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
10
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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
14
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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
15
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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
17
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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
19
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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
20
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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
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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
23
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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
25
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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.
29
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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
30
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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
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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
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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.
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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.
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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.
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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
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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
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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
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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
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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)
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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.
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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
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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
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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
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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
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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).
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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
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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.
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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:
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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.
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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:
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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.
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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
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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
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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
115
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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
116
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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
117
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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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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
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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
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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
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designed with this consideration in mind as such combined efforts generally lead to a
better surveillance/monitoring program.
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176
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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
-------
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
-------
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
-------
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
»— 1
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 >
>
-i <
O (/)
m
77
77 CO
§S
CO
TJ
> 13
I X
P?
Is
•
63
OJ **• .**
CJ1 ijSj ^J1
IJ^ i^fr ^*Cj^
C/)
m
-D
o
o
s
o
•^
F
-------
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
rKM
™ M
••
1 1
1 LM»
JZB
•M
i IAM
•••
M
••
^
•
•
••
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
t
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. .-
Jii .
J^C
D
L«"
au
•» Jll7
APR MAY JUN JUL AUG SEP OCT NOV DEC
r
••
k
[
•* [
M
E»B
HYPOLimiCN
•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 $ £
$"
I
Tl
t— «
X ^
s
1 *
s
1
s *
r~
i R
2 "
S
1 D 1 ^
1 | 1 S
1 a . — —I
* ^
1 •"• 1
1 9
i CL i ^
1 Q 1 S
in , , |
t »
i
8
y
1171 1
Ig 1
i nn i
1 i1 '
i (•! l
Ll a \
, *B , »
§ ' S
I D I
1 0 _J
1 ft T
. i | " j
1 I; '
-------
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
IIO
TE
NTRATI
1
8
y.y.y.y.y.y.y.y.y
*
t
t
1
t
-------
700.1
EPILIKJION
500.1
400.1
300.1
200.1
100.1
0.0L
Clli
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
m
EPILIMNION
•
•
.
•
•
'
•
•
a
!••
1 1
a28
•••
C
"H w
i |g
323
tm
1
•••
••
I
M
••
3
•M
1 1
L
1 1^
JS3
•M
i L.
L
••
^»
•^
L
[
•M
"U
•^ 1^
mtf
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
_i
1 ^
i r=l -1
.1 | 1
i rri i *
1 P 1 £
i rri , i
1 1*1 1
to
P
s
• 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
UK)
55
45
^ 40
3 35
° on
M 30
| 25
z
a 20
8 15
10
5
fl
•
k
.
•
•
•
•
••
c
» _
Ml
«•«•
128
r
I i
^B
[
"I
1
•^
i « i
KVl 1 '
1 1 • •
L
^•i
M*
EPILIMNION
L
«•!
«•
Is
C
•M
^B
t
^
•M
1 1 *
]*
[id
— ' • • .. .1... ...... . «
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
3
fl
•
•
EPLINNIQN
•
-,
•
•
C
APR NAY
•
•
HYPOLINNION
c
•
3127
D
JIB
Ij
«•
an
D
i
h
•>
•
•a c
.
JUL
•L-
•JiMi F
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G
m
AUG
••
•»
te c
S
•
]• L
Ml
C
JOt
EP DC
1
J22
M
a»c
T
«•
3118
C
«
MOV
h
»
DEC
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
0.1
•
e
••
•
dl"
. —
[
41
•• «
kll
••
•
L
•
Ml
JUi
APRHAYJUNJULAUCSEPOCTNOVOEC
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
0.0
•
EPILIMNION
•
•
R
•
••
•
c
mmi
._ . .... A . . . 1 , ,
mm
328
mm
— • 1
••
1
•1
mm
MB
••
1 E
^
•^
•^
323
Jf_-{f
c
••i
1 — 1 — i — 1_
••
mm
*•
3»L
^m
•^
_. 1
«•
1 |
MA
•*••
mm
L
mfmM
mm
•i
I
^
•
••
J
MAX 118.4
28
•••
1 i
L
IB
> I
J26
tmm
Jao
mm
1 • 1 1 1 1 • • •
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
15.0
10.0
5.0
0.0
EPILIMNION
C.E9
r
i
i
i
WH
c
^m
Hl8 [
- ^H
G
18 J
•••
1 1
Is
•»
••
t
MB
C
>•»
is-'
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
»-«
a
18,1
9.1
8.1
7.1
8.1
5.1
4.8
3.8
2.1
1.1
0.1
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
0.1
EnUMOflN
0 377.
