Problem Area
Problem Area
Problem Area
(Toledo, Port Clinton)
Problem Area
Problem Area
Problem Area

-------
                                             TABLE 54 CONTINUED

                SUMMARY OF LOCATIONS AND PARAMETERS IDENTIFIED AS AREAS OF CONCERN
Local
Parameter
Status
             Nearshore

             Water Intakes
                Kelleys Island
                Milan
                Vermilion
                Huron
                Sandusky

71      Ohio
oo         Lorain County
             Tributaries
                Black River
         Vermilion River
      Nearshore
      Water Intakes
         Avon
         Lorain
                                   Cd, Cu, Ni, Zn, Fe, pH, fecal coliforms
                                   specific conductance

                                   Cd*, Zn
                                   Cd*, Zn
                                   Cd*, Zn
                                   Cd*, Zn
                                   Cd*, Zn
Cd, Cu, Ni, Mn, Fe, phenolic compounds,
Cyanide, P, NO., DO, specific conductance,
fecal coliforms
Cu*, Cd*, Ni*, Cr, Pb, Fe, Zn, phenolic
compounds, P, NO., specific conductance ,
fecal coliforms

Cd, Cu, Zn, Ni, Mn, Hg, DO, specific
conductance
Cd*, Cu*, Pb*, Fe*
Cd*, Cu*, specific conductance, fecal
coliforms
                                             Area of Concern
                                             (Sandusky Bay)
Problem Area


Problem Area
Problem Area
(Lorain)

-------
                                                   TABLE 54 CONTINUED

                       SUMMARY OF LOCATIONS AND PARAMETERS IDENTIFIED AS AREAS OF CONCERN
      Local
Parameter
Status
10
         Cuyahoga County
            Tributary
               Cuyahoga
               Euclid Creek

               Rocky River
         Lake and Ashtabula
            Tributaries
               Grand River
               Chagrin River

               Ashtabula River

               Conneaut Creek
      Ohio
         Lake and Ashtabula
            Nearshore
Cd, Cu*, Ni*, Zn, Pb, Fe, phenolic
compounds, TP, DO, specific conductance,
fecal coliforms - rare occurrence Se, Cr,
Mn, N, NH,
Cd*, Cu*,1»b, Ni», Fe , Zn, specific
conductance , pH, fecal coliforms
Cd, Cu, Pb, Zn, Pb, Mn, Hg, DO, specific
conductance
Cd* , Cu* , Fe , Pb, Ni, Zn, Mn, Hg,
phenolic compounds, DO, specific
conductance , fecal coliforms
Cd*, Cu*, Ni*, Pb, Zn, Mn, Fe , phenolic
compounds, fecal coliforms
Cd*, Cu*, Fe, phenolic compounds , P, DO,
specific conductance
Cd*, Ni*, Pb, Fe, Zn, phenolic compounds ,
P, specific conductance, fecal coliforms
Cd , Cu , Ni, Zn , Hg, Mn, DO - rare
F, Se Cyanide, phenolic compounds, pH,
specific conductance
Area of Concern



Problem Area

Problem Area
Area of Concern


Area of Concern

Problem Area

Area of Concern
Area of Concern
(Fairport, Ashtabula,
Conneaut)

-------
                                                  TABLE 5
-------
                                  TABLE 55

          NEUROTOXIC AND ONCOGENIC HUMAN HEALTH PROBLEMS
    ASSOCIATED WITH CHRONIC EXPOSURE TO SELECTED TRACE METALS
TRACE METAL
              EFFECT
Aluminum

Arsenic


Cadmium

Lead, inorganic


Mercury, inorganic

Mercury, organic


Manganese


Nickel
Mental deterioration; aphasia; convulsions

Oncogenic*   -  eye,larynx,  myeloid  leukemia;  ischaemic
disease of the extremeties

Franconi's syndrome, loss or impairment of sense of smell

Child development;  disoreientation; blindness;  nerve damage
to hands and feet; mental retardation

Tremors in hands, face and legs

Minamata disease; visual field constriction; nerve damage in
hands and feet

Psychosis; impaired speech; tremors;  loss of coordination;
muscular weakness

Oncogenic* - mouth, intestine
*Selected studies  have identified a correlation  with  cancer;  however, a  causal
relationship has not been found.


Data from National Institute for Occupational Safety and Health.
                                      T-81

-------
                                               TABLE 56



                  OBJECTIVES AND/OR STANDARDS FOR METAL CONCENTRATIONS IN LAKE ERIE
AUTHORITY
Ar
Cd
      OBJECTIVE STANDARD (ug/1)



Cr    Cu    Fe     Pb     Mn    Hg
Ni
Zn
International Joint Commission
Ontario Ministry of the Environment
Commonwealth of Pennsylvania
State of New York
State of Ohio
Lake Erie
excepted areas
State of Michigan
96 RLC 50
proposed
50.0
100.0
50.0


50.0




0.2
0.2
10.0
300.0

1.2
12.0
12.0


50.0
100.0



50.0
100.0
100.0


5.0
5.0
100.0
200.0

5.0
10.0



300.0
300.0
1500.0
300.0
1000.0


300.0


25.0 0.2
25.0
50.0 1000.0

50.0
30.0
30.0
30.0


25.0
25.0
10.0


25.0
200.0



10.0
100.0
10.0


10.0
50.0



30.0
30.0



30.0
55.0




-------
                                 TABLE 58

NUMBER OF TOTAL CADMIUM, TOTAL COPPER, TOTAL LEAD, TOTAL NICKEL, TOTAL SILVER
 AND TOTAL ZINC OBSERVATIONS CALCULATED TO EXCEED USEPA PUBLISHED CRITERIA
               FOR WATER QUALITY, 1978-1979 PERIOD OF RECORD.
 STATION NUMBER
          OBSERVATIONS
           EXCEEDING
           CRITERION/
PARAMETERTOTAL OBS. (N)
STATION LOCATION
1 12 WRD 0*165700
112 WRD 04193500
112 WRD 0*208000
112 WRD 0*208503


112 WRD 0*212200
112 WRD 0*213500
21 MICH 5800*8
21 OHIO 501260
21 OHIO 501510

21 OHIO 501520

21 OHIO 501800

21 OHIO 502020

21 OHIO 502130

21 OHIO 5021*0
21 OHIO 502*00

21 OHIO 502520

21 OHIO 502530

21 OHIO 502870


21 OHIO 50*030

Cadmium
Cadmium
Cadmium
Cadmium
Copper
Zinc
Cadmium
Copper
Cadmium
Cadmium
Cadmium
Copper
Cadmium
Copper
Cadmium
Copper
Cadmium
Copper
Cadmium
Copper
Cadmium
Cadmium
Copper
Cadmium
Copper
Cadmium
Copper
Cadmium
Copper
Zinc
Cadmium
Copper
1/9
3/9
2/7
3/9
3/9
1/9
1/9
1/22
1/7
1/1*
5/23
3/23
2/15
2/15
2/18
2/18
*/12
1/12
3/13
1/13
1/3
*/16
3/16
1/18
2/18
7/13
6/13
15/16
10/16
1/16
12/13
12/13
Detroit River at Detroit
Maumee River at Waterville
Cuyahoga River at Independence
Cuyahoga River in Cleveland


Grand River at Painesville
Cattaraugus Creek at Gowanda
Intake, City of Monroe water supply
Vermilion River near Vermilion
Black River below Elyria

Black River at Elyria

Rocky River near Berea

Cuyahoga River at Independence

Cuyahoga River in Cleveland

Cuyahoga River in Cleveland
Chagrin River at Willoughby

Grand River at Painesville

Grand River near Painesville

Conneaut Creek at Conneaut


Intake, Sandusky water supply

                                  T-83

-------
                            TABLE 58 CONTINUED

NUMBER OF TOTAL CADMIUM, TOTAL COPPER, TOTAL LEAD, TOTAL NICKEL, TOTAL SILVER
 AND TOTAL ZINC OBSERVATIONS CALCULATED TO EXCEED USEPA PUBLISHED CRITERIA
               FOR WATER QUALITY, 1978-1979 PERIOD OF RECORD.
                           OBSERVATIONS
                           EXCEEDING
                           CRITERION/
 STATION NUMBER   PARAMETEHTOTAL OBS. (N)
STATION LOCATION
21 OHIO 504090

21 OHIO 50*130

21 OHIO 5042*0

21 OHIO 50*250

21 OHIO 50*260

Grand totals



Cadmium
Copper
Cadmium
Copper
Cadmium
Copper
Cadmium
Copper
Cadmium
Copper

Cadmium
Copper
Zinc
3/3
3/3
1/1
1/1
9/12
5/6
5/25
3/25
3/5
1/5

89/3*8
60/3*8
Crown intake, Cleveland water

supply

Intake, Mentor-on-the-Lake water supply

Intake, Oregon water supply

Euclid Creek at Euclid

Turkey Creek near Conneaut


(25.6%)
(17.2%)










2/3*8 (0.6%)
                                  T-84

-------
                                         TABLE  66

                  TOTAL METAL CONCENTRATIONS  (ug/L)  FOR LAKE  ERIE,  1982
                                 (Taken  from Rossman  1983)
East (n=3)
                                    Central  (n=4)
                   West  (n=3)
Element  X
                    Median
Median
                                                                    Median
Ag
Al
As
Ba
Be
Bi
Ca1
Cd
Co
Cr
Cu
Fe
Hg
K1
Li
Mg1
Mn
Mo
Na1
Ni
Pb
Sb
Se
Sn
Sr
V
Zn
0.038
57.
0.30
49.
0.039
1.4
35.
0.058
0.086
0.38
2.1
42.
0.075
1.2
1.9
10.
2.4
2.1
9.3
1.0
0.21
0.062
2.8
0.18
150.
0.30
0.95
0.0021
19.
0.020
1.1
0.038
0.28
0.57
0.020
0.024
0.035
0.52
4.6
0.062
0.030
0.079
0.39
0.96
0.13
0.11
0.32
0.039
0.041
1.2
0.031
10.
0.068
0.27
0.039
52.
0.30
49.
0.022
1.5
35.
0.052
0.096
0.39
2.1
42.
0.048
1.2
1.9
10.
2.3
2.1
9.3
0.85
0.20
0.071
2.2
0.18
140.
0.32
0.96
0.025
120.
0.57
51.
0.022
0.68
35.
0.051
0.077
0.29
1.0
76.
0.082
1.2
1.9
11.
10.
1.5
8.6
0.99
0.26
0.31
2.6
2.8
150.
0.48
1.2
0.0097
80.
0.14
3.0
0.0072
0.38
1.2
0.014
0.023
0.094
0.38
45.
0.057
0.015
0.21
0.050
3.0
0.48
0.18
0.13
0.096
0.11
0.72
2.3
9.8
0.11
0.69
0.019
97.
0.54
52.
0.021
0.45
34.
0.044
0.068
0.30
0.84
37.
0.063
1.2
1.7
11.
8.9
1.2
8.6
1.0
0.21
0.34
2.5
1.4
150.
0.42
1.1
0.035
4200.
0.61
55.
0.16
0.37
31.
0.20
0.59
3.6
3.0
400.
0.066
1.6
3.2
10.
44.
1.2
5.8
2.9
2.4
0.056
0.85
2.3
130.
3.2
20.
0.013
1800.
0.28
4.3
0.088
0.19
0.87
0.10
0.45
0.68
1.7
220.
0.0052
0.14
0.14
0.30
11.
0.29
0.63
1.5
0.66
0.025
0.97
1.2
24.
1.3
3.7
0.033
5100.
0.52
57.
0.20
0.28
31.
0.14
0.84
3.6
2.3
1400.
0.065
1.6
3.3
10.
48.
1.2
6.2
2.3
2.4
0.047
0.63
1.9
120.
3.7
18.
mg/L
                                           T-85

-------
                          TABLE 67


      CALCULATED TOXICITY UNITS FOR LAKE ERIE, 1982
                   (Taken from Rossman 1983)
              Water Quality.        Observed
Metal
Ag
As
Cd
Cr
Cu
Fe
Hg
Ni
Pb
Se
Zn
Toxicity Unit
Objective (op1
0.1
50.0
0.2
50.0
5.0
300.0
0.22
25.0
5.03
1.0*
30.0
(2M./0.)
n=l
Concentration (M-)
0.035
0.43
0.096
0.39
1.8
100.0
0.024
1.1
0.34
2.1
1.2
M^O.
0.35
0.0086
0.48
0.0078
0.36
0.33
0.12
0.044
0.068
2.1
0.040
3.91
 Median (ug/L)


 Filtered sample


 3.0 ug/L for Lake Huron

4
 Recommended objective
                              T-86

-------
                                                   TABLE 68



              NUMBER ASSIGNMENTS, AGENCIES AND LOCATIONS FOR STATIONS SELECTED FOR TREND ANALYSIS
oo
ASSIGNED
NUMBER
Tl
T2
T3
T4

T5

T6
T7
T8
T9
T10

Til


T12
T13
m
T15
STATION
STORET
CODE
820011
000024
000029
Not obtained
from STORET
0419*023

0419350
580046
04198005
0420050
04208000
50202
502130
502140
380126
01 0006
01 C005
01 0007
04219640
AGENCY
MDNR
MDNR
MDNR
City of
Toledo
City of
Toledo
USGS
OEPA
USGS
USGS
USGS
OEPA
OEPA
OEPA
OEPA
NY DEC
NY DEC
NY DEC
NY DEC
STATION DESCRIPTION
U.S. shore of Detroit River
Middle of Detroit River
Canadian shore of Detroit River
Maumee River at C and O Dock

Maumee River at Toledo

Maumee River at Waterville
River Raisin at ERA Dock
Sandusky River below Fremont
Black River below Elyria
Cuyahoga River at Independence

Cuyahoga River at Cleveland
Cuyahoga River at Cleveland
Cuyahoga River at Cleveland
Buffalo River
Black Rock Canal
Niagara River
Niagara River near Lake Ontario
LATITUDE
42°03'13.5"
43°03'16.2"
42°03'17.5"
41°41'46.0"

40°4r36.0"

41030'00.0"
41°54'02.0"
41 22' 12.0"
f\
41°24'42.0"
41°23'43.0"

41°26'52.0"
41 49' 17.0"
41 29'39.0"
41°51'42.3"
42°54'54.4"
42°57'02.0"
43°15'40.0"
LONGITUDE
83°10'40.1"
83°08'00.5"
83°07'08.3"
83 21'39.0"

83028'20.0"
f*
83 42'46.0"
83°21'16.0"
&3006'W.O"
f\
82°05'45.0"
81 37'48.0"
f\
81 41'06.0"
81 41'07.0"
^\
81042'12.0"
78°52'04.0"
78°54'10.0"
78°54'10.0"
79°03'47.0"

-------
                                               TABLE 68 CONTINUED


             NUMBER ASSIGNMENTS, AGENCIES AND LOCATIONS FOR STATIONS SELECTED FOR TREND ANALYSIS
00
00

ASSIGNED
NUMBER
11
12
13
14
Ml
MDNR
uses
OEPA
NY DEC
STATION
STORET
CODE AGENCY STATION DESCRIPTION
580048 MDNR Monroe water intake
504030 OEPA Sandusky water intake
504090 OEPA Crown water intake
J4108 Erie Co. Erie water intake
Dept. of
Health
Not obtained Toledo Locust Point - Davis-Besse
from STORET Edison
Michigan Department of Natural Resources
United States Geological Survey
Ohio Environmental Protection Agency
New York Department of Environmental Conservation


LATITUDE
41°56'12.3"
41°27'51.0"
41°31'08.0"
42 09'24.0"
41°35'57.0"
(cooling



LONGITUDE
83°13'24.3"
82°38'50.0"
81 52'46.0"
80°09'12.0"
83°05'28.0"
tower)

