DNR
UPPER GREAT LAKES
CONNECTING CHANNELS
STUDY
Volume
FINAL REPORT
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FINAL REPORT
of the
UPPER GREAT LAKES
CONNECTING CHANNELS
STUDY
VOLUME II
DECEMBER 1988
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Environment
Ontario
ef Engfemn
LETTER OF TKANSMITTAL
Valdas A. Adamkus
Regional Administrator, Region V
U.S. Environmental Protection Agency
Elizabeth Dowdeswell
Regional Director General, Ontario Region
Environment Canada
David F. Hales
Director
Michigan Department of Natural Resources
j. Walter Giles
Associate Deputy Minister
Ontario Ministry of the Environment
On behalf of the Management Committee we are pleased to submit
the final report and executive summary of the Upper Great
Lakes Connecting Channels Study. The report is a
comprehensive and detailed review of the project studies and
their results.
Respectfully submitted, February 1989.
Ron Shimizp
Co-Chair \J
Environment Canada
Carol Finch
Co-Chair
U.S. Environmental
Protection Agency
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ACKNOWLEDGEMENTS
Many people contributed to the completion of this document. There
were over a hundred principal investigators and associated staff
who contributed the most essential ingredient to the study - the
data and preliminary interpretations. Although too numerous to
mention, the Management Committee of the Upper Great Lakes Con-
necting Channels Study extends thanks to all.
Members of the numerous committee, workgroup, task force and
synthesis writing teams are listed in Appendix I, The Management
Committee would especially like to acknowledge the members of the
Activities Integration Committee. This committee co-ordinated
the technical studies, chaired individual workgroups, and
assisted with and directed the writing of the final report,
These people include: Daryl Cowell (Canadian Co-chair), Vacys
Saulys (U.S. Co-chair}, A.S.Y. chau, Tom Edsall, Yousry Hamdy,
Tom Fontaine, John Moore, Paul Horvatin, Griff Sherbin, Rick
Lundgren, Don Williams, Keith Rodgers, Wayne Wager and Bill
Richardson (Appendix I).
The principal writers of the final report are: Yousry Hamdy,
Diana Klemens, Barry Oliver, Pranas Pranckevicius, Paul Bertram,
Paul Hamblin, David Kenaga, Cynthia Fuller, Daryl Cowell, Vacys
Saulys and Wayne Wager. The overall editing of the final report
was conducted by the Activities Integration Committee. The prim-
ary editor was Daryl Cowell with the assistance of Wayne Wager
and Vacys Saulys. Again, the Management Committee extends their
appreciation.
The Management Committee and editors would also like to specif-
ically acknowledge the work of George Ziegenhorn (technical sec-
retary to the Management and Activities Integration Committees),
Tonya Moniz (word processing), Brent Hosier (drafting), Deepak
Dath (hardware/software assistance), Donna Schmidtmeyer (Appendix
II), Darrell Piekars {executive summary editing), and John
Forwalter and Cynthia Fuller (editing support).
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PREFACE
This Report provides the major findings and recommendations of
the Upper Great Lakes Connecting Channels Study (UGLCCS). The
study was first announced as a U.S. Program in November, 1983 by
then United States Environmental Protection Agency (U.S.EPA)
Administrator, William Ruckelshaus. In July, 1984 it became a
multi-agency U.S./Canada investigation of toxic chemicals and
other environmental concerns in the Upper Great Lakes Connecting
Channels. The study area included the Detroit, St. Clair and St.
Marys Rivers and Lake St. Clair. The principal agencies involved
were the U.S.EPA, Environment Canada, the Ontario Ministry of the
Environment, Michigan Department of Natural Resources, U.S. Fish
and Wildlife Service, U.S. Geological Survey, National Oceanic
and Atmospheric Administration, U.S. Army Corp of Engineers, the
City of Detroit, Fisheries and oceans Canada and the Ontario
Ministry of Natural Resources.
The UGLCC Study was organized such that the participating agen-
cies could focus and co-ordinate their on-going studies in the
four areas and identify priorities- for new studies. All programs
and individuals benefited from working together and sharing their
individual strengths. The total cost of this study approxi-
mately $20 million. This included existing agency program funds
as well as "new" money allocated to additional studies in the
channels.
The Impetus for this study was specifically for the improved
regulatory management of point and nonpoint pollution sources in
the four study areas. As such, the technical and management
recommendations identified for each area are the key outputs of
the study. It should be pointed out, however, that the regula-
tory agencies have not waited for the final release of this study
before implementing controls. Numerous actions have been under-
taken throughout the course of the study whenever investigations
uncovered significant pollution sources and problems. For ex-
ample, the total loadings of certain organic chemicals from Sar-
nia area chemical companies have been drastically reduced since
late 1985 following the discovery of perchloroethylene puddles on
the bed of the St. Clair River,
This report is volume II of a three volume set containing the
complete output of the UGLCC Study. Volume I is an executive
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VI
summary describing the major study findings and recommendations.
Volume III is a compilation of the many principal investigator
reports, workgroup reports and other supporting documents, Cop-
ies are on file with each of the participating agencies and with
the International Joint Commission in Windsor, Ontario.
This volume (II) is the main report describing the results of the
UGLCC Studies. It consists of five introductory chapters and
four area chapters (one for each study area). The introductory
material covers study purpose and organization, characteristics
of the four study areas, regulatory guidelines and programs, the
data quality management program, and modeling activities. The
last four chapters present the findings for each study area using
a comparable reporting format.
Detailed study area maps are provided in Chapter II. These,
along with tables and other information in Chapters III, IV, and
¥, are intended as reference material for the reader in support
of the area chapters.
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Vli
TABLE
O P
CONTENTS
LETTER OP T1ANSMITTAL , , iii
, iv
PREFACE ...... ... v
CHAPTER I
1. Purpose and Objectives . . . . . 1
2. Study Approach ............... 2
3. Management Structure ........... 4
4. Schedule . 5
5, Technical Activities ...... 6
6, Parameters of Interest 6
7, References , , , , 8
CHAPTER II OVERVIEW OP UPPEE LAKES CONNECTING
CHANNELS
1. Introduction ............... 11
2. St. Marys River." ,...,.....,.. 18
3. St. Glair River. , . . 20
4. Lake St. Clair 22
5, Detroit River, .,,,.,.,,..,., 25
6. References , 28
CHAPTER III REGULATORY OUTLINE
A, Introduction .... ........ 29
1. Binational Agreements 29
2. Federal, State and Provincial
Environmental Control .......... 30
B. Environmental Media Standards, Criteria,
Objectives and Guidelines .......... 35
1. Water Quality. ,...,..'..,.... 35
2. Sediment Quality ........ 39
3. Aquatic Biota ...... ... 41
c. Point Source Contaminant Controls ....... 44
1. Industrial Point Sources 44
2. Municipal Point Sources 47
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vili
D. Nonpoint Source Contaminant Control 50
1. Agricultural Runoff 50
2. Pesticides ...... 50
3. Shipping 52
4. Spills 53
5. Urban Runoff and combined Sewer Overflows, 54
6. Atmospheric Deposition 54
7, In-place Pollutants . 55
E. Solid, Liquid and Hazardous Waste Controls . . 57
F. Reference ......... 59
CHAPTER IV DATA QUALITY MANAGEMENT
A. Data Requirements and Procedures 61
1. Intended Use of Data 61
2. Field and Laboratory Procedures 62
B. Data Quality Management 63
1. Activities 63
2, Project Plan Review Findings 65
C. Interlaboratory Performance Evaluations .... 67
1. Background 67
2. Approach , 67
D. UGLCCS Quality Assurance Results ....... 70
1. Percent Recoveries 70
2. Overall Laboratory Performance ...... 74
E. Findings and Conclusions 78
F. References 80
CHAPTER V INTRODUCTION TO MODELING ACTIVITIES
A. Introduction 81
B. Methods 84
1. Mass Balance Calculations 84
2. Process Models 86
C. Recommendations 89
D. Reference 90
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ix
VI ST. MARYS RIVER
A, Status of the Ecosystem 91
1. Ecological Profile 91
2. Environmental Conditions 99
B, Specific Concerns . 154
1. Water. 154
2. Sediment , 157
3, Biota. 157
4, Uses Impaired 158
C. Sources ,....161
1. Point Source 161
2. Nonpoint Sources 170
3. Atmospheric Deposition 176
4. Contaminated Sediments . 178
5. Groundwater Contamination/Waste Sites . . 178
S. Navigation 180
7. Spills 180
8, Summary. 182
D. Data Quality Assessment 184
E. Process Modeling 185
1. Physical: Hydrodynamics, Wind, Waves
and Currents 185
2. Physical-Chemical-Biological: Fate and
Transport Models 189
F. Goals and Objectives for Remedial Programs . . 194
G. Adequacy of Existing Programs and Remedial
Options 196
1. Existing Regulatory Programs 196
2. Actual Discharges vs. Control Requirements 200
3. Adequacy of Control Mechanisms 201
4, Ontario Regulatory Initiatives 202
H. Recommendations 204
A. Industrial and Municipal
Point Source Remedial Recommendations . . 204
B. Nonpoint Source Remedial
Recommendations ........205
C. Surveys, Research and Development .... 206
I. Long Term Monitoring 209
1. UGLCCS vs. Other Monitoring Programs . . . 209
2. System Monitoring for Contaminants .... 210
3. Sources Monitoring 213
4, Habitat Monitoring 214
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J. References 216
CHAPTER ¥11 ST..CLAIR RIVER
A. Status of the Ecosystem . 223
1. Ecological Profile 223
2. Environmental Conditions 231
B. Specific Concerns 251
1. Conventional Pollutants 251
2. UGLCCS Toxic Organics and Heavy Metals . 253
3. Other Specific Contaminants 254
4. Habitat Alterations. ...... 255
C. Sources 256
1. Municipal and Industrial Point Sources . . 256
2. Urban Nonpoint Sources 262
3. Agricultural Nonpoint Sources 264
4. Atmospheric Deposition 268
5. Groundwater Contamination/Waste Sites . . 269
€. Spills 283
7. Contaminated Sediments 284
8. Navigation 289
D. Data Requirements and Assessments ....... 290
E. Modeling and Mass Balance Considerations . . . .291
1. Dispersion Models 291
2. Hydrodynamic Model 295
3. Chemical Transport Models 295
4. Unsteady Flow Model 296
5. Other Models 297
6. Model Applications . 297
F. Objectives and Goals for Remedial Programs . . .300
1. Water Quality, Sediment and Biota 300
2. Habitat Goals. 304
3. Uses to be Maintained and Restored .... 305
G. Adequacy of Existing Programs and Remedial
Options 306
1. Projection of the Ecosystem Quality. . . . 306
2. Assessment of Technical Adequacy of
Control Programs 308
3. Assessment of Regulatory Adequacy 311
H. Recommendations 313
A. Industrial and Municipal
Point Source Remedial Recommendations . .313
1. Nonpoint source Remedial Recommendations . 315
C. Surveys, Research and Development . . . .316
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xi
I. Long Term Monitoring .319
1. UGLCCS vs. Other Monitoring Programs ... 319
2. System Monitoring for Contaminants . . . . 323
3. Sources Monitoring 324
4. Habitat Monitoring 325
J, References .......... 325
VIII ST. CLAIR
A. Status of the Ecosystem 335
1. Ecological Profile 335
2. Environmental Conditions 342
B. Specific Concerns 375
1* Conventional Pollutants 375
2. Toxic Organics and Heavy Metals 377
3. Habitat Alterations 382
C. Sources '»,..,.. 385
1. Municipal Point Sources 385
2. Industrial Point Sources 392
3. Urban Nonpoint Sources 392
4. Rural Nonpoint Runoff 393
5. Atmospheric Deposition 395
6. Groundwater Contamination/Waste Sites . . 397
7. Spills 401
8. Contaminated Sediments 401
9. Navigation 402
D. Data Limitations 403
1. Sediment Surveys 403
2. Tributary Loadings 403
3. Point Sources .405
4. Fish Consumption Advisories 405
E. Modeling and Mass Balance Considerations . . . .406
1. Mass Balance Models 406
2. Process-Oriented Models 410
3. Summary. 420
F. Objectives and Goals for Remedial Programs . . . 421
1. Water Quality 421
2. Sediment Quality 422
3. Biota and Habitat 423
4. Management Issues 424
G. Adeciuacy of Existing Programs and Remedial
Options .426
1. Projection os Ecosystem Quality 426
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xii
2. Assessment of Technical Adequacy of Control
Programs ,.426
3. Regulatory Control Programs 429
H, Recommendations 431
A. Industrial and Municipal
Point Source Remedial Recommendations . .431
B. Nonpoint Source Remedial Recommendations . 431
C. Surveys, Research and Development . . . .433
I. Long Term Monitoring , 436
1. UGLCCS vs. Other Monitoring Programs . . 436
2. System Monitoring for Contaminants .... 437
3. Sources Monitoring . . , .' 440
4. Habitat Monitoring 441
J. References 442
IX DETROIT RIVER
A. Status of the Ecosystem ............ 447
1. Ecological Profile 447
2. Environmental Conditions 456
B. Specific Concerns 492
1. Conventional Pollutants 492
2. Organic Contaminants 492
3. Metals 494
4. Habitat Alterations . . • . . . 495
C. Sources 497
1. Point Sources 497
2. Urban Nonpoint Sources 513
3. Groundwater Contamination/Waste Sites . .517
4. Spills 527
S. Rural Runoff and Tributary Input ..... 527
6. Atmospheric Deposition ..... 530
7. Integrated Contaminant Input . 534
D. Data Quality Assurance and Control 537
1. Limitations 537
2. General Observations 537
E. Modeling and Mass Balance Considerations . . . .538
1. Mass Balance Models ..... 538
2. Process Modeling 551
F. Objectives and Goals for Remedial Programs . . . 555
1. Water Quality 555
2. Sediments 557
3. Biota and Habitat .558
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xiii
4. Other Issues , 560
G. Adequacy of Existing Programs and Remedial
Options ..... 561
1. projection of Ecosystem Quality 561
2. Assessment of Technical Adequacy of Control
Programs 562
3. Assessment of Regulatory Adequacy 565
H. Recommendations , 568
A, industrial and Municipal
Point source Remedial Recommendations . .568
B. Nonpoint Source Remedial Recommendations . 571
C. Surveys, Research and Development . . . . 573
D. Management Strategy for Remedial Programs 575
I. Long Term Monitoring . 577
1. UGLCCS vs. Other Monitoring Programs . . 577
2. System Monitoring for Contaminants .... 577
3. Habitat Monitoring 580
4. Sources Monitoring 581
J. References . . . . 583
APPENDIX I Lists of Committee, Workgroup, Task Force
and Area Synthesis Team Members 593
APPENDIX II Glossary and Units of Measure 607
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CHAPTER I
INTRODUCTION
The Upper Great Lakes Connecting Channels (UGLCC), for the pur-
pose of this report, includes the St. Marys River, St. Clair
River, Lake St. Clair, and the Detroit River, They are important
components of the Great Lakes Basin ecosystem and a valuable
resource. They serve as commercial transportation corridors, as
a source of drinking water and industrial water, as historical
and recreational resources, and as habitat for a wide diversity
of fauna and flora.
The intensive use which has taken place throughout this system
has resulted in serious environmental degradation in many areas.
As early as the 1940s concern existed about bacterial contamina-
tion, phenol problems and excessive levels of metals, phosphorus
and mercury. Attention is currently being focused on toxic
substances in water, sediment and biota throughout the system and
their effects on human health and the ecosystem.
Since 1974 the Detroit, St. Clair, and St. Marys Rivers have been
designated as "Problem Areas" and, more recently, as "Areas of
Concern" by the International Joint Commission. Despite massive
clean-up efforts and the expenditure of millions of dollars by
industry and government there remain areas in which general or
specific objectives of the 1978 Great Lakes Water Quality Agree-
ment (GLWQA) are exceeded (1). There have been noticeable im-
provements since the 1960s; however/ significant environmental
degradation and continuing impairment of beneficial uses occur.
1. Purpose and objectives
Although there have been numerous investigations and reports on
the environmental quality of the Connecting Channels, there has
previously been no attempt to integrate the information and focus
the scientific studies to produce recommendations for specific
action or identify remedial needs. This study was a landmark
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tdnational efforts in the continuing restoration of the Great
Lakes system. This report, by the Management Committee of the
UGLCC Study to the sponsoring agencies, is intended to provide
guidance for the remediation of these degraded waters and a
framework for long term monitoring to assess the effectiveness of
pollution controls. The vehicle for the delivery of the recom-
mendations , options and implementation will be the Remedial
Action Plan (RAP) process, RAPs are currently being prepared for
all 42 "Areas of Concern". These plans will identify problems,
goals for remediation, and remedial actions as well as
responsible agencies for implementation, a schedule for implemen-
tation, and necessary monitoring programs (1).
Specifically, the objectives for the study were as follows:
1) To determine the existing environmental condition of
the St. Marys River, St. Clair River, Lake St. Clair
and the Detroit River at its influx into the Western
Basin of Lake Erie and to identify information gaps.
2} To undertake additional, needed studies to:
a) identify and quantify the impacts of conventional and
toxic substances from point sources, nonpoint sources
(both runoff and contaminated groundwater) and tribu-
taries, on beneficial human uses and on plant and
animal populations in, along, and below these waters?
b) determine the adequacy of existing or proposed control
programs to ensure or restore beneficial uses,- and
c) recommend appropriate control and surveillance programs
to protect and monitor these waterways and the
downstream lakes.
2, Study Approach
In establishing this study, certain concepts were identified
based on the 1978 GLWQA and experience gained from earlier bina-
tional efforts. Of particular importance to the overall study
design were the concepts: ecosystem approach, enhanced data
quality management, mass balance requirements, and regulatory
management focus.
i) Ecosystem Approach. The Connecting Channels and Lake
St. Clair are complex ecosystems characterized by high
volumes and flows, strong currents and circulation
patterns, deposition and re-suspension of sediments,
diverse biota, extensive wetlands, and atmospheric and
terrestrial interactions. Superimposed on this system
are human activities in terms of physical alterations
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and pollutant loadings. In order to identify impacts
to the system and develop management scenarios for
control and remediation, all factors and their interac-
tions have to be evaluated and taken into considera-
tion. This effectively is the ecosystem approach as
defined in the Great Lakes Water Quality Agreement
between Canada and the United States, (1978, amended
1987} (1).
ii) Enhanced Data Quality Management. The experience of
earlier interagency, multi-media studies on the Great
Lakes has demonstrated the need to recognize and incor-
porate data quality assurance and quality control
(QA/QC) which are crucial to the overall utility of
study results. These considerations need to be taken
into account at the beginning of the study and not
viewed in hindsight. This concept was given consid-
erable priority within the UGLCC Study and respon-
sibility was vested in a Data Quality Management
Workgroup, Responsibilities of this workgroup included
reviewing analytical and field protocols; reviewing
internal quality assurance programs of participating
laboratories; assessing the statistical validity of
program results; and running a series.of "round robin"
analyses based on controlled mixtures. In addition,
investigators were encouraged to exchange split
samples.
iii) Mass Balance Requirements. In setting-up the UGLCC
Study emphasis was placed on providing data that could
be directly applied to identify remedial strategies and
develop regulatory actions. In order to relate the
potential source data to the environmental conditions,
study participants agreed to explore the use of pol-
lutant mass balance models. This was considered to be
the most comprehensive approach for the study design
and was also compatible with the ecosystem approach
noted earlier. If mass balance models could be develop-
ed and verified, aquatic ecosystem objectives could
easily be related to pollutant loads.
Ecosystem complexity and a general lack of historical
data for some areas, along with the limited time frame
of the UGLCC Study have limited the use of complex
models. Preliminary models have been developed and will
be utilized to provide a guide to the development of
management options where possible,
iv) Regulatory Management Focus. Previous binational stu-
dies of the Great Lakes tended to emphasize baseline
descriptions along with identification of stresses to
the overall environment. Rarely have specific regula-
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tory options and strategies been identified and agreed
to by the participating jurisdictions. From the outset
the UGLCC Study has emphasized regulatory management
recommendations (i.e. control and abatement) as the key
output for the study. This is particularly timely as
given the request by the Great Lakes Water Quality
Board of the International Joint Commission and the
recently updated GLWQA for specific RAPs in the Areas
of Concern.
These four concepts formed the framework to the study, although
it should be noted that in all cases time and resource con-
straints prevented their complete implementation. However, their
identification and subsequent guidance to the study were extreme-
ly valuable,
3. Management Structure
To oversee planning, implementation and reporting, a three-tier
management structure was established consisting of the Management
Committee, the Activities Integration Committee and eight specif-
ic activity workgroups. Resources necessary to undertake and
maintain the planning and administration of the study were pro-
vided by the participating agencies. Secretarial support was
provided by the U.S.EPA's Great Lakes National Program Office
.
i) Management Committee. This committee consisted of
representatives of the principal U.S. and Canadian
agencies. It was co-chaired by U.S.EPA and Environment
Canada. Members were agency managers who were in a
position to ensure follow-up to study priorities and
needs. In addition to the regular members, the chair-
person of the International Joint Commission's UGLCC
Task Force was an observer on this committee. He
provided a formal link with the Great Lakes Water
Quality Board.
The Management Committee provided overall guidance to
the study by identifying issues, establishing the
study's structure, approving the work plans, and ap-
proving the final report. This committee was also
responsible for identifying environmental management
requirements in the study area with regard to appro-
priate regulatory options.
ii) Activities Integration Committee. The AIC was a sub-
committee of the Management Committee. It was respon-
sible for preparing and overseeing implementation of
the study work plans and for the final report. The AIC
was co-chaired by Environment Canada and the U.S.EPA.
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Members were workgroup chairpersons plus 2 scientific
coordinators.
iii) Study Workgroups. Eight workgroups were established
for this study: biota, sediment, water quality, data
quality management, modeling, point source, nonpoint
source, and long-term monitoring. A regulatory task
force was established to review existing regulatory
measures and help evaluate proposed remedial measures.
The results of this review have been incorporated
directly into the final report (Chapter III). Members
of workgroups were technical experts from among the
participating agencies. Each workgroup operated under
the guidance of a single chairperson.
4. Schedule
The UGLCC Study was conducted in 3 phases. Phase 1 was the
planning stage which included the development of work plans,
quality assurance programs and preliminary models. This phase
was initiated with a planning workshop for 60 key participants,
A comprehensive technical literature review was also carried out
during the planning phase in order to identify gaps and plan the
next phase (2).
Phase II included the two field seasons (1985 and 1986). A'mid-
course workshop was held between the two study years for the
benefit of about 100 of the principal investigators. This work-
shop was established to prepare work plans for the 1986 activ-
ities; exchange information from the previous field season;
identify progress to date and additional needs; and identify and
resolve logistics of ship support and equipment sharing.
The final phase - the report writing phase - began in January
1987 at a writers workshop held in Windsor. This workshop pro-
vided 40 workgroup participants, both chairmen and principal
investigators, the opportunity to discuss and finalize reporting
formats, writing process, logistics, and timing as well as iden-
tify inter and intra workgroup co-ordination needs. A workshop
was held in Ann Arbor in January 1988 for six of the workgroups
to present their results and information to those synthesizing
workgroup reports into the four area reports. A final workshop,
held in Burlington in June 1988, was conducted for the AIC to
review each of the four area reports prior to submission of the
draft final report to the Management Committee.
The report writing was carried-out in four stages. The first
stage consisted of the preparation of the approximately 170
individual project reports by the principal investigators. The
second stage consisted of 26 media specific workgroup reports (3)
which were prepared from the project reports. Area synthesis
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writing constituted the 3rd stage. Four teams (1 for each geo-
graphic area), each with Canadian and U.S. co-leads, integrated
the workgroup products into a single report for each of the
geographic areas. The 4th stage of writing was the drafting of
the final report and executive summary. At this stage the key
conclusions and recommendations of the study were identified and
prepared by the AIC, The draft final report was presented to the
Management committee on July 20, 1988 for final review. The
technical comments that were received were used to prepare the
final report which was formally submitted to the sponsoring
agencies.
5. Technical Activities
In order to meet the objectives of the UGLCC Study a number of
activities were identified with regard to technical data needs.
These were grouped according to workgroup subject areas (eg.
point source, biota, sediment, etc.) and formed the basis for
defining specific projects or investigations. Activities in-
cluded, for example, assessing combined sewer overflows, tribu-
tary monitoring, describing circulation patterns and sediment re-
suspension, and estimating nonpoint source loadings of nutrients
and toxics. For the 1986 field season, 72 activities were de-
fined and approximately 170 specific projects were undertaken.
The technical activities were designed particularly to: (1)
describe the nature and abundance of macrophytes, benthos and
fish in order to establish baseline conditions to which future
monitoring of habitat and population structure could be compared;
and (2} identify pollutant sources loadings in order to drive
the models and develop remedial strategies.
6. Parameters of Interest
The Activities Integration Committee identified a number of
contaminants including heavy metals, organic contaminants and
conventional pollutants which are known or suspected to be in
exceedence of criteria or at high levels in portions of the study
area. These are listed in Table 1-1. For additional information
on the selection of these parameters and their occurrence in the
study area, the reader is referred to the report outlining pre-
Study conditions (2).
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1-1
UGLCCS parameters of concern.
COMMON
ABBREVIATIONS
PARAMETERS
Organics
PCBs
HCB
OCS
PAHs
Polychlorinated biphenyls
Hexaehlorobeniene
Octachlorostyrene
Polycyclic aromatic hydrocarbons
Oil Grease
Phenols (total phenolics)
Chlorinated phenols
Metals
Cd
Pb
Zn
Hg
Cu
Ni
Co
Fe
Cr
Cadmium
Lead
2inc
Mercury
Copper
Nickel
Cobalt
Iron
Chromium
Conventional/Other
P
NH3
Phosphorus
Ammonia
Chlorides
Residule chlorine
Cyanide
Chioramines
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7. References
1. International Joint Commission, 1988, Revised Great Lakes
Water Quality Agreement of 1978. IJC, Windsor, Ont. 130 p.
2. Limno-Tech. 1985. Summary of the existing status of the
Upper Great Lakes Connecting Channels data, unpub. manu-
script prepared for the UGLCC Study. March, 1985. Limno-
Tech Inc. 156 p. plus appendices and bibliography.
3. a. Water Workgroup, UGLCCS. 1988. St. Clair and Detroit
Rivers. Prepared by Water Workgroup. D.J. Williams, Chair.
Level II unpublished Mss., 89 pp.
b. Biota Workgroup, UGLCCS. 1988. Detroit River Biota and
Their Habitats: A Geographic Area Report. Prepared by
Edsall, T.A., P.B. Kauss, D. Kenaga, J. Leach, M. Munawar,
T. Nalepa and S. Thorney. Level II unpublished Mss., 90 pp.
c. Biota Workgroup, UGLCCS. 1988. St. Clair River Biota
and Their Habitats: Geographic Area Report. Prepared by
Edsall, T.A., P.B. Kauss, D. Kenaga, J. Leach, M. Munawar,
T. Nalepa and S. Thornley. Level II unpublished Mss., 90
pp.
d. Biota Workgroup, UGLCCS. 1988. Lake St. Clair Biota and
Their Habitats: A Geographic Area Report. Prepared by
Edwall, T.A., P.B. Kauss, D. Kenaga, J. Leach, M. Munawar,
T. Nalepa, G. Sprules and S. Thornley. Level II unpublished
Mss., 80 pp.
e. Biota Workgroup, UGLCCS. 1988. St. Marys River Biota
and Their Habitats: A Geographic Area Report. Prepared by
Edsall, T.A., P.B. Kauss, D. Kenaga, T. Kubiak, J. Leach, M.
Munawar, T. Nalepa and S. Thornley. Level II unpublished
Mss., 80 pp.
f. Modeling Workgroup, UGLCCS, 1988. Modeling workgroup
Geographic Area Synthesis Report. Prepared by Modeling
Workgroup, T.D, Fontaine, Chair. Level II published Mss.,
193 pp.
g. Point Source Workgroup, UGLCCS. 1988. Geographic Area
Report; Detroit River. Prepared by Point Source Workgroup,
P, Horvatin, Chair. Level II unpublished Mss., 160 pp.
h. Point Source Workgroup, UGLCCS. 1988. Geographic Area
Report; St. Marys River. Prepared by Point Source
Workgroup, P. Horvatin, Chair. Level II unpublished Mss,,
65 pp.
-------
i. Point Source Workgroup, UGLCCS. 1988. Geographic Area
Report: St. Clair River. Prepared by Point Source
Workgroup, P. Horvatin, Chair. Level II unpublished Mss.,
125 pp.
j. Point Source Workgroup, UGLCCS. 1988. Geographic Area
Report: Lake St. Clair. Prepared by Point Source Workgroup,
P. Horvatin, Chair, Level II unpublished Mss., 95 pp.
k. Data Quality Management Workgroup, UGLCCS. 1987,
revised. Report of the Data Quality Management Work Group.
Prepared by the Data Quality Management Workgroup, A.S.Y.
Chau, Chair. Level II unpublished Mss., 182 pp.
1. Data Quality Management workgroup, UGLCCS, 1988.
Interlaboratory performance evaluation study integrated
report Part II: trace metals. Prepared by W.c. Li, A.S.Y.
Chau and E. Kokotich, NWRI, Environment Canada, Burlington,
Ont: 11 p + Tables and Figures.
m. Data Quality Management Workgroup, UGLCCS, 1988.
Interlaboratory performance evaluation study integrated
report Part I: organic Parameters, prepared by W.c. Li,
A.S.Y. Chau and E. Kokotich, NWRI, Environment Canada,
Burlington, Ont: 19 p + Tables and Figures.
n. Sediment Workgroup, UGLCCS. 1987. Sediments of the
Detroit River. Prepared by A.G. Kizlauskas and P.E.
Pranckevicius. Level II unpublished Mss., 224 pp.
o. Sediment Workgroup, UGLCCS. 1987. Current and
Historical Contamination of Sediment in the St. Marys River.
Prepared by R.J, Hesselberg and Y. Hamdy. Level II
unpublished Mss,, 42 pp.
p. Sediment Workgroup, UGLCCS. 1987. St. Clair River
Sediments. Prepared by B.G. Oliver. Level II unpublished
Mss., 54 pp.
q. Sediment Workgroup, UGLCCS. 1988, Lake St. Clair Bottom
Sediments. Prepared by Sediment Workgroup, Y. Hamdy, Chair.
Level II unpublished Mss., 80 pp.
r. Sediment Workgroup, UGLCCS. 1988. Integrated Study of
Exposure and Biological Effects of In-Place Sediment
Pollutants (Interim Results). Prepared by Kreis, Jr., R.G.
Level II unpublished Mss., 1038 pp.
s. Nonpoint Source Workgroup, UGLCCS. 1987. Contaminants
in Urban Runoff in the Great Lakes Connecting Channels Area.
Prepared by J. Marsalek and H.Y.F. Ng. Level II unpublished
Mss., 71 pp.
-------
10
t. Nonpoint Source Workgroup, UGLCCS. 1987. Agricultural
Sources of Pollution; Detroit River. Prepared by Wall,
G.J., E.A. Pringle and T. Dickinson. Level II unpublished
Mss., 11 pp.
u. Nonpoint Source Workgroup, UGLCCS. 1987. Agricultural
Sources of Pollution: Lake St. Clair. Prepared by Wall,
G.J., E.A. Pringle and T. Dickinson. Level II unpublished
Mss., 224 pp.
v. Nonpoint Source Workgroup, UGLCCS. 1987. Agricultural
Sources of Pollution; St. Clair River. Prepared by Wall,
G.J., E.A. Pringle and T. Dickinson. Level II unpublished
Mss., 12 pp.
w. Nonpoint Source Workgroup, UGLCCS. 1988. Waste Disposal
Sites and Potential Ground Water contamination: St. Clair
River, Prepared by Nonpoint Source Workgroup, G. Sherbin,
Chair. Level II unpublished Mss., 77 pp.
x. Nonpoint Source Workgroup, UGLCCS. 1988. Waste Disposal
Sites and Potential Ground Water Contamination: St. Marys
River. Prepared by Nonpoint source Workgroup, G. Sherbin,
Chair. Level II unpublished Mss., 39 pp. •
y, Nonpoint Source Workgroup, UGLCCS. 1988. Waste Disposal
Sites and Potential Ground Water Contamination: Detroit
River. Prepared by Nonpoint Source Workgroup, G. Sherbin,
Chair. Level II unpublished Mss., 75 pp.
z, Nonpoint Source workgroup, UGLCCS. 1988. Waste Disposal
Sites and Potential Ground Water Contamination: Lake St.
Clair. Prepared by Nonpoint Source Workgroup, G. Sherbin,
Chair. Level II unpublished Mss., 45 pp.
-------
CHAPTER II
OVERVIEW OF THE
1. Introduction
The Upper Great Lakes Connecting Channels serve as conduits for
the waters of the upper lakes (Superior, Michigan and Huron) to
feed into the lower lakes (Erie and Ontario - Figure 11-1}»
The setting for the Connecting Channels is the Great Lakes Basin.
This basin is the product of complex geological, hydrological,
climatological, biological and sociological processes operating
over various scales of time^. These processes are not static but
dynamic and thus, the system will continue to evolve. This rep-
ort is, therefore, very much a snapshot in time. However, its
implications are far reaching. Implementation of the recommen-
dations will influence the nature and quality of our Great Lakes
Ecosystem as it evolves.
The Upper Great Lakes Connecting Channels are integral components
of the Great Lakes Basin, They function as the plumbing system
of the lakes' basins funnelling large volumes of water, sediment
and nutrients through relatively narrow channels. As such they
have been an attraction to both wildlife humans.
Nutrients and diverse habitat conditions have provided sustenance
to large populations of numerous species of flora and fauna,
particularly fish waterfowl. The abundance of as well
as fresh drinking water attracted native Indian settlements,
Europeans, in turn, were attracted to these channels for the
additional benefits related to shipping,- relative of
1 For an overview of these process and additional referen-
ces, the reader is referred to {!).
-------
FIGURE 11-1
MICHIGAN
MS/H
H-Jf }
j$t, Mtfn Rfftf i
GREAT LAKES
BASIN
SHOWING UPPIH CONN1CTINC
CMANNILS
MICHIGAN
ONTARIO
KIIe*n«tr*« i I . ^^.
Ma* oi io "is
-------
13
crossing (each river is currently a. major international crossing
point); large volumes of water for cheap power, industrial proce-
sses and waste receiving; and recreational pursuits.
The vastness of the Great Lakes' water and fisheries resources
must have appeared limitless to the early Europeans. However,
physical damages as a result of dredging (channelsj, filling
(wetlands), increased sedimentation and water temperature (re-
lated to forest clearing for agriculture), and over-fishing,
along with pathogen loadings (from human waste) quickly impacted
the ecosystem. In less than 100 years of settlement, by the
early 1900s, these impacts were considered very serious and re-
sulted in disease and death among dwellers along the channels,
Physical and chemical disruptions continued through the liOOs
resulting in crashes of certain native fish populations and in-
creasing occurrences of oil films, human waste, dead, fish, algae
and other visible problems. Less visible but just as serious
types of pollutants - heavy metals and organic chemicals - were
released into the ecosystem virtually uncontrolled during the
mid-190Os. Mercury, lead, DDT, PCBs, and others were released as
products of the rapidly growing North American industrial com-
plex. The Great Lakes Connecting Channels (including the Niagara
and St. Lawrence Rivers) were to many of the industries
manufacturing, utilizing, and discarding these contaminants.
Since about 1970 environmental concern and actions by federal,
state and provincial governments have resulted in dramatic im-
provements. Industrial and municipal sources of contaminants
have been controlled to various degrees. However, we have the
legacy of historical pollution manifested in river and lake sedi-
ments (in-place pollutants) and groundwater contributions from
active and inactive waste sites.
Continued improvements to the Great Lakes ecosystem must consider
these, along with ongoing discharges, and inputs from diffuse
sources such as urban and agricultural runoff and atmospheric
deposition,1
The remainder of this chapter will summarize characteristics of
the St. Marys, St. Clair Detroit rivers and Lake St. Clair.
Each area is portrayed in Figures II-2 through II-5 and specific
information is provided in Tables ll-l through II-4, These ta-
bles summarise watershed characteristics (II-l), water uses {II-
2), land uses (II-3), and environmental concerns {II-4) compara-
tively for each of the 4 study areas. Each area is discussed in
detail with regard to study findings and recommendations for
remedial measures in Chapters VI through IX,
-------
TABLE Il-i
Watershed characteristics of the Upper Great Lakes Connecting Channels.
Inlet
Outlet
Length (Area!*
llevation Fall(m)*
Flow m3 /s x 1000*"
Minimum
Average
Maximum
Average Plow Vel. m/s*
Depth (ml*
Width (km)*
Retention Times
Controlled Flow
Land Drainage Area***
km2 x 1 , 000
(cummulative total)
* LTI document (2).
** David Cowgill, U.S.
»** Calculated from (1)
St. Marys
River
L. Superior
L. Huron
101-121 km
6.75
1.2
2.2
3.7
0.6-1.5
Shallow-30
0.3-6.4
" 2 days
Y
49.3
Army Corps of
and (2).
St. Clair
River
L, Huron
L. St. Clair
64 kB
1.5
3.0
5.2
6.7
0.6-1.8
9-21
0.25-1.2
21 hrs
N
146.6 .
Engineers, pers.
Lake
St. Clair
St. Clair R.
Detroit River
1,115 k«2
-
-
-
-
0.02-0.08 0
3.4 avg.
8.2 Max.
39 0
2-9 day a
N
159.0
coma.
Detroit
River
Lake St. Clair
L. Erie
51 km
1.0
3.2
i.3
7. 1
.3-0.fi
6-15
.66-3.0
21 hrs
N
160.9
-------
15
TABLE II-2
u»e of the Upper Qre«t b«ke» Cemneetini Ch«nn«ii,
St. Marre St. Clair Luke Detroit
!iv*r Riv«r St. Clair River
Shipping S I S S
Coamereiail Fishing L M F N
Sport Fiihinf S I S S
Bo*ting/Sailin< F i I S
Swimming L F S 0
S01FACI KftTSl SUPPIUS TO:
Drinltinf W«t«r Intalw
- M«nicip»l S I I X
- Cannunai./Private K X X X
1 n £ a ke s
- Iron 4 Steel " X X
- Pulp 4 Paper X
» Peireeh««ie»l X X
- Refining X X
— Ttwrital Generating X
- Hydroelectric X
- Mavisation (LoekiI X
- Mineral (Salt i Li»«I X
lieITvise WATER FOR:
Municipal STP X X X X
Industri al
- Iron 4 Steel X X
- Pulp 4 Paper X
- Petrochenicai X X
- Refining X
- Th«r«*i G*n«r«tinf X X
- Mineral (Salt It Linn) X
- Fabrication (Auto I X
Ship Ballast X X X X
N - Neflifible Use
L - Limted Us*
0 - Occasional Use
F - Frequent Uae
S - Significant - High Use
X - Present
-------
TABLE 11-3
Land use within 5 km of the Upper Great Lakes Connecting Channels* shoreline
St. Harys St. Clair Lake Detroit
River River St. Clair River
Urban
Rural Residential
Agricultural
Recreational
( Marinas/Beaches 1
Wildlife Habitat/Open Space
Industrial
Waste Disposal
Native Lands
F
O
N
O
S
O
X
X
F
S
O
F
F
S
X
X
O
O
S
S
F
N
X
X
S
F
O
S
L
S
X
N
N - Negigible Use
X - Present
L - Limited Use
O - Occasional Use
F - Frequent Use
S - Significant - High
-------
Contaminant
TABLE II-4
of contaninant concern* In the Upper Great Lakei Connecting Channels,
Water
Sed merit
* SH - St. M«ry» River LSC - Lake St. Clair
D - Detroit River SC - St. Clair River
Biota
Nutrients
- Phosphorus
- Nitrogen
Bacteria
Chlorides
Oil and Grease
Phenols
Pesticides
PCBs
PAHs
Other Organic!
Heavy Metals
Mercury
Cyanide
Habitat Alteration
SM* SC LSC 0
SN LSC 0
SM LSC D
SM SC D
SC D
SM SC D
SM SC D
LSC
D
SM D
SC D
SM SC LSC D
SC
SH
LSC
SM SC LSC D SM SC
SM
D SM
SO
SC
SM SC D SM SC
SM SC
LSC
SH SC LSC II SH SC
SH SC LSC D SM SC
SC LSC D SC
SH SC LSC D SM SC
SM SC LSC SM SC
SC LSC D SC
LSC
LSC
LSC
LSC
LSC
LSC
LSC
LSC
LSC
LSC
11
D
D
D
D
D
D
P
0
D
D
D
D
-------
18
2. St. Marys River2
The St. Marys River delivers the outflow of Lake Superior to Lake
Huron (Figure II-2), It is partially controlled by locks and
compensating structures to allow navigation and power generation.
Thus, the river is not subject to large unpredictable fluctua-
tions in flow rates. Sediments in the river range from sands and
gravels, particularly in the upper reaches and near the rapids,
to silts and clays. The finer material generally occurs in down-
stream locations and in embayments. The St. Marys River has an
active sports fishery based primarily on trout, salmon, walleye,
yellow perch, pike, and smelt. It formerly supported a major
whitefish commercial fishery. The river is known to have 75
species of fish.
Water is withdrawn to provide the major source of drinking water3
for a U.S. population of approximately 15,000 as well as process
water for the steel industry (Algoma Steel Co.), pulp and paper
processing (St. Marys Paper) and other smaller industries. Most
of the industrial development is found on the Canadian side of
the River which is also home to the largest population along the
river (85,000). Other primary water uses include navigation and
recreational boating.
The watershed draining into the river is predominantly forested
with low intensity agriculture occurring on the relatively flat-
lying plains or either side of the river.
Industrial and municipal effluents have resulted in contaminant
problems in sediment and water related to phenols, cyanide, PAHs,
PCBs, iron, zinc, phosphorus ammonia. Contaminant problems
have also resulted in impaired benthic fauna. Physical disrup-
tion related to power generation navigation has also adverse-
ly impacted fish habitat. Past surveys of sediment, benthos and
water quality indicate that conditions along the U.S. shore and
in Lake Nicolet are good and these areas can support a variety of
water uses. The zone of greatest impact in the St. Marys River
is along the Canadian shore downstream of industrial and munici-
pal discharges. This zone includes the Algoma slip, the area
below the rapids, the Sault Ste. Marie waterfront and downstream
of the East End Sewage Treatment Plant in the channel feeding
Lake George.
*• Primary sources for sections 2 to 5 are (2,3).
3 Wells provide the primary source of drinking water for
the Canadian population. It is supplemented with St. Marys River
water as necessary.
-------
FIGURE 11-2
St. Marys River
KILOMETERS
2468 tfl 12 14 16
2345678*510
MILES
GREAT LAKES INFORMATION SYSTEM
DEPARTMENT OF NATURAL RESOURCES
LAND AND WATER MANAGEMENT DIVISION
-------
20
3. St. Clair River
The St. Clair River is not controlled in any manner. It serves
as the natural outlet of Lake Huron and drains into Lake St.
Clair where it has formed the only major riverine delta on the
Great Lakes - the St. Clair delta, also known as the St. Clair
flats (Figure 11-3}. The conditions which have contributed to
the formation of this delta include: rapid deceleration of the
flow from the river as it disperses into the wide shallow basin
of Lake St. Clair; very high suspended sediment loads carried by
the river from sources in the Lake Huron watershed; stable condi-
tions at the river/lake interface since the channel was first
established; and the straight channel of the St. Clair River with
few islands or other depositional sites.
The bed of the river is characterized by relatively coarse frac-
tions consisting of sand and gravel and by an erosional surface
of clay till. This reflects the high energy environment of the
river which acts as a conduit to Lake St. Clair and the delta for
the finer material (fine sands, silts, and clays) originating in
the Lake Huron watershed.
The St. Clair River provides a corridor for fish between Lakes
Huron and Erie jbut also supports an indigenous fishery. Promin-
ent species include walleye, muskellunge, rainbow trout, lake
sturgeon, smelt, salmon, bass, catfish, yellow perch and fresh-
water drum. The St. Clair River and its delta are known to serve
as habitat for fish during their sensitive life stages (spawning,
rearing). The delta is unique, serving not only as an important
fish habitat but also as habitat .for other wildlife including
waterfowl, reptiles, amphibians, fur-bearing mammals and plant
species. This diversity is due, in large part, to the remaining
extensive wetlands and wetland-upland complexes of the delta and
its environs.
The St. Clair River serves as a major shipping channel; as a
recreational resource (including boating, fishing, hunting, and
swimming); a food source for native Canadians; a source of drink-
ing water for U.S. and Canadian citizens; industrial process
water for Canada's largest petro-chemical complex; and a recep-
tacle for treated municipal and industrial effluents. Clearly,
these uses conflict in terms of maintaining good water, sediment
and biota quality.
The immediate shores of the river are used for a mixture of
urban, industrial and recreational uses. Inland, the predominant
land use is intensive agriculture.
Contaminant problems specific to the St. Clair River include
sediment contaminated with PCBs, oil and grease, mercury, and
other metals; and fisheries impacted by PCBs and mercury. Con-
taminants -characteristic of the petro-chemical industry and found
-------
FJGURf II-3
Q+ /"•!«:.. n:
-------
22
in elevated levels in biota, sediment and water include; hexa-
chlorobenzene, hexachlorobutadiene, octaehlorostyrene, carbon
tetraehloride, perehloroethylene, and hexachloroethane. These
chemicals are confined to a band of water approximately 100 m
wide along the Ontario shoreline adjacent to the industrial area
at Sarnia,
In addition to direct point discharges from industrial and mun-
icipal sources, concern for ongoing and potential contamination
of the river has been identified for such nonpoint sources as:
surface landfill sites, liquid waste disposal zones in deep geo-
logical strata ("deep wells"), urban runoff, and agricultural
runoff. Even though the petrochemical industry is concentrated
on the Canadian side of the river, municipal outfalls and similar
nonpoint sources occur on the U.S. side.
Recent surveys of benthic organisms in the St. Clair River indi-
cate that the benthic community is impaired in the immediate
vicinity of the petro-chemical industry. However, the zone of
impairment has decreased significantly since the late 1960s.
This reflects improvements in industrial and municipal effluent
duality throughout the 1970s and 1910s. Significant reductions
of organic contaminants {80 to 90%} in certain outfalls have been
achieved even since the initiation of the Upper Great Lakes Con-
necting Channels Study (4},
4. Lake St. Clair
Lake it. Clair is not considered of the five Great Lakes,
however, it is a large lake (Figure II-4 and Table 11-3). It is
a very shallow lake compared to its surface area, resulting in
extreme variability in water levels over and time due to
short term climatic changes (winds, barometric pressure) and
hydrologic flow regime (inflow-outflow),
The shallow character of the lake also influences sediment dynam-
ics. The primary source for sediments is the Lake Huron watershed
via the St. Clair River. Deltaic formation at the mouth of the
river has, in a relatively short geologic time (post-glacial),
resulted in the in-filling of approximately one-fifth of the lake
area. Fine grained sediments, particulary clays, are deposited
in the deeper portions of the lake. The majority of the lake
bottom, however, consists of relatively coarse sands and gravels
reflecting the high wave-energy environment. Sediment depth in
the main body of the lake, in fact, averages only 7 cm overlying
the glacial till. Thus, much of the material entering the lake
from the delta and its major tributaries (the Clinton, Sydenham
and Thames Rivers) ultimately moves out of the lake, through the
Detroit River and into Lake Erie.
-------
FIGURE 11-4
Lake St. Clair
OMM UXES IMFO»«t!OH WStEN
DEnWTHDtr Of MSTUBK. BESOUBCES
LM« «») WMIII mmCEMEXT onisrw
-------
24
Over 70 species of fish are known to reside in or migrate through
Lake St. Clair. The lake is particularly known for its muskel-
lunge fishing. Other warm water species common to the lake in-
clude pike, bass, perch, crappie, and bluegills. Walleye, sal-
mon, trout, whitefish, smelt, and suckers are also part of the
sport fishery. The delta area and Anchor Bay are known to be the
most active spawning areas of the lake. Generally, the near
shore areas and tributaries to the lake provide habitat which is
crucial to the lakes' fishery. The impressive fisheries and
other wildlife resources (both indigenous and migratory) owe
their existence, in large part, to the extensive wetland com-
munities in the delta and along most of the undeveloped shoreline
of Lake St. Clair.
Direct uses of the lake are primarily recreational. This in-
cludes the largest number of registered boats on the Great Lakes
as well as fishing, and hunting for fur-bearing animals and
waterfowl. Other uses include drinking water and commercial
shipping. Lake St. Clair is unique among the other UGLCCS areas
in that there are no significant industries or major urban cen-
tres located on its shores (except for the northern portion of
the Detroit Metropolitan area). However, several large com-
munities are found on the tributaries which feed into the lake.
Surrounding land uses are primarily natural (wetlands) and inten-
sive agriculture. Large expanses of the original wetlands have
been drained for agricultural purposes. In Ontario, for example,
over 90% of the original wetland area surrounding Lake St. Clair
has been converted to agriculture (5), In fact, over 400,000 ha
of wetlands in three contiguous counties have been converted
since the late 1800s. This has undoubtedly exerted a very
significant impact on the wildlife resources of Lake St. Clair
and its environs.
Lake St. Clair is the only UGLCCS area which is not also clas-
sified by the IJC as an "Area of Concern". There is a lack of
direct point sources of contaminants and/or heavily contaminated
sediments. The lake does, however, act as a mixing zone for
various organic and inorganic contaminants originating from up-
stream sources and from atmospheric deposition. These include
industrial and municipal sources from 2 Areas of concern (St.
Clair and Clinton Rivers) and nutrients and pesticides from agri-
cultural drainage via drainage ditches and the tributary rivers.
Phosphorus loadings (primarily agricultural) and mercury contam-
ination of the fishery are primary concerns in Lake St. Clair.
Levels of mercury in fish have declined since the early 1970s and
conservation authorities in southwestern Ontario (particularly
the Thames River C.A.) have developed programs to reduce sediment
loads derived from agricultural lands (and hence adsorbed nu-
trients/pesticides} .
-------
25
5. Detroit River
The Detroit River is the furthest downstream Connecting Channel
of this study. It connects Lake St. Clair with Lake Erie (Figure
11-5}, Flow in the Detroit River is complex due to numerous
islands and channels, particularly in the lower half of its
reach, and to unique effects from fluctuating water levels in
Lake Erie, Wind set-up and barometric pressure changes can cause
the western portion of Lake Erie to rise 2 to 2.5 m during
storms. This is greater than the total elevation change of the
Detroit River from head to mouth (< i m), When such conditions
occur, the river flow slows down and actually reverses for short
distances.
Bottom sediments in the Detroit River vary from clay to boulders
and bedrock. Overall, sediments tend to be coarse (sand and
gravel) due to medium to high current velocities which transport
most of the suspended materials into the western portion of Lake
Erie. Minor depositional zones for fine material (clays, silts)
occur in the river adjacent to islands (particulary downstream of
the islands) and the near shore (mostly along the Canadian side),
Bedrock forms the river bed in some portions of the lower channel
such as in the 10 km reach between Fighting and Bois Blanc Is-
lands ,
Although fish spawning and nursery habitats are less .available in
the Detroit River than in Lake St. Clair, the river sustains a
diverse fishery. Both resident (rainbow smelt, alewives and
gizzard shad) and migratory species are known to be present.
Species common to this river include walleye, bass, and yellow
and white perch. The river is considered to have a fairly
healthy fishery in terms of numbers and diversity given its his-
tory and degree of pollution and habitat alterations (dredging,
filling, bulkheading, etc). However, these activities, due to
large scale urbanization, have clearly restricted plant and other
wildlife abundance and diversity relative to the study areas.
During spring and fall migrations, the lower Detroit River, en-
compassing the Wyandotte National Wildlife Refuge, is especially
critical as a feeding and staging area for several waterfowl
species.
The Detroit River watershed is the most urbanized of the four
areas covered in this study. It is home to a population greater
than 5 million and is one of the world's most heavily industrial-
ized areas. This industry includes a vast automotive complex
including fabrication and assembly as well as many metal and
plastic based support industries. Numerous other types of manu-
facturing also occur. Water uses include drinking water, recrea-
tional activities (boating and fishing), shipping, industrial
cooling and process water withdrawals, and municipal and indus-
trial waste discharges.
-------
GREAT LAKES INFORMATION SYSTEM
DEPARTMENT OF NATUFWL RESOURCES
LAND AND WATER MANAGEMENT DIVISION
FIGURE 11-5
Detroit River
-------
27
Surrounding land uses are principally urban (U.S.) and agricul-
tural (Canada) although numerous recreational areas are present
{e.g. Belle Island, Boblo Island and Dieppe Park). A particular
concern is the restricted river access due to urban and indus-
trial developments along the waterfront, particularly on the U.S.
side.
Contamination problems in the Detroit River include: sediments
contaminated with PCBs, oil and grease, mercury, and other
metals; water quality violations for phenols, iron, and fecal
coliform; and an impacted fishery {particularly by PCBs), water-
fowl and benthic community. Surveys of benthic communities show
a zone severely impacted by contamination off-shore and just
downstream of Zug Island. The remainder of the river downstream
of this island, but confined to the U.S. shore, also shows evi-
dence of severe impairment. Normal communities are found up-
stream of Zug Island and along the entire Canadian shore.
Contaminants originate from point and nonpoint sources including
numerous municipal and industrial outfalls, urban runoff, combin-
ed sewer overflows, agricultural runoff, and shallow groundwater
contributions impacted by many waste sites. In addition to
these, the river receives contaminants from upstream sources
including 3 IJC Areas of Concern (St. Clair River, Clinton River
and Rouge River),
-------
28
6. References
1. U.S. Environmental Protection Agency and Environment Canada,
1987. The_Great lakes: An Environmental Atlas ,_and..Resource
Book... U.S. EPA, Env. Can., Brock U, and Northwestern U. ,
Toronto and Chicago. ISBN 0-662-15189-5, 44p plus wall map.
2, Limno-Tech. 1985. 1985 Summary of the existing status of the
Upper Great Lakes Connecting Channels data, unpub.
manuscript prepared for the UGLCC Study, March 1985, Limno-
Tech Inc. 156 p. plus appendices and bibliography.
3. Great Lakes Water Quality Board. 1987. 1987 Report on Great
Lakes Water Quality. GLWQB, International Joint Comm.,
Windsor, Ontario. 236p.
4. Ontario Ministry of the Environment and Environment Canada.
1988. Status report of the recommendations of the 1986 St.
Clair River Pollution Investigation Report. OMOE and DOE,
Toronto.
5. Snell, E.A, 1987. Wetland distribution and conversion in
southern Ontario. Lands Dir, Env. Can., Ottawa, working-'
Paper #48. 53p. .
-------
CHAPTER III
REGULATORY BASIS OF ENVIRONMENTAL QUALITY CONTROL
A. INTRODUCTION
Environmental quality of the Upper Great Lakes Connecting Channels
is influenced by major environmental regulations, agreements and
programs which have been developed at several governmental levels.
The Canadian and United States federal governments, the State of
Michigan, the Province of Ontario, and their regulatory agencies
have promulgated acts and regulations to protect and enhance the
environmental quality of the Great Lakes, Binational agreements
at both the federal, state and provincial level have also been
made. As a result, an extensive and comprehensive base of legis-
lation and agreements exists to protect environmental quality of
the connecting channels.
This chapter provides an overview of existing regulatory and
administrative programs which act to protect and enhance the en-
vironmental quality of the Upper Great Lakes Connecting Channels.
A more extensive review of existing regulatory programs pertinent
to these shared waterways is presented in Appendix 3.
1. Binational Agreements
The governments of Canada and the United States have long shared
a concern for the environmental quality of the Great Lakes Basin.
To confirm their commitment to restore and enhance the water
quality of the Great Lakes both federal governments entered into
the Great Lakes Water Quality Agreement in 1972 (GLWQA). The
GLWQA and its associated Annexes were subsequently amended in
1978, 1985 and 1987. The Agreement contains general and specific
objectives to maintain and augment water quality by ensuring the
Great Lakes are free from substances resulting from human ac-
tivity, are unsightly or deleterious, or interfere with benefi-
cial uses of the water. The seventeen Annexes of the GLWQA
outline specific objectives and programs aimed at maintaining and
-------
30
improving the quality of these shared waters. For many para-
meters, the Annexes provide numerical ambient water quality and
fish contaminant objectives, as well as narrative guidelines for
other categories of contaminants and discharges. The GLwQA,
while outlining objectives which both governments strive to
achieve, is an agreement only and has no regulatory authority in
and of itself.
Ontario and Michigan have also entered into binational agreements
regarding Great Lakes water quality issues. Recently, in April
1988, two Memoranda of Understanding were signed; one concerning
accidental discharges of contaminants into the Great Lakes and
the other, an associated Joint Notification Plan for such dis-
charges .
2. Federal, State and Provincial Environmental Control Legisla-
tion and Programs - An Overview
Numerous legislative acts, regulations and programs exist at the
federal, state and provincial levels which regulate point and
nonpoint source discharges, and affect ambient water, sedi-
ment and biota quality. Table III-l lists major environmental
acts from which specific environmental regulations and programs
are derived. In most cases, a variety of regulations and pro-
grams are developed from each act, making their effect far-
reaching. These major acts provide a comprehensive framework
with which to control or reduce inputs of contaminants to the
Great Lakes basin, and are discussed below.
-------
31
fABLi III-l
Environmental Legislation affecting Great Lakes ecosysten quality.
BTNATIQNAL
LEGISLATION
Great Lakes Water
Quality Agreement (GLWQA J
Ontario-Michigan Memorandum
of Understanding an
Notification
Ontario-Michigan Declaration on
Partnership and Memorandum on
Cooperation
MEDIA 01 ACTIVITY
A; B
2
*
2
2
2
C
2
2
D
2
1
E
2
2
p
2
G
2
2
H
1
2
I
2
2
$
J
2
1
K
*>
i
i
L
2
•
M
2
1
EEI TO., CODES;.
A; Anbient Surface Water and Ground Water Quality and Management
B: Sediment Quality and Management
C; Biota Quality and Habitat Management
D; Industrial Point Source Discharge Control
I: Municipal Point Source Discharge ControL
F: Solid and Hazardous Waste Management
G: Pesticide Manufacture and Management
H: Urban Runoff and Combined Sewer Overflow Management
I: Air Point Source Discharge and Ambient Air Quality Control
J: Agricultural Land Management
K; Spills and Shipping Activities
L: Drinking Water Quality Control and Management
M; Fish Consumption Guidelines or Advisories
1; Legislation is responsible for legally enforceable standards
and/or has direct authority over the media or activity.
2i Legislation provides non-enforceable guidance or authority over
media or activity,
3: Legislation is not directly applicable to the media or activity,
but media/activity may be impacted by execution of its legislative
mandate,
-------
32
TABLE TIT-1. (cont'd 2\
CANADA
LEGISLATIOM
Fisheries Act
Canada Water Act
Canadian Environmental
Protection Act (CEPA)
Food and Drug Act
Canada Shipping Act
Transportation of Dangerous
Goods Act (TDGA)
Pest Control Products Act
(PCPAi
Canadian Clean Air Act
Environmental Contaminants Act
MEDIA OR ACTIVITY ADDRESSED
A
1
n
3
3
3
3
2
3
3
*l
C
1
3
3
3
3
D
1
1
E
2
1
F
3
1
1
G
1
1
H
2
I
1
1
J
3
K
•»
1
I
L
M
3
1
.^ _ _ .,
v /IN I M ft J. U
LEGISLATION
Ontario Water Resources
Act CQWRA)
Ontario Environmental
Protection Act (EPA!
Dangerous Goods Act
Drainage Act
Pesticides Act
MEDIA OR ACTIVITY ADDRESSED
A
P---I
'I
3
B
.--•i
3
2
C
.— — .
1
3
D
(•--•<
1
1
E
k-^H
l
1
F
».— - .
1
i
G
k H
1
g
!•- — •*
2
2
!
k — — H
i
J
2
3
1
K
i
i
2
L
1
H
-------
TABLE III-l. (cont'd 3)
33
UNITED Sf ATIS
LEGISLATION
Clean Water Act (CWA)
Safe Drinking Water Act ( SDWA 1
Food, Drug and Cosmetic Act
Clean Air Act ( CAA )
Comprehensive Environmental
Response, Compensation and
Liability Act JCERCLAJ
Solid Waste Disposal Act ( SWDA )
Toxic Substances Control
Act (TSCA)
Federal Insecticide, Fungicide
and Rodent icide Act (FIFRA)
Agricultural, Rural Development
and Related Agencies
Appropriations Act
Soil Conservation and Domestic
Allotment Act
Endangered Species Act
National Environmental Policy
Act (NEPA)*
MEDIA OR ACTIVITY ADDRESSED
A
1
1
1
"%
"3
*?
B( C
1
3
2
1
3
I
2
D
i
2
E
1
2
F
3
1
3
1
1
1
3
2
O
3
1
1
1
2
H
2
2
I
1
*y
£*
J
3
2
2
2
K
i
i
i
1
2
&
L
1
2
£>
M
1
2 '
*• i
NEPA is discussed in Appendix 3.
-------
TABLE ITI-1. (cont'd 4)
34
t
MICHIGAN
LEGISLATION
Water Resources Commission Act
(Act 245)
Safe Drinking Water Act
(Act 399!
Michigan Air Pollution Act
Watercraft Pollution Control Act
(Act 167!
Michigan Hazardous Waste
Management Act lAct 641
Michigan Liquid Industrial
Waste Disposal Act (Act 136)
Michigan Solid Waste Management
Act ( \ct 641 )
Michigan Environmental Response
Act (Act 307!
Inland Lakes and Streams Act
(Act 3461
Great Lakes Submerged Lands
Act (Act 247)
Michigan Resource Recovery Act
{Act 366)
Michigan Underground Storage
Tank Act (Act 423)
Michigan Wetlands Protection Act
Michigan Shorelines Protection
and Management Act
Michigan Motor Vehicle Emissions
Inspection Act (Act 83)
Michigan Oil & Gas Act (Act 611
Michigan Act 98
MEDIA OR ACTIVITY ADDRESSED
A
1
1
rl
*J
-I
1
1
3
B
3
1
Z
1
3
C
1
j*
1
"•t
D
1
E
1
1
P
1
•j
1
1
1
a
i
i
G
1
i
H
1
I! J
i
1
1
K
1
1
1
1
\
1
L
^
M
-------
35
B. ENVIRONMENTAL MEDIA STANDARDS, CRITERIA, OBJECTIVES AND
GUIDELINES
Media quality is often evaluated by comparing media contaminant
concentrations with numerical concentration limits, set by regu-
lation or agreement. Point source discharges are often con-
trolled by the imposition of contaminant concentration or loading
limits on effluent or stack air emissions. Various regulations
and agreements have developed "standards", "criteria", "objec-
tives" or "guidelines" to specify these concentration or loading
limits. In general, standards, and in some cases criteria, are
enforceable by law. These limits are usually based on regulatory
agency policies (e.g., state water quality standards), but may be
derived from scientific principles or studies (e.g., concentra-
tion and loading limits achieved by the use of best available
technology).
Objectives, guidelines and, in most cases, criteria are suggested
limits established by regulatory agencies, such as the United
States Environmental Protection Agency (U.S.EPA), Michigan De-
partment of Natural Resources (MDNR) or Ontario Ministry of the
Environment (OMOE), as well as by other non-regulatory agencies,
such as the International Joint Commission (IJC). These limits
are often based upon known or suspected impacts on human, animal
or aquatic life, and may be used to establish legally enforceable
limits as agency standards, or by incorporation into specific
agency documents, such as Certificates of Approval.
1. Water Quality Regulations and Guidelines
Numerical ambient water quality limits have been established by
federal, state and provincial statutes, as well as by binational
agreement. Parameter-specific ambient water quality standards,
criteria or objectives applicable to the UGLCC Study parameters
of concern are summarized in Table III-2; a comprehensive list of
ambient water quality limits is contained in the Regulatory Task
Force Report (I). These limits establish maximum concentrations
allowable in surface waters for the protection of human health,
animal and aquatic life and recreational use. These limits are
continually being reviewed and updated by state, provincial and
federal agencies. Regulatory agencies may adopt objectives set
by other regulatory or nonregulatory agencies on an interim basis
for parameters for which agency objectives have not been es-
tablished.
GLWQA specific objectives are nonenforceable goals for water
bodies within the Great Lakes Basin, in both the US and Canada.
Ontario Provincial Water Quality Objectives (PWQO), developed
under the authority of the Ontario Water Resources Act, and
U.S.EPA Ambient Water Quality Criteria (AWQC), developed under
the authority of the Clean Water Act, are similar in that they
-------
TABLE III-2
Ambient water quality criteria, guidelines, or objectives for parameters of concern in the UQLCC (ug/Ll.
PARAMETER
AM MONT A
KABMFDM
CHUWAMINES
CHLORIDES
CHI.OHINK
GREAT LAKES
WATER QUALITY
AGREEMENT
SPECIFIC
OUJKCTIVE
0.02
0.2
-
_
_
ONTARIO
WATER
QUALITY
OBJECTIVE
< PWQO )
O.02
0.2
-
_
0.002
U.ij . EPA
ACUTE AMBIENT
WATER QUALITY
CKfTKKIA
( AWQC 1
U.S. EPA
CHRONIC AMBIENT
WATEK QUALITY
CHITKHIA
1 AWtJC 1
U.S. EPA AWQC
HUMAN!
HEALTH
CRITERIA
(Water (,
Fish)1
U.S. EPA AWQC
HUMAN
HEALTH
CRITERIA
(Fiah only)«
pH/terop dependent - -
3 . 9 +
-
-
0.019
1 .1 +
-
-
0.011
10
-
-
-
—
-
-
-
cHi.oHi MATED PHENOLS- - - - -
CHROMIUM ( TOTAL 1
CHROMIUM (HEXAl
riWOMTHN (THI \
COBALT
COPPER
CYANIDE
HOB
IRON
Lfc'AD
MERCURY
NU'KEL
01 L/URCASE
CK'S
PHKNOI,
PHOSPHORUS < LAKES 1
PHOSPHORUS { RIVERS )
PHH
PAH
ZINC
50
~
-
-
5
-
-
3OO
25^
0,2
25
-
-
-
-
-
-
-
30
100
-
-
-
5
5
0.0065
300
25
0.2
25
-
-
-
0.02
0.03
0,001
-
30
-
16
1700+
-
18+
22
-
-
82 +
2.4
1400 +
-
-
10,200»
~
-
2.0
-
120 +
-
11
210 +
-
12 +
5.2
-
1000
a, 2 +
0.012
ISO*
-
-
2560*
-
-
0.014
-
1 10 +
-
SO
170mg/L
-
-
200
0.72ng/L
300
50
144n«/L
13.4
-
-
3500
-
-
0.079r>S/L
2.8ng/L
-
-
-
3,433mg/L
-
-
-
0.74ng/L
-
-
14finf /L
100
-
-
-
-
—
O.O79nf/L
31 , Ing/L
-
MICHIGAN
RULE ft?m
GUIDELINE
LEVELS2
20* coldwater J
0.4 +
-
-
6
_t
52+
6
-
-
21 +
5
0.0019
-
3+
0,6ng/Ls
78 +
-
-
230
-
-
O.OlZng/L
-
98
OJ
Ch
Criteria is hardness-dependent,. Value shown is based on a calcium carbonate hardness of 100 ntg/L,
V«lue shown is not criteria, but is lowest observed adverse effect level (LOAEL),
U.S.EPA Ambient Wst-er Quality Criteria for Human Health ia based on either consumption of 2 liters of water per day and
6.5 gm of fish per day, or consumption of 6. ft g of t'isih per day only. Guidance for carcinogens ia based on a 1E-06 risk
level, using the U.S.EPA-adopted risk extrapolation method,
Michigan Rule 57(21 Guidelines apply to contaminant concentrations at the edge of a defined mixing zone (values as of
Jnnuary 19HB, subject to chunge)
Not, applicable to Lakes Huron or Superior.