APRNAYJUNJULAUGSB>OCTNOVOEC
M
o
11.1
18.1
911
8.1
7.1
8.1
5.1
4.1
3.1
2.1
1.1
fl.1
HmiHflON
f'Mk
i
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
3.5
g 3.0
x 2.5
& 2.0
1.5
1.0
0.5
0 a
EPILIMNION
*
•
•
[
mmt
•
L
mm
»
mm
m
m*
l_
•*
•
mm
6
^M
•* mm
J13 [
H» mM
r
mm]
__, • « - - • 1 i__
••
Jl3 -p
[]l3 ^^ *--'13
_L _L _.
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
IB.!
II
7.!
flu I
4.!
3.1
1.!
LI
15.1
13.!
12.1
IB.!
9.1
7.!
8.1
4.(
3.1
1.!
II
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»
o
1-4
n
»-«
u
o
UJ
CO
10.0
9.0
8.0
7.0
6.0
5.0
4.0
3.0
2.0
1 ft
1. V
a a
•
A EASTERN BASIN
0 CENTRAL BASIN
* WESTERN BASIN
•
»
2
•
0
r A
6 fi °
ft O A
6 o
w w
* m
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
S
Si ^ S
co •—• n
SS
"-F
^t-1
-f-1
W
CONCENTRATION CMG/D
1
\-E—I
g
«
1-«
I 1 1
I fr
-------
28
26
S 24
5 22
M **
21
18
16
14
EPILINNIQN
APRMAYJUNJILAUGSEPOCTNOVDEC
28
28
24
22
28
18
18
14
HYPOLimiON
APRMAYJUNJULAUGSEPOCTNOYDEC
FIGURE 59. THE MEAN EASTERN BASIN EPILIHNION AND
HYPOLIMNION CHLORIDE CONCENTRATIONS
FOR 1978 (USEPA-GLNPO).
F-71
-------
24
22
20
\ 18
z 16
o
1 "
h-
| 12
I
10
8
R
••
»
MB
.
•
"I
J28-
E
•M
_ ••
1
r
MM
^H
li [
••»
^H
«•
Mk
]»c
^H
M
IM»
••
!UC
^
•••
•••
•••
i
ja»
1 |
L
mm
mm
M*
i i r*
•^
mm
^•>
•M
T
L
1 1
•»
^H
^W
T
L
i^
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
-n
»— i
I S
sig s
*•* ™
§i| g
•— • Z z
e S m
-n S S
**• *" *T! 53
S ™ § £
Q g to es
• 2 Z
3 «-« Q
a r-
ai B
Is 3
i s
<
g
i s
I n i «-•
1 I I g
ULJ
1 B 1
I H I
l_ n i fe
1 g 1 «
1)
' I&J ^S
T S
: s
<
^
S
i i , ,.j
t »
i • i
1 1 i
IB 1
1 i '
i , n ._i
1 | 1
t • i
1 L 1
L, D _J
8 i
-------
-------
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
<
o
h-
H
100.0
90.0
80.0
70.0
60.0
50.0
40.0
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
-------
«
CD
O
1-1
m
10.0
9.0
8.0
7.0
6.0
5.0
4.0
3.0
2.0
1.0
0.0
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
2
\
CD
w
(/)
s
o
I—I
GQ
1.8
1.6
1.4
1.2
1.0
0.8
0.6
0.4
0.2
0.0
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).
-------
CO
CO
o
K^^
r^
CD
I
«•!
<
0
i-
*
100.0
90.0
80.0
70.0
60.0
50.0
40.0
30.0
20.0
10.0
am
»
•
•
»
»
»
.
»
»
•
...«>*.!
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
-------
U)
10
o
ffl
<
1
r-
O
1-
*
100.0
90.0
80.0
70.0
60.0
50.0
40.0
30,0
20.0
10.0
ft ft
•
•
•
•
•
•
•
•
•
•
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
-------
l
Af* if
f°* a>
"" J
T
\ T ' r- r- <
/./
>-<
*«
I
J^^
r"
^r^"
-------
1000
900
fiflfl
OvV
G 700
o
B 600
f-^
2 500
t 400
z
UJ
(J
o
o
200
100
a
t
»
•
••
-i |j
1.
i9 .