      T = tributary stations
      I = municipal water intakes
      M = industrial monitor

-------
I
00
vo
                                                 TABLE 69


    SUMMARY OF LINEAR REGRESSION TRENDS OF WATER QUALITY PARAMETERS AT SELECTED STATIONS ON LAKE ERIE





    STATION LOCATION       TEMP  pH   ALK.   DO  COND. CHLOR. TURB.SOLIDS RES.  SIL.   BOD   NIT.
Tributaries
820011 (US Shore)
000024 (Livingstone Chan.)
000029 (Canadian Shore)
River Raisin
C and O Dock
Toledo
Waterville
Sandusky River
Black River
Cuyahoga at Independence
Cuyahoga R. at Cleveland
(1963-1974)
Cuyahoga R. at Cleveland
(1974-1981)
Buffalo River
Black Rock Canal
Niagara River (0007)
Niagara River at Lake Ont.
Intakes
Monroe water intake
Sandusky water intake
Crown water intake
Erie water intake
Davis-Besse

0
0 +
0 +

0
0
0 +
0

+
+



0 +
0 +
0
+ 0

0 0
+
+
0
0 0

_



_
0
0
0
+
0
+

+

0

0
0

0
-
+
_
0

_
+
0

_

0







+
0

0


0
0
+
0

_
_
+

0
0
0
-

0
-



_
0
0
-

0
+
0



_
_
0
0
+
0
+
0

0
0

0

_
_
-
-

0
0
0
_
_

_ _ —
0 0
000

0 0
0 0
0 0







0
0 0
0 0
0

0
0 +
-
+
0 0

0-0
000
000

+

0 0


+




-
0 0
0
0


0


0 0

-------
                                           TABLE 69 CONTINUED

SUMMARY OF LINEAR REGRESSION TRENDS OF WATER QUALITY PARAMETERS AT SELECTED STATIONS ON LAKE ERIE
STATION LOCATION
Tributaries
820011 (US Shore)
000024 (Livingstone Chan.)
000029 (Canadian Shore)
River Raisin
C and O Dock

Toledo
Waterville
Sandusky River
Black River
Cuyahoga at Independence
Cuyahoga R. at Cleveland
(1963-1974)
Cuyahoga R. at Cleveland
(1974-1981)
Buffalo River
Black Rock Canal
Niagara River (0007)
Niagara River at Lake Ont.
Intakes
Monroe water intake
Sandusky water intake
Crown water intake
Erie water intake
Davis-Besse
TOTAL
NH,+ K3EDHAL NO,-
NO, NH^ NIT. NO,
34 2

0
_
000
0
0
(NHJ
J
0 0
0

00 +
-

0 0

+ 0
00 0
0 0
00 0

0
+ 0 0
00 0

+
TOTAL
ORGAN. TOTAL ORTHO TOTAL FECAL
CARBON PHOS. PHOS. COLI. COLI.

0 0
_
_ -i-

-


0


+ 0 +
0 0

+ 0 0

00 0
0 0

0

0 00
+ 0 - 0
+ 0 +
0 - -
0
PHENOLS IRON

-
0
0







0 0
+

0

0
0

0

+
+

-

                                    + = a significant increasing trend (P .05)
                                       - = a significant decreasing trend
                                        0 = no significant trend observed
                                  A blank indicates the parameter was not sampled

-------
                                                            TABLE 70



COMPARISON OF HISTORICAL DATA FROM BEETON (1961) WITH 1978 CENTRAL BASIN NEARSHORE DATA (HEIDELBERG COLLEGE)

                                                    (Taken from Richards 1981b)
Regression analysis
Parameter
Conductivity
@TDS
.62
@TDS
.65
Calcium
Sodium plus
Potassium
Chloride
Sulfate
Y

267.04
254.72
36.9
8.91
17.6
22
X-1900

40.20
40.20
46.6
45
42.4
48.75
of Beeton's data
N

24
24
20
17
30
20
b

1.25
1.20
.098
.115
.305
.177
V

7.97
7.97
3.09
3.87
16.12
5.58
Extrapolation
to 1979
V

.001
.001
.01
.01
.001
.001
Y S

315.67 6.81
300.91 6.45
40.09 1.13
12.84 1.11
28.91 .767
27.25 1.08
HCWQL data
N

1041
1041
146
145
1031
1029
Y

293.09
293.09
35.79
11.48
19.16
24.13
sy

14.53
14.53
3.06
2.19
2.47
5.56
t**

3.31
1.21
3.73
1.21
12.65
2.86
Comparison
p*»

.001
n.s.
.001
n.s.
.001
.01
     "calculated t value, and associated probability level, for t-test of the null hypothesis, H : b = 0.


     All regression slopes are significant, i.e., significantly different (greater than) from 0.
    **calculated t value, and associated probability level, for t-test of the null hypothesis, H : Y
                                                                                      O

      Y   .. All parameters show highly significant decreases except sodium plus potassium, which is lower


      than, but not significantly different from the trend of Beeton's data.

-------
                                                        TABLE 71

                              R-SQUARE AND T VALUES FOR REGRESSION ANALYSES OF DATA
                                 FROM THE DIVISION OF WATER INTAKE, CLEVELAND, OHIO,
                      BEFORE AND AFTER FILTERING THE DATA TO REMOVE SEASONAL FLUCTUATIONS.

                        n.s. indicates slope not significantly different from 0 at the .05 level of significance.
                       A negative t value indicates a decrease in that parameter's concentration through time,
                                           a positive t value indicates an increase.

                                                (Taken from Richards 1981b)
to
rv>
Parameter
Before
2 2
r t significance r
After
t
significance
Total Phosphorus
Soluble Reactive P
Nitrate + Nitrite
Ammonia Nitrogen
Sol. Reactive Silica
Alkalinity
pH
Specific Conductance
Sulfate
Chloride
.021
.354
.122
.010
.029
.005
.012
.001
.053
.264
-1.8
-7.66
4.53
-1.21
1.61
1.52
2.29
-0.65
3.43
-8.83
n.s.
.001
.001
n.s.
n.s.
n.s.
.05
n.s.
.001
.001
.028
.454
.319
.010
.015
.004
.030
.001
.050
.298
-2.07
-9.43
8.32
-1.25
1.17
1.30
3.72
-0.66
3.35
-9.63
.05
.001
.001
n.s.
n.s.
n.s.
.001
n.s.
.001
.001

-------
                                TABLE 72


           COMPARISON OF MAXIMUM STANDING CROP VALUES1
 FROM THE 1979 and 1980 LAKE ERIE CLADOPHORA SURVEILLANCE PROGRAM


SITE YEAR

1979
Stony Point
1980
1979
South Bass
1980
/i
1979
Walnut Creek 3
1980
/i
1979*
Rathfon Point
1980
/i
1979*
Hamburg ,
1980


0.5
107 g/m2
<•*
186 g/m^
10 g/m2

218 g/m2
-)
24g/rn

18 g/m2
•7
983 g/rn

ND
•7
36g/mz
0.1 g/m2

DEPTH
1
64

70
75

174

20

37

444

ND

48
63

(m)
2
30

T
110

49

24

18

410

ND

52
61


3
0

0
2

T

16

59

214

ND

100
86
TRANSECT2
AVERAGE

50

64
49

110

21

33

513

ND

59
53
 Based on dry weight 64°, except Rathfon Point, dry weight 105°


2Transect Average = dry weight of °-V? 2? 3m
3                               *
 Data from Catherine Carnes, Great Lakes Laboratory, State University College at
Buffalo, New York. Personal Communication, 1981.

4
 Data from Sweeney 1980
                                    T-93

-------
Table 73.  ANNOTATED LIST OF LAKE ERIE FISH SPECIESJ
FAMILY/COMMON NAME/SCIENTIFIC NAME2
Petromyzontldae
silver lamprey (Ichthyomyzon unlcuspis)
sea lamprey (Petromyzon marl mis!
AclpenseHdae
lake sturgeon (Aclpenser fulvescens)
Lep1soste1dae
spotted gar (Lepisosteus oculatus)
longnose gar (Leplsosteus osseus)'
Am11dae
bowfln (tola calva)
Clupeldae
alewlfe (Alosa pseudoharengus)
gizzard shad (Dorosoma cepedTanum)
Salmonidae
long jaw Cisco (Coregonus alpenae)
Cisco, lake herring (Coregonus arted11)
lake whiteflsh ( Coregonus cl upeaf orml s )
coho salmon (OncorhyncnuT klsutch)
Chinook salmonTOncorhynchus tshawytscha)
rainbow trout (Sal mo gairdneri)
lake trout (Salvellnus namaycush)
Osmerldae
rainbow smelt (Osmerus mordax)
Hiodontidae
mooneye (Hiodon terglsus)
Umbridae
central mudmlnnow (Umbra limi)
Esocidae
grass pickerel (Esox americanus)
northern pike (Esox luclus)
muskel lunge (Esox masqu' nongy)
Cyprinldae
goldfish (Carassius auratus)
common carp (Cyprinus carpi o)
silver chub (Hybopsls storeriana)
golden shiner (Notemigonus crysoleucas)
pugnose shiner (Notropls anpgenus)
emerald shiner (Notropls atherlnoides)
striped shiner (Notropls 'chrysocephaTus )
pugnose minnow (Notropls ealnae)
blackchln shinerlTjo^ropIs heterodon)
blacknose shiner (Notropls heterolepis)
spottall shiner (Notropls hudsonius)
spotfln shiner (Notropis spilopterus)
sand shiner (Notropls stramlneys)
mimic shiner (Notropls yojuceltus)
bluntnose minnow (Plmephales notatus)
fathead minnow (Plmephales promelus)
longnose dace (Rhlnichthys cataractae)
Catostomidae
quill back (Carpi odes cyprinus)
longnose sucker (Catbstomus catostomus)
white sucker (Catostomus comnersonTJ
lake chubsucker (Erimyzon sycetta)
northern hogsucker (HypenteTium nigricans)
biqmouth buffalo (Ictiobus cyprinelTus)
spotted sucker (Hjnytrema melanops)
silver redhorse (Moxostoraa anisurum)
golden redhorse (Hoxqstoma erythrurym)
shorthead redhorse (Moxostoma macrolepidutum)
Ictaluridae
black bullhead (Ictalyrus melas)
yellow bullhead (Ictaluru's natal is)
brown bullhead (Ictalurus nebulosus)
channel catfish (Ictalurus punctatus)
flathead catfish (Pylodictis olivaris)
stonecat (Noturus flavus)
tadpol e madtom (Noturus gyrinus)
brindled madtom (Noturus mi urus)
ABUNDANCE3
PRE-1900 PRESENT

A
-

A

U
C

C

-
C

U
A
A
U
U
U
C

-

C

C

C
A
A

U
U
A
C
C
A
C
C
C
C
A
C
C
C
C
US
C

C
C
A
C
C
A
C
C
C
A

C
C
C
C
U
C
C
C

U
U

R

E
CO

CD

A
A

E
R
R
C
C
U
E

A

R

CO

CO
U
R

C
A
U
CO
E
A
C
R
E
R
A
C
C
C
C
C
U

C
CD
A
R
C
C
U
C
C
C

C
U
C
C
U
C
U
CO
NOTES4

Ml, SS
CM, SS

UU, SS, CS*. SF*

UW, UD
WW, WO

UW, WO

CW, RS, HI, PS
WW, SS, RS. CS, PS

CW
CW. RS. CS*, PS*
CW, RS, CS*. PS*
CW. SS. El. CS. SF
CW, SS. El. (*, SF
CW, SS, El, RS. SF
CW. RS, CS*. SF*

CW, SS, RS, MI/EI, CS, SF. PS

WW, SS, RS, CS*. PS

WU, WO

WW, WO
WW. WO, SS, CS*, SF
WW. WO, SS, CS*, SF*

WW, WO. SS, El. CS
WW, WD. SS. El, CS, SF, PS
WW, SS, RS, PS*
WW, WO. PS
CW, WO
WW. CS, PS
WW
WW. WO. PS*
CW, WO, PS*
WW, WD, PS*
WW, PS
WW, PS
WW, PS
WW. PS
WW, PS
WW, PS
CW, SS

WW. SS, CS, SF
CW, SS, CS*
WW, SS, RS. CS, SF, PS
WW, WO
WW, SS
WW, SS, CS
WW. WD. SS
WW, SS
WW. SS
WW, SS. CS. PS

WW, WD. SS, CS, SF
WW, WO, SS, SF
WW, WD. SS. CS, SF
WW, SS. CS, SF
WW, SF
UU
UW. WD
UU
                       T-94

-------
                                                   TABLE 73  CONTINUED
FAMILY/COMMON NAME/SCIENTIFIC NAME2
AnguilHdae
American eel (Angullla rostrata)
Cyprinodontldae
banded kllUflsh (Fundulus dlaphanus)
Gadldae
burbot (Lota Iota)
Percopsidae
trout-perch (Percopsis omi scomaycus )
Percichthyldae
white perch (Horone ameri cana )
white bass (Morone chrysops )
Centra rchidae
rock bass (Amblpplites rupestrls)
green sunf 1 sh (LepomiT cyanellus)
pumpklnseed (Lepomis glbposus)
bluegill (Lepoims macrochl rus )
sraal Imouth bass (Hlcropterus dojonrieui)
largemouth bass (H1cropteru7 salniol3e?)
white crapple (Pomoxls annul arls)
black crapple ( Pomoxls nigromaculatus)
Percldae
eastern sand darter (Ammocrypta pellucida)
greenslde darter (Etheostoma blennloides)
Iowa darter (Etheostoma exile")
fantail darter~TETRiostoma~7Tabenare)
Johnny darter (Etheostoma m'grum)
yellow perch (Perca flavescens)
logperch (Perclna caprodes)
channel darter (Percina copelandi)
river darter (Perclna shumardi )
sauger (Stlzostedlon canadense)
blue pike (Stlzostedlon vltreum glaucum)
walleye (Stizostedion vltreum vltreum)
Sciaenidae
freshwater drum (Aplodinotus grunnlens)
Cottidae
mottled sculpin (Cottus bairdi)
spoonhead sculpinTCottus ricel)
fourhorn sculpin (Hyoxocephalus quadrlcornls)
Atherinldae
brook silverside (Labldesthes sicculus)
ABUNDANCE3
PRE-1900 PRESENT

U

C

C

C

-
A

A
C
C
A
A
A
A
A

C
C
C
C
C
A
C
C
U
A
A
A

A

C
R
R

A

U

R

R

CD

C
A

C
C
CO
C
C
C
A
CD

R
U
E
U
C
A
CD
R
E
U
E
A

A

C
E
E

U
NOTES4

WU, MS, MI

CM, WO

CW, RS, CS*

UU, PS

VM, SS, RS, MI, CS, SF, PS
UU. SS, RS, CS. SF. PS

«M. CS*. SF
WW. CS*. SF
WU, WO, CS*, SF
VW, CS*, SF
WW. CS*, SF
WW, CS*, SF
WW, CS*, SF
WW, WD, CS*, SF

WW
WW
cw, wo
WU
WU
WW, RS, CS, SF, PS
WU
WW
WW
WW. SS. CS*. SF*. PS
CW. RS, CS*. RS*
WW. SS, RS, CS, SF. PS

WW, SS, RS, CS, SF, PS

WW
CW
cw

WW, PS
 From Trautman  (1957, 1981), Hubbs and Lagler (1964), and Van Meter and Trautman  (1970); excluding species present  in the Lake Erie
 basin but  restricted entirely to tributaries with only occasional strays in the  lake.

2From Robins et al.  (1980).