Owirleiines do exist for specific chlorinated phenols; see Appendix 3,
Guideline is for methyt mercury.
-------
37
are also goals for water quality. However, both PWQO and AWQC
are often the starting point for the development of point source
effluent limitations, and in the case of AWQC, become enforce-
able state water quality standards in states which have not pro-
mulgated more stringent state standards. U.S.EPA AWQC Human
Health Criteria are criteria for water quality, based on the
potential human health effects resulting from consumption of 2
liters of water and 6.5 g of fish per day, or consumption of 6.5
g fish per day only.
In Michigan, criteria for ambient water concentrations of toxic
contaminants are based on Rule 57(2), which is based on Part 4 of
the Michigan Water Resources Commission rules. Rule 57(2) was
developed to protect human health, fish and wildlife from ex-
posure to toxicants in surface water. It is a narrative rule for
the calculation of "edge-of-the-mixing-zone" concentrations for
toxics and is intended to be used in determining allowable levels
for point source discharges. However, MDNR uses Rule 57(2) al-
lowable levels as goals, particularly where ambient concentra-
tions are in excess of these values. Rule 57(2) values are water
body-specific, where appropriate, and are based on the most re-
strictive of human health, fish or wildlife criteria. Use of
Rule 57(2) values may not be appropriate if ambient water quality
exceeds Rule 57(2) allowable levels. In such cases, Rule 98,
Antidegradation, may be more appropriate.
Both federal governments and the province have also established
drinking water quality limits to protect human health. These
limits for the UGLCC Study parameters of concern are summarized
in Table III-3; a comprehensive list of drinking water limits is
provided in the Regulatory Task Force Report (1). These require-
ments are based on known or suspected human health effects, but
may include consideration of other factors such as treatment
techniques, cost and available laboratory analyses. Drinking
water limits may also be promulgated for nonhealth based para-
meters, such as odor and color, which are used to judge the ac-
ceptability of surface water supplies and treated water quality
for drinking water purposes. Drinking water quality limits may
be more or less stringent than ambient water quality objectives,
standards or criteria, depending on the parameter considered.
The U.S.EPA National Primary Drinking Water Regulations, devel-
oped under the authority of the Safe Drinking Water_ Act_, include
Maximum Contaminant Levels (MCLs) and Maximum Contaminant Level
Goals (MCLGs). MCLs are enforceable drinking water standards
with which drinking water supplies must comply. MCLs are based
on health effects, but also consider economic and technical fac-
tors. MCLGs are entirely health-based and are not enforceable.
A chemical's MCLG serves as a starting point for the.development
of its MCL, which is set as close to the MCLG as feasible. U.S.
EPA Secondary Drinking Water Regulations (also called MCLs) are
recommended limits for aesthetic qualities of drinking water,
-------
TABLE I11-3
Drinking irater standards, objectives and criteria for parameters of concern in the UQLCO (mg/L),
PARAMETER U.S. EPA
MAXIMUM
CONTAMINANT
LEVEL
f MCLI1 -a
AMMON1 A
CADMIUM 0.01
CHLORAMINES
CHLORIDE
CHLORINE
CHLORINATED PHENOLS
CHROMIUM 0.05
COBALT
COPPER
CYANIDE
HCB
IRON
LEAD 0.05
MERCURY 0.002
NICKEL
OIL/GREASE
DCS
PHENOLS
PHOSPHORUS
PCB t total!
PAH ItotalJ
ZINC
U.S. EPA U.S. EPA HEALTHAWELFAHE ONTARIO ONTARIO
MAXIMUM SECONDARY CANADA MAXIMUM MAXIMUM MAXIMUM
CONTAMINANT DRINKING WATER ACCEPTABLE ACCEPTABLE DESIRABLE
LEVEL GOAL REQUIREMENT CONCENTRATION CONCENTRATION CONCENTRATION
(MCLO»».a IMCLI* (MAC)2 (MAC>2 (MDC)*
0,005 - 0.005 0.005
_ -
250 250 - 250
_ _ _ _
_ •
0.12 - 0,05 0.05
_ _ -
1.3 1.0 - 1.0 1.0
0.2 0.2
_ _ _
0.3 - 0.3 O.3
0.02 - 0.05 0.05
0,003 - 0,001 0.001
_ - -
_ _ -
_ _
- - - - 0,002
_ - _
- - - 0.003
_ _ _ _
5 - 5
CO
National Primary Drinking Water Regulations.
Enforceable drinking water requirement.
Nonent'orceable heaJ th-based drinking water guidance.
Nonenforceable guidance for aesthetics.
-------
39
such as color, taste and odor, and are not federally enforceable.
There are no state-developed drinking water standards, however,
Michigan uses the federal standards by reference in the state's
Drinking Water Act.
The Health and Welfare Canada Maximum Acceptable Concentration
(MAC) is the enforceable drinking water requirement in Canada.
Ontario has adopted most of these MACs for the provincial stan-
dards, which are developed under the authority of the Ontario
Water__Resources Act. The Ontario MACs are based on known or
suspected human health effects, and are enforceable standards for
drinking water supplies in Ontario. The Ontario Maximum Desira-
ble Concentration (MDC) is based on aesthetics, and is a nonen-
forceable goal.
Other statues which can impact on surface water quality include,
in Canada, the Fisheries Act and the Canadian Environmental Pro-
tection Act__ (CEPA) , and in Michigan, the Michigan Wetlands Pro-
tec tion Act_(Act_2Q3), the Inland Lakes and Streams Act (Act
346), the Michigan Shorelines Protection and Management Act (Act
245)_ and the Great Lakes Subm_erged,_Lands_ Act (Act 247) .
2. Sediment Quality Regulations or Guidelines
The GLWQA, in Annexes 7 and 14, addresses sediment quality from
the perspective of studying, evaluating and monitoring dredging
activities and in-place, contaminated sediments within the Great
Lakes, but has not derived specific objectives for contaminants
in sediments.
Guidelines for the disposal of dredged material, based on con-
taminant concentrations in sediments, have been established by
the OMOE 1978 revised Guidelines for Dredged Spoils for Open
Water Disposal and the U.S.EPA Guidelines for the Pollutional
Classification of Great Lakes Harbor Sediments. The OMOE allows
open water disposal of dredged materials that meet or are lower
than the established guidelines, providing existing water uses
are not affected. The U.S.EPA Region V Guidelines were developed
under pressure for the need for some guidance, but have not been
adequately related to the impact of sediments on lakes, and
should be considered interim guidelines until more scientifically
sound guidelines are developed. The U.S.EPA is in the process of
developing sediment criteria. Dredging guidelines are summarized
in Table 111-4. Table III-4 also shows the guidelines for eva-
luation of Great Lakes Dredging Projects, developed by the Dredg-
ing Subcommittee of the Great Lakes Water Quality Board. These
guidelines are average concentrations of surficial sediments in
Lakes Huron and Erie {guidelines for the other lakes have also
been developed). Sediment concentrations exceeding these levels
-------
TABLE II1-4
USKPA, OMOE and Great Lakes Water Quality Board sediment dredging guidelines I Big/kg |.
PARAMETER
Total Phosphorus
Total Kjeldahl Nitrogen
Ammonia
Volatile Solids
Chemical Oxygen Demand
Oi I ft Grease
Arsenic
Barium
Cadmium
Chromium
Cobalt
Copper
Cyani de
Iron
Lead
Manganese
Mercury
Nickel
PCB
S i 1 ver
Se leniura
Z i nc
ONTARIO HOE
GUlDELlNESl
1000
2000
100
60,000
50 , 000
1500
8
-
1
25
SO
25
0,1
10,000
50
_
0.3
25
0,08
0,5
-
100
U.S. EPA
GUIDELINES*
Nonpol luted
<420
<1000
<7S
< 50, 000
<40,000
1 {"Polluted"!
20-50
> 10 1 "Pol luted" )
-
-
90-200
U.S. EPA
GUIDELINES*
Heavily
Polluted
>650
>2000
>200
>80,000
>80,000
>2000
>8
>60
>6
>75
-
>50
>0.26
>25,000
>60
>500
>50
GLWQB
DREDGING
OUT RELINKS'
Lake Huron
5TO
-
-
«
-
-
1.1
-
1.4
32
-
32
_
-
49
_
0.22
39
0.009-0.033 0
_
-
>200
-
0.9
62
GLWQB
DREDGING
GUIDELINES*
Lake Erie
960
-
-
_
-
-
3.2
-
2.5
53
-
39
_
-
112
_
0.58
49
.074-0,252
-
0. 79
177
*»•
o
Ontario Ministry of the Environment Guide tines for Dredge Spoils for Open Wat.er Disposal
U.S. EPA Guidelines for the Pol Int. ions I Classification of (ireat. l.nkea Harbor Sediments
Guide lines for the Evaluation of fireat Lakes Dredging Projects, Dredging Subconni t.tee, Great Lakes Water
Quality Board, International Joint Commission,
-------
41
are considered degraded and should not be disposed in the open
lake. Since guidelines for contaminant concentrations in in-
place sediments have not been derived, these dredging guidelines
are often used in place of sediment criteria.
Contaminated sediments constitute a significant environmental
concern in the Great Lakes Basin, and these guidelines are under
review by most agencies. Special advisory groups, such as the
Polluted Sediment Subcommittee under the Canada-Ontario Agree-
ment, have been established to review sediment guidelines and
assessment criteria, to evaluate dredging activities and in-place
remedial options, and to provide expert advice on infilling prac-
tices.
Regulations which address dredging or remediation of contaminated
sediments are discussed in a later section.
3. Aquatic Biota Quality Regulations or Guidelines
Many of the ambient water quality limits and guidelines were
developed from an understanding of the effects of contaminants on
aquatic life. Therefore, such limits and guidelines directly
affect the health of aquatic biota. . There is considerable legis-
lation, not directly related to environmental quality, which
exists to protect terrestrial and aquatic species, such as the
U.S. Endangered Species Act of 1973, which identifies threatened
and endangered species and their habitats. A more complete dis-
cussion on such legislation is contained in the Regulatory Task
Force Report (1).
The quality of aquatic biota is also important from a human
health perspective, when biota are consumed as a food source.
Pish consumption advisories are developed by different regulatory
agencies to provide guidance to the public on the safety of con-
suming fish which are, or may be, contaminated. These advisories
are usually based on the concentration of contaminants contained
in the edible portion of fish, and restrict consumption to vary-
ing degrees when contaminant concentrations exceed these levels.
Different concentration limits have been established by the
GLWQA, the U.S. Food and Drug Administration (FDA), Ontario Mini-
stry of the Environment, Health and Welfare Canada, and the
Michigan Department of Public Health. Table III-5 summarizes
these limits. Some of the sampling and analytical techniques
associated, with determining contaminant concentrations may vary
from jurisdiction to jurisdiction. For example, Ontario employs
a skinless fillet as an edible portion, whereas Michigan employs
a skin-on fillet for some fish and a skin-off fillet for others.
-------
TABLE III-5
Fish consumption guidelines, objectives, tolerances and action levels applicable to the UQLOG Iug/gI.
PARAMETER
GREAT LAKES
WATKR QUALITY
ABHKKMENT
SPECIFIC
OBJECTIVE1
U.S.FDA
ACTION LEVEL!A I
OR
TOLERANCEft)*
HEALTH i,
WELFARE
CANADA
FISH
CONSUMPTION
ONTARIO
FISH
CONSUMPTION
GUIDELINES4
( Restricted
ONTARIO
FISH
CONSUMPTION
GUIDELINES*
{No
ADVISORIES* Consumption! Consumption)
MICHIQAM
PUBLIC HEALTH
FISH CONSUMPTION
AIWISORY
TRIGGER
LEVELS*
0.3
A Idr i n
Oh 1ordane -
f'hlordecane
2 ,4D
DDT 1 .0
Dieldrin 0.3
Diquat
Kndrin 0,3
FIur idone —
GIyphosate -
Heptachlor * H.Epoxide I). 3
L e « d ~
I in.Jane 0.3
Mercury 0.5
Mi rex
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43
FDA action levels and tolerances are contaminant limits in edible
fish flesh developed by either the PDA or the U.S.EPA, and apply
only to fish in interstate commerce. The authority for the de-
velopment of action levels and tolerances comes from the Federal
Food, Drug .and Cosmetic_Act. FDA action levels and tolerances
differ in that tolerances apply to registered chemicals in cur-
rent use and action levels to chemicals for which legal use has
been prohibited. FDA action levels and tolerances are not in-
tended to be used to regulate sport-caught fish. Michigan Trig-
ger Levels, which do apply to sport-caught fish, are, in many
cases, identical to FDA action levels and tolerances; however,
the Trigger Levels were derived independently.
Health and Welfare Canada, under the Fooa_and Drug,.Act, has es-
tablished some federal fish consumption advisories, with res-
tricted consumption being advised for fish exceeding the guide-
lines. The Ontario Fish Consumption Guidelines, developed by
OMOE and Ontario Ministry of Natural Resources, based on guidance
from the federal Food and Drug Act, have adopted many of the
federal consumption guidelines, and provide restricted consump-
tion guidelines below which consumption may be unrestricted and
above which restricted consumption is advised {or no consumption,
in the cases of women of child-bearing age and children under 15
years of age). Mercury also has a No Consumption guideline,
above which no consumption is advised for all populations.
Both Ontario and Michigan publish readily available fish consump-
tion advisory guides identifying consumption advisories in effect
for various fish species, sizes and water bodies. The GLWQA has
established specific objectives for several contaminants in the
edible portion of fish for the protection of human health, in
addition to contaminants in whole fish for the protection of
fish-consuming wildlife and aquatic birds.
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44
C. POINT SOURCE CONTAMINANT CONTROLS
Much of the focus of federal, provincial and state legislation
and the GLWQA is directed towards the control and reduction of
excessive contaminant input from point source dischargers. The
regulatory basis for these control programs is discussed below.
1. Industrial Point Sources
Surface and Groundwater
Article VI of the GLWQA requires the governments of Canada and
the U.S. to develop and implement programs to abate, control and
prevent pollution resulting from industrial point sources by
establishing effluent limits and effective enforcement programs.
Environment Canada, through industry-specific regulations under
the Fisheries .Act-, regulates the discharge of conventional con-
taminants and acute toxicity (defined by bioassays) from petro-
leum refineries, pulp and paper mills and other specific in-
dustrial sectors. These federal regulations and guidelines for
effluent quality are based on the application of best practicable
technology. Regulations and guidelines have not been promulgated
for some major industrial sectors, such as organic chemical, iron
and steel industries.
Ontario establishes and enforces effluent requirements at least
as stringent as that established by the federal government. In
addition, provincial objectives are implemented under the En^
vironmental Protection Act (EPA) and the Ontario_Water Resources
Act (OWRA), using voluntary measures, formal programs, Control
Orders, Directions and Requirements, Certificates of Approval and
prosecution. Industrial effluent objectives for conventional
parameters, metals, phenols and some toxic substances are es-
tablished under OWRA, which sets out desirable effluent discharge
characteristics necessary to protect receiving water quality.
These industrial effluent objectives are shown in Table III-6,
Enforceable effluent limits, such as Control Orders, may require
the attainment of the industrial effluent objectives and. may also
require compliance with additional parameters.
A recent initiative is being taken in Ontario to reduce toxic
substance discharges to surface waters; the Municipal and In-
dustrial Strategy for Abatement (MISA). MISA will require, by
regulation, each of nine industrial sectors and the municipal
sector to implement a comprehensive monitoring program to charac-
terize its effluent and then to implement the best available
technology economically achievable (BATEA) to reduce the dis-
charge of toxic contaminants. If, after installation of BATEA,
any environmental impacts resulting from a facility's discharge
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45
TAIL! III-6
Ontario industrial effluent objectives1•
PARAMIT11
ONTARIO
INDUSTRIAL EFFLUENT
OBJ1CTIVI
Ammonia-Nitrogen mg/L
BGBs ing/L2
Cadmium mg/L
Chromium mg/L
Copper mg/L
Fecal Coliforms MF/100mL
Lead rag/L
Mercury ng/L
Nickel mg/L
Oil and Qrease
P«
Phenols mg/L
Phosphorus mg/L
Suspended Solids mg/L
Tin ng/L
Totai Residual Chlorine mg/L
2 i ne mg / L
10
15
0.001
1,0
1,0
1.0
0.001
1.0
IS
5.5-9.5
0.01
15
1.0
1.0
Established under Ontario Water Resources Act.
5-day biological oxygen demand
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46
persist, the facility will be required to implement additional
effluent treatment. Implementation of MISA monitoring and ef-
fluent limit regulations will occur over the next two years.
The U.S. Clean Water Act authorizes the U.S.EPA to delegate, to
state regulatory agencies, regulatory authority over the dis-
charge of contaminants from municipal and industrial point sour-
ces. Michigan was delegated this authority in 1973, and directs
the National Pollutant Discharge Elimination System (NPDES) per-
mit program for point sources in the state. Under this program,
discharge permits are issued to facilities, and stipulate the
extent of allowable contaminant discharge. Effluent limits are
often based on best available technology (BAT) for unconventional
anc toxic pollutants and on best conventional technology (BCT)
for conventional pollutants, and may be expressed as a concentra-
tion, a mass loading limit or both. Often, effluent limitations
are placed on only a few parameters, usually conventional pol-
lutants. Industries may discharge to the sewer system of a muni-
cipal waste treatment facility, rather than discharging directly
to a surface water body. In such cases, the municipal facility
may issue an Industrial Pretreatment Program (IPP) permit to the
industry, specifying acceptable industrial effluent quality.
Alternately, states may issue the IPP permit to the industrial
facility.
In both Ontario and Michigan, site-specific effluent requirements
are frequently based on protection of the receiving water. In
Ontario, this is done by way of requirements and Direction, or
Certificates of Approval, both under the Ontario Water Resources
Act, or by Orders (e.g., Control or Directors Orders) under the
Environmental Protection Act. In Michigan, this is accomplished
under the NPDES permit program.
Air
Annex 15 of the GLWQA instructs the two governments to conduct
research, surveillance and monitoring, and to implement control
measures to reduce atmospheric deposition of toxic substances to
the Great Lakes Basin. The Agreement calls for the development
of control measures and technologies to reduce the sources of
atmospheric emissions.
Under Canada's Environmental Protection Act (CEPA), industrial
emission standards, regulations and guidelines have been es-
tablished for several substances. The provincial Air Pollution
Control (General) Regulations prescribe the maximum concentration
of a contaminant at a point of impingement.
In the U.S., the Clean Air Act (CAA) gives authority to the U.S.
EPA to develop programs affecting air quality. The U.S.EPA has
developed ambient air standards and emission standards for speci-
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47
fic pollutants. National Ambient Air Quality Standards (NAAQS)
have been developed for several chemicals. Control of these and
other "hazardous" air pollutants (as defined) is obtained by
regulating their emission from point sources. The basic point
source emission standard developed under the CAA is the National
Emission Standard for Hazardous Air Pollutants (NESHAP). NESHAPs
are applied to different industrial categories. For certain
classes of new industrial sources, New source Performance Stan-
dards (NSPS), based on best demonstrated technology, also apply.
In addition, other emission permits may be needed.
Under the CAA, primary control over point source air emissions
and other air programs occurs at the state level through state
air programs. In 1973, Michigan submitted, and subsequently
received approval for, their State Implementation Plan (SIP).
Through the SIP, Michigan's Air Quality Division has delegation
of authority from the U.S.EPA for compliance and enforcement of
NESHAPs. Inspection of NESHAP sources are required to be rou-
tinely performed.
2. Municipal Point Sources
Article VI and Annex 3 of the GLWQA support the adoption of con-
trols to reduce pollution resulting from municipal waste treat-
ment facilities. Goals include the development of programs and
measures to ensure proper facility construction and operation,
development of pretreatment requirements, establishment of effec-
tive enforcement programs, and the reduction of most effluent
phosphorus concentrations to 1 mg/L or below.
In Canada, control over municipal waste treatment facilities lies
primarily with the provincial government, under the authority of
the Ontariq_Water Resources Act and the Ontario Environmental
Protection Act. The federal government does, however, restrict
the phosphorus content in detergents to 0.5% (as phosphorus pen-
toxide on a weight/weight basis) as a method of reducing phospho-
rus discharges from municipal facilities, and has recommended
municipal effluent objectives. The provincial government es-
tablishes minimum treatment requirements for municipal facili-
ties, which limit concentrations of total phosphorus in effluent
to 1 mg/L, as well as specifying minimum removal rates or maximum
concentrations for biological oxygen demand (6005) and total
suspended solids (TSS), based on the level of treatment performed
at the facility (Table III-7). Municipal waste treatment facili-
ties will also be regulated under the MISA program..
In the U.S., the NPDES program of the Clean Water Act regulates
municipal facilities, and permits are issued to individual
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48
TABLE It 1-7
Revised Ontario effluent guidelines for wastewater treatment facilities (OMOE
policy 08-01 I.
TREATMENT
BIOLOGICAL
OXYGEN
DEMAND
SUSPENDED
SOLIDS
TOTAL
PHOSPHORUS
Img/L)
PRIMARY
without P removal
with P removal
30% removal
50% removal
50% removal
70% removal
1.0
SECONDARY
withoyt P removal 25 mg/L
with P removal 25 mg/L
CONTINUOUS DISCHARGE LAGOON
without P removal 30 mg/L
with P removal 30 mg/L
SEASONAL DISCHARGE LAGOON
with P removal, 30 rtg/L
continuous P removal 30 mg/L
batch P removal 25 mg/L
25 mg/L
25 mg/L
40 mg/L
40 mg/L
40 mg/L
40 mg/L
25 mg/L
1.0
1.0
1.0
1 .0
Note: "Where warranted, a higher degree of treatment shall be required to
nest the site-specific effluent requiremetits developed for each
particular receiving water."
Table Adapted from "Report to the Great Lakes Water Quality Board, Guidance on
Characterization of Toxic Substances Problems in Areas of Concern in the Great
Lakes Basin.", March, 1987.
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49
facilities specifying concentration and/or mass loading discharge
limits on specific parameters, usually conventional pollutants.
As mentioned, Michigan has obtained primacy for control of this
program, and NPDES permits are issued by the MDNR. Among other
previously mentioned legislation, Michigan's Act 98, as amended,
provides for the classification, specification, certification and
supervision of municipal waste treatment systems by the state
health commissioner, as well as providing penalties for viola-
tions .
Municipal facilities which receive waste water from industrial
facilities usually operate an industrial pretreatment program
{JPP}. In this program, permits are issued by either the munici-
pal waste treatment facility or the state to industries which
discharge to sewer systems, and specify pretreatment requirements
for the effluent. The pretreatment requirements are either local
limits developed for the protection of the waste treatment faci-
lity, or federally promulgated categorical pretreatment require-
ments, whichever are more stringent.
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50
D, NONPOINT CONTAMINANT CONTROL
1. Agricultural Runoff
The GLWQA identifies agriculture as an activity which requires
management programs to reduce contaminant and nutrient loading
and soil erosion to adjacent surface waters. The Agreement sup-
ports the implementation of programs which are consonant with
these goals, including improved fertilization and manure manage-
ment practices, conservation tillage practices and others.
Agriculture Canada and the Ontario Ministry of Agriculture and
Food (OMAF) have instituted programs to educate farmers on new
technologies, crop rotation and soil conservation practices
through the Soil and Water Environmental Enhancement Program
(SWEEP). OMAF provides soil testing services for farmers to
determine appropriate application rates for fertilizers and lime.
The Agricultural Code of Practices for Ontario (1973} promotes
proper application of livestock manure to cropland in order to
reduce nutrient loads to ground- or surface water. The Ontario
Ministry of the Environment has outlined restrictions or. applica-
tion rates and times and contaminant concentrations in sewage
sludges applied to agricultural land, as shown in Table III-8.
In the U.S., control of pollution from agricultural activities is
also based on a management approach. The U.S. Department of
Agriculture (USDA) can reduce funding benefits to farmers who
produce agricultural commodities on highly erodiJole lands or
wetlands as an indirect incentive to reduce erosion and preserve
wetlands. The USDA and the U.S. EPA also use programs developed
under the Agricultural, Rural Development ..and Related Agenci_e_g
Appropriations,,Act and the Soil Conservation and Allotment^ Act to
protect against soil erosion, and to prevent and/or abate water
pollution for agricultural sources. Michigan's Nonpoint Sources
Management Program, the Michigan Phosphorus Reduction Strategy
and the Michigan Energy Conservation Program are all intended to
provide management, technical, or financial support to minimize
erosion and the loss of fertilizers, pesticides and manure to
rural surface waters. Michigan's Guidance for Land Application
of Wastewater Sludge is shown in Table ITT-8.
2. Pesticides
Article VI of the GLWQA calls for measures to inventory, control
and research the impacts of pesticides used in the Great Lakes
Basin, and to ensure they are used in a correct and legal manner.
The GLWQA has also developed specific objectives for several
pesticides in both water and biota.
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TABLE II1-8
Guidelines and criteria for agricultural application of wastewater sludge.
PARAMETER ONTARIO MAXIMUM MICHIGAN GUIDELINES
PERMISSIBLE CONCENTRATION CLASS 1*
(mg/kg solids!1 Sing/kg)
Arseni c
Cadmium
Chromium
Cobalt
Copper
Lead
Mercury
Mo 1 ybdenun
Nickel
PCB
Selenium
Zinc
170
34
2800
340
1700
1100
11
94
420
34
4200
100
6
50
250
250
2
10
25
1
10
750
FOR APPLICATION
CLASS 23
(rag/kg)
OP WASTEWATER SLUDGE
CLASS 3*
ting/kg |
100-2000
5-125
50-5000
250-2000
250-2000
2-10
10-50
25-1000
1-10
10-80
750-5000
200O
125
5000
2000
2000
10
50
1000
NA
80
5000
For all aerobic sewage sludge and dried/dewatered anaerobic sewage sludge; other regulations apply for
liquid anaerobic sludge.
May be applied to ull manner of crops with little restrictions on use.
May be applied to crops in accordance with computed site limitations on annual and lifetime metal a
accumu lation.
May onLy be applied to crop lands under carefully controlled rates which are consistent with computed
site assimilation rates; sludges containing greater than 10 ppm PCB may not be land-applied.
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52
Canada's federal Pest Control Products,.Act, and the Ontario Pes-
ticides Act regulate the manufacture, registration and use of
pesticides in. Canada. Nonregulatory programs at the federal
level include the Integrated Pest Management Program, currently
being developed by Agriculture Canada, Its aim is to develop a
management scheme to reduce reliance on chemical pest control,
The Provincial Pegticides Act prohibits the harmful discharge of
pesticides and requires the licensing of commercial pesticide
applicators. The Ontario Ministry of Agriculture and Food (OMAF)
is also involved in the Integrated Pest Management Program.
In the U.S., the Federal Insecticide, Fungicide and Rodenticide
Act., IFIFRA) regulations address the manufacture, distribution,
storage, disposal and use of approximately 50,000 pesticide pro-
ducts and devices. FIFRA also provides standards for the cer-
tification of commercial and private applicators of restricted
use pesticides. Regulations under the Federal, Food, Drug and
Cosmetic Act establish allowable limits (residues) of pesticides
in food or feed crops prior to pesticide registration. The Re-
source Conservation and Recovery Act (RCRAj regulates the treat-
ment, storage and disposal of some pesticides. Many aspects of
Michigan's Nonpoint Source Management Program address the use of
pesticides used on agricultural land.
3. Shipping
Article VI and Annexes 5 and 6 of the GLWQA contain provisions
for the control of contaminants from shipping activities. Of
primary concern are discharges of oily waste water, bilge water
and untreated sewage, along with garbage and other hazardous
substances in washings or spills.
The Canada Shipping Act (CSA) has spawned regulations directed at
shipping that control discharges of oil and vessel wastes. The
CSA .requires ships to either treat their sewage before discharge
or install holding tanks. The Transportation of Dangerous Goods
Act (TOGA) prescribes safety requirements and standards for all
means of transportation across Canada, including shipping. On-
tario's Environmental JProtectLio,n Act requires pleasure craft to
be fitted with sewage holding tanks to contain waste water, which
are emptied in a controlled manner at marinas.
In the U.S., the National Oil and Hazardous Substances Pollution
Contingency Plan (NCP) under the Comprehensive Environmental
Response.Compensation and Liability Act (CERCLA) is, in part,
concerned with the discharge of oil to navigable waters of the
U.S. Michigan's Watercraft Control Act of 1970 prohibits the
activities of littering or polluting the state's waters with
sewage, oil or other liquid or solid material. Violators are
fined and are responsible for cleanup of wastes.
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53
4, Spills
Annex 9 of the GLWQA calls for a coordinated and integrated res-
ponse to pollution incidents in the Great Lakes by responsible
federal, state, provincial and local agencies through a Joint
Contingency Plan. The objectives of this plan include develop-
ment of preparedness measures, adequate cleanup response and
extent, and other factors, Ontario and Michigan entered into
such an agreement in April 1988, with the signing of the Ontario-
Michigan Letter of Intent on Notification and Consultation Proce-
dures for Unanticipated or Accidental Discharges of Pollutants
into Shared Waters of the Great Lakes and Interconnecting Chan-
nels,
In Canada, control over spills lies primarily with the provincial
government. The "Spills Bill", part IX of Ontario's Environmen-
tal Protection Act, deals with spills of pollutants into the
natural environment, and establishes notification requirements,
response procedures and compensation mechanisms, Ontario's
Spills Action Centre (SACJ coordinates the Ministry's response
network and other emergency respenders,
In the U.S., regulations under CERCLA identify "hazardous sub-
stances", reportable quantities of these substances and notifica-
tion requirements in the event of a release, . CERCLA created the
NCP, which is concerned with oil and hazardous material spills in
navigable waters and the environment. The Clean Water Act also
prohibits discharge of oil in harmful quantities, and requires
owners and/or operators of facilities which present a threat of
an oil discharge to surface water to prepare a Spill Prevention
Control and Countemeasure (SPCC) plan. The Solid Waste Disposal
Act (a.k.a, RCRA) requires transporters of hazardous substances
to take appropriate action in the event of a spill, and to notify
the National Response Center, The Emergency_Planning and Right-
To-Know Act requires participation by certain facilities in emer-
gency planning procedures for spills. The Toxic Substances Con-
trol Act (TSCA) contains the PCB spill cleanup policy.
Michigan's Water Resources Commission Act rules (Part 5, Rules
151-169) regulate oil loading and unloading and storage, and
specifies emergency response procedures for spills, Michigan Act
§]., referred to as the Oil and Gas Act, requires operation of
production and. disposal wells in the state in such a -manner as to
prevent the escape of oil, gas, saltwater, brine or oil field
wastes which would pollute, damage or destroy freshwater resour-
ces. Michigan DNR's Pollutional Emergency Alert System (PEAS)
investigates and responds to emergency spill occurrences and
coordinates with other concerned agencies.
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54
5. Urban Runoff and Combined. Sewer Overflows
Annex 13 of the GLWQA calls for the development of programs to
abate, control and prevent contaminants from being discharged
from nonpoint sources, including runoff from urban land. Article
¥1 calls for, in part, control of contaminants from combined
sewer systems.
In Canada, Guidance for Urban Drainage Design, Erosion and Sedi-
ment Control for Urban Construction Sites is developed under the
provincial Drainage Act, while stormwater is informally con-
trolled through reviews and comments on official plans and ap-
plications for development of subdivisions. No control strate-
gies exist for treatment of combined sewer overflows (CSOs);
however, the province has worked with municipalities to segregate
sanitary and storm sewers. The MISA program will consider abate-
ment requirements for CSOs. Guidelines for Snow Disposal and
Deicing Operations in Ontario minimize impacts on surface and
groundwaters,
The U.S.EPA Region ¥ {ChicagoJ developed a two-phased manage-
ment program of CSOs under the authority of the CWA through the
municipal waste treatment facility NPBES permit process. The
purpose of the Region ¥ NPDES Permit Strategy for Combined Sewer
Systems is to incorporate planning and management procedures into
combined sewer system operations to result in a more effective
management of the system. The program initially institutes man-
agement controls on the existing combined sewer system, in an
attempt to reduce receiving water impacts. If satisfactory re-
sults are not achieved, rehabilitation of the sewer system, or
other more extensive steps, may be required. In addition, Mi-
chigan has drafted a CSO policy which may contain limitations
much like any other point source discharge.
6, Atmospheric Deposition
Annex 15 of the GLWQA calls for research, surveillance and moni-
toring, and implementation of control measures to reduce at-
mospheric deposition o£ toxic substances to the Great Lakes
Basin, Annex 15 also requires that measures to control emission
sources which significantly contribute to pollution of the Great
LaK.es be studied, developed and implemented. The Memorandum of
Understanding between Ontario and Michigan, recently signed,
contains the Ontario-Michigan Joint Notification Plan for Unan-
ticipated or Accidental Discharges of Airborne Pollutants, out-
lining steps and actions to be taken by both governments in the
event of such an incident,
In Canada, National Ambient Air Quality Objectives have been
established under the Canadian Clean Air Act as a guide in devel-
oping programs to reduce the damaging effects of air pollution.
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55
These national objectives assist in establishing priorities for
reducing contaminant levels and the extent of pollution control
needed, provide a uniform yardstick for assessing air quality in
all parts of Canada, and indicate the need for and extent of
monitoring programs. CSPA, in addition to regulating point sour-
ces of air emissions, also has the authority to regulate fuel and
fuel additives, which may impact on atmospheric deposition of
combustion products and lead. Provincial Ambient Air Quality
Criteria are developed under the Ontario Environmental Protection
Act. QMOE, often in conjunction with other groups and agencies,
prepares a yearly summary of transboundary air contaminant move-
ment and conducts studies on the long range transportation and
deposition of contaminants to the Great Lakes.
In the U.S., the clean Air Act (CAA) gives authority to the
U.S.EPA to approve programs affecting air quality, implemented at
the state level. National Ambient Air Quality Standards (NAAQS)
have been developed by the U.S.EPA, and consist of both primary
and secondary standards, to protect public health and welfare,
respectively. A few atmospheric nonpoint source programs have
implemented at the federal level. The CAA provides the
U.S.EPA with authority to control and/or prohibit fuels and fuel
additives used in motor vehicles which have been determined to
endanger public health. To this end, the U.S.EPA requires regis-
tration of fuel and fuel additives, and prohibits the production
or importation of gasoline containing an average lead concentra-
tion of 0.1 g lead/gallon fuel or greater. The CAA regulations
stipulate emission requirements for new motor vehicles as a
method of controlling air quality. Michigan manages its own air
program, adopting and adhering to the federal NAAQS. Ambient air
monitoring is conducted in Michigan in some industrial areas
known or suspected of having significant releases of toxic air
pollutants. An Air Quality Index is reported to the public
daily.
7. In-place Pollutants
Article ¥1 and Annex 7 of the GLWQA provide for the development
of a Subcommittee on Dredging to review the existing practices in
the U.S. and Canada relating to dredging activities, and to
develop guidelines and criteria for dredging activities in boun-
dary waters of the Great Lakes. Annex 14 of the GLWQA calls for
parties to develop a standard approach and agreed upon procedures
for the management of contaminated sediments.
In Canada, federal authority over contaminated sediments in the
Great Lakes is limited; the province of Ontario is primarily
responsible. However, under the Canada-Ontario Agreement, a
Polluted Sediment Subcommittee has been formed, charged with
developing a standardized assessment procedure for assessing
contaminated sediments and their remedial options. Under the
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56
Environmental Protection Act., the Ontario Minister of Environment
can order the removal of contaminated sediments.
In the U.S., the Clean Water Act authorizes funds to identify
areas containing contaminated sediments and to develop plans for
sediment removal and disposal from critical ports and harbors.
Section 404(b) of the CVA empowers the U.S. Army Corps of En-
gineers to issue permits to govern dredging and fill operations
for the purposes of navigation. Control over the discharge of
dredged and fill material at specified disposal sites is main-
tained through a permitting process. In some instances, con-
taminated sediments may be regulated under RCRA, such as in in-
stances when dredged sediments exhibit one or more of the hazar-
dous waste characteristics defined under RCRA, or if a release
occurs at a Treatment, Storage and Disposal facility, as defined
under RCRA. All dredging projects in Michigan are subject to
review and certification under the CWA. Dredging permits may
also be required under Michigan's Inland Lakes and,Stream Acts
(Act 346)_ and the Gre_at Lakes Submerged Lands Act (Act 247).
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57
E. SOLID, LIQUID AND HAZARDOUS WASTE CONTROLS
The GLWQA, in Annex 13, calls for the development of programs to
abate and reduce pollution resulting from land use activities,
including waste disposal sites. At the present time, no specific
guidelines are developed for siting or management of solid or
hazardous waste sites.
Regulations concerning the use, handling, storage and disposal of
hazardous wastes in Canada are primarily developed at the provin-
cial, rather than federal, level. Some federal statutes do,
however, offer some control. The federal Environmental Con-
taminants Act restricts the use, handling and/or disposal of
selected hazardous substances: PCB and PCB products, mirex, poly-
chlorinated terphenyls and polybrominated biphenyls. The recent
passed Canadian Environmental Protection Act (CEPA) provides
control over the manufacture, transportation, use, disposal,
importation and exportation of chemicals and wastes where not
adequately controlled by regulation in other legislation. The
federal Transportation of Dangerous Goodjs Act prescribes safety
requirements, standards and safety marks on all means of trans-
port across Canada, including the transport of hazardous
material.
At the provincial level, solid and hazardous waste programs are
regulated under the Environmental Protection Act (EPA). The EPA
develops standards for siting, maintenance and operation of waste
sites, and operates a paperwork manifest system to monitor the
transport and handling of hazardous wastes. Under EPA, all waste
sites are required to have a Certificate of Approval-prior to
operation. In addition, Ontario regulations prohibit deep well
injection of any liquid industrial waste into the Detroit River
Group geological formation in Lambton County, and prohibits the
deep well injection of brines within 8 km of the St. Clair River,
In the U.S., the federal Solid Waste Disp_osal_Act_(SWDA) , as
amended (which includes the Resource Cons_ervat_ion__and Recovery
Act and the Hazardous and Solid Waste Amendments), develops regu-
lations to manage solid and hazardous wastes. Three distinct
programs have been developed: the Solid Waste Program, the Hazar-
dous waste Program and the Underground Storage Tank Program. The
Solid Waste Program defines both technical and management crite-
ria for the proper operation of a solid waste facility. The
Hazardous Waste Program defines certain wastes or characteristics
as "hazardous", describes the Uniform Hazardous Waste Manifest
System for the tracking of hazardous waste movement, and develops
requirements for generators, transporters and owner/operators of
Treatment, Storage and Disposal facilities. The Underground
Storage Tank program develops construction criteria, performance
standards and notification requirements for underground storage
tanks. Michigan has obtained primacy for most of these solid and
hazardous waste programs, with regulations being developed under
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58
Michigan Act 64 (Michigan Hazardous Waste Management Act), Act
136 (Michigan. Liquid Industrial Waste Disposal_AcT:)_, Act 641
(Michigan Solid Waste Management Act), Act 423 (Michigan Under-
ground_Storage Tank Act) and Act__3_66 (Michigan Resource Recovery
Act) . Michigan Act ..61, referred to as the Oil and Gas Act, which
generally addresses permitting, drilling, production and abandon-
ment of production and disposal wells, specifically requires
operation of the wells in such a manner as to prevent the escape
of oil, gas, saltwater, brine or oil field wastes which would be
damaging to fresh water resources.
The U.S. federal Comprehensive Environmental,.Response, Compensa-
tion and. Liability Act_jCERCLA), colloquially referred to as
"Superfund", was amended in 1986 by the Superfund Amendments and
Reauthorization .Act._(SAgA). (which contains the Emergency ^ Planning
andt,Community Right__To Know_Act of 1986 (Title III) and the Radon
Gas and Indoor Air Quality Research Act of 1986 (Title IV)}.
CERCLA identifies an extensive list of substances as "hazardous",
and authorizes the remediation of uncontrolled waste sites con-
taining hazardous materials, involving a stepwise evaluation of
the hazards present. CERCLA, sharing a dual authority with the
Clean Wate_r Act, is also concerned with uncontrolled releases of
oil and hazardous materials to navigable waters to the U.S. The
Michigan _Eny_ironmental_Response Act (Act 307) provides for the
prioritization of hazardous waste sites in the state, and recom-
state funds for remediation. Michigan may, through this
regulation, remediate sites not being addressed by the federal
Superfund program.
The U.S. Toxic _S_ub stances ..Control _Act (T5CA) provides the U.S. EPA
with broad authority over the manufacturing, importation and
processing of about 63,000 chemical substances intended for com-
mercial purposes. TSCA has effectively banned the manufacture
use of PCB and PCB products, prohibited chlorofluorocarbon
use as a propellant, and has proposed a phased-in ban on the use
and importation of asbestos,
Summari z at ion
This chapter has provided an overview of existing environmental
legislation and programs within the U.S. and Canadian federal
governments, the State of Michigan and the Province of Ontario.
Considerable legislation exists to control and influence environ-
mental quality in the Great Lakes Basin, along with mechanisms to
effect further improvements in Great Lakes ecosystem quality.
Discussion of each Act, or program mentioned within this chapter,
along with, others, is expanded upon in a more comprehensive re-
view of regulatory programs in the Regulatory Task Force Report
(1) which is included in Volume III.
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59
P. REFERENCE
1. Regulatory Task. Force Report, UGLCCS. 1988. Summarization
of environmental regulations, agreements and programs in the
United States, Canada, Ontario and Michigan, C, Fuller
(chairperson). Final Kept June, 1988.
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CHAPTER TV
DATA QUALITY MANAGEMENT
A. DATA REQUIREMENTS AND PROCEDURES
1. Intended Use of Data
The UGLCC study's main objectives were to assess the current
status of the ecosystem and recommend remedial action where nece-
ssary. Parameters were selected for study based on historical
problems in the various study areas and to provide information on
a range of chemicals with different properties. Analytical
methods for most of the study parameters are well established.
The only exception to this was the analysis of trace organics at
ambient concentrations in water. For the most part, only re-
search laboratories have the capability to perform these analyses
because of the low detection limits (parts per trillion)
required.
The data generated for the study needed to be of sufficient qua-
lity to provide the approximate concentrations of the study para-
meters in the various media so that these concentrations could be
related to ecosystem objectives. The data also needed to be of
sufficient quality to show whether a particular study area was a
net source or sink for the study parameter. The UGLCC Study was
not intended to provide accurate loadings of the contaminants to
the system or precise concentrations in all media; however, esti-
mates of loadings and concentrations permit relative comparisons
between contaminant sources.
A secondary study objective was to identify additional toxic
contaminants that could be causing problems in the study areas.
Thus, the laboratories must be able to identify the presence of
these contaminants and to estimate their approximate concentra-
tion in the media analyzed..
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62
2. Field and Laboratory Procedures
Sample collection procedures followed by all agencies are well
documented in the principal investigator reports. For the most
part, sampling was conducted according to established protocols,
For specialized sampling, such as ambient waters, thoroughly
tested published procedures were used. Water and effluent
samples were stored at 4^C with the addition of appropriate pre-
servatives (for example, acid for metal analyses). Sediment and
biota samples were kept frozen until analysis.
Samples of effluent for the point source survey were 24 hour
(U.S.) or 3 to 6 day (Canada) composites. Most other samples
collected were grab samples. The samples collected were appro-
priate to address the objectives of the study. For all studies
the number of samples collected was limited.
Field blanks and replicates comprised over 10% of the analytical
output of the study. In general, most parameters were not de-
tected in the field blanks. In most cases the percent deviation
between field replicates was less than 20%.
U.S.EPA methods were used by most laboratories for the analyses.
These methods specify frequencies of calibration, blanks, spikes,
duplicates, and surrogate spikes. The achievement of lower de-
tection limits by some research laboratories required the use of
large volume samples (up to 200 litres), larger than are speci-
fied in the U.S.EPA methods. Proportionally larger volumes of
extraction solvents were used for these samples. The final de-
terminations were usually by U.S.EPA or comparable methodology.
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63
B, DATA QUALITY MANAGEMENT
The experience of earlier international multi-media studies in
the Great Lakes Basin, particularly the Niagara River Toxic Com-
mittee Report (NRTC) (1), demonstrated the need for a careful and
systematic program to ensure data quality and the utility of
analytical results. Those involved in the NRTC Study strongly
recommended the establishment of a data quality management pro-
gram as one of the first actions of the Upper Great Lakes Con-
necting Channels Study,
The earlier studies found that commercial, government, and aca-
demic laboratories use different analytical methods, instruments,
standards, levels of detection and reporting formats. Without
external checks, there are no means to ensure that data generated
by two or more laboratories would generate comparable data.
Furthermore/ agreement had to be reached among representatives
from agencies having differing missions, goals and study require-
ments for a common protocol or strategy for data quality manage-
ment. As part of such a strategy, the Management Committee agr-
eed that, wherever possible, the number of laboratories providing
analytical support would be minimized and laboratory facilities
would be shared by the agencies in the study. This was an impor-
tant step in minimizing potential variability in the data.
1, Activities
The Management Committee formed a Quality Management Workgroup
(QMWG) from the agencies providing field and analytical service
support. Consulting personnel experienced in statistical design
and data quality analyses were also identified. The terms of
reference for the Workgoup were as follows:
1) establish a quality management system for the UGLCC Study;
2} review and evaluate the suitability, completeness and com-
petence of individual project quality assurance plans;
3) recommend quality assurance requirements for sampling, sam-
ple handling, analysis, management of project data and qua-
lity control data;
4) compile, review and report on the appropriateness of analyt-
ical and field protocols identified in the Quality Assurance
Project Plan, as they became available;
5) provide guidance to other workgroups in the analysis and use
of historical data as required by the Activities Integration
Committee;
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64
6) require and review periodic Quality Assurance (QA) reports
from the individual workgroups; and
7) review draft project reports with respect to QA issues,
Throughout the Study, the QMWG maintained close contact with the
Management Committee and the Activities Integration Committee,
The QMWG Chairman or a representative participated in their meet-
ings and provided verbal and written briefings on issues as they
arose. A data quality management strategy was agreed upon (2).
This included a project data quality plan document which was
given to each project leader. This project plan was submitted to
the workgroup by the principal investigators and was then re-
viewed by the QMWG. The review assessed the proposed project
quality assurance and quality control procedures as well as,
where feasible, the statistical design of the project. The data
quality management strategy also included a series of thirteen
interlaboratory "round robins" consisting of the analyses of
"standardized" samples of blind concentration and composition.
The results of the studies were provided to the Activities In-
tegration Committee and the Management Committee such that cor-
rective action could be taken as necessary.
It must be recognized that each agency has its own criteria for
determining suitable field and laboratory procedures. In most
cases these are chosen to meet the agencies' specific mandates.
Within the time available to UGLCCS, it was not possible, and
probably not advisable, to institute method changes to achieve
standard procedures among the participants. The most that could
be achieved was to:
a) encourage good project planning, including all necessary
quality assurance activity;
b) encourage documentation of methods; and
c) initiate a limited number of round-robins, using such stand-
ards as were readily available to evaluate the accuracy of
participating laboratories.
It was known from the start that many of the field techniques
employed for sampling and sample handling were relatively un-
tested, especially for the organic constituents, because they
were part of exploratory research programs. There were questions
about analytical procedures that might be employed, in terms of
their ability to identify and quantify the many chemical con-
stituents of interest in the water, sediment, biota and effluent
samples. These issues were recognized early on by the other
workgroups, and were the topic of much discussion.
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65
Some difficulty was anticipated because the different jurisdic-
tions employed a variety of control practices to a greater or
lesser degree. There was concern that existing field and labora-
tory methods might not include the quality control and quality
assurance protocols needed to verify proper application, and to
document the level of quality achieved for UGLCCS. In the past,
the impact of ongoing laboratory quality control activity in all
these areas had been limited by the absence of a "top-down" ma-
nagement system to define responsibilities and ensure adequate
documentation. Hence, Management Committee formally endorsed a
modified U.S.EPA guidance document (3) as the basis for a quality
assurance project plan to be filed for each project for initi-
ating a verifiable QA process. The documentation and procedures
required by the UGLCCS Project Plan guidance document is shown in
the workgroup report {2}.
2. Project Plan Review Findings
The magnitude of the study required intensive effort on the part
of all workgroup chairmen to keep projects on track. Ultimately,
most projects were implemented without adequate prior QA review,
however, laboratory support for one project often provided data
to serve other activities. A total of 30 project plans (out of
170 projects) were received from the workgroups, the majority
dealing with biota and sediment. The workgroup QA project plans
were distributed as received for review by teams of one or two
QMWG members based on their expertise in field, laboratory, QA,
sampling design, and related statistical factors. Project plans
tended to follow the guidelines but were not necessarily complete
in defining or justifying their methodology, data quality needs,
or relationships to methodologies used by the other related pro-
jects.
Many project leaders had difficulty in providing detailed up-to-
date descriptions of their field, laboratory or QA/QC procedures.
This is not due to the absence of defined procedures, nor the
lack of appropriate QA/QC activities: but, simply because the
necessary documentation was not readily available. Some provided
excellent documentation in one or more areas; but, there was not
always a clear link between project needs and the specific tech-
nology used. Not all plans were evaluated for sampling
design or other statistical aspects because some projects were
essentially exploratory or were already in progress or even com-
pleted.
In general, the concept of a centralized quality assurance review
on a project by project basis was new to many of the partici-
pants. Most project leaders had never experienced such a respon-
sibility for providing the type of detail required in the QA
review protocol. The normal relationship for most project
leaders to their supporting analytical laboratories was that of a
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66
client to a service organization. As a result, significant dif-
ficulty was encountered in providing not only the requested de-
tail but the type of material to be provided, its actual rel-
evance to the UGLCCS, and the volume of material that was needed
for review. Due to the large scope of the project, not all the
members of the QMWG were fully familiar with specific laboratory
practices, the analytical methods or the statistical methodology
used by various organizations.
Delays in QA project plan reporting were encountered due to in-
complete reports and the large volume of background information
that had to be gathered, compiled and reviewed by disparate
groups of professional individuals in both the field study and
the QA review process.
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67
C. INTERLABORATORY PERFORMANCE EVALUATIONS
1. Background
Field sampling procedures, sample handling and preservation,
delays initiating analyses, sample matrix effects on the analyt-
ical process all affect data quality. However, there is no ques-
tion that the analytical measurement is especially critical to
the validity of project data. Traditionally, the single most
serious source of variation between results from different labor-
atories is the control of standards and the instrument calibra-
tion process. For this reason the QMWG agreed to place most
emphasis on the distribution of a series of check standards co-
vering all of the UGLCCS parameters for which checks were avail-
able.
2. Approach
The QMWG recommended that interlaboratory performance evaluation
quality control studies should be designed and carried out at
least three times with test materials containing all constituents
at low, medium, and high concentrations. Such studies would be
presented and evaluated before, during and at the close of all
analytical and field related activities. These studies were
carried out in conjunction with a quality management strategy and
in concert with an interagency split-sample program, and allowed
management full control and assurance of data quality for the
UGLCC Study. It was evident that this comprehensive program
could not be issued in a timely manner (2). A reduced program
was adopted that involved less frequent studies, use of only
standard solutions, surrogate spikes and a limited number of
natural reference materials.
The samples for the thirteen studies listed in Table IV-1 were
prepared and distributed to twenty-six laboratories in different
portions of the "round robins". The laboratories were requested
to analyze for 36 inorganic and 50 organic parameters (see Table
IV-1}. Three reports for each interlaboratory study were gener-
ated by the QMWG:
a) a raw data summary to the participants (for verification);
b) a final data summary when the study was closed; and
c) a final laboratory performance evaluation report.
In addition, 3 status reports were prepared to advise MC and AIC
chairpersons on extreme results. Extreme results were those
results that deviated significantly from target values. Brief
advisory reports reviewing the results of each interlaboratory
performance assessment study from the QMWG to the MC/AIC, were
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TABLE IV - 1
study parameters for interlaboratory performance
evaluation of UOLCCS QC studies.
Study
QH-1
OM-2
QN-3
ON- 4
8W-5
QM-8
QH-7
QH-8
QM 3
OM-10
QM-ll
QM-12
t>H-13
Teat Samples
4 arapu 1 a
4 ampuls
4 amp j I a
4 ampul a
6 sediments
4 water*
4 waters
4 sediments
2 ampuls
2 ampul*
2 ampul a
4 ampuls
4 ampuls
4 a»puls
4 waters
2 ampuls
4 ampuls
4 waters
4 waters
2 ampuls
2 oils
'i tissues
Parameters
Aroclors
O,C. Insecticides*
Chlorinated Hydrocarbons**
16 PAHS
10 Metal*
23 Major Ions fc Nutrients
7 Metals
Chlorinated Hydrocarbons**
Chlorinated Hydrocarbons**
Aroclors
Chlorinated Hydrocarbons**
Aroclors i Chlorinated
Hydrocarbons**
Chlorinated Insecticides*
Chlorinated Insecticides*
Hereury
16 PAHa
IS PAHs
Cyanide
Total Phenol
5 Chioro phenols
Substrate
std solutions
atd solutions
£td solutions
std solutions
sediment CRN or RH
water CRN
water CRM
sediment CRN or UN
ntd solutions
std solutions
std solutions
spiking solutions it
natural water
std solution
spiking solutions I
natural water
water RM
std solution
spiking solutions t
natural water
water RH
water RH
std solutions
fish oils
fish tissues
* HCB, talph*, gamna) BHC' Mirex, pp'- DDE' pp - ODD, pp*-DDT, heptachlor epoxide, dieldrin, ialpha,
Chlordane, oxychiordane,
** (1, 4, 1, 3, 1. 2t dichlorobenzene, U, 3, S, 1, 2, 4, 1, 2, Si trichlorobenzene
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69
used by the UGLCCS management to Implement the QA. management
strategy and to ensure that appropriate corrective action could
be taken.
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70
D. UGLCCS QUALITY ASSURANCE RESULTS
1. Percent Recoveries
The following results have been summarized from QMWG integrated
reports evaluating interlaboratory performance for organics (4)
and trace metals (5). As part of the QMWG recommendation for a
QA/QC program for UGLCCS, values determined for samples should
fall within a window of +/-25% of the design values,
Trace jvietals
Figures IV-1 and IV-2 present graphically condensed results of
the range and average values of percent recoveries of interlabor-
atory medians for all elements analyzed and all samples reported
in sediments and waters, respectively.
For the sediment samples analyzed in QM-3, results for seven out
of 10 elements, namely Pb, Zn, Hg, Cu, Ni, Co and Pe, were satis-
factory because average recoveries for all samples tested were
within +/-25% of the design values and the ranges of recoveries
for all samples were within +/-25% of the design values. The
performance for Cd and Se in these sediment samples were also
satisfactory with average recoveries for all samples falling
within +/-25% of the design values. However, the ranges of re-
coveries for all samples tested showed wide variations and fell
outside the limits (+/-25%) of the design values (Figure IV-1).
The interlaboratory results for Cr were less satisfactory with
average recovery for all samples exceeding +/-25% of the design
value. This was assumed to be due to incomplete digestion of the
sediment samples.
For the water samples analyzed in QM-5 and QM-9 as shown in Fig-
ure IV-2, the interlaboratory comparability was excellent. All
seven elements, (Cd, Pb, Zn, Cu, Ni, Co and Fe), determined in
QM-5 and Eg in QM-9 were satisfactory with the ranges and aver-
ages of interlaboratory medians for all samples within +/-25% of
the design values. The ranges of recoveries among test samples
had wider variations for Zn and Hg than those obtained for the
remaining elements.
Overall, comparing the precision of interlaboratory results for
sediment and water samples, the less scattered results among test
samples were obtained for water samples than those obtained for
sediment samples, except for Hg. The wider variations of rela-
tive standard deviation (RSD) for Hg among test samples for water
samples as compared with those for sediment samples, perhaps, was
attributed to the lower concentrations of Hg in these water sam-
ples. In general, the interlaboratory comparability for the
accuracy and precision of trace metals in sediment and water
samples was satisfactory in most cases.
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FIGURE IV-1. Percent recovery for trace
metals (sediments).
FIGURE IV-2, Percent recovery for trace
metals (waters).
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72
Organic Parameters
i) OCs (Organochlorines)
The QMWG had set results within +/-25% of the design values for
organic parameters as satisfactory. The agreement of interlabor-
atory medians for organochlorines was excellent. The results for
all the samples were satisfactory within +/-25% of the design
values for all OC parameters except sample 108 in QM-1 for p,p-
DDD.
In order to detect the bias of interlaboratory results, the range
and average of interlaboratory medians for all OC parameters in
various studies were summarized. Figure IV-3 presents condensed
results of average recoveries of interlaboratory medians for all
samples in various studies. As can be seen from this figure, the
interlaboratory results were compatable and satisfactory for all
OC parameters in ampules of both QM-1 and QM-8. Furthermore, the
interlaboratory results in QM-8 were more accurate than those in
QM-1 for all OC parameters in most cases.
The percent average recoveries of OCs in spiked water samples in
QM-8 were less accurate as compared with ampule samples in both
QM-1 and QM-8 studies. However, the interlaboratory results for
all OCs in QM-S were still satisfactory within +/-25% of design
values except for HCB.
ii) PCBs (Polychlorinated Biphenyls)
The agreement of interlaboratory medians in PCS test samples was
excellent and percent recoveries of interlaboratory results were
all satisfactory (within +/-25% of the design values) in both
studies. The accuracy of interlaboratory comparability for PCBs
in ampules and spiked water very satisfactory in both stud-
ies.
iii) CHs (Chlorinated Hydrocarbons)
The results of CH analyses suggest that interlaboratory perfor-
mance by participating laboratories, in most cases, improved in
QM-6 and QM-7 as compared with the earlier QM-1 using ident-
ical samples in various studies. In QM-1, CHs were dif-
ferent by more than +/-25% of the design values; while all CHs
were satisfactory within +/-25% of the design value in sample 606
of QM-6 and samples 703 and 704 of QM-7, These results suggest
that the earlier interlaboratory studies helped the participating
laboratories correct their internal quality control and that the
quality of the test samples used for these evaluations was veri-
fied.
In order to evaluate the interlaboratory comparability, the range
and average of percent recoveries of interlaboratory medians in
-------
14O
180
0
i
468
OC Parameter No.
QM-I (ampules)
QMS (ampules) • QM-8 (waters)
140
-------
74
various studies were summarized. Condensed results of average
recoveries of interlaboratory medians for all 13 CH parameters
are shown in Figure IV-4.
As expected, the interlaboratory results for spiked waters (QM-7)
and sediments (QM-6) were less satisfactory as compared with the
ampule samples (QM-1, QM-6 and QM-7). Overall, only six out of
thirteen parameters (1,4-DCB; 1,2-DCB; 1,2,4,5-TeCB; PeCB; HCB;
and OCS} in water samples (QM-7) were within +/-25% of the design
values. The performance of spiked waters for CHs (QM-7) was less
satisfactory as compared with those of spiked waters for OCs (QM-
8) and PCBs (QM-7). However, the interlaboratory results for
sediments were less satisfactory as compared with ampule samples
but were better than those in spiked water. Overall, seven out
of 12 CH parameters were satisfactory within +/-25% of design
values (HCE was not evaluated since a reference value was not
available),
Poor quantitative recoveries of CHs from spiked waters were ex-
pected because of the volatility of most CHs, resulting in evapo-
rative losses. In addition, the high water solubilities of some
CHs also cause poor extraction recoveries.
iv) PAHs (Polycyclic Aromatic Hydrocarbons)
Figure IV-5 presents graphically the condensed results of percent
average recovery of interlaboratory medians for all 16 PAHs in
various studies. For the ampule samples, the interlaboratory
results were satisfactory within -t-/-25% of the design values in
most cases. Only three out of 16 parameters (fluorene, phenan-
threne and chrysene) varied by more than +/-25% of the design
value in QM-2 while all 15 PAH parameters were satisfactory
within +/-25% of design values in QM-10. The performance of PAHs
showed a significant improvement in QM-10 as compared with the
earlier QM-2.
2. Overall Laboratory Performance
Acceptance Criteria
The key to administering information involving the laboratory
performance data is the selection of acceptance criteria. The
overall performance evaluation in this integrated report is based
on percent biased of parameters analyzed and percent flagged of
results reported. For the flags, the number of results reported
by each laboratory excluding those with "ND" (not detected), "NS"
(not separated; 2 parameters co-eluted), and "LT" (less than)
codes, sum of results flagged with VH, H, L or VL, (very high,
high, low, very low) for all parameters, and the percentages of
results flagged were calculated. In addition, values less than
detection that were flagged were included in the calculation of
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75
140
0 2 4 6 8 10 12 14
40
PAH Parameter No.
10 (»mpui»S) • QM 10 (w»l»ri) G QM 2 (ampulas)
FIGURE VI-5, Average recovery (%) for PAH's (various studies).
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76
the percent flagged. Similarly for the bias, the number of para-
meters analyzed, by each laboratory, the sum of parameters biased
with VH, H, L, VL based on average recovery for each set of samp-
les and the percent of parameters biased were calculated. Note
that the H and L parameters biased were counted as half of a VH
or VL parameter.
To simplify the overall assessment of laboratory performance in
various studies, the average of percent biased and percent flag-
ged is calculated. The criteria or performance index provides a
simple way to compare laboratory performance in various studies
as shown below:
Average of Percent Biased
and Percent Flagged Comments
< 25% Satisfactory (A)
26-50% " Moderate (B)
> 51% Poor (C)
Trace _Metals
Most laboratories provided consistent and satisfactory results
for the interlaboratory studies for trace metals (5) .
Organic Parameters
i) ocs
For the laboratory performance of OCs in various studies, few
laboratories have achieved consistency for producing satisfactory
results for both ampule and spiked water samples. Some other
participating laboratories also produced satisfactory results but
only participated in one study: either QM-1 for ampules or QM-8
for both ampules and spiked waters. However, for these OC in-
terlaboratory studies, only one laboratory produced inconsistent
and rather poor results for OCs in both ampules and spiked
waters.
ii) PCBs
Three laboratories achieved consistency for producing satis-
factory results for PCBs in both ampules and spiked waters. Al-
though the PCS results for ampules were satisfactorily generated
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77
by all participating laboratories in most cases, poor results for
spiked waters were produced by several laboratories. It was
obvious that less satisfactory results for spiked waters were
attributed to sample preparation involved with extraction, con-
centration and clean-up steps because the results for ampules
were satisfactory within +/-25% of design values by all partici-
pating laboratories.
iii) CHs
The laboratory performance for CHs in various studies was less
satisfactory as compared with those obtained for OCs and PCBs.
Only one laboratory, which analyzed all the samples provided, and
most parameters requested, achieved the consistency for satis-
factory results in all matrices (ampules, waters and sediments).
On the other hand, there were more poor results generated by
participating laboratories in either matrices in these CH inter-
laboratory studies than for other parameters,
iv)
Only one laboratory achieved the consistency for producing satis-
factory results for PAHs in both ampules and spiked waters.
However, less than satisfactory results were generated by only
two laboratories in either ampules or spiked waters. The per-
formance of one laboratory in QM-10 very satisfactory for
both ampules and spited water as compared with that obtained in
QM-2, This extensive improvement for this laboratory demons-
trated that the impact of these interlaboratory studies was very
valuable in assisting participating laboratories to correct their
internal QA/QC problems.
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78 •" -^
E. FINDINGS AND CONCLUSIONS
It is difficult to summarize the performance of laboratories
because data quality varies with each parameter, matrix, and
laboratory as well as over time. Furthermore, the acceptability
of data for each laboratory depends on project objectives. In
general, the large service laboratories performed consistently
better than the smaller service laboratories and research labora-
tories did not perform as well as the routine laboratories.
It must be stressed that the QC samples in the interlaboratory
performance evaluation studies for UGLCCS are generally easier to
analyze than actual field samples. Most of these quality as-
surance samples were standard solutions at reasonably high con-
centrations and did not require special preparation. It is also
recognized that many laboratories took extra care and performed
repetitive analysis when dealing with the QC samples. Therefore,
unsatisfactory performance in these interlaboratory studies may
indicate a poorer quality of data for real samples in routine
analysis.
The impact of these interlaboratory studies on laboratory opera-
tions is illustrated by a couple of examples. A large contract
laboratory was identified as having severe analytical problems in
several performance evaluatipn studies partly due to ineffective
in-house QC. The laboratory took corrective actions. The data
quality for one type of parameter (PAHs), when subsequently re-
evaluated, drastically improved. Three research laboratories and
one large routine laboratory on separate occasions stated that
the interlaboratory performance evaluation studies induced them
to re-examine instrument calibration and the accuracy of the
standards for chlorophenols, chlorobenzenes, PCBs and octachloro-
styrene. Consequently, the analyst discovered poor in-house
standards and improper calibration. Without these interlabora-
tory test samples, these laboratories would not have been aware
of their internal biases.
The timeliness of QMWG follow-up on the findings of these studies
was significantly impaired by the slow response of some of the
participating laboratories. The reporting deadlines were fre-
quently exceeded due to internal schedule conflicts. The actual
number of laboratories providing results Cor any given test para-
meter depended on whether their UGLCCS project included that
parameter. Hence, where severe scatter between laboratories was
observed, it was not possible to decide whether this reflected
poor control, or just the current "state of the art".
Many of the check samples were standards, and one would expect
reasonably good recoveries and precision. In fact, for many of
the organic tests, although a given lab frequently reported very
similar results on the duplicate samples, the spread of results
across labs was quite large. There is a definite need for an
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79
intensified effort by organic analysts for better control of
standards, and the overall calibrations and quantification pro-
cess , The findings in this area complement the findings of simi-
lar studies conducted by the Great Lakes Water Quality Board of
the International Joint Commission.
The data quality management effort required intensive record
keeping and imposed a significant additional sample load on the
participating project managers and supporting analytical labora-
tories. The effort necessary to staff and organize the process
precluded using the review as a preventative measure in most
cases. However, it did flag facilities having quality assurance
problems, precluded the use of data outside the specifications
demanded by specific studies and allowed participating labora-
tories to make corrections to their standards and procedure dur-
ing the course of the study. The data quality effort ensured
better data for decision making both for this study and for sub-
sequent environmental activities. It demonstrated clearly that
joint studies require more than a sharing of equipment, personnel
and laboratory space but also an active, ongoing data quality
management program between the United States and Canada, There
is insufficient time during the design and planning phase of
large multi-agency co-operative studies to develop a common data
management program that will assure a reliable and compar- able
data base during the subsequent study. Agencies must recognize
the importance of quality assurance documentation as an on-going
requirement, not only for internal laboratory reviews but also
for external scrutiny.
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80
F.
1» Report of the Niagara River, Toxics Committee 1984.
N.Y State Dept. Env, Cons., Env. Can, U.S.EPA, and Ont.
Min. Env: 630 p.