IH
•••
r
1 1
T-
JO
^
•
^
1
Jl6
^m
^K9
L [
^m
'[
1-
M>
I 1 1
•
1
- lie
-MAX 2000
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
L
••w-rf f^nl T^^O 1 i LA
• ••••iii «J
Cuyahoga River
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
CONCENTRATION (UG/L)
?
•I I • I
So?
m
a
m
en
CO
en
en
CO
CO
no
CO
i—»
en
i—»
CO
00
CO
IP-
t
t
t
t
I-
-E
1^-H
i m i
rgn
* 2 I ^ 5 2 O JO I D
8 g"SSS g3
-------
2000 r ** Detroit River 11.
1800
1600
a 1400
o
3 1200
, 2 1000
71 1-
*"* ^C
8 £ 800
UJ
§ 600
u
400
200
a
2. Huron River 12.
3. River Raisin 13.
. 4. Ottawa River 14.
5. Maumee
6. Portage
River 15.
River 16.
. 7. Sandusky River 17.
8. Huron River (OH) 18.
9. Black River 19.
Cuyahoga
River -p-
Grand River (OH)
Ashtabula
Conneaut
River
Harbor
Dunkirk Harbor
Cattaraugus Creek
Rush Creek
Smokes Creek
Buffalo River
10. Rocky River
•
•
•
1 I
I 1
- C
__
J
Lie
jgl -
^M
•*
£^
_
•
i
M*
318
•^
^•L^
-r-
~*~ ^*^» P" T
RIVER DESIGNATION
FIGURE 80. SOUTH SHORE RIVER AND HARBOR MEAN AMMONIA
CONCENTRATIONS SUMMARIZED FOR 1978 AND 1979.
-------
o
I—I
I-
<
ui
u
o
u
1000
900
800
700
600
500
400
300
200
100
ft
r 1. Colborne 11. Maumee Bay MAX 2000 -i
2. Port Maitland 12. Locust Point
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
*•
•M
•
•
=F«C
••
^w
M
^SSl-ZlIu^ S2*1!29-
.•*
C
-3W
^•i
3144
a
^B
^»
^n
C
*¥X*
aZaS
M«
1*
371
C3
MB
••
olflB
Jl
•^ «•
]l4f
-MAX 2000
~V7\
U
~T~ T~
aaK am ojfl
• •clO M _oW
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20
REACH NUMBER
FIGURE 81. MEAN NEARSHORE REACH CONCENTRATIONS
OF TOTAL PHOSPHORUS FOR 1978 - 1979.
-------
100 r
f\fm
90
80
^^\ n4v
3 70
o
3 60
2
2 50
<
£ 40
Ul
o
z 30
o
u
20
10
LV
0
•
•
•
mi
*•
I44
i, -P
MAX 112
M
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
L"
a
Colborne
Port Maitland
Nanticoke
Long Point Bay
Port Burwell
Port Stanley
Wheatley
Leamington
Colchester
Monroe
^mvmm
m
^—.gjoaieCDe;
- +? —- —
MAX 119 MAX 195
1 1 . Maumee Bay
12. Locust Point
13. Sandusky Bay
14. Huron
15. Lorain
16. Cleveland
17. Fair port
18. Conneaut
19. Erie Harbor
20. Dunkirk
~T~
mm
T rtMl
522 ^
-i 1 1
__.
C
i
J29B
!••
1 •• —
o381
]l44
C
mm
mm
D24£
1 i
"L~
179
c
__t nn
Jlog
«•
^
- L
D158
mm
-*!
Pg-l
a
o296
mm ^™
mm
o21ft
mmi
asa.
-349
1 2 3 4 5 6
7 8 9 10 11 12 13 14 15 16 17 18 19 20
REACH NUMBER
FIGURE 82. MEAN NEARSHORE REACH CONCENTRATIONS
OF SOLUBLE REACTIVE PHOSPHORUS
FOR 1978 AND 1979.
-------
9000 r !• Colborne 11. Maumee Bay -,-
8000
7000
^N
\ 6000
D
z 5000
o
i— i
< 4000
L_
^•~
z
| 3000
O
u
2000
1000
& **»**^
n
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
•
•
•
•
m
,
••
^44=
•^
^
T
=>37sp31Sp21,^l^e =¥=22^40Q
••
[
r
««cb3Bl
s29
•B
]l44
r
1?4R
T
i^
"U
H72
c
•M
a!92
^M
^m
Bi4a
^M
••i
^51
•
^»
^6fi
^IgTsi- -349
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20
REACH NUMBER
FIGURE 83. MEAN NEARSHORE REACH CONCENTRATIONS OF NITRATE
PLUS NITRITE FOR 1978 AND 1979.