 A = abundant; C * common; CD * common but decreasing; U - uncommon; R • rare;  E  »  probably extirpated; - « absent


 WW = warmwater or coolwater species; CW = coldwater species; WD « largely or entirely wetland dependent; SS • migratory stream
 spawner; RS • migratory reef spawner; MS * migratory marine spawner; El « intentional exotic Introduction; MI • marine Invader;
 CS * commercially significant; SF * significant  sport fish; PS « significant prey  fish; Currently not significant due to depleted
 populations or legal protection.
                                                           T-95

-------
Species
                                                              TABLE 74
                                CURRENT POPULATION STATUS OF MAJOR LAKE ERIE FISH SPECIES
Figure
Reference
Date of Decline
or Extinction
Current
Status
 Reasons for Status Change
Lake Whitefish    128
Lake Herring      128
Lake Sturgeon     —
Lake Trout
 10
 CTt
Muskellunge
Northern Pike
Blue Pike
Sauger
128
128
               1961


               1960's
               Mid
               1950's
               1930
               1950
               1915
1960
1960
                   Commercially
                   Insignificant

                   Extinct
                   Rare
                    4,500 kg/yr


                   Extinct
                   Virtually
                   Extinct
                   Uncommon
Extinct
Extinct
Environmental degradation of three major spawning sites by 1920
Overharvest of cyclically low populations

Over harvest of cyclically low populations (collapse 1925)
Siltation of clean gravel spawning areas
Deterioration of dissolved oxygen regimes in central basin

Deliberate and destructive overharvest
Loss of clean gravelly spawning areas required  in tributaries and
nearshore waters due to dams, channelization and siltation

Overharvested as early as 1850
Siltation of the rock and gravel  spawning areas
Deterioration of dissolved  oxygen regimes in its deepwater central
basin habitat

Siltation and  damming of tributaries
Draining, filling and diking of marshes around the western basin
Overharvest

Siltation and  clamming of tributaries
Draining, filling and diking of marshes around the western basin
Overharvest

Commercial overharvest
Siltation and  pollution of nearshore spawning areas
Habitat loss due to deteriorating summer dissolved oxygen regimes
Hybridization with the more abundant walleye populations

Commercial overharvest
Siltation and  pollution of nearshore spawning areas
Habitat loss due to deteriorating summer dissolved oxygen central
basin regimes
Hybridization with the more abundant walleye populations

-------
                                                        TABLE 74
                                                       CONTINUED
                             CURRENT POPULATION STATUS OF MAJOR LAKE ERIE FISH SPECIES
Species
Walleye

Yellow Perch
Rainbow Smelt
Carp
— i
^ Suckers
Channel Catfish
Bullheads
White Bass
Freshwater Drum
Figure
Reference
128

129
129
130
130
130
130
130
130
Date of Decline Current
or Extinction Status
1962 Abundant

— Abundant
— Increasing
— Abundant
— Common
— Common
— Common
— Common
Common
Reasons for Status Change
- Overharvest
- Competition with the increasing smelt population
- Environmental degradation
- Increased landings due to use of nylon gill nets, increased
fishing pressure and increased market demand
- Increased commercial landings reflect seasonal and
changes in marketability rather than absolute stock size
- Increased commercial landings reflect seasonal and
changes in marketability rather than absolute stock size
- Increased commercial landings reflect seasonal and
changes in marketability rather than absolute stock size
- Increased commercial landings reflect seasonal and
changes in marketability rather than absolute stock size
- Increased commercial landings reflect seasonal and
changes in marketability rather than absolute stock size
- Increased commercial landings reflect seasonal and
changes in marketability rather than absolute stock size
- Underexploited



Canadian
longterm
longterm
longterm
longterm
longterm
longterm

Bowfin

Gizzard Shad      130

Pacific Salmon
Abundant
  Not available

  Underexploited

  Artificially stocked since 1870
Goldfish
Common
- Underexploited

-------
Species
                                                           TABLE 74
                                                         CONTINUED
                              CURRENT POPULATION STATUS OF MAJOR LAKE ERIE FISH SPECIES
                Figure
                Reference
                                Date of Decline
                                or Extinction
Current
Status
Reasons for Status Change
Burbot



American Eel

White Perch

Centrarchids
                               1950
Extinct          - Environmental degradation (siltation and pollution)
                - Overharvest
                - Loss of deep water central basin habitat due to oxygen depletion

Uncommon      - Not available

Increasing       - Not available

Common        - Not available
00

-------
                            TABLE 75

      RELATIVE ABUNDANCE OF LARVAL FISHES CAPTURED IN
             THE WESTERN BASIN OF LAKE ERIE IN 1977
SPECIES
Gizzard Shad
Yellow Perch
Emerald Shiner
White Bass
Carp
Freshwater Drum
Log Perch
Walleye
Rainbow Smelt
Spottail Shiner
Unidentified Sun fish
(Lepomis spp.)
Whitefish
Unidentified Cyprinidae spp.
White Sucker
Quillback Carpsucker
Channel Catfish
Trout Perch
Sauger
Unidentified Percidae spp.
Unidentified Crappie
(Pomoxis spp.)
TOTAL
AVERAGE DENSITY1 PERCENT OF.
( # larvae/ 100m3) TOTAL CATCH
1 266.16
21.31
18.72
7.85
2.82
1.76
1.43
0.99
0.88
0.18
0.05
0.04
0.03
0.02
0.02
0.01
0.01
0.01
0.01
0.01
322.30
82.58
6.61
5.81
2.44
0.88
0.55
0.44
0.31
0.28
0.06
0.02
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01
0.01

1
 Average densities found by dividing the sum of the calculated
densities by the number of tows taken during period of larval
occurrence.

 Species ranked according to descending percent of catch.
                           T-99

-------
                      TABLE 76
RELATIVE ABUNDANCE OF LARVAL FISHES CAPTURED ALONG THE
       OHIO SHORELINE OF THE CENTRAL BASIN IN 1978
SPECIES
Emerald Shiner
Gizzard Shad
Spottail Shiner
Freshwater Drum
Rainbow Smelt
Carp
Yellow Perch
Trout Perch
Johnny Darter
Log Perch
Mottled Sculpin
Cyprinidae
Notropis sp.
Percidae
Unidentified Larvae
Unidentified Sunfish
(Lepomis spp.)
Striped Shiner
White Sucker
AVERAGE DENSITY
(# of larvae/ 100mJ)
32.30
28.42
16.37
3.92
3.40
2.85
1.25
1.00
0.80
0.74
0.47
0.46
0.25
0.20
0.07

0.07
0.06
0.05
PERCENT OF
TOTAL CATCH^
34.28
30.53
17.58
4.21
3.66
3.06
1.34
1.01
0.84
0.79
0.50
0.48
0.26
0.21
0.08

0.06
0.06
0.04
                        T-100

-------
                        TABLE 76 CONTINUED

   RELATIVE ABUNDANCE OF LARVAL FISHES CAPTURED ALONG THE
           OHIO SHORELINE OF THE CENTRAL BASIN IN 1978
SPECIES
Walleye
White Bass
Rock Bass
Burbot
Golden Shiner
Unidentified Crappie
(Pomoxis spp.)
Sauger
Quillback Carpsucker
Black Crappie
Smallmouth Bass
TOTAL
AVERAGE DENSITY
(// of larvae/lOOm3)
0.04
0.03
0.02
0.02
0.02

0.01
0.01
0.01
0.01
0.01
92.76
PERCENT OF
TOTAL CATCH^
0.04
0.03
0.03
0.03
0.02

0.02
0.02
0.01
0.01
0.01

Average density found by dividing the sum of the calculated
densities by the number of samples collected during the period of
larval occurrence.

Species ranked in descending order of average density.
                               T-101

-------
o
ro
                                                        TABLE 77



                 LARVAL FISH ENTRAINMENT ESTIMATES FOR WESTERN BASIN POWER PLANTS PER YEAR (1977)
Species
Gizzard Shad
Rainbow Smelt
Carp
White Bass
Sauger
Walleye
Yellow Perch
Total*
Monroe
2.70 x 10*
6.53 x 106
3.79 x 10^
1.10 x 10
2.13 x 10?
1.05 xlO'
3.31 xlO*
4.68 x 10


3.10 x 107
4.35 x 10b
2.97 x 10*
1.50 xlO5
Whitting
4.90 x 10?
8.10 x 10
2.98 x 10*
4.27 x 10^
1.50 x 10*
1.64 x 10^
2.05 x 10^
2.51 x 10
4.34 x 10JJ
4.89 x 10
5.35 x lof
4.79 x 10*
2.09 x 107
2.06 x 10b
5.49 x 10?
3.09 x 10'
Bayshore
1.20 xlO*
2.00 x 10*
7.24 x 106.
1.04 x!0b
3.65 x 10c
3.99 x 10
4.99 x 107.
6.09 x 106
1.05 x 10*
1.19 x 10
1.30 x 10*
1.16 xlO^
5.07 x 107
5.01 x!0b
1.33 x 10^
6.62 x 10'
Davis-Besse
1.30 xlO7-
3.21 x 10b
1.99 xiof
3.32 x 10*
2.54 x 10*
4.23 x KT
2.63 x 10*
4.24 x 10J

1.22 xlO^
1.23 xiO*
2.24 x 10^
6.48 x 10J
1.58 x 10c
7.47 x 10^
Total
4.40 x 10«
5.86 x 108
1.08 x 107
1.64 x!0b
2.18 x lo!
5.28 x 10°
7.37 x lol
1.14 xlO'
1.49 x 10^
2.49 x 10
1.96 xlO^
2.93 x 10^
1.05 x lof
1.01 x 10'
4.87 x 10«
2.43 x 10s
              *Total represents the sum of all species collected



               Lower number in each cell is equal to one standard error of the mean.

-------
                                               TABLE 78



         LARVAL FISH ENTRAINMENT ESTIMATES FOR CENTRAL BASIN POWER PLANTS PER YEAR (1978)
Species
Gizzard Shad
Rainbow Smelt
Emerald Shiner
Spottail
Shiner
Walleye
Yellow Perch
Total*
Edgewater
7.91 x loj?
2.03 x 10
2.91 x 10:j
1.5* x ID"*
9.73 x 10*
2.10 x 10
2.48 x lof
5.52 x 10*

4.83 x 10*
8.05 x 10-*
1.18 x 107
4.21 x 10^
Avon Lake
2.38 x 107
3.44 x 10b
1.27 x 10*
1.53 x 10J
7.44 x 10*
1.65 x 10^
1.12x 10?
2.91 x 10

9.84 x 10*
3.61 x 10^
3.67 x 107
1.36 x 10b
Eastlake
9.21 x 10*
2.60 x 10b
2.19 x 107
3.44 x 10b
1.33 x 107
2.91 x 106
5.82 x 10*
5.84 x 10^
7.65 x 10*
1.28 x 10*
8.57 x 10*
1.59 x 10^
5.40 x 107
1.38 x 10b
Lake Shore
4.77 x 10*
8.60 x 10^
9.33 x 10*
1.03 x IV
2.39 x 10*
7.02 x 10
5.45 x 10*
7.45 x 10*
4.05 x 10*
4.75 x 10J
1.10x10*
1.89 x 10-*
1.62 x lol
3.00 x 10J
Ashtabula
A&B
1.01 x 107.
2.90 x 10b
4.46 x lo!
3.40 x 10^
3.18 x 107
8.69 x 10b
4.11 x 10^
8.68 x 10^

1.70 x 10^
1.57 x 10^
7.61 x 107
1.71 x 10b
Ashtabula
C
5.60 x 10J?
1.75 x 10
3.06 x 10^
3.88 x 105
3.09 x 107
6.76 x 10
3.32 x 10 =
1.50 x 10^

7.94 x 10^
1.98 x 10^
5.12 x 10!
1.68 x 10b
Total
6.14 x 107-
2.59 x 10b
3.19 x 107
3.08 x 10
8.01 x 107
5.48 x 10b
1.12x10^
9.20 x 10J
1.17 x lof
1.20 x 10*
4.60 x 10^
2.33 x 10^
2.52 x lof
8.59 x 10b
*Total represents the sum of all species collected



Lower number in each cell is equal to one standard error of the mean.

-------
                          TABLE 79








     COMPARISON OF NEARSHORE VOLUME WEIGHTED FISH LARVAL



            ABUNDANCE WITH ESTIMATED ENTRAINMENT
               VOLUME WEIGHTED   TOTAL NUMBER    % OF



SPECIES           ABUNDANCE       ENTRAINED     ABUNDANCE
Western Basin
g
White Bass 2.65 x 10
9
Yellow Perch 1.35 x 10
7
Walleye 6.08 x 10'
Central Basin
Yellow Perch 1.09 x 108
9
Rainbow Smelt 4.28 x 10*

7
7.73 x 10' 29.0
9
1.05 x 10* 7.8
f.
1.96 x 10° 3.2

4.60 x 106 3.7
7
3.19 x 10' 7.4
                              T-104

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                                                             TABLE 80

                             SUMMARY OF TOXIC SUBSTANCES FROM LAKE ERIE FISH STUDIES, 1977-1980
Author(s)
Gessner &
Griswald
Report
Year
1978
Collection
Year
1977
Sampling
Area
Maumee Bay
Locust Pt.
Sandusky Bay
Fish Tissue(s)
Shad WB & F
Perch
Carp
Drum
Catfish
Parameters
% lipid
DDE
ODD
Total DDT
Dieldrin
o
en
                                                                   Aldrin
                                                                   trans-chlordane
                                                                   cis-Chlordane
                                                                   BHC
                                                                   Heptachlor epoxide
                                                                   Lindane
                                                                   PCB (1254 + 1260)

          Study Variables
1. PCB analysis included Arochlors 1254 + 1260 only
2. Results presented without correction for recoveries
3. Recoveries ranged from 50-100%
4. Includes a good review of toxics in water, sediment and fish for Lake Erie south shore
Gessner 1980 1978 Locust Pt.
Port Clinton
Cedar Point
Bass Islands
Erie, PA



C. Catfish WB & F
Drum
Walleye
Walleye (age 1)
Y. Perch
C. Salmon


% lipid
pp1 DDE
pp' ODD
pp' DDT
Dieldrin
Aldrin
Chlordane
BHC

-------
                                                TABLE 80 CONTINUED

                      SUMMARY OF TOXIC SUBSTANCES FROM LAKE ERIE FISH STUDIES, 1977-1980
              Report   Collection    Sampling
Author(s)       Year      Year       Area
                                   Fish
                                      Tissue(s)
Parameters
Gessner
(cont.)
1980
1978
  BHC (Lindane)
Heptachlor
PCB (1254 only)
                          Study Variables
                1. 15 composites of 5 fish for each species
                2. Dieldrin and pp' DDE were the only pesticides found in the samples
                3. All PCB 1254 and pp1 DDE data reported was corrected for % recovery
                4. With the exception of yearling walleye, all fish collected were sexually mature
Burby et al. 1981 1979 Tributary Survey
Raisin River
Maumee River
Toussaint
Sandusky
Black
Cuyahoga
Chagrin
Grand, Ohio
Ashtabula
Walnut Creek
Cattaraugus Cr





W. Bass WB
Y. Perch
Drum
Shad
S. Shiner
E. Shiner
C. Shiner
R. Smelt
N. Pike
C. Catfish
B. Bullhead
Carp




%Fat
Aldrin
BHC
BHC
BHC

Chlordane

op' ODD
pp1 DDD
op1 DDE
pp1 DDE
op1 DDT
pp' DDT
Dieldrin

-------
                                                TABLE 80 CONTINUED

                      SUMMARY OF TOXIC SUBSTANCES FROM LAKE ERIE FISH STUDIES, 1977-1980
Author(s)
Report  Collection
 Year      Year
                                    Sampling
                                     Area
Fish
Tissue(s)
Parameters
                          1980
                                    Uptake Survey
                                    Maumee
                                    Cuyahoga
                     Uptake Survey
                     Maumee
                     Cuyahoga
                     Ashtabula
                                     YOY Bluegill  WB
                                     YOY C. Catf.
                                                   YOY Bluegill  WB
                                                   YOY C. Catf.
Burbyetal.      1981       1979      Uptake Survey                                 aEndosulfan
(cont.)                              Maumee        YOY Bluegill  WB               ft Endosulfan
                                                                                  Endrin
                                                                                  Heptachlor
                                                                                  Heptachlor epoxide
                                                                                  Heptachlorobenzene
                                                                                  2,4-D (Isopropyl ester)
                                                                                  Methoxychlor
                                                                                  Mirex
                                                                                  Toxaphene
                                                                                  Trifluralin
                                                                                  PCB's
                                                                                   arochlor 1016
                                                                                   arochlor 1254
                                                                                   arochlor 1260

                          Study Variables
                1. Fish species broken down by age group before analysis
                2. Study was broken down into 2 parts:
                    1.  Survey of 11 tributaries
                    2.  Uptake Studies
                      a. 1979, Autumn
                      b. 1980, Spring
                3. 1979 Uptake Study consisted of 4 weeks exposure
                4. 1980 uptake study lasted 6 weeks with some fish removed weekly to check exposure with time
                5. Percent recoveries varied for the survey (15-85%) and uptake (40-104%) studies
                6. Data is not corrected for recoveries

-------
                                                      TABLE 80 CONTINUED

                             SUMMARY OF TOXIC SUBSTANCES FROM LAKE ERIE FISH STUDIES, 1977-1980
o
00
Author(s)
Clark et al.