2. Quality Management Workgroup UGLCCS. 1987. Report of
the Quality Management Workgroup. Revised draft, July,
1987. A.S.Y. Chau (Chairman), NWRI, Environment
Canada, Burlington, Ontario: 26 p. + append.
3. U.S.EPA. 1983. Guidance for preparation of combined work
quality assurance project plans for water monitoring. OWNS
QA1 1983.
4. Quality Management Workgroup, UGLCCS, 1988.
Interlaboratory performance evaluation study integrated
report Part II: trace metals. Prepared by W.C. Li,
A.S.Y, Chau and E. Kokotich, NWRI, Environment Canada,
Burlington, Ont; lip. + Tables and Figures.
5, Quality Management Workgroup, UGLCCS, 1988.
Interlaboratory performance evaluation study integrated
report Part I: Organic Parameters. Prepared by W.C.
Li, A.S.Y. Chau and E. Kokotich, NWRI, Environment
Canada, Burlington, Ont: 19p. + Tables and Figures.
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CHAPTER V
INTRODUCTION TO MODELING ACTIVITIES
A.
Mathematical modeling of ecosystems is a relatively young tech-
nique which, in simplest terms, seeks to simulate actual environ-
mental conditions in a numerically quantifiable fashion. Ideal-
ly, a model is a dynamic conceptual framework which enables a
clearer understanding of major factors affecting existing states
within an ecosystem, under certain conditions, some numerical
simulations offer the added advantage of using data on existing
environmental states, coupled with ecosystem process information,
to enable predictions of future trends and tendencies. Quite
logically, the predictive capability of such a tool is only as
good as the conceptual framework of the model, the data set upon
which it is based, the assumptions required to develop the model,
and the extent to which the model has been both calibrated and
verified.
Two types of models were developed in the UGLCCS. The first type
of model is based on mass balance calculations. The second type
of model is a process-oriented model. Both types of modeling
efforts are valuable for indicating needed research, remedial and
regulatory actions.
With sufficient data, mass balance calculations are useful for
determining (1) whether an area is a source or sink of contamin-
ants, and (2) the relative importance of known and unknown con-
taminant sources. Mass balance calculations were made for a
number of water quality parameters in Lake St. Clair and the
Detroit River (including the Trenton Channel, Table v-l). The
balances calculated for these systems represent order of
magnitude "snapshots" of contaminant fluxes since measurements
were made during short time intervals only. Annual mass balances
cannot be inferred from these calculations unless specifically
noted.
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82
TABLE V-l
balance calculations performed on the
Upper Great Lakes Connecting Channels. .-
Location Date(s) Parameters
St. Clair R. Aug., Sept., Oct., Organics (concentration
1985 profiles only)
Lake St. Clair July 21-29, 1986 Metals, Organics, Total
Phosphorus
Detroit River April 21-29, 1986 Metals, Organics, Nutrients,
(SMB I) Chlorides, Suspended Solids
July 25 - August 5, Metals, Organics, Nutrients,
1986 (SMB II) Chlorides, Suspended Solids
Trenton Channel May 6-7, 1986 Metals, Organics, Nutrients,
Chlorides, Suspended Solids
August 26-27, Metals, Organics, Nutrients,
1986 Chlorides, Suspended Solids
Process-oriented models are based on mechanistic relationships
(e.g. contaminant-sediment interactions) and represent a working
hypothesis of how a dynamic system works. Process-oriented mo-
dels are useful for (1) understanding the relative importance of
processes that affect contaminant fate, and (2) given proper
calibration and verification, for answering "what if" questions
(e.g., if a particular contaminant is added to a system, where
will it go, how long will it stay, what physical-chemical form
will it be in, and what organism exposure might occur?). Models
describing a variety of physical, chemical and biological
processes were developed for the St. Marys River, the St. Clair
River, Lake St. Clair, the Detroit River and the Trenton Channel
(Table ¥-2).
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83
TABLE V-2
Process models developed for the Upper Great
Lakes Connecting Channels Study.
Location
Type of Model
St. Marys
River
St. Clair
River
Lake
St. Clair
Detroit
River
Trenton
Channel
3-D steady state finite element hydrodynamic
(upper river)
Steady state, depth averaged, mixing model
(lower river)
Contaminant fate model (driven by hydrodynamic
models, above)
Unsteady flow model with flow separation around
islands
Steady state depth averaged mixing model
Contaminant fate model (water column only)
Contaminant fate model (TOXIWASP-based water
and sediments)
Water level models (hydrodynamic and empirical)
Currents (predicts mean and daily currents)
Particle transport model
3-D finite element flow field model
Waves and sediment settling and resuspension
Contaminant fate, 2-D model (TOXIPATE)
Contaminant fate, 2-D model (TOXIWASP-based)
Contaminant fate, 1 box kinetic model
2-D plume model of water and contaminant dis-
charge from Detroit's sewage treatment plant
- 3-D hydrodynamic and toxicity transport model
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84
B. METHODS
1, Mass Balance Calculations
Mass is a conservative property. As such, a material balance
framework can be applied to a control volume (i.e., water body)
where, assuming conservative behaviour and steady state condi-
tions, the change in mass of the system can be described as:
D = wout ~ win
w~in is the sum of all loads (flux) coming into the control
volume (mass/time). WOU£ is the mass flux leaving the control
volume. If all loadings into the system are accounted for and
the mass flux leaving the system is known, then "D" should equal
zero for a conservative substance. In general, if D is not zero,
then the control volume is either a sink (D<0) or a source (D>0)
of the substance. For substances that "leave" the system through
volatilization or degradation it is important to note that a D<0
does not necessarily mean that the substance is accumulating in
the control volume. A process-oriented calculation would be
needed to define how much substance was lost through-volatiliza-
tion or degradation before an accurate estimate of accumulation
could be made. Figure V-l provides examples of mass balance
calculations and interpretations based on various situations.
In the Connecting Channels where horizontal flow (advection)
dominates, the w terms can be computed from:
W = Q * C
Where, w is mass flux (M/T)
Q is the flow rate (L.3/T) > snd
C is the concentration (M/L^).
There are two sources of error in calculating W. First, there
are analytical errors associated with measurement of Q and C.
Second, errors can be introduced by inadequate temporal and spa-
tial sampling. Ideally, analytical errors would be non-existent
and sampling of Q and C would be continuous at all locations.
This is never the case, however, so W is always an estimate of
the true load. Annual loads would ideally be calculated based on
continuous measurements of Q and C throughout a year period.
However, Q and C measurements might have been taken on a weekly
basis only. Annual loads calculated with weekly information will
be less certain than if the measurements were continuous.
Contaminant concentration data are sometimes reported as non-
detectable or below the detection limit. This does not imply
that the contaminant is not present in the sample, but merely
that it cannot be quantified.
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85
Situation
upstream and down-
stream flux known,
external loaos
unknown
Cartoon
Interpretation
Study area is a source
of contaminant (net
flux = 5).
Upstream ana down-
stream flux known,
external leads
unknown
10
Study area is a sink
for contaminant (net
deposition » 5)
10 5 2
case- i
Case
Upstream anc down-
stream flux known;
external loads
known,
5
verage: 1
052
10
/\ /\ /\
1- std, 5 15 2.5 75 1 3
Net deposition- cf
5, study area ;s
a sink
NO net deposition
Net export or 3;
study area is a
source
case:
Upstream and down-
stream flux known;
external loads
approximated,
i j iui
10
Upstream and down-
stream flux
approximated;
external loads
approximated,
average
»/- std,
average
*/- std.
average
*/- std.
Case
i No deposition •
deposition of 5,
II In-place source of 2.5
- net deposition of
2.5
iij In-piace source of
4 to 2
Can be difficult to
interpret; deoe^ss
on temporal resolu-
tion of samples.
FIGURE V-l. Mass balance calculation examples.
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86
Given a high, flow condition and non-detectable concentrations, a
significant portion of a contaminant mass balance can be over-
looked if non-detectable concentrations are treated as zero con-
centration. Therefore, a method for handling non-detectables in
all mass balances was devised. Details of the method used are
supplied in the Modeling Workgroup Report (1),
Comparability of point source sampling between Canada (3 to 6 day
sampling composites) and the U.S. (24 hour composites) was an
issue. An additional issue was the use of gross loadings (U,S,-
effluent only) versus net loading (effluent minus influent-
Canada) . The loads used in mass balance calculations that follow
were those that the Point and Nonpoint Source Workgroups fur-
nished to the Modeling Workgroup. No modifications or correc-
tions to their numbers were by the Modeling Workgroup.
All balance calculations that could be made were summarized
as shown in Figure ¥-2, With this type of diagram the relative
importance of loads can be visualized, the relative contributions
of U.S. and Canadian sources can be evaluated, unknown loads can
be identified, and the source-sink question can be answered for
the time period in question. In balance diagrams the width
of the arrow shafts indicate the relative importance of the
average load and loss terms. Average loading terms are sub-
divided into Canadian and U.S. contributions. A detailed break-
down of loading figures can be obtained from the Point and Non-
point Source Workgroup reports. At the bottom of the figure is a
box that provides an interpretation of the balance data.
Statistical conclusions are given in this box although all data.
leading to the interpretation are not indicated.
2, Process Models
Process-oriented models represent working hypotheses of cause and
effect linkages. These simulation tools can be used to inves-
tigate the relative importance of the various processes that
control the linkages. As such, process models can provide a
framework for identifying needed field measurements and experi-
mental studies. Process models have the potential for being used
in more than one system because they are theoretically based.
The process models developed in this study range from purely
physical models of water movement to temporally and spatially
complex contaminant fate and behaviour models. Verification of
the latter models have been difficult due to lack of necessary
and sufficient data. Nevertheless, these models are based on
well documented cause and effect relationships. Thus they can be
used to speculate upon the possible fate of new contaminant in-
troductions and related organism exposures in the Connecting
Channels.
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SMB1 Contaminant ABC (Kg/d)
Upstream Input
U.S.A.
Rouge R.
WWTP
Ecorse R.
Detroit
River
Downstream Output
Canada
Little R.
Turkey C.
Apparent
Surplus =X
....a surplus suggests
an unknown source
FIGURE V-2, Example of mass balance model presentations,
(Detroit River Chapter VII only).
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88
The output from process models is subject to uncertainty. Sour-
ces of uncertainty for these models include loading information,
boundary conditions, initial conditions, parameter estimates
(e.g., coefficient values used in process equations), and concep-
tual problems (e.g., are the boxes and arrows used the correct
ones?). Although the Modeling Workgroup sought to conduct com-
plete uncertainty analyses on all UGLCCS process models, time
constraints and the computer resources needed for Monte Carlo-
type simulations became limiting factors for most modelers.
However, uncertainty analysis of models still may take place
after the UGLCCS is over. Through sensitivity analyses, modelers
were able to identify some parameters and processes that may
require further research in order to improve contaminant fate
models.
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C. RECOMMENDATIONS
1. The goals of the study must be clearly defined. Recommenda-
tions for appropriate data collection and model development de-
pend on it.
2. Goals fall into several categories: research, regulatory,
remedial and political. The resource priority that each of these
categories can expect to receive should be identified early on
and be consistent with the goals of the study,
3. Goals must be realistic given time, personnel, financial, and
laboratory capacity constraints. Realistic goals may not equate
with ideal goals, but realistic goals promulgate realistic ex-
pectations .
4. Modelers are often asked to give direction to a study because
models include the physical, chemical and biological processes of
a system that are important for understanding its functioning and
the behaviour of contaminants in it. By understanding the sensi-
tivity of the system's behaviour to these processes, areas can be
identified where data collection is most important. Modelers
should be encouraged to develop "speculative" models as quickly
as possible in order to perform these sensitivity analyses.
5. Monitoring and research requirements for any study should be
identified in close cooperation with the modelers.
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90
D, • REFERENCE
1. Modeling workgroup, UGLCCS 1988. Modeling Workgroup
geographical area synthesis report. Dra£t May 1988, T.D,
Fontaine (Chairman), NCAA-Great Lakes Env, Res, Lab. Ann
Arbor, Ml; 96 p + Append,
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CHAPTER VI
ST. MARYS RIVER
A. STATUS OP THE ECOSYSTEM
1. Ecological Profile
Watershed Characteristics
The St. Marys River connects Lake Superior and Lake Huron. The
river originates in Whitefish Bay on Lake Superior between Point
Iroquois, Michigan and Gros Cap, Ontario and flows 112 km to Lake
Huron. The lower St. Marys River has irregular shorelines and
contains four large islands: Sugar, Neebish and Drummond on the
American Side and St. Joseph on the Canadian side, as well as
approximately 100 small islands less than 4 km^ j_n area. Sugar
Island separates the main river into the Lake George and Lake
Nicolet channels (Figure II-2).
The surface geology of the southwestern St. Marys River valley is
composed primarily of lacustrine sediments and moraines. On the
southwestern edge of the valley, in Michigan, level lake bed
plains are interrupted by gently rolling plateaus, low rounded
ridges, sand dunes, bluffs, and marshlands. In Ontario, on the
northeastern edge of the valley, knobby Precambrian rock is
partially covered by a thin layer of till or lacustrine clay.
Much of the bedrock of the basin consists of volcanic and gran-
itic rocks of Precambrian origin in the north, and Qrdovician and
Silurian dolomites in the south.
The primary influence on surficial geology of the St. Marys River
basin during recent times has been the fluctuating water levels.
As recently as 3,000 years ago, crustal rebound lifted up rock
ledges at Sault Ste. Marie to a level higher than the water level
of Lake Huron. This changed the strait connecting Lakes Superior
and Huron into the St. Marys River. The influence of fluctuating
water levels on the St. Marys valley during the last 4,000 years
has been to erode surface deposits, leaving remnant beaches, sand
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dunes, and other littoral features. Lacustrine clays form most
of the soil of the area south of the Canadian Shield.
There are a number of watersheds that drain into the St. Marys
River. By far the most important is the Lake Superior basin,
which also includes the Goulais River on the Canadian side.
Other drainage basins that discharge to the St. Marys River are
much smaller. On the U.S. side, these include the Charlotte,
Little Munuscong, Munuscong and the Gogomain Rivers. These drain
about 64% of the immediate watershed. On the Canadian side are
the Big Carp, Bar, Little Carp, Root, Garden, Little Garden and
Echo Rivers.
Hydrology
Hydrologically, the St. Marys River may be divided into three
major reaches: the upper river, extending from Whitefish Bay to
the St. Marys rapids; the rapids; and the lower river, extending
from the foot of the rapids to the De Tour Passage at Lake Huron.
The upper river rapidly decreases in width in its 22.5 km of
length and is characterized by sandy shores, with emergent wet-
lands occurring only in protected areas. The rapids separate the
upper and lower river, and in an area 1.2 km long and 1.6 km
wide, the river drops 6.1 m. The lower river is divided into two
main outlets, Lake Nicolet and Lake George, and is slower moving.
Water currents of the river are highly variable and influenced by
the quantity of discharge to the river from Lake Superior and the
water level of Lake Huron. Current velocities are impeded by
high surface water levels in the river's mouth at Lake Huron, by
easterly or southerly winds, or by low barometric pressure. High
surface water levels in Lake Superior result in greater discharge
to the river and increased current velocities. Discharge to the
river has been partially controlled by compensating gates at the
Sault Locks since 1921.
Recorded outflow from the St. Marys River fluctuates greatly.
The mean flow rate for the 124 years of record (1860 - 1984) is
2,200 m^/sec, and have ranged from a minimum of 1,200 ni^/sec to a
maximum of 3,700 m^/sec. Since the completion of the Long Lake
and Ogoki Diversions in the 1940s, in which some waters original-
ly draining north into James Bay were diverted to Lake Superior,
there has been an increase- in the mean discharge by about 8%.
During the period April to October 1983, 74% of the total dis-
charge measured at Sault Ste. Marie flowed through the Lake
Nicolet reach. The balance flowed through Lake George.
Water levels of the St. Marys River are subject to three types of
fluctuation: seasonal; long range, and short term. Seasonal
fluctuations are over a period of one year. These are the most
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93
regular, with highest water levels occurring during the summer
and lowest during the winter. There is about a 0.3 m change in
water level during the year.
Flushing rates were calculated and found to average 1.31 lake
(Nicolet) volumes per day. Because of this, and the hydrographic
features of the lower river, materials in suspension or solution
tend to be transported through the length of the St. Marys River
in a short period of time.
Habitats and Biologic Communities
A series of narrow channels and broad lakes exist throughout the
St. Marys River. The shorelines are without major areas of set-
tlement except for the cities of Sault Ste. Marie, Michigan and
Ontario. Rocky shores characterize the narrow reaches and clay,
sand or mixed detritus-sediment combinations are found in shallow
areas. The shorelines tend to be inhabited by emergent vege-
tation, sometimes uninterrupted for 3 to 5 km or more. The 12 km
tract of hardstem bulrush and bur reed that extends northward
from the Charlotte River is an example.
Annual production of bioinass in these wetlands is dominated by
three emergent plants: hard stem bulrush, giant bur reed and
spike rush. Submerged species occur as a diffuse understory of
low biomass. Growth that produces the emergent wetlands is vege-
tative and colonial, usually in rnonotypic stands. Areal surveys
of the last three decades show that these stands tend to be long-
lived, and relatively permanent features of the St. Marys shore-
line. Rootstocks of the dominant species are present in the
hydrosoil year round. They reach maximum biomass late in the
growing season and degenerate in winter. Live rootstocks die
back rapidly in the spring, yielding their food and nutrient
reserves to new shoot growth. A tight cycling of nutrients re-
sults from this cycle, leaving little available for invading
species.
Lake Superior and the St. Marys River are subject to important
wind-driven forces, such as waves and seiches. Strong prevailing
northwesterly winds cause formation of large waves which travel
long distances before reaching whitefish Bay and the headwaters
of the river. Regions of wide expanse on the lower river have
shorelines variously exposed to waves and currents. Shores with,
the most exposure have no emergent vegetation; the bottom is rock
and shifting sand, where emergent vegetation does occur, least
protected sites have square bulrush or spike rush as the dominant
vegetation. Most protected sites have hardstem bulrush and bur
reed. The west shore of the St. Marys River lies in the lee of
prevailing winds and emergent wetlands are more entrenched on
this shore.
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94
Upstream of the St. Marys fork at Mission Point and throughout
Lake Nicolet and its downstream reaches, submerged wetlands
spread as a meadow of low growing plants over bottom sediments
wherever the river is broad, the substratum suitable'and water
clarity good. Twenty-two known species of plants occur in these
wetlands.
Diatoms dominate the transient phytoplankton community and the
species are characteristic of oligotrophic waters. Seventy-two
species have been identified in the Lake Wicolet reach of the
river. A mix of planktonic and benthic species has been found in
the plume of the St. Marys River in Lake Huron. Benthic popula-
tions comprise as much as 40% of the total algal assemblage in
terms of cell volume, while the remainder is planktonic. Chloro-
phyll a_ concentrations show that planktonic algal biomass varies
only slightly from one end of the river to the other.
The species composition of benthic fauna changes from the upper
river downstream with downstream communities exhibiting increased
oligochaete abundance. Generally, the bottom fauna of the river
is indicative of good water quality. However, pollution tolerant
species are present near Sault Ste. Marie, Ontario as a result of
contaminant loadings to the river. Ephemeroptera, Aiuphipoda and
Mollusca are common and abundant and contribute substantially to
the standing stock biomass. Mayflies may be the most abundant
species of benthic invertebrates in the river. However, nymphs
of two species, Hexagenia limbata and Ephemera siraulans, are
particularly abundant in areas of soft substrate. Hexagenia
limbata is most abundant in portions of lakes George and Nicolet
and in the lower river where fine sediments occur; Ephemera
simulans is more common in the coarser sediments of Lake Nicolet
and the upper river. The bottom of the shipping channel, because
of dredging, is poor habitat for benthic niacroinvertebrates.
Primary fish habitats in the St. Marys River have been classified
as (i) open-water and embayments, (ii) emergent wetlands, (iii)
sand and/or gravel beaches, and (iv) the rapids (1). Although
most species are associated with only one habitat, some are found
in more than one habitat and some use different habitats on a
daily or seasonal basis. Rainbow smelt, spottail shiners, trout,
common white suckers, rock bass, and yellow perch were collected
in all habitats {2,3,4}.
In general, the open water fish community is dominated by demer-
sal species although two pelagic species, lake herring and rain-
bow trout, are abundant. Other fish found in open water areas
are yellow perch, white sucker, lake whitefish, northern pike,
and walleye, Smallmouth bass, Chinook and pink salmon, and lake
sturgeon are seasonally abundant in open water areas,
Liston et al. (4) collected 49 species of fish in the wetlands of
the river which serve as spawning, nursery and feeding areas for
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95
many species, particularly yellow perch, northern pike, small-
mouth bass, bowfin, longnose gar, brown bullhead, and walleye. A
similar species mix was found in the sand and gravel beach zones
together with of the small bottom species found in the open
water areas. Trout, perch, shiners, and juvenile walleye are
common in these areas.
The fish community inhabiting the St.-Marys rapids is discrete
from the fish communities of other parts of the river. Thirty-
eight species have been collected from the rapids (5), many of
which are of interest to anglers, including lake whitefish, rain-
bow trout, lake trout, brown trout, brook trout, and'Chinook
salmon. Important forage species in the rapids are longnose dace
and slimy sculpin. Sea lamprey adults are present in the rapids
during the spawning season (especially July) and appear to be
increasing in number.
Local Ecological_jtelationships
i) Food Web and Trophic Structure
Emergent plants are by far the most productive component of the
river system, some 200 times more productive than phytoplankton,
and 40-50 times more productive than submerged plants. Periphy-
ton on submerged shoots of emergent wetland plants have annual
productivity of the same order as the phytoplankton. Thus, in
the St. Marys system, food production for consumers is concen-
trated along the edges of the river in emergent wetlands and
along the bottom in submerged plant communities.
Among secondary producers, zooplankton represent an important
link between phytoplankton and higher trophic levels. Phyto-
plankton in pelagic zones of lakes and rivers have a low standing
stock biomass, but constitute the basis of pelagic food webs.
ZooplanJcton concentrate the energy available from phytoplankton
biomass and are then available to fish and other planktivorous
feeders.
The zooplankton community emptying into the river from Whitefish
Bay consists of some 30 crustacean species. The winter zcoplank-
ton community consisted mostly of adult stages of Diap_tonvus
cicilis, Diaptomus ashlandi, Limnocalinus micrurus, and immature
copepodids of Cyclops bicuspidatus tomasi. During summer, im-
mature calanoids, adult Cyclops bicuspidatus tgmasj. and Cladocera
dominate the open water environment.
The 2ooplankton of the lower river is very similar in species
composition to the summer community of the upper river, but far
less abundant. The zooplankton density in emergent wetlands is
more than an order of magnitude greater than the maximum den-
sities found in open water.
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96
The benthic macroinvertebrate community of emergent wetlands in
the St. Marys River is taxonomically diverse with a total of 171
recorded species or taxa of aquatic insects. Chironomidae are
the richest fauna, with 39 species, with Hemiptera, Odonata and
Coleoptera also well represented. However, chironomids and oli-
gochaetes numerically dominate the benthic macroinvertebrate
community. Larva of the beetle Donacia sp. are phytophagus and
develop within the stems of the macrophyte Sparganium eurycarpum.
Larva of the moth Bellura sp. do the same in Scirpus spp. stems.
Mayflies, Hemiptera and Odonata are found in more dense macro-
phyte stands.
Ichthyoplankton studies in the St. Marys River have identified 39
species. Fish larva collected in the river include larva from
the river, the tributaries and Whitefish Bay. Rainbow smelt
dominate all reaches of the river, spawning in small tributaries
or along rocky shorelines. A marked succession of fish larvae is
apparent and is the result of differential timing of reproduction
by various species in response to environmental stimuli.
ii) Plant Nutrients and Dissolved Gasses
Data on alkalinity, pH, and dissolved oxygen are available for
the St. Marys River from a number of sources. Alkalinity is
typically 40 mg CaC03/L (or 0,8 milliequivalents/L), pH ranges
between 1 and 8, and dissolved oxygen concentration varies sea-
sonally. Dissolved oxygen concentrations throughout the river
are adequate to support all forms of aquatic life and are well
above the 5.0 mg/L U.S.EPA recommended limit.
Total nitrogen (TN) ranges from 0.262 to 0.668 mg/L and averaged
0.413 mg/L during 1982-83. Total phosphorus (TP) averages 13
ug/L, The ratio of TN to TP in the photic zone is a useful index
for separating lakes into N-limited and P-limited categories. If
the TN/TP ratio is greater than 10, algal production is likely to
be phosphorus-limited. The average TN;TP ratio for the St. Marys
River is 32 but varies during the growing season and always ex-
ceeds 10.
iii) Biological Links of the Great Lakes
Many of the fish species in the river undertake seasonal move-
ments from one area to another. For some of these species these
movements are only dispersal into adjoining habitats. However,
for other species, such as Chinook salmon, lake herring and
walleye, these seasonal movements may be characterized as sea-
sonal migration.
The parasitic lamprey is present within the St, Marys rapids.
Twenty percent of the adults captured from Lake Huron tributaries
in 1983 were taken at the powerhouse near the St. Marys rapids.
Sea lamprey spawn in the St. Marys rapids, in tributaries to the
-------
97
river, and probably at lesser rapids located below Lake Nicolet
and Lake George.
There are 172 known species of birds which frequent the St. Marys
River and adjacent riparian areas (15- Waterfowl, colonial wa-
terbirds and some raptors have traditionally been useful as in-
dicators of water quality in the Great Lakes. Of these bird
groups, species which breed, stage or overwinter on the river are
particularly useful. A list of these species is included in
Table VI-1. Duffy et al.(1), provide a detailed list of all the
St. Marys River bird species.
Waterfowl nest along the shorelines and on islands within the St.
Marys River. Census data from the 1980s are not available for
most species that breed along the river. However, weise (6)
estimated a density of 8.9 pairs/km2 of ducks at Munuscong Lake
marshes during breeding season. Common goldeneye, mallard, blue-
winged teal and black ducks nest in munuscong lake marshes while
common mergansers, american coots, Canada geese and occasional
northern pintails and common loons nest in emergent wetlands
adjacent to the river.
Recent data from aerial surveys (6) show the highest absolute
abundance of waterfowl in the river occurs during the fall migra-
tion period when virtually all the waterfowl species listed- in
Table VI-1 occur in the St. Marys River, During the October and
November staging and migration period, the dominant species are
redhead, scaup, ringnecked duck and mallard (6). The most common
species which winter along the St. Marys River are common gold-
eneye, common merganser and mallard (7), and greater and lesser
scaup.
The many islands of the St. Marys River provide nesting sites to
colonial waterbirds (8,9). Herring and ring-billed gulls, common
terns and great blue heron are present during the spring/summer
breeding season. Nesting sites are found throughout the St.
Marys River area, but only the herring gull winters here.
Bald eagles are year-round residents of the St. Marys River area.
There are two active nests used by bald eagles, one on Sugar
Island and one on the Munuscong Lake shoreline. In the winter,
eagles are found in the area surrounding the north end of Sugar
Island. Approximately 15 pairs of osprey breed on the river.
This small but significant number of birds has stabilised since
growing rapidly from 1 breeding pair in 1973.
The mammalian fauna of the St. Marys River area reflects the
region's transitional position at the northern edge of the Great
Lakes hardwood and the southern edge of boreal forests. Some 55
species of mammals inhabit the area, 46 small mammals and 9 large
ones.
-------
98
TABLE VI-1
Waterfowl, colonial waterbirds and raptors which are or could b« used as
important water quality indicators in the St. Marys River.
Scientific
GAVIFORMES
AMSEBIFORMES
SSL
n
WATEHFOWL.
Common Loon
AfiSS
Anna aeut
3treper>
eollorla
nag,,,! Ls
Aythya »f finis
Sueeph^JLa clanftMlA
Mar»ca aniericana
eucullatua
M«r
-------
99
Associated with the river are beaver, muskrat, racoon, river
otter, American water shrews and the northern water shrew. Musk-
rat are the most common and the two species of shrews are abun-
dant* Nonriverine species of shrews, moles, mice, squirrels,
chipmunks and hares abound. Badger and gray fox occasionally
inhabit the area.
Mixed boreal forest and northern Great Lakes forest species of
large mammals include numerous white tail deer, moose, black
bear, bobcat, lynx, coyotes, red fox and gray wolves within the
St. Marys Valley.
Climate
Area winters are cold and snowy, with total snowfall accumulation
ranging from a minimum of 0,82 m to a maximum of 4,54 m. On
average, permanent snow cover begins on November 21, and remains
until April 7th. The 30 year (1950-1980) averages for precipita-
tion (water equivalent) at Sault Ste, Marie, Michigan show an
annual mean average of 0.85 m. Monthly variations are signifi-
cant, with February being the driest month, having a monthly mean
of 4.3 mm, while September is the wetteit with a monthly of
9.9 mm.
The coldest month of the year in the region is January, which
averages -10.4°C, while July is the warmest, averaging 17,5°C,
Air temperatures are moderated throughout the year by the waters
of Lake Superior which seldom freeze. Based on the thirty year
period (1951-1980) the average first day of frost is September
27th and the average last occurrence is May 26th. Most summers
pass without temperatures reaching 32,2°C and the highest temper-
ature of record is 36.7°C, which occurred in 1888.
The water temperatures of the St. Marys River are near 0°C for
four months of the year;; annual temperatures of the headwaters in
Whitefish Bay range from 0°C to 16°C. Ice forms on the St. Marys
River with broad, shallow areas freezing first followed by the
deeper, faster reaches.
2, Environmental Conditions
'"* ","
Water jpualitv
Water quality degradation has resulted from steel and paper mills
and municipal sewage treatment plant discharges. Considerable
progress has, however, been since 1970 by Algoma Steel Cor-
poration Ltd. in reducing ammonia-nitrogen, free cyanide,
phenol discharges; by St. Marys Paper in reducing suspended so-
lids loading; and by the municipal sewage treatment plants in
improving the removal of phosphorus and organic matter.
-------
100
A system of transects across the St. Marys River between White-
fish Bay and the outlets of Lake George and Lake Nicolet has been
used by the Ontario Ministry of the Environment to monitor water
quality (Figure VI-1). Each transect was sampled at several
locations from the Canadian shore to the U.S. shore.- Transects
are numbered by their distance in statute miles upstream (prefix
- SMU) and downstream (prefix-SMD) of the Algoma Steel Terminal
Basins' submerged diffuser outfall. About 20 samples for each
water quality parameter were collected across each transect. The
water quality parameters which were measured in most of the stud-
ies were phenols, cyanide, ammonia, phosphorus, heavy metals
(such as total iron and zinc), and several polynuclear aromatic
hydrocarbons (PAHs). In assessing the significance of contamin-
ant concentrations in the St. Marys River, comparison can be made
with the Ontario Ministry of Environment (OMOE) Provincial Water
Quality Objectives (PWQQ), the Great Lakes Water Quality Agree-
ment (GLWQA) specific objectives and the Michigan Ambient Water
Quality Standards (Table III-2, Chapter III),
i) Cross Channel Variations in Water Quality
In general, contaminants such as phenols, ammonia, cyanide, iron
and zinc, attributable to Algoma Steel discharges, were found
along the Ontario shoreline of the river with no transboundary
pollution in the main channel upstream of transect SMD 2.6.
Typical distribution of contaminants across the main portion of
the river is shown in Figure VT-2. The cross channel variation
at sampling transect SMD 2.6 indicates that the phenol, ammonia,
zinc and iron concentrations increased from the stations located
near the Michigan shoreline to those stations adjacent to the
Ontario shoreline. Data from 1986-87 indicate that transboundary
movement of iron, zinc, and ammonia did not result in exceedences
of water quality standards in Michigan waters. However, the mean
phenols concentration exceeded the GLWQA specific objective of 1
ug/L in Michigan waters.
Contaminants are confined to the Ontario shoreline as far as
Sugar Island. The curving flow at the beginning of the Lake
George channel creates a zone of high velocity towards the Sugar
Island shoreline (10) because of the division of flow between the
Lake Nicolet Channel, west of the island and the Lake St. George,
northeast of the island. Secondary currents enhance the trans-
verse mixing process across the Lake George Channel (11), Thus,
contaminants attributable to upstream industrial discharges which
were confined to the Ontario shoreline of the main portion of the
river will be found along the Sugar Island shoreline of the Lake
George Channel. Additional inputs of contaminants from the Sault
Ste. Marie, Ontario East End Water Pollution Control Plant (WWTP)
to those of upstream industrial discharges result in the persis-
tence of contaminants in the downstream reaches.
-------
SAULT STE. MARIE
ONTARIO
SAULT STE. MARIE
MICHIGAN
0 1 2
km
MAJOR POINT SOURCES
1,2,4 ALGOMA STEEL
ST. MARYS PAPER
WWTP
EAST END WPCP (WWTP)
WEST END WPCP (WWTP)
(offshore discharge)
FIGURE VI-1. Sampling transects and major point source dischargers.
-------
102
rso,
- 1 00,
t-
A
maunstmi
0.0*
0.04.,
9-81
too 400 »oo aoo moo net
tUHMIlB
tat 400 eoo no moo 1200
i
M
B.91
4, -*
Nif i
...A
1W
*00 tOO
1000
0,10 ,
0.01.
.......... -*•
o too 4« 900 too 1000 1100
IX HtTIMS fRQtt U.S
FIGURE VI-2, Distribution of contaminants across St. Marys River at
transect 2,6 (1986-87),
-------
103
Hamdy and LaHaye {12} documented the transboundary pollution of
ammonia in the Lake George Channel downstream from the East End
WWTP, Ammonia concentrations increased, by 20% in Michigan waters
near Sugar Island,
ii) Longitudinal Variations in Water Quality
Bacteria;
In 1986, analyses for fecal caliform (FC), fecal streptococci
(FS) , E. Coll and P. ae rugino a a in the St. Marys River indicated
several problem areas. Geometric mean densities of FC along the
Canadian shoreline were greater than the PWQO (100 organisms/
100ml) at stations near storm sewers and major industrial out-
falls. For example, at two stations (SMD 0.8 and 1,0} immediate-
ly below these outfalls and in the vicinity of of the storm
sewers, the mean FC densities over 3 days were 477 and 428/100ml,
The corresponding densities for E. coli were 311 27I/100ml;
for FS, 24 and 13/100ml; and for PA, 4/100ml. At a further 1.5
km downstream, densities of FC were below the PWQO*
Bacterial densities were also elevated below the outfall of the
Sault Ste, Marie, Ontario East End WWTP in the Lake George Chan-
nel, The densities over 3 days at two stations (SMD 5.0E
and 7.9E3 downstream of this facility were; FC, 184 and
182/lOOml; E. coli, 120 153/lOOml; FS, 24 and 19/100ml; and
PA, 5 and 7/10Oml.
Densities of fecal coliform streptococci along the U.S. shore
were below the respective PWQO at all etations, with the excep-
tion of immediately downstream of the Edison Sault Electric Com-
pany Canal (SMD 1.2). Compliance with Michigan's fecal coliform
standard (200 cells/100ml) is determined on the basis of the
geometric mean of any 5 consecutive samples taken over not more
than a 30 day period. Because only 3 samples were collected from
this site, comparison with Michigan water quality standards is
not possible. However, the 3-day geometric means of E. coli,
fecal coliform, fecal streptococci P.. aeruginosa were 1,149
organisms, 2,2SO organisms, 233 organisms, and 20 organisms,
respectively, per 100ml. The sources may be combined sewer over-
flows that discharge to the Edison Power Canal (see urban runoff
section).
Phenols:
The redevelopment of the Great Lakes Power Limited hydroelectric
generating station in 1982 resulted in changes in the distribu-
tion of river flow at the regulating works (Figure VI-3), The
portion of total river flow along the Ontario shoreline increased
from 21% to over 40% of the total river flow. This increase in
flow is in part responsible for the reduction of river concen-
trations of phenols, cyanide and ammonia (12).
-------
ONTARIO
SI. Mary$ Mis
Canal
MICHIGAN
o
FIGURE ¥1-3. Average flow distribution (%) at the St. Marys River Rapids
(2.2 x ID3 m3/s post 1982).
-------
105
The year-to-year variations of total phenol concentrations meas-
ured at various distances downstream from the Algoma Steel dis-
charges are shown in Figure VI-4. There is a downward trend of
phenol levels over the years. Mean phenol levels 300 m down-
stream of the Algonia Terminal Basins outfall (at river range SMD
0.2) declined from 50 ug/L in 1973 to 15 ug/L in 1980 and to 1.2
ug/L in 1986.
In 1986, all stations downstream of Algoma Steel discharges had
phenol levels approaching the PWQO and Great lakes Water Quality
Agreement specific objective of 1 ug/L. However, phenols ex-
ceeded the objective in the Algoma Steel Corp. Slip (3.6 ug/L)
and at the mouth of the Slip (3.4 ug/L) in 1986, The Algoma Slip
is a ship loading and off-loading facility located upstream of
the Terminal Basins and power canal.
In 1986-87, average phenols along the Michigan shoreline were
below the PWQO and the GLWQA specific objective of 1 ug/L.
Ammonia:
The ammonia concentration distribution along the Canadian shore-
line downstream of the Algoma Steel discharge, is illustrated in
Figure VI-5. The 1916 levels along the Canadian shore exhibited
significant decreases as compared to previous years. The calcu-
lated unionized ammonia concentrations were below the PWQO and
GLWQA specific objectives of 0,02 mg/L,
The ammonia concentration increased downstream of the Sault Ste,
Marie East End WWTP (see Figure VI-4, 5,0). The impact of the
WWTP effluent is localized, as concentrations at the Lake George
Channel outlet were the as those observed at the beginning
of the Lake George Channel {0,046 mg/L) upstream of this facili-
ty.
Cyanide;
The distribution of free cyanide along the Canadian shore in 1974
and 1980 indicated peak concentrations 300 m downstream from the
Algoma Steel discharge and uniformly low concentrations further
downstream (Figure VI-6), The 1986 levels indicate a decline
from the previous years, and uniformly low concentrations from
upstream to downstream. All levels were in compliance with the
PWQO of 0.005 mg/L and the U.S.EPA chronic of 0.0052 mg/L,
Heavy Metals:
During 1986-87 the concentrations of total iron in the St. Marys
River ranged between 0.018 and 0.69 mg/L and no distinct long-
itudinal variations were noted. Just downstream of the Terminal
Basin's outfall (SMD 0,2), the average concentration was 0.06
mg/L with a maximum of 0.69 mg/L, This maximum was one
-------
180
106
3COM DOWNSTREAM OF ALGOMA STEEL DISCHARGE (SMD 0,2)
60
to
_J
o
z
LJ
I
O.
01
•3
V)
_l
O
z
kJ
I
0.
1970 1972 t974 1976 1978 1980 1986
50
40
38
20
10
1500M DOWNSTREAM OF ALGOMA STEEL DISCHARGE (SMD 12)
1970 1972 1974 1976 1978 1980 1986
3KM OOWNSTEAM OP ALGOMA STEEL DISCHARGE (SMO 20)
1948 1970
1974
1978
1986
FIGURE Vl-4. Phenol concentrations in the St. Marys River at various distances
downstream of the Algoma Steel discharge along the Canadian
shoreline.
-------
0.000
0.8OO
_j
"^ 0.700
a
s
*^*"
CONCENTRATION
p p o p p
(0 W * 01 03
o o o o a
o o o o o
0.1 OO
RANQCS
1
f
' . - . 1474 (APR MINF AHA )
1980 (MAY, JULY, AUG. .OCT.,
NOV.)
j , 19 06 (JUNE )
^ \ +x
^
\
\ ^—~ 4. --4--- »
5O>o ' *t * R "* <* ^ ttH
••'dSo eJ*-"5 •> « •» <• •
1 *5 2 3 4 5 « '
l->
o
-j
*
M
DISTANCE FROM HEAD RANGE ( SMU 1.S ) IN MILES
FIGURE VI-5. Ammonia distribution and yearly trends along the Canadian
shore.
-------
0.18
^0.14
"""
|0. 12
<
BE 0.10
Z
in
0 0.08
0
0
o.oa
0.04
O.O2
; -\
t 1874 ( JUNE, *UO. )
i - - iQAn ( u A v mt v AJ in
r i --_— — _ I wCMUP \ MAT | *IMi-« * **Uyi»||
1 OCT.t MOV* 1
1OHF ( JtINF )
1 J 1 9 Vlf % Wl***** r
m
1
1
1
\
I
1
\ — — 3^" *~ ~-
-fc 4-— " """' — ~-~~_
.
•4-' * j .
^ jr. "• " ' * i#*" I*
,_.
0
oo
HAMOiS
DISTANCE FROM HEAD RANGE ( SMU 18 ) IN MILES
FIGURE VI-6. Cyanide distribution and yearly trends along the Canadian
shore.
-------
109
exceedence of the water quality objectives in 40 samples across
the transect. In the Algoma Slip, iron exceeded the PWQO and
GLWQA specific objective of 0.3 mg/L (average 0,445 mg/L with a
maximum of 1.0 mg/L). All samples met the U.S.EPA chronic AWQC
of 1 mg/L for chronic toxicity. Iron levels along the Michigan
shoreline in 1986/87 ranged between .008 mg/L to 0.087 mg/L.
The elevated iron levels during the period 1970-74 decreased to
levels in the range of 0.11 - 0.15 mg/L during the period 1976-
1980 (10) .
Total zinc levels in the St. Marys River along the Ontario and
Michigan shorelines in 1986-87 displayed no distinctive longitud-
inal variations. Concentrations ranged between 0,001 and 0.009
mg/L» a decrease from. 1980, when concentrations of 0,01 mg/L were
prevalent. All these concentrations are below relevant water
quality standards or guidelines.
Phosphorus:
In 1986-87, phosphorus levels along the Canadian shore ranged
from 0.002 to 0.051 mg/L from 0.005 to 0,014 mg/L along the
Michigan shore. The highest level of phosphorus (0.051 mg/L3
along the Canadian shore noted just downstream of the Ontario
Sault Ste. Marie East End WWTP (SMD 5.0), No elevated levels of
phosphorus {relative to upstream levels) were noted downstream of
the Sault Ste. Marie, Michigan waste water treatment plant
(WWTP) , Phosphorus levels were slightly higher along the U.S.
and Canadian shores at Pointe Aux Pins {SMU 5.0) in 1986. The
levels were 0.012 and 0.014 mg/L, respectively. However, all
phosphorus levels in the St. Marys River the PWQO of 0.03
mg/L with the exception of immediately downstream of the East End
WWTP.
Polynuclear Aromatic Hydrocarbons (PAHs);
With the exception of polynuclear aromatic hydrocarbons (PAHs),
trace organic contaminants such as chlorinated benzene halo-
genated volatiles are not generally found in the St. Marys River,
The environmental significance of PAHs in the St. Marys River
cannot be determined due to the absence of surface and drinking
water criteria Cor PAH compounds with the exception of the inter-
im benzo(a)pyrene Ontario drinking water Maximum Acceptable Con-
centration (MAC) of 10 ng/L, For the maximum protection of human
health from the potential carcinogenic effects of PAHs due to
ingestion of contaminated aquatic organisms which may result in
an incremental increase of cancer risk of 1Q~6 over a 70 year
lifetime* a criterion of 31 ng/L for total PAHs was developed by
the U.S.EPA (13). This is used as a yardstick to assess the
significance of levels found in the St. Marys River.
-------
110
Worldwide information on PAHs (14) indicates concentrations of
benzo(a)pyrene range from approximately 0.1 to 100 ng/L. In Lake
Erie, near Buffalo, Bass and Saxene (15) found 0.3 ng/L benzo(a)-
pyrene and 4.7ng/L total PAHs. Williams et al. (16) extracted
large volumes of municipal treated drinking water taken from 12
plants using Great Lakes water. The winter and summer concentra-
tions (+/- 1 standard deviation) respectively were relatively
high for pyrene (11.2 +/-20.0 and 3.9 +/- 10,2 ng/L) and fluoran-
thene (9.2 +/- 12.0 and 10.6 +/- 25.0 ng/L). Eadie (17) found 15
(+/- 9} ng/L of fluroanthene and 14 (•*•/- 6) ng/L of both pyrene
and benzo(a)pyrene in filtered offshore waters of southern Lake
Michigan. The concentration of these compounds on suspended
particles was 2-4 ug/g. At a concentration of I mg/L of total
suspended matter, greater than 75% of these PAHs were in the dis-
solved phase.
In 1985, large volume sampling was used to determine PAHs as-
sociated with the aqueous phase in the St. Marys river, focusing
on the industrial and municipal areas of Sault Ste. Marie,
Ontario (Table VT-2 and Figure VI-7). Total PAHs in samples
taken from Leigh Bay (station #3) and off the Algoma Slag Site
(station #4) were similar to the upstream background level of 4.0
ng/L (station #2).
Total PAH concentration increased downstream, reaching a peak
concentration of 31.8 ng/L in the Algoma Slip. Benzo(a)-
anthracene, which was absent in the upstream samples, was found
at levels of 0.23 ng/L at Station 17 and 0.38 ng/L at Station #5.
Benzo(a)pyrene was found only at station #5 (0.08 ng/L). Elevat-
ed total PAHs, relative to the upstream site, persisted down-
stream (station #10) at least 1km from the Terminal Basins' dis-
charge. The PAH levels along the Michigan shore (3.2 - 3.6 ng/L)
were similar to background concentrations (4.0 ng/L) indicating
no transboundary pollution.
In order to provide insight into the partitioning of PAHs, con-
centrations in the whole water samples as well as those associat-
ed with the suspended particulates were determined as part of a
centrifuge sampling program in 1986. Twelve stations along the
St. Marys River from Leigh Bay to immediately downstream of the
Sault Ste. Marie East End WWTP were sampled (Figure VT-8).
Oliver (18) found a significant correlation between octonol/water
(Kow) and organic carbon corrected partition coefficients (Koc).
Utilizing total organic carbon levels (Figure VI-9)» suspended
particulate levels (Figure ¥1-10), PAHs measured on suspended
particulates (Table VI-3), and appropriate partition coefficients
and assuming that equilibrium had been reached between the PAHs
in the aqueous and particulate phases, estimates of both aqueous
and whole water PAH concentrations were derived (Tables VT-4 and
VT-5, respectively).
-------
TABLE VI-2
PAHs associated with the aqueous phase from APLE sampling in the St. Marys River (1'JBS).
STATION
PAHa Ing/L)
Phenanthrene
Anthracene
Fluoranthene
Pyrene
Benzo( a ) anthracene
Chrysene
Benzo( b \ f luoranthene
Perylene
Benzo( k ) f luoranthene
Benzo ( a Jpyrene
Benzo [ g , h , i )perylene
Coronene
TOTAL PAHs
'I
1.4B
0.1B
0,83
0,28
-
~
0.54
0.49
-
-
0.09
0,02
3,iS
3
1.
0,
1,
0.
0.
0,
0.
0.
o.
4.
90
•IB
33
40
-
2
OS
096
-
-
18
02
48
4
1,04
0,06
0.91
0,15
-
-
0.04
0,07
-
-
o.ia
0.02
2.4?
5
7,
0.
10
1.
0.
0.
0,
0.
0.
0.
'11
80
ay
.00
30
38
34
34
-
20
08
-
29
.31
f «
15,90 13,58
1.70 1.86
11.64 8,73
1.59 1.57
0.23
0.33
0,29
-
-
_
0.12
0.12 O.Oi
31.8 25. 9
10
3,45
0,36
3.24
0.54
-
-
0.11
-
0.07
0,02
-
O.04
?.«3
12
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
13
1.61
0,22
1.33
0.32
-
-
o.oe
-
0.03
0.02
0.05
0.02
3.56
14
i.ui
0,15
0.94
0,15
-
-
0,05
-
0,03
-
O.03
0.02
3,19
-------
31,8
25.9
ng/L
FIGURE VI-7. Total PAHs associated with the aqueous phase from APLE
sampling (1985).
-------
IITTlt LAKE
GfORCE
500
ng/g dry weight
FIGURE VI-8. Total PAHs associated with centrifuged particulate matter (1986),
-------
290
LITTLE LAKf
GEORGE
FIGURE VI-9. Total organic carbon levels in St. Marys River (1986).
-------
35,4
LITTLE LAKE
GEOflUf
I/I
FIGURE VI-10. Suspended paniculate levels in the St. Marys River (1986),
-------
TABLK VI-S
PAHs associated tilth the centrifuge*) matter in the St. Marys Biv*i>
STATION*
VAtts J ng/g Dry Weight)
HDL
1
ng/f i
Naphthalene
Ac^napht.hv) ene
Aeenaphthene
M H Fluarene
fhenanthrene.
Ant hraeene
1-' 1 ii £> f 14 n I. he ne
Pyr<*ne
€hr¥sene
fienzof s ) anthracene
B«*ns£*l a &pvrene
Benzol kj and Benzol b Jf luoranthene
Dt henzoj a , h (anthracene
Benzol g, h,t Iperylene
Indenol 1,2, 3-e,dlpyrene
TOTAL PAHa
SO
50
50
60
4(>
41)
4()
40
50
5O
5O
50
50
50
SO
ND
ND
ND
ND
TR
TH
TR
TR
TR
TR
TR
TR
2
T
NB
ND
ND
NO
NB
ND
ND
TR
ND
ND
ND
ND
ND
ND
ND
TR
4
V
ND
ND
ND
ND
TR
ND
498
479
T.ass
i, as?
593
1,144
ND
TR
ND
12,046
B
ND
ND
ND
ND
ias
ND
ND
290
233
2B«
ND
330
ND
84
TH
1,412
ft
B
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
NO
ND
ND
2
1
U
2
7
6
1
t
3
&
55
fi
B
,834
623
,oat»
aua
,37S
,444
,UK7
,310
,266
, b84
,8B2
,B1S
33B
B22
731
, 6Hti
H
T
au
NO
TR
TR
1U8
120
las
151
78
109
61
122
ND
TR
TR
1,020
T
I.OB4
ND
ND
ND
509
Nil
i.ua
Bltt
Bin
BUS
465
1 ,002
ND
ND
ND
b, 5(il
a
a
801
ND
ND
ND
718
ND
1,377
tiay
B7S
1 ,258
660
1,350
ND
TR
TR
7,822
f
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
to
i
ND
ND
ND
ND
ND
ND
1, 35B
1 ,262
TR
1 ,036
ND
1,419
ND
ND
ND
5,07*
It
T
1 ,1)48
MD
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
I.94H
B
B40
ND
ND
ND
44?
120
95?
t>90
538
BBC
535
933
ND
NO
ND
5,&40
12
B
2?B
ND
ND
ND
ND
ND
624
4K9
3fl2
4«5
2B3
4H6
ND
ND
ND
2,877
14
B
ND
ND
ND
ND
ND
ND
111
8?
ND
ND
ND
ND
ND
ND
ND
198
IS
T
104
ND
ND
ND
lau
ND
335
295
264
408
NO
511
ND
NO
ND
2,186
B
ND
ND
ND
ND
ND
ND
NO
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND - Not Detected, TR - Trace
* T - Sftmpl £ f&k£*ft I , & a h**l^w Ain*f~
B — S a mp i** t.aken 0,5 m ct ft hfi* t-1" £*H
-------
TABLE VI-4
Estimated concentrations of PAHa associated with the aqueous phase in the St. Msrya River (1SB6),
STATION"
PAHa
B
357.79
NA
NA
NA
Z4.9O
HA
8.90
4 . 35
2,24
o.&s
0,27
NA
NA
NA
399.23
T
NA
HA
NA
NA
NA
NA
NA
NA
HA
NA
NA
NA
NA
NA
NA
10
B
NA
NA
NA
NA
NA
NA
6.BI
7.98
1 ,K4
NA
O.28
NA
NA
!«...
11
T
870, 14
NA
NA
NA
NA
NA
NA
NA
NA
HA
HA
NA
NA
HA
B70.J4
B
2B5.B8
NA
NA
NA
15.50
4.26
4.80
4.3S
1 -21
0,49
0.19
NA
NA
NA
an. MB
12
B
124. 18
NA
NA
NA
NA
NA
3.13
2.96
O.HS
0.26
0.10
NA
NA
NA
132-27
14
NA
NA
NA
NA
NA
NA
0.
0.
NA
NA
NA
NA
NA
NA
J .1
15
T
82.19
NA
NA
NA
NA
NA
53 1 .fit)
55 l.Kii
(» , 7 :t
NA
0.10
NA
NA
NA
1 87.15
B
NA
NA
MA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
ND - Not Detected.
TR - Trnoe.
NA - Not upplicahle aft PAHs were not detected on the centrifuged part i dt J nfc*? matter (Table VT-CII.
* T - Samples taken 1.5 m htrlow surface.
B - Sflmpleg tnken 0.5 m o!T bottom.
-------
TAhLE VI -ft
£sti*nted concentrations of PAHs in whole «ster phase of the Si. M«rys River I iyntil.
STATION
PAHs (ng/L)
Naphthalene
Aeenaphthylene
Acenaphthehe
9 H Klusrene
Phe na ft t h r e ne
Anthracene
Fluorantheiie
Pyrene
Chrysene
Benzol a lanthraeene
Benzol a Ipy rene
I
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
Bunzolkl 4 Benzol fa If luoranthene NA
Di ben 20! & , h lsiȣ hracene
Benzol g >h, i iperylene
1 nde no 1 1 , 2 - 3 - e , d J py rene
TOT At PAH»
T - Saaple taken 1,6 •
B - S&iaple taken 0.5 m
NA
NA
HA
NA
below surface
off hat ton
2
T
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
4
T
NA
NA
NA
NA
NA
NA
3.04
3.55
2«,8U
3.85
i.iy
1.4H
NA
NA
NA
»..>
B
KA
NA
NA
NA
fs.76
NA
NA
2.15
0.78
0.82
NA
0.43
NA
0. 10
NA
11. U4
S
b
NA 1
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
b
,414.
SB.
»y .
33,
5«7,
173,
2B5.
283.
273.
285,
140.
207.
12.
2S.
O,
»,..!
43
SIS
24
71
15
23
5M
la
4M
BH
Jt)
15
00
IS
02
...
H
T
»
T
B
38.33 4B3.14 301.72
HA
KA
NA
4.34
5.15
2,10
2,07
0.75
1.00
O.&fi
0,93
KA
NA
NA
83. 83
NA
NA
NA
2 1 , 37
NA
13, H9
12,110
5.96
7.S4
3.U?
7. HI
NA
NA
NA
bit). J8
NA
NA
NA
30.21
NA
17, oa
S.45
9.44
11. SS
S.40
10.211
NA
NA
NA
4ST.12
10
T 8
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
11
T
NA B75.2U
NA
NA
HA
HA
NA
IB. 72
17.18
HA
tt.40
NA
10.84
NA
NA
NA
5J.B4
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
875,20
B
zsi.afi
KA
NA
NA
1(1.88
4.63
7.76
6.49
2.B7
1.32
2,15
3. OB
NA
NA
NA
33&.04
B
124.21
NA
NA
NA
NA
NA
3,19
a. 01
0.85
0,87
0.2M
0.15
NA
NA
NA
132. S7
14
B
16
T
NA 82. as
NA
NA
NA
NA
NA
0,77
0,71
NA
NA
KA
HA
NA
NA
NA
1...
NA
NA
NA
NA
HA
2.BU
2.S2
1 .54
1.54
NA
I.M4
NA
NA
NA
94,32
B
NA
MA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
NA
ND - Not detected
TR - Trace
NA - Not applicable as PAHs were not detected on the centrifuged part leu late natter I Table VI-31
00
-------
119
Upstream samples {station #1 and #2} exhibited trace amounts of
PAHs on the suspended particulates implying that PAHs may only be
in the dissolved phase as found in 1985. In the vicinity of the
Algoma Slag Site (station #4} the total PAHs associated with the
suspended particulate amounted to 12,046 ng/g and 1,412 ng/g at
1.5m below the surface and 0.5m off the bottom, respectively,
These concentrations correspond to an aqueous phase having 27
ng/L and 9 ng/L in the water column, resulting in a whole water
concentration of 40 ng/L. This level is above the criterion of
31 ng/L for total PAHs developed by U.S.EPA for the ingestion of
aquatic organisms.
In a near-bottom sample from the Algoma Slip, in the vicinity of
the 30" and 60" blast furnace sewer outfalls and downstream of
East Davignon and Bennett Creeks, the total PAH concentration
associated with the suspended particulate phase was 55,686 ng/g.
This level, the highest observed in the study area, corresponded
to an estimated whole water concentration of approximately 3,900
ng/L, greatly exceeding the U.S.EPA guideline for total PAHs of
31 ng/L. This high concentration may be related to both ongoing
discharges as well as past losses, such as spills of coal tar.
At this location, measured concentrations for 12 PAH compounds in
whole water (phenanthrene, anthracene, fluoranthene, pyrene,
benzo(a)anthracene, chrysene, benzo{b)fluoranthene, benzo(k)-
fluoranthene, benzo(a)pyrene, benzo(g,h,i)perylene, dibenzo-
(a,h)anthracene, and indeno(l,2,3,c,d)pyrene) ranged from 504
ng/L to 2,520 ng/L. The upper range of these measured concentra-
tions is similar to the concentrations estimated from the levels
associated with suspended particulates for the 12 PAHs (2,258
ng/L). The estimated and measured concentration of benzo(a)-
pyrene in the whole water phase in the Algoma Slip locations
exceed the interim Ontario drinking water MAC of 10 ng/L, There
are no drinking water intakes downstream from the industrial
discharges.
Immediately downstream of the Terminal Basins' discharge (station
$9), total PAH concentrations associated with the suspended par-
ticulates at 1.5 m below the surface (6,561 ng/g) and 0.5 m off
the bottom (7,822 ng/g) were similar due to vertical mixing. The
estimated total PAH concentrations (naphthalene, phenanthrene,
fluoranthene, pyrene, chrysene, benzo(a)pyrene, benzo(b,k)fluor-
anthene, and benzo(a)anthracene) associated with the aqueous
phase were 508 ng/L and 399 ng/L in the samples taken at the
surface and 0.5 m off bottom, respectively. The predicted total
concentration for the 12 PAH compounds in the aqueous phase of
surface water in 1986 was 33 ng/L. This was similar to the mea-
sured PAH concentration (same 12 compounds at station #6) of 26
ng/L in 1985. The estimated whole water total PAH concentrations
were 556 ng/L and 457 ng/L in samples taken at 1.5 m below the
surface and 0.5 m off the bottom, respectively. Both of these
estimated levels exceed the U.S.EPA AWQC Human Health Criteria
-------
120
(fish consumption only) for total PAHs of 31 ng/L, The estimated
concentration of benzo(a)pyrene associated with the whole water
phase averaged 5 ng/L, lower than the interim Ontario MAC of 10
ng/L.
At station #11, located in a sheltered embayment, the total PAHs
associated with the centrifuged particulate matter were much
greater at the bottom than at the surface, reflecting the char-
acteristics of depositional zone. Compounds attributable to
industrial discharges were found in the sample taken 0,5 m off
the bottom. The estimated concentration of total PAHS in the
aqueous and whole water phases for this sample were 318 ng/L and
335 ng/L, respectively. This level greatly exceeds the U.S.EPA
AWQC Human Health Criteria (for fish consumption) for total PAHs
of 31 ng/L.
Generally, these elevated PAH levels associated with the suspend-
ed particulates persisted downstream of the Terminal Basin's dis-
charge as far as the Sault Ste. Marie East End WWTP in Lake
George Channel (Figure VI-8). At station #15, downstream from
the Sault Ste. Marie East End WWTP the concentration of total
PAHs associated with the suspended particulate matter at the
surface was 2,186 ng/L. PAHs at 0.5 m off the bottom were not
detected. This reflects the buoyant nature of the WWTP effluent.
The estimated total PAHs associated with the whole water phase
was 94 ng/L.
Along the U.S. shoreline, downstream of the Edison Sault Electric
Company Canal, the concentration of total PAHs associated with
the suspended particulates was 198 ng/g. The estimated concen-
tration of total PAHs in the aqueous and whole water phases was
1.11 ng/L and 1.48 ng/L, respectively, considerably lower than
levels identified along the Canadian shoreline.
Biota
The OMOE and the U.S. Fish and Wildlife Service (U.S.FWS) have
monitored biota from various trophic levels in the St. Marys
River since the early 1970s with the aim of defining the health
of the river ecosystem. The St. Marys River Biota Workgroup
Report synthesizes the published information together with the
unpublished results of investigations conducted as part of the
UGLCC Study (19,20,21).
i) Phytoplankton
Chlorophyll a_ showed very similar concentrations in the upstream
and downstream reaches of the St. Marys River with a mean value
of 0.78 mg/m^ (4). Similarly, primary productivity studies using
Carbon 14 techniques showed relatively low carbon assimilation,
ranging from 5.5 to 57.9 mg C/rn^/d. Based on chlorophyll a_ con-
-------
121
eentrationSi primary productivity and. species composition (mainly
diatoms) Listen et al. (4) concluded that the phytoplanton com-
munity of the river is similar to that of Lake Superior.
ii) Macrophytes and Macroalgae
Production;
Unpublished estimates of total primary production for the St.
Marys River by Duffy et al. (1) show the contribution of
emergent plants (4,710 tonnes/yr), is about 20 times that of
phytoplankton and periphyton combined but only about 3 times that
contributed by submerged plants. Thus, the emergent and sub-
merged plant communities are the major primary producers in the
St. Marys River (1,20).
Biomass Drift;
Observations of plant detritus drift in the St. Marys River
(1,21,22) indicated a general pattern. In the spring a pulse of
plant detritus from the emergent wetlands and, from the submerged
plant communities further offshore is initially retained and
utilized in-situ. Eventually, a portion of the detritus is dis-
persed to offshore and downstream areas by currents and wave
action*
The living component of plant drift constitutes a small fraction
of total plant biomass drift as compared to the detritus com-
ponent. The total living plant biomass entering the St. Marys
River from Whitefish Bay in April to October 1986 was approxi-
mately 1,555 tonnes wet weight and 77.7 tonnes ash-free dry
weight. During the time the combined total leaving the
river through the St. Joseph Channel below Lake George and the
outlet of Lake Munuscong 10,362 tonnes wet 518 tonnes
ash-free dry weight (233.
The drift of detritus and living plant material may be an import-
ant mechanism for the redistribution of food resources within the
river. However, the drift of plant material containing contamin-
ants may also facilitate the dispersal of contaminants within the
river and their transport from the river into Lake Huron,
ill) Benthie Invertebrates
The St. Marys River supports a diverse benthic invertebrate com-
munity composed of more than 300 taxa (1). Chironomidae and
Oligochaeta are the most numerically abundant. The Ephemeroptera
and particularly the burrowing mayflies (Hexagenia and Ephemera)
are also abundant, and they may be the most important benthic
invertebrates in the river because of their central role in tro-
phic interactions, The Chironomidae are more strongly repre-
sented numerically in the upper and middle reaches of the river,
-------
122
while the Qligochaeta and Ephemeroptera are more abundant in the
lower river (2,3,6,21,24). Overall, the abundance of benthic
invertebrate is highest in the middle reaches of the river, and
slightly higher near the head of the river near whitefish Bay
than in the lower reach near Lake Huron (1).
The benthic macroinvertebrate community of the St. Marys Rapids
and Lake Nice-let Rapids (5,25) is typical of those found else-
where in rapids or rocky streams and differs substantially from
communities found in other portions of the river (1) .
The navigation channels in the river are not intensively colon-
ized by benthic invertebrates (1,2,4). Only Oligochaeta and
Chironoitiidae are common in this habitat and both taxa generally
occur only in low densities. Vessel induced turbulence and the
removal of soft substrates by dredging are probably responsible
for the poor benthic invertebrate community typically observed in
the navigation channels.
Studies of impairment in the benthic communities in the St. Marys
River were conducted in 1967 (26), 1973 (10), 1974 and 1975 (27),
1983 (28), and 1985 (29,30). Generally, zones with impaired
benthic communities corresponded with the occurrence of visible
oil and elevated levels of other contaminants in the sediment.
Specifically, an inverse relationship between the abundance of
Hexagenia nymphs and visible oil in the substrate was noted.
Impact zones were restricted to the Ontario portion of the St.
Marys River and were found immediately downstream of the dis-
charges of Algoma Steel, St. Marys Paper, and the East End WWTP
and in the depositional zones of Lake George. In Michigan waters
and all portions of the river upstream of point source dis-
charges, benthic communities were unimpaired. No impacts from
transboundary transport of contaminants were apparent along the
Michigan shoreline.
To better determine zones of impact, cluster analysis was per-
formed on the 1985 data using various physical, chemical, and
biological components of the benthic system (29). Seven major
clusters were distinguished and four pollution impairment zones
were identified.
1. SEVERE:
This zone is found in the Algoma Slip area and in embayments
downstream from the industrial and municipal discharges
along the Ontario shoreline of the river. This zone is
characterized by extreme tubificid dominance (i.e., L.
hoffmeisteri and immatures without capilliform chaetae),
pollution tolerant chironomids, low numbers of taxa and high
total densities, or communities with either very low total
densities and low numbers of taxa, and/or high densities of
nematodes with few other taxa.
-------
123
2. MODERATE:
This zone, mainly confined to the Ontario shoreline, is
approximately 500 m wide, extending 4 km downstream from the
industrial and municipal discharges. Tubifieid_dominance
with high densities of nematodes and facultative chirono-
mids, absence of polychaete worms, reduced numbers of taxa
and high total densities are the major characteristics of
this zone.
3. SLIGHT:
Some recovery was apparent with increased distance from
industrial and municipal discharges; however, complete re-
covery was not apparent until the lower section of Lake
George. Nematode and polychaete dominate with moderate
densities of tubificids and some nontolerant groups are
present.
4, UNIMPAIRED:
This zone was found in the upper reaches of the river and
along the Michigan side of the river. Communities tended
towards chironomid dominance, with several nontolerant
groups (e.g. Ephemeropterans and Trichopterans) present,
together with low tubificid densities and high numbers of
taxa.
The macroinvertebrate community impairment zones are summarized
in Table VI-6 and illustrated in Figure VI-11. It is important
to realize, however, that areas of the St. Marys River defined as
"unimpaired" by benthic community structure analysis may never-
theless be unsuitable or "impaired" habitats to Hexagenia when
oil is present even in a physically suitable substrate. This
organism has a central role in the food webs.
Over the years only slight improvements have been noted in the
benthic community in the Ontario waters of the St. Marys River.
Sediment Quality-Benthic Macroinvertebrate Contamination:
Persaud et al. (31) examined contaminant concentrations in ben-
thic invertebrates and in corresponding sediments at four sta-
tions, located downstream of the discharges of Algoina Steel, St.
Marys Paper and the East End WWTP (Figure VI-12).
The <63um size fraction of the sediments includes the very fine
sand, silt and clay components. This size range is normally
ingested by benthic invertebrates (32). Most chemical contam-
inants were associated with this fraction. Sequential chemical
extractions on the <63um sediment identified six geochemical
phases.
-------
TAiLl Vl-i
Characteristic* of benthie comnunity mortem in the St. Marys River 11 BBS I.