-------
3
o
g
o
a:
z
LU
U
O
U
1000 r ['
900
800
700
600
500
400
300
200
100
0
2.
3.
. t.
5.
6.
. 7.
8.
9.
. 10.
•
•
•
•
•
_s
4
Colborne
Port Maitland
Nanticoke
Long Point Bay
Port Burwell
Port Stanley
Wheatley
Leamington
Colchester
Monroe
14. Huron
15. Lorain
16. Cleveland
17. Fairport
18. Conneaut
19. Erie Harbor
20. Dunkirk
(Bay
Point
yBay
nd
t
Jt
rbor
1°
•Ml
mm
3381
urn-
«••
]144
C
PV
mm
a240
Q
^M
mm
108
mm
1.191
f*t
. a
[
]14Z
ri
••
J235
1
1590
•••
3251
M
••
^B
^1§
•••
••
=53
•
^
i
3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20
REACH NUMBER
FIGURE 84. MEAN NEARSHORE REACH CONCENTRATIONS OF
AMMONIA FOR 1978 AND 1979.
-------
7000
i
o:
LJ
u
o
u
2000
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
•
>
•
^M
SC43E
•^
^B
C
=29
"""
^•i
••
q
a»l
«•
]l44
C
^H
M»
P-
D
3248
^
••
T
0*
E
^ ^
•*
•••
3l8g
•M
MB
Die!
•^
^
3256
c
-MAX 10.040
d298oiftH52.
• MCtV ™" ••
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20
REACH NUMBER
FIGURE 85. MEAN NEARSHORE REACH CONCENTRATIONS OF DISSOLVED SILICA
FOR 1978 AND 1979.
-------
o
o
UJ
o
CJ
00
90
80
70
Rffl
OKI
50
40
30
20
10
a
•
MAX 115.2-1
1. Colborne 11. Maumee Bay
- 2. Port Maitland 12. Locust Point
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
. 8. Leamington 18. Conneaut
9. Colchester 19. Erie Harbor
10. Monroe 20. Dunkirk
.
^
•
"1
•
•f«c
r
- S28^1*^12?4^
Diejze-n
L JL c
C
o9
[
D3«l
^H
^ «
MM
]l44
C
^m
M»
324
•H
PI
|
•
B
-MAX 198.4
•
72
c
•M
mtm
3102
•
•^
••
«•
.142
^M
^
«•
••
JI42
••
^92
••
••
c
"11«
MM
•mfmrfc
3292
-T882.
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20
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 "
•
•
m
. [
*
••
1
•M
is
1 1
mm
1 1
^»
•Ml
iJ-
1 1
' I>M%
' na
•••
i — i
*M
i 1
[
1 1
••
I 1
fe
^H
1 1
•V
1 1 J^""'
•J^b
C
••
•B
1 1
•••
341"
i — Z
~7»,
IB* ^™
1 1
<•»
•••
182
-H
•••
... _.T
•M
•M>
m-
M«M
1^ «•
«^
•*
C
N.153T
1 fU
C
3115
mm
1
C
3137
•»• «•
i._ _i
IM
mm
3MP
TJ
••»
«•
•
••
C
T9?fl
rMAX 11.5
3215
E
«••
1 L 1
•M
C
It
'
^
3340
M*
1 1
123456
REACH NUMBER
FIGURE 87. MEAN NEARSHORE REACH CONCENTRATIONS OF
SECCHI DEPTH FOR 1978 AND 1979.
-------
o
\-/
o:
LU
u
o
u
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
* !••
•
"10. Monroe
mm
mm
—1—
k
ft
, ,
mm
mm
328[]
mm
i2j .