Report Collection Sampling
Year Year Area
1982 1980 Detroit Rv
Huron Riv., OH
Chagrin Rv.
Trout Run, PA

1980 Detroit Rv
Huron Rv, OH
Chagrin Rv, OH
Trout Run, PA
Fish Tissue(s)
C. Salmon F
(3 yr.)

C. Salmon WB
(3 yrs.)
Parameters
PCB's
1260
1254
1248
1242
total PCB's
ppDDE
pp DDD
ppDDT
total DDT
                                                                                       "Apparent Toxaphene"
                                                                                       Mirex
                                                                                       Dieldrin
                                                                                       Endrin
                                                                                       cis-Chlordane
                                                                                       trans-Chlordane
                                                                                       cis-Nonachlor
                                                                                       trans-Nonachlor
                                                                                       Mercury
                                                                                       Hexachlorobenzene
                                                                                       Octachlor epoxide

-------
                                                       TABLE 80 CONTINUED

                             SUMMARY OF TOXIC SUBSTANCES FROM LAKE ERIE FISH STUDIES, 1977-1980
       Author(s)
               Report  Collection
                Year      Year
Sampling
 Area
Fish
Tissue(s)
Parameters
o
VO
Clark et al.      1982      1980                                                     Heptachlor
(cont.)                                                                             Heptachlor epoxide
                                                                                     BHC
                                                                                     BHC (Lindane)
                                                                                   Dacthal
                                                                                   pentachioro-pheny methyl ether
                                                                                   Hexachlorobutadiene
                                                                                   1,2,3,4-Tetrachlorobenzene
                                                                                   Chloryrifos
                                                                                   Diazinon
                                                                                   Trifluralin
                                                                                   8, monohydromirex

1. Three composites of 5 fillet samples each were analyzed for k tributaries in Lake Erie as well as for tributaries
  in all the Great Lakes
2. Lipid content was not analyzed
3. Selection of sites not based on agricultural or industrial use but where 15 echo's could be obtained.
      WB = Whole Body
      F = Fillets

-------
                                   TABLE 81

 FISH SAMPLES1 COLLECTED FROM LAKE ERIE TRIBUTARY MOUTHS FOUND IN EXCESS
          OF IJC^ AND FDAJ LIMITS ON FISH TISSUE CONCENTRATIONS - 1979
                           (Taken from Burby et al. 1981)
Contaminant
 Limit (UR/R)  Tributary     Species     Age
IJC         FDA
 Concentration
Group  (ug/g)
DDT and Metabolites 1.0
(sum total) (whole fish)
Mirex Detection
Limit










Sandusky
Black
Raisin
Maumee
Maumee
Maumee
Maumee
Maumee
Sandusky
Sandusky
Sandusky
Sandusky
Sandusky
Sandusky
Channel Catfish
Carp
Spottail Shiner
Gizzard Shad
Spottail Shiner
Yellow Perch
White Bass
Carp
Freshwater Drum
Freshwater Drum
Gizzard Shad
White Bass
White Bass
Carp
VI
IX
I
0
I
II
0
IV
0
I
0
I
II
IV
2.34
1.55
0.05
0.03
0.02
0.01
0.03
0.03
0.04
0.02
0.06
0.02
0.04
0.02

-------
                              TABLE 81 CONTINUED
              .1
  FISH SAMPLES  COLLECTED FROM LAKE ERIE TRIBUTARY MOUTHS FOUND IN EXCESS
          OF I3C AND FDAJ LIMITS ON FISH TISSUE CONCENTRATIONS - 1979
                           (Taken from Bur by et al. 1981)
Contaminant
Limit (ug/g) Tributary    Species      Age
Concentration
IJC FDA
Mirex (cont'd.) Detection Sandusky
Limit Black
Black
Cuyahoga
Chagrin
Chagrin
Grand
Grand
Ashtabula
Ashtabula
Total PCBs 5.0 Raisin
(edible Raisin
portion) Raisin
Sandusky
Group
Channel Catfish
Spottail Shiner
Freshwater Drum
Gizzard Shad
Gizzard Shad
Emerald Shiner
Emerald Shiner
Gizzard Shad
Gizzard Shad
Emerald Shiner
Carp
Spottail Shiner
Brown Bullhead
Channel Catfish
VI
I
0
0
0
I
I
0
0
I
IV
I
II
VI
(ug/g)
0.02
0.04
0.04
0.01
0.02
0.04
0.01
0.03
0.02
0.01
17.60
5.76
9.6
5.1
 All samples were homogenates of whole fish.
 International Joint Commission (1978)
 Food and Drug Administration (1978)

-------
                 PLAN IMPLEMENTATION
                 AND LAKE ASSESSMENT
           INTERNATIONAL JOINT COMMISSION


                    Water Quality Board


             Water Quality Program Committee


                  Surveillance Work Group


                   Lake Erie Task Force


            Lake Erie Technical Assessment Team
         Lake Erie Surveillance Plan Implementation
          a.    Intensive Surveys (1978-1979)
          b.    Annual Survey (1980)
          c.    Lake Assessment
Figure 1.  Organizational   Structure   Responsible   for   the
          Implementation of the Lake Erie Study Plan  (Taken
          from Herdendorf, 1981).
                        F-l

-------
-n
ro
      Topic

   A. MAIN LAKE

1.  Main Lake Monitoring Report
2.  Oxygen Studies
3.  Sedimentation/Carbon Flux
4.  Sediment Oxygen Demand
5.  Lake Response to Nutrient Loading
6.  Lake Circulation
7.  Lake Physics Studies
   a. Interbasin transfer
   b. Nearshore-offshore movement
   c. Vertical drift

   B. NEARSHORE

1.  Canadian Nearshore
2.  Western Basin, U.S.
3.  Central Basin, U.S.
4.  Eastern Basin, U.S.
5.  Cladophora
6.  Cleveland Intakes
7.  Toledo/Maumee Bay

   C. INPUT AND  PROBLEM AREAS

1.  NY Beaches, Tributaries, Intakes
   and Pt. Sources
2.  PA Beaches, Tributaries, Intakes
   and Pt. Sources
3.  OH Beaches, Tributaries, Intakes
   and Pt. Sources
                                          Organization
                                          Responsible
                                          USEPA/CLEAR
                                          NWRI/CCIW
                                          NWRI/CCIW
                                          CLEAR/NWRI
                                          USEPA/LLRS
                                          NOAA/GLERL
                                          NWRI/CCIW
MOE
OSU/CLEAR
Heidelberg Coll.
SUNY/GLL
SUNY/GLL
NOACA
TPCA
                                          NYSDEC

                                          ECDH

                                          OEPA
4. MI Beaches, Tributaries, Intakes, Point
   Sources and and Detroit River
5. ONT Beaches, Tributaries, Intakes, Point
   Sources, and Niagara River
6. Tributary, Point Source, and Atmospheric
   Loading
7. Meteorological/Hydrological Summary

   a CONTAMINANTS

1. Radioactivity
2. Fish Contaminants
3. Wildlife Contaminants

   E. DATA QUALITY

1. Data Quality Report
2. Data Management Report
3. Field and Lab. Procedures

   F. SPECIAL CONTRIBUTIONS

1. Fish Stock Assessment
2. Remote Sensing Experiments
3. Wastewater Management Study
4. Tributary and Storm Event
   Reports
5. Phosphorus Management Study
6. Primary Productivity Study
                                                                Organization
                                                                Responsible
                                                                MDNR

                                                                MOE

                                                                I3C

                                                                NOAA/GLERL
                                                                                                          I3C
                                                                                                          USEPA/USF&WS
                                                                                                          Canada Wildlife
                                                                                                          I3C
                                                                                                          DC
                                                                                                          I3C
                                                                GLFC
                                                                NASA
                                                                USACOE
                                                                USGS

                                                                I3C
                                                                NWRI/CCIW
                                                                OSU/CLEAR
   Figure 2.
                  The Major Organizations and Participants Involved in the Two-Year Lake Erie Plan (taken from Herdendorf,
                  1981).

-------
          fV/s     V
                                                                       . Station Number
                                                                       • Beginning Sampling Day

                                                                       * End Sampling  Day

                                                                      ~~ Cruise Track
                                                                      •- Travel Between Cruise Days
FIGURE  3.  REPRESENTATIVE CRUISE TRACK USED BY USEPA-GLNPO  DURING 1978
          (TAKEN FROM CRUISE 7, AUGUST 29 - SEPTEMBER 6).

-------
                                     TEMPERATURE  C  O
Q.
LU
Q
     10.0
     20.0
     30.0r
     40.0
     50.0
     60.0
                                  — EASTERN BASIN
                                   ••• CENTRAL BASIN
                                  — WESTERN BASIN

                                   D SAMPLE DEPTH
          FIGURE 4.
SCHEMATIC REPRESENTATION OF THE HORIZONS SAMPLED
IN THE THREE BASINS DURING THE STRATIFIED SEASON.

-------
                                                                                  Cruise Track
                                                                                •  Station Number
                                                                                •  End Track
FIGURE 5.  REPRESENTATIVE CRUISE TRACK USED BY  CCIW-NWRI  DURING  1978  (TAKEN FROM CRUISE  103, May  15 - June 2).

-------
                                                                              •  Station  Number
                                                                              •  Beginning Sampling Day
                                                                              *•  End Sampling Day
                                                                                 Cruise Track
FIGURE 6.  REPRESENTATIVE CRUISE TRACK USED BY CCIW-NWRI
           DURING 1979 (TAKEN FROM CRUISE 103, MAY 15 - MAY 18),

-------
                    CONCENTRATION CUG/L)
o
m
xj
&
•o
o
(O
o
H

-------
    108. 0T
            CENTRAL BASIN 1078
     80.0

     70.0
I
fe
50.0

40.0

30.0-

20.

10.

 0.0
                                                             -NVRI
                                                      ©-USEPA-GLNPO
              APR    MAY    JUN    JUL    AUG    SEP    OCT    NOV    DEC
            EASTERN BASIN 1978
     70.

     80.0-

     50.0

     40.0

     30.0

     20.

     10.

      0.0
                                                 3K-CCW-NVRI
                                                 0-USEPA-GLNPO
                             
-------
                Monroe
    01-010
    M26-K27
               0      8      16   Point
              Scale 1n Kilometers
                                                                      Reach 13
                                                        lUach 17

                                                        0102-0139
                                                                         AshtibuU
                                                          B   16
                                                     Scale in Kilometers
   torrieaut


FIGURE  9.
                                 Reach 19
                                                                             Buffalo
                                             0   8  16
                                         Scale in Kilometers
U.S.  NEARSHORE  STATION  PATTERN  AND  REACH
DESIGNATION FOR 1978 and 1979.
                               F-9

-------
Lo»s Point
                               0
                               Sc*1t In
                                            16
                               185  201
                               186  207
                               190  213
                               192  217
      236  2S7
      2*2  2S9
      24<  260
      2SO  262
      254  264
      2SS  26S
          2C6
          •39
       8   16
Stile 1n Kilometers
                                           28C  289
                                           281  293
                                           283  295
                                           285  296
                                           287  299
                    16
       Sct'e'ln Kilometers
            FIGURE  10.   CANADIAN  NEARSHORE STATION
                           PATTERN AND  REACH DESIGNA-
                           TION  FOR  1978 AND 1979.
                               F-10

-------
     25.0
     20.0
U
LJ
o:

i-

o:
LJ
Q_
15.0
      10.0
       5.0
       0.0
                                     EASTERN BASIN CCIV


                                     CENTRAL BASIN CCIV


                                   A VESTERN BASIN EPA
                                                                     -i	L.
                 APR     MAY    JUN     JUL     AUG    SEP     OCT    NOV     DEC
          FIGURE  11.   OPEN LAKE SEASONAL SURFACE TEMPERATURE PATTERN

                       RECORDED FOR ALL THREE BASINS  IN  1979.

-------
TEMPERATURE C O

-------
                                                                  July 31-
                                                                    August 4
FIGURE 13.   SEASONAL PATTERN OF HYPOLIMNION THICKNESS (m)  AS RECORDED
            IN THE CENTRAL  AND EASTERN BASINS OF LAKE ERIE DURING THE
            1978 CCIW-NWRI  FIELD SEASON.

                                F-13

-------
                                                                  August 19-
                                                                  August 23
                                                                 September 13-
                                                                 September 19
                                                                September 30-
                                                                October 4
FIGURE 13.  Continued
                                F-14

-------
                                    TEMPERATURE  C C)
      0.0
     10.0
CL
LU
Q
15.0
     20.0
     25.0
         FIGURE 14.
                REPRESENTATIVE SEASONAL THERMAL STRUCTURE
                FOR THE CENTRAL BASIN AS RECORDED BY
                CCIW-NWRI AT STATION 12 C1078).

-------
                                10,0
                       15.0
20.0
25.0
     10.0
     20.0
Q.
LU
a
     30.0
     40.0J-
     50.0
     60.0
          FIGURE 15.
REPRESENTATIVE SEASONAL THERMAL STRUCTURE

FOR THE EASTERN BASIN AS RECORDED BY

CCIW-NWRI AT STATION 4 C1979).

-------









^^
-J
2E
w
o
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T^_
*i
•
LU
0
"Z.
o
u




16.0


14.0



12.0



10.0

8.0

6.0


4.0

2.0

fl a
-
A .
• » * *
A" '>
A
* * % ^^^* ^
'• **' X »*' **•»

t A'
^•^ t * <
\ A*'* ^ 	 -©
\ /
\ ^-®^^\ y
\^*^^ \^-^* i
.
EPILIMNION ©DISSOLVED OXYGEN ^
A X SATURATION

•
.
K
'

120.0

110.0

100.0


90.0


80.0

70.0
60.0
50.0
40.0


30.0
20.0

10.0
a ci












O)

-H
i— <
o








       APR    MAY    JUN     JUL     AUG    SEP    OCT    NOV     DEC
FIGURE 16.  THE MEAN WESTERN BASIN DISSOLVED OXYGEN CONCENTRATIONS
            AND PERCENT SATURATIONS FOR  1978 USEPA - GLNPO.