Common Taxa
Mean No. Taxa
Mean Total
Density INo/mZ}
Substrate
Water Bepth(Bj
Macrophytes
Visible Oil
Current
Unimpaired
Imniat.fubif icids
w/o chatae
*N«»atoda
Prog 1 ad 1 us
Bgzzia
Chtronomidae
BsiyBSii turn
ChironoBKja
A™, «1 1 C 3 la. A i m&SA
Hydracarina
Va Ivata sincera
27-40
56,000-201,000
Variable Sllty-
Coarse Sand
1-13. I
Variable
Absent-Very Strong
None-Moderate
ZONES
Slight
*I««i«t,Tubifieid«
w/o chaetae
*Wematoda
•Manayunkia
Hemertea
Stvlodri lua
PisidiuiB
I mm at .Tub if icids
with chaetae
23
192,000
Coarse Sand
w or w/o Silt
2,5-14
Absent or Sparse
Absent-Very Strong
Slight-Moderate
Moderate Severe
* lama t.Tubi fields *Immat> Tub! field*
w/o chaetae w/o chaetae
•Nenatoda *Nenatoda
Najs var iabilia »ChirQnomidBe
15 12
288,000 71,000
Organic Silt Silt
1-18 1.5-8.5
Variable Usually Absent
Slight-Very Strong Absent-Very
Strong
None None-Strong
* Dominant Taxa
-------
6a
Sault Ste. Marie
Ontario
1,2,3 Algomi Sin.il
4 St Mary* p»p«r
5.6a,6b WWTPs
Sault Ste. Marie
Michigan
to
in
FIGURE VI-11. Distribution and zones of impairment of benthic fauna (1985).
-------
* Station Location
NCB-No Contaminant
Bioconcent ration
FIGURE VI-12. St. Marys River station locations and parameters showing biocon-
centration factors greater than 1.0.
-------
127
In the St. Marys River, 77% of the copper, 96% of the cadmium,
94% of the lead, 84% of the zinc, 23% of the manganese, and 12%
of the iron was in potentially available forms. With the excep-
tion of Fe and Mn, most of the potentially available metals were
associated with the organic/sulphide fraction. The largest
fraction of Pe and Mn was held in the residual phase.
Table ¥1-7 shows the levels of metals in benthic tissue and sedi-
ment and the ratio of the tissue/sediment values referred to as
bioconcentration factors. The sediment metal values used in
these tables were the "available" metal concentrations obtained
from the sequential extraction data, Bioconcentrations factors
of copper, zinc and mercury were greater than one only at a
station located in Little Lake George (station #45) which had the
lowest bulk sediment contaminant levels. The uptake of these
three metals was found to be inversely proportional to the or-
ganic matter content of sediments, especially the solvent extrac-
tables (oil and grease). In areas with high levels of organic
matter, uptake was very low, despite the fact that the concentra-
tions of metals were generally at their highest in the sediment.
Also, copper and zinc concentrations in organisms appeared to be
related to specific geochemical fractions.
These data show that contaminated sediments can be a source of
contaminants to benthic organisms. The high levels of contamina-
tion and the concentration of certain contaminants in the tissue
of these organisms raises concerns related to the potential for
transfer of these contaminants to higher organisms that feed on
these species. Toxic effects could also result in the complete
elimination of benthic organisms or reduction in species diver-
sity and individuals to a few tolerant organisms.
Recently, increased emphasis has been placed on determining the
concentrations, distribution and availability to biota of polynu-
clear aromatic hydrocarbons {PAHs) in river water. In 1985 un-
contaminated clams were exposed in cages along the nearshore of
the St. Marys River for three weeks. Clams placed in areas down-
stream from the Canadian discharges accumulated significantly
higher levels of PAHs than clams exposed at the upstream loca-
tions (Figure vi-13). PAHs accumulated in clams exposed along
the U.S. shoreline, but generally at lower levels than along the
Canadian shoreline. Caged clams introduced in the Algoma Steel
Slip accumulated the highest levels of total PAHs. The degree of
accumulation of compounds in decreasing order of magnitude in the
Slip were: phenanthrene; fluoranthene; pyrene; acenaphthene;
fluorene; naphthalene; anthracene; chrysene/benzo(a)anthracene;
and benzo(a)pyrene. Benzo(a)pyrene in clams was well below the
proposed IJC objective (33) of 1 ug/g for organisms serving as a
food source for fish.(34)
-------
Concentrations of metals in gedisent 4PP& dry Me
bioeoneentration factors In the St. M«rys River,
TABLE Vl-T
and in benthic tissue I pj>ia drv weight, gut corrected J and corresponding
SAHPLINQ STATION
45
46
4T
48
S
23.
IBB.
89,
188,
SAMPLINO STATION
45
46
41
48
S =
*
**
S
6,272.
15,043.
a, 949,
13,280.
Sediment, BT = Benthic T
Exeeedes GMGE guidelines
Negative values are the
BT
1 22, i
V* 24,0
4* 11,4
1* 11,0
IKON
BT
3 1,030,2
8 258,2
2 Tl&.l
3 104,2
COPPER
BCF
1,0
0.1
0.1
0.1
BCF
0,2
0.0
0.1
0.0
S
118.7*
73O, 3*
493. B*
841.3*
S
64,9
197.1
12B.O
362.4
BT
131,3
115,8
107.5
110.1
HANGANKSE
BT
39. B
12.0
e.s
~1 .2**
issue » BCF ~ Bioconcentration Factor > NA
for the open water disposal of dredged
result of extremely low levels of Mn in
ZINC LEAD CADMIUM
BCF S BT BCF S BT BCP
1.1 54.4* 2.4 0.0 l.O O.3 0.3
O.2 217.4* O.2 0.0 3.5* 0.3 0.1
0.2 161.1* 1,2 0,0 2.0« 0.3 0.2
0,1 619.3* 6.8 0.0 4,5* 0.3 0.1
MBBCURY AKSENIG
BCF S BT BCF S BT BCF
0.8 0.1 0.5 5.0 NA MA NA
O.I 0.6 0.3 0.5 34.3 18. O 0,5
0.1 0.4 0.1 0.3 HA NA NA
0,0 0.6 0.0 0.0 NA NA NA
= Data Not Available
materials,
benthic tiasue compared with sedisent values.
08
-------
ITS
3093
FIGURE VI-13. Total PAH concentrations (ng/g) in caged clams (Elliptic
-------
130
iv) Contaminants in Fish
Sport fish in Ontario waters of the river are tested regularly by
the OMOE for dorsal fillet concentrations of selected contamin-
ants (mercury, PCBs, mirex, organochlorine pesticides, and
2,3,7,8-TCDD), As shown in Table VI-8, dieldrin, heptaehlor,
mirex and 2,3,7,8-TCDD were not detected in any fish samples.
PCBs, DDT and lindane were below consumption guidelines. Concen-
trations of chlordanes, hexachlorobenzene and octachlorostyrene
were also low, but there are no guidelines for these parameters.
Only mercury is found in fish in excess of the Canadian federal
government guideline for fish consumption in the St. Marys River,
Usually, only large specimens of certain species of sportfish
contained sufficient mercury to warrant the Ontario government to
issue consumption advisories (Table VI-9). There were no fish
consumption advisories issued by the Michigan Department of Pub-
lic Health for 1988, Data for trend purposes are limited and
indicate that trends in mean concentrations of mercury in walleye
and northern pike since 1977 are not significant. Mean concen-
trations of mercury in rainbow trout declined by about 60% be-
tween 1978 and 1985.
Young-of-the-year yellow perch collected near Sault Ste. Marie,
Ontario contained PCBs, but these concentrations (average 25 ppb)
were well below the GLWQA specific objective (100 ppb) for the
protection of birds and animals which consume fish (35) and the
Ontario and Michigan fish consumption guidelines. No detectable
levels of chlorophenols or chlorinated aromatics were found in
these fish. Preliminary analysis of whole fish (36) indicate
that white sucker and brown bullhead from the North Channel of
Lake Huron contained detectable levels of naphthalene, acena-
phythylene, acenaphthene, phenanthrene, anthracene, fluoranthene
and pyrene. These concentrations were similar to those found in
these species from other industriali2ed areas of the Great Lakes,
such as Hamilton Harbour and the St. Lawrence River.
v) Contaminants in Birds
The early 1980s saw a marked resurgence in the number of young
produced per active nest of both ospreys and bald eagles. In
1986 and 1987, bald eagles successfully nested on the Mumiscong
Lake shoreline and produced two young each year.
Limited data are available for current contaminant levels in
birds. Monitoring has generally been limited to eggs, owing to
the susceptibility of embryos to the effects of toxic organic
compounds which bioaccumulate, Common tern eggs that were col-
lected in 1984 from Lime Island had very low or undetectable
concentrations of organochlorine compounds (U.S.FWS, unpublished
data). The exceptions were p,p-DDE and PCBs. The mean DDE con-
centrations in 10 eggs was 1.8 ug/g and for PCBs, 0.9 ug/g.
-------
131
VI -8
Contaminant! in dorsal fillets of sport fish from Ontario wateri
of the St. Marys River.
Concentration (ppm wet wt,)
Contaainant
Mercury
PCBa
Chlordanes
(Alpha & Gauut)
Dieldrin
DDT and metabolites
Heptaehlor
Endrin
Lindane (Gamma-BBC)
Mirex
Hexaehlorobeniepe
Octachloroityrene
2,3,7, 8-TCDD
Consumption
Guideline*
0.5
2.0
MA
0.3
5.0
0.3
0.3
0.3
0.1
HA
NA
0.000020
Observed
Bangs
0.4-1.30
ND-1.260
MD-0.04S
ND
ND-0.4S6
ND
NA
ND-O.QQl
SD
ND-0.011
ID-O.OOi
ND
ND-Not Detected NA-No Data Available
Note: * Health and Welfare Canada guidelines and Great Lakes
Quality Agreement specific objectives for
the protection of human consuners of fish,
Ontario Ministry of the Environment (OMOEJ data (A.
Johnson pers. conn.) for individual dorsal fillets of
various species collected from the St. Marys River
below the rapids, Lake George, St. Joseph Channel and
St. Joseph Island since 1982.
-------
132
TABLE VI-9
Species of sportfish from Ontario waters of the St. Marys River
with fillet concentrations of mercury in excess of the Canadian
Government Guideline for Fish Consumption iO.5 ppm).
Location
Species*
Size
Hg Concentration
Range (ppm)
St. Marys R.
( below rapids )
Lake George
White Sucker
>35
Longnose Sucker >30
Walleye
Northern Pike
Lake Trout
Walleye
Walleve
>45
>65
>55
45-55
>55
era
cm
cm
cm
cm
era
cm
0
0
0
0
0
0
1
.5
. 5
.5
.5
. 5
. 5
.0
- 1
- 1
- 1
- 1
- 1
- 1
- 1
.0
,0
.0
.0
.0
.0
.5
St. Joseph
Channel
Northern Pike
>75 cm
0.5 - 1,0
St. Joseph
'Island
Walleye
45-55 cm
0.6 - 1.0
* from "The 1988 Guide to Eating Ontario Sport Fish" (345.
-------
133
The highest PCB concentration was 7.3 ug/g, a level which could
have subtle intrinsic (to the egg) and extrinsic effects in
terns, Mercury and selenium levels were not above reasonable
background levels reported in bird eggs,
The Canadian Wildlife Service collected herring gull eggs from
Pumpkin Point in 1985 and 1986, Only and PCBs exceeded 1
ug/g in 10 egg composite samples, (Dr.C. Weseloh, personal com-
munication) , PCBs had the highest concentration, 22 ug/g, in
1985 and 14 ug/g in 1986. Although this is below the perceived
toxicological threshold for herring gulls, it is important to
recognize that a resistant species with a relatively high body
(or egg) burden can be a source of significant contamination if
consumed by other predators/ such as raptors or mammals.
The concentration of 2,3»7,8-TCDD also measured in herring
gull eggs. Levels were considered in the background range at 4
pg/g in 1385 and slightly above background at 16 pg/g in 1986,
Other dioxin-lilce compounds, including the highly toxic, non-
ortho PCB congeners were detected in bullheads and walleye from
the St. Marys River in 1984 (U.S.FWS, unpublished data). It is
thought that these dioxin-like PCB congeners account for the
majority of toxic effects in Green Bay Forster terns (37). Bird
samples collected from the St. Marys River have not been analyzed
for these congeners.
Bottom, Sediments
i) Physical Characteristics
Physical characteristics of sediment samples taken during 1985
from the St. Marys River (38) indicated that sediment composition
was strongly related to flow velocities. Sediment composition
varied across the river according to the flow distribution.
Upstream from the Sault locks, medium and fine sanct constituted
80% of the particles. This sediment texture is attributed to the
high river velocities in the channel where coarse material set-
tled first and fine materials (silt and clay) remained in suspen-
sion and settled in embayments along the Ontario shoreline of the
river.
A typical sediment composition from below the rapids at transect
SMD 2.6, 4 km downstream of the Algoma Steel discharges is il-
lustrated in Figure VI-14. The Michigan shoreline is charac-
terized mainly by coarse and medium sand which represents about
63% of the sediment composition. Along the Ontario shoreline,
where several embayments exist, the sediment is composed of silt
(82%). In the mid-river, fine and very fine sand and silt con-
stituted about 90% of the sediment composition. This particle
sorting is attributed to the river flow distribution in the lower
river where 69% of the total river flow is along the Michigan
-------
o
t-
K
>2000
62 US
PARTICLE SIZE >»
S - 63 -t - 5 < 4
Ul
FIGURE VI-14. St. Marys River typical particle size.
-------
135
shoreline and 31% is along the Ontario side.
ii) Sediment Transport
No bedload transport study was conducted in the St. Marys River.
However, sedimentation rates were determined using Cs-137 meas-
urements on two 1985 core samples from Lake George (OMOE stations
#100 and 102) . The peak of radionuclide Cs-137 occurred at
approximately the 15 cm sediment depth in Lake George (Figure VI-
15). The testing of large-scale nuclear weapons in the northern
hemisphere started in. 1954, Increased significantly around 1958-
59, and peaked during 1962-64. Since then the fallout of debris
has decreased markedly. Consequently, in the dating of the sedi-
ment, the peak of Cs-137 is referred to the 1962-64 fallout peak
activity of the atmospheric testing. This would correspond to a
sedimentation rate of 0.22 g/cm^/yr (0,7 cm/yr) and 0.19 g/em^/yr
(0*53 cm/yr), or an average of 0,6 cm/yr. Results for sediment
mixing for the two samples were 1.3 g/cm^ {4.7 cm) and 1.7 g/cm^
(5.8 cm).
In 1986 a joint U.S.EPA. and OMOE seismic survey conducted in
portions of the St. Marys River including Lake George and Little
Lake George. Preliminary seismic data indicate that the combined
thickness of glacial deposits unconsoliflated sediments over-
lying bedrock exceeds 30 m in Lake George. The thickness of
recently deposited sediment in this lake is in the order of 1 m.
The data indicate that Little Lake George is also an active depo-
sitional area. There is about 0.3 m of sediment over bedrock and
glacial deposits.
ill) History of Contamination
The concentrations of PCBs and DDT in the Lake George core taken
in 1986 at station #102 are shown in Figure VI-16 (39) together
with sediment dates estimated from the Cs-137 profile. The pro-
duction of PCBs in the United States began in 1929 and peaked in
1970. In the core samples, PCBs are first detected in the seg-
ment corresponding to the 1950s and reach their maximum concen-
tration in the early to mid-1970s, DDT usage in the U.S. began
in 1944, peaked in 1959, and was banned in 1971. DDT first ap-
pears in the mid-1950s part of the core and reached its highest
concentration in the early to mid-1960s. The peak concentration
of PCBs and DDT in the core occurred approximately 5 years after
peak production or usage of the chemicals. The major sources of
PCBs and DDT in the area are likely remote and nonpoint, thus,
time delays in their transfer to the St. Marys River sediment are
likely. The low concentrations of these contaminants in the
cores is further support for diffuse remote sources.
The concentration of total PAHs, particularly the PAH, benzo(a)-
pyrene, in the sediment core are plotted versus depth and date in
Figure VI-17. The PAH concentrations are three orders-of-mag-
-------
i
u
4
6
8
10
1 2
X 14
H
0.
0 16
1 8
20
22
136
Cs-137 (dpm/g)
FIGURE VI-15. Variation with depth of Os jn Lake George sediments
-------
137
70-1
80-
SO-
40-
30-
20-
• 10-
g
£
c
o
z
o
o
19TO
I960
1950
1940
1930
2 PCi
n. .«.
5-
4-
3-
2-
2 DOT
0-1
5-6
1C-11 19-W
CORt OEPTH cm
25-28
FIGURE VI-16, Total PCBs and DDTs in Lake George sediments (station 102, 1986).
-------
138
24-,
20-
12-
8-
a .
a. 4-
z
O
1980
19O
1930
Z PAH
n n n
z
UJ
O
Z
O
Q
I -
a PYftENi
f> n P n
1
-------
139
nitude higher (ppm versus ppb) than those of the chlorinated
organics, indicating major PAH sources in the area. The Algoma
Steel Mill in Sault Ste. Marie is likely the principal source of
these chemicals to the river, because PAHs are known-to be by-
products of the coking process. Virtually the same concentration
profile was found for total PAHs and for benzo(a)pyrene. The
core concentration profile shows that PAH discharges in the area
increased substantially in the early 1940s, probably due to in-
creased steel production during World War II. A small lag in
steel production occurred in the late 1940s to early 1950s, fol-
lowed by a sharp increase in the late 1950s, peaking during the
late 1960s or early 1970s. The pattern of PAH concentrations in
the core segments is in excellent agreement with historical steel
production in the area. Much lower concentrations of PAHs are
found in the more recent sediments. This is probably due to a
combination of lower steel production and improved pollution
control.
Changes occurring in the relative distribution of PAH compounds
at various core depths are illustrated in Figure VI-18. At a
depth of 29-30 cm, corresponding to about 1930, indeno-
(1,2,3,c,d)pyrene and benzo{g,h,i)perylene were the major PAHs in
the sediment. Benzo(a)pyrene was below the detection limit at
this core depth. During the peak of industrialization (1968, 11-
12 cm) benzo(a)pyrene was the most dominant PAH but the other 4
and 5-ringed PAHs, pyrene, benzo(a)anthracene, chrysene, benzo-
(b)fluoranthene and benzo(k)fluoranthene were also present at
high concentrations relative to the other PAHs. In recent sur-
ficial sediments (0-10 cm, 1968) naphthalene and phenanthrene
represent a significant fraction of the total PAHs, together with
the 4- and 5-ringed PAHs. The concentrations of naphthalene and
phenanthrene in the core are much less variable than benzo(a)-
pyrene, indicating that they may originate from a different
source.
Results for heavy metals in the core from Lake George (OMOE
station #102) are presented in Table VI-10 (40). Only the first
20 cm of the core were analyzed, Distributions of Mi, Co, V and
Cu were relatively uniform with depth but Zn, Pb and Cr were not,
Zinc increased gradually from 185 to 410 ug/g between 4 and 12 cm
and then decreased back to 139 ug/g at 20 cm depth (Figure VI-
19). Lead peaked at 94 ug/g in the 10-11 cm segment and decreas-
ed to 39 ug/g at 20 cm of depth. Chromium peaked at 189 ug/g in
the 15-16 cm section. Using the estimated sedimentation rate of
0.7 cm/yr for this sample, zinc, lead and chromium reached peak
concentrations in the river around 1968-70.
The distribution of oil and grease in the core (Figure Vl-19) was
different than for total PAHs and zinc. Oil and grease increased
gradually from 2,700 to 3,580 ug/g between 0 and 7 cm depth,
increased drastically to 8,190 ug/g in the 7 to 8 cm segment
(mid-1970s) and then decreased gradually to 360 ug/g at 30 cm.
-------
140
500
400H
300-
200-
100-
0
ja
i:300o^
Z
O
2000-
Z
LLJ
1000-
O
O
80-
60-
40-
20-
0-1 cm
DnH
H-O i
n
n
29-30 cm
n
AY AE FL PH AN F FY KA CM Bt>F BtF BlP I"P CTA BT
FIGURE VI-18. Vertical distribution of PAHs in Lake George sediments
(station 102, 1986).
-------
141
TABLE VI-10
Eesults from metal analyses in a sediment core sample collected
during 1986 at OMOE station 102 in Lake George (ug/g, dry
weight I.
Depth cm
0-1
1-2
2-3
3-4
4-5
3-6
6-7
7-8
8-9
9-10
10-11
11-12
12-13
13-14
14-15
15-16
16-17
17-18
18-19
19-20
Ni
41
41
4S
41
44
44
44
43
43
44
45
42
42
39
41
39
39
43
41
40
Co
18
ie
17
91
17
20
17
li
17
18
ii
li
17
18
18
li
17
16
16
16
Cr
95
107
95
91
it
98
100
102
99
104
111
121
123
141
184
189
152
117
94
83
V
59
50
57
54
60
54
60
57
57
SO
60
65
68
63
68
63
67
62
§3
83
Zn
190
191
183
IBS
238
259
328
332
38§
369
384
410
407
379
334
2§7
227
188
154
139
Cu
35
34
35
35
35
34
35
35
41
38
39
39
37
33
34
29
33
33
34
37
Pb
41
3T
39
35
48
51
61
61
75
82
94
89
78
72
71
eg
57
48
42
39
-------
T1
)_H|
o
c:
pa
M
" o
o
p g
— CL
o
Ki 00
* "1
3
O.
P
O
p
tt
CO
O
o
00
ft
a
^.
3
p
6
o
v
a
o
o
0
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
0
o
50
I
100
i
150
200 250 300
mg/kg, dry wt
i
350
I
400
O
to"
a
3
CX
O
-1
-------
143
In summary, results from the core sample reflect the effective-
ness of the ban on DDT and PGB and the reduction of total PAHs,
oil and grease, zinc, chromium and lead loadings to the St. Marys
River over the past 20 years.
iv) Spatial Distribution of Contaminants in Surficial
(Recent) Sediments
During 1985, the U.S.EPA and PWS collected sediment samples from
125 stations (Figure VI-20) covering the entire St. Marys River
(41). The OKOE collected sediment samples at 71 river stations
(Figure VI-21) and 8 Canadian tributaries (38).
In comparing the levels of contaminants in sediments, comparison
is made to the OMOE Guidelines for Dredge Spoils for Open Water
Disposal and the U.S.EPA Guidelines for Pollutional Classifica-
tion of Great Lakes Harbor Sediments (Table III-4, Chapter III).
These guidelines are not based on biological effects and, there-
fore, will not provide insight into impacts on the river eco-
system. However, their use provides a comparison of relative
concentrations. There are no ecologically based sediment guide-
lines .
Hesselberg & Hamdy (38) found that oil and grease, loss on igni-
tion (total volatile solids), cyanide (CN), arsenic (As), chro-
mium (Cr), copper (Cu), lead (Pb), nickel (Ni), and zinc (Zn)
exceeded both U.S.EPA and OMOE guidelines in 20% or more of the
samples in at least one group of samples (Table VI-11). Concen-
trations of chromium, copper, and iron (Fe) most consistently
exceeded both U.S.EPA and OMOE guidelines.
The percent of samples exceeding both U.S.EPA and OMOE guidelines
in the vicinity of industrial discharges, as well as further
downstream, are shown in Table VI-12 (33,34,35,36,37,38,39,40,41,
42). Percents were calculated using the lowest of U.S.EPA moder-
ately polluted or OMOE guidelines for each contaminant. It is
apparent from Table VI-12 that the area near Algoma Steel, the
City of Sault Ste. Marie, Ontario, and Little Lake George repre-
sent the most contaminated areas in the St. Marys River. However,
as shown by the spatial distribution of zinc and oil and grease
in surficial sediments during 1973 and 1983 (42), both the areal
and downstream extent of heavily polluted sediments has decreased
(Figures VI-22 & 23). This coincides with the core data from
Lake George (Figure VI-19).
Contaminant concentrations in Lake George sediment samples were
lower overall. However, over 20% of the samples exceeded the
guidelines for most contaminants except for PCBs and cadmium.
Lake Nicolet sediment samples exhibited a much lower frequency of
contaminants exceeding guidelines but As, Cr, Cu, Fe, Ni and Zn
still exceeded guidelines in 14% or more of the samples. In Lake
Munuscong and Lime Island Channel a surprising percent of samples
-------
144
FIGURE VI-20. U.S. EPA/FWS St. Marys River 1985 sediment sampling sites.
-------
SMD-0.1/O.S/1 2/2,«S,QE/«,4i
1S-O08
Sugar
Island
Punt tut ..
§*r f
S»ult StB Mari«
MI
SMD* Saint Marys downitream
SMU* Saint Mary* iipitr»»m
° Sampling till
Ui
FIGURE VI^2L MOE 1986 St. Marys River sediment sampling sites.
-------
TABLI VI-11
Percent of sediment sample* collected from the St. Marys Hiver during 19i6 by U.S.EPA, USPHS, or OMOI that exceeded
noderately polluted U.S.iPA and/or OHOE sediment poilutation guidelines given in ng/kg, except where noted.
Sources af Total
Samples Samples
Oil
and
Grease
Percent
Loss on
Igni-
tion
X Exceeding U.S.
Guidelines
U.S. EPA 1985 19
U.S.EPA/FWS 1985 125
OHOE 1985 71
1000
5
17
42
S
5
ia
28
X Exceeding OMOE
Guidel ines
U.S. EPA 19B5 19
U.S.EPA/FHS 1885 125
OHOE 1«J»5 71
1500
0
10
3»
6
5
12
21
P TKM
EPA Mode rate iy
420 1000
63 10
NA NA
45 35
Guidelines
1000 2000
0 0
NA NA
0 NA
Cyanide
Polluted
0.1
100
78
NA
0.1
100
18
NA
PCBs
As Cd Cr
Cu PeX Pb Hg Ni
Zn
Guidelines
1*
0
1
0
0.05
0
21
14
3 <6* 25
0 0 44
NA 0 Sfi
58 0 58
B 1 26
0 0 44
NA 4 56
31 3 58
2S 1.7 40 1 20
17 2« 0 0 32
34 NA 11 0 34
49 44 34 0 21
25 1 50 0.3 25
17 47 0 0 32
34 MA tt 1 19
49 60 23 1 6
90
0
18
49
100
0
It
46
NA - Not analyzed or not available
* - Heavily polluted
cn
-------
TABLE VI-12
Percent of samples by area at or exceeding U.S.KI'A moderately polluted or OMOB sediment pollution Guidelines.
Area Location
Algoina Steel
Sault Ste. Marie
Little Lake George
Lake George
Lake Nicolet
Lake Munuseong
Line Inland Channel
Agency
Samples
U.S.EPA/FWS
OMOE
U.S.EPA/FWS
OMOE
U.S. EPA/FWS
OMOE
U.S.EPA/FWS
OMOE
U.S.EPA/FWS
OMOE
U.S.EPA/FWS
OMOE
No.
Samples
8
9
4
5
24
22
IS
7
30
NA
21
NA
Oil
and
Grease
25
56
so
100
21
45
0
14
0
NA
19
NA
Loss on
Ignition
38
55
50
ttO
12
32
7
0
0
NA
5
NA
Total
PCfla
12
11
50
20
I?
a
33
o
30
NA
o
NA
A»
NA
8'J
NA
100
NA
72
NA
2»
NA
NA
NA
NA
Cd
0
0
50
20
0
5
7
0
0
NA
0
NA
Cr
5O
78
SO
0
33
64
33
29
77-
NA
76
NA
Cu
38
67
50
100
29
59
NA
14
37
NA
52
NA
Fe
NA
89
NA
100
NA
95
NA
29
NA
NA
NA
NA
Pb
38
44
SO
60
21
32
7
0
0
NA
0
NA
Ni
12
22
60
4
25
30
1
H
43
NA
62
NA
? it
38
56
50
100
H9'
69
7
14
0
NA
19
NA
NA = Data not available or not analyzed
-------
148
Zone Range
mg/kg (dry w«ight! K] -
< 60 94-S8
60-199 81-130
> 199 200-110O
Sault St* Marie
ONT
1973
Zone Range
^^ rng/kg (dry weight)
P] < 60 71-58
60-199 60-180
> 199
200-8S4
Sault Ste Marie
ONT
1983
FIGURE VI-22. Distribution of ziac in the St. Marys River surficial sediments.
-------
149
Zone flange
fog/kg (dry weight)
44-800
1000-2000
> 2000
1000-1700
2000-19000
Sault Ste Marie
ONT
1973
Zone Rang*
ffli/kg (dry weight)
f"1 < 1000 210-930
["I 1000-2000 10SO-1S70
fB * 2000 2050-17630
Sault Ste Maria
ONT
1983
FIGURE VI-23. Distribution of oil and greases in the St, Marys River
surficial sediments.
-------
150
exceeded guidelines for cr, Cu, and Mi. It appears these ele-
ments settled out with the sediment in the slower moving waters.
Most chlorinated organic contaminants had low concentrations in
the sediment. PCBs exceeded OMOE guidelines in the upper river;
however, no more than 1% of the total samples exceeded the U.S.
EPA moderately polluted guideline.
The distribution of PAH compounds (Figure VI-24) indicated that
sediment from the Algoma Slip contained the highest levels of
total PAHs (711 ug/g). Individual compounds, notably acsna-
phthene, phenanthrene, anthracene, fluoranthene, pyrene, dibenzo-
thiophene and carbazole in the Algoma Slip area were also the
highest levels in the river as shown in Table VI-13. A semi-
quantitative analysis of samples collected during a coal tar
spill investigation in Bennett Creek during 1987 indicated that
total PAH concentrations (naphthalene, acenaphthylene, acena-
phthene, fluorene, phenanthrene, anthracene, fluoranthene,
pyrene, chrysene, benzo(a)anthracene, benzo(b,k)fluoranthene,
(benzo(j)fluoranthene, benzo(e)pyrene, benzo(a)pyrene, perylene,
indenod, 2, 3-c,d) pyrene, dibenzo(a,h)anthracene, benzo(g,h,i)-
perylene) were approximately 3,300 ug/g. Bennett creek flows
into the Algoma Slip. The Algoma Steel and/or Domtar Inc.
operations are likely the major source of PAHs to the slip and
Bennett Creek and subsequently to the St. Marys River.
As a result of the strong association of PAHs with silt and clay,
higher concentrations of PAHs were found in the embayments down-
stream from the Terminal Basins than those observed in non-embay-
ments immediately downstream from the discharge.
Along the Michigan shore, with the exception of a location im-
mediately downstream from the Edison Sault Electric Company
Canal, total PAHs were similar to background levels (Figure VI-
24) . Total PAH concentrations immediately downstream of the
Edison Sault Electric Company Canal (334 ug/g) may be the result
of historical inputs from a coal stockpiling operation on the
shore.
Few guidelines are available for PAHs in sediments. However, the
IJC has (1983) (33) proposed an objective of 1 ug/g for benzo (a)--
pyrene. This concentration was exceeded along the Ontario shore-
line in samples from the east end of the Algoma slag Site to as
far downstream as the beginning of the Lake George Channel and
also below the Edison Sault Canal in Michigan.
Tributaries may also contribute contaminants to the river system.
In the vicinity of Algoma Steel and the City of Sault Ste. Marie
Ontario, tributaries such as East Davignon and Fort Creeks are
likely sources of As, Cr, Cu, Fe and oil and grease. Fort Creek
is also likely a source of Ni, Pb, Zn and total PCBs. The levels
of Cr, Hi and Fe in McFarland Creek, a tributary to Little Lake
-------
Til
•LOOM*
LANOFIL
FIGURE ¥1-24. Total PAHs in surficial sediments in the St. Marys River (1985).
-------
TABLE VI-13
PAH8 in sedieenta In the St. Harva River, 1985 lug/g),
STATION
COMPOUNDS
Naphthalene
Acenaph t hvlene
Aeenaphthene
Fluorene
Phftnsn threne
Anthracene
Fluoranthene
Pyrene
Chrysene
Benzol a ^anthracene
Benzol b, IO flua ran these
Benzoi j ) f luoranthene
Denzo! e 1 py ren.e
Banzai a 1 pyrene
Perylene
I ndenolt 1,2, 3-e ,d )|»yrene
DibenzoC a, h ) anthracene
BenscMg,h, i ^peryiene
Benzothiophene
Quino 1 ine
D i be n zo t h i aphe n.e
Af^r idine
Carbag-ol e
Be nzCa^fteridine
Dimethyl benzl ft Janthraeene
BenzoC b (chrysene
Anthanthrene
Cart? lie ne
1
HD
0.2
ND
NO
0.07
0.1
0.14
0.09
ND
0.21
0.44
ND
0.24
0.35
ND
ND
ND
NO
ND
ND
ND
ND
NO
ND
ND
ND
ND
ND
'£
NO
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
NO
ND
ND
Ni)
ND
ND
ND
ND
HO
ND
ND
3
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
ND
NB
ND
ND
4
0.06
0.08
ND
No
0.86
ND
4
3
3.4
18
16
1.1
7.4
9.2
2.2
3.6
1.5
3.5
ND
ND
ND
0.5B
0,28
Z.I
ND
ND
ND
ND
&
3.4
0.93
1.1
2.3
ia
4.5
11
5.6
1.1
4.2
4.H
o.»
2-fi
3.5
1
1 .2
0.55
1.1
0.45
0.07
1 .8
0.71
0.8
1.2
ND
ND
ND
ND
0
29
4.8
19.5
28.5
1HS
3?
135
71.5
9.3
32
32.5
5.5
16.0
24.5
7.3
5.3
2,3
4.5
3.S
0.4B
24.5
8.7
14
10.2
ND
ND
ND
ND
7
33
0.42
0.93
1.9
14
3.5
13
7.4
1.5
5.S
4.3
O.K'4
2,1
2.D
0.74
O.U2
0.35
O.B2
0.39
0.12
1.7
1.3
1. J
l.S
ND
ND
ND
ND
a
0.06
0.42
ND
0.06
0.29
0.22
0.53
0.32
0.26
1.3
5.5
l.tt
4.3
4.3
1.4
0.7
N»
0.2
ND
ND
ND
0.08
ND
0.13
ND
ND
ND
ND
•
5.9
O.SS
0.18
0.47
3.S
1.4
6.4
3.6
1
4.6
6.2
1.1
3
4.4
1.2
1.1
0.48
O.B8
0.31
ND
O.S9
0.61
0.81
0.84
ND
ND
ND
ND
10
0.69
4.6
0.62
3.4
25
10
30
17
9.9
36
67
17
37
48
11
4,9
2.5
1 .7
0.06
ND
2.3
1.2
2.2
5.7
ND
ND
ND
ND
11
6.6
0.52
0.17
0.36
2.2
1.0
3.7
2.2
1.0
4.2
11.0
3.0
7.0
«. 4
2,3
0.69
ND
0.21
0.26
ND
ND
0.22
0.3
0,49
ND
ND
ND
ND
12
1.7
O.SS
ND
0.1?
1.1
0.52
1.7
1.1
0.45
2.1
2.8
ND
2
1.9
0.55
ND
ND
ND
ND
ND
0. 14
0.1B
0.1
0.31
ND
ND
ND
ND
13
0.03
ND
NO
NO
0.09
0.03
0.12
0.07
0.02
0.09
0.13
ND
O.UB
0.11
O.OJ2
0,04
ND
0.04
ND
N»
NB
O.U8
O.U4
NB
NO
ND
ND
ND
14
0.13
0,18
ND
ND
0.4
0.18
0.59
0.36
0.14
0.55
0.97
0. 16
0.56
0.71
0,39
0.34
0.11
0.31
ND
ND
ND
0.25
0.28
0. 13
ND
ND
ND
ND
Ifi
0.125
0.07
ND
0.03
0.25
0.07
0.425
0.27
0.06
0.28
0.325
0.06
0,16
0.21
0.11
0,07
0.025
0.065
O.06
0.03
0.15
0,lfl5
0, 186
o. lae
ND
ND
ND
ND
Ul
Total PAHa
1.84 ND
ND
71.5
67.8
711 100,5 21.8 49.S
334 55.82 17.4
1.0
6.66
3.42
-------
153
George* represented a moderately polluted sediment according to
the U.S.EPA Dredging Guideline, The levels were 38 mg/kg, 25
mg/kg and 19,000 mg/kg, respectively,
In 1985, U.S.EPA collected 19 samples of bottom sediment from 18
Michigan tributaries. The samples were analyzed for a broad
range of conventional pollutants, metals, pesticides, PCBs and
other organic chemicals (43). Various benthic organisms were
present in most samples and there was no obvious evidence of
pollution. Analyses for conventional pollutants, metals, aro-
matics, DDT and metabolites, phthalate esters, PCBs, and PAHs
indicated that, although parameters resulted in the sediment
being classified as moderately polluted (U.S.EPA guidelines),
most were classified as nonpolluted. The results of this study
indicate that Michigan tributaries are not a significant source
of contaminants to the St. Marys River. Samples collected from
streams which drain the City of Sault Ste- Marie, where contamin-
ant sources are most likely, were generally free of significant
contaminant concentrations. Exceedances of specific U.S.EPA
guidelines are believed to be the result of natural sources.
-------
154
B. SPECIFIC CONCERNS
Table VI-14 summarizes contaminants of concern in the St. Marys
River by matrix. The following discussion provides more detailed
information on the areas or species impacted. In general, where
the same contaminant was measured in all matrices (e.g., PAHs)
the zones of environmental impact were similar.
1. Water
Degradation of the water quality in the St. Marys River resulting
from industrial and municipal discharges is a concern for citi-
zens of Sault ste. Marie, Ontario and Michigan. Generally the
concerns are focussed on the possible combined toxic effect of
ammonia, cyanide and heavy metals {e.g. zinc); excessive amounts
of oil and grease as a result of discharges or spills; phenols
which continue to exceed the objective, albeit in a small zone
downstream from the industrial discharges; and, PAHs because of
the carcinogenic nature of certain PAH compounds.
Water quality impairment in the St. Marys River is mainly re-
stricted to a narrow band along the Canadian shore, downstream of
Algoma Steel and St. Marys Paper effluent discharges. Partial
recovery from the effects of these industrial inputs takes place
throughout the St. Marys River downstream, however, discharges
from the Sault Ste. Marie, Ontario East End WWTP delay the com-
plete restoration of satisfactory water quality with respect to
several contaminants (i.e. phenols, ammonia, cyanide) until Lake
George. There is some transboundary pollution in the Lake George
Channel.
A band of phenols which slightly exceeds the PWQO and the GLWQA
specific objective of 1 ug/L was noted along the Canadian shore
for a distance of 3 km below the Terminal Basins discharge.
Although ammonia and cyanide levels are within their respective
objectives throughout the St. Marys River, the combined effect of
these contaminants may result in toxic conditions.
In the St. Marys River, measured. PAHs associated with the aqueous
phase of the water column increased downstream from Leigh Bay,
reaching a peak concentration in the Algoma Slip. Although PAHs
are commonly reported as a group, the toxicity and relative car-
cinogenicity of individual substances vary greatly as shown in
Table VI-15. In the aqueous phase, 95% of the PAH compounds
measured in the St. Marys River were considered to be not or
weakly carcinogenic. Estimated concentrations of PAHs associated
with the whole water phase exceeded the U.S.EPA AWQC for Human
Health Criteria (for fish consumption) of 31 ng/L for total PAHs
from the Algoma Slag Site to downstream of the Sault Ste. Marie,
Ontario East End WWTP. Estimates of PAHs associated with both
the whole water and aqueous phase that are considered noncar-
-------
155
TABLE VI-14
Summary of contaminants of concern in the St. Marys River,
MATRIX
WATER SEDIMENT
CONTAMINANT
BIOTA
BENTHOS
GOMM.
OLIGO-
CHAETES
CAGED
CLAMS
SPORT
FISH
Bacteria
(Fecal coliform) E
Phosphorus E
Ammonia P
Cyanide P
Heavy Metals
- Chromium
- Copper
- Lead
- Mercury
- Nickel
- Zinc P
- Iron E
Phenols E
Oil and Grease P
PCBs, total
PAHs, -total P
- Benzo(a)
pyrene E
E
E
E
E
E
E
E
E
P
P
P
P
IS?)
P
P
Notes:
E = exceeds available guideline
P = present above background
I = impacted by contaminant indicated
-------
TABLE VI-15
Carcinogenic activity of individual PAHs,
Individual PAHs
Carcinogeric
Potential
Naphthalene
Acenaphthyiene
Acenaphthene
Fluorene
Phenanthrene
Anthracene
Fluoranthene
Pyrene
Benzofa Janthracene
Chrysene
Benzo(b)fluoranthene(2, 3-berizf luoranthane )
Benzo( k ) fluoranthene ( 8 , 9-benstf luoranthane )
Benzo(a)pyrene(1,2-benzpyrene}(3,4-benzpyrene)
Dibenzo(a,h )anthracene( 1,2,5 , 6-diben.2anthraeene
Benzo(g,h,i tperylene
lndenoll,2,3-c,d Jpyrene(o-phenylene pyrene)
Benzo(e ) pyrene(4,5-benzpyrene H1>2-benzpyrene J
Perylene
Benzo ( j ) f 1 uoranthenet 7 , B-benzt'luoranthene )
Coronene
Acridine
Dibenzol a,h)acridine(1,2,5,6-dibenzacridine)
Carbazole
Benzo(a)carbazoie
Quinoline
Benzot f)quinoline
Dibenzthiophene
Benzot 2,3)phenanthro(4,5-b,c »d)thiophene
Inactive
Inactive
Inactive
Inactive
Disputed
Disputed
High Active
Moderate
Moderate
Inactive
Slight
Slight
High
* Source: National Academy of Sciences (1972): Particulate Polycyclie Organic
Matter; Washington, D.C.
Indications are "-" for not carcinogenic, "+/-" for uncertain or weakly
carcinogenicr "+" for carcinogenic and "++( +++" for strongly carcinogenic
from (44).
** Source: Polynuciear Aromatic Carcinogens, Dipple, Anthony in Chemical Carcinogens,
p., 245-307.
-------
157
cinogenic constitute greater than 80% of total PAHs at all sites
monitored along the St. Marys River, PAH levels along the U.S.
shoreline were similar to the background or upstream levels in-
dicating no transboundary pollution.
2. Sediments
Bottom sediments of the St. Marys River exhibited contaminant
concentrations that exceeded both the OMOE and U.S.EPA dredged
material disposal guidelines. The parameters of concern are
arsenic, cadmium, chromium, cyanide, copper, iron, lead, mercury,
nickel, zinc, nutrients, and oil and grease. Most of these con-
taminants, together with chlorinated organics and PAHs, are of
concern due to bioconcentration and the potential for toxic ef-
fects.
Sediments along the Ontario shore near Algoma Steel and Sault
Ste. Marie and in Little Lake George were the most contaminated
in terms of percent of samples having concentrations equal to or
greater than dredged material disposal guidelines. The sediments
in the St. Marys River upstream of the industrial complexes were
uncontaminated.
Sediments containing chlorinated organic contaminants, coupled
with external loadings, may result in excessive body burdens for
aquatic life. Sediment core data indicates improvements but PAH
concentrations remain a concern. As a result of the strong as-
sociation of PAHs with silt and clay, higher concentrations were
found in the embayments downstream from the Terminal Basins.
3. Biota
Benthic macroinvertebrate distribution in a system is often used
as an indicator of ecological health and environmental impact.
Normal benthic communities are characterized by diverse popula-
tions, presence of pollution intolerant taxa (e.g. caddisflies),
and a relatively higher number of organisms per unit area. Ad-
versely impacted benthic communities in the St. Marys River gene-
rally were restricted to a narrow band approximately 500 rn wide,
extending 3 km along the Canadian shore downstream of industrial
discharges. Some recovery was apparent with increasing distance
(e.g., 5 km) downstream from the Algoma Steel and St. Marys Paper
discharges, however, complete recovery was not realized until the
lower section of Lake George, some 24 km downstream from these
discharges. Recovery was, in part, delayed by effluent from the
East End WWTP. Clean water fauna characterized the nonindus-
trialized U.S. shore, the whole river upstream of pollution
sources, and Lake Nicolet.
Despite reductions in certain pollutants from Algoma steel, St.
-------
158
Marys Paper, and the East End WWTP little improvement has been
observed in the benthic community of the St. Marys River. Con-
taminants in the sediments, together with contaminants in the
water column, are thought to severely restrict the survival of
most macroinvertebrates in certain areas of the St. Marys River.
It was generally observed that areas with visible oily residues
were characterized by the absence of ephemeropteran Hexagenia.
Elimination or alteration of normal populations of aquatic in-
sects and other invertebrates and their replacement by pollution
tolerant species (which have limited value as fish food organ-
isms) will also result in the alteration of the suitability of
the river for supporting game fish populations. Further, contam-
inated sediments are a likely source of contaminants to benthic
organisms and can exert toxic influences on them, either com-
pletely eliminating benthic populations or reducing the diversity
to a few tolerant species. Uncontaminated clams exposed to river
water near and downstream of the discharges accumulated signif-
icantly higher levels of certain PAH compounds, than clams intro-
duced in the river upstream from the discharges.
The effects of contaminants on the food web in the St. Marys
River and ecosystem is a concern that should be fully invest-
igated. Toxic compounds that are deposited in the sediments may
transfer to water, biota, and the atmosphere. Sediments may not
be the final sink for persistent contaminants (e.g. PCBs} but may
rather act as a source through redistribution of compounds to
water and the atmosphere (45).
In general, it appears that past reductions in pollutant loadings
to the St. Marys River have not been adequate to reduce sediment
contamination and impacts to benthic organisms. The contaminants
remaining in the sediment, particularly oil and grease but also
metals and PAHs, are a major concern in this channel.
4. Uses Impaired
Fish Consumption
Fish from the St. Marys River (collected below the rapids) do not
currently contain levels of organochlorines (PCBs; DDT; lindane;
2,3,7,8-TCDD) above available consumption guidelines. The con-
sumption advice tables in the 1988 "Guide to Eating Ontario Sport
Fish" indicate that mercury levels in large specimens of some
game species (i.e. lake trout, northern pike, and walleye) are
between 0.5 and 1.0 ppm and thus long-term consumption should be
restricted to 0.226 kg/wk. It is recommended that children under
15 years of age and women of child bearing age should consume
only those fish with a mercury content of less than 0.5 ppm.
Mercury concentrations in fish are believed to be the result of
natural sources.
-------
159
Young-of-the~year yellow perch collected from Sault Ste. Marie,
Ontario contained PCBs, but these concentrations (average 25 ppb)
were well below the GLWQA Objective (100 ppb) for the protection
of birds and animals which consume fish. No detectable levels of
chlorophenols or chlorinated aromatics were found in these fish.
Preliminary analysis of whole fish, showed that two bottom feeding
species from the North Channel of Lake Huron contained detectable
levels (low ppb range) of some PAHs. The only guideline for PAHs
is the U.S.EPA Human Health criteria of 31 ppb (ng/L) based
on consumption of 6,5 gm of fish per day.
Aesthetics
In recent years, the occurrence of aesthetic problems has become
less frequent than previously observed. Mats of oily fibrous
material mixed with fine wood chips are noticed only occasionally
on the Sault Ste, Marie waterfront extending as far as the Lake
George Channel. These intermittent problems are, in part, due to
the decomposition of fibers and fine wood particles found to be
prevalent in the river sediments along the Canadian shore.
Occasional oil slicks resulting from spills have been sighted on
the St. Marys River. However, the oil slicks have lately been
confined to the Algoma Slip area and very occasionally downstream
of the Terminal Basins. This suggests that the oil booms in the
slip area are effective in containing the spills but that the oil
separators at the Terminal Basins are not 100% effective.
Habitat
Commercial navigation, both the vessel traffic and engineering
modifications of the river (i.e. building of locks, canals, and
dredging), affect the aquatic biota and their habitats in the St.
Marys River. Important fish spawning and rearing habitats have
been destroyed by modification for locks and channels. Regulated
flows for hydro power development have occasionally resulted in
dewatering of the St. Marys Rapids with the resultant loss of
benthic ntacroinvertebrate and fish productivity.
The shipping channel is essentially a portion at the soft bottom
habitat which has been altered by dredging. The shipping channel
is poor habitat for benthic macroinvertebrates as only two taxa
are common, and both diversity and density are much lower in the
shipping channel than in all other habitats. Turbulence created
by passing ships and their propeller wash and oil spills are
likely the reason for the lack of benthic organisms in the ship-
ping channel. There are, however, no indications of pronounced
sediment bound toxicity in the St. Marys River as a result of
navigational activities (46).
-------
160
The aquatic organisms in the emergent wetlands may be affected by
ship passage which results in the temporary drawdown along the
shore. A study of emergent wetland invertebrate populations of
the St. Marys river showed that 18.9% of the mortality of Lestes
disjunctus was attributable to ship passage (47). Drawdown in-
duced by ship passage may also affect the survival of larval fish
that inhabit the wetlands (48) , Sediment is transported and
deposited at increased rates during ship passage, and survival of
aquatic organisms is threatened.
The present and proposed expansion of the dredging operation by
A.B. McLean Ltd. at the headwaters of the St. Marys River (White-
fish Bay) is a concern to both Ontario and Michigan citizens.
This proposed operation may allow up to 500,000 m^ per year of
sand and gravel to be dredged. Because Whitefish Bay is a major
spawning habitat for Lake Superior whitefish, the Ontario govern-
ment has requested A.B. McLean Ltd. to submit a detailed fisher-
ies assessment of the current and proposed operation.
A.B. McLean Ltd. has also altered the southwest shoreline of the
Algoma Slag Site to develop a dock facility. Development of the
dock included the sinking of an old ore carrier and the dredging
of the river bottom. Concern was expressed about the resulting
downstream siltation.
-------
161
C. SOURCES
Pollutants enter the St. Marys River system from both point and
nonpoint sources. Point sources include effluents from municipal
and industrial wastewater treatment facilities directly to the
river and indirectly via tributaries. Nonpoint sources include
atmospheric deposition, intermittent stormwater discharges, com-
bined sewer overflows, rural land runoff/ navigation, groundwater
migration (including pollutants coming from waste disposal sites
and landfills) and release from bottom sediments.
1, Point Source
An inventory of direct and indirect point source discharges to
the St. Marys River is presented in Table VI-16. Direct point
sources are defined as those facilities discharging directly into
the St. Marys River, while indirect sources are those discharging
to a tributary of the St. Marys River. There are no indirect
municipal sources. The only major indirect industrial sources
are the Algoma Steel Tube Mill and Cold Mill (cooling water only)
which discharge to East Davignon Creek.. The total 1986 annual
average flow of municipal wastewater was 59 X 103 m3/d. Indus-
trial flows were 530 x 103 m3/d.
All Ontario direct point source discharges were sampled by En-
vironment Canada and OMOE in a 3 to 6 day survey conducted in
August 1986 (49). Average daily gross loadings calculated from
the survey results are presented in Table VI-17.
Loading estimates from the August 1986 UGLCCS survey were com-
pared to estimates based on two long-term surveys,* the OMQE MISA
pilot site study (May to November 1986} and the effluent self-
monitoring program (January to December 1986). This comparison
revealed that loadings for phenols, total PAHs, ammonia, suspen-
ded solids and oil and grease from Algoma Steel are quite vari-
able and that the UGLCCS data for some parameters are probably
not representative of the operational conditions of treatment
facilities. Therefore, average gross loadings calculated from
the self monitoring or MISA pilot site data are introduced and
included in Table VI-17. Table VI-18 illustrates the marked
variability in concentrations of contaminants in effluents over a
1 year period (MISA data).
The total loading of oil and grease to the St. Marys River during
the UGLCCS survey was approximately 10,000 kg/d. An average of
9,488 kg/d was discharged from Algoma's Terminal Basins, far
exceeding the Control Order limit of 1,589 kg/d which was to be
met by December 31, 1986. The oil and grease loading from Algoma
during the UGLCCS survey was well above the average daily load as
calculated from 1986 (annual) self monitoring data {1,950 kg/d),
the August 1986 self-monitoring data (1,470 kg/d) and the MISA
-------
NSIBe- and Location
J^irec t Pi schargepg
Munic i pai
I. Sault Ste, Marie,
Ontario, East
End WPCP
2. Sault Ste. Marie,
Ontario West End
WPCP
3. Sault Ste. Marie,
Michigan, POTW
4. St. Barys Paper, Sault
Ste. Marie, Ontario
5. The Algouia Steel Corp, ,
Ltd., Sault Ste, Marie
Ontario
None
8, The Algoma Steel Corp.
Ltd. , Sault Ste. Harie
Ontario
Type of Facility
TABLE VI-1B
St. Marys River point source inventory.
Population Served/
Primary (without
phosphorus
removal)
Secondary, with
continuous phosphorus
removal
Secondary, with
chiorination with
phosphorus removal
Groundwood Pvi Ip
and faper Hill
Integrated Steel
Hill
Integrated Steel
Hill
Rece; v i na Stream
52,000
17,
\'j,OlMJ
St. Marys River
St. Marys River
St. Marys River
106,000 T/yr St. Marys River
x 106 T/yr St. Marys River
TOTAL FLOW
East Davignon
Creek
Outfall Name!3 >
Final effluent
Final effluent
Final effluent
Final effluent
Tube Mill
Outtalt
24" Ooid Miti
Ban in OTCW
Average
ftfinual Flgjj 103gj
41.7
fl.l
(1986-first year
Operation)
H.O
27.5
Terminal Basin
Bar and Strip
Lagoon
BO" Blast Funaca
Sewer
30" Slant Funace
Sewer
354
§9
4S
29
.6
.9
.5
676.2
6. •£
7.8
to
-------
TABLE VT-tl
•»
Loading aumnary of point source discharges to the Si. M«rya River (M/d),
Parameter
Flow (mJ/d)
Oil and Grease
Ammonia
Total Phosphorus
Suspended Sol Ida
Chloride
Cyanide
Total Phenols
Copper
Iron
Lead
Mercury
Zinc
Xylene
Sty rene
Benzene
Chlorof orn
Methyl ene Chloride
To Ltiene
2 , 4 , 6-Tr ichlorophenoi
2 , 4-Dimethylphenol
Total PAH'fi < 16 )
1 ,4-Diohl oro benzene
Mono A Dichloramine
Aigoma St
Steel
486,375 2
a, 441
(1950)+
(3547)**
6,254
( 3990>*
20.0
4 , 234»
SO,7fl6
10,035
<•! I 1 M
6,481
(4227)
IHH.6
10,274
( 15300 |
24,137
73,2
11
(116)
U.83
1,889
(2417)
6. 18
0.0056
37 .3
0,66
O.OB4
1.18
O.ltt
0.4
0. 5«
i .52
I. US
0. 72
( 1 . ?3 )
0.21
3.24
NA * Not Analyzed, ND = Not Detected
1 {(M>«** ** 4**°~- t-vltec-fad /i) /
* iyy6 self monitoring
* Loadings far Terminal
data.
Basins from
average
for the self
aoni tor ing
program
for 1986 substituted i
nto database
as August.
o\
Ul
loadings for those parameters considered atypical.
Hepresents data of MOE Pilot Site investigation.
Loadings from November 1»«ft to October ia«B facility monthly operating report.
-------
TABLE ¥1-18
.Mean and range of contaminant concentrations observed in Algoma Steel and St., Marys Paper effluents.
Parameter HDL
Oil and Grease 1.0 mg/L
Ammonia 0.5 "
Suspended Solids 0.1
Cyanide 0.001 "
Total Phenols 0.2 ug/L
Iron 0.05 mg/L
Lead 0.01
Mercury 0.01 ug/L
Zinc O.OOS mg/L
Algoaa Steel
30" Blast 60" Blast
Furnace Furnace
3.7
(ND-40.G)
27.17
(ND-1,060)
52.19
(2.10-353)
0.028
(ND-0,590)
473
(0.4-29,000)
8.53
(0.55-200)
O.O3B
(ND-0.59)
0.514
(ND-19,0)
0. 168
CO. 007-5 ,00)
3.6
(ND-SG.O)
0. 100
(ND-l.OBO)
30.48
( 1 .90-557)
0.025'
(ND-2,00)
3.06
( .20-28.4)
5.20
(ND-140)
0.016
(NB-2.50)
- 0.018
(ND-.230)
0.039
(ND-1 .00)
Bar & Strip
Lagoon
8.3
(NB-581)
1.356
(ND-5.30)
12.85
(3.60-59.4)
0.545
(MD-2.BQ)
15.5
(0.40-144
1 .95
IND-43.0)
0.076
(ND-0.82)
O.O09
(ND-.050)
O.B21
t .10-13.00
Terminal
Basins
7,6
(ND-48)
7.481
(ND-16.50J
28.04
(2,4-121)
0.108
(ND-0.90)
395
(1.20-8750)
a. 01
(0.36-B4.0)
0.018
(Nll-0.600)
0.045
(ND-,700)
0.021
) (ND-.500)
St. Marya
Paper
18.4
(ND-720)
0.078
(ND-720)
190
(1 .8-2150)
0.004
(ND-0.02)
20.8
(0.6-374)
1.36
(0.27-15.0)
0.030
(ND-0.830)
0.018
(ND-.050)
0.063
( .005-. 740)
ND = Not Detected at method detection limit (MOD.
Data from St. Marya River MISA Pilot Study, t«ice-weekly
(approximately 100 sanples).
cn
grab sampling, March 2 1987 to March 28 1987
-------
165
pilot site investigation data (3,547 kg/d). The reason for this
variability is unknown. The East End WWTP had the second highest
loading of oil and grease (350 kg/d) during the UGLCCS survey.
The Terminal Basins and the Bar and Strip Lagoon discharges of
Algoma steel were the principal sources of ammonia during the
UGLCCS survey, contributing an average of 5,960 kg/d and 210
kg/d, respectively. The average ammonia loading from Algoma
during this survey (5,254 kg/d) was higher than loadings based on
the 1986 annual self monitoring data which indicated an annual
average of 3,990 kg/d and the August 1986 average of 2,490 kg/d.
The average suspended solids (SS) loading to the St. Marys River
during the UGLCCS survey was 10,274 kg/d. Approximately 8,000
kg/d was discharged by industrial and municipal facilities.
Algoma Steel had the highest S3 loading (4,234 kg/d), of which
the Terminal Basins contributed 3,950 kg/d. This load was well
below the average SS load from the Terminal Basins as estimated
from the 1986 annual self monitoring data (7,790 kg/d), and the
load on August 1986 self monitoring data (6,640 kg/d).
Based on the UGLCCS data, the Terminal Basins' effluent met the
Amending Control Order limits required by March 31, 1990. How-
ever, self monitoring data indicate that the loads were above
this limit as well as the current Control Order limit (7,355
kg/d).
St. Marys Paper contributed an average SS load of 2,830 kg/d, the
second highest. Although effluent concentrations exceeded the
Ontario Industrial Discharge Objective of 15 mg/L, St. Marys
Paper in compliance with their Certificate of Approval.
Suspended solids loadings from the paper plant have declined
steadily since 1968 (Table VI-19).
The average total phenols loading to the St. Marys River during
the August 1986 UGLCCS survey was 11 kg/d. Algoma Steel con-
tributed 9.0 kg/d, of which 8.2 kg/d was discharged from the
Terminal Basins. The Point Source Workgroup Report (49) con-
sidered the measured loading from the Terminal Basins to be quite
atypical and not representative of the true loadings when com-
pared with Algoma1s 1986 annual self monitoring data (95.7 kg/d).
Loadings of total phenols to the St, Marys River from Algoma
Steel, using Algoma's data and the MISA pilot site investigation
data were 97 kg/d and 114 kg/d, respectively. St. Marys Paper
had the second highest total phenols loading during the UGLCCS
survey (0.7 kg/d). Average concentrations of total phenols mea-
sured in the Terminal Basins' effluent and St. Marys Paper final
effluent exceeded the Ontario Industrial Discharge Objective of
20 ug/L.
During the UGLCCS survey, 17 PAHs were measured in the effluents.
An average of 0.691 kg/d of total PAHs was discharged during the
survey. The highest average loading of total PAHs was from the
-------
TABLE VI-19
Historical summary of loadings to the St. Marys River (kg/d)
Parameter
1968
1973
1983
St. Marys Paper
Sault
East
Total suspended solids
BODg
Ste . Marie , Ontario
End WPCP1
BOD&2
Total dissolved solids
Total phosphorus
Total kjeidhal
Nitrate
Ammonia
Chlorine
23,800 13
68,800 5
2,146 2
14,220 IB
-
1
-
-
— 2
,400
,600
,150
,227
163
,000
10
700
,500
3,400
5,300
3,500
~
194
-
-
-
_
1 Water Pollution Control Plant.
2 Five-day biochemical oxygen demand
CTi
m
-------
167
East End WWTP (0.417 kg/d). However, this average was skewed by
high results on the first day of sampling, presumably due to an
industrial spill to the sanitary sewer system. On the remaining
5 days of the survey those compounds were not found, indicating
that, under normal conditions, PAHs would not be detected at 1.0
ug/L in the East End WWTP effluent. During the August 1986 sur-
vey, an average of 0.2 kg/d total PAHs was discharged by Algoma
Steel. All PAH compounds analyzed for were detected in the
Algoma Steel coke plant effluent which discharges to the Terminal
Basins. However, only 3 compounds were detected in the Terminal
Basins* effluent and only at trace concentrations, close to the
analytical detection limits. As with other loading data pre-
sented thus far, there is substantial variability in calculated
PAH loadings from Algoma Steel. Based on the MISA pilot site
data, an average of 1.14 kg/d total PAHs was discharged from the
Terminal Basins alone.
Total phosphorus loads during the UGLCCS survey were greatest
from the Sault Ste. Marie, Ontario East End WWTP, averaging 90
kg/d. Effluent concentrations from this primary treatment fa-
cility exceeded the GLWQA objective of 1 mg/L. Historical data
presented in Table VI-19, indicate that total phosphorus loadings
from the East End WWTP increased from 1968 to 1983, probably due
to overloading the system because of population growth. This
problem may be alleviated by the new West End WWTP which, came on-
line in 1986.
Comparisons of the point source loadings during the UGLCCS survey
(Table VI-17) indicates that Algoma Steel had the highest loading
of oil and grease (9,441 kg/d), ammonia (6,254 kg/d), suspended
solids (4,234 kg/d), chloride (18,885 kg/d), cyanide (72.9 Kg/d),
total phenols (90 kg/d), total metals (4,535 kg/d), total vola-
tiles (1.95 kg/d) and chlorinated phenols (2.69 kg/d).
In the Algoma complex, the Terminal Basins' outfall is the major
source of pollutants, followed by the Bar and Strip Lagoon for
lead, zinc and cyanide (Table VI-20). The Terminal Basins ef-
fluent comprises about 80% of Algoma Steel's effluent flow.
yearly trends in the Terminal Basins effluent quality (Figure VI-
25) indicate a steady decline in ammonia, cyanide and phenols
during the last decade. These trends are based on data collected
through Algoma's self-monitoring program.
During the August 1986 UGLCCS survey, the Sault Ste. Marie,
Ontario, East End WWTP had the highest loadings of total phos-
phorus (89.9 kg/d), mono and dichloramine (2.64 kg/d), and chlor-
inated benzenes - chloroethers (0.341 kg/d). The East End WWTP
was also the second highest contributor of oil and grease (350
kg/d), ammonia (196 kg/d), chloride (2,011 kg/d), total metals
{47 kg/d), volatiles (1.06 kg/d), PAHs (0.42 kg/d) and chlorina-
ted phenols (1.31 kg/d).
-------
TABLE Vl-20
Loading summary ot Algoma Steel effluents to the St. Marys River {k«/d|.
Parameter
Flow m3/d
Oil and Or ease
Ammonia
Total Phosphorus
Suspended Solids
Chloride
Cyanide
Total Phenols
Copper
Iron
Lead
Mercury
Zinc
Xylene
Styrene
Benzene
Chloroform
Methylene Chloride
Toluene
2,4, 6-Trichlorophenoi
2 , 4-Din>e thyl phenol
Total PAH s
1,4 Dichlorobenzene
MDL
0.1 tng/1
0.1
0.1
1.0 "
0.5 "
0.001 "
1.0 ug/1
0.005 mg/1
0.005 "
0.005
0.025 ug/1
0.005 mg/i
1.0 ug/1
1.0 "
1.0
1.0
1.0 "
1.0
2.0 "
2.0
1-2.0 "
1.0
30" Blast
Furnace
22, 100
N
N
ND
ND
504
4.9
NA
0. 147
12. 8
ND
N
0.33
N
ND
ND
0 . 002
0.013
N
ND
N
0.007
(0.038)**
N
CO" Blast
Furnace
67,980
N
tt , 3
4,5
N
759
9.8
NA
0.136
48.7
0.08
0.002
2.1
N
ND
NO
ND
N
N
ND
N
0
(0.006)**
N
Bar & Strip
Lagoon
80,395
9.9
290
ND
347
6,726
sa. a
0.8
N
507
2.93
0.007
2«.8
ND
ND
ND
0.0014
0.019
ND
ND
0,367
0 . 024
(0.022)**
0.02
Terminal
Basins
315,900
9.4BB
5.95S
(3090 J*
15.5
3,946
(7790)t»
10, 895
H8.4
8, IB
(95.7 )«
N
1,178
{ 1685 >**
2.6
0.003
3.2
0.41S
0.084
1 , 12
ND
0.10?
0.277
1.48
0.892
0.157
( 1.14 )**
0-135
N = Negative Net Loading, ND = Not Detected, NA = Not Applicable, MDL = Method Detection Limit
** June 1986 OMOE MISA pilot site investigation (MDL=10 ng/L).
% 1986 average self monitoring program of Algoma Steel.
a\
00
-------
169
18-
14
o>
12-
o
X
O 10
z
o
g
^ 8
8 6
cc
UJ
A Ammonia
O Phenols
* Cyanide
• Terminal basin
Algoma Steel total
1972
1975
1978
1981
1984
FIGURE VI-25. Annual average daily loading from Algoma Steel
-------
170
No loadings were obtained for the Sault ste. Marie, Michigan
Wastewater Treatment Plant (WWTP) for 1986 as the plant was being
upgraded. Average suspended solids, total phosphorus and BOD
loadings calculated from the facility's monthly operating reports
(November 1986 to October 1987) were 47.3 kg/d, 6.3 kg/d and 53.6
kg/d, respectively. For the period of June 1987 to June 1988,
inclusive, the reported average monthly loading (and ranges) for
these three parameters were 79,9 (27.7 - 303}, 13.6 (4.6 - 11.4)
and 58.4 (11.5 - 102) Kg/d, respectively with flows averaging
10,754 (6,232 - 15,390) m3/d.
In general, the three Ontario tributaries {East Davignon, Port
and Bennett Creeks) do not appear to be significant sources of
industrial contaminants to the St. Marys River when compared to
the other sources. However, East Davignon Creek had the highest
loadings for all parameters monitored. Total PAH loadings from
East Davignon Creek (0.04 kg/d) during the 1986 MISA pilot study
were comprised mainly of benzo(k)fluoranthene, dibenzo(a»h)-
anthracene, fluoranthene, pyrene, indeno{l,2,3-c,d}pyrene and
benzo(g,h,i)perylene. These compounds are related to the Algoma
Steel operations. Although total PAH loadings from Bennett Creek
in 1986 were an order of magnitude lower than from East Davignon
Creek, the detection of coal tar in this creek during 1987 indi-
cates the potential for additional inputs from this area.
2. Nonpoint Sources
Nonpoint pollutant loads are more difficult to assess than point
sources. Nonpoint source pollutant loads are introduced into the
environment from diffuse sources which enter the water system
through a wide range of pathways. Furthermore, nonpoint pol-
lutant loads are dependent on many uncontrollable natural phenom-
ena such as rainfall, wind events, soil types and geological
conditions. Due to the nature of nonpoint source pollutant
loads, assessment of their magnitude and impacts is often dif-
ficult.