.f
11. Maumee Bay
12. Locust Point
13. Sandusky Bay
14. Huron
15. Lorain
16. Cleveland
17. Fairport
IS. Conneaut -i
19. Erie Harbor
2C
—r— 1 (
L
i >
_J4
1. D
•HI
llC
Dunkirk -
•^
^^
]38
C
••
^
329o
•M
^
^•1
^
^B
313§
••
3226
•^
••
382
C
•M
mm
• Itlllltl
mm
C
3189
3127
a
i^
G
o251
^
mm
*mSml
oZDO
n
^•i
^H
•M
T?1R
•^
^B
C
Tf)l
"• —
=349
••
^^^v
mm
I I 1 I t I .1
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-
»•
..348
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
z 30
8
^•J
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
•
•
«••
C 331 c
* «M
•
• i • I • • I
«••
^•t
rUflO
O4P
•••
•••
— —
]28
C3
•••
•H
C
3138
••»
380
c
^
^•i
«••
u
alflO
•M
1 1 I • I
•••
••>
_ja
DW
c
••
••
^•i
alfli
•••
MW
a
r 4^
i^
.lee
HHJ^jQB fllMI^^V1"*
™^^»^rB — __P^L*
1 «1A ^^ «CMI
••^^•••tli UI ^ri ^0X00
•••
,,,,,,,
REACH NUMBER
FIGURE 91. MEAN NEARSHORE REACH CONCENTRATIONS OF
CHLORIDE FOR 1978 AND 1979.
-------
l-»
!-•
ro
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
••*
••
]*
C
t^
••»
i
mm
3128
mm
| I
i
M
MAX 279.8
M
C
••
mm
3l8f
m*
aM
mm
mm»
mm-mMl
a256
m
mm
mm
mm
•28BLlia
-L _
••
••
a28-
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
-
.
•
.
•
Mi
N/D r
L
• *"*
»
vi
r
— 1 '
_ L
jj W
J4
^
••
^M
T r
> 1 L
J4 -1
M*
-
••
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
g
?
s
fer1 '
JO
OB
i m i
I p-l 1
ea
I m .j „
1 UJ 1 p
o
2 P
L, ra. .._i ^ "
1 r ' S
g f*
I — B j r •
W |
?
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
*"* t H 1
BB 1 n 1
i n i
p- HP
ea
88 i o I
nr
jii
f* ' | a \
nr1
« 1
p
ea
P
181 i n i
h-fH
P
• • • i • i
r
m
ea
o
1 ••
2 ea
g P
5 *
ea
P
ea
P
ea
P
ea
i go i
P
P
fir
3
P
I
*
1 I 1 \
KJ
-------
3
3
§
^4
|
1
*
a
5
§
M
H
1
*
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
_ ^
]c j
1
J« f
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
•
•
•
P MM
•
: [
•-^f
"1
J10
•
" * T f * J 1
•w
1
.
r-
3
•••
[
1 ]
•^
1
/•'•Pi
i
••
i
t
•
5
.
•
•
3
I
•
i
t
4
mm
i
m»
1 T
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
§
CE
• |
3
I
P
ea
ca
(O
r\>
GO
—
53
53
cn
0)
»— »
-------
30.0
27.0
24.0
G 21.0
3 18.0
2 15.0
| 12.0
LJ
(J
z 9.0
o
o
6.0
3.0
0.0
•
•
•
•
•
•
»
•
•
.
mm
•
•
.J
fl
1 1
1
mm
mm
10
• 1 i 1 1 , J
n
1 1
J3
•Jw
1
••
••
I
mm
mm
I
mm
M
,
8
"TP™
I
.
I
_
••••••
,
5
i
-LJ2
,
•M
[
mmi
I
,
mmmmm
\
mmmmm
mm
_ —
I r
'L r
Jo L
mm
T
i r
Jo
i. .. 1 1 '
•i
)
•1
mm
•1
J?
mm
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
> H
z > >
o en (/)
•-•me:
o
a m m
-------
ERIE ISLANDS
CROUP
DETROIT
CLEVELAND
FIGURE 122. AREAS OF WIDESPREAD CLADOPHORA COLONIZATION AS REPORTED BY AUER AND CANALE, 1981,
-------
TOLEDO
DETROIT
ERIE
CLEVELAND
FIGURE 123. STATION LOCATIONS USED IN THE CLADOPHORA SURVEY.
-------
M
I
STONY POINT. MICHIGAN
APR
OCT NOV DEC
188.
98.
88.
^ m
iS «,
58.
8
48.
38.
28.
IB.
0.