-------
                                                HYPOLIHHON
                                        Cle
                                                  cut
              APR    HAY    JUN    JUL    AUG    SEP    DCT    NOY    DEC
§
1-4
I-


55
X
130. t
120.8
110.8
100.0
 98.0
 80.0
 70.0
 88.0
     40.
     38.0
     20.0
     IflLi
      0.
                                                             DEPILIMUQN
               APR   HAY    JUN    JUL    AUG   SEP    OCT    MOV    DEC
          FIGURE 17.  THE MEAN CENTRAL BASIN DISSOLVED OXYGEN
                      CONCENTRATIONS  AND PERCENT  SATURATIONS
                      FOR 1978 CCIY - NWRI.
                                   F-18

-------

-------
                                                   August 19-August  23
                                                   Hypo! i mm'on
                                                   September  13-September  19
                                                   Hypolimnion
                                                   September 30-October 4
                                                   Hy poll mm'on
FIGURE 18.   Continued.
                                F-20

-------
16. fl
14. fl
12.0

10.8

8.8
6.8
4.0
2.0
a a

G





•




42 -
*- e


HYPOLIMNION
A ~
c




382"
C





JK
E





377 E




177""
C*2




    150,1
    140.1
    130.1
    120.1
    110.1
    100.1
§    90.1
£    80.1
|    70.1
£    60.1
x    50.1
     40.1
     30.1
     20.1
     10.1
      0.1
                                 •O---O
O HYPOLIMNION
d EPILIMNION
                APR    MAY    JUN    JUL    AUG    SEP    OCT    NOV     DEC
          FIGURE 19.   THE MEAN EASTERN BASIN  DISSOLVED OXYGEN
                        CONCENTRATIONS  AND PERCENT SATURATIONS
                        FOR 1978 CCIV - NWRI.
                                    F-21

-------
                                                   nay 29-June 2
                                                   Epilimnion
                                                   May 29-June 24
                                                   Epilimnion
                                                   June 19-June 24
                                                   Epilimnion
                                                   June 19-June 24
                                                   Hypolimnlon
FIGURE 20.  THE SEASONAL  EPILIMNION AND liYPOLIMNION TOTAL PHOSPHORUS
            (ug/1)  DISTRIBUTION PATTERNS FOR THE CENTRAL AND EASTERN
            BASINS  OF LAKE  ERIE FOR 1978 (CCIW-NWRI).

                              F-22

-------

-------
                                                   September 13-September 19
                                                   Epilimnion
                                                   September 13-September 19
                                                   Hypolimnion
                                                   September 30-October 4
                                                   Epilimnion
                                                   September 30-October 4
                                                   Hypolimnion
FIGURE 20.  Continued
                                F-23

-------
                      CONCENTRATION  CUG/L)
                      •--   r\>
  TI
  m
o -H

is
o
m s
z m
-H >

>
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O (/)
  m
  77
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-------
                  CONCENTRATION OJG/U
                                     CONCENTRATION CUG/O
GO



O



I
                  v .  y . ? . y
                                 1-4
                                 s
t
 t
               •-f
                                             8
                                  y.y.y.y.y.y.y.y.y.y.y
                                  >-r
t
                                                    i	1

-------
40.0r

35. £

30.0J-

25.0-

20.0

15.

10.

 5.0f
 0.0L
                                                      B>ILIMNION
                            CJlli
                                              c alii J47
         APR    MAY    JUN    JUL    AUG    SEP    OCT    NOY    DEC
70.0r
50.0-


40.0

30.0


20.0f


10. B
 0.0
                                                      HYPOLIMNIQN

           APR    MAY    JUN    JUL    AUG    SEP    OCT    NOV     DEC
     FIGURE 23.  THE MEAN EASTERN BASIN EPILIMNION AND
                  HYPOLIMNION  TOTAL PHOSPHORUS  CONCENTRATIONS
                  FOR 1978  (CCIW - NWRD.
                               F-26

-------
130.0
120.0
110.0
100.0
3 90.0
8 80.0
2 70B0
£ 60.0
tt
£ 50.0
LU
S 40.0
8 30.0
20.0
10.0
a a
-
•
•
>
-
•
•
•

M
1
•



-MAX 218

•
•



^JLmm






EPILIHNION
27

^»
1 i
»
^m
^
[
329
^
M»
••
— «•
1
JB
i"i
•w
•M
^
1 1
L
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™ M
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1 1
1 LM»
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•
•

••
MAX 248


•M

•[

M

t [


3»


      APR     MAY    JUN    JUL    AUG     SEP     XT    NOY
DEC
FIGURE 24.  THE MEAN WESTERN BASIN TOTAL PHOSPHORUS
            CONCENTRATIONS FOR 1979  OJSEPA-GLNPO).

-------
                 CONCENTRATION OJG/O
                             CONCENTRATION CUG/D
        i
P
             y..?. .y. .*. .». .*..». .*. .y. .y     y. .y. .y. .y..». .*. .y. .y. .y..». .y
                      "-f-1
•F
                                             is
                                                              i—§—t
                                        f
                                                      i—e—i
i—a	1
                                t
                                                         i—?

-------
98.1
27.1
24.1
2tl
18.1
15.1
12.1
 0.1
 6.1
 3.1
 B.BL
                              [L
                                         Lie
                                                C17
         APRNAYJUNJULAUGSEPOCTNOVDEC
30.1
27.1
24.1
21.1
12.1
 9.1
 8.1
 3.1
 0.1
       HYPOLIMNION
                        [L  [fe
EL
         APRMAYJUNJULAUGSEPOCTNOVDEC
     FIGURE 26.   THE MEAN EASTERN BASIN  EPILINNION AND
                  HYPOLINNION TOTAL PHOSPHORUS CONCENTRATIONS
                  FOR 1979  (CCI1HWRI).
                              F-29

-------
                          CONCENTRATION CUG/L)
                                                         CONCENTRATION  CUG/O
   •— •  m

   o  m

o »—••—•
o •<.  r-
»—• m  •—•
              s
                 IT1
                  KB
t
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                                     y   .  it
                                                                     -t-
                                                                                                        9

-------
38.
                EPILIKttDN
d 20.01-
1 15-|
| *4
5.0|
at
10.8
9.0
8.0
3 7.i
| 6.0
§ S.S
1 4.0
I 3.0
2.0
1.0
0.0
?"•
! - - - i 	 , .-L. .-

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APR MAY JUN JUL AUG SEP OCT NOV DEC






r

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•t
c
A



16 C

3»-r
•J-
         APR    MAY   JUN    JUL    AUG   SEP    OCT    NOV   DEC
    FIGURE 28.  THE MEAN EASTERN BASIN EPILIMNION AND
                HYPOLIMNION  SOLUBLE REACTIVE PHOSPHORUS
                CONCENTRATIONS FOR 1978 (CCIW-NWRI).
                            F31

-------
                                                  July 31-August 4
                                                  Hypolimnion
                                                  August  19-August 23
                                                  Hypolimnion
                                                   September 13-September  19
                                                   Hypolimnion
                                                   September 30-October 17
                                                   Hypolimnion
FIGURE 30.   CONTINUED

-------
     78.

     68.


1    *

3    48.
t-»    ^*»

     38.

     28.

     IB.

     a.
            BWJIMION
L.L
    188.1
             APR    MAY    JUN    JUL   AUG    SEP    OCT   NOV    DEC
           HYPOLItWCN
                                                Cfc7
              APR   MAY    JUN    JUL   AUG    SEP    OCT   NOV    DEC
         FIGURE 31.  THE MEAN CENTRAL BASIN EPILINNION AND
                     HYPOLINNION AMMONIA CONCENTRATIONS
                     FOR 1978 (CCIV-NVRD.
                                 F-35

-------
CONCENTRATION OJG/D
                                                             CONCENTRATION OJG/O
P   jS    $    £
                                            $"
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-------
                                                   May 29-June 2
                                                   Epilimnion
                                                   May 29-June 2
                                                   Hypolimnion
                                                   June 19-June 24
                                                   Epilimnion
                                                   June 19-June 24
                                                   Hypolimnion
FIGURE 33.  THE SEASONAL EPILIMNION AND HYPOLIMNION NITRATE PLUS NITRITE
            (mg/1) DISTRIBUTION PATTERNS FOR THE CENTRAL AND EASTERN
            BASINS OF LAKE ERIE FOR 1978 (CCIW-NWRI).
                                F-37

-------
                                                   July 13-July 18
                                                   Epilimnion
                                                   July 13-July 18
                                                   Hypolimnion
                                                   July 31-August 4
                                                   Epilimnion
                                                   July 31-August 4
                                                   Hypolimnion
FIGURE 33.  Continued
                               F-38

-------
                                                   August 19-August 23
                                                   Epilimm'on
                                                   August 19-August 23
                                                   HypollmnIon
                                                   September 13-September 19
                                                   Epillmnion
                                                   September 13-September 19
                                                   Hypolimnion
FIGURE 33.  Continued
                                F-39

-------
                                                   September 30-October 4
                                                   Epilimnion
                                                   September 30-October 4
                                                   Hypollmnlon
FIGURE 33.  Continued
                                F-40

-------
           1100
            700
2    £
     K
     8     300
            100



              0
                                  -r- WX14M
EPILIMNION
                                       C3Z7
                     APR    MAY     JUN    JUL     AUG
                                              OCT     NOV     DEC
               FIGURE 34.   THE MEAN WESTERN BASIN NITRATE PLUS NITRITE

                            CONCENTRATIONS FOR  1978  CUSEPA-GLNPO).

-------
                      CONCENTRATION CUG/U
                                            CONCENTRATION •
232
  5
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-------
700.1
        EPILIKJION
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400.1

300.1

200.1

100.1

  0.0L
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     calft
          APR    MAY    JUN    JUL    AUG    SEP    QCT    NOV    DEC
400.1
350.1
300.1
250.1
        HYPQLINNIQN
158.1

100.1

 50.1
                                      odtt
                                                tarn
          APR    MAY    JUN    JUL    AUG    SEP    OCT    NOY    DEC
      FIGURE  36.   THE MEAN EASTERN BASIN EPILIMNION AND
                   HYPOLIMNION  NITRATE  PLUS NITRITE CONCENTRATIONS
                   FOR 1978 CCCIY-NYRI).
                                F-43

-------
                                                  May 29-June 2
                                                  Epilimnion
                                                  June 19-June 24
                                                  Epilimnion
                                                  duly 13-July 18
                                                  Epilimnion
                                                  July 31-August 4
                                                  Epilimnion
FIGURE 37.   THE SEASONAL EPILIMNION DISSOLVED SILICA (ug/1) DISTRIBUTION
            PATTERNS FOR THE CENTRAL AND EASTERN BASINS OF LAKE ERIE FOR
            1978 (CCIW-NWRI).    M4

-------

-------
3KU0U
2700
2400
3 2100
o
3 1800
z
2 1500
| 1200
UJ
z 900
u
600
300
a
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APR    MAY    JUN     JUL
AUG
                                          SEP
OCT    NOV
DEC
FIGURE 38.  THE MEAN WESTERN BASIN DISSOLVED SILICA
            CONCENTRATIONS FOR  1978 OlSEPA-GLNPO).

-------
                           CONCENTRATION CUG/D
CONCENTRATION CUG/D
                                                                                      •-»
                                                                                      p

               1
•-i -< ac
r— 3 m
2
      !S       !S

	 	 	 1 «-,
1 i
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1 P 1 £
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to
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• iiiiii*iiiiiiiii
-------
   3158.1
p  2458.1
|  2188.1
§  1758.1
   1488.1
   1858.1
    788.1
    358.1
      8.1
                EPILINNIQN
                APRHAYJUNJULAUGSEPOCTNOVDEC
     1880
     1688
     1488
     1288
      408
      200
HYPOLIMNION
                                                   E XB
                APRMAYJIUJULAUGSEPOCTNOVDEC
          FIGURE 40.  THE NEAN EASTERN BASIN EPILINNION AND
                       HYPOLINNION CONCENTRATIONS OF DISSOLVED
                       SILICA FOR 1978  (CCIV-NVRD.
                                    F-48

-------
                                                   May  18-May 27
                                                   Epilimnion
                                                   June 5-June 15
                                                   Epi 11 mm'on
                                                   June 23-July 1
                                                   Epilimnion
                                                   July 9 - July 29
                                                   Epilimnion
FIGURE 41.  THE SEASONAL EPILIMNION CORRECTED CHLOROPHYLL a. (ug/1)
            DISTRIBUTION PATTERNS FOR THE CENTRAL AND EASTERN BASINS
            OF LAKE ERIE FOR 1978 (USEPA-GLNPO).
                               F-49

-------
                                                      August 8-August 16
                                                      Epilimnion
                                                     August 29-September 6
                                                     tpilimnion
                                                    October 24-November 1
                                                    tpilimnion
                                                   November 10-November 19
                                                   Epilimnion
FIGURE 41.  Continued
                                F-50

-------

-------
                                                 August 19- August 23
                                                 Epilimnion
                                                 September 13- September 19
                                                 Epilimnion
                                                 September 30- October 4
                                                 Epilimnion
FIGURE  42.  CONTINUED
                              F-52

-------
CO
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55
45
^ 40
3 35
° on
M 30
| 25
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a 20
8 15
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                      APR
MAY    JUN     JUL     AUG    SEP    OCT     NOV     DEC
               FIGURE 43.  THE MEAN WESTERN BASIN CORRECTED
                            CHLOROPHYLL A CONCENTRATIONS
                            FOR 1978  OJSEPA-GLNPO).

-------
30
27
24
21
18
15
12
9
8
3

30
27
24
21
18
15
12
9
8
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     APR   MAY    JUN    JUL    AUG    SEP    OCT    NOV   DEC
FIGURE 44.  THE MEAN CENTRAL BASIN EPILIMNION  AND
            HYPOLIMNION CORRECTED CHLOROPHYLL  A
            CONCENTRATIONS FOR 1978  (USEPA-GLNPO).
                        F-54

-------
20
18
18
14
12
10
 8
 8
 4
 2
                                     EPILINNION
       APR    MAY    JUN    JUL    AUG    SEP    OCT    NOV    DEC
20
18
18
14
12
10
 8
 8
 4
 2
 0
          HYPOLIMNION
c
•
In
C
••
3W [

IT T I*
- i18 & z11
         APR   MAY    JUN    JUL    AUG    SEP    OCT    NOV    DEC
    FIGURE 45.  THE MEAN EASTERN BASIN EPILIMNION AND
                  HYPOLIMNION CORRECTED CHLOROPHYLL A
                  CONCENTRATIONS FOR 1978  (USEPA-GLNPO).
                            F-55

-------
     1200
§    m
     200
                EPILINNIQN
                           GSt
                               E3112
                                             on*
              APR    KAY    JUN   JUL    AUG    SEP    OCT    NOV    DEC
     1600

     1600

     1400

     1200
     400
       0
HYPOLINNION
                           C 372 B 387
                                            [fo  EJ27
             APR    MAY    JUN    JUL    AUG    SEP    OCT    NOV    DEC
         FIGURE 46.  THE MEAN CENTRAL BASIN EPILINNION AND
                      HYPOLINNION PARTICULATE ORGANIC CARBON
                      CONCENTRATIONS FOR 1978  (CCIV-NVRI).
                                  F-56

-------
sy
oo m
                    CONCENTRATION CUG/U
           s
           H
               •-fr
*\—•
                                            CONCENTRATION CUG/L)
                                                                 i  i  s  i  e  i  i
                                                f
3	—I
                                                    t
                                                                   r

-------
in
00
            FIGURE  48.   THE  1978  SEASONAL MEAN  DISTRIBUTION  PATTERN  OF TOTAL  SUSPENDED SOLIDS (mg/1)
                        FOR  CENTRAL  AND  EASTERN BASINS OF  LAKE  ERIE  (USEPA-GNNPO).