Urban Runoff
i) Michigan
The City of Sault ste. Marie, Michigan has a combined storm and
sanitary sewer system with ten Combined Sewer Overflows (CSOs) at
the Edison Sault Electric Company Power Canal and along the
river. A study completed in 1978 indicated that there were no
adverse impacts from these CSOs on river water giiality. The WWTP
has since been upgraded and expanded (1986) and impacts are
therefore expected to be minimal. However, the presence of CSOs
indicates the occurrence of sporadic loadings to the river.
Also, there are 8 storm drains discharging into the St, Marys
-------
171
River, 15 to Edison Sault Electric Company Power Canal, and 11 to
three minor tributaries {Seymour Creek - 2; Ashmun Creek - 7; and
Mission Creek - 2), No loading estimates are available.
iij Ontario
Surface drainage in the City of Sault Ste, Marie is provided by
storm sewers which discharge either directly into the St. Marys
River or into one of several creeks draining into the river.
Stormwater also enters the sanitary sewer system and has caused
hydraulic overloading of the Sault Ste. Marie East End WWTP.
Three stormwater outfalls were sampled (50) in each of the sub-
areas (residential, industrial and commercial) as shown in Figure
¥1-26. The mean concentrations of measured parameters are sum-
marized in Table VI-21.
A methodology for estimating loadings of contaminants has been
developed and applied to the City of Sault Ste. Marie, Ontario
(50). Annual contaminant loading estimates (Table VT-22) were
obtained by multiplying the annual flow volumes by the mean con-
centrations. The loading calculations were done separately for
the land use types studied and the total loading was obtained as
the of individual components. A summary of total stormwater
loadings to the St. Marys River is given in Table VI-23, and
where applicable, the low and high estimates are given.
In terms of loading magnitudes, there is a great deal of consis-
tency among all three subareas. In general, ,the loadings can be
ranked in a descending order as follows: chloride, iron, oil and
grease, ammonia, phosphorus, lead, zinc, copper, nickel, phenols,
PAHs, cyanide, cadmium, cobalt, Hg, PCBs (total), HCB.
Rural Runoff
i) Michigan
The St. Marys River geographic area encompasses 203,546 ha with
the predominate land use being forest (73%). Wetlands cover 11%
of the area, while cropland accounts for 11% of the land use.
Due to the agricultural base of Chippewa 'county, the nonpoint
source pollutants of concern are sediments, nutrients and pes-
ticides .
Estimated annual soil erosion for the St. Marys River geographic
area is 173,889 tonnes. The total estimated soil loss included
wind, sheet and rill erosion categories. It does not include
cropland ephemeral gully erosion which has been documented to be
a significant source of erosion in some flat-lying areas in the
State of Michigan. Nonirrigated cropland erosion accounts for
100% of the total estimated erosion.
-------
i Sampling Sites
1 Georgina St.
2 Station Mall
3 Hudson St.
Storm Sewer Outfall
FIGURE Vl-26. Storm sewer outfalls and sampling locations in
Sault Ste. Marie, Ontario.
-------
TABLE VI-ZJ
Mean concentrations observed in urban runoff in Sault Ste. Marie, Ontario.
Parameter Units
Ammonia (N) mg/L
Total Phosphorus "
Chloride
Cadmium "
Cobalt "
Copper "
Iron "
Lead "
Mercury " 0.
Nickel "
Zinc "
Oil & grease "
Phenols "
Cyanide "
HCfl ng/L
DCS
Total PCBs "
17 VAUs "
I Equivalent mean concentration.
2 Mean of concentrations detected
0
0
0
0
0
0
0
0
MDL
.001
.001
.050
.001
.001
.001
.020
.001
00002
0
0
0
0
.001
.001
0,1
.001
.010
0.4
1.0
a.o
50
in all
Residential
0.87
0.36
0,00
0.009
0,00
0.02
0.042
5. a
0.09
0.000032
0.012
0.027
0. 29
2.5
0.0185
0.001?
0.23
0.43
-
26
11,500 •
23,900
three subareas.
Stormwater
Commercial
0.42
0.23
1421
2B51
0.0011
0.008
0.0062
0.00
0.02
0.00352
0.063
11.4
0.21
0.000013
0.000021
0.014
0.024
0.29
2.6
0.0120
0.002?
O.15
0.42
-
40
4,700
5,100
Industrial
0.49
0.1?
0,00
0.009
O.OO
0.02
0.031
8.3
O.li
0.000030
0.000033
0.003
O.021
0.21
2.8
0,0100
0.0030
0.00
0.40
—
13
3,000
3,500
Note:
At some sites large variations in concentrations of specific compounds were observed and/or a significant
percentage of data was below the detection limits and for that reason two estimates, low and high, are given.
-------
174
TABLE VI-22
Summary of loadings in urban runoff from the Sault Ste. Marie,
Ontario area.
Parameter Total Stormwater Total Stormwater
(kg/yr) (kg/d)
Ammonia (N)
Phosphorus
Chloride
Cadmium
Cobalt
Copper
Iron
Lead
Mercury-
Nickel
Zinc
Oil 4 grease
Total Phenols
Cyanide
HCB
Total PCBs
17 PAHs
9,800
4,100
1 ,850,000
3,700,000
2.0
78.0*
0
263(46 )*
572
91, 100
1,550
0.4
144
338
3.6SO
33,300
196
27
0,002
0.006
0.4
3.2
122
23S
28.8
11.2
S,068
10,137
.0055
,0214
0
0.721
1.57
i§2.3
4.25
0,0011
0,395
G.92S
10,03
91.2
0.537
0.074
S.4S x 10-*
16.43 x !Q-«
.0011 '
.009
.334
.852
* Loadings calculated from data above the detection
Note:
At some sites large variations in concentration and/or a
significant percentage of the data was below the detection limit
and thus two loading estimates, low and high are given.
Daiiy loadings have been calculated assuming that annual loadings
were uniformly distributed throughout the year.
-------
TABLE VI-23
Loading summary of nonpoint source discharges to the St. Marys River (kg/d).
Parameter
Urban Runoff
Ontario
Rural Runoff
Michigan
( 1 ivestock &
aoii erosion)
Atmospheric
Deposi tion
Ontario
Groundwater
Michigan
Flow (m3/day)
Oil and grease
Ammonia
Total phosphorus
Suspended sol ids
Chloride
Cyanide
Total phenols
Copper
Iron
Lead
Mercury
Zinc
Xylene
Stryene
Benzene
Chloroform
Methylene chloride
Toluene
2,4,6-Trichiorophenoi
2,4-Dimethylphenoi
Total PAHsUG)
Di-n-octyIphthaiate
1,4-Dichlorobenzene
Mono & Dichioramine
35,077
91 ,2
26.8
11.2
5,068-10,137
0.074
0.537
1.5?
252
4.3
0.0011
10.03
6.3B
184,150
1,400
ui
0.334-0.652
0.247
-------
176
Major sources of nutrients, in particular phosphorus, within the
St. Marys River drainage area are fertilizer (commercial or
manure spreading), livestock operations and soil erosion. It is
estimated that a total of 5,18 tonnes of phosphorus are delivered
per year to the water resources from livestock operations while
soil erosion annually contributes approximately 1.18 tonnes of
phosphorus to the water resources. A comparison of sources of
phosphorus indicates that soil erosion contributes approximately
19% of the volume contributed by livestock operations and soil
erosion. No estimates of pesticide loadings to the St. Marys
River have been made.
ii) Ontario
No estimates of loadings from rural runoff are available for
Ontario.
3, Atmospheric Deposition
Michigan
There are no estimates of atmospheric deposition available for
the Michigan area for any of the UGLCCS parameters.
Ontario
Estimates of atmospheric loadings were attempted only for PAHs,
Boom and Marsalek £51} collected 20 snowpack samples located in a
grid centred around the City of Sault Ste. Marie, Ontario in
order to establish the areal distribution of PAH depositions
(Figure ¥1-27}.
The areal distribution of PAH loadings in. the snowpack tends to
indicate that industrial emissions are the main source of PAHs to
this area, with the highest loadings observed immediately down-
wind from the steel plant. Chemical finger printing indicated
that the westerly stations were dominated by steel plant emis-
sions, with the easterly stations being influenced by the other
urban sources. The total quantity of PAHs stored in the snowpack
in the study area estimated to be about 18 kg for the 11 week
accumulation period. PAHs stored in the snowpack are quickly
released during the snowmelt period and thereby create a shock
loading on the receiving waters (52). The average concentrations
of total PAHs in fully mixed meltwater from the study area was
estimated to be about 3 ug/L.
Although the data base refers to winter conditions, in industrial
urban areas there are no seasonal variations in PAH depositions
(53), Hence, the annual PAH loading extrapolated from the 2.5
month accumulation would be nearly 90 kg/yr. Based on this
-------
LEGEND
STUDY AREA BOUNDARY
SAMPLING STATION
HIGHWAY
STEEL COMPANY
PROPERTIES
RAILROAD
CREEK, LAKE
INTERNATIONAL BOUNDARY
SAULTSTE. MARIE
ONTARIO
Km
FIGURE VI-27. Snowpack PAHs sampling grid in Sault Ste, Marie, Ontario,
-------
178
annual loading, estimates of annual atmospheric deposition rates
for the most common PAHs found in the snowpack ranged from 13.6 •
21.8 kg/yr for phenanthrene; 17.2 -27.1 kg/yr for fluoranthene;
10.4 -16.9 kg/yr for pyrene; 1.5 - 5.2 kg/yr for both benzo{a)-
pyrene and benzo(b)fluoranthene; and 2.2 - 5.7 kg/yr for benzo-
(k)fluoranthene.
4. Contaminated Sediments
studies have shown that polluted sediments have a direct impact
on associated biota {29} and can be significant sources of con-
taminants to both the water column and aquatic organisms (31).
Furthermore, such sediments can continue to be a source long
after the external inputs (point and nonpoint) have been elimina-
ted (31). However, the actual amounts of contaminants released
from the sediment to the water column and. organisms of the St.
Marys River have not been quantified.
5. Groundwater Contamination/Waste Disposal
Michigan
Groundwater movement was investigated in an area extending 19 km
inland along the St. Marys River from Whitefish Bay to Neebish
Island. An inventory of active and inactive waste sites within
19 km of the St. Marys River was conducted as part of this inves-
tigation (19). Groundwater in the St. Marys River study area
flows radially towards the St. Marys River. Total Michigan
groundwater discharge directly to the St. Marys River is 2,156
L/s and contributes about 1,400 kg/d chloride (Table VI-23).
Groundwater discharge from outside these areas contributes to the
stream flow of the tributaries. Groundwater within the study
area contributes about 47 percent of tributary flow.
Twelve sites of known, or potential groundwater contamination in
the study area were identified and ranked. The majority of sites
are solid waste landfills, storage sites and spills. Ranking of
sites was based on their potential for contributing contaminants
directly to the St. Marys River via groundwater by evaluating the
hydrogeology, nature of waste material, and the distance to the
St. Marys River.
One round of samples for analyses were collected from four wells
installed by the United States Geological Survey (USGS) and three
private wells. Some wells sampled by USGS were down-gradient
from waste or spill sites including a well down-gradient from the
Cannelton Industries Tannery waste site. Other locations were
chosen to provide background information.
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179
Organic compounds were generally less than their limits of analy-
tical detection, Phthalate esters were detected at Cannelton
Industries Tannery disposal site and downgradient from the Sault
Ste. Marie disposal site (Union Carbide). It is possible, how-
ever, that the phthalates were related to shipping or laboratory
contamination.
All samples exceeded GLWQA specific objectives and PWQO for zinc
and total phenols and most exceeded the PWQO for phosphorus.
Several other samples exceeded U.S.EPA AWQO for acute and chronic
effects for mercury, lead and zinc. U.S.EPA Drinking Water Maxi-
mum Contaminant Levels were generally not exceeded except at the
well at Cannelton Industries for chromium (primary standards) and
iron and zinc (secondary standards).
Trace metal concentrations are based on nonfiltered well water
and are probably not reflective of groundwater that discharges to
the St. Marys River which is believed to be free of fine particu-
lates. Thus, computation of loadings to the St. Marys River of
chemical substances transported by groundwater is not currently
feasible.
Local impacts on the water quality of the St. Marys River are
posed by only one site in Michigan: Cannelton Industries Tannery
disposal site. Impacts on the St. Marys River due to this site
may occur through a combination of groundwater discharge, surface
runoff, and erosion of contaminated soils and waste into the
river.
State and federal regulatory file data indicate that high levels
of chromium and other metals exist at the Cannelton Industries
Tannery site. Down-gradient movement of contaminated groundwater
from this site was detected by analyses of the well water. A
remedial investigation/feasibility study has been initiated at
this site under Superfund authorization.
Potential minor impacts on St. Marys River water quality are
posed by the Sault Ste, Marie Disposal (Union Carbide) waste lime
pile located near the river. This site is also known to contain
cyanide contaminated wastes. The Superior Sanitation Landfill (3
Mile Road), containing municipal and light industrial refuse as
well as sludges from the Sault Ste. Marie WWTP, is another poten-
tial source to the river.
Ontario
Two waste disposal sites were identified in Ontario. The Algoma
Steel Slag Site was characterized as having a definite potential
for impact on human health and safety. At this site, approxi-
mately 718,600 tonnes of solid waste and 66,800 tonnes of liquid
waste disposed each year. The predominant waste is slag from
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180
iron and steel operations. However, lime, industrial refuse,
waste acid and oil, coke oven gas condensate, and sludge are also
disposed on the site.
Detailed hydrogeological investigations at the Algoma Steel Slag
Site have established that groundwater flows toward the St. Marys
River, either directly, or indirectly by discharge to the Algoma
Slip. High hydraulic conductivities in surficial slags and sands
suggest rapid groundwater flow. Several investigations have
documented groundwater and surface water contamination with
metals, ammonia, cyanide, and PAHs which may be associated with
this site. Work completed to date on the Algoma Slag Site has
not conclusively proven the significance nor the magnitude of
contaminants migrating off the site and impacting on adjacent
groundwater, surface waters or biota. In early 1988, OMOE
initiated a two year intensive study to quantify loadings and
impacts associated with leachates from the site.
The other site in the area, the Sault Ste. Marie (Cherokee) Land-
fill is believed to have a negligible impact on surface waters of
the St. Marys River, This landfill is licensed to handle munici-
pal waste composed of 60% domestic waste '(200 tonnes/d), 10%
commercial waste (35 tonnes/d) and 30% sewage sludge (100
tonnes/d).
As summarized in Table VI-23, the majority of data on nonpoint
source loadings is for urban runoff in Ontario. Therefore, few
comparisons can be made between this source and other nonpoint
sources of pollutants to the St. Marys River,
6. Navigation
The average number of vessels passing through the locks has de-
creased from 26,122 vessels in 1953 to 12,712 in 1970, and to
8,345 in 1986, The vessels carry mainly crude oil, grain, steel,
coal, petroleum products, taconite and iron ore between Lake
Superior and the industrial centres on the lower lakes.
Significant enhancement of the primary productivity takes place
immediately after tanker passage (46) . These observations sug-
gest that there is an absence of pronounced sediment-bound toxic-
ity in the St. Marys River.
7. Spills
Spills can be a significant source of contamination to a river
system and constitute a major concern. The concern is that the
river may, during a short period of time, be subjected to a shock
contaminant loading that may be several orders of magnitude
greater than the annual loading. A summary of spills from Algoma
-------
TABt.B VT-24
niBJttry of spills to the St, Marys River? i^auadian sources I 1983~l£JH6)
Dat. c o f Occu rrenee
Material/Source
Action
Algona Steel :
March 7, », 9/U3
July Z6/B3
Novenber i
January K4/B4
December 13/H4
January 22/85
Aprii 17/85
August 11/86
August 1S/H6
August
High phenols/ Terminal Hafiins 2,200, 1,870
3, 100 pp^» rtjspttct.
De-pheno11 zed liquor/Tank Leak
De-Phenol. Itquor/ptn-hole in tank/
min. ^uant. lost
500-1,000 Ig
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182
Steel and St. Marys Paper (Table VI-24) indicated that the spill
on March 7,8 and 9, 1983 from the Terminal Basins may represent a
short-term phenol loading of about 2.4 tonnes to the St. Marys
River which is 1 to 2 orders of magnitude greater than the normal
loading from this discharge (Table VI-20). This demonstrates a
significant shock loading to the river over a short period.
Over the past 50 years there have been numerous coal tar and
product spills on Algoma and Domtar properties in proximity to
Bennett and Spring Creeks. The spills have been from tank over-
flow, pipeline breaks and process leaks. These spills have been
up to 10,000 gallons or more into creeks and onto slag-filled
shorelines.
In May of 1987, an oil slick was observed on Spring and Bennett
Creeks. Upon further investigation, the creek beds were found to
contain coal tar saturated sediments to depth in excess of .75 m
and a dense oily free-phase liquid (suspected of being coal tar
and/or creosote) was flowing along the surface of the sediments.
Both companies were directed to remove any free-phase material
from the creek bed. and to install coffer dams and/or sandbags to
prevent the flow of free-phase material to the St. Marys River.
The companies were also directed to conduct studies to determine
the extent of contamination of the creeks and adjacent soils, to
determine the source(s), and to recommend remedial options to
prevent further contamination of the St. Marys River.
8. Summary
Table VI-25 summarizes the relative contributions of point and
nonpoint source loadings of selected organics and heavy metals to
the St. Marys River. In general, the river is subject to a daily
loading of 14 tonnes of suspended solids, 5 tonnes of free am-
monia, 4.5 tonnes of oil and grease, and 3 tonnes of iron. Load-
ings of other contaminants such as PAHs, volatiles, phenol and
cyanide ranged from 3 kg/d (PAH) to 117 kg/d (phenols),
The high loadings of suspended solids and oil and grease repre-
sent a major factor in the destruction of river habitat as re-
flected by an adversely impacted benthic community along the
Ontario shoreline of the river.
Although loadings of contaminants from nonpoint sources were not
sufficient to set a priority on these sources, available informa-
tion indicated that up to 50% of PAHs, zinc and lead loadings to
the river may be attributed to nonpoint sources.
-------
TABLE vi-25
Loading summary of point source* and nonpoint summary to the St. Marys River (kg/di.
Sou rce
Parameter
Poi i*t Sourc es
Industrial
Munic i [>al
Tributary
Nonpoint
Urban 0.
Rural
Atmospheric
Grounciwater
TOTAL
PAH 3
1 .25
0.423
0.051
334-0. 652
NA
O.Z4T
NA
2.621
Suspended Oil 4
Voiatiles Solids Greaae Ammonia
3.1 11,090 3,810 4,395
1.14 9B7 3«3 21O
ND 2,224 NA 21
NA NA at 27
NA NA NA NA
HA NA NA NA
NA NA HA NA
4.24 14,301 4,264 4,«53
Total
Lead Zinc Iron Cyanide Phosphorus
7.4 38 2,230 74.0 25
1.2 2.3 48 NA 102
NA 0.94 8$ 0-32 3.2
4.3 10.0 2Si! 0.074 11
NA NA NA NA fi,4
NA NA NA NA NA
NA NA NA HA NA
12,9 51 2,«75 74 14fl
Total
Phenols
115
O.S3
0.69
0.54
HA
NA
NA
118
00
NA - Not Available, ND - Not Detectable
* - Various data sources (Table VI-171
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184
D. DATA QUALITY ASSESSMENT
The OMOE data for PAHs in caged clams and surficial sediments was
generated by an external contract laboratory that performed poor-
ly in the UGLCCS round robins (Chapter IV). Consequently, this
data was checked by OMOE GC/MS laboratory staff and only after
their data quality concerns were addressed and the data declared
qualitatively and quantitatively accurate was this information
used in the report.
Some of the effluent and river water samples analyzed, by the OMOE
laboratory for total phenols in 1986 were flagged as possibly
having been contaminated by phenolic substances due to an im-
proper cap liner (i.e. concentrations may have been reported
higher than actual). However, this data was used when subsequent
sampling, during the 1987 MISA pilot site surveys, revealed simi-
lar concentrations in effluents and water.
In the Canadian point source study, the federal laboratory which
analyzed PAHs had somewhat lower method detection limits (1-2
ug/L) than did the OMOE lab analyzing samples for the MISA pilot
site study during 1986 (10 ng/L). Because this difference af-
fected the quantification of PAH loadings from dischargers, the
UGLCCS data set was supplemented by the MISA data.
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185
E, PROCESS MODELING
1) Physical: Hydrodynamics, wind, Waves and currents
For the purpose of the modeling study, the St. Marys River has
been divided into an upper reach - above the regulatory works,
and a lower reach - below the regulatory works.
Upper St. Marys River
The primary factors involved in the flow distribution in the
upper river are gravity, wind, bed friction and the associated
pressure forces. One of the causes of water movement in the deep
channels of the upper St. Marys River is the inertial forces
exerted by the large inflows from Lake Superior through the nar-
row mouth at Pointe Aux Pins. In the localized shallows of Leigh
Bay and Pointe Aux Pins Bay, an appreciable influence on the
water circulation is exerted by wind stresses.
One objective of the modeling was to describe the hydrodynamics
of this area using mathematical models. A three dimensional
steady state finite element model was applied to this area. The
mathematical formulations were based on the three dimensional
equations for conservation of mass and momentum. The principal
assumptions used were:
i) the pressure was assumed to vary hydrostatically;
ii) the rigid-lid approximation was made, i.e. the vertical
velocity at the undisturbed water surface was assumed
to be a constant value of zero;
iii) eddy coefficients were used to account for the tur-
bulent diffusion effects (the vertical coefficient was
assumed constant while the horizontal coefficients were
assumed to be zero); and
iv) the dimensions of the study area were small compared to
typical weather systems, so that the geostrophic wind
is assumed uniform over the entire area.
The basic equations (55,56) contain three empirical constants,
i.e., the vertical eddy diffusion coefficients, the wind drag
coefficient and the bottom slip coefficient, which cannot be
determined from theory alone but must be tuned by means of proper
field data in such a way that agreement between the model and
prototype is satisfactory. A sensitivity analysis involving a
large number of computer runs was made for these coefficients in
order to assist with the calibration process.
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186
The model was calibrated and verified using current meter data
from the following sources:
i) the U.S. Corps of Engineers;
ii) the Ontario Ministry of the Environment;
iii) Integrated Exploration Limited; and
iv) aerial photographs taken of the area.
The model indicates that the upper river is highly responsive to
wind speed and direction. Its dynamic behaviour is important in
the shallow bays where gyres readily form. Examples of gyres
formed under no wind and north wind (19 km/hr) conditions are
shown in Figures VI-28 & 29.
Some of the contaminants {e,g. PAHs) in the bays are associated
with the movement of fine grained sediment particles; it is ex-
pected that the gyres will play a significant role in the trans-
port of contaminants from the area of the slag site to Leigh and
Point Aux Pins Bays. The model has indicated that up to two
strong gyres can be formed simultaneously.
Combined with existing field data on current measurements in this
area, the calibrated model provides a better understanding of the
cause and effect relationship between the, wind and the circula-
tion patterns in the upper river. This will eventually lead to
the construction of more detailed fate models for management
purposes. In addition, the model may provide new insights to the
complex hydrodynamics of the upper river for those who are in-
volved in collecting field data for the area.
Lower St. Marys River
The lower river is a nonuniform natural channel with slightly
over half of its width dredged to a minimum of 8.5 m for the
passage of ships. The velocity field data on the lower river is
available from the U.S. Corps of Engineers. The data indicate
the presence of some dead zones and re-circulation zones in the
river due to natural or man-made protuberances from the shore-
line .
The lower river was simulated by KETOX (57). This is a model
that has a steady-state depth averaged hydrodynamic submodel
coupled to a convection-diffusion (mixing) submodel. KETOX model
has the following features:
i) it provides a forward marching solution to the con-
tinuity and momentum equations for the river (58);
ii) it provides solution for the lateral dispersion coef-
ficients across each cross-section of the river based
on the turbulence transport equations (K and E); and
-------
3.20
2.40 ,
-------
41
OJ
c
I/I
"f~
Q
3.20
2,40
1.60 .
0.80
0.00
0.00
CXI
CO
0.80
1.60 2.40 3.20
Distance in Miles
4.00
4.80
5.60
FIGURE VI-29. Dimensionless stream function circulation pattern
(north wind).
-------
189
iii) it can accept discharges from multiple outfalls.
The hydrodynamic component of KETOX was calibrated using U.S.
Corps of Engineers (COE) 1984 field data based on current meter
measurements and drogue surveys,
2. Physical-Chemical-Biological: Fate and Transport Models
The contaminant dispersion submodel of KETOX was calibrated using
the 1974 OMOE phenol loadings and ambient measurements (10), The
Model was subsequently verified with the 1983 OMOE phenol field.
data. The calibration and verification are illustrated in Figure
VT-3Q which is a dimensionless plot of the measured and predicted
phenol concentrations along the Canadian shoreline starting from
the Terminal Basins outfall location for the years 1974 and 1983.
The mixing model {K-E model) for the lower river {including the
Algoma Slip and Control Structure) has been calibrated for hydro-
dynamics. For steady-state loading, isoconcentration maps can be
developed with longitudinal resolution of the order of 15 m and
lateral resolution as low as 1 % of the flow in the reach. This
permits a reasonably accurate zone of effect or mixing zone to be
defined so that various loading scenarios can be compared and
evaluated.
Table V.I-26 illustrates the longitudinal extent of the mixing
zones associated with discharge from the Terminal Basins under
the average summer river flow (2,450 m3/s). The 1986 loadings
for ammonia and cyanide (4,066 and 29 kg/d, respectively) will
result in a mixing zone equal to or less than 100 in where the
GLWQA and OMOE Water Quality Objectives are met. Also, there are
no toxic effects within the mixing zone, although the effluent is
toxic. The mixing zone associated with the phenol loadings from
the Terminal Basins extends at least 7 3cm along the Ontario
shore. Although the frequency of occurrence of low river flow
(1.53 x 10^ L/s) is about 0.1%, an estimate of the mixing zone
associated with the 1986 loading is predicted to provide insight
into the need for urgent reductions of phenol loadings. Figure
VI-31 indicates that transboundary pollution may occur under the
lowest flow possible.
Oil and grease within the bed sediment constitutes a major factor
in the absence of Hexagenia. To model the impact of discharged
oil and grease upon bed sediment, partitioning between water and
sediment phases must be considered. For demonstration purposes,
it is assumed that the concentration of oil and grease within the
water column should not be more than 10% 'above the upstream back-
ground level (i.e., about 0.5 ppm). Using this guideline, the
zone of effect is about 0.8 tan. This same arbitrary guideline
may be used for suspended solids, in order to minimize the amount
of the organic portion of solids (which is responsible for most
-------
1.0
!.!
2s
o*-
u
m
a
D
— O
*- 0}
c o
0) o
o—
° ca
O
O
m
O
x
O
-Q
C
3 C
O O
A
•* Z
O 4-
ss
If
0) a
00
§.£
O
O
m
O
b
O
.01
.001
O 1974 Predicted Variable Conditions
H 1974 Measured
Q 1983 Predicted Variable Conditions
0 1983 Measured
U3
O
I
_J I 1 i t I i 1
10
wo
1000
FEET
10000
1O
100
METRES
1000
10000
FIGURE VI-30. Predicted and measured phenol concentrations versus
distance along tlie Canadian shoreline.
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191
TABLE ¥1-28
Point source impact zone predictions from the Terminal Basins
under average summer river flow.
Parameter Ii86 Loads Length of Zone for 1988
_ 1 kg/d 1 Terminal Basin Loadi < kml
Ammnionim 4
Cyanide 29** <0.1
Phenoi 114*** >7.0
Gil 4 Grease 1,413* 0.8
Suspended Solids 7,788* 7,0
Note: Loads from Table VT-19
* Average of self monitoring program of Algoma Steel
** UGLCCS data.
*** 1986 MISA Pilot Site data,
TABLE VI-27
.Loadings (in kg/d) required to limit point source impact zones
to 300 and 100 m from the Terminal Basins, under average summer
flow {see text) ,
Parameter
Phenols
Oil & grease
Suspended solids
300 m Impact Zone
li
950
1,900
100 m Impact
12
590
1.200
Zone
-------
Zon* of tfftct far 100 kg/a
FIGURE VI-31. Zone of exceedence of phenol concentration of 0,002 mg/L
for loads of 100 kg/d from the terminal basin under the
St. Marys River's lowest flow conditions.
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193
contaminants}. Thus the concentration of suspended solids should
not exceed about 1 ppm within the water column. This would
result in a zone of effect of about 7 km,
These modeling tools may be used in a "regulatory mode" to derive
the maximum effluent loads so as to meet the objectives and
guidelines at selected distances downstream of any outfall. Table
VI-27 summarizes these calculations for phenol, oil and grease,
and suspended solids discharged from the Terminal Basins under
the average summer flow in the river.
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194
P. GOALS AND OBJECTIVES FOR REMEDIAL
The goals of remedial measures in the St. Marys River should be
the ultimate elimination of unacceptable adverse impacts on
aquatic life and to ensure that the water is acceptable for
drinking and recreation. Objectives will focus on the need to
decrease the Input, transport and biological availability of
conventional and toxic pollutants in the St. Marys River.
Exceedences of water quality objectives are mainly restricted to
a narrow band along the Ontario shore downstream of Algoma Steel
and St. Marys Paper effluent discharges. Partial recovery from
the effects of these inputs occurs downstream; however, dis-
charges from the nonpoint sources (e.g. urban runoff) and the
Sault Ste. Marie, Ontario East End WWTF delay complete restora-
tion of satisfactory water quality with respect to several con-
taminants until Lake George.
Objective 1: Reduce point source loadings of phenols, oil and
grease, iron, phosphorus, and fecal eoliform
bacteria to meet water quality objectives through-
out the river.
Objective 2; Eliminate point source impact zones downstream of
each outfall through the reduction {to zero) o£
chronic and acute effluent toxieity.
Although no water quality criteria exist for suspended solids,
there is some indication that suspended solids and the associated
contaminants may be a concern in the St. Marys River. Contamin-
ants adsorbed onto the particulates can be deposited locally or
transported long distances before settling out, thereby increas-
ing the downstream extent of their impact,
Obj eetive 3: Reduce suspended solids loadings to the river,
The full environmental'significance of PAHs in the St. Marys
River is presently difficult to evaluate due to insufficient
data, and lack of compound specific toxicity information and
standards. However, concentrations of total PAHs and selected
PAHs, such as ben2o(a)pyrene, were above available guidelines in
river water and surficial sediments at one or more locations in
the Sault Ste. Marie area. The presence of elevated levels of
PAHs in caged clams introduced to the St, Marys River indicates
that these compounds are potentially available to biota.
Objective 4; Reduce PAH Point and Nonpoint Source loadings to
the river.
The benthic macroinvertebrate community in the St, Marys River is
degraded along the Ontario shoreline downstream to Lake George.
Generally, degraded communities exist in the vicinity of indust-
-------
195
rial discharges and in areas where sediments contain high con-
centrations of metals and organic contaminants. General reduc-
tions in conventional pollutant loadings from the major Ontario
point sources do not appear to have resulted in proportional
improvements in the health of the benthic- community and may be
related to occasional spills or persistent effects of contamina-
ted sediments. The correlation of high oil and grease levels in
sediments with low densities of Hexagenia nymphs indicates that
reductions in the levels of oil and grease may be an important
factor in the re-establishment of a healthy benthic community.
Depending on their geochemistry and organic content, polluted
sediments may be a source of contaminants (e.g. heavy metals) to
benthic organisms. This availability of contaminants may affect
the benthic community as well as higher trophic levels.
Objective 5: improve the benthic niacroinvertebrate community
along the Ontario shoreline by reducing contamin-
ant loadings and by the appropriate remediation of
contaminated sediments.
In addition to point and nonpoint discharges of contaminants,
manmade modifications to the upper St. Marys River have resulted
in changes and/or destruction of important benthic habitats and
fish spawning areas (e.g. St. Marys Rapids), Currently, there is
concern that human activities (e.g. aggregate reclamation) may
result in further destruction of habitat due to physical removal
and/or increased siltation.
Objective 6: Prevent further benthic and fish spawning habitat
degradation through the careful evaluation of
proposed activities and modifications in the St.
Marys River and upstream.
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196
G. ADEQUACY OF EXISTING PROGRAMS AND REMEDIAL OPTIONS
1. Existing Regulatory Programs (see Chapter III)
Ontario
i) Algoma Steel Operations
Table VI-28 shows Algoma1s current discharge requirements. On
June 13, 1983, Algoma Steel was served with an Amended Control
Order aimed at controlling contaminants such as phenols, cyanide,
ammonia, oil and grease and suspended solids which were found to
be in contravention of Ontario's Environmental Protection Act.
Since the issuance of the Control Order, Algoma's economic situa-
tion deteriorated to the point that the company could not fulfill
all the Control Order requirements or dates of completion. As a
result, on November 4, 1986, the Control Order was amended to
extend the dates for compliance. In the spring of 1988 OMOE and
Algoma negotiated ammendments to the 1986 Control Order to allow
the operation of the #7 coke oven battery and to advance air
emission requirements for the Algoma complex. The order was
issued September 23, 1988 and included the following require-
ments :
Action Deadline
- Reduce oil and grease loading to
1,023 kg/d March 31, 1990
- Reduce total suspended solids loading
to 5,108 kg/d March 31, 1990
- Reduce phenol loading to 22.7 kg/d June 30, 1989
- Reduce cyanide and ammonia to below
level graphically illustrated by the Feb. 15, 1989
diagonal line shown in Figure VT-32
ii) St. Marys Paper
The St. Marys Mill is not subject to federal requirements because
it existed prior to 1971 when the Federal Pulp and Paper Effluent
Regulations were first promulgated. However, the federal limits
may be used as a guideline and OMOE has incorporated the federal
limit for total suspended solids (TSS) into the Certificate of
Approval for the mill. This limit is based on the production
rate for various unit processes, which varies from day to day.
-------
TABLE V1-2B
Comparison of point source effluent levels and permit requirements.
Algoma Steel St. Marys Kast End West End Michigan
Current Requirements Terminal Basins Paper WWTP WHTP WHTP
(Control Order)
Oil and grease — 1,413*
1 ,58a kg/d
Suspended solids - 6,717*
1,355 kg/d
Phenols - 22.1 kg/d 95.7
(Compliance date OK.30.tSil)
Cyanide -» Ammonia 0/15 rog/L /
See graph (Fig. VI-32) 11.5 mg/l,»
(Compliance date 02.15.89} toxic above limit
St. Marys Paper
(Certificate of Approval)
Suspended solids - 3 T/d
10 T/d
(Certificate of Approval)
Suspended solids - 50X
removal
BODS -30X removal 17X J^
Phosphorus 1.0 og/ll it. 9 mg/L ^j
Vieat End WPCP
(Certificate of Approval)
Suspended Solids - 20 rog/L 4.8 mg/LIS
BOD& - 2U «g/L 4.0 mg/L*
Phosphorus - 1.0 ng/L 0.7 rog/L»
Phenoj - 0.01 rag/1, 0.003 Big/US
Aminonia - 8 mg/L . 1.9 mg/Mi
Chlorine - 0.5
(NPDES Permit I
BODS - 30 isg/L ' 6.4**
pH - 6.5 to 9.0 7.2**
Suspended Solids - 30 mg/L 5.5**
Total Phosphorus - 1 oig/L 0.76**
* Baaed on average annual self monitoring data,
** Based on monthly operating report from November 1386 to October 19B7.
IS Survey average concentration.
I The plant is not required to meet this limit until phosphorus removal facilities cone on-line.
-------
26-
24-
22-
r «M
1986 Average for
self monitoring data
CD
.025
,Q5Q .075 .100
FREE CYANIDE ma/I
.125
.150
.175
HGURE Vl-32. Algoma Sleel allowable discharge concentrations of
total ammonia and free cyanide from the terminal basin.
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199
ill) Municipal Sewage Treatment Plants
Municipal WWTPs in Ontario are required to meet the general ef-
fluent limits specified by the Ministry of the Environment in
OMOE Policy 08-01 "Levels of Treatment of Municipal and Private
Sewage Treatment works Discharging to Surface waters" and OMOE
Policy 08-04 "Provision and Operation of Phosphorus Removal Faci-
lities at Municipal, Institutional and Private sewage Works".
This latter policy has not been applied to the Sault Ste. Marie
East End WWTP. However, the GLWQA, Annex 3, does call for phos-
phorus controls of 1 mg/L on municipal waste water treatment
facilities in the Great Lakes Basin with flows exceeding 3.7 x
10-3 m^/d. A primary plant (e.g. East End WWTP) without phospho-
rus removal must achieve, on a annual average basis, a 30% remo-
val of BODj and a 50% removal of suspended solids (see Table III-
1, Chapter III).
The West End WWTP, which is a secondary plant with phosphorus
removal, is expected to meet the following Certificate of Ap-
proval requirements on the basis of arithmetic means of a minimum
of 12 consecutive month analytical results from a minimum of one
daily composite sample per month: BOD5 and suspended solids, 20
mg/L; total phosphorus, 1.0 mg/L; total phenol, 0,01 mg/L; am-
monia, 8 mg/L; and residual chlorine, 0.5 mg/L.
A model by-law ("By-Law to Control Industrial Waste Discharges to
Municipal Sewers") was prepared by the OMOE and has been adopted
by the city of Sault Ste. Marie. The by-law is intended to en-
sure the protection of WWTPs (including collection and disposal
facilities) and to regulate the discharge of industrial wastes to
municipal sewers.
The "Sault Ste. Marie Sewer By-Law" was passed in August 1968 and
amended in April 1969. This by-law specifically regulates the
discharge of conventional pollutants, metals and total phenols to
sanitary and storm sewers. Other materials such as radioactive
waste, benzene, gasoline and solvents are strictly prohibited.
Cooling water or other unpolluted industrial water cannot be
discharged to a sanitary sewer (City of Sault Ste. Marie, 1969).
Michigan
The effluent limitations contained in the NPDES Permit for the
Sault Ste. Marie, Michigan WWTP are based upon application of
regulations promulgated in accordance with the Federal Water
Pollution Control Act Amendments of 1972 and the State of Michi-
Water Quality Standards. The permit includes limits for BODj
- 30 mg/L monthly average, 45 mg/L 7-day average; pH - minimum
6,5, maximum 9,0; suspended solids - 30 mg/L monthly average, 45
mg/L 7-day average; and total phosphorus - 1.0 mg/L monthly
average. Prom May 1 to October 15 of each year fecal coliform
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bacteria limits are 200/100 nil on a monthly average and 400/100
ml on a 7-day average. Effective January 1991 the 7-day average
total residual chlorine in the effluent must not exceed 0,03
mg/L.
2. Actual Discharges vs. Control Requirements
Ontario
i) Algomai Steel
The levels of oil and grease and suspended solids associated with
Algoma Steel's Terminal Basins discharges are periodically in
excess of the Control Order's current requirements (Table VI-28)-
These exceedences have been referred to OMOE Investigations and
Enforcement Branch for further action. The self-monitoring data
indicated that discharges of cyanide and ammonia from the Term-
inal Basins were above the limits scheduled for February 15, 1989
(Figure VI-32). The combined effect of ammonia and cyanide dis-
charging from the Terminal Basins constitutes toxic conditions.
Bioassays on effluent samples collected from the Algoma Steel
complex indicated that the Bar and Strip Lagoon effluent the
most toxic discharge to the river. The 5€ hr LCjp for the Bar
and Strip Lagoon effluent ranged from 2,2% to 100%. The Terminal
Basins' effluent 96-hr LCgg ranged from 51% to 96% effluent in
1987. In the first quarter of 1988 the Terminal Basins' effluent
96-hr LC-5Q ranged from 7% to 52%.
There are no limits set in the Control Order for PAH compounds
despite their presence at appreciable amounts in Algonia dis-
charges. There are no zinc effluent limits set in the amended
control order since measurement through self-monitoring or pilot
site investigation programs indicated average concentrations less
than the OMOE guideline of 1 mg/L. On occasion, however, daily
levels of zinc from the Bar and Strip Lagoon exceeded the 1 mg/L
level. The MISA pilot site investigation in 1986 revealed that
12% of samples exceeded 1 mg/L,
ii) St. Marys Paper
The St, Marys Paper Certificate of Approval {C of A) contains
limits for only suspended solids. Currently, the suspended
solids loading {3 tonnes/d) is well below the C of A requirement
(Table VI-28),
iii) Municipal WWTPs
The East End WWTP must achieve, on an annual average basis, a 30%
removal of 8005 and a 50% removal of suspended, solids. In 1985
and 1986 the annual average removal for BOD5 was 39% and 54%,
respectively. The annual average total phosphorus concentration
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was 4,2 mg/L in 1985 and 3.4 mg/L in 1986, Thus, the 8005 and
suspended solids requirements were both met in 1985 and 1986;
however, the annual average total phosphorus concentration was
above the GLWQA objective of 1.0 mg/L.
During the survey, the average BOD5 removal was 17% and the total
suspended solids removal 65% (Table VI-280. Effluent total phos-
phorus ranged from 2.8 to 3.1 mg/L, The implementation of phosp-
horus removal facilities, currently scheduled for January 1989,
would be necessary to bring the total phosphorus concentration
below 1 mg/L. Such facilities would also improve the reduction
of BOD5 and suspended solids. With phosphorus removal facilities
in place, this plant would also be required to achieve 50% remo-
val of BODs and 70% removal of suspended solids on an annual
basis.
The West End WWTP has only been on line since March 1986. During
the first three months of operation the average effluent con-
centration of total phosphorus exceeded 1.0 mg/L. However, since
then the plant has consistently met this requirement. The BOD5
and suspended solids 20 mg/L limit was achieved on an annual
basis and, except for BOD§ in March 1986, the monthly averages
have been consistently below 20 mg/L,
Michigan
The City of Sault Ste. Marie WWTP was not surveyed for the UGLCC
Study, Because this plant was upgraded to secondary treatment in.
1985 (on line 1986), historical effluent quality data collected
prior to this period is no longer applicable. The compliance
evaluation based on monthly average concentrations from November
1986 to October 1987 indicated the plant was in full compliance
its WPDES permit for BOD5, suspended solids, pH and phosphorus
(Table VI-28).
3. Adequacy of Control Mechanisms
Control Orders
Models developed for the St. Marys River were used to assess the
adequacy of effluent requirements stated in the Control Order for
Algoma Steel Corp. Ltd. The regulatory mixing zone of 300 m is
considered as the allowable zone beyond which no exceedence of
water quality objectives is permitted under the expected range of
natural conditions. This is based on an assessment of the sig-
nificance of sites for aquatic, biological and/or human contact.
The 300 m zone is recognized as a somewhat arbitrary limit and,
after consideration by the RAP process, could be altered.
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Table VI-26 indicates the existing discharges from Algoma Steel
are exceeding a 300 m regulatory zone. Table VI-29 indicates the
loading requirements which will result in levels complying with
the OMOE and GLWQA at the boundary of the regulatory zone under
average summer river flows. Ammonia and cyanide loadings of
7,000 and 95 kg/d will ensure no toxic effect at the end of the
Terminal Basins' outfall. Levels at the boundary of the regula-
tory zone will be nontoxic during medium and low river flows.
The phenol loading requirements (19 kg/d) in the Control Order
will result in an exceedence during low river flow conditions but
with a frequency of 0.1%,
Loadings of oil and grease and suspended solids stated in the
Control Order may not be adequate to protect aquatic life in the
river. An assumption that the concentrations of oil and grease
and suspended sediment within the water column not exceed the
background levels by more than 10% at the edge of the regulatory
zone is used to provide adequate protection for aquatic organisms
(e.g. Hexagenia). Based on this assumption, the Control Order
requirements may have to be decreased to 950 kg/d for oil and
grease and 1,900 kg/d for suspended solids. These loadings
should be reduced further by about half to meet the requirements
of the regulatory zone during low flow conditions. Limiting the
oil and grease loadings to about 480 kg/d, should allow the reco-
very of aquatic organisms that were adversely affected by oil and
grease discharges.
4. Ontario Regulatory Initiatives
Under Ontario's new MISA Program (Chapter III) effluent limit
regulations will be developed on the basis of Best Available
Technology Economically Achievable, for Algoma Steel Corp. Ltd.,
St. Marys Paper and the two Sault Ste, Marie WWTP's (to be promu-
lgated by 1990/1991).
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TABLE VI-29
Adequacy of effluent requirements for Algoma Steel.
Parameters
Control Order Loadings
(kg/d)
Loading Requirements (kg/d)
to Acheive the Regulatory
Zone (300 m)
Ammonia
Cyanide
Phenol
Oil and grease
Suspended solids
Reduce ammonia and cyanide
to levels below the diagonal
line (Fig.VI-32)
22. 7
1,023
5 , 100
7,000
95
19
950
1 ,900
to
o
1*1
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H, RECOMMENDATIONS
Surveys of sediment quality, benthic community structure and
water quality have revealed an impacted zone along the Ontario
shore downstream of the industrial and municipal discharges.
This zone was characterized by an impaired benthic community,
contaminated sediments (zinc, cyanide, oil and grease, phenols,
PAHs) and elevated concentrations of phenols, PAHs, iron, zinc,
cyanide, phosphorus, ammonia, and fecal coliform bacteria in
surface waters. Notwithstanding reductions in Algoma Steel ef-
fluents, impacts still exist in the benthic community in the
river. Generally, the studies revealed that biota, sediments and
water quality along the Michigan shore of the St. Marys River and
in Lake Nicolet were good.
Based on these findings, the following recommendations are made
in support of remedial programs already underway and to address
the goals identified in Section P,
A, Industrial and Municipal Point Source Remedial Recommendations
1. Ontario and Michigan should incorporate the Great Lakes
Water Quality Agreement's goal of the virtual elimination
of all persistent toxic substances into their respective
regulatory programs,
2. Algoma Steel which was the major contributor of ammonia,
phenols, oil and grease, cyanide and suspended solids must
continue to reduce loadings of these substances to meet the
requirements of the Ontario Ministry of the Environment
Control Order, the compliance dates of which should be
strongly enforced. This recommendation is subject to reco-
mmendations 8 to 10, below.
3. The Sault Ste. Marie, Ontario East End WWTP should be equi-
pped with phosphorus removal in order to bring the total
phosphorus concentration in the final effluent down to the
required 1 mg/L (this is expected to be on-line in 1989).
4. The treatment capacity of the East End WWTP is frequently
exceeded. To reduce the frequency of plant overflows and
bypasses this plant must be upgraded to provide secondary
treatment and expanded, or a portion of the wastewater must
be rerouted to the West End WWTP.
The Sault Ste. Marie, Ontario East End WWTP contributed the
highest loadings of benzene-chloroethers and was the second high-
est contributor of oil and grease, ammonia, chloride, total me-
tals, volatiles, PAHs, chlorinated phenols and phthalates. Elev-
ated levels of PAHs and chlorinated phenols were observed only on
the first day of sampling, presumably due to an industrial spill
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into the sanitary system.
5. The municipality, with the support of the OMOE, take steps
to strictly enforce the Sault ste. Marie Sewer By-Law and
thus prevent the discharge of untreated industrial wastes
to municipal sewers. The municipality and/or OMOE should
also initiate an educational program to discourage home
owners from disposing of hazardous or toxic waste in sew-
ers.
6. Discharges of fecal coliform and fecal streptococci from
Algoma Steel, WWTPs and combined sewer overflows must be
reduced to meet Provincial Water Quality objectives.
7. The A.B. McLean aggregate extraction operations is poten-
tially a significant source of suspended solids to the St.
Marys River. The current, permitted extraction must be
closely monitored and the requirements must be strictly
enforced. Furthermore, the pending permit application must
not be issued until a comprehensive environmental review
indicates that the increased activity would not result in
unacceptable adverse impacts.
In moving toward the virtual elimination of persistent toxic
substances, future toxic controls will place increased emphasis
on the ambient conditions of the St. Marys River ecosystem.
8. Discharge limits for point sources should be based on mix-
ing zones with all water quality objectives met at the
boundary of the mixing zone. This zone is expected to be
reduced {ultimately to zero) as advances in treatment tech-
nology are implemented.
9. Depending on the parameter, Algoma Steel samples their
effluent on a daily, weekly or monthly basis. Most of the
controlled parameters are based on 12 month averages. Due
to the variability in effluent characteristics* sampling
should be more frequent. The frequency and type of samp-
ling should be re-evaluated and audit sampling by OMOE
should be increased.
10. Additional parameters, such as PAHs, should be regulated
and incorporated into Algoma's monitoring program,
B. Nonpoint Source Remedial Recommendations
Concentrations and estimates of loadings from urban runoff are
available only for the Ontario side. Estimates of atmospheric
deposition on the Ontario side of the river indicated that sig-
nificant amounts of PAHs might reach the river through the storm
sewers. For rural runoff, loading estimates were available only
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for the Michigan side.
11. Ontario and Michigan should conduct additional stud-
ies £or both urban and rural runoff to better iden-
tify and quantify loadings of trace inorganic and
organic compounds.
Several active and inactive waste sites in Michigan and Ontario
were identified as having the potential for contributing con-
taminants to the St. Marys River. These studies have been limit-
ed in scope and do not quantify the magnitude of the contaminant
loadings entering the river.
12. Investigate the kinds of contaminants, the pathways of
contamination (surface water and groundwater), and the
magnitude of the contaminant flux; establish monitoring
networks as required; and undertake necessary remedial
clean-up activities at the following waste sites:
i) the Algoma Slag Site;
ii) Cannelton Industries Tannery disposal site (under CER-
CLA authority);
iii) Union Carbide and Superior Sanitation landfills (under
Michigan Act 307).
13. Spill containment must be improved at both industrial and
municipal facilities to minimize the frequency of shock
loadings to the aquatic ecosystem. This will entail spill
prevention, development of contingency plans to deal with
material reaching the river and following established proc-
edures for the reporting of spills.
C. Surveys, Research and Development
14. Many PAHs have been shown to be bioaccumulative or to have
toxic effects on aquatic organisms and some are proven car-
cinogens. The absence of specific, numerical water quality
standards makes it difficult to regulate the discharge of
PAHs. An accelerated effort to assess the ecological sig-
nificance of PAHs and to develop compound specific criteria
is required.
15. There are no regulatory guidelines 'to permit assessment of
the biological significance of sediment associated con-
taminants . Development of such guidelines is required to
aid in site-specific evaluations of contaminated sediments.
16. Impacts to benthic macroinvertebrate communities have been
related to sediment quality. Further site specific work
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must be completed to prioritize sediment "hot spots" based
on biological impacts. In addition, physical and chemical
characteristics of the sediment should be evaluated. This
information will be used to determine appropriate remedial
actions for sediments. Suggested studies include acute and
chronic sediment bioassays as well as physical/chemical and
bedload assessments.
17. The development of water quality based effluent limits for
specific PAH compounds requires additional monitoring of
point source discharges (water as well as air) and deter-
mination of PAH concentrations in resident aquatic indicat-
or species.
18. There is a paucity of data on the near-field atmospheric
deposition of metals and organics. This information should
be obtained, and evaluated relative to other sources (e.g.
effluents, urban runoff, Lake Superior) to the river.
19. Suspended solids are of concern due to their ability to
deposit contaminants locally or to transport them long
distances, before settling out. An investigation of the
combined effects of suspended solids discharges from Algoma
Steel, St. Marys Paper, and WWTPs should be completed.
This may involve a sediment transport modeling effort that
considers the sources, transport and ultimate deposition of
sediment and contaminants. This study would also allow
prioritization of sources'for remedial action.
20. The NPDES Permit for the Sault Ste. Marie, Michigan WWTP
includes effluent limits for 8005, pH, suspended solids,
total phosphorus, fecal coliform, and residual chlorine.
No loadings were measured for UGLCCS parameters during the
1986 survey period. Although no adverse impacts on the
river ecosystem have been observed, trace contaminant load-
ings from this facility should be determined to verify the
absence of environmentally significant loadings to the
river.
21, The OMOS has issued fish, consumption advisories for many
large game fish due to mercury contamination. Although the
main source of mercury is believed to be natural, there are
potential sources in the Sault Ste. Marie urban area.
Mercury has been detected, for example, in all point source
effluents and in stormwater in Sault Ste. Marie, Ontario.
Therefore, it is recommended that a study to determine the
relative contributions of background and urban source(s) of
mercury be completed.
22, Fecal coliform bacteria densities were detected in river
water downstream of the Edison Sault Power Canal in
Michigan. Further sampling must be conducted to determine
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whether Michigan's fecal coliform standard is being ex-
ceeded and, if so, to identify the source{s} and appropri-
ate remedial action.
23. For chemicals where ambient data and standards are avail-
able, the agencies must develop an ecosystem model. The
model should provide insight into the fate of chemicals
entering and leaving the river by various pathways as well
as a systematic process for predicting the relative effect-
iveness of proposed corrective actions.
24. Although the current water quality objective for oil and
grease is narrative {i.e. no visible sheen), a numerical
objective should be developed that is based on no adverse
impacts on sediment quality and associated benthos.
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I. LONG TERM MONITORING
1. UGLCCS vs. Other Monitoring Programs
A presentation of the purposes for monitoring and surveillance
activities is included under Annex 11 of the GLWQA and a discus-
sion of considerations for the design of a long term monitoring
program can be found in Chapter 7 of the Report of the Niagara
River Toxics Committee (59) . Because the focus of the UGLCC
Study was toward remedial actions to alleviate impaired uses of
the Connecting Channels System, long term monitoring recommenda-
tions will likewise focus on the evaluation of trends in environ-
mental quality in order to assess the effectiveness of remedial
actions. In general, post-UGLCCS monitoring should be sufficient
to 1} detect trends in conditions noted by the UGLCCS, and 2}
detect changes in ambient conditions which have resulted from
remedial actions. Monitoring programs should be designed to
specifically detect the changes intended by the remedial actions
so as to ensure relevance in both temporal and spatial scales,
Two major programs sponsored by the IJC also contain plans for
long term monitoring: the Great Lakes International Surveillance
Plan (GLISP) and the Remedial Action Plans (RAPs) for Areas of
Concern (AoC's) identified by the IJC. The GLISP for the Upper
Great Lakes Connecting channels is presently incomplete, pending
results of the UGLCC Study, but it is expected to provide moni-
toring and surveillance guidance to U.S. and Canadian agencies
responsible for implementing the provisions of the GLWQA that
include general surveillance and research needs as well as moni-
toring for results of remedial actions.
The St. Marys River is one of the AoCs, and a RAP is being devel-
oped jointly by Michigan and Ontario. The RAP will identify uses
impaired, sources of contaminants, desired use goals, target
clean-up levels, specific remedial options, schedules for im-
plementation, resource commitments by Michigan and Ontario as
well as by the federal governments, municipalities and industries
and monitoring requirements to assess the effectiveness of the
remedial options implemented. Results and recommendations coming
from the UGLCC Study will be incorporated extensively into the
RAP, which will then be the document that influences federal,
state and provincial programs for the St. Marys River, The reco-
mmendations for long term monitoring that are presented below are
intended for consideration and incorporation into either or both
the GLISP and RAP for the St. Marys River.
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2. System Monitoring for Contaminants
Water
Knowledge of the concentrations of the principal contaminants in
the water of the St. Marys River should be used to indicate gene-
ral exposure levels for the biota, to identify changes and trends
over time in the concentration levels, and to be used for general
assessment of contaminant impacts. The parameters to be monito-
red include phenols, iron, cyanide, ammonia, total PAHs, oil and
grease, benzo(a)pyrene, and ether solubles. Monitoring stations
should provide information on contaminant concentrations through-
out the river. For continuity, these should include the sampling
transects identified in this study (i.e., SMU 1.0 and 0,5; SMD
0.2, 1.0, 1.2, 2.6, 4.2E, and 5,OE), Sampling frequency should
be influenced by the variability in contaminant sources. Spring
high flow conditions and late summer low flow conditions would be
expected to bracket the normal seasonal variability in flow that
could influence measured contaminant concentrations.
A mass balance approach to contaminant monitoring will help to
identify any changes in the contaminant mass over time, and it
will provide the basis for targeting future remedial actions by
providing a comparison of the magnitude of the sources. A mass
balance analysis should be conducted approximately once every
five years, assuming that some effective remedial action has been
implemented against one or more sources such that the total load-
ings of contaminants, or the relative contribution of the sources
to the loading, has changed. The sources to be measured should
include:
1) Head and mouth transects for upstre'ara and downstream bound-
ary movements. The number and locations of stations should
relate to measured or predicted plume distributions. Sug-
gested locations include Point Aux Pins, the head of Sugar
Island, and the downstream end of Lake George and Lake
Nicolet. Both dissolved and particulate fractions should
be analyzed. The quantity of suspended sediment flux sho-
uld also be measured.
2) Municipal and industrial point sources. During the survey,
the sampling must be frequent enough to accurately reflect
the likely loading fluctuations from the major point sour-
ces. The sources include the major outfalls of Algoma
Steel, St. Marys Paper, and the East End WWTP, the West End
WWTP and Sault Ste. Marie, Michigan WWTP.
3) Tributaries. Preliminary assessment has shown that con-
tributions from tributaries to the St. Marys River are
secondary to the industrial and municipal point sources.
These findings should be confirmed periodically.
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4) CSOs and Runoff, To provide an estimate of contaminant
mass loadings expected during storm events, occasional
studies on selected urban drainage areas should be con-
ducted. Estimates should be made for all urban and agri-
cultural runoff on both sides of the river.
5) Groundwater inflow. Groundwater monitoring systems de-
signed to detect potential loadings to the St. Marys River
need to be installed at the Algoma Slag Site and at
Cannelton Industries Tannery disposal site following re-
mediation. The existing monitoring system at the Cherokee
Landfill should be utilized to detect potential loadings to
the river.
6} Sediment transport. Preliminary studies indicate that bed-
load sediments moving into and out of the St. Marys River
carry contaminant masses similar to, or exceeding the other
sources. The mass flux should be quantified.
7} Atmospheric deposition. Direct atmospheric deposition of
contaminants to the St. Marys River is expected to be
minor. Deposition to the drainage basin and subsequent
runoff into the river or its tributaries, however, could be
an important source for some contaminants. Estimates of
contaminant mass in both wet and dry deposition to the
drainage basin should be made when unidentified nonpoint
sources are found to be a major contributor of any of the
contaminants of interest.
Sediments
Monitoring of sediments for concentrations of contaminants should
be conducted periodically throughout the St. Marys River in order
to assess both the trends in surficial contaminant concentrations
and the movement of sediment-associated contaminants within the
river. The grid used by the U.S.FWS during the 1985 survey would
be appropriate for consistency in sampling sites and sediment
composition. An analysis of sediment chemistry including both
bulk chemistry, organic and inorganic contaminants, and particle
size distribution should be conducted every 5 years, in conjunc-
tion with a biota survey (see "habitat monitoring" below). In
the St. Marys River, particular attention should be given to
sediment concentrations of oil and grease, phenols, cyanide, and
PAHs.
Because the grid stations are distributed throughout the river
reach and are associated with appropriate habitat for a sensitive
benthic invertebrate (Hexagenia), the periodic survey will allow
assessment of 1) contaminant distribution throughout the river
sediments, 2) relative movement of the contaminants within the
river sediments between surveys, and 3} correlation of contamin-
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ant concentrations with benthic biotic communities.
The sediment at any stations established 'at the mouths of tribu-
taries to the St. Marys River should be monitored for organic and
inorganic contaminants on an annual or biannual basis when sig-
nificant remedial actions are implemented within the watershed
for the tributary. The remedial actions should be expected to
measurably reduce loadings of one or more particular contaminants
via the tributary in order to trigger the more frequent sediment
monitoring programs.
Biota
Long term monitoring of concentrations of contaminants in biota
will provide a time series useful to track the bioavailability of
contaminants to selected representative organisms. Three long-
term monitoring programs are already in place and should be con-
tinued:
i) Annual or bi-annual monitoring of sport fish.
This program should focus especially on PAHs, mercury, and PCBs.
The monitoring should be continued regardless of the differences
that may be observed between acceptable concentrations or action
levels that may be established by governmental agencies and the
measured contaminant concentrations in the fish flesh. As a link
between human health concerns and integrated results of remedial
programs to reduce contaminants in the UGLCC System, this program
is critically important.
ii) Spottail shiner monitoring program.
This program is designed to identify source areas for bioavail-
able contaminants. In locations where spottail shiners contain
elevated levels of contaminants, additional studies should be
conducted to identify the sources of the contaminants. Some
upstream studies in tributaries may be required. Spottails sho-
uld also be employed to confirm that remedial actions have been
effective in removing or reducing the loading of one or more
contaminants.
iii) Caged clams contaminants monitoring.
Caged clams should continue to be used at regular time intervals,
perhaps in conjunction with spottail shiners, to monitor inte-
grated results of remedial actions to reduce contaminant loadings
to the water. Clams may be located at tributary mouths and down-
stream of suspected source areas. Repeated assays from the same
locations should confirm results of remedial actions.
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iv) Benthic survey
The macrozoobenthic community should be evaluated at least every
3 years. As a minimum, the abundance and distribution of the
mayfly Hexagenia should be determined to serve as an indicator
species of environmental quality. The grid used by the U.S.FWS
during the 1985 survey {Figure VI-20) would be appropriate for
consistency in sampling sites each survey. An analysis of sed-
iment chemistry, including bulk chemistry, organic, inorganic and
extractable (available) contaminants, and, particle-size distribu-
tion, should be conducted for samples taken concurrently with the
macrozoobenthic survey. These data will provide information on
the quality of the benthic habitat.
v) Toxicity testing
Sediment toxicity tests, using whole sediment and. sediment pore
water or elutriate should be conducted at selected sites in con-
junction with the benthic survey. Results will assist to dif-
ferentiate between toxicity and substrate or dissolved oxygen
effects.
3, Sources Monitoring
Remedial actions intended to reduce concentrations and/or load-
ings of contaminants from specific point sources generally re-
quire monitoring for compliance with the imposed criteria or
standards for permittee! contaminants. The monitoring may be
conducted by the facility or by the regulating agency, whichever
is applicable, but attention must be given to the sampling sched-
ule and analytical methodology such that mass loadings of the
contaminants can be estimated, as well as concentrations in the
sampled medium. Monitoring of the "near-field" environment,
i.e., close downstream in the effluent mixing zone, should be
conducted regularly to document reductions in contaminant levels
in the appropriate media and to document the recovery of impaired
ecosystem processes and biotic communities. Such monitoring may
be required for a "long time", but over a restricted aerial ex-
tent, depending on the severity of the impact and the degree of
reduction of contaminant loading that is achieved.
For the St. Marys River, four actions were recommended that would
affect specific sources of contaminants:
a} Reduction of toxic substances from Algoma Steel effluents,
especially at the Terminal Basins. Reductions in loadings
of phenol, cyanide, ammonia, oil and grease, and suspended
solids are expected as a result of new effluent limitations
imposed as part of the MISA program. Monitoring of sed-
iments and biota for contaminant concentrations and effects
downstream of the effluent should be conducted regularly to
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document any improvement in environmental conditions,
b) Enforcement of the regulatory mixing zone for the Sault
Ste. Marie, Ontario East End WWTP. Ontario must design a
monitoring plan adequate to determine that all water qual-
ity objectives are met at the boundary of the regulatory
zone, and to determine if adverse environmental effects
continue in the sediments and biota despite compliance with
water quality objectives,
c) Enforcement of the Sault Ste. Marie, Ontario Sewer By-Law
to prevent the discharge of untreated industrial wastes or
contaminants disposed by homeowners into municipal sewers,
Ontario will provide additional monitoring, inspection and
enforcement tools £or implementing controls of toxic dis-
charges to sewer systems, The monitoring component must
include assessment of continuing environmental effects in
sediments and. biota downstream of the sewer outfall, as
well as monitoring for concentrations of selected contamin-
ants in the sewer influent.
d) Equip the Sault St. Marie, Ontario, East End WWTP with
phosphorus removal facilities. Frequent in-plant monitor-
ing will be required to document that the target discharge
limit of 1 mg/L is being met.
Other recommendations for specific contaminant sources involve an
assessment of the present conditions or a study to quantify con-
centrations or loadings: review of PAHs for risk and hazard in-
formation ; assess the need for further reduction of suspended
solids from St. Marys Paper," quantify trace contaminants from the
Sault St. Marie, Michigan WWTP, estimate loadings of trace or-
ganic and inorganic compounds from urban and rural runoff, and
quantify potential releases of contaminants from waste disposal
sites. Each of these items requires a specific program of data
collection and analysis. Additional needs for longer term moni-
toring may be identified as a result of these studies.
4, Habitat monitoring
Habitat monitoring should be conducted to detect and describe
changes in the ecological characteristics of the St. Marys River
through periodic analysis of key ecosystem elements. In par-
ticular, quantification of the extent of wetlands along the St.
Marys River should be conducted every three years. Aerial pho-
tography or other remote sensing means would be appropriate to
discern both emergent and submergent macrophyte beds that are
important as nursery areas for larval fish and other wildlife.
Verification of aerial data should be conducted by inspection of
selected transects for plant species Identification and abun-
dances. Changes in wetland areas should be correlated with flue-
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215
tuating water levels and other natural documentable influences so
that long term alterations in wetlands can be tracked and causes
identified.
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216
J. REFERENCES
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5. Koshinsky, G.D. and C.J. Edwards. 1983. The fish and
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6. Weise, F.T, 1985. Waterfowl, Raptor, and Colonial Bird
Records for the St. Marys River, Mich. DNR. Unpubl. Rept.
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Natural Sites in the U.S. Great Lakes. U.S. COE Tech.
Rept. D-78-10. Vicksburg, Miss. 165 pp.
9. Scharf, W.C. 1979. Nesting and Migration Areas of Birds
of the U.S. Great Lakes. U.S. FWS Rept. FWS/OBS-77/2, 363
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10. Hamdy, Y., J.D. Kinkead, and M, Griffiths. 1978.
St. Marys River Water Quality Investigations, 1973-
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11. Fischer, H.B. 1969, The Effects of Bends on Dispersion In
Streams, Water Resources Research, vol. 2.
12. Hamdy, Y, and G.J. LaHaye. 1983. St Marys River
Water Quality Investigations. OMOE, Toronto.
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Objectives 1984.
14. Neff, J.M. (1979). Polycyclic aromatic hydrocar-
bons in the aquatic environment. Applied Sci.
Publ., London, England.
15. Bass, O.K. and J. Saxena (1979). Polynuclear arom-
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waters and their raw water sources. Environ. Sci.
Technol. 12: 795-798.
16. Williams, D.T., E.R. Nestmann, G.L. LeBel, P.M.
Benoit and R. Otson. (1982). Determination of
mutagenic potential and organic contaminants of
Great Lakes drinking water. Chemosphere 11; 263-
276.
17. Eadie, Brian J. (1983). Partitioning of polycyclic
aromatic hydrocarbons in sediments and pore waters
of Lake Michigan. Geochim. Cosmochim. Acta. in
press.
18. Oliver,B.C. (1986). Partitioning Relationships for
Chlorinated Organics on Particulates in the St.
Clair, Detroit and Niagara Rivers. In: QSAR in
Environmental Toxicology. K.L.E. Kaiser, ed. D.
Reidel Publishing Co.
19. Edsall, T. A., P.B. Kauss, D, Kenaga, T. Kubiak, J.
Leach, M. Munawar, T. Nalepa, S. Thornley. 1987.