O 15 METERS
A &8 METERS
•
•
•
i
•
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
-------
STANDING CROP CGDW/M3)
IN)
P r
oa ca
ro
V* P>
63 C9
C9
Ga
en
-------
STANDING CROP (GDV/M3)
STANDING CROP CGW/M3)
to
fa pa
• en
-------
1000
a
o
a.
o
CL
u
o
o
700
500
300
100
0
I STONY POINT
I SOUTH BASS
I WALNUT CREEK
I RATHFDN POINT
• HAMBURG
FIGURE 127 A COMPARISON OF THE MAXIMUM CLAOOPHORA STANDING
CROPS FOR THE FIVE SURVEY LOCATIONS, 1978.
-------
22.1
20.1
18.1
I *'
g 14.1
5 12.1
g *
M
| &
-J 8.
4.
2.
0.
o
o
o
OHERRIN6
1888 1800 19H 1910 1020
1970 1980
5
1-4
l-l
5
O BLUE PIKE * WALLEYE
ID BLUE PIKE
WALLEYE
SAUCER
1880 1890 1900 1918 l920 l930 1940
1970 1980
FIGURE 128.
TOTAL COMMERCIAL LANDINGS OF HERRING.
VHITEFISH, SAUCER, BLUE PIKE
AND VALLEYE FROM 1880 TO 1980.
F-150
-------
TOTAL LANDINGS (MILLION KG)
5s1
ca
ea ca
m
i-*
CO
_> g
« m
c/> o
m >
i~ r*
P
3C •-*
00 (A
fQ f^
•n
o -<
m
TJ
m
CO
i—»
ca
»—»
CO
s
ca
(O
CO
a
_, P
ro
csa
ea
-------
1
5
i
OCMP
AORUN
1.1
I!
1885
1071
1875
i
3
fr4
9
s
09UCKB8
JKCHMMEL CATFISH
1981
FIGURE 130.
TOTAL LANDINGS OF CARP. DRUM. WHITE BASS.
GIZZARD SHAD, CHANNEL CATFISH
AND SUCKERS FROM 1960 TO 1980.
F-152
-------
co
DETROIT
TOLEDO
ERIE
CLEVELAND
FIGURE 131. WESTERN BASIN (1977) AND CENTRAL BASIN (1978) FISH LARVAL SAMPLING STATIONS.
-------
MEAN LARVAL DENSITY (NO./100 M3)
-------
FIGURE 133. MEAN LARVAL YELLOW PERCH DENSITY FOR INDIVIDUAL
WESTERN BASIN SAMPLING TRANSECTS DURING 1977.
F-155
-------
/N
CO
i
vx
Ld
Q
V
I
LJ
35
30
25
20
15
10
0
NAY
JUN
JUL
FIGURE 134. MEAN LARVAL WHITE BASS DENSITY IN THE WESTERN BASIN
DURING 1977.
-------
FIGURE 135. MEAN LARVAL WHITE BASS DENSITY FOR INDIVIDUAL
WESTERN BASIN SAMPLING TRANSECTS DURING 1977.
F-157
-------
8ST-J
MEAN LARVAL DENSITY CNO. /100 M3)
ro a)
en
I
m
en
s
8
-------
FIGURE 137. MEAN LARVAL WALLEYE DENSITY FOR INDIVIDUAL
WESTERN BASIN SAMPLING TRANSECTS DURING 1977.
F-159
-------
09I-d
MEAN LARVAL DENSITY CN0. /100 M3)
ea
-------
^/
X
'a
V
5
3
2
!/
\
t
J
il
^
y
%
V
>
^
\
^
I— J^
B
• §
"1 "o
2
6 ^
X
4J
>K v4
8 0)
C
4 £
3 1
IN
2 J
c
' 1
i
FIGURE 139. MEAN LARVAL YELLOW PERCH DENSITY FOR INDIVIDUAL
CENTRAL BASIN SAMPLING TRANSECTS DURING 1978.
F-161
-------
«9
s
ca
x
0
71
*-*
ro
LU
Q
-I
Z
UJ
18
16
14
12
10
8
6
4
2
0
MAY
JUN
JUL
FIGURE 140. MEAN LARVAL SMELT DENSITY IN THE CENTRAL BASIN
DURING 1978.
-------
o
73
CO
I
I—•
CO
30 —I
-x>
z o
t/» m
m z
o
-H •-•
CO —I
70 O
•-< -73
2;
o •-•
\s> »-•
^4 «=
00 M
w » g» e» -4 » •
Mean Larval Density (No/100 m3)
-------
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
-------
|