-------
       enuMtnM
                                         -r MY 441
1811
16.1
HI
12.1
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10.1
 911
 8.1
 7.1
 6.1
 5.1
       WPQUNNION
                                         tb
        APRMAYJUNJULAUGSEPOCTNOVDEC
    FIGURE 49.   THE MEAN CENTRAL BASIN EPILINNION AND
                 HYPOLIMNION TOTAL SUSPENDED SOLIDS CONCENTRATIONS
                 FOR 1978 (USEPA-GLNPO).
                             F-59

-------
       EWLDWW
                                         Eta
                                                Ek  C
         APRNAYJUNJU.AUGSEPOCTNOVIEC
a. i
18.1
lfl.1
14.1
12.1
18.1
 8.1
 8.1
 4.1
 2.1
 8.1
HTPOLMHMN
                             [I?
         APRMAYJUNJULAUGSB>OCTNOVDEC
     FIGURE 58.  THE MEAN EASTERN BASIN EPILIMNION AND
                 HYPOLIMNION TOTAL SUSPENDED SOLIDS  CONCENTRATIONS
                 FOR 1978 (USEPA-GLNPO).

-------
50.0
45.0
40.0
G 35.0
o
5 30.0
2 25.0
£ 20.0
LU
§ 15.0
o
10.0
5.0
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      APR    MAY    JUN    JUL     AUG    SEP    OCT    NOV     DEC
FIGURE 51.  THE MEAN WESTERN BASIN  TOTAL SUSPENDED
            SOLIDS CONCENTRATIONS FOR 1978 OJSEPA-GLNPO).

-------
a
i—i
m

:D
40.0




35.0




30.0




25.0




20.0




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            APR     MAY    JUN    JUL     AUG    SEP     OCT     NOV    DEC
    FIGURE 52.   THE MEAN WESTERN BASIN TURBIDITY

                 VALUES FOR 1978 OISEPA-GLNPO).

-------
1-4
Q
28.1
18.1
18.1
14.1
12.1
18.1
 8.1
 8.1
 4.1
 2.1
 8.1
                                                          HH&4 -r
            B>ILIMNION
                                                can
                APRMAYJUNJU.AUGSEPOCTNOYDE
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 1.1
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             HTPOLIUCON
                                            []•
                                                        • •••*	
                APRMAYJUNJULAUGSEPOCTNOVDEC
          FIGURE 53.   THE MEAN CENTRAL BASIN EPILINNION AND HYPOLINNION
                        TURBIDITY VALUES FOR 1978 (USEPA-GLNPO).
                                    F-63

-------
s
311
27.1
24.1
21.1
iai
15.1
12.1
 9.1
 8.1
 3.1
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              APRNAYJUNJULAUGSB>OCTNOVOEC
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 8.1
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                                  f'Mk
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              APRNAYJUNJULAUGSffOCTNOVOEC
         FIGURE 54.   THE MEAN EASTERN BASIN EPILINNION AND HYPOLINNION
                     TURBIDITY VALUES FOR 1978 (USEPA-GLNPO).
                               F-64

-------
01
vU V
4.5
4.0
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x 2.5
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1.5
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                     APR     MAY    JUN    JUL     AUG    SEP    OCT     NOV    DEC
               FIGURE 55a.  THE MEAN WESTERN BASIN SECCHI VALUES
                            FOR 1978  OJSEPA-GLNPO).

-------
15.1
13.!
12.1
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 II
 7.!
 flu I
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 9.1
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EPILHNION
 CENTRAL BASIN
                                    llm    T
  APRNAYJUNJULAUCSffQCTNOVOEC
EPILDMION
EASTERN BASIN
                                                 EkEk
         APRMAYJINJULAUGSEPOCTNOVDEC
     FIGURE 55b.   THE NEAN CENTRAL AND EASTERN BASIN SECCHI
                    VALUES FOR 1978 (USEPA-GLNPO).
                               F-66

-------
C7»




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9.0
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r A
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                      APR    MAY     JUN     JUL    AUG    SEP     OCT     NOV    DEC
               FIGURE 56.  THE CENTRAL AND EASTERN  BASIN SECCHI
                           RATIOS BASED UPON A  NORMILIZATION OF
                           THE 1978 WESTERN BASIN VALUES.

-------
                                                        Alkalinity ( mg/l )
                                                        as CaCps
                                                        Epilimnion
                                                         Conductivity  ( umhos/cm )
                                                         Epilimnion
                                                         Calcium  ( mg/l )
                                                         Epilimnion
                                                        Sulfate  ( mg/l )
                                                        Epilimnion
FIGURE 57.   THE DISTRIBUTION PATTERNS FOR EPILIMNION CONCENTRATIONS
            OF PRINCIPAL  IONS MEASURED DURING JUNE 1978 (USEPA-GLNPO).
                               F-68

-------
(I/BO,.

-------
                    CONCENTRATION CMG/U
    is
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co •—• n

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-------
      28

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        APRMAYJUNJILAUGSEPOCTNOVDEC
28

28

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14
                HYPOLimiON
       APRMAYJUNJULAUGSEPOCTNOYDEC
   FIGURE 59.  THE MEAN EASTERN BASIN EPILIHNION AND
                HYPOLIMNION CHLORIDE CONCENTRATIONS
                FOR 1978 (USEPA-GLNPO).
                             F-71

-------
24
22
20
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       APR    MAY     JUN    JUL    AUG    SEP     OCT    NOV    DEC
FIGURE 60.  THE MEAN WESTERN  BASIN CHLORIDE CONCENTRATIONS
            FOR 1978 .

-------
D
LU
O
       50
       45
       40
       35
       30
       25
       20
       15
                  EPILIMNION
                                    Eb
                                                                     Cie
               APR     MAY     JUN    JUL    AUG     SEP    OCT    NOY    DEC
          FIGURE 61.   THE MEAN WESTERN BASIN SULFATE  CONCENTRATIONS

                      FOR 1978 CUSEPA-GLNPO).

-------
35
33
31
29
27
25
23
21
19
17
15
                   EPILINNIQN
                                       Cte
                                               COM
         APRMAYJUNJULAUGSEPOCTNOVDEC
35
33
31
28
27
25
23
21
19
17
15
HYPQLINNIQN
         APR   MAY    JUN    JUL    AUG    SEP    OCT    NOV    DEC
    FIGURE 62.   THE MEAN CENTRAL BASIN  EPILINNION AND
                 HYPOLIMNION SULFATE CONCENTRATIONS
                 FOR 1978  (USEPA-GLNPO).
                             F-74

-------
CONCENTRATION O4G/U
CONCENTRATION CMG/O
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sig s
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-------

-------
                                                   Cadmium  ( ing/kg )
                                                   Surface Sediment
                                                   Chromium  ( ing/kg )
                                                   Surface Sediment
                                                   Lead  ( mg/kg )
                                                   Surface Sediment
                                                   Copper  ( mg/kg )
                                                   Surface Sediment
FIGURE  64.  CONTINUED
                               F-77

-------
64.
                    ^

-------
                                                       Silver  ( mg/kg )
                                                       Surface Sediment
                                                       Barium  ( mg/kg )
                                                       Surface Sediment
                                                       Vanadium  ( mg/kg )
                                                       Surface Sediment
FIGURE 64.  CONTINUED
                       F-79

-------
FIGURE 65a.   THE DISTRIBUTION PATTERN OF METAL  CONCENTRATIONS BASED
             UPON CLUSTER ANALYSIS FOR LAKE ERIE SURFICIAL SEDIMENTS
             IN 1979.
                                                                Non depositional

                                                                Depositional
FIGURE 65b.  THE MAJOR SEDIMENT DEPOSITIONAL AREAS IN LAKE ERIE
             (THOMAS, ET AL,  1976).
                                F-80

-------
                                                          less than 300

                                                          300- 999
                                                          1000-2000

                                                          greater than 2001
FIGURE 66a.
THE DISTRIBUTION  PATTERN OF MERCURY CONCENTRATIONS (mg/kg)
IN THE SURFICIAL  SEDIMENTS OF LAKE ERIE DURING 1970
(THOMAS AND JAQUET,  1976).
FIGURE 66b.  THE DISTRIBUTION PATTERN OF MERCURY CONCENTRATIONS
            (mg/kg) IN THE SURFICIAL SEDIMENTS OF LAKE  ERIE
            DURING 1979.
                              F-81

-------
                                                                            •  Sampling location 1978

                                                                               Sampling location,
                                                                               1978 and 1979
FIGURE 67.   PHYTOPLANKTON SAMPLING  LOCATIONS  FOR  1978
            AND THE MODIFIED 1979 COLLECTION  SITES
            (USEPA-GLNPO).

-------
s
CO
           18.0

           16.0

           14.0

           12.0
     ^    10.0
     o
     »—i
     m
8.0

6.0

4.0

2.0

0.0
             1978
             1979
                      APR    MAY    JUN     JUL     AUG
                                                      XT    NOY    DEC
               FIGURE 68.   SEASONAL FLUCTUATIONS  IN WESTERN BASIN TOTAL
                           PHYTOPLANKTON BIOMASS  FOR
                           1978 AND 1979 CUSEPA-GLNPO).

-------




0)
o
5
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100.0
90.0
80.0
70.0
60.0
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30.0
20.0
10.0
d a




t
t

•
•
•
•
       APR    HAY    JUN    JUL    AUG     SEP     OCT    NOV    DEC
FIGURE: 69.  SEASONAL FLXTUATIONS IN WESTERN BASIN PHYTOPLANKTON
            COMPOSITION FOR 1078 CUSEPA-GLNPO).

-------
                              S8-J
                         X TOTAL BIOMASS
           ea   ea
  p
ss

-------
«

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 O
 1-1
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10.0

 9.0

 8.0

 7.0

 6.0

 5.0

 4.0

 3.0

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                  O 1978
                  A 1979
                                                                     t
                                                                     t
                                                                    *
                                         ...  .
                  APR     MAY    JUN    JUL     AUG     SEP
                                                              NOY    DEC
          FIGURE 71.   SEASONAL FLUCTUATIONS IN CENTRAL BASIN TOTAL
                       PHYTOPLANKTON BIOMASS FOR
                       1978 AND 1979 CUSEPA-GLNPO).

-------
(Jo
CO
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 \
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1.6


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                  01978

                  A 1979
                                                         	A
                                              -A	
                      APR     MAY
                                 JUN
                                 JUL    AUG     SEP     OCT
DEC
               FIGURE 72.  SEASONAL FLUCTUATIONS IN EASTERN BASIN TOTAL

                           PHYTOPLANKTON BIOMASS FOR

                           1978 AND 1979 CUSEPA-GLNPO).

-------



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90.0
80.0
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                                                               Cyanophyta
       APR     MAY     JUN    JUL    AUG     SEP    Oa    MOV    DEC
FIGURE 73.  SEASONAL FLUCTUATIONS IN CENTRAL BASIN PHYTOPLANKTON
            COMPOSITION FOR 1978 CUSEPA-GLNPO).

-------
              X TOTAL BIOMASS
pa   pa

-------



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                                                                   Unk.Flagellate
                                                                   Chrysooonadinae
                                                                    Dinophyclnae
                                                                   Cryptononadinae
        APR    MAY     JUN     JUL    AUG     SEP
XT
NOY
DEC
FIGURE  75.   SEASONAL  FLUCTUATIONS IN EASTERN  BASIN PHYTOPLANKTON
             COMPOSITION FOR 1978  (USEPA-GLNPO).

-------
      I6-J
* TOTAL  BIOMASS
                 1

-------
                                                     temp  15.2
                                                     00   10.2
                                                     00 sat 97.9
                                                     Conn  299
temp  i«.7
00    1C.O
00 Mt 94.5
Cond  359
       temp  ]3.0
       DO   10.7
       DO sat 96.7
       Cond  304
                                                     Keach 1
                                                     CChla 2.4
                                                     TSS
                                                     VS
                                                     SeccM 3.2
FIGURE 77.   MEAN  CONCENTRATIONS FOR  THE  1978 AND 1979  NEARSHORE DATA
              BASE  SUMMARIZED FOR EACH DESIGNATED  REACH  AREA.
                                    F-92

-------
                                      Keach 6

                                      temp    15.3
                                      DO      6.4
                                      00 «t  82.2
                                      Cond   285
t«m?    17.4
DC      9.2
DC Mt  93.0
Cond   286
            temp   9.9
            DO     10.6
            DO stt 93.8
            Cond  282
            CChli 6.6
            TS$   —
            VS
            SeccM 2.1
FIGURE  77.   CONTINUED
                                           F-93

-------
                                          Temp   8.8
                                          DO     9.8
                                          DO s»t 81.1
                                          Cond 281
                                         SiOj 596
                                         Reach 9
                                         CChl.  2.9
                                         TSS
                                         VS
                                         SeccM 0.7
FIGURE 77.    CONTINUED
                                         F-94

-------
                   Monroe
    Reich 11
Te«p
DO
DO S
Cond
 17
  9
 93
387
                  Monroe
                                    «mn 10
                                    TP    101
                                    SRP    6
                                    N*N   596
                                    NN,    91
                                    S10,   879
                                                                                 Reach 13
                                           TP    97
                                           SRP   15
                                           N+K 1053
                                            H,   60
                                            S10, 1248
                                    CChlc  27.3
                                    TSS   28.3
                                           7.6
                                    Secchl  0.7
                                                                                  CCM*  61.7
                                                                                  TSS    42.8
                                                                                        12.4
                                                                                  Secchi  0.3
 FIGURE  77.    CONTINUED
                                         F-95

-------
                                                                      Ashtabula
                                                      Reach 17
        Reach 15

        TP   56
        SRP    9
        N+N  525
        NH,   89
        SiO,
              Reach 16

              TP   55
              SRP  12
              N+N 510
              NH, 276
              SiO, 943
832
                      Cleveland
                                                      Reach 17
                               11   1       XfTl
                                6.8 \    A
                                7;6  x   i
                                 •y\    ?
                                  Cleveland
FIGURE  77.   CONTINUED
                                       F-96

-------
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1. Detroit River 11.
2. Huron River 12.
3. River Raisin 13.
it. Ottawa River 14.
5. Maumee River 15.
6. Portage River 16.
7. Sandusky River 17.
8. Huron River (OH) 18.
9. Black River 19.
•t 10. Rocky River








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                                                                 Grand River (OH)
                                                                 Ashtabula River
                                                                 Conneaut Harbor
                                                                 Dunkirk Harbor
                                                                 Cattaraugus Creek
                                                                 Rush Creek
                                                                 Smokes Creek
                                                                 Buffalo River
                             RIVER  DESIGNATION
FIGURE 78.  SOUTH SHORE  RIVER AND HARBOR  MEAN TOTAL PHOSPHORUS
             CONCENTRATIONS SUMMARIZED FOR 1978 -  1979.

-------
                               66-d



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-------
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3. River Raisin 13.
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6. Portage
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River 16.
. 7. Sandusky River 17.
8. Huron River (OH) 18.
9. Black River 19.
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River -p-
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Conneaut
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FIGURE 80.   SOUTH SHORE RIVER AND HARBOR MEAN AMMONIA
            CONCENTRATIONS SUMMARIZED FOR 1978 AND 1979.

-------
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900


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600
500
400
300
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100
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3. Nanticoke 13. Sandusky Bay
4. Long Point Bay 14. Huron
5. Port Burwell 15. Lorain -i
6. Port Stanley 16. Cleveland
7. Wheatley 17. Fairport
8. Leamington 18. Conneaut
9. Colchester 19. Erie Harbor
10. Monroe 20. Dunkirk
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         FIGURE 81.  MEAN NEARSHORE REACH CONCENTRATIONS

                     OF TOTAL PHOSPHORUS FOR  1978 -  1979.