St. Marys River Biota and their Habitats: A Geo-
graphic Area Report of the Biota Workgroup, Upper
Great Lakes Connecting Channels Study. December
1987.
20. Edwards, C.J., P.L. Hudson, w.G. Duffy, S.J,
Nepszy, C.D. McNabb R.C. Haas, C.R. Liston, B,
Manny, and W.D. Busch. 1988. Hydrological, mor-
phometrical, and biological characteristics of the
connecting rivers of the International Great Lakes:
a review. Can. J. Fish. Aquat, Sci. 44. (In press).
21. Poe, T.P., and T.A. Edsall. 1982. Effects of
vessel-induced waves on the composition and amount
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218
of drift in an ice environment in the St. Marys
River, U.S. Fish, Wildl. Serv., GLFL/AR-8Q/6 Ann
Arbor. 45 pp.
22. Jude, D.J., M, Winnell, M.S. Evan's, P.J. Tesar and.
R. Futyma, 1986. Drift of zooplankton, benthos and
larval fish and distribution of macrophytes and
larval fish during winter and summer 1985, Univer-
sity of Michigan, Great Lakes Research Div. 174 pp
+ Appendices.
23, Nichols, S.J., D.W. Schloesser, T.A. Edsall and
B.A, Manny. 1987. Drifting Submersed Macrophytes in
the Upper Great Lakes Connecting Channels. United
States Fish and Wildlife Service. National Fisher-
ies Centre; Great Lakes - pp. 14,
24. Hiltunen, J.K. 1979. Investigation of Macrobenthos
in the St. Marys River during an experiment to
extend navigation through winter, 1974-75. U.S.
Fish Wildl. Serv., Great Lalces Pish. Lab. Report,
Ann Arbor. 98 pp,
25. Schirripa, M.J. 1983. Colonization and production
estimates of rock basket samplers in the St. Marys
River, 1983. Unpub. MS. Mich. State Univ., E.
Lansing.
26. Veal, D.M. 1961. Biological'survey of the St.
Marys River. Ont". Min. Environ... Water Resour,
Corom. and Int. Joint Coirai. 23 pp' + app.
2*7. Hiltunen, J.K. and D.W. Schloesser, 1983. The
occurrence of oil and distribution of Hexagenia
(Ephemeroptera; Ephermeridae) nymphs in the St.
Marys River, Michigan and Ontario Freshwat,
Invertebr. Biol. 2 (43:199-203.
28. McKnee, P.M., A.J, Burt, D.R. Hart. 1984. Benthic
Invertebrate and Sediment Survey of the St. Marys
River, 1983. I.E.G./Beak report prepared for
Ontario Ministry of the Environment, Mississauga,
Ontario.
29, Burt,A. J., D.R. Hart, and P.M. McKee. 1988. Ben-
thic invertebrate and sediment survey of the St.
Marys River 1985. Beak Consultants Ltd., Missis-
sauga, Ontario, Canada Prepared for Ontario
Ministry of the Environment.
30. Schloesser, D.w, et al., 1988.
(1985 Benthic Study)
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31. Persaud, D,, T.D. Lomas and A. Hayton. 1987. The
In-Place Pollutants Program, Volume III, Phase I
Studies. OMOE, Toronto.
32. Krantzberg, W. and Baily, 1983.
(Sediment Size/Invertebrates)
33. International Joint Commission, 1983. Annual
Report. Report of the Ecosystem Objectives Commit-
tee to the IJC, Windsor, Ont.
34. Ministry of the Environment/Ministry of Natural
Resources. 1988. Guide to eating Ontario sport
fish. Toronto, Ontario.
35. Suns, K., G.E. Crawford, D.D. Russell, and R.E.
Clement. 1985, Temporal trends and spatial dis-
tribution of organochlorine and mercury residues
in Great Lakes spottail shiners (1975-83).
Ontario Ministry of the Environment.
36. Zenon. 1985. To Devise and Implement a Revised
Monitoring Scheme for Persistent and Toxic Or-
ganics in the Great Lakes Sport Fish. Report pre-
pared for Ontario Ministry of the Environment
Inc., Burlington, Ontario, October 10, 1985.
37. Kobiak, T.J., H.J. Harris, L.M. Smith, T.R.
Schwartz, D.L. Stalling, J.A. Trick, L. Sileo, D.S.
Docherty and T.C. Erdman. 1988. Microcontaminants
and Reproductive Impairment of the Forster's Tern
on Green Bay, Lake Michigan - 1983. Arch. Env.
Cont. Toxic. (Submitted for Publication).
38. Hesselberg, R.J. and Y. Hamdy. 1987. Current and
historical contamination of sediment in the St.
Marys River, 1987. UGLCCS Sediment Workgroup Re-
port. 17 pp.
39. Oliver, B.C., J.A. Robbins, and Y.S, Hamdy. 1987,
History of PAH and PCB contamination of the St.
Marys River by anlaysis of Lake George sediment
core. (In review). National Water Research In-
stitute, Canada Centre for Inland Waters.
40. Orchard, Ian and A. Mudrock. 1987. Report on sedi-
ments, water, and the distribution of benthic or-
ganisms in the St. Marys River in 1986. Environ-
mental Protection service. Ontario Region,
Toronto.
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41. Bertram, P., T.A. Edsall, B.A. Manny, S.J. Nichols,
and D.W. Schloesser. 1987. Physical and Chemical
characteristics of sediment in the Upper Great
Lakes Connecting Channels, 1985. Sediment Work-
group - UGLCCS. U.S.EPA/GLNPO.
42. Kauss, P.B. 1986. Presentation to citizens hearing
(Great Lakes United) on St. Marys River water
pollution. August 7, 1986, Sault Ste. Marie,
Michigan. Ontario Ministry of the Environment,
Toronto, Ontario, Canada. 24 pp..
43. Pranckevicius, Pranas E. 1987. Upper Great Lakes
Connecting Channels Tributary Sediments. A prelim-
inary Data Report. U.S.EPA.
44. DAS, B.S. 1983. Applications of HPLC to the anal-
ysis of polycyclic aromatic hydrocarbons in en-
vironmental samples. In Liquid chromatography
environmental analyses, ed. J,F. Lawrence, The
Humana Press.
45. Larssen, P. 1985 "Contaminated sediments of lakes
and oceans act as sources of chlorinated hydrocar-
bons for release to water and atmosphere. Nature
Vol. 317.
46. Munawar, M. 1987. Bioavailability and Toxicity of
In-Place Pollutants in the Upper Great Lakes Con-
necting Channels. Fisheries and Ocean Canada,
Great Lakes Laboratories for Fisheries and Aquatic
Sciences, Canada Centre for Inland waters,
Burlington, Ontario.
47. Duffy, W.G. 1985, The population ecology of the
damselfly, Lestes disjunctus disjunctus, in the St.
Mary River, Michigan. Ph.D. Diss, Mich. State
Univ., East Lansing. 119 pp.
48. Holland, L.E., and J.R. Sylvester. 1983. Evalua-
tion of simulated drawdown due to navigation traf-
fic on eggs and larvae of two fish species of the
Upper Mississippi River. U.S. Army Corps Eng.
Resp. Contract No. NCR-LO-83-C9. Rock Island 111.
49. Point Source Workgroup Report. 1988. St. Marys
River Geographic Area,
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50. Marsalek, J. and H.Y.F. Ng, 1987. Contaminants in
Urban Runoff in the Upper Great Lakes Connecting
Channels Area. National Water Research Institute,
Burlington, Ontario, Unpublished Report No. RRB-87-
27.
51. Boom, A. and J. Marsalek. 1987. Accumulation of
Polyeyelie Aromatic Hydrocarbons (PAHs) in an Urban
Snowpack, National Water Research Institute, Bur-
lington, Ontario, Unpublished Report No. RRB-87-
62.
52. Lygren, E., E. Gjesaig, and L. Berglind. 1984.
Pollution transport from a highway. Sci. Total
Environ., 33: 147-159.
53. Seifert, B. and E. Lahmann. 1980. Luftstaub-
Untersuchungen mit eier Hochleistutngs-eluessigkeits-
Chromatographie. In: Luftverunreingung durch poly-
eyelisclie aromatische Kohlenwasserstoffe, V.D.I*
Beriehte Nr. 358, Duesseldorf, pp. 127-131.
54. Nonpoint Source Workgroup 1988. Upper Great Lakes
Connecting Channel Study Nonpoint Source Workgroup
Report Waste Disposal Sites Potential Ground-
water Contamination St. Marys River.
55. Liggett, J.A., and Hadjitheodorou1, C, 1969. Cir-
culation in shallow homogeneous lakes analysis. J.
Hyd. Div., ASCE. pp 609-620.
56. Ibrahim, K.A. , and Mccorquodale, J.A. 1985. Finite
element circulation model Cor Lake St. Clair. J.
Great Lakes Research, vol.11(3), p 208-222, Inter-
national Assoc. Great Lakes Research.
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"Report on St, Marys River Hydrodynamic Dis-
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Hyd, Div.. ASCE, No. HY3, pp. 397-420.
59, Report of the Niagara River Toxics Committee. 1984,
U.S. EPA; ; Env. Can.; .
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CHAPTER VII
ST. CLAIR RIVER
A. STATUS OF THE ECOSYSTEM
1. Ecological Profile
Watershed Characteristics
The St. Clair River flows in a southerly direction forming the
international boundary between the United States and Canada,
This navigable waterway physically separates Lambton and Kent
Counties in Ontario, and St. Clair County in Michigan, The St.
Clair River is not a typical river system, occupying an alluvial
valley, but must technically be regarded as a strait (I). This
system is a true connecting channel or conduit which transports
water, nutrients, sediments, and biota from Lake Huron to Lake
St. Clair {Figure II-3).
The complex connecting channel between Lake Huron and Lake Erie
that involves the St. Clair River, Lake St. Clair, and the
Detroit River came into existence nearly 10,000 years ago with
the retreat of the Pleistocene ice sheet. As the massive weight
of ice was removed, an uplift in the form of glacial rebound
occurred, leaving the St. Clair River/Lake St. Clair/Detroit
River channel as the dominant outlet for the waters of the Upper
Great Lakes. As time passed, the actions of the moving water
enhanced the exit mechanism, until some 3,000 years ago, when the
complex connecting channel became a permanent feature of the
landscape.
The St. Clair system overlays 4,200 metres of sedimentary
Paleozoic bedrock resulting from the hardening of ancient silts
and muds to form extensive deposits of sandstones, limestones,
dolomites, salts and shales. This thick depositional sequence
rests upon a foundation of Precambrian igneous and metamorphic
rocks. Fossil fuels have been extracted from the area for more
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than a century, beginning with the first oil field in North Amer-
ica developed at Oil Springs, Ontario, in 1858. Minerals of
evaporative origin, such as halite (rock salt), have been exten-
sively extracted by the Morton Salt Company for decades in St.
Clair, Michigan.
The geologic origin of the St. Clair River resulted in a river
system which forms the single outlet for Lake Huron, conducting
its waters approximately 64 km southward to Lake St. Clair,
Sediments in the river consist of gravel with sand in the inter-
stices over glacial clay. Very little sediment deposition occurs
along the river channel above the river delta. Prior to entering
Lake St. Clair, the diminished velocities of the river with
broadening provided an extensive depositional area. Thus, a
large river delta system developed containing numerous distri-
bution channels and an extensive region of wetlands. The shore-
line of the St. Clair River, including the principal delta dis-
tribution channels, is 192 km in length.
Hydrology
As might be expected, water velocities within the St. Clair River
are highest in the northern stretch of the river adjacent to the
exit of Lake Huron, and lowest in the southern delta area. The'
total flow time from Lake Huron to Lake St. Clair is shown in
Figure VII-1. It has been estimated to be 21.1 hr from Lake
Huron to Lake St. Clair (2). The total average fall in this
stretch is 1.5 m in vertical height (3). The mean water velocity
is 3.5 km/hr, with a minimum of 1,1 km/hr in the delta area ad-
jacent to Lake St. Clair (Figure VII-1}(2).
The river flow ranges between approximately 3,000 m^/sec and
6,700 m^/sec (2). The mean monthly discharge was 5,200 m^/sec
between 1900 and 1981 (6). Eight percent of this mean flow (410
m3/sec) passes through the Ontario channels of the St. Clair
Delta; the remainder (92 percent) passes through the more
westerly main channels of the delta (7).
The river behaves like three separate panels of water: two near-
shore sections strongly influenced by discharges; and a centre
panel which passes through the river with minimal change.
On the Michigan side of the St. Clair River, four heavy indus-
tries are the principal users of river water for metal plating,
paper manufacturing, and salt processing. By far, the heaviest
municipal and industrial use occurs on the Canadian side of the
river with ten major industrial plants in the Sarnia area produc-
ing refined petroleum, petrochemical and agricultural products. A
large coal-fired power generating station is also located on the
Ontario shore. A number of studies have shown that effluents
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225
LAi— 20.0
MICHIGAN
Distance Flow Velocity
From Tirn« (Hr) Of Flow
'UFOO Source (Km) CKm/Hr}
0.0
0.1
0.9
44
6.0
O N TA R I O
9.8
12.0
12.5
52.0
- 64.0
17.9
21.1
0.0
6.0
3.9
2.9
2.6
2.4
1.1
FIGURE VII-1. St. Clair River indicating approximate flow times and
velocities of flow of various reaches of the river.
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226
from a number of these plants have degraded the quality of the
St. Clair River system (8-12).
Historically, waterborne commerce has been a very heavy user of
the St. Clair River system. Traditionally, iron ore, limestone,
and coal account for 90 percent of commercial shipping on the St.
Clair River (13).
Habitats and Biological Communities
The St. Clair River ecosystem consists of five fundamentally
distinct biologic zones: (i) open-water, (ii) submerged wetland,
(ill) emergent wetlands, (iv) transition or ecotone, and (v)
upland. Each of these zones may be subdivided by the community
of organisms which occupy them, or by their physical character-
istics .
The open-water zone may be subdivided into two major groups: (i)
the channelized flow communities, and {ii) the open-water marsh
communities. The channelized flow communities include such
diverse groups as free-swimming nekton, e.g., fish, amphibians,
and reptiles; drift communities, e.g., uprooted submerged and
emergent plants, phytoplankton, and zooplankton; and sessile,
burrowing, or attached communities, e.g., immature aquatic in-
sects, invertebrates, and mollusks. The open-water marsh com-
munities predominate in the St. Clair Delta area. They are typi-
cally either bullrush marshes, or cattail marshes. The
open-water bullrush marsh is prevalent in the abandoned channels
of the St. Clair Delta, or mixed with cattail marshes where water
depth and sandy sediments favour the development of bullrush
communities. Open-water cattail marshes are found in delta sec-
tions of the river where peaty or clayey hydrosoils predominate,
and where water depth exceeds 15 cm (5). '
The St. Clair River system contains approximately 550 ha of
coastal wetlands. The primary type of wetlands in the St. Clair
River belong to the river wetland group, and are composed largely
of submerged species (5,14,15), These shoreward, submerged com-
munities may be conveniently divided by location into the delta
channel, and the river shoulder. The delta channel communities
include both abandoned and active delta channels. The river
shoulder communities border the channelised area of the river for
a distance of 30-40 m, and rarely exceed 2 m in depth (2). Emer-
gent wetland communities occasionally occupy the river shoulder
area, but more often, these forms are to be found on point bars
and within the river delta structure.
The transition zone, or ecotone, may be conveniently subdivided
into three major categories of community types: (i) the island
shoreline and transgressive beach, (ii) sedge marshes, and (iii)
the transition wet-meadow. Long, narrow beaches of fine sand
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227
which support emergent vegetation are found on the Canadian side
of the river delta. Transgressive or stranded beaches are also
found on the islands of the delta area which support intermediate
or transition communities, including tussock sedge (Carex sp.),
reed (Phragmites austral is.) , swamp thistle (Cirsim ntuticum) ,
bluejoint grass (Calamagrostis canadensis), willows (Salix sp.),
and the eastern cottonwood (Populous deltoides) . The sedge marsh
communities occupy a very narrow 2one of transition between the
wetter cattail marshes and the more terrestrialized upland zones.
Typical residents of this community are nearly all members of the
tussock sedge group (Carex sp.), with the exception of bluejoint
grass (Calamagrostis canadensis). The transition wet-meadow
communities represent a transition state between the sedge
marshes and the upland communities. This community lies above
the water table and is infrequently flooded. It consists of a
mixture of grasses, herbs, shrubs, and water-tolerant trees,
including quaking aspen (Populus tremuloides), red ash (Fraxinus
pennsylvanica), red osier dogwood (Cornus stolon!fera), swamp
rose (Rosa palustris), bluejoint grass (Ca1amagrostis cana-
den si_s) , rattlesnake grass (Glyceria canadensis), and panic grass
(Panicum sp.).
The terrestrialized upland communities bordering the St. Clair
River system include upland shrub, and deciduous hardwood. The
upland shrub community consists of mixed shrubs and water toler-
ant trees, including eastern cottonwood and quaking aspen (Pop-
ulus sp.}, red ash (Fraxinum pennsylvanica), red osier dogwood
and gray dogwood (Cornus sp.)/ wild grape (Vitis palmata), and
hawthorn (Cratae_gus sp.) . The deciduous hardwood community ad-
jacent to the St. Clair River begins on an average of 1-3 m above
the level of the river. Major species in this community include
red ash (Fraxinus pennsylvanica) and members of the genus
Quercus, including swamp white oak, pin oak, and burr oak. Other
hardwoods include silver maple (Acer saccharinum), the American
elm (uImus americana), eastern cottonwood (Populus_ deltoides),
and shagbark hickory (Carva ovata). The terrestrialized upland
communities are chiefly found in the less industrialized portions
of the basin, particularly in southern reaches of the river, and
notably in the island complex associated with the delta area.
i) Macrozoobenthos
The macrozoobenthos of the St. Clair River exhibits a higher
taxonomic diversity than Lake St. Clair, The number of individ-
ual species observed in the river is in excess of 300 (2). Mem-
bers of the Oligochaeta, Chironomidae, Gastropoda, Epheineroptera,
Trichoptera, and Amphipoda contribute most significantly to total
macrozoobenthic biomass. Large numbers of Hydra sp. are present,
but contribute little to biomass.
The genera Cricotopus, Parachironpmus, Parakiefferiella, Rheo-
tanytarsus, and Stictochironomus are the dominant chironomid
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228
forms. The most common amphipod is Hyalella, and the common
trichopteran genera include Cheumatopsyche, Hydropsyche, and
Oecetis. Species diversity is greatest in the Chironomidae,
Trichoptera, and oligochaeta. Numerous freshwater mussels are
present in abundance in the St. Clair River, as are the common
snail genera Amnicola and Elimia.
ii) Zooplankton, Phytoplankton and Macrophytes
The St. Clair River harbors relatively low densities of limnetic
zooplankton (16) . Several authors report that the St. Clair
River zooplankton community is dominated by fugitive drift com-
munities of zooplankton from Lake Huron (2,16,17). A total of 18
rotifer genera, 9 calanoid copepods, 4 cyclopoid copepods, and 6
cladocerans have been observed in the St. Clair River (18).
While rotifers were most frequently seen (17), the dominant
zooplankton species observed were Bosmina longirostris, Cyclops
thomasi, and Diaptomus minutus.
The primary production system of the St. Clair River consists of
phytoplankton, emergent macrophytes, submerged macrophytes, and
the periphyton community associated with the submerged portions
of the latter two groups. A single source of information is
available regarding the phytoplankton composition of the St.
Clair River. This study was completed more than a decade ago
(17,19), and suggests that the phytoplankton community of the St.
Clair River is dominated by diatoms occurring in patterns similar
to the communities of Lake Huron. Dominant species reported in
1974 included Cyclotella sp., Fragillaria sp., Melosira sp.,
Stephanodiscus sp., Synedra sp., and Tabellaria sp. At the time
of preparation of this manuscript, no published data were avail-
able related to native periphyton communities in the St. Clair
River.
Submerged macrophytes are a prominent feature of the littoral
waters of the St. Clair River. These extensive macrophyte beds
provide food, shelter, and habitat requirements for fish and
wildlife populations. Not only do they support a wide variety of
migratory waterfowl, but young fish were observed to be more
abundant from spring to fall among the submerged macrophytes than
in the plant-free areas of the St. Clair River islands (20).
More than 20 submerged macrophyte taxa occur in the St. Clair
River system (20,21). In order of frequency of occurrence, these
include Chara sp,, Vallisneria americana, Potamogeton sp., and
Heteranthera dubia. Of this group, only Chara forms single
species or monotypic stands of vegetation. Typically, submerged
macrophyte stands are composed of 2-3 species; however, a stand
with a maximum of 11 taxa has been reported (2). The greatest
depth of water colonized by submerged macrophytes is not docu-
mented for the St. Clair River system, but most stands occur in
water depths of 3.7 m or less. The 3.7m depth contour accounts
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229
for 16 kiti^ of the St. Clair River shoreline. It has been es-
timated that 88 percent of the St. Clair River bottom is covered
by plant material within the 0-3.7 m range of depths (2).
A total of three submerged macrophyte taxa are found in the St.
Clair River system. These species include Potamogeton crispus,
Nitellopsis obtusa, and Myriophyllum spicatum. P_._ crispus is one
of the first aquatic plants to appear in the spring. This plant
serves as a host for aquatic invertebrates which are consumed by
northward migrating waterfowl (1). Since it is also one of the
most abundant macrophytes in the river during April to June, P.
crispus provides an important spawning substrate for fish (22),
N_._ obnusa was first reported in the St. Clair River in 1984 (23) .
M. spicatum was first observed in Lake St. Clair in 1974 (24),
and became the fourth most common submerged macrophyte in the St.
Clair River system by 1978 (21).
Emergent macrophyte distributions are less well understood.
While Herdendorf e_t al. (5) provide some discussion of the emer-
gent forms of the lower St. Clair River, no definitive study of
species compositions, abundance, distribution, occurrence, or
productivity has yet been made. Estimates, however, suggest that
as much as 3,380 ha of the St. Clair River may be colonized by
emergent vegetation (25,26). It is further estimated that 95
percent of the stands of emergent vegetation occur in the lower
reaches of the river (1). Typical emergent vegetation within the
river area proper includes cattails (Typha sp.) and reed
(Phragmites. australis) . Within the delta, numerous canals,
ponds, and abandoned channels support a wide diversity of emer-
gent plant communities, including the yellow and white water
lilies (Muphar advena and Nymphae_a tubejrosji, respectively) ,
buttonbrush (Cephalanthus occidental!s) , arrowhead (Saga.tta.ri_a
latifolia), bullrush (Scirpus sp.), and water smartweed Pplyhonum
amphibium).
iii) Fish
With regard to fish populations, the St. Clair River is important
in two respects: (a) it supports its own native fishery, and (b)
it serves as a conduit, providing a means of access for movement
of fish to both Lakes Huron and Erie. The latter aspect is par-
ticularly significant in association with fish spawning.
The St. Clair River is critical to the spawning and nursing of
juvenile fish of between 23 and 41 taxa (4,27,28,29), with larval
fish densities averaging 296 per 1000 m^. Fish species observed
within the river include walleye, muskellunge, rainbow trout,
lake sturgeon, smelt, coho and Chinook salmon, smallmouth bass,
channel catfish, yellow perch, and freshwater drum (30).
Juvenile and adult fish were most often observed in the lower
reaches of the river where macrophyte communities were abundant.
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230
Forty-eight fish species are known or presumed to utilize the
wetland areas associated with the St. Clair River, The manage-
ment of this system is critical to protect both the habitat of
these fish and the fish themselves from accumulating body burdens
of chemical contaminants.
Haas e_t al. (31), conducted seven monthly surveys of fish in the
St. Clair River which identified rock bass, yellow perch, and
walleye as the most common forms. Fish populations vary season-
ally, with smallmouth bass most numerous in the fall, and white
suckers dominating the spring populations.
As was noted above, the river serves as a corridor for fish move-
ment between Lakes St. Clair and Huron. Walleye are known to
spawn in the delta area and tributaries of Lake St. Clair, and to
move in late spring through the St. Clair River to southern Lake
Huron. These fish typically return through the river in the fall
of the year (30) . This migration pattern is further complicated
by walleye breeding migrations in which fish from Lake Erie move
into the St. Clair River complex to spawn.. Spawning areas in the
St. Clair River area are also important for the rare lake stur-
geon. The lake sturgeon enters the St. Clair River to spawn in
the north channel of the St. Clair River Delta.
Regional Climate
The St. Clair River basin is characterized by typical inland
climatic patterns modified by the water mass of the Great Lakes
which surrounds it. Summer temperatures are regarded as warm and
mild, and winter temperatures are moderately cold. Mean annual
temperature regimes range from a high of 23.6°C in July, to a low
of -4.4°C in January. Periodic cyclonic storms of varying inten-
sity occur throughout the year, with the general exception of the
high summer months (June, July, and August). During this period,
thunderstorms are common as a function of atmospheric convection-
al uplift.
The modifying influence of the adjacent Great Lakes provides the
St. Clair River region with the second longest frost-free season
in the Great Lakes basin. On an average, the interval between
the last vernal frost and the first autumnal frost is 160 days.
The fall warming effect provided by the surrounding water masses
retards the occurrence of autumn frost, thus extending the grow-
ing season. The spring cooling effects of the lakes also prevent
premature vegetational growth, lessening the chances of crop and
plant loss to late spring frosts (32). The length and intensity
of the growing season may also be estimated from the accumulation
of growing degree-days. This value is an index of the amount of
heat available during a given growing season. The growing
degree-day index is normally defined as the number of degrees of
mean daily temperature above a threshold value of 5.6°C for the
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231
period in which that limit is exceeded, A normal year in the
Port Huron/Sarnia area consists of 2,Q56°C (2).
Average annual water temperature values describe a classic sig-
moidal curve, with winter minima occurring in mid-February (ap-
proximately 0.5°C), and the annual maxima being achieved in
mid-August at values approaching 21°C (4), Mean water tempera-
ture recorded for the St. Glair River for the years 1967-1982 was
11.8°C (5) .
Characteristically, the climate of the Great Lakes region is
marked by a lack of major seasonal fluctuations in precipitation
patterns. Extensive records for three adjacent weather stations
- Mount Clemens, Michigan (1940-1969); Detroit City Airport,
Detroit, Michigan (1940-1069); and Windsor, Ontario Airport
(1941-1970) - indicate that the mean annual precipitation is
77,83 cm (33) .
2. Environmental Conditions
Water Quality
Despite the highly industrialized character of the upper reaches
of the St. Clair River, water clarity in the river is exception-
ally high. This exceptional clarity is largely because Lake
Huron is the primary source for the waters of the river. As a
result, the suspended sediments are largely silicate in nature,
derived from southern Lake Huron shoreline sands (1,2).
Urban centres are found along the length of the St. Clair River,
and a major petrochemical complex is concentrated along the
Ontario side in the Sarnia-Corunna area. Concerns relating to
bacterial contamination, phenols, metals (particularly iron and
mercury) and phosphorus were identified as early as the 1940s
(34). Mercury (35) and lead (10) have been the metals of most
concern. Phenols, oil and grease, and a variety of chlorinated
organics including PCBs, hexachlorobenzene, octachlorostyrene,
hexachlorobutadiene, and volatile organics were considered the
major problem organics in the river (8,12,36).
Many of these inputs have been reduced significantly as a result
of implemented control programs. Over the years, the focus of
attention has shifted from nutrients and conventional pollutants
to toxic substances that have been detected throughout the
system, and concern for their effects on human health and the
ecosystem.
The high flows in the St. Clair River are conducive to dilution
of material inputs from sources along the river. But it should
be kept in mind that, because of the flow pattern of the river,
contaminant plumes tend to hug the shoreline, and thus, only a
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232
portion of the total flow (perhaps 5%) is available for dilution.
Nonetheless, the concentrations of many of the contaminants of
concern in the water column are extremely low, often from un-
detectable to the low ng/L range. This requires the use of
state-of-the-art sampling and analytical methodologies to provide
accurate results. Higher concentrations are often found in close
proximity to sources. It should be recognized, however, that
even low concentrations coupled with the high flow still produce
loadings that are often significant. Table VII-1 illustrates
approximate loadings for several UGLCCS parameters at typical
concentrations and flows found in the river. While organisms
respond in the short term to concentrations (e.g., acute tox-
icity), the system as a whole is ultimately responsive to load-
ings. This is particularly critical for persistent toxic organic
pollutants and toxic metals, since these contaminants can have a
severe impact on downstream lakes.
TABLE VII-1
Loading Ranges for UGLCCS Parameters in the St. Clair River.
Parameter
Concentration
Range
1-10 ppm(mg/L)
10-100 ppb(ug/L)
0.1-1.0 ppb(ug/L)
10-100 ppt(ng/L)
1-10 ppt(ng/L)
0.1-1.0 ppt(ng/L)
Associated
Loading Range
(kg/yr)
1.7xl08-1.7xl09
1.7xl06-1.7xl07
1.7xl04-1.7xl05
1.7xl03-1.7xl04
1.7xlQ2-1.7xl03
17-170
_ Chemical
Chloride
Phosphorus, Iron
Lead,Cobalt, Copper
Mercury
PCBs, PAHs, Cadmium
HCB, OCS
Even though considerable dilution does occur, the lack of lateral
mixing leads to a considerable concentration gradient across the
St. Clair River. For example, at Port Lambton (a distance of 34
km downstream of point sources in Sarnia), 95% of the contamin-
ants still remain in Canadian waters. To illustrate, on
September 23, 1985, HCB and OCS concentrations at Port Lambton
were 1.6 and 0.05 ng/L, respectively, near the Canadian shore,
and 0.02 ng/L and not detected near the U.S. shore. Similar gra-
dients were found on three other occasions for samples collected
at 100 m intervals across the river (37). These results show
that contaminant inputs along each shoreline travel downstream in
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233
plumes which tend to hug the shoreline with limited lateral,
cross-stream mixing. This fact has implications for locating
water intakes for communities downstream of industrial sources
using st, Clair River water for drinking purposes,
A comparison of typical ambient concentrations of UGLCC Study
chemicals in the river and concentrations near point sources to
water quality and drinking water guidelines for 1986 are shown in
Table VII-2. Hexachlorobenzene {HCB) concentrations in the river
near point sources below Sarnia are far in excess of both the
Canadian water quality and WHO drinking water guidelines. Am-
bient water samples collected near the Canadian shoreline at Port
Lambton are about one-tenth of the guideline values. No guide-
lines are available for octachlorostyrene (OCS), but an estimated
water quality guideline can be calculated by multiplying the HCB
guideline by the ratio of the bioconcentration factors of the two
substances, BCFjjcB/BCFgcS• This procedure assumes that HCB and
OCS have similar toxicities. Comparing the OCS water concen-
trations to this estimated guideline suggests that OCS would
exceed this calculated value in the river near point sources, but
mean ambient values would be below this guideline. On the other
hand, PCBs do not appear to present such an acute problem in the
St. Clair River, even in the industrialized Sarnia area.
Benzo-a-pyrene (BaP) was assessed as a representative polynuclear
aromatic hydrocarbon (PAH). No direct measurement of water con-
centrations was made for BaP. The BaP water concentration was
estimated by using the Ontario Ministry of Environment's (OMOE)
caged clam data (38) downstream of Imperial Oil (20 ng/g) and
dividing by the bioaccuiaulation factor for invertebrates found by
Frank et al., 680 (39) . Near Sarnia and downstream at Port
Lambton, the estimated BaP water concentration appears to exceed
the guidelines by a factor of 3 or 4.
All metals, with the exception of lead near Sarnia and near Ethyl
Corporation in Corunna, are well below the guidelines. The lead
values near point sources slightly exceed the Canadian water
quality objectives, but are well below drinking water standards.
Some other significant St. Clair Eiver organic contaminants are
compared to the guidelines in Table VII-3. All parameters exceed
guideline values near point sources. Exceedences were particu-
larly evident for perchloroethylene, carbon tetrachloride, hexa-
chlorethane, hexachlorobutadiene, and pentachlorobenzene. Am-
bient mean concentrations are well below guidelines for all para-
meters . Maximum concentrations found well downstream of the
sources are within an order of magnitude of the guidelines for
benzene, perchloroethylene, and carbon tetrachloride.
Table VII-4 compares the concentrations of chemicals in suspended
solids and unfiltered water at the head and mouth of the St.
Clair River. The data clearly show that major sources of
-------
TABLE VIT-2
Comparison of UG1.CC par«ineter concentrations in unfiltered1 water to water quality and drinking water guidelines (all
concentrations ug/l. I.
c,
ILWQA
Spec i t i
Ontar io+ +
c Water Qua 1 i ty Dr
WHO+++
i nit i ng Water
Chemical Objectives* Objectives Guide) i ne«
tiexach 1 oi*obenzene
Oc tachiorostyrene
P(*B
Benzo-a-Vyren*
Lead
Cadmium
Wereyry (Filtered)
Coj>per
I ron
Cobalt
» From (36,37,41
+ International
_.
--
—
--
25
0. 2
0.2
5
300
_„
.511.
Joint
0. 0065
t 0.0006 1*
0.001
--
25
0.2
0.2
5
300
"
Conniaa ion , Canada and
0.01
--
3
0.01
50
6
1
1000
300
"
the United States,
Near 1
Mean
0.4
0 .027
< 0,02
Amtiisnt Near
ndustrial Outfalls
Maxi muni
K.4
0.14
< 0.02
(0.03 »** --
1 .5
--
0.01 1
--
140
""
, (Sreat
2.7
—
__
--
__
..
l.akea Water Quality f
Canad i an
Shore
DoHnstre»ni of Sources
Mean
l). 0008
O.OOO2'
0.0015
HAX ioiMiB
O.tlOlfi
1 G.OQQiy
0.0022
10.041**
0. 'A3
0.01
0.007
0.42
240
o.ia
igreei»ent
2.0
0.09
0.04
1 .3
310
0,18
at 1978 («« Ameadet
*»•
I9B71.
+ * Ontario tProvincinl ) Water Quality Objectives (fW()O K101 J.
++t Uorld Health Organization (WHOH1OKJ.
* Estimated using the ^mdeline 0.1)065 uij/l. for Hf'H and multiplying by RCFn e«/ BCFocs ( 22 ,000/240,000)1103 ).
** EstimatKil from Ontario Min. of the Env. imaged ol«m Btudiea J3B).
M«rc.»ry - (-'iltered.
All other roet.als - Total.
-------
TABLE VI1-3
Comparison of other organic compounds found in the St. Clair River1 to water quality and drinking water guidelines
(all concentrations in ug/L).
Ontario WHO** Near
Water Quality Drinking Water Industrial
Chemical
Benzene
Toluene
Perch loroethylene
Carbon Tetrachloride
Hexachlo roe thane
Hexach L orobutad i ene
Pentach 1 oro benzene
1 From (36,37 ,73,74 J,
* Estimated using the
Objective Guideline hiea.n
251 interim 1
2&OI interim}
-
-
-
-
0.03
guideline U.I ug/L
10 5.3
__
10 HI
3 38
0. 2
0.40
0.005
for HHBD and roui t i pi y i ng
Outfalls
Maximum
23
--
1120
665
0.83
1.3
0.15
by BCFKTBB
Ambient Near Canadian Shore
Downstream of Sources
Mean
0,56
0.71
0,21
0.33
0.004
0.002
0.00007
/BCFuri (17,000/1
Haximun
4,3
2,2
2.4
2.0
0,007
0.006
0.00001
,200|C75t.
** World Health Organization {WHOK102}.
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236
TABLE VII-4
Comparison of chemical concentrations in unfiltered water (UW) and
suspended sediments ISS> at the head and mouth of the St. Clair River.
Compound
UGLCCS Parameters
Head Mouth
Hexaehlorobenzene
Ocrt.ach 1 orostyrene
PCBs
Lead
Cadmium
Mercury
Copper
Iron
Cobalt
Chloride
SStng/ft.)
2.0
0.7
SSUig/g>
23
1 .0
0.04
24
16000
17
UW( ng/L 1.
0.03
0.008
2.3
UW(ug/41
<3
(0.01)*
0.002
I 0.24)*
110
(0.17)*
6200
SSI
130
23
42
0.8
0.28
25
16000
16
0.8
0.12
L.5
UW(yg/Li
<3
10 .008 )*
0.011
f0.25 >*
140
(0.17)*
8400
Co unsound
Other Parameters
Head Mouth
SS>ng/g>
Benzene
To Luene
Perchloroethylene
Carbon Tetrachioride
Hexachloroethane
Hexachl orobutadiene
Pentach I oro benzene
* Estimated assuming
10 mf/L.
—
--
—
-.-»
0.5
1 .0
2.2
an average suspended
ND
ND
ND
ND
0, 16
0.09
0.012
sed iment
--
—
--
—
0. 5
20
4.5
concent rat
560
710
210
330
3.6
2.3
0.072
ion of
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237
chemicals such as HCB, OCS and mercury occur along the river.
There is no water or compound solids data for PAHs, but other
media (caged clams and sediments) show that there are significant
PAH sources in the Sarnia area. The chloride concentration also
increases over the river's course. Marginal increases occur in
lead and mercury concentrations; whereas, cadmium, copper, and
cobalt do not exhibit significant concentration differences bet-
ween uhe head and mouth. There is no apparent change in PCB
concentrations along the river based on this very limited data
set.
Some chemicals not on the UGLCCS contaminant test list that show
significant sources along the river are the volatiles benzene,
toluene, perchloroetheylene, and carbon tetrachloride, Hexa-
chloroethane, hexachlorobutadiene, and pentachlorobenzene also
display significant positive changes in concentration between the
head and mouth of the river.
The partitioning of chemicals between the suspended solids and
dissolved phase has a considerable impact on the ultimate fate of
the contaminant. The more volatile organics such as benzene,
toluene, perchloroethylene, carbon tetrachloride, and hexa-
chloroethane exhibit little tendency to bind to suspended sedi-
ments. These compounds will be subjected to continual dilution
as they move downstream, and will also be lost from the water by
the process of volatilization. The other organics and the metals
in Table VII-4 exhibit a much stronger tendency to become ad-
sorbed to suspended particulates. This adsorption reduces the
tendency of the chemicals to volatilize from the system. The
ultimate fate of the particle-bound organics and metals will be
temporary storage in Lake St. Clair followed by transport via the
Detroit River to Lake Erie.
Once the particle-bound material reaches these lakes, it is par-
tially available to benthic organisms. These organisms serve as
a food, source for fish, so the presence of these chemicals in the
lake sediments causes an increase in the contaminant burden in
consumable sport fish through the process of bioaccunmlation,
Details of the sediment/water partitioning of some of the per-
sistent organics have been documented as part of the UGLCC Study
(37,40).
In addition to concerns about the effect of effluent discharges
on water quality, serious consideration must also be given to the
effects of intermittent spills on aquatic life and drinking water
quality in the river and in downstream areas, including Lake St.
Clair and the Detroit River. Between 1974 and 1986, there were a
total of 32 spills involving 10 metric tonnes or more of deleter-
ious materials discharged directly to the St. Clair River (36).
The most studied spill was that of 9,400 gallons of perchloro-
ethylene (August 13 to 16, 1985) by Dow Chemical Company of
Sarnia (36). Drinking water supplies in the downstream towns of
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238
Wallaceburg, Walpole Island, Windsor, Amiierstburg, and
Marysvllle, Michigan, were analyzed twice weekly after the spill.
As would be expected because of the lack of lateral mixing of the
river no perchloroethylene was detected in the Marysville treat-
ment plant on the U.S. side of the river. The highest concentra-
tion observed was 7 ppb in raw water at Wallaceburg and Walpole
Island, Perchloroethylene concentrations of 2-3 ppb were found
much further downstream at Windsor and Amherstburg on the Detroit
River. The former values approach the World Health Organization
(WHO) drinking water standard for lifetime exposure of 10 ppb.
Some water sampling conducted during the UGLCC Study indicated
that higher concentrations of such chemicals as hexaehlorobenzene
and octachlorostyrene in unfiltered water and suspended sediments
were associated with rainfall events (41,42), Further studies
are required to assess the importance of such events to water
quality.
Biota Impairments
A number of studies of various biologic components of the St.
clair River ecosystem, (phytoplankton, wetlands, submerged maero-
phytes, macrozoobenthos, and fish), suggest that the river is
increasing in biological productivity in formerly impaired habi-
tats (9,15,19,21,43,44), This increase in productivity is ap-
parently a function of remedial actions to control the input of
conventional pollutants and toxic substances and to improve the
quality of the river water.
The distribution of macrozoobenthos in an aquatic ecosystem is
often used as an index of the impacts of contamination on that
system. Undisturbed benthic populations are normally character-
ized by very diverse populations with a relatively high number of
organisms per unit area. Frequently, these populations -include
significant numbers of pollution intolerant organisms. Perturbed
or impaired areas will demonstrate a characteristically reduced
diversity of species, an absence of pollution intolerant forms,
and typically a reduced number of organisms per unit area, except
in the case of pollution with organic materials (e.g., sewage),
where certain species tolerant of these conditions can thrive at
incredible densities,
Distributions of macrozoobenthos in the St. Clair River have been
well documented (1,2,9,45,46,47,48). In 1968, the Canadian
shoreline exhibited macrozoobenthic populations characteristic of
degraded conditions, compared with the U.S. shoreline. By 1977,
however, it was clear that significant improvement had occurred,
apparently in response to improved effluent treatment initiated
some years prior.
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239
Currently, benthic health along the U.S. shore is good (49,50),
although there have been some historical problems downstream of
the Black. River (46). Figure VII-2 shows the water quality zones
along the Canadian side of the river based on benthic inverte-
brate community structure. Term definitions in the figure are;
toxic = no benthic organisms; degraded = large numbers of pol-
lutant tolerant organisms; impaired = lower numbers of pollutant
tolerant organisms plus facultative species; fair = atypical
community structure; good = normal benthic community structure.
The benthic community begins to be impacted at km 5 near Sarnia*s
industrial complex. Conditions deteriorate to toxic downstream
of Dow Chemical (km 6.5), The ecological status gradually im-
proves until Talfourd Creek (km 10) where the water quality
changes adversely to a degraded state. Following this 1 km zone,
the benthic community along the Canadian shoreline gradually
improves and reaches a "good" condition at km 20,
Historically, conditions along this river shore were much worse.
In 1968, the toxic and seriously degraded zone extended over the
entire portion of the river surveyed (at least 44 km)„ This
major impact zone decreased to 21 km in 1977. A further improve-
ment is evident from the above 1985 data which showed a major
impact zone of 12 km (46).
Direct contaminant toxicity impacts to benthic fauna in the St.
Clair River appear to be confined to the Sarnia industrial water-
front and a few km downstream. Recent studies (51) have shown
that the sediments from the industrial area are lethal to Hexa-
genia, Hydallela, and fathead minnows. This confirms earlier
work that showed only pollution-tolerant benthic organisms could
survive in this region of the river (9).
A wider ranging problem is the bloconcentration and bioaccumula-
tion of chemicals in biota at all trophic levels in the river and
in downstream Lake St. Clair. Elevated concentrations of several
contaminants with known sources in the St. Clair River have been
found in plankton (51), macrophytes (51), benthic organisms [in-
cluding native (36) and introduced clams (52)], young-of-the-
year spottail shiners (36,53), and sportfish (36) in the river.
Of the UGLCCS contaminants, hexachlorobenzene, octachlorostyrene,
and mercury are of greatest concern in the St, Clair River.
Concentrations of between 50 and 100 ng/g of HCB and DCS have
been found in various sportfish from the river (36), although
some species contain little or no HCB or pcs. Elevated concen-
trations of chlordane, G-BHC and mercury were found in young-of-
the-year spottail shiners at the mouth of Perch Creek on Lake
Huron near the head of the St, Clair River (36). No fish con-
sumption guidelines exist for these compounds, but the World
Health Organization (WHO) has set a very low drinking water
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240
Black River
\
Marysvllle
St. Cfair
Michigan
Lake Huron
Sarnia
Talfourd Creek
Corrunna
Mooretown
Courtright
Bowmans Creek
Roberts LandingC
Algonac
Ontario
ZONES OF IMPAIRMENT
f^Yj:.'S'.U-.;| Moderate
|~ I Unimpaired
Channel
Seaway
Chenal Ecarte
SCALE (km)
Lake St. Clair
Goose Lake
NOTE:
Zones of impairment refer to the relative occurrence of pollution tolerant species and to the
diversity of benthie species in general-
Figure VII - 2. Zones of benthle fauna Impairment in the St. Clair River.
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241
guideline of 10 parts per trillion for HCB, OCS is probably of
comparable concern since it has a higher bioconcentration factor
than HCB.
The University of Windsor (54) studied waterfowl and muskrats on
Walpole Island in the St. Clair River. Their data show that the
nonmigratory ducks contained consistently higher HCB and OCS
residues than did their migratory counterparts. Muskrats on the
island also contained measurable HCB and OCS residues. Weseloh
and Struger (55) showed that flightless Peking ducks released on
Bassett Island in the St. Clair River rapidly accumulated HCB.
Residues of PCS, HCB, DDT and other chlorinated organics found in
diving ducks in the Lower Detroit River also suggest that water-
fowl in the St. Clair River may be a source of human toxicity
(56) .
Mercury levels in the edible portion of walleye from the Lake St.
Clair/St, Clair River vicinity have shown a steady decline from a
1970 maximum value of nearly 2.5 rug/kg or ppm. Current mercury
concentrations for walleye up to 45 cm in length are reported as
less than 0.5 ppm and are suitable for unlimited consumption
(57). Walleye in the 45-65 cm length class generally contain 0.5
to 1.0 ppm mercury, and above 65-75 cm are between 1.0 and 1.5
ppm (57).
In 1970, mercury in northern pike fillets was more than double
that of walleye. Levels now, however, are less than 25 percent
of the 1970 values. Northern pike up to 55 cm contain less than
0.5 ppm mercury while those larger than 55 cm contain between 0.5
and 1.0 ppm. Similar reductions in the mercury levels in white
bass have been observed (57). Individuals up to 30 cm contain
less than the 0.5 ppm consumption guideline. Larger fish of most
species still contain mercury concentrations in excess of 0.5
ppm. This may be due, in part, to historical mercury contamina-
tion and to mercury recycling within the system. The PCS content
of most fish in the St. Clair River and Lake St. Clair is below
the 2 ppm consumption guideline set by the OMOE and the Michigan
Department of Natural Resources (MDNR), as well as the U.S. Food
and Drug Administration action level, but levels exceeding the
Great Lakes Water Quality Agreement (GLWQA) Specific Objective of
0.1 ppm were found.
Alkyl lead compounds have been detected in game fish near Ethyl
Corporation (11) . Since the organolead compounds are much more
toxic than inorganic lead, some attention may be required to
control loadings from this source. There are no fish consumption
guidelines for these compounds, although a tentative consumption
guideline of 1.0 mg/kg was established by OMOE in 1984 for total
alkyl lead.
Elevated concentrations of several PAHs have been found in caged
clams downstream of Sarnia's industrial discharges. The data on
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242
these chemicals in the river are too limited at this stage to say
whether or not these chemicals are a problem. Other trace metals
on the UGLCCS parameter list, including cadmium, iron, copper,
and cobalt do not appear to pose any problems in biota along the
river.
Other contaminants that have been found at elevated concentra-
tions in caged clams and fish from the river are: hexachloro-
ethane, hexachlorobutadiene, pentachlorobenzene, perchloro-
ethylene, carbon tetrachloride, and benzene (36). These con-
taminants may exert an individual toxicity effect. Further, the
potential additive, antagonistic, or synergistic effects of mul-
tiple contaminant exposure to the river's biota and to fish and
water consumers is completely unknown.
Bottom Sediments
The St. Glair River is essentially a conduit of water between
Lake Huron and Lake St. Glair. Very little sediment accumulates
because of the high current velocities in the river (0,6 - 1.8
m/s). Sediments are largely a pavement of well-rounded cobbles
and boulders, with sand or till in the interstices over cohesive
glacial clay, and sand ripples and dunes moving as bed load.
There was no consistent trend along the shore in sediment thick-
ness, but variations in an offshore direction indicate a wedge-
shaped deposit that is thickest at the shoreline. The average
thickness of the deposit is 9 cm, with a mean width of 100 m.
The average texture of the samples was 63% sand, 32% gravel, and
5% silt-clay, with a mean grain size of 1.7 mm. (585.
Based on very limited sampling, the inorganic elemental composi-
tion of the St. Clair River sediments was: Si02» 65%; A1203,
6.3%; F6203, 6.9%; MgO, 3.5%; CaO, 12.7%; Na20 , 1,3%; K20, 1.6%;
Ti02, 0.4%; MnO, 0.06%; and P2Qs/ 0.05% (59). On average, the
organic carbon content of the sediments is fairly low (0.9%) as
would be expected from the coarse nature of the river's sediments
(60) .
The most extensive recent sediment surveys of the river were
conducted by the OMOE (60) in 1985 (78 stations), and by Oliver
and Pugsley (61) in 1984 (45 stations). In addition, a more
limited study of 33 stations (21 in the U.S.), in which the only
organics analyzed were PCBs and oil and grease, was conducted in
1985 by the United states Fish and Wildlife Service (62). A more
intensive survey covering 60 stations in the Sarnia industrial
area was conducted by Environment Canada and Ontario Ministry of
the Environment in 1985 (36).
These samples were collected using a variety of techniques in-
cluding cores, Shipek dredge, and divers. The information deriv-
ed from all these sampling methods is similar in this river
-------
243
because most of the surficial sediment is of recent origin (36).
Only limited historical information is available from sediments
in the river, since they are shallow and transitory in nature,
Despite the coarseness of the sediments, some heavily contamin-
ated deposits were found in the river. Table VII-5 compares the
sediment chemical concentrations to the criteria for open-water
disposal of dredged spoils. The contaminant range indicates that
a sediment guideline is exceeded at some location for every para-
meter except nitrogen and phosphorus. In the cases of PCBs,
mercury, lead, copper and iron, the mean contaminant concentra-
tion in river sediments exceeds both the Ontario and several
U.S,EPA guidelines. Most guideline exceedances occurred along
Sarnia's industrial waterfront, but sediment samples collected at
several other locations along both the Canadian and United States
shores of the river also exceeded the guidelines for some param-
eters.
No sediment objectives are available for two of the important
UGLCCS parameters, hexachlorobenzene (HCB) and octachlorostyrene
(OCS). These chemicals are present at high concentrations in
several locations along the river.
The UGLCC Study shows that the mean values for all parameters are
highest along Sarnia's industrialized waterfront and gradually
decrease downstream. The wide range of concentrations encounter-
ed in each river reach shows the extreme variability of sediment
contamination along the river. This is likely due to the transi-
tory nature of the sediment and their lack of homogeneity.
Areas of elevated concentration for HCB and OCS are found down-
stream of the Cole Drain (also known as the Township Ditch) and
adjacent to Dow Chemical's First Street sewer discharge. Con-
centrations of HCB and OCS are in the high ppm range at the
latter site. These extremely high sediment concentrations are
caused by contamination of the area with nonaqueous waste mater-
ial that has leaked from the Dow site in the past (63). The Dow
First Street Sewer has been closed. It should be noted that some
HCB/OCS-containing streams have been diverted to Fourth Street
since the time of this survey. The HCB and OCS concentrations in
bottom sediments diminished by one or two orders of magnitude
downstream of Dow, but remained elevated, well above background
levels, along the entire length of the Canadian Shoreline to Lake
St. Clair (61).
Sarnia's industrial waterfront sediments also contain high con-
centrations of oil and grease. For oil and grease, other high
concentration areas along the Canadian shoreline were found ad-
jacent to downtown Sarnia upstream of major industries {2,200 and
1,300 ppm), adjacent to Imperial Oil (1,200 ppm), just above
Talfourd Creek (4,700 and 1,200 ppm), just north of Corunna
{2,300 and 1,100 ppm), and below Courtright (1,400 ppm).
-------
TABLE VI1-5
St. Clair Hiver sediments compared to various criteria for open water disposal of dredged material (ing/kgl.
Chemical
PCBs
Oil and Grease
Mercury
Lead
Cadrn i um
Copper
I ron
Phosphorus
Kjeldahl Nitrogen
Criteria
1 Canada )
__
1500
0.3
--
—
—
—
1000
2000
Cr i teria
(Ontario J
0,05
1500
0.3
50
1
25
10,000
1000
2000
Criteria U.S.KPA 1977 St. CJLaJLc .River
Non-
Pol luied
__
< 1000
< 1.0
< 40
--
< 25
< 17,000
< 420
< 1000
Moderately
Pol luted
__
1000-2000
__
40-tiO
—
25-80
17 ,000-26,OOO
420-850
1000-2000
Heavi ly
Polluted
>10
>2000
>1 .0
>60
>B
>60
>25,000
>650
>2000
Han«te
ND-2.6
43-5300
ND-51
ND-620
ND-2.2
3.3-190
3,300-75,000
100-500
ND-1400
Sed ^ mept. 3*
Mfan
0.13
1000
2.2
Si)
O.fil
30
1 2 , OOO
230
420
" Data from 176).
-------
245
Somewhat elevated concentrations of PCBs were found in the Sarnia
area, but this may be due to an analytical interference problem
from other chlorinated organics (64). The only additional PCB
elevated concentration area was located just below Ontario Hydro,
downstream of the industrial complex (1,900 ppb), and could indi-
cate a PCB source to the river at this location.
In general, sediments on the U.S. side of the river do not con-
tain significant quantities of HCB and OCS. PCB concentrations
along this shoreline are also quite low, ranging from undeteet-
able to 150 ppb (mean value, 36 ppb). A few minor areas of ele-
vated concentrations for oil and grease were found above the Blue
Water Bridge adjacent to Port Huron (2,300 ppm), above the Belle
River adjacent to Marine City (2,000 ppm), and along the North
Channel downstream of Algonac (1,200, 1,200 and 1,300 ppm).
The concentrations of metals along the Canadian shoreline from
OMOE's complete river study (1985) show cadmium and cobalt con-
centrations are low and reasonably constant over the entire
length of the river. A few minor exceedences of dredging guide-
lines are found for iron and copper, but in general, the con-
centrations of these metals in the sediments do not appear to be
a problem. The highest value of copper (180 ppm) was found just
downstream of Sarnia's sewage treatment plant outfall. The
highest iron concentration (7,5%) was observed just'south of
Beckwith Street, Corunna, and the Corunna Waste Water Treatment
Plant.
Total lead concentrations in the sediments were low over most of
the river except just south of Ethyl Corporation. The highest
value found was 330 ppm for the site closest to Ethyl, with down-
stream concentrations decreasing systematically (244 ppm, 180
ppm, and 79 ppm). Ethyl Corporation produces alkyl lead com-
pounds which are used as anti-knocking agents in gasoline. It is
likely that the sediments contain a mixture of inorganic and
organic lead forms, all of which have been shown to bioconcen-
trate in fish (11). The high sediment lead concentrations at
these sites indicate an active lead source in this location.
Historically the most serious heavy metal problem in the St.
Clair River has been mercury. Mercury is present at significant-
ly elevated values at and downstream from Sarnia's industrial
complex. The highest mercury value (51 ppm) was recorded ad-
jacent to Dow chemical but all sites below the Cole Drain exhibit
high concentrations. Although these concentrations are consider-
ably lower than peak mercury values observed in the late 1960s
and early 1970s (1,470 ppm)(35), they are- still quite high. This
suggests that continuing, albeit low level, sources of mercury in
the area may be inhibiting reductions in sediment concentrations.
Prior to 1973, Dow Chemical operated mercury cell chlor-alkali
plants on site. These plants were identified as the source of
-------
246
mercury. These facilities have since been decommissioned and
replaced by new plants using the diaphragm process which does not
use mercury. Point source data show that low concentrations {< 1
ug/L) of mercury are still discharged from the Dow site (65).
For the metals on the U.S. side of the river, the only major
anomalous value was 620 for lead for a site just downstream
of the Canadian National Railway tunnel. The next site (approxi-
mately 1 km downstream) had a somewhat elevated concentration of
69 ppm. This site is also downstream of .the Black River which
had an elevated lead level in river mouth sediments. Most of the
other metal concentrations on the U.S. side of the river are near
Lake Huron background values, Sediment nutrient concentrations
were low on both sides of the river and do not to be a prob-
lem (64) .
Many other organic compounds not included in the UGLCCS parameter
list are present in St, Glair River sediments. Hexachloro-
butadiene, hexachloroethane, and pentachlorobenzene are other
major components of waste byproducts from Dow's chlorinated sol-
vent production. These compounds are present at high concentra-
tions in the sediments adjacent and downstream of Dow, and are
strongly correlated with HCB and OCS distributions. Similarly,
the solvents perchloroethylene and carbon tetrachloride have been
found at concentrations up to the percent range in sediments
opposite Dow due to solvent spillage and leakage of non-aqueous
wastes into the river at this site (61). Dow has taken action to
reduce these problems since these analyses (66).
Polynuclear aromatic hydrocarbons (PAHs) have been found at con-
centrations up to 140 near Sarnia's industrial complex. The
alkylated PAHs were present in all samples at lower concentra-
tions than the parent compounds. As high temperature combustion
does not produce alkyl-PAHs, their presence indicates petroleum
as a likely source. The presence of n-alkane concentrations that
correlate well with oil and grease distributions in the area
support the contention that refineries and petro-chemical plants
are the probable sources.
A limited amount of data are available on dibenzo-p-dioxins and
dibenzofurans in St. Clair River sediments (363 . Maximum con-
centrations of total dioxins and furans found downstream of Dow's
First Street sewers were 12 and 100 ppb, respectively. Most of
these compounds consisted of the octa- and heptacongeners, The
2,3,7,8 tetrachlorodibenzo-p-dioxin was not found in any of the
samples.
Four other chemicals were found at high concentrations in sedi-
ments collected near Sarnia; diphenylether, biphenyl, 4-ethyl-
biphenyl, and diethyl biphenyl (67), The concentrations of these
chemicals ranged- from undetectable (ND) to 490 ppm for diphenyl-
ether, from ND to 150 ppm for biphenyl, from ND to 5 ppm for
-------
247
4-ethylbiphenyl» and from ND to 5.2 ppm for diethylbiphenyl. The
ratio of these chemicals in the sediments is similar to that
present in heat transfer fluids. Two such fluids, Dowtherm A
(73.5% diphenylether/26.5% biphenyl) and Therminol VP-1, are
produced only in the United States by Dow and Monsanto. These
fluids also contain ethyl and diethylbiphenyls as lesser com-
ponents. The sediment data indicated that heat exchange fluids
entered the river from Sarnia's industrial complex.
Tributary Sediments
Sediment samples were collected from the mouths of tributaries
entering the St. Clair River to identify other potential con-
taminant sources to the river. The analysis of the Canadian
tributaries was conducted by the Ontario Ministry of the Environ-
ment in 1984 1985 (68). The Canadian tributary that con-
tributes the greatest chemical burden to -the river is the Cole
Drain. While no bottom sediment samples were obtained at the
Cole Drain during the Canadian tributary study, water quality and
suspended sediment data reflect treated leachate and untreated
runoff from several industrial landfill sites upstream. Levels
of HCB (0-210 ng/L), HCBD (0-345 ng/L), HCE (0-550 ng/L) and OCS
(0-160 ng/L) in whole water were generally 1-2 orders of mag-
nitude higher than at other tributaries (68). Sediment samples
from Talfourd Creek and Murphy Drain contained HCB levels of 55
103 ppb, respectively. Metal contamination in tributary
sediments resulted in provincial dredging guidelines being ex-
ceeded at several Ontario tributaries for chromium, copper, iron
and nickel. Mercury guidelines were exceeded in a single sample
obtained from the Talfourd Creek mouth (0.76 ppm). Mean instan-
taneous loadings based on suspended sediment and water chemistry
and instantaneous flow were calculated for four Ontario tributar-
ies (Table VII-6).
The U.S. tributaries were analyzed in 1985 by the Great Lakes
National Program Office (GLNPO) of the U.S.EPA (69). For the
U.S. tributaries, a high value for lead (270 ppm) and somewhat
elevated copper concentrations (160 ppm) were found in Black
River sediments (Table VII-7). The Black River is potentially a
source for anomalous lead concentrations observed south of the
Black River confluence on the St. Clair River. Elevated con-
centrations for several parameters (PCBs 76 ppb, PAHs 33 ppm, oil
and grease 11,600 ppm, lead 230 ppm, TKN 6,600 ppm and phosphorus
1,300 ppm) were found in an unnamed creek across the river from
Lambton Generating Station. The only other anomalously high
concentrations were found for PCBs, 490 and 95 ppb, in the Belle
River. High levels of calcium, strontium and sodium were found
in sediments near the Diamond Crystal Salt Company and suggest
continuing inputs of total dissolved solids. Otherwise the
-------
TAHl.K VI 1-6
L'hlo[inale() Organic!*
HCB 0
DCS 0
CCBa 41
HCKO NA*
HCE NA
Pesticide^ i us /see I
Atrazine O
alpha-BHC U
ga..a-BHC 0
Dieldrin o
£ndoaul phan- I 0
pp-UDE 0
Hetala ( na/sec 1
Cadniuit 0
Chro.iu. 14
Copper 4
[ ron ti33«t
Lead 5
Herciiry o
2 i nc 26
J DMCA I rOFi refVr^i
2 Th» tntmfaMcx i
I'errh
las) I wa I
.00 O.UO
.00 0.00
.5 0.00
0.00
0.00
. 0 186.0
.00 o.o
.00 5.O
.4 0,0
,00 0,0
.03 o.oo
.IT 0.09
.3 20,7
.4 3X.B
9163
.02 I3.b44
.009 0.063
•"* "'"
UC# ll.MI,
on uniBFio r riisursriea' ii>r
IJTBIH
t S3 1 1 WH I
17.6 6u,oO
14. ti 20, UO
4 , OO 0 , 00
NA 53.0
NA 62.0
1 .0 8S.O
0.04 2.5
0.01 0.4
0.2 0.0
0.1. 0.0
O.OB o.oo
0.02 0.03
1.5 0.2
4.4 O.I
434 37k
1.02 2,43
o .ooti o . u 19
6.1 12.33
Tat I'ourO
( uper ri>a»i
las! I wal
O.SO
O.UU
9. BO
NA
NA
o.o
0.00
o.oo
0.4
o.oo
o.uo
0.07
3.4
2.9
2494
1.93
0.041
11 .6?
I
0
0
0
0
512
0
0
0
0
0
0
5
7
2648
3
0
1!»
to the
.00
,00
.00
,00
,00
.0
.»
.2
.0
,0
.00
.IT
,7
,3
.673
.012
.32
St..
'is i i ouro Bfttiy
»"re*-h Creek
t *oui hi
1 a a I I MB 1 1 11*1 I wml
3.70
0.05
1.70
NA
NA
0.0
o.oo
o.oo
0.7
1,1,
0.00
o.os
7.2
6. J
lt>44
2.9
0.019
13.22
Clair Hiirei
17.
0.
0,
1.
18.
557.
S.
0.
0.
0.
0,
0,
5.
1 .
1124
T.
0,
25.
OO O.OB U.OO
oo o,w7 o.oo
oo 0.30 0,00
01) NA 0.00
0 NA 0.00
0 0.0 271.0
a o.oo u.o
a o.oo u.02
M
0 0,02 O.O |^
o o.oi o.o °°
UO 0,02 0.00
57 0.01 0.06
S 0.7 1.4
ft 1.0 2.1
SI2 550
442 U.42 0.364
Oi>4 O.U01 0,004
24 2.B7 S.83
Hot. Available.
-------
249
TABLE VII-7.
Summary of sediment quality in mouths of Michigan tributaries to the St. Clair
River.
NUMBER
OF ANALYTICAL
DETECTIONS
STANDARD
MAXIMUM
MINIMUM
MEAN DEVIATION
MAJOR METALS AND TRACE METALS < n«/k« )
CALCIUM
MAGNESIUM
SODIUM
POTASSIUM
ALUMINUM
IRON
ARSENIC
BARIUM
BERYL I UM
BISMUTH
CADMIUM
CHROMIUM
COBALT
COPPER
LEAD
MANGANESE
MOLYBDENUM
NICKEL
SILVER
STRONTIUM
VANADIUM
ZTNC
TIN
LITHIUM
SELENIUM
YTTRIUM
MERCURY
NUTRIENTS AND
COD
OIL AND GREASE
AMMONIA
TKN
PHOSPHORUS
CYANIDE
TOTAL SOLIDS <
TOTAL VOLATILE
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
7
OTHERS PARAMETERS IN
10
10
10
10
10
10
X) 10
SOLIDS (X) 10
TOTAL PCBs, PAHs, PHTHALATE ESTERS
TOTAL PCBs
TOTAL PAHs
TOTAL DDTs
7
6
7
TOTAL PHTHALATES 8
SELECTED OTHER
ORGANICS
-------
250
Michigan tributaries do not appear to be significant sources of
contaminants to the river.
Most sediments in the St. Clair River are transitory, having a
lifetime in the river of less than one year (61). The moving bed
sediments constitute only a very minor component (less than 1
percent) of total contaminant transport along the river (64),
The ultimate sink of this fine sand that constitutes bed load
appears to be the St. Clair River Delta. Sand cores taken from
the delta area contain mercury and other contaminants to a con-
siderable depth (54). Because of the contaminant storage in this
area, contaminant body burdens in wildlife could remain elevated
for a considerable period, even after control measures have been
implemented. Most of the contaminants are transported via water
and suspended solids which would be carried and dispersed further
down the system into Lake St. Clair and Lake Erie.
-------
251
B. SPECIFIC CONCERNS
A summary of specific concerns including contaminants and as-
sociated use impairments, media affected jand location is provided
in Table VII-8.
1. Conventional Pollutants
Nutrients
Phosphorous reduction programs have had a major impact on the
discharge of phosphorus to the St. Clair River. Water column
concentrations for total phosphorus (1984) were low, ranging from
0.009 to 0.03 mg/L (41). These values are much lower than re-
ported for the river in the 1970s (45). Bottom sediments (64)
and suspended sediments (41) for the river are both below the
1000 ppm guideline for open-water disposal of dredged sediments.
The nitrate/nitrite concentration range found in the river
(0.29-0,31 mg/L) is typical of that found in oligotrophic waters
(70). Thus, the discharge of nutrients to the St. Clair River
seems to be largely under control.
Chloride
Chloride loadings to the St. Clair River are very high. The
chloride concentration changes from a mean of 6.2 mg/L at the
head of the river, to 7,7 mg/L at the river's mouth (41). This
change amounts to a daily river loading of about 585 metric
tonnes of chloride. Chloride is a conservative parameter that
will not be lost from the system. The increased salinity of the
lower Great Lakes from these very large chloride inputs could
potentially have a significant effect on the structure of bio-
logical communities in the system (71). A shift in the organism
diversity to more saline-tolerant species (halophilic) could
occur over long time scales.
Bacteria
Concentrations of bacteria increase along the course of the St.
Clair River. Heterotroph counts in bottom waters along the
Canadian shore increased from 2,200 organisms/ml at the head of
the river, to 10,500 at the mouth (51). sediment bacteria in-
creased from 1,500 bacteria/ml at the head, to 450,000 at the
mouth. Head to mouth changes along the U.S. shore were 110 to
13,000 organisms/ml for the water, and 700 to 27,000 hetero-
trophs/ml for the sediments. In some cases, swimming areas along
the river have been closed due to bacterial contamination (72).
-------
TABLE VII-H
Sppc*it"ir concerns in thft St. Clitir River, UB»B impaired, and geographic acope of the perceived probten.
CONCERN
IMPAIRMENT
MEDIA
GEOGRAPHIC SCOPE
Convent tonal Pollutants
chl oricle
bacteria
Mfi LCC Parameters
hexachlorotaenaene
potential alteration of
biological community
struct lire
potential human health
hazard
toxicity to biota
hiimftn health
water
wster» sediment*
water, sediments, biota
fish
whole river
lower Great Lakes
some areas along
river, increases
downstream
below Sarnia
whole river
octachlorostyrene
PAH a
oil and grease
PCRs
lead
Other Contaminants!
hexachlorobutadiene
be xacihloroe thane
pentachlorobenzene
benz.ene
perch!oroethylene
carbon tetrachloride
diphenyi ether
biphenyl
pheno1s
i>**stini des
toxicity to biota
human health
toxicitv to biota
toxicitv to benthic
communi ty
human health hazard
toxicity to fish
human health
toxicity to biota
human health
toxicitv to biota
toxicity to biota
toxicity to biota
toxicity to biota
water, sediments, biota
f ish
sediments, biota
sediment
water (?I
some fish
sediments, biota
fish, sediment
fish
sediment
water, sediments, biota
water, sediments, biota
water, sediments, biota
water, biota
water, biota
water, biota
sedi uents
sediments
water
below Sarnia
whole river
below Sarnia
below Lambton
whole river (esp.
Ontario shore!
whole river
below Lambton
whole river Jbelow
Sarnia, eap, near Dow I
below Ethyl Corp,
below Ethyi Corp.
below Sarnia (esp»
near Dow I
below Sarnia
below Sarnia
be low Sarnia
Sarnia
Sarnia
Sarnia dischargers
whoie river
in
K)
? - Further studies required to determine potential impact.
* - Historical problem, however, little data available on present concentrations in various media.
-------
253
2. UGLCCS Toxic Organics and Heavy Metals
The priority contaminants in the St. Glair River found from the
water, biota, and sediment reports are remarkably consistent.
Hexachlorobenzene (HCB) and octachlorostyrene (OCS) are the two
chlorinated UGLCCS chemicals of most concern. These chemicals
are associated with Dow Chemical's Sarnia operations. Major
sources include Dow Chemical's direct sewer discharges, and in-
direct leachate from Dow's Scott Road landfill via the Cole
Drain. HCB in the St. Clair River water exceeds water quality
guidelines near the discharges, and OCS exceeds an approximate
guideline value calculated from bioconcentration considerations.
The river sediments are contaminated with HCB and OCS all the way
to Lake St. Clair (59,76). HCB and OCS are also bioaccumulated
by all trophic levels of biota including plankton, benthic organ-
isms, young-of-the-year fish, and sport fish.
PAHs, including benzo-a-pyrene, have been found in caged clams
and sediments in the river. PAHs were not detected in water
samples obtained from the mouth of Talfou'rd Creek, Baby Creek,
Murphy Drain or the Cole Drain in 1984. Data on PAHs in the St.
Clair system are limited at present, but sufficient information
exists to demonstrate cause for concern.
The importance of PCB loadings to the St. Clair River is not a
clear-cut issue. PCB concentrations in bottom sediments along
Sarnia's industrial waterfront appear to be elevated. However,
analytical difficulties in PCB determinations in this area have
been cited (64). The presence of other halogenated organics may
be leading to false high PCB readings (by a factor of 4) in sedi-
ments from this region (64,77). PCBs in fish from the river may
also be misidentified and overestimated. Maximum PCB levels in
sediments from Ontario tributaries were observed at the mouth of
Talfourd Creek (65 ppb).
PCB levels appear to be somewhat elevated in sediments and young-
of-the-year fish downstream of Lambton Generating Station.
Because this site is about 15 km downstream of Sarnia's indus-
trial discharges, PCB analytical interferences may be less sig-
nificant at this site. Thus, a PCB discharge to the river may be
occurring in this region. The PCB residues in fish from the
river and Lake St. Clair have declined by 50% since 1976 (36).
Except for a few of the larger fish of some species, most sport
fish are less than the 2 ppm guideline.
Because of the considerable number of refineries and petrochem-
ical plants along the Canadian side of the river, oil and grease
discharges to the river are of concern. Oil and grease in sedi-
ments are highest along Sarnia's industrial waterfront, with many
values exceeding open-water dredge disposal guidelines. Tar-
saturated sediments were observed from just north of the
Imperial/ Polysar boundary, to south of the Suncor property (36).
-------
254
They occur at or just below the surface in cores collected up to
25 meters from the shore. The cohesion provided by the tar
apparently stabilizes the contaminated sediments and hinders
their incorporation into bed load transport.
Additional areas on the Canadian shoreline with high sediment oil
and grease levels were adjacent to downtown Sarnia (upstream of
the industrial complex), just above Talfourd Creek, just north of
Corunna, and below Courtright. On the U.S. side of the river,
oil and grease sediment levels were high above the Blue Water
Bridge adjacent to Port Huron, above the Belle River adjacent to
Marine City, and along the north channel downstream of Algonac.
An unnamed creek across the river from Lambton Generating Station
also contained anomalously high oil and grease sediment concen-
trations. However, the creeK has no visible discharge to the St.
Clair River and the high level here may be the result of a spill
on Michigan Highway 29 (64). Oil and grease levels measured at
the mouths of Baby Creek and the Murphy Drain were generally an
order of magnitude higher than other Ontario tributaries with a
maximum value of 7,380 ppm observed at the Murphy Drain.
Of the UGLCCS heavy metals, only mercury and lead appear to be of
concern. Mercury concentrations of the larger fish of some
species still exceed the consumption guideline of 0.5 ppm. Sedi-
ment mercury concentrations near Dow are still elevated, indi-
cating a continuing mercury source in the area. The discharge of
mercury to the river has been reduced dramatically since the
1970s, and fish mercury concentrations may be due, in part, to
mercury recycling in the system.
Lead concentrations in sediments and biota are elevated down-
stream of Ethyl Corporation. Because a portion of the lead load-
ing from this source is the more toxic alky! lead compounds (11),
the environmental implications of this discharge to the river are
of concern.
3. Other Specific Contaminants
Three other contaminants associated with Dow's chlorinated sol-
vent production that are consistently present in water, sedi-
ments, and biota in the river are hexachlorobutadiene, hexa-
chloroethane, and pentachlorobenzene. The concentrations of
these contaminants are highly correlated with HCB and OCS. The
discharge of volatile organics to the river is also fairly high.
Volatile substances of greatest concern in the area are benzene,
perchloroethylene, and carbon tetrachloride. Near source inputs,
these chemicals are found at higher concentrations than recom-
mended water quality guidelines. They are also found in biota,
including fish, in the river. Diphenylether and biphenyl are
found at very high concentrations in sediments along Sarnia's
industrial waterfront. The loss of heat exchange fluids to the
-------
255
river at this location is apparent.
Phenols have been a historical problem along the Canadian side of
the river downstream from Sarnia. Since the implementation of
improved waste water treatment by industrial waste dischargers in
the area, the phenol loadings to the river have been drastically
reduced (78). Very little data on phenols was produced for the
water, biota, and sediment studies. The Point Source Workgroup
(65) showed that discharges of phenols were still of concern in
certain industrial and municipal discharges in Sarnia.
Pesticides are common organics that have been studied extensively
throughout the Great Lakes Basin. Several common pesticides such
as DDT and its breakdown products, alpha- and gamma-benzene hexa-
chloride, and dieldrin are found in the St. Glair River (79),
However, the concentration of these contaminants does not change
significantly over the river's course, indicating that there are
no significant sources along the river (37,79). Elevated con-
centrations of ehlordane, gamma-BHC and mercury were found in
young-of-the-year spottail shiners at the mouth of Perch Creek on
Lake Huron near the head of the St. Glair River (36), Several
pesticides were frequently detected in Ontario tributaries to the
St. Glair River. These included alpha-BHC, a breakdown product
of the insecticide lindane and atrazine, a triazine herbicide,
found in whole water samples. The latter compound was estimated
to account for a nearly 1 mg/s loss to the St. Clair River, from
Talfourd and Baby Creeks and Murphy Cole Drains, The pre-
dominant pesticide occurring on suspended solids was dieldrin;
however, total loading from these creeks was in the order of 0.9
ug/s (68).
4, Habitat Alterations
Historically, humans made considerable changes in the it. Clair
river for navigational purposes (80). Recent physical habitat
alterations along the St. Clair River appear to be minimal;
however, more information about shoreline development and its
effects is needed before a definitive statement can be made.
There has been periodic dredging in the lower channels of the
river about every two years. Chemical alteration of the habitat
is a problem for 12 km downstream of Sarnia's heavy industry, as
indicated by benthic studies (49).
-------
256
C. SOURCES
1. Municipal and Industrial Point Sources
A study by the UGLCCS Point Source Workgroup (65) indicates that
a total of 52 known point sources were discharging to the St.
Clair River in 1986. The total point source flow was estimated
at 91,800 x 103 m3/d. Apparently, 96 percent of this total was
utilized by electrical generating facilities for once-through,
noncontact cooling; of the remainder of the flow, 2,590 x 10^
m-Vd, was contributed from industrial sources. Eighteen of these
sources were sampled for a total of 26 study parameters. The
calculated loadings from these analyses are presented in Table
VII-9.
Industrial sources were found to be important contributors of
most of the UGLCC Study parameters, compared with municipal faci-
lities. The predominant sources were the petrochemical plants in
the Sarnia, Ontario area, known as "Chemical Valley", The major-
ity of the sources were located in the upper 10 km of the St.
Clair River. These industrial sources were responsible for the
majority of the loadings of HCB, QCS, PAHs, oil and grease, lead,
mercury, copper, nickel, cobalt, iron, chromium, chlorides, total
organic carbon (TOC), total suspended solids (TSS), and a spec-
trum of organic contaminants including volatile hydrocarbons,
acid and other base neutral extractable hydrocarbons.
A comparison of municipal direct and indirect sources, and in-
dustrial direct and indirect sources by country of origin for
each parameter of concern is shown in Table VII-10. Direct
sources are those discharged to the river, indirect are dis-
charged to tributaries or drains which flow into the St. Clair
River,
The point source data are too limited (single day survey by the
U.S., and three to six day surveys by Canada) to permit the cal-
culation of precise annual loadings. For more common parameters,
the data were compared to self-monitoring data collected by the
industries and municipalities. This provides an indication as to
how representative the sampling was. For most parameters, the
point source samples were within normal r'anges. Despite the
limitations, the data are adequate to make conclusions and recom-
mendations concerning relative point source contributions, and
identify major point sources of concern.
The point source contributions of the following parameters were
considered important by the Point Source Workgroup Report (65),
based on concentration alone, for the reasons indicated;
-------
257
TABLE VI1-9
summary of principal sources of UBLCCS param*r*rs to the St. Glair River
(based on data collected in 1986).
PARAMETER
fatal PCBa
He scaehloro benzene
Oetaehlorostyrene
Total Phenols
PAHS
Total Cyanide
Oil and Sreaa*
Total Cadiiiwm
Total Lead
Total Zinc
Total M#rc«rf
Total Copper
Total Nickel
Total Cobalt
Total Iron
Chloride
Phoaphorua-P
Anmonia-N
Total Qrfanie
Carbon
Total Suspended
Solids
Biochemical
Qx^aen Demand
Tot«l Chromium
Total Volatiles
Total Acid
Extractablea
Total Other
lase/VeutcaLs ,
i
TOTAL !
LOADING! PRINCIPAL
(kf/d) ! SOURCE! S)
0,006 [Dow Chemical
[Port Huron WWTP
i
0,024? JDo« Chemical
i
0,0047 !Do« Chemical
12.1 JSurnia WPCP
j DOH Chemical
j Pt , Edward WPCP
0.331 ICole Drain
IPolirsar Sarnia
3,12 ! Marine City WWTP
3170 ICol* Drain
0 , 143 ! Sarnia WPCP
i
29.0 ! Ethyl Canada
J
44,9 I Sarnia WPCP
0,0443 ',Do» Chemical
11.8 !Do» Chenical
4,3? ! Sarnia WPCP
J Po 1 jrsa r Sa rn i a
!Dow Chemical
0.857 jPolycar S«rni«
1
Si! JCIL Inc.
j Sarnia HPCP
356,000 jDow Chemical
Si, 8 [Sarnia WPCP
IPort Huron WWTP
1670 i Sarnia WPCP
[Polysar Sarnia
ICIL" inc.
{St. Clair County
!- Alzonae WWTP
S700 {Polysar Sarnia
! Sarnia wpcp
9400 ICIL Inc.
i
7?4Q | Sarnia WPCP
16, 1 ICIL Inc.
iPolvmar Corunna
254 j Polysar Sarnia
{Dow Chemical
SIthvl Canada
1.09 IPolysar Sarnia
1.03 JDow Chemical
% OF
TOTAL
S3, 3
33.4
>90
'100
39,6
14, a
13.9
32,6
30, 1
55 . i
41 ,0
95.8
65.9
47.9
§4 .5
52.9
22.3
15.0
14,7
78.!
33. 9
L-JU-l
78. 1
27 ,4
15,3
37. i
21 ,0
15,3
10, g
34
_il__i
53
26
56
16
SI
20
17
S6 ,4
78
LOADING
I kf/d )
0.0032
0,002
0,03
0.0047
4,32
1.78
1.69
0.172
0.163 .
1.8
1,300
0.137
19.1
19.7
0 ,0217
S, 24
O.i13
0, 657
0 , 844
0.67
209
137
883 ,§20
43 , (j
14, §
633
3SO
2S6
1§1
2 , 200
1.850
4,980
1,000
8.96
2,5
124 ,0
SI .0
43.3
0.74
0, 78
CONCSNT1A-
TION RANGE
(ug/Lt
ND-Q.441*
0.02S
ND-0,32i
0,024-0,094
82-163
3.5-4.5
11-17BO
1.2 ( a-vf 1
0, 4S 1 aw« )
270
1 , 700 f avj i
ND-7
293-910
no-Tio
TO-0,88
ND-1CJ7
6-15
2S-44
0,88 i i¥f> )
2S-41
530-870
li§0-31 SO
211 ,000 -
1 ,271 ,000
580-1300
480
5800-20000
1 7300-20000
800 ( avg 1
21,000
4SOOO-SOOOO
33000-dlOOO
I70OO-24000
41000 ( avg )
20-21
S58-5€7
ND-3?,40G
ND-1 ,500
ND-1 , 500
ND-7 7
ND-tt
1MPOH-
TAMT
PA SAME-
TIB I*)1
"
*
-
«
™ j *
it
-
-
*
-
-
—
-
—
—
-
*
™~
•*
-
*
*
-
—
1 Facilities and
described in the
«r* designated as "important" under the condition
text and in the UGLCCS Point, Source Workgroup Report I 681 .
1 Detected once only in 6 samples of First Street 64" sewer IMDL O.Oi
-------
TAHLR VI I- 10
for won re
PABAHRTiilt
KI.OW*
I0*nj /it
SIWVKYRD)
DCS*
P*H»
TOTAL
CYANIDE
on. *
ORE*SI
TOTAL
CAOHIUH
TOTAL
fcRAB
TOTAL
7. SHC
TOTAL
PHENOLS
U.S.
CDN ,
TOTAL
U.S.
ri»N .
TfiTAl*
U.S.
CDN,
TOTMi
U.S.
(JON,
TOTAL.
U.S.
CON.
JOTA.L
U.S.
CBN.
TOTAL
U.S.
CDN.
TOTAL
U.S.
CDN,
TOTAL*
U.S.
CBW.
TOTAL
U.S.
CDN.
TOTAL
U.S.
emu.
IBTA.L
HI) I.I hi
lUlj/iil
..#
-
. DU01
. 1
.uuuul
0.1)2
„
-
0,02
_
to
1
1-15
I-Z
_
g
1
_
2,000
100
_
0.1
6
1
&
2
s
NUN 1C! PA I.
DIHFCT
Mi.tt
S3.X
... , 1±U
O.UWZi
o,u
^ II.OUUB
O.UVIIli!
o.uttua
L u.odiMi:
U.OUUUU&
u,U
O . jJO(JH
6 35-.—,
O.UO4il7
tt. 131
.. «,Hi^_,
0.1SH
2 . Z«
. ;'.;»«. _.
:».«z
IB. a
...*:«. 1. _i
HUN in PAL
INItlKKCT
NS»*
a. «i
!>,4.»
N»"
N**»*
„
NS
NA
.
NS
NA
NS
NA
-
NS
NA
-
NS
NA
-
NS
NA
-
NS
NA
NS
NA
NS
NA
IMlMSTllI Al
niHRCT
BU.l
1 , 7BO
, 1 ,JtiU, ...
CI.(M>tt21>
O.tt032
U.UO-tfi
U. UUOUI4H
u.OiJb
g.iizJM
NA
U.U04U
_
0.0
4.S2
4.5Z
(1.0
O.U396
u.iKmfi
o.o
0.1H/NA
_
ia. i
HUH
aaa
0.0
O.UU14
O . OUJL4__
0 . 02D
SIS. 7
.. . 2S.?.
o.aiis
18. ft
J8.8 _,
INnilSTNIAi,
INIifHKOT
Jil.U
tfl
^ 11*!!....
NA
o.u
U,C1
N*
u.ooos
O . CHIOS
NA
U.OUUI
_
u, isa
D.VHl
i_ Ij-LJ
o.o
0. IT2
0. 172
O.O
1) I, kl.i
._0.«MJ .
Z94
i ,3S!0
1 ,«10
u.o
u.u
U.fi
o.o:iin>
O.MHIi
i1- •*( "»...
V . 00 1 >
2.«»
u itIS. ..J
TOTAL
DIBKCT
107
1 ,U1U
ijiau
O.(tu671
o.ooast
..O.OUH97
o.ooootu
0 ,024 1
L -ttiM32
0.004«
_
V.60U
1U.S
!_ 11 ,0
0.0
0. 158
0.168
23?
O.I7I/NA
_ 4.5J+
JilO
1 ,170
1 ,MU
O,OU4S»1
o, i :»B
o . 1 4 :i
0, 17U
21.il
. *a,i..
;i.ia
;««.4
.«iL..
TOTAL
THRIRKCT
;io.«
itii
_UU _
o.o
, 0,0
o.uuos
,^J,.OUU8
o.oooi
.
0. 158
0.9B3
t 1,14
0.0
0.112
o. nz
o.o
O.BU3
0.8B3
294
1 ,320
L I.Blft
O.O
U.O
0,0
O.U 306
O.MHit
o^tia i
O. Ott 13
2.H«_
2,78
PT. SOtliCK
TDTAL
1 ,18
1,1174
.1 ».UO....
" 4I.O0677~"
O.ttO-li
O-UOHfll
0 . uuuOle
O.OJ4B
O.OZ47
0.0041
O.BST
n.s
i__lS-!JL-_
O.l>
0.131
tt.331_
Z.37
41.H54 +
3.Z2*.
tisn
2,490
3^2
41.1
41, IL
% OK PT.
SOU Mil i
TOTAL
S,&
91. S
L__LOJ
t)4.3
35. 7
1OO
O,3
Vtt.1
104
-
_
5,4
SM.H
ioa
0
100
100
-
_
21 . t
5H.4
i ua i
U.J
S8.1
100
0.7
»».3
to«
B.4
•u ,i>
igo_.
to
tn
00
-------
l I-1II. 4eBnt'dl
PAHAMKTEK
TOTAL ;
J TOT A"£
jll.S.
TOTAL !
COPPER iCHN.
{TOTAL
jll.S,
TOTAL !
NICKEL ifiBN.
i TOTAL
[U.S.
TOTAI, j
COBALT ;cnn.
; TOTAL
iU.S.
TOTAL ]
IRON j(TDN,
: TOTAL
[U.S.
CHLORIDE jfi ON.
.'TOTAL
[U.S.
PHOSPHORUS 1
AS p '.cat.
! TOTAL
[U.S.
AHHONIA I
AS N [CON.
I TOTAL
TOTAI. [U.S.
OH11AN1C |_ ,
OAK RON ICON.
I TOO 1 i
i TOTAL
TOTAL ! 11 , S .
SUSPENDED
SOLIDS ICON.
iss) ;
JTCTAL.
RineHKMICAL [U.S.
OXVflKN i
IWHANB IC1IN.!*"
I H01»S I |
JTOTAl.
Ml! I.I • )
luc/LI
O.O11I11
U.UBft
1
S
_
4
6
-
O.O01
S
_
14
i
_
louo
soo
til
100
to
100
to
too
_
4 , OOO
1 tUOO
2,000
2.0OO
MUNICIPAL
D I BKfiT
O.I1O144
It . lltiz I
U.U4I3S4
U.!)(i4
1 . hb
t . S 2
a. 429
t ,O3
§ |_. JB
0,024
U. 1 JO
.o.jjii
56 .0
151
207
8,6 JO
6,724)
IS. SOO
51 ,8
4B.2
]OU
2.2
bia
.. 940
B14
I . aid
2 aso
«««
azs
t .4341
1 ,22O
5,1011
, _ -.. .j s^azy ._
MUNICIPAL
INO1MECT
Ni
NA
„
NS
NA
^
NS
NA
^ _
MS
NA
-
NS
NA
„
NS
NA
^
N9
O.4I2
fi_ 4 I 2
NS
NA
_
NS
NA
_
NS
23.3
23. J
NS
6.8k
Sitffl .
INOUSTMIAL
UIMKCT
O.OUUtNi
W . U^fl4
0 . 0 3 & 4
0, I O1
f .B4
1.75
IJ.U-UO
2. 1 1
•A. Ift
O.OO3
O.lilO
O.BI:I _
1 .S3
33H
;i;ia
4.72.1
3 36, OHO
341 .000
O.fiO
-2*.(t=
-2li 2£
1 .4&
121
1E'^
llli
2 , T4IO«
Z,«T4I
«,S40
4).4>itU
78.lt
NA
-
INUII.1TKIAI.
1NDIKECT
NA
. -
u.o«5a
0. 104
1 .48
I , Ali
NA
4I.THI
,__ K.7fiJ
NA
u.o
41.11
ti.Mft
2B.3
>___., .3ft ,a
:»S»H
16, :too
| ti . TOO
tt.114
15-1
o.iiy
4 . fc.'
S.^J
s&t
434
SHS
30 S
1 .250
135
NA
-
TOTAI,
UIUGCT
O.O014U
U.U319
0.0389
a. ait
y.ao
10.1 . .
O.408
3.14
3. el
0,o2T
O.H1O
o.as?
97. S
4«y
548
i;s,aoo
342,000
3S5.OOO
5Z.4
21 ,4
, 1J.B
283
1.3BO
t .580
SIS
4.740*
B.720
1 ,240
1> , af 41
B^IZSL
1 ,300
T«TAL
-
o.yosa
O.OOS3
0.1(14
1.4*
1-ib
0.76 1
tt.Jlil
O,0
0.0
".y&
IS. 3
Ib, JOO
16.7OO
&.1»
10.3
IK.}
o.ya
4.82
S.S1
S51
434
SMS
3Oti
at,d
1.Z10
TOTAL.
O.UO] 4 a
O.U4XU
0 y443
1 .OK
10. a
t— 11. M_
U,4t>(>
3. SO
4.31
0,021
O.B3O
0,!ji7
*4.«
61T
&BZ
1 4,OaO
342 ,OOO
JtSJUQijO ,
58.2
SI ,1
ny . 9
2H4
t ,3«0
rri jo
1 ,530
6 , 1 10«
H , ?OO
i ,$4)0
7 ,B4«
. a.Vuu." ..
2.040
i, or FT,
TOTAL
3.1
»i,J
IOO
til .4}
10. a
US, 2
i_UHI
0.5
»a,5
11. i
a*. a
mo
90. 1
IOO
£4.1
38.3
1OO
11. a
B3.0
10.6
22. a
IT. 2
IfiO. .
ie.fi
H3.4
|04>
"
! 1 I_
Ul
I tt5 |.
f iitant *li I ffrencres for NOI.S.
net ii^«lin||H at- ClLt Dc*w ChttHiC
Ciiiiiirt i #*n I fwiusn* i»I »»>iiirni?H un I
-------
260
UGLCCS Parameters: Non-UGLCCS Parameters:
i. Hexachlorobenzene (HCB) vii. Chromium
ii. Total Phenols vli±. Total Volatiles
iii. Chrysene, Pyrene and Fluoranthene
iv. Cyanide
v. Lead
vi. Ammonia Nitrogen
i) Hexachlorobenzene (HCB): the major source of HCB, the Dow
Chemical 1st Street 42" and 54" sewers, had variable con-
centrations {ND-0,829 mg/L). Although effluent quality
cannot be directly compared to ambient water quality stan-
dards or guidance, effluent concentrations exceeded the
Provincial Water Quality Objective of 0.0055 ug/L. Since
the survey, the process streams containing HCB have been
diverted to a spill containment pond. The pond discharges
to the Dow 4th Street Sewer. The effect of this change on
the loadings is unknown. The total loading was 25 grams/
day.
ii) Total Phenols: the Ontario Industrial Discharge Objective
of 20 ug/L was exceeded at Polysar Sarnia and Suncor.
Effluent concentrations at the Sarnia WWTP and the Pt.
Edward WWTP also exceeded the Ontario Municipal Effluent
Objective of 20 ug/L. The total loading was 12.2 kg/d of
which about 70% was contributed by these four facilities.
iii} Chrysene, Pyrene, Fluoranthene: these PAHs were found in
one source and only at low concentrations. However, these
concentrations were in excess of the U.S.EPA AWQC Human
Health Criteria for total PAHs for fish ingestion of 31.1
ng/L; the only ambient water quality guidance available for
PAHs. This criterion is below the method detection limit
of the analytical methods used. This suggests that other
point sources may too be discharging at levels of concern.
The total loading of these three compounds was 190 g/d.
iv) Total Cyanide: an exceptionally high concentration of
total cyanide (270 ug/L) was found at the Marine City WWTP.
The City has an industry that discharges potential cyanide
containing waste water to the WWTP and cyanide has been
detected in the WWTP in the past. Other point sources
discharged total cyanide at levels below industrial dis-
charge objectives and often below ambient water criteria.
The total loading was 3.22 kg/d.
v) Total Lead: this parameter is of concern only in the Ethyl
Canada effluent. This is due to its presence in concentra-
tions in excess of the GLWQA specific objective and the
OMOE Provincial Water Quality Objective (PWQO) of 25 ug/L.
The total loading of lead was 29 kg/d, 66% of which was
-------
261
attributed to Ethyl Canada.
vi) Ammonia-Nitrogen: concentration in excess of the 10 mg/L
Ontario Industrial Discharge Objective were present in the
Sarnia WWTP and the Polysar Sarnia Biox effluents. The
total loading was 1,67 tonnes/d.
vli) Total chromium: high concentrations (258 to 567 ug/L) were
detected at Polysar Corunna. The effluent would require
substantial dilution to meet the GLWQA Specific Objective
of 50 ug/L and the Michigan Rule 57 allowable level of 1,5
ug/L at the edge of the mixing zone. The total loading from
all sources was 16.1 Jtg/d.
viii) Total Volatiles; the total loadings of this group of com-
pounds was 254 kg/d. Benzene, chloroethane and toluene
accounted for 72% of the total. Polysar Sarnia (51%), Dow
Chemical (20%), and Ethyl Canada (17%) were the main
contributors of these compounds, Each facility had con-
centrations of one or more volatiles well in excess (> lOx)
of ambient guidelines.
Principal Effluent Contributors:
In terms of effluent loadings, the following facilities were
considered to be the principal contributors of one or more of the
parameters studied.
Canada:
a. Sarnia WWTP - phenols, nickel, phosphorus, and ammonia.
b. The Cole Drain, Sarnia - PAHs, oil and grease, and cyanide.
c. Polysar, Sarnia - benzene, phenols, cobalt, and ammonia.
d. Dow Chemical, Sarnia - HCB, OCS, PCBs, copper, mercury, and
volatiles,
e. Suncor, Sarnia - volatile aromatics (associated with a pro-
cess upset at the time of the survey).
f. Ethyl Canada, Corunna - lead, mercury, volatiles (chloroeth-
ane) .
g. CIL, Courtright - iron, TSS, and chromium,
U.S. ;
a. Port Huron WWTP - PCBs, phosphorus.
b. Marine City WWTP - cyanide.
c. St. Clair County - Algonac WWTP - ammonia.
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262
2. Urban Nonpoint Sources
Michigan
There is a remarkable lack of data regarding the impacts of urban
nonpoint sources on the water quality of the St. Clair River
system from Michigan. In 1986, the Michigan Department of
Natural Resources (81) completed a stormwater discharge inventory
of the areas adjacent to the St. Clair River. The data within
this inventory consisted only of location and size of discharge
pipes within the St, Clair River study area. No data relative to
flows, water quality, contaminant concentration, annual dis-
charge, or loading values were provided.
The inventory reports that, on the Michigan shoreline, three
urban areas have storm sewers which drain directly or indirectly
into the St. Clair River. These urban areas include: Port Huron,
which identified 10 storm sewers discharging directly into the
St. Clair River, and 14 which discharge into the Black River;
Marine City, which describes three storm sewer outlets discharg-
ing into the Belle River; and Algonac, which reports two storm
sewers discharging directly into the St. Clair River. The cities
of Marysville and St. Clair, Michigan, have no stormwater dis-
charges .
Ontario
No data were available for contaminants in U.S. sources of urban
stormwater and combined sewer overflow. But a comparison of
Canadian discharges due to urban nonpoint sources, with indus-
trial/municipal point sources is shown in Table VII-11. In most
cases, the point source to nonpoint source ratio is much greater
than one, suggesting that most materials are derived from in-
dustrial and municipal point sources.
While the total number of stormwater discharges on the Ontario
side of the St. Clair River were not identified, considerably
more information is available from the study of Marsalek and Ng
(82) for the urban runoff for the city of Sarnia. The 50,200
residents of the City of Sarnia are served by combined and separ-
ate sewers, and in some of the less developed areas, by open
channels. Combined sewers serve the older areas of the city (540
ha) and discharge into an interceptor which runs along the St,
Clair River. The interceptor has four overflow structures which
allow direct dumping of untreated combined sewage into the St.
Clair River when interceptor capacities are exceeded. In nonover-
flow periods, the sewage is conducted to the sewage treatment
plant.
Available resources prevented Marsalek and Ng (82) from directly
measuring combined sewer flow rates. Instead, they used the U.S.
Army Corps of Engineers STORM model (83) to estimate urban runoff
-------
263
TABLE VII-11
Comparison of induatrial/munic ipai point source discharges with
urban stormwater and combined sewer overflow8a (kg/yr, Canadian
sources only).
PARAMETER
Ammoni a-Nitrogen
Phosphorus
Chloride
Cadmium
Cobalt
Copper
I ron
Lead
Mercury
Nickel
Zinc
Oil and Grease
Total Phenols
Cyanide
HCB
DCS
Total PCBs
1 7 PAHs
POINT
505,000
27,000"
131,000,000
50.4
0.84
3,930
189,000
10,500
15,6
1 ,420
15,000
907,000
4,200
311"
8.9
1 .7
1.2
120
ST. CLAIR RIVE
URBAN NON-
POINT SARNIA
7,300
18,600
2,200
5, 100
1 ,180,000
2,360,000
8.6
4B.2
150
460
43,100
48,800
2,030
0,8
1.5
149
242
2,430 •
47,200
73,400
121
136
23
0.8
0.015
1.4
1 .5
52
74
R
FS/NPS RATIO
69
37
12
5,3
111
56
5.9
1 .05
0.0054
11
4.4
3.9
5,2
19
10
9.5
5.9
6.2
19
12
35
31
13
11
113
0.86
0.80
2,3
1.6
Based on Canadian Industrial/Municipal Point Source Survey Data idaily
average multiplied by 365), and results reported by Harsalek and Nf
(82). Some urban runoff values have upper/lower estimates.
Industrial point sources only.
-------
264
and combined sewer overflow. Using this model, they calculate
annual surface runoff in Sarnia to be 6.7 x 10" m-Vyr, snd a
combined sewer overflow value of 1.0 x 10 6 m.3/yr, for a total
annual average of 7,7 x 10^ m
Contaminant concentrations in Sarnia stormwater and combined
sewer overflows were measured in samples collected during storm
events . Mean values for these parameters are presented in Table
VII-12. For parameters with a significant percentage of data
below detection limits, a low estimate where undetected values
are considered zero, and a high estimate, where they are set
equal to the detection limit, are reported.
The concentrations for the various contaminant parameters meas-
ured in field studies were multiplied by annual flow volumes to
yield annual contaminant loading estimates. The results of these
calculations are presented in Table VII-13. Where applicable,
both low and high loading estimates are given.
When loadings derived from stormwater and' sewer overflows are
compared, overflow incidents are a major source of ammonia and
phosphorus. Both sources are apparently equal in their contribu-
tions of loadings of oil and grease, zinc, and mercury; but for
all remaining parameters, stormwater is the dominant source.
Marsalek and Ng (82) estimate that stormwater contributes ap-
proximately 80 percent of total loadings of industrial chemicals
derived from urban runoff.
3. Agricultural Nonpoint Source
The watershed of the St. Clair River region includes a geographic
area of approximately 340,000 ha, of which approximately 6 per-
cent, 20,976 ha, are located within Lambton County, Ontario.
Within this drainage area, major tributary watersheds include
Talfourd Creek in Canada, and the Belle, Pine, and Black Rivers
in Michigan (84).
A total of nearly 70 percent of the St. Clair River geographic
area is agricultural land. More than 60 percent of the total
cropland in both Canada and the U.S. is under intensive cultiva-
tion. The chief cash crops grown are corn and soybeans. Live-
stock operations are dominated by beef and dairy farming, fol-
lowed by swine and poultry husbandry.
Nonpoint sources of aquatic pollution associated with agricult-
ural operations have traditionally included the additions of
nutrient compounds, increases in particulate burdens from land
erosion, and the inputs of fugitive pesticides and herbicides
(84) .
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265
TABLE VII-1 2
Mean concentrations observed in stormwater and combined sewer overflows
in Sarnia ( 82) ,
Parameter
Unit
Stormwater
Residential Commercial Industrial
Combined
Sewer
Overflows
Ammoni a ( N )
Phosphorus
( total )
Chloride
Cadmium
Cobalt
Copper
T ron
Lead
Mercury
Nickel
Zinc
Oil 4 Grease
Phenols
Cyanide
HCB
DCS
PCBs 1 total 1
17 PAHs
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
ng/L
ng/L
ng/L
ng/L
0.4
0,37
--
--
0,00
0.006
0.00
0,02
0,009
3. 1
—
0,066
0.00006
0,000063
0.018
0.026
0.18
—
2.1
--
0.0170
—
0 . 0035
1,55
--
—
75
8 , 500
12,000
0,27
0.16
172"
343*
0,0023
0.008
0.00
0.02
0,051
5.0
—
0.28
0.00004
--
0.005
0.025
0.33
—
4.1
—
0.0107
--
0.0017
4,4
—
2
146
2,800
3,300
0.70
0.22
—
—
0.0007
0.009
0.00
0.02
0.087
9,4
—
0.45
0.00018
--
0.030
0.039
0,48
--
10,3
—
0.0188
—
0.0030
257
--
—
324
6,700
7,000
3.9
15.7"
0.4
3.4
32.9
65.3
0.005
0.008
0,00
0.02
0.14
2.5
8.4
0.29
0,00005
0.00075
0.005
0.023
0.24
1 .64
7.5
34.8
0.0099
0.0255
0.0030
12
43
2
ISO
5,000
15,400
* For parameters with a significant percentage of data below detection
limits, a low estimate where non-detected values are considered zero,
and a high estimate, where they are set equal to the detection limit,
are reported.
* Equivalent mean concentration.
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266
VII-13
Summary of annual loadings in urban runoff from the Sarnia area
fkg/yr*) (82).
Parameter
Storiwater
Overflows
Total
Ammonia (Nl
Phosphorus
Chloride
Csdmiuit
Cobalt
Copper
Iron
Lead
Mercury
Nickel
Zinc
Oil ft Grease
Phenols
< total I
Cyanide
HCB
OCS
PCBs ( total 1
I? PAHs
3,600
—
1 ,800
—
1,190,000
2,300,000
3.8
40.2*
0
131(23)*
326
40, 700
--
1 ,750
0.7
0.8
144
220
2,200
40,000
111
—
20
0.8
0.013
1 .3
—
47
59
3,700
15,000*
400
3,300
31 ,600
62,700
4.8
8.0*
0
19(3)*
134
2,400
8, 100
280
0.1
0.7
5
22
230
7 , 200
33 ,400
9
24
3
0.0
0.002
0.1
0.2
5
15
7
18
2
5
1 , 180
2,363
43
48
2
2
47
73
0
,300
,600
,200
, 100
,000
,000
8,6
48.2*
0
150i 26 i*
460
,100
,800
,030
0.8
1 . 5
149
242
,430
,200
,400
121
136
23
0.8
.015
1 .4
1 .5
52
74
* Where applicable, both low and high loading estimates are given.
* Loadings calculated from data above the detection limit.
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267
Nutrient Additions
The use of commercial fertilizers and livestock manure as soil
builders potentially contributes to the pollution of adjacent
aquatic resources by adding excessive burdens of bacteria, nitro-
gen, and phosphorus. On the U.S. side of the St. Clair River,
commercial fertilizers are applied to approximately 78 percent of
tillable land, while livestock wastes are added to 8 percent.
The total quantity of phosphorus generated from manure has been
estimated at 3,800 tonnes/yr (85). In Canada, croplands receive
an estimated 3,800 tonnes of commercial fertilizer per year.
This value translates to 376 kg/ha. Analysis of soil fertility
and crop requirements indicate that as much as two times more
phosphorus fertilizer is being used than is required in both the
U.S. and Canada. Livestock operations on the Canadian side of
the river generate a further 6.3 tonnes/yr of phosphorus, ul-
timately disposed of on farm land.
Studies of the Black River (84,85), a U.S. tributary to the St.
Clair River, noted that phosphorus concentrations ranged from
0.03 to 0.73 rag/L, and averaged 0.14 mg/L. The PWQO for phos-
phorus in rivers is 0.03 mg/L. In Ontario, several creeks were
monitored with similar results. Phosphorus concentrations ranged
from 0.033 to 0.665 mg/L in Talfourd Creek, Baby Creek, Murphy
Drain and the Cole Drain (68,84,86). All samples from the
Ontario tributaries exceeded provincial water quality standards
for phosphorus.
Pesticide Additions
Agricultural pesticides are used extensively in the St. Clair
River basin for the control of weeds, plant diseases, and in-
sects. Wall et al. (84,85) estimate that some 500,000 kg were
used annually on the U.S. side. The majority (75 percent) of the
compounds used were herbicides, with atrazine, alachlor (now
banned in Canada), cyanazine, and inetolachlor being the most
frequently used. Additionally, nearly 9,000 kg of restricted-use
pesticides were sold in four counties of the St. Clair River area
(84). In this category, parathion and other organophosphorus
insecticides were highest in sales. In Canada, approximately
30,000 kg of pesticides were applied annually (2,3 kg/ha). At
the time of the study, the most common herbicides used were iden-
tical to those used on the U.S. side.
The Belle and Black rivers on the U.S. side were monitored for
pesticides between April and August of 1985 (84) . The loads to
the Black River for atraziae, alachlor, cyanazine, and metola-
chlor were reported as 0.3, 0.22, 0.99, and 0.07 g/ha» respec-
tively. Loadings for the same compounds to the Belle River were
reported as 0.12, O.Q3r 0.03, and 0.07 g/ha, respectively.
-------
268
Analysis of sedimentary materials from the St. Clair River tribu-
taries yielded the observation that restricted-use pesticides
were present in 70 percent of the samples. Chlordane and meta-
bolites of DDT were most frequently observed.
Ontario tributaries were monitored for pesticides including
organochlorine, organophosphorus and carbamate insecticides as
well as phenoxy acid and triazine herbicides.
Atrazine was detected in 47% of all water samples from Ontario
tributaries of the St. Clair River at concentrations up to
8,450 ug/L. Additional pesticides which were detected less fre-
quently, included gamma-BHC, pp-DDE and endrin. Alpha-BHC was
detected in 62% of water samples but typically at levels below 5
ng/L.
The frequency of sampling was insufficient to estimate annual
loadings; however, mean instantaneous loadings for atrazine indi-
cate that Talfourd Creek is discharging approximately 0.5 mg/sec
to the St. Clair River.
Industrial organic compounds were detected primarily on suspended
solids and were consequently observed in bottom sediments at the
tributary mouths. Concentrations of HCB, OCS and PCBs were ob-
served in whole water, suspended solids and bottom sediments from
Ontario. Several elevated levels were measured on suspended
solids at the Cole Drain (HCB - 5,800 ng/g; OCS - 5,400 ng/g) and
at Talfourd Creek (PCBs - 77,840 ng/g)(68,84,85). The signifi-
cance of these intermittent peaks cannot be determined based on
the limited data available.
4. Atmospheric Deposition
Direct atmospheric deposition of contaminants to the St, Clair
River is likely to be negligible because of the relatively small
surface area of the river. However, atmospheric deposition may
be defined as the sum of the contaminants deposited from the
atmosphere on a stream or lake surface (direct input), plus that
material which has fallen on upstream areas and is transported
through the connecting channels to downstream bodies of water.
This phenomenon is likely the mechanism responsible for the regu-
lar observation of common pesticides observed in the St. Clair
River (87). Such compounds as the metabolites of DDT, alpha- and
gamma-benzene hexachloride, and dieldrin are routinely reported
in water samples from the St. Clair River, but the concentration
of these contaminants does not change significantly over the
length of the connecting channel. This fact suggests that there
are no active sources along the St. Clair River (37,79).
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269
5. Groundwater Contamination/Waste Sites
Three different groundwater flow systems contribute to the over-
all groundwater discharge, or flux, including discharge from
surficial aquifers, from intermediate flow systems and from deep
bedrock systems. Groundwater in the unconsolidated surficial
deposits generally flows to the St. Clair River. Locally, how-
ever, the direction of groundwater flow is influenced by surface
water drainage and glacial landforms. Groundwater flow direc-
tions in the deeper units are as yet not well defined.
Total groundwater seepage directly to the St. Clair River was
estimated by three independent teams of investigators to range
between 645 L/s and 741 L/s and to average about 700 L/s. The
U.S. Geological Survey estimated total groundwater discharge to
the river from groundwater discharge areas, based upon tributary
baseflow information. The University of Wisconsin - Milwaukee
used a combined geophysical and hydrological method to compile
continuous measurements of groundwater flow passing through the
St. Clair River bed. The University of Windsor Great Lakes
Institute deployed seepage meters and mini-piezometers to measure
seepage in the sarnia area (88).
Shallow groundwater in the study area, which does not discharge
directly to the St. Clair River, contributes about 10% of stream
flow to the tributaries of the St. Clair River. Rates of ground-
water seepage to the St. Clair River generally decreased down-
stream, with higher fluxes noted in the Sarnia and Port Huron
area, and between stag island and Courtright coinciding with
areas having the largest number of sources of groundwater con-
tamination.
Although the total amount of discharge to the St. Clair River is
small relative to the St. Clair River's water budget, the hetero-
geneities that are apparent in the nature and the distribution of
groundwater flux suggest that inputs of contaminated groundwater
may be locally significant.
Surface Runoff from Landfills,
Groundwater is not a principal route of contaminant transport
from many waste sites in the St. Clair study area. Low hydraulic
conductivities of surficial materials here restrict infiltration
and groundwater movement. Surface runoff from waste sites to
storm drains, and small tributaries which flow to major surface
water bodies appears to be of greater importance as a contaminant
transport pathway.
-------
270
Michigan's Potential Groundwater Contamination Sources
Groundwater movement was investigated in an area extending 19 km
inland along the St. Clair River. An inventory of active and
inactive waste sites within this area was conducted as part of
this investigation. Twenty-six sites of known, or potential
groundwater contamination were identified and ranked. The major-
ity of sites are solid waste landfills, regulated and unregulated
hazardous waste disposal sites, storage sites and spills. Other
potential sources that were reviewed included leaking underground
storage tanks, contaminated well water, and underground injection
wells. Underground injection wells were not ranked for potential
contributions to contaminant burdens and are treated separately
below.
Those sites in areas which discharge directly to the river were
ranked and assigned priorities for potential impacts upon the St.
Clair River. Ranking of sites, using a modification of U.S.EPA's
DRASTIC ranking system, was based on their potential for con-
tributing contaminants directly to the St. Clair River via
groundwater by evaluating the hydrogeolog-y, the nature of waste
material as described in state and federal files, and the dis-
tance to the river (89). The 7 highest ranked sites had the
greatest potential for impact upon the St. Clair River (Table
VII-14). The water table in this region was generally less than
4.6m below the land surface and the individual sites had prior-
ity pollutants and/or inorganic contaminants.
Evaluation of Potential_Impacts
One round of samples were collected from 8 observation wells that
were installed by the U.S. Geological Survey (USGS3 in each
groundwater discharge area. Actual locations of wells depended
upon the number of up gradient waste sites, the size of the
groundwater discharge area, and on permission for drilling from
landowners. It was possible to locate two wells near waste
sites, including a well installed down gradient of both A and B
Waste Disposal and the Hoover Chemical Reeves Company, and a well
installed down gradient from the Wills Street Dump Site. Other
locations were chosen to provide background information.
Analyses were made for 72 volatile, base neutral, acid extract-
able, and chlorinated extractable hydrocarbons, and 24 trace
metals and other chemical parameters. These analyses were com-
pared to both surface water quality criteria and objectives, and
drinking water standards,
i) Organic
The pesticide endosulfan was detected in one sample. Phthalate
esters were found in four of eight samples. N-nitrosodiphenyl-
ainine, was detected in a well at a level in excess of U.S.EPA
-------
271
TABLE VTT-14
Confirnnd or possible Michigan contamination sites within the
St. dair River groundwater discharge areas* ,
1. Grand Trunk Ba,iJlrqpd ! CE8CLIS /RCftA/Act 307)
The Grand Trunk Railroad site is an oil pipeline leak. There is a perched water table about 2 feet
below the surface that is underlain by about 100 feet of lake clays and a gravel aquifer. Oil may have
discharged to a sever and ditch ( MDNR > . Groundwater contamination is not indicated in the Act 307
listing. There are no monitoring wells. The upper, perched aquifer is contaminated with diesel fuel.
Sandy soils on site are saturated with oil and may contribute oils to the shallow aquifer (observed,
1979, from PA I . Oils and *2 diesal fuel flowed to WTP via storm drain on aite (observed 19"8 - 1$79,
from PA I . Note: CERCLA authorities were not applied because the observed release was limited to
petroleum products which are covered under the Clean Water Act.
2. A and B Waste Disposal ( CERCLIS/ftCRA/Aet 307)
The A and B waste Disposal site is a transfer facility where wastes are sorted for resale/cycling and
disposal. Soil and groundwater staples contain toluene, xylene, trichioroet hylene and
tet rachloroe t by 1 ene . There are alleged incidents of dumping paint thinner on the ground, Ground-
water contamination is not indicated in the Act 301 listing. There are no monitoring wells,
3. Hoover Chemical Reeves Coaoany ( CERCLIS/RCRA/Act 307)
The Reeves Company buys and distributes paint products locally. In the past , th* facility byilt
fiberglass buildings for Port-a-john. Hoover Chemical manufactures adhesives. Drums containing paint
and adhesive wastes are stained on site. Groundwater contacination is not indicated in the Act 30?
listing. There are 5 monitoring wells.
4. Eltra Corp. Prestolite Wiring ICERCLIS/RCRA/Aet 307)
This company is a RCRA generator and treatnent/storage/disposal facility. Various h«io?enated and non-
halogenated solvents, electroplating wastes, lead and ketones are stored in containers on site. There
are no moni to ring wel Is,
Hills Street Dump Site < CESCLIS/Act 307
The site was not submitted to MPL for the following reasons: Marvsviiie's drinking water surface, water
intake is iocated I 4 5 mi . upstream of the Wills St. Dump and 90 s of clay overlies the aquj ter used for
drinking water. None thelefts, the site is near a wetland* On-ai te soil samples contained low levels of
1 , J-dichloroethane, I , I f i-trichloro*thane and tol ue/ne , Also found were el evated levels ot phenol and
Arochlor - 1^60.
6. General Technical Costings (Act 307}
Paint and solvents are stored in barrels at the General Technical Coatinfs site, The site is within
one-quarter mile of the S t • Clair River. Ground-««te r cent aminati on is not indicated in the Act 30"
iistinCr The site vas removed from the Act 3O7 list after cleanup*
7, Winchester Disposal Area £C£RCLl5/Acl 307}
The "inchester Di sposal Area site is an unlicensed refuse dump, It is located in a 4ow marshy area
near Port Huron, The site is unfenced and con t i nued dy taping i s possible • So records ot" the types or
amounts of vastea present exist. Drums have been seen on the site and acre may be buned (NDNR1,
Ground-water contamination is not indicated in the Act 30? listing* There are no mom tori ng wells *
The fill on-mite im at least ten feet thicJe in »ome areas, No csvsr was *%'er applied^ Bruias, eoncret*
and househe id appllances are exposed. Tens of thousands of tir*s are staffed on site up to ten fe*t
hjrh in areas . In I9rfl three mon i tor i us wel is in this »rea were sampled - Dovij-f r ad lent wel 1 s in the
vicinity of Winchester Disposal Ares, showed hi gher concentrations of phenolics, cadmium, copper, lead,
2 i n.c and iron than were found in an up tf radi ent well in the vicinity of the Wi nchester Di aposal Area.
CERCLIS: Site is listed within the info rmat ion system for Superfund and i a considered for clean-up
under the Compren*n3ive Envi ronmental Compensation and Recovery Act of 1980 *
RCRA: Facility has a Resource Conservation and Recovery Act identification number*
Act 307: Site 13 ii sted on Michigan's compi. i at ion of sitc^ of known and possible environmental
degradat i on,
• In format ion front f 8$ 1 -
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272
Human Health Criteria for carcinogens at a 10-^ risk level. It
is possible that phthalate esters were introduced during sampling
or shipment,
ii) Inorganic
U.S.EPA Drinking Water Primary Maximum Contaminant Levels (MCL)
were exceeded for chromium at one well, for lead at six of eight
wells and for barium at two wells„
Table VII-15 contains a summary of groundwater quality in these
wells based on unfiltered samples (88). The metals are generally
associated with finely-divided particulates, Groundwater that
discharges to the St. Glair River is thought to be free of fine
particulates, and thus of lower trace metals concentration than
determined for these samples. Thus, a computation of the loading
of the St. clair River by chemical substances transported by
groundwater does not feasible at the current time.
Several sites that were selected as priorities for investigation
by the USGS may have potential for local impacts upon the St.
Clair River.
Elevated levels of barium, cobalt, copper, lead, sine, and nickel
contamination, as well as the n-Nitrosodiphenylamine contamina-
tion in"well G3 appear to be related to discharges from A and B
Waste disposal, or Hoover Chemical Reeves Company, or a combina-
tion of the two. The proximity of well G3 and of the two sites
to the St. Clair River suggests that seepage of contaminated
groundwater originating from the sites may result in local im-
pacts upon St. Clair River biota or water quality.
Elevated lead, mercury, and zinc in well G4 might be attributable
to the Wills Street Dump Site.
Elevated chromium, lead, iron, zinc and phosphorus concentrations
in well Gl, and elevated, barium, copper, "iron, lead, nickel,
total organic carbon, and oil and grease concentrations in well
G8 had no identifiable source.
Generally, it that environmental problems of waste, stor-
age, treatment and disposal facilities are associated with over-
land flow or runoff, rather than through groundwater discharge.
Low hydraulic conductivities, and hydraulic gradients suggest
that groundwater is not a major route of contaminant transport to
the St. Clair River from these sites. Nonetheless, the possible
presence of unidentified discontinuous stringers of sand and
gravel may aerve to enhance contaminant transport locally.
-------
TABLE VlI-15
y of St. Clair River- area groiindwat.er quality1 in Michigan U.S.GS wells*.
NUMBER MAXIMUM
OF ANALYTICAL
DETECTIONS
Antimony, t.otai ( u g / L )
Arsenic, total (ug/LI
Barium, dissolved tug/1,)
Beryllium, dissolved lug/LJ
Cadmium, total (ug/LJ
Chromium, total lug/LI
Cobalt, total lug/LJ
Copper, total (uij/Ll
Iron, total Img/LJ
Lead, total (ug/L. 1
Mercury, total lug/1,)
Niokel , total ( ug/L J
Selenium, total (ug/L)
Zinc, total Img/LI
Carbon, total organic (mg/LJ
Chloride (mg/I. k
Cyanide, totat ( mg/I, )
Dissolved solids (mg/Lk
Oil-grease, t.otai (mg/L)
Nitrogen, total ling/1,)
pH { nn its)
Phenols, total lug/ 1.)
Phosphorus, total Img/L)
Specific conductance (us/cm)
ECndosu 1 f an tug/1,)
Bis ( 2-ethyl hp\y) Iphthal ate {ug/L!
Butyl henzy! pht.hnlnte Itig/L)
ri — N i t r osod iphenylamine ( ug /[. )
8
8
«
H
a
8
8
8
8
8
8
8
8
H
£
8
8
8
B
7
8
H
8
8
]
a
2
1
13
IS
2100
21
<1
S9
200
730
500
tiiiOO
0,5
1300
<1
390
1 90
250
<0.01
1560
18
2.5
11,2
6
0.5?
2380
0.08
1500
e
10
MINIMUM
<1
<1
51
<1
<1
-------
274
Ontario's Potential Groundwater Contamination Sources
On the Ontario side of the -St. Clair River, a total of 16 design-
ated waste disposal sites were identified in Lambton County, The
Ontario sites were prioritized to determine those sites that
require monitoring or remedial investigations. In designing
criteria for this evaluation, emphasis was placed on identifying
sites which lack specific information that, is important in
assessing environmental impacts. Thus, sites lacking particular
information could rank higher than sites having evidence of im-
pact. Seven main groups of criteria were selected:
1. Geologic Information
1, Hydrologic Information
3. Hydrogeologic Information
4. Geochemical Information
5. On Site Monitoring
6. Waste Characterization and Containment
7. Health and Safety
Specific questions within these groups, that are significant in
assessing the site environmental impact were used to derive a
quantitative score. Three categories of priorities were develop-
ed, including;
Priority 1 Sites; those sites with a definite potential for im-
pact on human health and safety,*
Priority 2 Sites: those sites which require immediate investiga-
tion in order to determine the potential for impact either on the
environment or human health and safety," and
Priority 3 Sites: those sites requiring additional monitoring,
but with lesser potential to impact their surrounding environ-
ment ,
The Nonpoint Source Workgroup (88) reported that three sites in
Lambton County were categorized as Priority 1 Sites. Included in
this category were;
1) Dow Chemical, Scott Road
2) Polysar Limited, Scott Road
3} P and E Oil Recyclers, Petrolia.
Ten sites in Lambton County were identified as Priority 2 Sites,
These locations included;
1) K and E Solid Waste, Sarnia Township
2) Unitec, Inc., Moore Township
3) C.I.L., Inc., Lambton Works, Sombra Township
4) City of Sarnia Landfill, Sarnia Township
5) canflow Services, Petrolia
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275
6} Dow Chemical, La Salle Road, Moore Township
7) Ladney, Moore Township
8} Sun Oil Company, City of Sarnia
9} Fiberglass Canada, Ltd., City of Sarnia
10) DuPont of Canada, Ltd., Moore Township.
Priority 3 sites in Lambton County included three listings.
These were;
1) Walpole Island, Walpole Island Indian Reserve
2) Esso Petroleum, Scott Road, City of Sarnia
3} Johnson Construction, Sarnia Township.
It is important to note that the ranking schemes for U.S. and
Canadian sites are not strictly comparable. Site characteristics
of the four highest priority sites are provided in Table VII-16.
Most contamination problems associated with waste sites are cen-
tered in the Scott Road area of Sarnia. Shallow groundwater and
surface water drainage here is to the Cole Drain, In addition to
Dow and Polysar landfills, other waste disposal sites may be
contributing contaminants to the Cole Drain and are situated
adjacent to the Dow and Polysar landfills. These include the
City of Sarnia sludge lagoons, Fibreglas Canada's landfill site,
and further south the Esso Petroleum Landfill site. Due to the
uncertainty of the origin of contaminants in the Cole Drain, the
Ontario Ministry of the Environment has undertaken a study of
surface runoff within the Scott Road watershed. Preliminary
findings to date indicated the presence of slightly elevated
levels of hexachlorobenzene and octachlorostyrene in surface
water draining from the landfill area.
Underground Injection Wells
i) Michigan
In the United States, the U.S.EPA has the primary responsibility
to establish and enforce protection of underground sources of
drinking waters through its Underground Injection Control (UIC)
program. This program regulates five classes of injection wells:
Class 1: Industrial and municipal disposal wells which inject
below the lower most formation containing underground
sources of drinking water.
Class 2: Injection wells associated with oil and gas production
and liquid hydrocarbon storage.
Class 3: Special process wells used in conjunction with solution
mining of materials.
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TABLE VII-IK
Site characteristics of Ontario high priority waste sites in the St. Clair River area*.
I, Pew. Chemical, Scprt.Hpfld - The site has he-en in operation since liHH. Disposal operations
consisted of controlled land ' flTling and clav capping haa«rdoua and nan~hafcardous solid and liquid
waste that, originated from the production of vinyl chloride. Included were varioiia oily sludges and
solvents containing chlorinated hydrocarbons, spec i f i ca L t y hexachlorobutadiene. Also, contaminated
aoila ami equipment from around the production facilities have been transported to the waste disposal
site. Approximately 1000 tonnes of waste (i!HX non-hazardous, £t>X liquid and 4ti% hazardous waste, HOE
19H4 } were disposed annually. Surface and groundwater moni toring systems have been in place since
I9KO, as wo i i as a leachate control and treatment, system. The Jeacnate control system consists of" a
col lecrt ing/)><'> I rii ng ditch along the north boundary of the site. The contents of the ditch are treated
with activated carbon beds and released to the Scott Komi ditch, which drains to the Cole Drain, The
pffeetiveness of a steel aheet pile wall to contain off site arountiwater flow has not been
d^ffioftst. rat ed , Surface runol'f is the most likely pathway tor movement off site. Surface runoff is not
properly contained and mav be migrating towards the adjacent Fibreglas Canada site. Ground water
pounding within the landfill is likely to create a large hydraulic gradient across the sheet pile wall
resulting in short circuiting of the wall, and increased off site ground water flow. The present
monitoring program ia inadequate and needs to be improved. Pow haa also found and removed contaminants
from the Cole Drain.
2. f'ojygar Limited J.Scot.t Road I - The Polyaar Limited disposal site off Scott Road in Sarnia
serves tfie nearby PoTvsar manufacturing facilities. The site has been in operation since 1942 and
consists of industrial wastes and fly ash areas. Disposal operations consist of controlled land
filling of various inert sludges, plastic resins and alkali, inorganic and rut»toer-&ccoffij>anied waste
over an area of approximat.e1y ll hectares. At present* approximately 25,000 m^ of liquid wastes are
received per year. Land filling is waste with fly ash or imported clay and silted clay material,
Surface runoff and wasste leachate are directed into surface Storage lagoons where monitoring and
treatment is required. Monitored parameters include pH, total organic carbon, phenctiE, copper and
ammonia. Off site releases of surface waters has ceased, and all surface waters are now treat*3 at the
company's biological oxidation treatment plant. In general, groundwater monitoring in thi« site ia
inadequate to aetermine whether or not contamination is leaving the site. The company is* in the
process of retaining a consultant who_ will be charged with the tank ^ot initiating a_nore detailed
hydrofeologicai investigation of the site, including mor.e frequent sampling of existing piezometers.
3. £ S> E O i 1_. Re c_v_c I e r s - The P * E Oi I Recyciera site stores used oil in underground tanks and
disposes of oTlTTeTa Bnnes in two deep disposal wells. In laBZ, 51) nj < 10,GOO 8*13 ot waste were
accepted at the site. The major industries served are: Dome Petroleum, Imperial Oil| Polyaar Liiaitedj
and uniroyal. No surface water of groundwater monitoring programs are in effect. The site was
developed in the latter part of the 19th centxiry by the Canaaian Oil Company for the subaurf&e^ storage
of crude oil in underground cedar-lined tanks. The tanks were excavated in heavy clay soil to depth*
ranging from 4m (13 ft) to 18 m (60 ft I below grade. In 1S)B5 and 19K9 two deep disposal wells were
drilled into the Detroit River Group arid were used for the disposal of liquid industrial wastes until
1974, when the Ontario Ministry of the Environment regulated against the disposal of industrial
wastes, except for oil field brine, in this fashion. This regulation led to the storage of indtistrial
waste in the subsurface st.orarte tanks. The underground storage tanks have capacity to hold over 13,650
a3 (3.000.000 gall, and the last documented reports indicate that all tanks are full. The liquid
contents of the tanks were determined to contain oil, brine, water, caustic and/or acidic compounds,
phenolic compounds, nineral salts and heavy metals, including lead and chromium. The potential for
off-site migration exists and has been documented. At present, there is virtually no on-site
containment for the off-site migration. In addition, many of the tanks are uncovered, or those that
are covered have weakened, rotting wooden roofa. therefore allowing infiltration of precipitation
which will cause overflows of the contents. A Control Order has been proposed by the Ministry of the
Env i rorsraent
4. GlLt Lftglhbon Works - The Canadian Industries Limited Piant near Courtright, produces chemical
fertilizers. There is iiFEie topographic relief, but surface drainage is either directed to the St.
ftlair River, or eastward to Clav Creek. Prior to the decommiasloriina of the phosphate plant, the
facility used phosphate rock which naturally contains minor amounts of radioactive radium and uranium.
These eleaieiits appear in waste gypsum slurry which was dischurged into two SO hectare holding ponda.
The ponds also contain phosphate, ammonia, and fluoride, with a water pH of 1.0. Due to the use of
sulphuric acid originating from one of the company's other facilities in Quebec, the pond waters have
become contaminated with dinitrotoiuene (DNT | . From I'JTS to tHBl, separation filters containing radium
concentrations as high as 12,000 pCi/t; from the CIL murvut'acturing process were disposed at the Sombra
Township (Wilhesport Landfill Site). This disposal resulted in areas of elevated radiation exposure
rate and localiecd hot spots. Under tho direction of the Ontario Ministry of the Environment and the
Ministry of Labour, CI1. removed several truck loads of contain!noted soil from the landfill for storage
in the berm of one of CH.'s gypsum ponds, The waste soil and debris are presently contained inside the
walls of the gypsum pond, all radioactive materials are now stored in a concrete: bunker on site,
* Information from IBHI.
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277
Class 4: Hazardous waste wells which inject into or above under-
ground sources of drinking water (wells in this categ-
ory were banned in 1985).
Class 5: Wells not falling into one or more of the above cate-
gories; including heat exchange wells, domestic waste
wells, and cesspools.
A total of 72 injection wells are presently rule authorized or
permitted on the U.S. side of the St. Clair River. Of this
total, 63 are in current operation, two are temporarily aban-
doned, and seven are permanently plugged and abandoned.
Class 1 Wells:
Consumers Power Company Facility in Marysville, Michigan current-
ly has two temporarily abandoned Class I Non-Hazardous Industrial
Waste wells. These wells will be reclassified as salt water
disposal wells (2D) per clarification of 1986 Safe Drinking Water
Act Amendments. The wells are designed to inject brine associat-
ed with the hydrocarbon storage operations at their facility.
The injection zone for these fluids are the Eau Claire and Mt.
Simon Formations at a depth greater than 1,380 m at a pressure of
12,757 kPa (1,850 psi).
Class 2-D Salt Water Disposal Wells:
Eleven Class 2-D salt water disposal wells are currently operat-
ing in the St. Clair area. One additional salt water disposal
well is temporarily abandoned, and two others have been permanen-
tly plugged and abandoned. Disposal intervals for Class 2-D
wells in this area range from the Detroit River Group of forma-
tions at a depth of 267 m to the Eau Claire Formation at a depth
of 1,350 m. Permitted injection pressures range up to 8,960 kPa
(1,300 psi). All Class 2-D wells in the area with one exception
have passed mechanical integrity tests: one of the ANR Pipeline
Co. wells had failed its mechanical integrity test on April 9,
1986 and was shut down, but has since been reworked and retested
for mechanical integrity, and is functioning properly as of June
6, 1986.
Class 2-H Hydrocarbon Storage Wells:
Class 2-H, Hydrocarbon storage Wells service natural gas storage
reservoirs, or are used for storage of refined petroleum prod-
ucts, or liquified petroleum gas (LPG). Gas storage reservoirs
for natural gas are depleted gas fields into which gas produced
in other areas is stored for future marketing. Injection and
withdrawal of gas is typically through former gas production
wells which have been converted to storage. Injection and with-
drawal may be through the same well, or through separate wells.
Observation wells are used to monitor reservoir pressures, reser-
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278
voir capacity and other parameters.
Currently there are 11 hydrocarbon storage fields-or facilities
located in the St. Glair River area with an average surface area
of 406 acres. These fields have all been converted to hydrocar-
bon storage since 1970. Most gas storage reservoirs in St. Clair
County are in the Middle Silurian Niagaran Reefs, and salina
Carbonates and Evaporites. Depths to the gas storage reservoirs
range from 659 to 884 m and the thickness of the reservoirs
ranges from I to 92 m. The Middle Silurian Reefs are used prin-
cipally for the storage of natural gas that is produced elsewhere
and stored for future marketing. This activity is carried out
principally by the Consumers Gas Company, The Salina Evaporites
are primarily used for the storage of LPG and other refined
petroleum products,
Amoco Productions company operates a LPG storage facility having
seven wells in the Salina-A Evaporite. The depth to these
caverns ranges from 690 to 750 m and the estimated capacity of
all the caverns is 2,265,000 L. Consumers Power Company operates
9 wells completed in the Salina-B Salt for the storage of refined
petroleum, products.
Class 2-R Enhanced Oil Recovery Well;
Five Class 2-R, enchanced oil recovery wells, operate in the St.
Clair River area in the Detroit River Group of Formations and the
Niagaran Dolomite. One well, formerly operated by Vans Tank
Truck Service, failed its mechanical integrity test in April of
1986 and is no longer in operation.
Class 3-G Solution Mining Wells:
Solution mining wells operate through production of artificial
brines by wells completed a hundred m or more apart in the
salt bed. Salt is dissolved by pumping water through well
into the bedded salt, and out through the second well. The brine
that is produced is processed to recover bromine, iodine, and
sodium, calcium and magnesium chlorides. " The Salina Group
evaporltes presently produce brines, but the Devonian Detroit
River Group has also been used in the past for production.
Eight Class 3-G solution mining wells are operated by Diamond
Cryital Salt Co. Four additional solution mining wells have been
operated in the past by Morton Salt Co. but have since been
plugged and abandoned.
Other Wells;
No Class 4 wells operate in the St. Clair River area. Seventeen
Class 5 wells operate in the St. Clair River area.