-------
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                            REACH NUMBER
FIGURE 82.   MEAN NEARSHORE REACH CONCENTRATIONS
            OF SOLUBLE REACTIVE PHOSPHORUS
            FOR 1978 AND 1979.

-------
9000 r !• Colborne 11. Maumee Bay -,-


8000

7000

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3. Nanticoke 13. Sandusky Bay
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5. Port Burwell 15. Lorain
6. Port Stanley 16. Cleveland
7. Wheatley 17. Fairport ~|
8. Leamington 18. Conneaut
9. Colchester 19. Erie Harbor
10. Monroe 20. Dunkirk
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                            REACH NUMBER
FIGURE 83.   MEAN NEARSHORE REACH CONCENTRATIONS OF NITRATE
            PLUS NITRITE FOR 1978 AND 1979.

-------









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FIGURE 84.   MEAN NEARSHORE REACH CONCENTRATIONS OF
              AMMONIA  FOR  1978 AND 1979.

-------
         7000

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           0
. 1. Colborne 11. Maumee Bay
2. Port Maitland 12. Locust Point
3. Nanticoke 13. Sandusky Bay
4. Long Point Bay 1*. Huron
5. Port Burwell 15. Lorain
6. Port Stanley 16. Cleveland
7. Wheatley 17. Fairport
• 8. Leamington 18. Conneaut
9. Colchester 19. Erie Harbor
10. Monroe 20. Dunkirk
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             FIGURE 85.   MEAN NEARSHORE REACH CONCENTRATIONS OF DISSOLVED SILICA

                         FOR 1978 AND 1979.

-------
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3. Nanticoke 13. Sandusky Bay ~T
4. Long Point Bay 14. Huron
- 5. Port Bur well 15. Lorain
6. Port Stanley 16. Cleveland
7. Wheatley 17. Fairport
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9. Colchester 19. Erie Harbor
10. Monroe 20. Dunkirk


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                                      REACH NUMBER
          FIGURE  86.   MEAN  NEARSHORE REACH CONCENTRATIONS OF

                      CORRECTED CHLOROPHYLL A FOR  1978 AND  1979.

-------
10
9
8
7
x 6
x 5
i &
a 4
3
2
1
a
1. Colborne 11. Maumee Bay
2. Port Maitland 12. Locust Point
••
3. Nanticoke 13. Sandusky Bay
r 4. Long Point Bay 14. Huron
5. Port Burwell 15. Lorain
• 6. Port Stanley 16. Cleveland
7. Wheatley 17. Fairport
8. Leamington 18. Conneaut
9. Colchester 19. Erie Harbor
10. Monroe 20. Dunkirk "
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                            REACH NUMBER
FIGURE 87.   MEAN NEARSHORE REACH CONCENTRATIONS OF
            SECCHI  DEPTH FOR 1978 AND  1979.

-------
o

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20 r 1. Colborne


18


16
• mmf

14
12
4 f9
10
6
4
2
a
2. Port Maitland
3. Nanticoke
4. Long Point Bay
5. Port Burwell
6. Port Stanley
7. Wheatley
S. Leamington
9. Colchester
mm
•
r
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mm

mm
—1—
k
ft
, ,
mm
mm
328[]
mm





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11. Maumee Bay
12. Locust Point
13. Sandusky Bay
14. Huron
15. Lorain
16. Cleveland
17. Fairport
IS. Conneaut -i
19. Erie Harbor
2C

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            1   2  3  4   5  6   7  8  9   10  11 12  13  14  15  16 17  18 19  20


                                      REACH NUMBER
         FIGURE  88-   MEAN NEARSHORE REACH CONCENTRATIONS OF

                      DISSOLVED OXYGEN FOR 1978 AND 1979.

-------
200 r *• Colborne 11. Maumee Bay


180


160
mt ^fmf

140
o 120
| 100
i-
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1 • 1
1  2   3   4  5   6  7  8   9  10 11  12  13 14  15  16 17  18 19 20

                          REACH NUMBER
FIGURE 89.
         MEAN NEARSHORE REACH PERCENT SATURATION OF
         DISSOLVED OXYGEN FOR 1978 AND 1979.

-------
              ION  CONCENTRATION AS % OF STANDARD
m
  •—*
  §

-------
100 1- Colborne 11. Maumee Bay


90


80


G 70
5 60
z
2 50
£ 40
UJ
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8
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20
10
01
2. Port Maitland 12. Locust Point
3. Nanticoke 13. Sandusky Bay
k. Long Point Bay 1*. Huron
5. Port Burwell 15. Lorain
6. Port Stanley 16. Cleveland
7. Wheatiey 17. Fair port "J"
8. Leamington 18. Conneaut _,„
9. Colchester 19. Erie
Harbor
10. Monroe 20. Dunkirk

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                            REACH NUMBER
FIGURE 91.   MEAN NEARSHORE REACH CONCENTRATIONS OF
            CHLORIDE FOR  1978 AND  1979.

-------
l-»
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100
90
80
D 70
»— ' MkfV
w 60
| 50
CONCENTRAl
£ £
20
10
fl
MAX 155.3 -i
1. Colborne 11. Maumee Bay
2. Port Maitland 12. Locust Point
3. Nanticoke 13. Sandusky Bay
4. Long Point Bay 14. Huron
5. Port Burwell 15. Lorain
6. Port Stanley 16. Cleveland
" 7. Wheatley 17. Fairport
8. Leamington 18. Conneaut
9. Colchester 19. Erie Harbor
' 10. Monroe 20. Dunkirk
.
N/D FOR 1 - 9
c
•
mm
MB
mm




[
Diee
^m
••*
••



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C
t^
••»



i





mm
3128

mm
| I
i





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MAX 279.8
M




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mm


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mm
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mm-mMl

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m
mm
mm

mm
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••




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mm


.188
imr

                 1   2  3   4  5  6   7  8   9  10 11  12  13  14  15 16  17 18  19  20


                                           REACH NUMBER
              FIGURE 92.
MEAN NEARSHORE REACH CONCENTRATIONS OF

SULFATE FOR 1978 AND 1979.

-------
200
180

160

G 140
o
~ 120
2 100
H~
<
| 80
UJ
o
z 60
o
(J
40
20
a

-



.

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.

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L
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r
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jj W
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^












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-





••

T—
J8
••

_uw P7Qft 1. Detroit River 11. CuyahoRa River
I 2. Huron River 12. Grand River (OH)
3. River Raisin 13. Ashtabula River
4. Ottawa River 14. Conneaut Harbor
5. Maumee River 15. Dunkirk Harbor
6. Portage River 16. Cattaraugus Creek
7. Sandusky River 17. Rush Creek
8. Huron River (OH) 18. Smokes Creek
9. Black River 19. Buffalo River
10. Rocky River


.4

~T~ T~


n ~r~
1 1 1 1 —i—
rn LJ8 |TJB
^TT^™ *^ ^* ^^L^rf% ^^^^^O H^BK^ ^^£J4 A •• ^A
** * r "* *
, i i i • • i • • • • i • • • i
1  2
                         REACH NUMBER
FIGURE 93.
         SOUTH SHORE RIVER AND HARBOR MEAN SULFATE
         CONCENTRATIONS SUMMARIZED FOR  1978 AND  1979.

-------
45
41
95
98
25
28
15
18
 5
 I

28
18
16
14
12
18
 8
 6
 4
 2
 8
                                            ©BICARBONATE
                                            KSILFA7E
                                            Z CALCIUM
IB    11    12    13
14     15    18
REACH NUMBER
                 OOLORIDE
                 A SODIUM
                 * MAGNESIUM
                 X POTASSIUM
            A.
                                      10.  Monroe
                                      11.  Maumee Bay
                                      12.  Locust Point
                                      13.  Sandusky Bay
                                      14.  Huron
                                      15.  Lorai'n
                                      16.  Cleveland
                                      17.  Falrport
                                      18.  Conneaut
                                      19.  Erie Harbor
                                      20.-  Dunkirk
17    18    19    28
                                       10.  Monroe
                                       11.  Maumee Bay
                                       12.  Locust Point
                                       13.  Sandusky Bay
                                       14.  Huron
                                       15.  Lorain
                                       16.  Cleveland
                                       17.  Fairport
                                       18.  Conneaut
                                       19.  Erie Harbor
                                       20.  Dunkirk
                        ->*-
                                                      -it-
      11     12    13    14    15    16
                       REACH NUMBER
                                                  17    18    19    28
    FIGURE 94.   THE  PERCENT CONTRIBUTION OF  THE  INDIVIDUAL
                  PRINCIPAL IONS TO  THE TOTAL  CONDUCTANCE
                  FOR  EACH  OF THE US.  REACHES.
                                F-114

-------
s\
\
36.0

34.0

32.0

30.0

28.0

26.0

24.0

22.0

20.0

18.0

16.0
                    1.  Colborne
                    2.  Port Maitland
                    3.  Nanticoke
                    4.  Long Point Bay
                    5.  Port Burwell
                    6.  Port Stanley
                    7.  Wheatley
                    8.  Leamington
                    9.  Colchester
                   10.  Monroe
11.  Maumee Bay
12.  Locust Point
13.  Sandusky Bay
1*.  Huron
15.  Lorain
16.  Cleveland
17.  Fair port
IS.  Conneaut
19.  Erie Harbor £
20.  Dunkirk    « *
A CONDUCTANCE
© CHLORIDE
                                                       %   «
i450.0

 400.0

 350.0

 300.0

 250.0

 200.0

 150.0

 100.0

 50.0
                                                                                                     n

                                                                                                     3
                                                                                                     m
                                                                                                     o
                                                                                                     8
                          -I	L.
        1   2   3   4   5  6  7   8   9   10  11  12  13  14  15  16  17  18  19 20

                                      REACH  NUMBER

         FIGURE  95.   MEAN NEARSHORE REACH CHLORIDE CONCENTRATIONS
                        AND  CONDUCTIVITY VALUES FOR 1978  AND 1979.
                        0.0

-------
                                       CONCENTRATION 
CONCENTRATION OJG/U
»-•
l-»
Ot
                       2
              §
OB
#"
p
p
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1 r ' S
g f*
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?
1 n I "*
*
1 £J 1
1
1
i rri 	 j
1 Ul I
1 ISl , J 9
i a ,,.j 5
* i

-------
        CONCENTRATION CMG/U
TVV"
 :   •—t-
    t—«
   •-t-1

         CONCENTRATION 
-------
                                      CONCENTRATION O4G/O
CONCENTRATION  CMG/U
                                                                      £
i—»
i—•
oo
            I  O Z



           OC —I CD
           m ^» —i
                       -

              8
1 1 1 . 1 . . 1 1 1^1 . . 1 1 1 1 1 1 1 1 1 1 i 1 1 I I 1 T 1
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BB 1 n 1
i n i
p- HP
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r

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-------



3
3
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a
5
§
M
H
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90. 0r
80.0
70.0
60.0

•

50. 0f
f
40. 0| r
30. 0[ L
20.01
10.01 -
ffl at





1
i, [

IV ••
TOTAL PHOSPHORUS
_ ^




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La

*•" 0.5 1.0 1.5 2.0 2.5 3.0 3.5 4.0 4.5 5.0
DISTANCE •

348 t


CHLORIDE


•«•


a



3SB

•
•

                       DISTANCE 
-------



1— «
o
u
LJ
CO
f\J

8.0
7.0
6.0
5.0
4.0
3.0
2.0
1.0
an
A
•
•
A
•
A A A
A
A
A A
     5.   10.   15.   20.   25.   30.   35.  40.   45.   50.   55.   60.  65.

                           CORR  CHL  A  CUG/L)
FIGURE 100.  SECCHI DEPTH AND CORRECTED CHLOROPHYLL A
             RELATIONSHIP FOR THE NEARSHORE
             REACHES  1978 AND 1979.

-------
ro
    Od
    UJ
    CD

    Z

    X
    UJ
    a
    o_
    o
    QC.
100.0

 90.0

 80.0

 70.0

 60.0

 50.0

 40.0

 30.0

 20.0

 10.0

  0.0
1.  Colborne
2.  Port Maitland
3.  Nanticoke
4.  Long Point Bay
5.  Port Burwell
6.  Port Stanley
7.  Wheatley
8.  Leamington
9.  Colchester
10.  Monroe
11.  Maumee Bay
12.  Locust Point
13.  Sandusky Bay
14.  Huron
15.  Lorain
16.  Cleveland
17.  Fairport
18.  Conneaut
19.  Erie Harbor
20.  Dunkirk
                                                                             EUTROPHIC - > 11
                                                                             EU/MESO -  9 - 11
                                                                             MESOTROPHIC «  4.6-8.9
                                                                             MESQ/OLIGO-  3.1 -4.5
                                                                             OLIGOTRQPHIC - < 3.1
                   1    2   3-4   5  6   7   8  9  10  11  12  13  14  15  16  17  18  19  20

                                                 REACH NUMBER

               FIGURE 101.   ANNUAL MEAN  COMPOSITE TROPHIC INDEX FOR
                               THE  NEARSHORE REACHES 1978  AND  1979.

-------
                                                        1972 -  1973
                                                   eutrophic  >. 11
                                                   eu/mesotrophic 9-11
                                                   mesotrophic 4.6 - 8.9
                                                   meso/oligotrophic 3.1
                                                   oligotrophic _> 3.1
- 4.5
         56.4
                                                        21.8
                                                            1978 -  1979
FIGURE 102.  COMPOSITE TROPHIC INDEX NUMBERS FOR THE SUMMER MEAN  1972-1973 AND
             THE ANNUAL MEAN FOR 1978-1979.
                                     F-122

-------
                                                1978
                                                       1979
FIGURE 103.   STEINHART WATER QUALITY INDEX NUMBERS FOR
             THE NEARSHORE REACHES 1978 AND 1979.
                                F-123

-------
100.0
90.0
80.0
G 70.0
o
3 60.0
2
~ 50.0
K 40.0
UJ
§ 30.0
o
20.0

10.0
i3 a
m
•
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1 EL r !r



   1970 1971  1972  1973  1974 1975 1976  1977  1978  1979 1980 1981 1982
FIGURE 104.  WESTERN BASIN  ANNUAL CRUISE MEAN CONCENTRATIONS
             OF TOTAL PHOSPHORUS FOR 1970 - 1982.

-------
                       CONCENTRATION OJG/U
CONCENTRATION 
3
             i
                   ts—i
                                   3	1      ]
                                   	1       g
                                   H                    !
                                                               hfrH

-------
                                 9ZI-J
                        CONCENTRATION  (UG/L)
^v
5
§
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 • |


3
I
            P
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                                                            ca
           (O
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           GO
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           53
           53
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           »— »
           
-------
30.0
27.0
24.0
G 21.0
3 18.0
2 15.0
| 12.0
LJ
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z 9.0
o
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6.0
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0.0
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1 « 1
   1970 1971 1972  1973  1974  1975 1976 1977  1978  1979  1980 1981 1982
FIGURE 107.  WESTERN BASIN ANNUAL  CRUISE MEAN CONCENTRATIONS
             OF CORRECTED CHLOROPHYLL A FOR 1970 - 1982.

-------
s
t-l
H
12,1
11.1
18.1
 9.1
 8.1
 7.1
 8.1
 5.1
 4.1
 3.1
 2.1
 LI
 8.1
                                                            CBdWJ. BASIN
            1978  1971 1972 1973 1974 1975 1978 1977 1978 1979 1088  1981  1982
     12.1
     11.1
     IB. I
      0.1
      8.1
      7.1
      6.1
      5.1
      4.1
      3.1
      2.1
      LI
      8.1
                                                       CASTBM BASIN
       EL
       1978 1971 1972 1973 1974 1975' 1976* 1977 1978  1979  1988  1981 1962
          FIGURE  108.  CENTRAL AND EASTERN BASIN ANNUAL CRUISE
                        MEAN CONCENTRATIONS OF  CORRECTED
                        CHLOROPHYLL A FOR 1970  - 1982.
                                    M28

-------
7*
i~»
S
X
CL
O
     _
     a
14.0
13.0
12.0
11.0
10.0
 9.0
 8.0
 7.0
 6.0
 5.0
 4.0
 3.0
 2.0
                  1971
                  1980
                     10.0    15.0    20.0    25.0   30.0   35.0   40.0   45.0    50.0
                                     TOTAL PHOSPHORUS CUG/L)
               FIGURE 109.   RELATIONSHIP BETWEEN YEARLY  TOTAL  PHOSPHORUS AND
                            CHLOROPHYLL A  CONCENTRATIONS CORRECTED FOR SPATIAL
                            AND SEASONAL EFFECTS FROM EL-SHAARAWI  (1983).

-------
FIGURE 110.   COMPOSITE ANOXIC AREA OF THE CENTRAL BASIN
             FOR THE PERIOD FROM 1930 TO 1982.
                              M38

-------
                                                            (HOD)
                                                  Hypoll'mnlon Oxygen Demand
                                 (UOD)
                        Water Oxygen Demand
                                  I
                                                                (SOD)
                                                     Sediment Oxygen Demand
                                                                I
K-'
Cu1
                    (BOD)
             Biochemical Oxygen
                  Demand
                Respiration
                   phytoplankton
                   zooplankton
                   fish
                   bacteria (including
                   decomposition)
                      (COD)

                 Chemical  Oxygen
                     Demand
                   Oxidation
                      reduced
                      metal  species
       (BOD)
Biochemical Oxygen
     Demand
   Respiration

      phytoplankton
      zooplankton
      benthic
       invertebrates
      bacteria
     (COD)

Chemical Oxygen
    Demand
  Oxidation
  reduced metal
  _ species  ._
                                                                      interface
             deep
            sediment
           FIGURE 111.
SCHEMATIC OF THE COMPONENTS AND PROCESSES OF
HYPOLIMNION OXYGEN DEMAND.

-------
                  OXYGEN  DEPLETION RATE  CMG/L/MO)
  m
m
(/) 77

> i-

<°OD
2) >
m 
-• x
m -c
°s
OJ O

82
  "^
/b rn
H H
ca

cs
      cncacnGacnscncacn
                                                            01

                                                            ca
           8
           en
S
cn
ea



CO
*>.
cn
           cn
           cn

-------
                                 OXYGEN DEPLETION RATE   CMG/L/MO)
                                                                             OXYGEN DEPLETION RATE  CMG/L/MO)
              m —i
              co 50
              m co
CO
CO
CD
              m -<
           CD O Z
           oo 3: i-*
           t\i >• o
              —I O
              O X


              z s
              *-\ m
              •— * z
              co
                 m
                 —i
                 •—*
                 o
                i

                >-»
                (D
                Ul
i

i-j»

-------
         Wood
                                  }••••••
                                                         •  Cuyahoga
                                                 Lora i n  ••••        *•
N
                                                    :
                                               ••••••i
FIGURE 114.  SHORELINE COUNTIES OF OHIO UTILIZED IN TABULATING NEARSHORE
             WATER QUALITY VIOLATIONS.

-------
X
Al
As
Cd
Cr
2nd qtr
1978 1979
251.26 83.06
	 2.00
4.96 1.38
3.52 2.62
3rd qtr
1978 1979
149.43 39.11
	 2.00
4.93 1.09
2.68 1.S8
4th qtr
1978 1979
100.00 12.33
	 2.00
5.00 1.40
2.00 3.80
                           13(2.73  73.48
                             0.92   0.00
                            10.66   0.47
                            20.21   8.84
                                                      EAST-CENTRAL
                                                      BASIN
                                  WEST-CENTRAL
                                  BASIN
   2nd qtr
1978    1979
   3rd qtr
1978    1979
   4th qtr
1978    1979
Al
At
Cd
Cr

1112.73
1.39 ...
.37
10.63

,... 827.85
.... 1.70 ..
, ... .59 ..
.... 21.40

.... 1394.00 	
.... 1.53 	
.... 3.61 	
.... 24.54 	

    FIGURE 115.
     SOUTH  SHORE METAL CONCENTRATIONS BY
     SEASON AND BASIN FOR  1978 AND  1979.

-------
»
Hg
N1
Se
Va
Zn
2nd qtr
1978 1979
	 0.17
28.28 80.77
2.0/ 2.00
10.61 5.93
2s. 58 86.29
3rd qtr
1978 1979
0.16 0.08
34.02 10.77
2.06 2.00
9.93 5.00
9.45 25.85
4th qtr
1978 1979
	 0.09
122.50 9.63
2.00 ?.00
10.00 5.00
3.75 55.50
            2nd qtr
         1978     1979
   3rd qtr
1978     1979
   4th qtr
1978     1979
Hg
HI
Se
Va
Zn
0.73
23.83
0.72
230.85
92.68
0.05
17.67
0.10
5.91 •
37.80
0.19
27.97
0.80
29.17
66.18
0.09
19.34
0.00

28.30
0.02
36.75
1.67
0.76
32.68
0.03
19.71
0.00

52.96
CO
(Tt
                                                                      EAST-CENTRAL
                                                                      BASIN
                                               WEST-CENTRAL
                                               BASIN
X
MA
HI
$e
Va
In

2nd qtr
1978 1979
0 03
28 90 ...
1 29 	
2 36
54 58

3rd qtr
1978 1979
0 03 	
22 19 	
1.02 	
0 87 	
U2.31 	

4th qtr
1978 1979
0.01 	
19.08 	
1.67 	
1.67 	
42. (S 	

                                                                                                                    o.io
                                                                                                                    13.67
                                                                                                                    0.75
                                                                                                                    5.00
                                                                                                                    34.27
                                                                                                   0.04
                                                                                                  31.00
                                                                                                   2.00
                                                                                                  10.00
                                                                                                   4.24
                                                                                           0.05
                                                                                           10.78
                                                                                           0.81
                                                                                           5.00
                                                                                           45.95
              FIGURE 115.  CONTINUED

-------
                                                                                   2nd qtr
                                                                                1978    1979
                   3rd qtr
                1978     1979
                          4th qtr
                       1978     1979
                                                                        Cu
                                                                        Pb
 7.39
25.28
 S.08
5.57
7.60
6.92
19.51
26.31
12.64
3.16
8.30
5.86
 6.00
25.00
 5.50
3.70
8.13
5.20
                                                         EAST-CENTRAL
                                                         BASIN
                                  WEST-CENTRAL
                                  BASIN
X
Cu
Pb
Hn

2nd qtr
1978 1979
17.50 	
4.41 	
46.79 	

3rd qtr
1978 1979
105.17 	
8.64 	
30.14 	

4th qtr
1978 1979
9 70
2.25
45.54

FIGURE  115.   CONTINUED

-------
                                                                                                     712,13,14.15
  ^~
  » DETROIT
T5.6.7
 TOLEDO
           It  T4

         BASS ISLANDS
                                                                                   ERIE
I - Water Intak*
M - Industrial Monitor
T - Tributary
                  T8
            FIGURE 116.  SHORELINE LOCATIONS USED TO DETERMINE LONG TERM TREND.

-------
                            CONCENTRATION  (UG/L)
  m
  i-»
  •-»
  >j
3D H
M O
50
< "0
o 50
* to
CO •-<
H Tl
«-« O
O 50
            CO
CO
*J
CO
            en


            i-^


            o>


            H-*
            CO
53
00
            CO
            •^4
            CO
                   C9    C9
                       &    Sfl   S
                       ja    p   CD

                       C9    C9   CS
                                                               CO
S3   Si

-------
                          CONCENTRATION  CUG/L)
                           en
                           oa
                           ca
                                                ca
  o
  o
m
m
< to
m -o

  o
X 3D

O CO

> -I
Z 70
o m
o >
CD Z
  en
  i— i
  0)
  o
  •73
  m
           i
           ro
O)




I—»

CO
en


i—»
CO
           00

-------
                                        CONCENTRATION  CMG/L)
i
i—«
-pa
rn ;o  m
—i     O
o —i  •-•

z S  ~n
   m  •—•
^     o
•-» o
 m  c5
•-••<:  z
^ m  o

^ 5:  8
Z Z  —I
a a  >•

33 >•  r>

r5Sm
a: >•  >•

^^  §
O CO
CO     O
   33  3=
*->. m  r—
i—» "^  C3
CD O  33
CO 5O  •—•
•-» —I  C3
^ m  m
•  o

   CD  33
   -<  m

       o
                 CO
                 •—«
                 CO
                           (O
                                                                                       CONDUCTANCE OJMHOS/CVD


                                                                                          rs>
                                                                                            J?U-~-*U
                                                                                                                         2
                                                                                                                         r»
                                                                                                          +         \   f

                                                                                                                    \l

-------
35.1
38.1
25.1
20.1
15.1
IB. I
 5.0
 iff-
50.0r
48. B
48.0
44.0
42.1
40.1
3&I
38.1
34.1
32.1
30.1
 SULfATE
         1900   1910    1920   1930   1940   1950   1960   1970   1960
CM-CIUM
         1900    1910   1920   1930   1940   1950   1980    1970   1980
     FIGURE 120.   SULFATE  AND CALCIUM TREND ANALYSIS
                    FOR THE  CLEVELAND AREA AS REPORTED
                    BY BEETON (1961)  AND RICHARDS  (1981).
                               F-142

-------
                               CONCENTRATION  CMG/L)
     o

     70
     m
     r\>
CD O (/>
m r~ o
m m o
H < •-«
o m c
z r s:

^ z TJ
(O
O)
     C
   > (/)
^ m -o
   > o
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                  ERIE ISLANDS
                  CROUP
DETROIT
                                 CLEVELAND
  FIGURE  122.  AREAS OF WIDESPREAD CLADOPHORA COLONIZATION AS REPORTED BY AUER AND CANALE,  1981,

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TOLEDO
   DETROIT
                                                                                ERIE
                                       CLEVELAND
        FIGURE 123.  STATION LOCATIONS USED IN THE CLADOPHORA SURVEY.

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M
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                                                      STONY POINT. MICHIGAN
              APR
                                                       OCT    NOV    DEC
     188.
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                                                      SOUTH BASS ISLAN&  OHIO
               APR
                                  JULAU6SEPOCTNOVOEC
          FIGURE 124.   WESTERN  BASIN CLADOPHORA STANDING CROP
                        ESTIMATES FOR STONY POINT,  MICHIGAN
                        AND SOUTH BASS  ISLAND* OHIO 1979  (CLEAR).
                                   F-146

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                    STANDING  CROP  CGDW/M3)
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STANDING CROP (GDV/M3)
STANDING CROP CGW/M3)
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                                                     I  WALNUT CREEK
                                                     I RATHFDN POINT
                                                     • HAMBURG
          FIGURE 127    A COMPARISON OF  THE MAXIMUM CLAOOPHORA STANDING
                        CROPS FOR THE FIVE SURVEY LOCATIONS,  1978.

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          FIGURE 128.
                         TOTAL COMMERCIAL LANDINGS OF HERRING.
                         VHITEFISH,  SAUCER,  BLUE PIKE
                         AND VALLEYE FROM 1880 TO 1980.
                                    F-150

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                                                           1981
         FIGURE 130.
TOTAL LANDINGS  OF CARP.  DRUM. WHITE BASS.
GIZZARD SHAD, CHANNEL CATFISH
AND SUCKERS FROM 1960 TO 1980.
                                 F-152

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co
    DETROIT
TOLEDO
                                                                                 ERIE
                                         CLEVELAND
          FIGURE 131.  WESTERN BASIN  (1977) AND  CENTRAL BASIN  (1978) FISH LARVAL SAMPLING STATIONS.

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MEAN LARVAL DENSITY  (NO./100 M3)

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FIGURE 133.  MEAN LARVAL YELLOW PERCH DENSITY FOR INDIVIDUAL
             WESTERN BASIN SAMPLING TRANSECTS DURING 1977.
                             F-155

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                                              JUN
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          FIGURE 134.  MEAN LARVAL WHITE BASS DENSITY IN THE WESTERN BASIN
                       DURING 1977.

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FIGURE 135.  MEAN LARVAL WHITE BASS DENSITY FOR INDIVIDUAL
             WESTERN BASIN SAMPLING TRANSECTS DURING 1977.
                            F-157

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                             8ST-J
               MEAN LARVAL  DENSITY  CNO. /100 M3)
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FIGURE 137.  MEAN LARVAL WALLEYE DENSITY FOR INDIVIDUAL
             WESTERN BASIN SAMPLING TRANSECTS DURING 1977.
                            F-159

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MEAN LARVAL DENSITY  CN0. /100 M3)
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FIGURE 139.  MEAN LARVAL YELLOW PERCH DENSITY FOR INDIVIDUAL
             CENTRAL BASIN SAMPLING TRANSECTS DURING 1978.
                            F-161

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              FIGURE 140.   MEAN LARVAL SMELT DENSITY IN THE CENTRAL BASIN
                            DURING 1978.

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TECHNICAL REPORT DATA ~~]
(Pleast nod liutnictiont on the rtverse before completing) ]
1. REPORT NO.
EPA-905/4-84-001
2.
4. TITLE AND SUBTITLE
Lake Erie Intensive Study 1978-1979
7. AUTHOR(S)
David E. Rathke

B. PERFORMING ORGANIZATION NAME AND ADDRESS
The Ohio State University
Center For Lake Erie Area Research
Columbus, Ohio
12. SPONSORING AGENCY NAME AND ADDRESS
U.S. Environmental Protection Agency
Great Lakes National Program Office
536 South Clark Street, Room 958
Chicago, Illinois 60605
3. RECIPIENT'S ACCESSION-NO. 1
B. REPORT DATE
January 1 Qft^
6. PERFORMING ORGANIZATION CODE
B. PERFORMING ORGANIZATION REPORT HO.
10. PROGRAM ELEMENT NO.
ii. CONTRACT/GRANT NO.
13. TYPE OF REPORT AND PERIOD COVERED
Final 1978-1979
14. SPONSORING AGENCY CODE
Great Lakes National Program
Office, U.S. EPA, Region V
15. SUPPLEMENTARY NOTES
David Rockwell
Project Officer
16. ABSTRACT
Lake Erie has experienced several decades of accelerated eutrophicatton and toxic
substances contamination. During the latter part of the 1960s, remedial actions
were planned and by the latter part of the 1970s, many of these plans were at
least partially implemented. The first signs of lake recovery are nov being
observed through comprehensive monitoring programs. The intent of this report
is to summarize the methods, findings and conclusions of the 1978-1979 Lake Erie
Intensive Study. The report also contains a set of recommendations to insure
continued improvement of the water and biotic quality of Lake Erie.
17.
KEY WORDS AND DOCUMENT ANALYSIS
a. DESCRIPTORS
Water quality Diatoms
Biota Nutrients
Epilimnlon Biomass
Hypolimnion
Thermal
Total Phosphorus
Fish Contaminants
18. DISTRIBUTION STATEMENT,
Document is available to th
the National Technical Info
Springfield, VA 22161
e public throug
rmationCNTIS)^
b. IDENTIFIERS/OPEN ENDED TERMS C. COSATI Field/Group

19. SECURITY CLASS (This Report) 21 . NO. OF PAGES
1 484
20. SECURITY CLASS (This page) 22. PRICE
Unclassified
EPA Form 2220-1 (»-73)
                                                                          U.S. GOVERNMENT PRINTING OFFICE: 1985-555-271/516

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