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279
The impacts of Michigan Underground Injection wells in the area
upon the St. Clair River are uncertain. However, it appears
that, with the exception of short-term mechanical integrity prob-
lems for a salt water disposal well and an enhanced oil recovery
well, all wells are operating in an environmentally sound manner.
ii) Ontario
In Lambton County, Ontario, deep injection wells were used to
dispose of industrial wastes during the period 1958-1972 and are
still used for the disposal of cavern brines and oil field brines
(88). There are about 35 deep wells in Lambton County {Figure
VII-3), The Lucas formation of the Detroit River Group was heav-
ily utilized prior to 1976 for the injection of industrial waste.
The freshwater aquifer lies above this bedrock, therefore the
potential exists for wastes to flow upwards into the aquifer and
thus migrate to the St. Clair River,
The industrial waste wells were located in three areas. The most
heavily utilized area was the industrialized section south of
Sarnia, adjacent to the St. Clair River. In this location wells
were used by Imperial Oil Ltd. (5 wells), Shell Canada Ltd. {2
wells), Sun Oil Company (1 well), Polymer Corp. (I well), and Dow
Chemical Ltd. (2 wells to the Salina formation) (Figure VII-3).
The second area is located inland from the river and included the
well of Marcus Disposal (1 well), Thompson Wright Co. (2 wells),
and Tricil-Goodfellow (2 wells). A third area is found in Court-
right adjacent .to the St. Clair River, and consists of 2 wells
belonging to Canadian Industries Ltd. (CIL) (Figure VII-3).
The Primary waste types disposed into the wells were spent
caustics, acids, phenols, minor hydrocarbons, and brine. The
volumes of industrial wastes disposed of into the Detroit River
Group total 7,513,722 m3. In the industrial area of Sarnia, it
was usually necessary to inject waste under pressure to achieve
the required injection rate. The wells close to the St. Clair
River often required pressures up to 3,103 kPA {450 psi) at
surface to inject the waste. The average injection pressure was
2,758 kPa (400 psi).
Cambrian Disposal Ltd., owned and operated 7 wells in Lambton
County, for the disposal of cavern-washing brine waters. Between"
1971 and 1985 the total volume of waste injected under gravity
into these wells, was 10,194,889 m^ t All wells used for the
disposal of brine materials have established monitoring well
networks on adjacent properties to determine water quality in the
freshwater aquifer. The company is also required to pay a levy
for each cubic metre of waste injected for the perpetual care of
the well once it is abandoned.
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280
Plympton
J Sarnia
Cavern Washing
Brine Injection
Oil Field Brine
Injection
Enniskillen
MARCUS
Oil Field Brine
- Injection to
Guelph Fm
19 Somore
__
Chatham
FIGURE VII-3. Injection wells.
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281
Of concern to the Ontario Ministry of the Environment and the
Federal Department of the Environment is the past practice of
injection of industrial wastes into the Detroit River geologic
formation, and the potential for contamination of the freshwater
aquifer. Because of high pressures used for injection and the
large volumes of wastes disposed, the potential exists for con-
taminants to migrate from the disposal unit to the freshwater
aquifer and hence, to the St. Clair River. The possible pathways
of migration include the following:
1. Numerous bore holes, many of them abandoned and unplugged,
provide open conduits through the bedrock confining units;
2. Poorly constructed injection wells could allow waste to
migrate along the outside of the casing;
3. Faults, fractures and joints are likely to exist in the
bedrock confining units. It is possible the pressurized
waste could travel great distances via these fractures; and
4. The permeability of the confining shale and limestone units
may be of sufficient magnitude to allow pressurized wastes
to migrate via pore spaces to the shallow aquifer.
In view of the possible migration pathways and the fact that
there were documented cases of upwelling in the Sarnia area,
which occurred between 1966 and 1972, there was the possibility
that the groundwater system had been pressurized above its nat-
ural state. This being the case, it was possible that the dis-
placement of formation fluids, or the upwelling of industrial
wastes, may have contaminated the freshwater aquifer in the St.
Clair River area or have migrated across the St. Clair River to
Michigan.
Detailed studies of the fresh water aquifer and the movement of
injected wastes were undertaken from 1986 to late 1988 by the
federal and provincial governments, and industry. The prelimin-
ary results of these studies were reported by Intera Technologies
Inc. (90). The executive summary of this report is reproduced
below:
"This report .... describes the results of a hydrogeologic
study of the fresh water aquifer and deep geologic forma-
tions in the Sarnia Ontario area. The study was undertaken
to assess the extent to which the St. Clair river and a thin
sand and gravel aquifer (fresh water aquifer) located at the
bedrock surface have been impacted by past practices of
industrial waste disposal to the Detroit River Group of
Formations located at 150 to 200 m below bedrock surface.,..
this study included: drilling, testing and installation of
fifteen groundwater monitoring wells to the fresh water
aquifer; drilling, testing and installation of one 300 m
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282
deep borehole to the disposal formation in the Detroit River
Group of formations; and quarterly groundwater sampling and
hydraulic head monitoring of a 29 point monitoring well
network of the fresh water aquifer and of the deep borehole,
The computer modeling included a numerical simulation of
groundwater flow in the fresh water aquifer and simulation
of waste migration within the disposal zone. The potential
size of contaminant plumes that may result from vertical
migration through an open abandoned borehole between the
disposal zone and the fresh water aquifer was also simulated
using a computer model.
"The results of this study show that the fresh water aquifer
is a thin, discontinuous aquifer located at or near the
bedrock surface with an average hydraulic conductivity of 5
x 10^6 m/s. A buried bedrock valley of depth 60-80 m below
ground surface and 30-40 m below surrounding bedrock is
located about 500-1000 m east of the current channel of the
St. Clair River. The fresh water aquifer has a higher
hydraulic conductivity of about 1 x 10~4 m/s within the
bedrock valley due to the presence of alluvial sands and
silts. The freshwater aquifer is generally overlain by 30-
70 m of low permeability clay till; however, below the St.
Clair River the thickness of confining till in places may be
a thin as 3 m.
"Groundwater flow within the fresh water aquifer toward the
bedrock valley averages 0.57 m^/yr per unit aquifer width.
Within the bedrock valley some flow is directed down to
deeper geologic formations and some of the flow is discharg-
ed to the St. Clair River. No groundwater flows under the
St. Clair River within the fresh water aquifer to the U.S.
"Phenol contamination of the fresh water aquifer by injected
industrial waste is evident on the Esso Petroleum Canada
property near the St. Clair River and below the St. Clair
River in the area of the CN Railway tunnel. Loading to the
St. Clair from this 800 m by 600 m contaminated zone is
calculated at 5.2 g/d which, given the volume of flow in the
St. Clair River, is rapidly reduced to below detection
levels. Chloride contaminant loading to the River from the
same area is calculated at 50 kg/d.
"It is recognized that some undetected contaminant plumes
may exist in the vicinity of disposal wells due to waste
migration up abandoned boreholes. Assuming such plumes did
exist adjacent to the St. Clair the total potential phenol
loading to the River is estimated at 25 g/d. This would
result in an increase in phenol concentration in the River
of 1.9 ng/L which is about 500 times less than the minimum
detection limit of 1 ug/L.
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283
"Industrial Waste characterized by Phenol (30,000 - 40,000
ug/L) volatile organics (e.g., benzene, toluene, etc., 200 -
5,800 ug/L) and naphthalenes (50 ~ 829 ug/L) is restricted
to a narrow 11 m interval between 185.9 and 196.6 m depth in
the upper section of the Lucas dolomite. Vertical migration
of this waste through the pore space of the overlying and
underlying rocks has been negligible and measured hydraulic
heads show fluid flow in the adjacent rocks is now to the
disposal zone. This study suggests that there is a rela-
tively active flow system within the disposal formation
today and that understanding the fate of 8,000,000 m^ of
waste disposed to the Detroit River Group will require
knowledge of the current rates and directions of flow within
the disposal zone.
"The hydraulic head within the disposal zone is now 14 to 15
m below that in the fresh water aquifer and 8 m below the
level of the St. Clair River. Therefore current flow direc-
tions are from the fresh water aquifer and St. Clair River
to the disposal zone.
"A significant finding of this study was the occurrence of
high hydraulic conductivity limestone layers in the Hamilton
Group of formations at 74 and 123 m depth that likely con-
tain industrial waste at phenol concentrations of 6000 -
10,000 ug/L and hydraulic heads above those in the fresh
water aquifer. The 2 in thick limestone layer at 74 m depth
is of particular concern to this study because groundwater
from, this horizon likely discharges to the fresh water
aquifer within the bedrock valley and this horizon flowed
industrial waste in 1967 and 1969 at rates of 10 to 238
L/rain. The extent of contamination in this and the 123 m
depth horizon is not known but is likely significant as the
only two monitoring wells to these horizons (from this and
an earlier study) detected industrial waste. This waste was
likely introduced to these limestone horizons from improper-
ly completed disposal, cavern or abandoned wells,"
6. Spills
A recent, well-publicized spill of perchloroethylene in the
Ontario waters of the St. Clair River underscored the potential
for accidental loss of large quantities of materials in this
river system (36) . This incident prompted a major investigation
on the biological effects of spills and related discharges (91).
The results of the study demonstrated that the waters, sediments,
and biota of the St. Clair River system were adversely affected
by discharges of contaminants to the river, and that the per-
chloroethylene spill aggravated an existing condition.
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284
The perchloroethylene spill was not an Isolated event. Rather,
it was simply another incident in a long history of accidental
spills. The data presented in Table VII-17 indicate that, on the
Canadian side, 11 major oil spills of 10 tons or more (a total of
1,282 tons) and 21 major spills of other hazardous compounds (a
total of 10,390 tons) occurred between 1974 and 1985.
The Michigan shoreline is considerably less industrialized than
the Ontario portion of the river. However, between 1973 and
1979, there were 120 spills of petroleum related compounds from
land based facilities and vessels which released over 18,500 L of
these materials into the St. Glair River. An additional spill
released 208 L of other hazardous substances to the river during
this period.
Tables VII-17a and 18 provide information on spill occurrences
during 1986, In 1986, a total of 48 surface water spills to the
St. Clair River were reported. There were 17 U.S. spills includ-
ing 3 chemical, 4 non-PCB oil, and 10 raw sewage. Sixteen chemi-
cal, and 22 non-PCB oil spills to the Canadian waters of the St.
Clair were reported. Very recently, (May IS883 a spill of
acrylonitrile (maximum 12,000 kg) occurred at Polysar Saxnia, but
the chemical was not detected in the St. Clair River,
Although improvements in water and sediment quality have been
made in the St. Clair River system in recent years, spills from
vessels and land-based facilities continue to threaten the suita-
bility of the river for fish and wildlife populations,
7, Contaminated Sediments
The sediments along the Canadian shore are significantly con-
taminated with a variety of chemicals (58,59,67), But compared
to chemicals in water and sediments, much less than one
percent of the contaminants moving along the river are transport-
ed by bed sediment movement (67), The total of contaminants
such as HCB and OCS in Canadian shoreline sediments in the river
is comparable to the annual loadings of these contaminants
(37,59). Unless a significant percent of this material is being
desorbed each year, it is unlikely that contaminated sediments
contribute significantly to the loading in the water column.
However, because no measurements have been made, it is not pos-
sible to come to a definite conclusion at this time.
Another way sediments can act as source of contaminants is
through the biological community, Benthic organisms have been
shown to accumulate contaminants from sediments in the river
(50). These organisms serve as a food source for higher trophic
levels such as fish. Thus contaminated sediments can act as a
source of higher body burdens of chemicals in biota in the
system. Sediments from the Sarnia industrial area are lethal to
Hexagenia, Hydallela, and fathead minnows.
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285
TABLE vu-i?
Spills of hazardous materials in excess of 10 tons into the Ontario
waters of the St, Clair River and its tributaries, 1974 - 1985*.
Source
Suncor
Suncor
CNR
Esso Petroleum
Hall Corp. (Vessel)
CNR
Esso Petroleum
Esso Petroleum
Esso Petroleum
Imp. Bedford (Shell)
Esso Chemical
Total
Polysar
Polysar
Polvsar
Po L vsar
Total,
Dow
Polvsar
Total
Dow
Dow
Dow
Dow
Polvsar
Suncor
Esso Chemical
Esso Petroleum
Total
Pol ysar
Esso Petroleum
Suncor
Eagle Transport
Dow
Esso Petroleum
Dow
Total
Substance
Spilled
Bunker 4 oil
Bunker & oil
Bunker & oil
Gas Oil
Bunker & Oil
Bunker & Oil
Gasoline
No, 2 fuel Oil
No. 2 fuel Oil
Catalytic cracker
Slop Oil
Latex
Latex
Latex
Latex
Styrene
Styrene
Hvdrochloric Acid
Sodium hvdroxide
Sodium chlorate
Sodium chloride
Sulphuric acid
Hydrochloric acid
Sodium hvdroxide
Brine
Lienin liquor
Phenolic wastewater
Process water
Xylene
Ethviene Glycol
Waste Water
Perchloroethyiene
Year
1976
1976
1977
1978
1980
1981
1981
1984
1984
1985
1985
1975
1976
1980
1980
1974
1978
1974
1975
1979
1981
1981
1982
1983
1984
1975
1975
1975
1975
1976
1982
1985
Amount ( Tons )
Spilled Unrecovered"
150
300
86
29
21
21
348
116
16
75
120
1 . 282
17
18
87
20
T4~2
4,504
411
21
28
4,080
379
13
16
19
164
159
239
91
11
13
46
54
FTJ
30
0
17
0
13
4
0
23
3
1
0
91
17
18
87
20
TT2
2,700
2,780
21
28
4,000
76
13
0
4
4, 175
33
239
73
2
0
46
7WT
a-Datafrom(36).
b - Estimate based upon reports of percent recovered.
-------
"DATE"
SOURCE"
TABLE Vll-Ua
Spills from Canadian sources to the St. Clair River (IDSfi).
I chemicals)
" 1 "CHEMTCSt r~~VOtUBE '"! RECETVTKG WATER""! l.OCATTON f
I
I1
i1
AMOUNT
186/03/28 !I)ow Chemical !~Polvethvene
j | j Powder
JB6/015/29 [CIL [30fc Phosphoric
j j j Powder
{ 86/05 / IT" {Suncor "Refinery {Toluene
[efi/Ofi/12 'Dow Chemical [ Styrene
I J [Benzene
j 86/06/12 'Bow Chemical J35X Ethylene
J | {filycol
Jfl8/07/I2 J!>owT?hemieal " jUnknown ""
J86/07725 iTmperiarTJil Ue- {Diesel 'Fuel
J finery Fueling !
| jtock j
[86/07/30 j Dow "Chemical ' {"ElhvT Benzene H
j j [Styrene
JB6/07/3I [imperial Oil Re-{0iesel Fuel
! finery Fueling !
[ [Dock ' J
[86/Oa/07~ {polvsar {"Tertiary Butyl
j j [Alcohol
jfifi/08/12 JFibergJas Canada {pheno I ic Seairi
J8S/08/1Z JDow Chemical JBenzene
[ee/oa/liT 'Polysar Jffalo-Butvl
j 1 j Rubber
'gB/n/24 [Piberglfts Canadafphenol Dyes
j j [Formaldehyde
JBfi/ll/ZS 'Polvsar j Calcium & Zinc
j | [St.earates
J86/12/18 [Polysar [stearic Acid H
I __
150 kg phos-
phorus
204IT"
2 'kg eacFT
2273 L
IIBODHL
h' 1 SI L H
'204 L
272 L
227 L
25 ktj
900-1360 L
90 1,
' 5-10'kg
20 L
"St.
St.
St.
St.
St.
St.
^SFT
St.
St.
St.
St.
St.
tit.
St.
Clair River jSarnia
1
Clair River JCourtright
t
Clair River Sarnia
Clair River ISarnia
j
Clair River I Sarnia
1
Clair River [Sarnia
Clair River [Sarnia
I
Ciair River [Sarnia
1
Clair River jSarriia
I
1
Clair River [Sarnia
1
j Drain j Sarnia
Clair River j Sarnia
Clair River 'Sarnia
1
Clair River jSarnia
I
Clair River JSarnia
1
Clair River JSarnia
i
i
_
j
i
i
1
I
J Samples
! taken ,
! feooms
[deployetl
1
.Plume
j mode 11 ing
1
1
1
1
1
1
Plume
j model linj?
[Booms
1 deployed
I
1
1
J Booms
[deployed
I _ 1
1 1
, — ... ^.. .
—
Storm
overflow
—
Tug
f ue 1 ing
leak
100*' '
*~
_
100%
CO
-------
j Tiate [ Source
1 1
] 86/0471 0 j SheTT~RefTnery
J86/04/lH|Suncor Refinery H
1 1
[8B/05/07JShell Refinery
1 1
| 8 S7Wlfit Imperial Oil
[ Ref inery
,8fi/0!>/lHJPolySar
jftfi/06/05 jOntnrio Hydro
[86706/11 [Shell Refinery
1 1
JBG/06/11 [Shel 1 Refinery
1 1
1 1
j i i
86/07/02 Imperial Oil
j Re f i nery
Hfi/OT7ff7 [Imperial Oil'
[ Re ri nery
88/07/12 Imperial Oil
[ j Re V i nery
] ftf)/07/12[Polygar
1 1
JBG/07/12[SheIl Hefinery
t 1
|86/07/20JPolysAr
1 1
[86/tra/02J Shell Hefinery
1 1
J86/08/07J Shell Refinery
] 86/08/08 j Shell Refinery
j 06/08/29 [ Polysar ""
jflfi/08705[ Polysar
J86/09/22J Polyaar
1 1
J BG/10/03J Polysar
i I
86/ro/26 Imperial Oil
j ] Refinery
Volume
45.4 L
9TW C
3,08 T; —
10 L
13.5 L
1818 L
0\ i V
water
-
4.5 L
4773 L
'
40y6 L
4091'L
(J
3'g'TT
2. 2" L'
^000 L~*
^STTH^TX1
45-S!) L
TARI-E VIT-17a. ii
Cnon-POB oi
Receiving Water j Location
Tal Fourd Creek JCorunna
St. Clair River|Sa'rnia"
1
St. Clair RiverjSarnia
1
St. Ulair RiverjSarnia
1
St. CUir RiverjSarnia
St. Clair Ri ver J Courtright
Talfourd Creek {Corunna
I
Talfourd Creek JCorunna
1
St.. CI«ir River|sarnia
1
St. Clair RiverjSarnia
1
St. Clair RiverjSarniA
1
St. Clair HiverjSarnia
1
Tallourd Creek JCorunna
1
St. Glair RiverjSarnia
1
Talfourd ^Creek JGbrunna
1
Talfourd Creek JCorunna
Talfourd Creek JCorunna
St. Clair RiverjSarnia
hSt. Clair RiverjSarnia
St. Clair RiverjSarnia
I
St. Clair RiverjSarnia
St. Clair RiverjSarnia
t
-ont'd j
ls« 1
Resolution
Booms deployed
Booms deployed
Booms deployed
Boons deployed
Booms deployed
Booms deployed
Rooms deployed
Booms deployed
Boons deployed
Hooraa deployed
Boons deployed
Boons deployed
Boons deployed
~
™
Boons deployed
Booms deployed
Clean up
initiated
Recovered; Comments |
Amount
i t
I
36.3 a litres loat
j to River
9. OB JA11 materials
j recovered
jOil not
j recoverable
i
I
1
JOverflow due to
j heavy rain
j Overt" low due to
j heavy rain
1
I
1
_ 1 Z
I
i
- j De-oiler heat
j exchanger l«ak
- {Overflow due to
heavy rain
I Overt low due to
j heavy rain
jBiox bypass due
j to heavy rain
1
:overriow due to
j heavy rain
iStorrawater
runoff
:st ornwater
runoff
j Pumps failed
i
j Power failure
[Overflow due to
j heavy rain
i i
to
CD
1 There were no reported apilJa of PCB contaminated oils.
* fn addition there were 3 reports of oil sheens on the river.
-------
TAHI.E VII-1K
U.S. raw sewage spills ( 19BB) ,
PP-KS
I'Bat'iT
Source
! ResoIiTtion
I Hecove reiTj Comments
_l_Ainau_nt I
2922-86 6/1 5/86 Ifiitv Of p0"ft
j j Huron WWTP
1 1
293J-86 '8/16/86 J~Citv of Port
{ | Huron WWTP
1 j
{ JwWTp"e 1 y
2392-B"6~ [TTB'/lT786~frritv of Por€
j j Huron WWTP
i 1
2931-86 jOS/tli/ftfetcitv or Port
{ |H»iron WWTP
i 1
D-tiOl-86!0B/23726jMarine City
] [WWTP
i i
06-H6~ [Ol/OIT/86 [Mueller Brass
t 1
1 1
1 1
1 1
1 1
1 1
1 Sire"- 86 j05/24/86JDetroit
j ( Edison
Ol 66-86 !l 1/1 S/86J Detroit
1 [Edison
i, ... i i
!2<) hrs. at
jfiDOU gal
[per hr
,24 hrs". "at"'
200 gal
j per mi n .
^ Hh
! via
1
, St .
[via
1
i 1 900 cpm foriSt.
{' 24 hr |
74 "hr"" aT St.
tiOOt) gal via
[per hr [
24 hr at
200 gal
j per nin.
1l9<)0 gpm
j 24 hr
1
[IO-I5 gal
1
1
jl g«l
t
i
j 120 gal
I
X™ „ ™-
St.
[via
1
]"st.
1
1
+Z?—
Jvia
1
1 via
I
I
1
[St.
1
[
jst.
t
CTTair RiverlSt. CLair Co.
Black River Port Huron
1
Clair Riverjst. Clair Co.
Black River Port Huron
1
Clair River St. Clair Co,
Mari ne Ci t.y
Clair Riverjst. Clair Co.
Black RiverjPort Huron
1
Clair RiverjSf. Clair Co.
Black River Port Huron
1
Clair Riverjst. Clair Co.
j Marine City
1
CLair Riverjst. Clair Co,
Black RiverjPort Huron
1
Clair Riverjst. CTair Co.
Black River [Port Huron
1
1
1
Clair River] St. Clair Co
] St. Clair
Clair Riverjst. Clair Co.
jst. Clair
t
1
t
1
t
[Spill controlled
[and cleaned up.
1
1
1
Station got
flooded.
1
I
1
1
{Pauls Road
iOiling contacted
j for clean-up.
Pauls Road
[Oiling contacted
[ for clean-up.
1
1
jBoota in place,
J ( Barrel tipped
! over)
{ Partially
contat necl .
luSCQ notified.
none j
1
1
1
I
I
t
80 gals J
I
none ]St,ormwa€er
! caused partial
[ bypass.
none jstormwater
[caused partial
1 bypass.
none [Stor«wat*r
[caused partial
j bypass .
20 gals IClean up
{supervised
jby USCG,
5 gala j Company inail-
! tuted jn-plftnt
[controls to
reduce f of
j spi 11 8.
none j
1
80 gals j
1
to
oo
00
TOTAL
IHfc gal
(704.91)
105 gals
(39B.1t
-------
289
8. Navigation
As stated earlier, ship traffic through the St. Clair River is
considerable. These ship movements cause some minor sediment
resuspension but should have little impact on the movement and
effects of contaminants in the river. Periodic dredging is
required in the lower channels of the river for navigation pur-
poses. The material dredged from the Canadian channels is placed
in a confined disposal facility (the Southeast Bend Cutoff Site,
Seaway island), because it exceeds open water disposal guidelines
for oil and grease, and mercury. Periodic U.S. shoal removal in
the upper reaches of the river of a few hundred m^ of sediment
are disposed in Lake Huron. A few hundred thousand m^ of
sediments are removed by the U.S. in the lower reaches of the
river approximately every three years. These materials are
placed in the Dickinson Island Confined Disposal Facility.
-------
290
D. DATA REQUIREMENTS AND ASSESSMENTS
In answering the source/sink question for the St. Clair River,
data sets from single laboratories were used. Thus, even if the
analyses were biased high or low, the relative changes in con-
centrations would still be apparent. Some of the bottom sediment
data for several parameters were combined and averaged. The
laboratories that generated these data performed acceptably in
the round-robins conducted by the Data Quality Management Work-
group (Chapter IV), and comparable data for the different studies
were found for overlapping sampling stations.
For the point source study, the United States methods provided.
much lower detection limits (DL) for three organics than did the
Canadian methods. For most chemicals, this did not impact the
study because of the lower concentrations found in the U.S.
sources for most organic parameters. However, for PCBs (U.S. DL
0.0001 ug/L? Canadian DL 0.1 ug/L), the difference in detection
limits could affect the ranking of the PCS sources along the
river. Fortunately, PCS discharges to the St. Clair River appear
to be fairly low, so remedial measures for PCBs may not be re-
quired.
While sensitivity analyses were applied to most of the models
used to simulate conditions in the St. Clair River, the quality
of the initial data utilized in most modeling exercises is dif-
ficult to judge. Furthermore, Monte Carlo simulations and other
uncertainty analyses are almost entirely lacking for the process
models developed to date. These shortcomings render existing
modeling tools less than fully useful for management authorities.
Additional resources will undoubtedly be a priority to overcome
these deficits.
-------
291
E. AMD CONSIDERATIONS
1. Dispersion Models
The St, Clair River, like the other connecting channels of the
Great Lakes is the recipient of large volumes of effluents. Under
normal circumstances, the apparent impact of these additions
would be less noticeable because of the large volume of water
conducted through this channel. However, because of the neces-
sity to maintain broad channels for navigation, shore based dis-
charge structures must be maintained relatively close to shore-
ward margins of the river. This fact dictates that only a rela-
tively small portion of the total river flow is available for
waste dispersal.
In an early study of lateral dispersion, Hamdy and. Kinkead (92)
adapted an existing numerical dispersion model to predict
in-streaia concentration of a conservative substance (chloride)
from shore based discharge outfalls to the St, Clair River, These
authors found that the nondimensional dispersion coefficient
measured in the field was in a range of 0.93 - 1.0, based upon a
shear velocity of 0.042 m/s a depth of 10 m. This coeffi-
cient observed in the St, Clair River substantially greater
than the classic value of 0,23 normally used in dispersion pre-
dictions.
A simultaneous parallel study conducted by Akhtar and Hathur (93)
used equations identical to Hamdy and Kinkead, but incorporated
the classic 0.23 value for the nondimensional dispersion coeffi-
cient. When Akhtar and Mathur reran their model using the Hamdy
and Kinkead value of 0,96, the transverse chloride distribution
predicted by the model agreed reasonably well with observed
values. The reported data suggest that the bulk of chlorides
were contained close to the Canadian shoreline. Shoreward con-
centrations of 80 mg/L were observed, while concentrations de-
clined to levels approaching zero 50 m off shore. Validation of
the model was against 1976 chloride data for the St. Clair
River at the sites. In this case, shoreward concentrations
of nearly 100 mg/L were shown to decrease laterally to concentra-
tions approaching zero 45 m off shore. The 1976 verifications
were against a point source loading for Cl~~ of 2,6 kg/s, a
function of a discharge rate of 3 m3/s and an initial concentra-
tion of 860 mg/L.
In a report to the Water Resources Branch of the Ontario Ministry
of the Environment, McCorquodale and Bewtra (94) provide a users
manual for a model designed to assess the convection-dispersion
and decay of vertically mixed pollutants from multiple outfalls.
The authors state that this model was developed using OMOE field
data on chlorides and phenols in the St. Clair River, While the
model was intended to simulate phenol concentrations along the
entire length of main channel of the St, Clair River, neither
-------
292
data nor model simulations are provided. No evidence of calibra-
tion, verification, or application of this model is available.
In the same short report to OMOE, McCorquodale and Bewtra (95)
consider the dispersion and transport of phenols in the St. Glair
River. These authors describe adapting a previously existing
model (characterized only as "The Detroit River Model") to condi-
tions existing in the St. Clair River.
Although this modified far-field model was used to simulate
phenol concentrations in the St. Clair River from outfall A to
the Delta, only estimations of pollutant loadings in the channels
of the St. Clair River delta are provided. The authors report
that 5 percent of the total flow and 14 percent of the total
phenol load exit the St. Clair River by way of Chenal Ecarte.
This loading approximates 4 kg/d of phenol. The South Channel is
responsible for conducting 42 percent of the total flow and 81
percent of the total phenolic load (23 kg/d, phenol) from the St.
Clair River. A total of 20 percent of the river flow, but less
than 5 percent of the total phenolic load exists the St. Clair
River via the Middle Channel. This burden represents only about
1.4 kg/d of phenol. While the North Channel is responsible for
conducting 33 percent of the total river flow, only a trace of
the total phenol loading is found in this channel. The authors
note that these values represent loadings without consideration
for decay. If degradation rates were added, the phenol loadings
to the channels could be reduced by as much as 30 percent.
Chan et al. (37) modeled the fluxes and the concentration dis-
tribution profiles in water column transects across the upper and
lower St. Clair River for the contaminants hexachlorobenzene
(HCB), hexachlorobutadiene (HCBD), pentachlorofaenzene (QCB) , and
octachlorostyrene (DCS). The data they derived clearly demon-
strated a plume of these contaminants for the Sarnia Industrial
Area. Dieldrin concentrations, on the other hand, were quite
consistent for all stations sampled, fluctuating about a mean of
approximately 0.25 ng/L. The ubiquitous distribution of this
contaminant suggests long-range transport as the likely mechanism
involved in this widespread contamination. The authors report
that similar concentration distributions to dieldrin were ob-
served for several other organic substances including alpha and
gamma BHC and PCBs.
A marked plume of contaminants was apparent, originating for the
Sarnia area. This plume was observed for HCB, HCBD, QCB, and
OCS. Very little of these compounds are present at the head
waters of the St. Clair River. At Port Lambton, however, peak
values were observed near the Canadian shoreline, with decreasing
concentrations across the river. This observation corroborates
the lateral distribution calculated for chloride by Hamdy and
Kinkead (92). Chan et al. (37) report that downstream, however,
Chenal Ecarte contained the highest concentrations, the South
-------
293
Channel was described as having significant levels, and very low
concentrations were observed in the North Channel. Unfortunate-
ly, no flow data are provided to enable an exact comparison of
channel burdens with the various values provided by McCorquodale
and Bewtra (95). However, if the normal flow value of 5,100 m3/s
for the St. Clair River provided by McCorquodale et al. (86) is
used, and if the percent of total flow reported by HcCorquodale
and Bewtra (95) for Chenal Ecaxte {5 percent of total), South
Channel (42% of total), and the North Channel (33 percent of
total) are accepted, a comparison of values may be made. This
comparison is presented in Table VII-19 below,
An order of magnitude agreement between the percentage contribu-
tions of the contaminants in the two data sets exists when the
differences in methodologies are considered, Chan et al. (37)
measured HCB in centrifuged water samples at the Port Lairtbton
stations. These samples represented "dissolved phase* HCB, since
the majority of suspended solids had been removed. The authors
note that 41 percent of the HCB observed at Port Lambton was in
the dissolved phase. When the percentage contributions to total
HCB loadings are adjusted for suspended solids concentrations,
the sum of the channel values approach 10-0 percent of the total
HCB loading rate of 1.63 Kg/d reported by Nettleton (96).
Chan et al. (37) also used the observed contaminant concentra-
tions and water depths to calculate the flux of each compound
across the river cross section at Port Lambton. Good agreement
of values was obtained when compared with Environment Canada and
Ontario Ministry of the Environment district monitoring data.
Between August and October of 1985, HCB fluxes ranged from 59 to
280 gm/day, QCB was observed from 22 to 31 gm/day, HCBD 240 to
1,700 gm/day, and OCS 5 to 15 gm/day.
These authors then calculated lateral mixing in the river channel
using a transverse mixing coefficient derived by varying the
coefficient until the calculated concentration profile matched
the measured profile. The original calculation of this factor
was made against the HCB data and applied to other measured para-
meters. With the exception of a single HCBD data set for 23
September 1985, excellent agreement with measured concentration
profiles was achieved. This single data set demonstrated no
plume-like distribution, but rather a relatively constant con-
centration across the river cross section. All other calcula-
tions demonstrated a plume which tended to remain near the
Canadian shore of the St. Clair River,
These authors also note that future studies should consider
special sampling procedures for modeling studies. They report
that the results of the water/suspended sediment partitioning
study showed that measurements should be made on both dissolved
and suspended sediment phases, or on unfiltered water samples if
contaminant fluxes or loadings are to be calculated.
-------
294
TABLE VTI-19
4 eimtsari son of burdens of chemical contaminants in the various channels
of the St. Clair River Delta Ikg/d>.
Distributary
Channel
Chenal Ecarte
South Channel
Middle Channel
Morth Channel
Phenol
Burden*
4.0
23.0
1.4
Trace
%^ of
Total Phenol
Load
14
81
<5
Trace
HCB
Burden"
0,286
0. 740
--
0.073
% of
Total HCB
Load<=
17
45
—
4
Data from (86 I.
Data from (371.
A total of * 45% of HCB loadings are unaccounted for, since Chan et
al. (371 used centrifuged water to measure HCB at the Port Lambton
stations. They note that 41% of the HCB observed at Port Lambton
was in the 'dissolved phase'.
-------
295
2. Hydrodynamic Model
A river transport model has been constructed by McCorquodale et
al. (86) which has potential for application to the St. Clair
River. This model has been variously referred to as the Univer-
sity of Windsor K-E model and the University of Windsor K-E River
Mixing Model (96). This model is a steady state, depth average,
turbulent mixing model designed to simulate complex river systems
with multiple outfalls. Nettleton (96) reports that velocity
distributions and dispersion characteristics of the St. Clair
River were computed with this model. The model divides the St.
Clair River into 14 segments, estimating the flow in each segment
using U.S. Army Corps of Engineers data adjusted to interpolated
sections in each segment based upon a normal flow rate of 5,100
m3/s (187,000 cfs),
Nettleton reports that the model was calibrated by adjusting
parameters for the lateral profile of the velocity to provide
predicted results similar to those measured. This author writes
that in addition to velocities and dispersion coefficients, this
model also provides the lateral locations of river streamlines in
the various river segments, Nettleton concludes that, based upon
the results of this and other OMOE applications of the hydro-
dynamic model, it would appear that the model is well suited for
use in the St. Clair River. At the present time, however, there
is no report of verification of this model.
3. Chemical Transport Models
Nettleton (96) reports that, to date, chemical transport modeling
for the St. Clair River has been accomplished only for the con-
taminant hexachlorobenzene (HCB). Two models were used to study
the chemical transport of HCB. One of these models, the Univer-
sity of Windsor Hydrodynamic Model discussed above, calculates
the depth averaged total contaminant concentrations in two dimen-
sions in the water column. The U.S.EPA TOXIWASP model (97),
estimates the dissolved, sediment sorbed,' and biosorbed concen-
trations of the contaminant in both the water column and the
sediment bed of the river.
The University of Windsor transport model was run with both
average and maximum loadings using both average and minimum flow
rates. The best agreement with measured field data was achieved
using average flows and maximum loadings of HCB. Nettleton (96)
reports that, under these conditions, the total loading rate of
HCB to the St. Clair River System was 1.63 kg/d. He notes that
in excess of 97 percent of this total loading results from a
single point source, the Dow Chemical First Street sewer complex.
Comparisons of the river model predictions of HCB concentrations
with measured values were reported to be in good agreement (86).
-------
296
The magnitudes of predicted concentrations were generally within
the probable error of field data measurement (96).
The TOXIWASP model is a multiple cell model which divides the
water column and bed into segments both vertically and hori-
zontally. The principal mass transfer mechanisms considered by
this model include contaminant advection and dispersion, sediment
settlement and resuspension, volatilization and biological degra-
dation of the contaminant, and point and nonpoint sources of
contaminant to the water column, including sediment bound ma-
terials.
In relation to the St. Clair River, this model was run using only
one layer of water column and bed sediments. The river was
divided horizontally into four flow panels. Both "fine" and
"coarse" grid patterns were used. The "coarse" grid considered
the entire river to the Delta area, while the "fine" grid was
used to concentrate on the analysis of the river in the vicinity
of the outfalls.
Nettleton (96) reports that comparisons between water column
concentrations of HCB predicted by TOXIWASP with those measured
in the field were satisfactory. He notes that both the trends
and the magnitudes of the predicted values are in good agreement
with the measured field data. Bed sediment predictions occa-
sionally tended to over-predict both magnitudes and trends when
compared with field data. However, both magnitude and trend
predictions appear to be within the estimated field measurement
accuracy.
Nettleton concludes that it would appear that both the University
of Windsor transport model and the TOXIWASP model can predict the
chemical transport of HCB relatively accurately within the St.
Clair River. He notes, however, that these results must be
regarded as preliminary. Confirmatory results (and presumably
model verification} await the final assembly of the 1986 St.
Clair River Municipal Industrial Strategy for Abatement data
base,
4. Unsteady Flow Model
An unsteady flow model for the St. Clair River from Lake Huron to
Lake St. Clair was developed by Derecki et al. (98). This model
simulates hourly and daily flow rates of the river. Unlike other
single-stem river models, the unsteady flow model provides flow
separations in the vicinity of Stag and Pawn Islands and in the
North, Middle, South, and Cutoff Channels of the St. Clair River
Delta. The model predicts stage, discharge, and velocity data
required to simulate the fate and transport of toxic substances.
-------
297
Derecki et a1. (98) suggest that the model has been calibrated.
This calibration consisted of adjusting the roughness coef-
ficients of the river channel. These coefficients were derived
from 14 sets of flow measurements conducted by the U.S. Army
Corps of Engineers between 1959-1979, No evidence of validation
of this model is available.
5. Other Models
In a departure from the usual academic modeling format, Nettleton
and Hamdy (91) have created a user-oriented model for assessment
of effects of spilled contaminants. The modeling format is
termed 'The St. Clair River Spill Manual'. This device was
developed to provide a convenient, easily used, rapid assessment
methodology for predicting the downstream effects of spilled
contaminants on water intakes. A total of 21 outfalls located in
the Chemical Valley near Sarnia are considered in this manual.
Using this well-designed instrument, assessments of impact are
possible all along the Canadian shoreline and at five Michigan
intake sites, including St. Clair, East China Township, Marine
City, Algonac, and Old Club. The Marysville intake was found to
lie outside of all the plumes observed, and is, therefore, not
considered in the manual.
Osers desiring to assess impacts of a spill need only know the
type and total mass of contaminant spilled, the duration of the
event, and the total river flow at the time of the spill. If
decay characteristics are known, there is a possibility to incor-
porate this information into the analysis.
With these data available, the manual is then consulted to ascer-
tain the peak contaminant concentration expected, and times of
arrival and departure of the spill plume at a given water intake.
This adaptation and coupling of two mathematical models in a
specific user-oriented fashion will undoubtedly be extremely
useful to managers charged with the responsibility of providing
of safe drinking water,
6. Model Applications
A major application of these hydrodynamical dispersion models and
fate and transport models, after calibration, is for the analysis
of hypothetical effluent discharge scenarios proposed in remedial
studies. This analysis can be approached in two ways: i) ef-
fluent loadings may be established based upon treatment tech-
nology, and the models used to ascertain the resulting short and
long-term changes expected in the quality of the downstream
water/sediment/biota of the receiver; or ii) the models can be
used to estimate appropriate effluent criteria assuming known
ambient water quality criteria downstream of the outfall.
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298
As an example, effluent loading criteria for HCB discharged to
the St. Clair River from. Dow Chemical can be determined (Table
VII-20). There are two important reasons to develop effluent
criteria for HCB: i) it has been shown to impact exposed sediment
and biota within the effluent plume due to its chemical char-
acteristics (e.g., large Kow); and ii) when reduced via the
appropriate industrial treatment, other related contaminants
should also be reduced from the effluent.
For this example, three criteria are used in the analysis for
HCB, The first is the 6.5 ng/L freshwater aquatic life guideline
for concentrations in the water column. The second criterion is
that HCB concentrations in the sediment are not to increase by
more than 1 ng/L above the background level. The third criterion
is that HCB concentrations in biota, as a result of bioconcentra-
tion, is not to increase more than 50 ug/L above the background
level. The second and third criteria are' arbitrarily selected
(for demonstration purposes) for protection of the sediment and
biota under long-term steady state conditions.
The calculations (as summarised in Table VII-20) are performed
for two selected mixing zone lengths. The first mixing zone is
to the south property line of Dow Chemical (about 1,200 m down-
stream of Dow's First Street sewer complex). In this case, the
total HCB load is assumed proportional among the various outfalls
as measured in 1986. The second mixing zone is two Dow's Second
Street outfall (about 300 m downstream of the First Street com-
plex) , In this case, all loading is assumed to be discharged via
Dow's First Street complex.
In this particular example, the arbitrary biota criterion for the
shorter mixing zone would result in the most stringent effluent
loading.
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TABLE Vir-20
Loads required to limit zones of effect for HCB discharged
from Dow Chemical-
Criterion N'o . Loads fkg/d! to limit the zone of effect to:
Dow's south property Second Street outfall
line ( 1 ,200 mH ' ( 300 ro>*
1. Water (6.5 ng/t) 0.106 0,065
2, Sediments (1 ppm 0.517 0.317
above background )
3 . Biota ( 50
above background) 0.041 0.025
No t e s:
1.Assumes load is proportioned - 83, 2, 5, 10% to Dow's 1st, 2nd,
3rd and 4th street outfalls, respectively.
2.Assumes load is entirely from Dow's 1st Street outfalls.
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300
P. OBJECTIVES GOALS FOR
1, Water Quality, Sediment, and Biota Standards, Guidelines and
Objectives
Setting goals and objectives based on water quality, sediment,
and biota guidelines is difficult because guidelines do not exist
for many of the contaminants found in the St. Clair River, The
guidelines and objectives that do exist are chemical specific and
do not take into consideration the cumulative toxicity of ex-
posure to multiple contaminants. However, comparing media con-
centrations to relevant guidelines or objectives which exist
allows the identification of areas and ecosystems likely to be
impacted by contaminants.
One of the goals of the UGLCC Study is to protect and maintain
the channels for the highest attainable use. If this goal is
achieved near industrial and municipal point sources of contamin-
ants, then impacts to the river downstream water bodies
should be greatly reduced. During the study, water samples col-
lected near point sources exceeded many of the Ontario Provincial
Water Quality Objectives {see Tables ¥11-2 & 3) for the protec-
tion of freshwater aquatic life. Objectives are available for
several chemicals of concern in the St. Clair River. However,
for some chemicals found to be impacting the river, such as
octachlorostyrene and hexachloroethane, there are currently no
surface water objectives.
Objective 1. Develop water quality guidelines or objectives
for OCS, hexachloroethane and other chemicals not
currently possessing water quality objectives.
Objective 2. Reduce surface water concentrations of organic
and inorganic contaminants found to be impacting
tne St, Clair River surface water quality to
concentrations below the most restrictive water
quality guidelines with virtual elimination as a
goal.
Several sets of sediment criteria are available with which to
compare sediment contaminant concentrations in the St. Clair
River. These include the Ontario Ministry of the Environment
Guidelines for Dredge Spoils for Open Water Disposal, the GLWQA
Guidelines for Open Water Disposal of Dredged Materials, and the
U.S.EPA Guidelines for the Pollutional Classification of Great
Lakes Harbor Sediments. Even though present sediment guidelines
are generally inadequate, a comparison with contaminant concen-
trations in St. Clair River sediments indicates that there are
several locations with which to be concerned. Many of these
locations are along Sarnia's industrial waterfront, although
there are impacted areas along other reaches of the river, as
well. Guideline exceedences occur for oil and grease, lead, and
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301
mercury (Table VII-5). Sediment guidelines do not exist for many
contaminants found in the sediments of the St. Clair River, in-
cluding hexachlorobenzene, pentachlorobenzene and octachloro-
styrene.
Objective 3. Delineate more accurately, the extent of con-
taminated sediments in the St. Clair River,
especially along Sarnia's industrial waterfront,
Sediment contaminant concentrations should also
be determined for the major St. Clair River tri-
butaries; Talfourd Creek, the Black River, the
Cole Drain.
Objective 4. Develop sediment guidelines for organic chemicals
of concern in St. Clair River sediments for those
not currently having guidelines (e.g. HCB and
OCS) .
Objective 5. Reduce the discharge (concentration and loading)
of chemicals which are impacting St. Clair River
sediments from known point sources to the lowest
level achievable through the use of best avail-
able technology with virtual elimination as a
goal.
Fish consumption guidelines are available for only a few St.
Clair River contaminants. The only exceedences occur for mercury
PCBs in the larger fish of some species (such as carp).
There are no fish consumption guidelines for most of the chemi-
cals of concern in the river.
Objective 6. Reduce inputs (with a goal of virtual elimin-
ation) of mercury, PCBs and other chemicals to
the St. Clair River which are resulting in con-
centrations of contaminants in fish exceeding
guidelines.
Objective 7. Develop fish consumption guidelines for chemicals
found in St. Clair River biota which do not cur-
rently have objectives, such as OCS and HCB, and
reduce, to the extent practicable, inputs of
these contaminants to the St. Clair River.
It is necessary for regulations to move away from requirements
and objectives based solely on concentrations towards those which
include targets for reducing the total mass loading of pollutants
entering the system. Basing effluent limitations on concentra-
tions alone does not account for the long term effect of persis-
tent contaminants which remain in sediments and biota. The dis-
charge of persistent toxic substances should be reduced to as
close to zero as possible (99), in keeping with the goals of the
Great Lakes water Quality Agreement. The only practical way of
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302
reducing/eliminating release of toxic substances to the environ-
ment is at the source of the release.
Several point sources which were identified as providing signif-
icant loadings of chemicals to the St. Clair River discharged in
compliance with their concentration based discharge limitations.
However, the magnitude of their effluent flow was such that sig-
nificant loads were still provided to the St. Clair River. In
other instances, significant discharges of chemicals originated
from point sources that were not regulated with respect to that
chemical (e.g. HCB, OC3 and mercury from Dow Chemical and HCB and
PAH from Polysar Sarnia).
Objective 8. Develop mass loading limitations for the point
source discharges of contaminants found to be of
concern in the St. Clair River.
Several municipal waste water treatment facilities, both in
Canada and the United States, periodically exceeded discharge
requirements for certain parameters during the study (e.g.,
Sarnia WWTP, Port Edward WWTP and St. Clair WWTP). Most munici-
pal facilities are only required to control conventional param-
eters, such as total suspended solids, phosphorus and BOD5.
Better control of operating conditions at these facilities and
some upgrading may be required to ensure that they are discharg-
ing in compliance.
In some instances, municipal facilities were found to be signifi-
cant contributors of unconventional and toxic substances which
are not regulated, such as, phenols, PAHs, cyanide, zinc and
iron, among others (e.g. Port Huron WWTP and Sarnia WWTP), Iden-
tification of the sources of these contaminants to the municipal
facilities needs to be performed and programs to reduce such
inputs developed if further control is required.
Objective 9. Upgrade the technology and operating procedures
at municipal waste water treatment facilities
found to be exceeding discharge limits to ensure
compliance with all effluent requirements.
Objective 10. Develop additional effluent requirements, in both
mass loading and concentration form, at waste
water treatment facilities identified as provid-
ing significant inputs of nonregulated contamin-
ants impacting the St. Clair River.
Objective 11. Identify the sources of unconventional and toxic
substances entering the municipal facilities
(i.e. industrial contributors) and reduce such
inputs.
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303
Urban nonpoint sources in Canada, such as stormwater and combined
sewer overflows, increase the river contaminant burden for
several parameters including oil and grease, PAHs, lead and iron.
A thorough evaluation of this pollution source on the United
States side of the river was not carried out for the UGLCC Study,
but is needed.
Objective 12. -Upgrade or redesign municipal facilities operat-
ing CSOs, such as the Port Huron and the Sarnia
WWTPs, to ensure that CSOs do not occur.
Objective 13. Identify the original sources of contaminants
contained in urban runoff {e.g. atmospheric
sources and spills) and take regulatory and man-
agement steps to reduce or eliminate contaminant
input.
Rural and urban industrial nonpoint sources have been poorly
characterized for the St. Clair River. Contaminant loadings
determined for the Black River and the Cole Drain showed these
tributaries to be significant contributors of many contaminants
including phosphorus, nitrogen, nickel, copper, zinc and cadmium
(Black: River) and PAHs, cyanide, and oil and grease (Cole Drain).
Although no contaminant loadings were determined for Talfourd
Creek, the presence of herbicides and pesticides commonly used in
agriculture and high concentrations of some metals supports the
supposition that Talfourd Creek may be a significant contributor
of contaminants,
Objective 14. Develop programs within the agricultural com-
munity to reduce excessive use of phosphorus and
pesticides. Develop new programs and support
existing ones which provide instruction on the
use of conservation tillage techniques and live-
stock waste management.
Several waste disposal sites have been ranked as having a high
potential to pollute the river. Several other waste disposal
sites appear to need additional information to assess their pre-
sent and future hazard. Improved contaminant and leachate con-
trol and treatment systems may be required for some sites, others
may require more intensive remediation. 'Sludges from municipal
and industrial wastewater treatment plants are either incinerated
or placed in approved land disposal facilities. The transport of
contaminants in surface runoff or groundwater leachate plumes
from the disposal facilities has not been fully assessed.
The ultimate fate of injected wastes disposed in the past by
pressurized injection in Ontario and by continuing pressurized
injection in Michigan is unknown.
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304
Objective 15. Determine the actual state of containment of the
waste sites having a potential to contaminate the
St. Clair River and its tributaries and monitor
groundwater and surface water discharges. For
those sites providing contaminant inputs to the
St. Clair River, remedial and enforcement actions
should be undertaken.
Objective 16. Further delineate the impacts, location and
migration trends of past and present liquid waste
injection into disposal wells, particularly the
role of the buried valley in transporting wastes
to the St. Clair River.
Chemical and oil spills into the river are a continuing problem
which require increased diligence. The feasibility of construct-
ing spill containment facilities at several of the major indus-
tries which frequently experience spills should be analyzed on a
case by case basis. Improved spill prevention plans and worker
training as well as better monitoring devices are other methods
of reducing spills at industrial sites,
Objective 17. Eliminate chemical and oil spills to the St.
Clair River. Management plans and prevention
structures of industries regularly experiencing
spill events should be studied and modified, if
necessary.
2. Habitat Goals
At present, portions of the river support a naturally diverse
assemblage of aquatic organisms generally indicative of an unim-
paired habitat, while in other portions of the river contaminant
discharges have extirpated or reduced the abundance of pollution
intolerant benthic invertebrates that typically have key trophic
roles and contribute substantially to the- maintenance of fish
populations. Contaminant controls are required to make the entire
river habitable.
Observable negative impact on benthic communities is apparent for
about 12 km downstream of Sarnia's industrial waterfront.
Because most sediments in the river are transient, reduced con-
taminant discharges should lead to fairly rapid restoration of
the habitat. To restore sediments along the 4-5 km industrial
waterfront, from the Cole Drain to Suncor, may require dredging
or suction removal. Some of the sediments in this area are ag-
gregated with a black tarry substance and show little tendency to
move down the river. There are several other smaller localized
impact zones along the river (described earlier) which will re-
quire the same type of discharge control strategies for clean-
up.
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305
Objective 18, Maintain the existing high quality wildlife
habitats throughout the river and delta area.
Objective 19. Restore a healthy biotic community in the 12 km
reach of the St. Clair River along the Sarnia
industrial waterfront.
3. Uses to be Maintained and Restored
At present, the river is inhabited by a variety of aquatic or-
ganisms. Because of contaminant discharges to the river, select-
ed regions are inhabited by few, if any, species, or species that
have a high pollution tolerance. Pollution control improvements
will make the entire river a suitable habitat for diverse aquatic
species.
The river is also used extensively for sports fishing. Fish from
the river contain a variety of contaminants for which fish con-
sumption guidelines have not been developed. The fish obtain
their chemical body burden from direct uptake from water and
through consumption of contaminated lower food chain organisms.
Reduction of discharges to the river would result in a lowering
of contaminant residues in fish and minimize any potential ad-
verse impact to fish consumers. These improvements would un-
doubtedly lead to more recreational use of the river and down-
stream lakes for fishing and other tourism activities.
The river is used by several communities as a drinking water
source. Not all contaminants found in the St. Clair River have
drinking water guidelines. Although drinking water requirements
are more extensive than water quality guidelines, development of
such requirements Is needed. The control of chemical discharges
to the river would reduce any potential health effects to drink-
ing water consumers.
033jactive 20. Ensure that the quality of fish, waterfowl, other
wildlife and drinking water is suitable for human
consumption by addressing the sources of con-
taminants .
Bacteria concentrations increase along the course of the St,
Clair River from head to mouth. Areas along the river which are
used for swimming have been posted, at times, due to bacterial
contamination.
Objective 21. Reduce the bacterial contamination of the river
to concentrations below public health guidelines
for body contact.
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G. ADEQUACY OF EXISTING PROGRAMS AND REMEDIAL OPTIONS
1. Projection of Ecosystem Quality Based on Present Control
Programs
Trend Analysis
The pollution situation in the St. Clair .River has improved
steadily over the years, Benthic surveys conducted along the
Canadian shoreline in 1968, 1977, and 1985 showed the seriously
degraded zone had. decreased from, over 44 km in 1968, to 21 km in
1977, to 12 km in 1985 (49). Yearly sportfish analysis by the
Ontario Ministry of the Environment in the St. Clair System has
shown that PCS and mercury concentrations in fish have steadily
declined since the 1970s (36). Restrictions in use to closed
systems, then finally banning PCBs, are the reason for the PCB
declines. Mercury discharges to the river have declined dramat-
ically since Dow Chemical (the major source} changed its chlorine
production process from mercury electrodes to the diaphragm
process.
Phenol violation zones (water concentrations above 1 ug/L) along
the Canadian shoreline near Sarnia's industrial waterfront and
downstream have decreased significantly in size since 1979
because of improved wastewater treatment (78). Also, the dis-
charge of hexachlorobenzene and octachlorostyrene have been mod-
erated by the addition of a carbon treatment system at Dow's
Scott Road Landfill and by dredging of the Cole Drain (78).
Because of the transitory nature of bottom sediments in the St.
Clair River, the use of sediment cores to infer historical con-
taminant trends is difficult and perhaps impossible. But a
detailed radiochemical analysis of one sediment core collected
downstream of Dow showed that some of the material had been there
for at least 10 years. The uppermost recent layer of this study
core was more contaminated with HCB and OCS than the deeper older
layers. This observation is probably due to the direct contamin-
ation of the sediment with nonaqueous waste material lost from
the Dow site (36). Thus, it is possible that effluent discharges
of these chemicals have decreased in recent years yet the sedi-
ments are more contaminated due to this direct contaminant con-
tact. Dow has made several modifications to its site and have
installed a nonaqueous waste recovery system in the river. The
amount of material lost to the river has decreased significantly
since the time of the UGLCC Study (100).
Superimposed on the large steady wastewater discharges to the
river are intermittent discharges which likely cause considerable
variability in water quality. Sampling in the river for the
UGLCC Study was too infrequent to pick up this variability. But
some studies showed that the concentrations of several contamin-
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307
ants in the river increased after rainfall events (41,42). Pre-
cipitation leads to contaminant loadings in urban runoff and
combined sewer overflows. Also, contaminated stormwater from
several industrial sites is discharged directly to the river.
Stormwater at other industrial sites.goes through wastewater
treatment lagoons prior to discharge. This can cause overloading
of low capacity systems. Several industries in the area have
increased their lagoon capacities to eliminate this problem
(100). Precipitation events also lead to increases in leachate
discharge from the waste disposal sites in the area.
Pollution control during rainfall events appears to require
special measures. Better housekeeping practices by industry
would lead to a lowering of contaminant concentrations in storm-
water. Also, improved stormwater storage and treatment systems,
and better leachate treatment for landfills would reduce con-
taminant loadings from, these sources. The urban pollution load-
ings could also be reduced by better collection and treatment
methods.
Another variable source of contaminants to the river is spills.
Forty-eight spills occurred in 1986 (65) . Large spills can have
a severe impact on biota near the source, and even well down-
stream because of the panelled nature of the flow in the river.
The regular occurrence of spills to the St. Clair must be stopped
if the river is to be restored.
The St. Clair River system should respond quickly to reduced
chemical loadings, The water residence time from Lake Huron to
Lake St. Clair is only 21 hours, Surficial bottom sediments
remain in the river for less than one year. There are a few
pockets of deeper sediments over bottom undulations, and of
the deeper sediments along Sarnia's industrial district to
be congealed together with black, tarry material, of these
sediments may require removal, but it is possible that they will
gradually disappear through natural weathering processes.
Mass Balance Model Scenarios
No mass balance models were constructed for the St. Clair Eiver
because of insufficient data. Before useful mass balance models
can be constructed for the river, more detailed information on
loading from various point and nonpoint sources, loadings during
precipitation events, and loadings from ambient water measure-
ments will be required. Ontario's Municipal and Industrial
Strategy for Abatement (MISA) program should provide sufficient
information on Ontario industrial and municipal contributions.
However, data for the U.S. sources and tributary/ambient water
measurements will still be required to provide sufficient data
for a mass balance model.
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308
Calculations show that the majority of contaminant discharge to
the river for most chemicals originates from point sources in
Canada. Net inputs to the river occur for HCB, OCS, PAHs,
chloride, mercury, and lead. Other parameters not on the UGLCCS
list; benzene, toluene, perchloroethylene, and pentachloroben-
zene, also have sources along the river. Thus, even though a
complete balance model was not produced during the UGLCC
Study, the study still provided sufficient information to priori-
tize sources and begin the cleanup task,
2. Assessment of Technical Adequacy of Control Programs
Adequacy, of Present Contro^ Technology
The largest users and dischargers of water on the St. Clair River
are four coal-fired power plants (89,170 x 103 m3/d): Detroit
Edison's St. Clair, Marysville, and Belle River Plants and
Ontario Hydro's Lambton Generating Station. For the most part,
water discharged is once-through cooling water. The effects of
this warm-water discharge on the ecosystem was not assessed
during the UGLCC Study, The maximum temperature of discharge
water was within government guidelines most of the time. The
cooling water at all facilities is normally chlorinated to pre-
vent slime buildup on the condenser tubes. The impact of the
chlorine residuals on St. Clair River biota should be limited to
near-field effects, because chlorine will quickly react and dis-
appear in the river. The impact of chlorine residuals from the
power plants was not accessed for the UGLCC Study.
Other contaminant sources from the power plants are storm runoff
from the coal piles and stormwater losses of fly and bottom ash.
All plants have settling basins to minimiie the losses of these
potentially toxic solids. The suspended solids concentration in
the effluents was within government guidelines. Analysis o£ the
contaminant concentration on these suspended solids has not been
performed, and to be needed before a proper assessment on
their effects on the environment can be made. Fly ash may con-
tain chlorinated dioxins and dibenzofurans, and coal fines will
contain PAHs.
PCBs were used in capacitors and transformers in the electrical
generating industry. Elevated PCS concentrations were found in
the sediments downstream of Lambton Generating Station. PCS
loadings from this facility need further evaluation.
The loadings of contaminants from the power plant effluents
difficult to evaluate because of the large cooling water dilution
that occurs. More detailed studies appear to be needed to assess
whether or not the current minimal wastewater treatment from
these facilities is adequate.
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309
The next largest effluent discharges to the river (1,150 x 1Q-*
m^/d) are chemical companies. A list of the major chemical com-
panies, their locations, and their wastewater treatment methods
are listed in Table ¥11-21. Methods of treatment vary from pri-
mary, physical/chemical treatment to secondary biological treat-
ment, depending on the nature of the product and wastewater
generated.
In general, these companies are required to meet annual average
discharge limits for ammonia, phenols, suspended solids, and oil
and grease. All facilities complied with government discharge
limits. But, many toxic and persistent contaminants are not
controlled by government effluent permits. An excellent example
of this is Dow chemical which is the largest discharger of hexa-
chlorobenzene to the St. Clair River. One of the effluent
streams at Dow is biologically treated, but the largest HCB load-
ings are from effluents that go into the river after receiving
only primary treatment. Biological treatment is not an appro-
priate method for HCB. Decreases in HCB effluent concentrations
which occur during biological treatment are due to adsorption of
HCB by the sludge. However, this simply transforms the phase of
the material, and therefore does not really eliminate the problem
from an ecosystem perspective.
Generally, biological treatment does not adequately treat persis-
tent chemicals. Even though these companies are putting more
emphasis and money into environmental control programs (100),
much more effort is needed to minimize the formation of persis-
tent toxic organics and/or to destroy them on-site. These per-
sistent chemicals should not be discharged into the environment.
The next largest dischargers (543 x 103 m'3/d} to the St. Clair
River are four petroleum refineries; Imperial Oil (Sarnia),
Suncor (Sarnia), Polysar (Corunna), and Shell (Corunna). As with
the chemical companies, these industries are regulated for am-
monia, phenols, suspended solids, sulphide, pH and oil and
grease. All companies are in compliance. The treatment for all
companies involves oil separators, dual media filters, and bio-
logical treatment. Studies have shown that this treatment se-
quence efficiently removes not only the regulated parameters, but
also the aromatic hydrocarbons and PAHs from the wastewater (66) »
Whether or not these chemically are biodegraded or simply
transferred to the air or sludge is an important question that
should be addressed.
Municipal wastewater treatment plants are the next largest dis-
chargers (151 x 10-* m^/<3) to the river. All plants except Sarnia
and Point Edward have secondary biological treatment plus phos-
phorus removal. Sarnia and Point Edward WWTPs have only primary
treatment plus phosphorus removal. Upgrading of these two plants
would reduce the discharge of some contaminants to the river.
The municipal wastewater treatment plants were significant
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TABLE VII-21
Major industrial facilities on the St. Clair River,
Company
ion
Products
Treatment
a J Canada
Canadian Industries Ltd
Dow Chemical Canada Ltd
Dupont Canada, Inc
Esso Chemicals
Canada Ltd.
Ethyl Canada, Inc
Novacor Ltd.
Polvsar Ltd.
Courtright
Sarnia
Corunna
Sarnia
Corunna
Corunna
Sarnia
- fertilizer
- polyethylene
- chlorinated
hydrocarbons
- vinyj chloride
- polystyrene
- propylene oxide
- polyethylene
po)yethylene
polyvinyl chloride
benzene,toluene,
xylene
tetraethvl lead
ethyl chloride
polyethy1ene
re sins
synthetic rubber
physical/chemical
physical/chemical
- secondarv biological
treatment on
selected streams
- plastic bead skimming
oil separators/dual
media filters/carbon
contactors
- physical-chemical
treatment on
selected process
streams
— process water recycle
- secondary biological
- physical/chemical
for selected streams
o
b) United States
Diamond Crystal
Salt Co.
St. Clair - salt
- sedimentation
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311
sources for some of the persistent contaminants; for example,
PCBs and trace metals. Since these materials are not readily
degradable, efforts must be made to stop their discharge into the
sanitary sewers at source,
Another significant source of industrial wastewater to the river
is the Cole Drain (147 x 10^ m^/d). In dry weather, the flow in
this open municipal ditch is largely industrial (65). Major
discharges to the drain were: leachates from disposal sites along
Scott Road owned by Polysar, Dow, Fiberglas, Imperial Oil, and
the City of Sarnia (sewage sludge); Canadian National Railway
yard runoff; Dome Petroleum; Esso Chemical (stormwater); Cabot
Carbon, Fiberglas, and Polysar (stormwater). Dow Chemical has
carbon treatment on the Scott Road landfill leachate, but this
seems to be inadequate to prevent the discharge of HCB, DCS, and
other persistent chlorinated organics to the drain. The Cole
Drain is also a significant source of PAHs, cyanide, and oil and
grease. Individual discharges to the ditch will need to be quan-
tified before the source of these chemicals can be traced. It is
apparent that much better treatment and control of effluents
discharged to the ditch will be required.
Urban runoff has also been shown to be a significant source for
some contaminants (82) . At present, this water is completely
untreated. Agricultural nonpoint sources are the most signifi-
cant contributor of phosphorus to the St. Clair River (84,85).
Improved tillage practices and reduced use of unnecessary
commercial fertilizers would be the only way to reduce these
inputs. Such a program would require extensive education of
farmers in modern agricultural techniques.
Several waste disposal sites could potentially seriously impact
the St. Clair River. These sites have been ranked by the Non-
point Source Workgroup (88). Clay or synthetic liners, leachate
collection systems, and monitoring well networks have not been
required for most of the sites. For most sites, there is minimal
or no treatment of waste or leachate.
3. Assessment of Regulatory Adequacy
Major industrial dischargers in the Sarnia area are subject to
discharge limits specified in Certificates of Approval, Control
Orders or the Ontario Industrial Effluent Guidelines. The in-
dustries are required to self-monitor on a regular basis and
supply the OMQE with the data. It is a violation of the Environ-
mental Protection Act to "knowingly give -false information". The
Ministry collects audit samples to check the validity of the
self-monitoring data. Sampling visits are frequently arranged in
advance. This could be a weakness in the system because surprise
visits would be more effective.
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The companies discharging to the St. Clair River are largely in
compliance with the regulations. Since problems in the river
still persist, this would seem to indicate that the laws and
regulations are insufficient to provide environmental protection,
If tougher regulations came into force, more environmental polic-
ing will likely be required. More frequent auditing of the
self-monitoring data will also be necessary.
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H. RECOMMENDATIONS
The UGLCC Study for the St. Clair River has revealed several
problems which need to be addressed. Point source discharges,
particularly in Sarnia's Chemical Valley, need to be reduced,
These sources represent the largest contributors of many con-
taminants to the system, so remedial measures here will provide
cost effective improvements in river quality. In addition, tri-
butary contributions and urban runoff appear to be supplying
significant loadings of certain contaminants. Sources of these
contaminants need to be identified and addressed.
Comparison of river media concentrations to guidelines is a quick
way of identifying areas of probable environmental impact or
impairment. However, the ecosystem approach may give a better
indication of contaminant impacts on the system as a whole, A
multi-media perspective must be developed so that the overall
impact on the system is assessed.
The following recommendations are designed to address the objec-
tives identified in Section F. As these recommendations are
implemented, monitoring programs should be undertaken to ensure
the objectives are being met.
A. Industrial and Municipal Point Source Remedial Recommendations
1. - Ontario and Michigan should incorporate the Great Lakes
Water Quality Agreement's goal of the virtual elimination of
all persistent toxic substances into their respective regu-
latory programs.
2. Polysar Sarnia should take action to significantly reduce
benzene and phenols in the American Petroleum Institute
(API) stereo separator effluent. The operation of the Biox
treatment system should be optimized to attain the Ontario
Industrial Effluent Objectives for total phenols and
ammonia-nitrogen. Effluent requirements (in both concentra-
tion and mass loading form) should be instated for PAHs and
HCB at the most stringent levels attainable through the use
of the best available technology.
3. Dow Chemical should significantly reduce its discharge of
organic chemicals to the river. The facility was a major
contributor of 5 of the 7 organic groups studied. It is
noted that current self-monitoring data is being made pub-
licly available to demonstrate the effect of recent remedial
efforts at this facility. Many improvements in operation
have been implemented at Dow Chemical since the time of the
UGLCCS survey. Self-monitoring data and other sampling
results should be reviewed to determine if additional rem-
edial actions are needed.
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4. The sources of ongoing mercury discharges from Dow chemical
and Ethyl Canada should be identified and eliminated,
5. Ethyl Canada should improve the operation of its treatment
plant to reduce concentrations of tetra ethyl lead to meet
the GLWQA specific objective and the PWQO of 25 ug/L. In
addition, enforceable mass loading limitations for lead
should be instated at this facility. Volatiles, especially
chloroethane, should also be significantly reduced in the
effluent.
6. Polysar Corunna should reduce the concentration of chromium
and zinc in the final effluent. This facility should con-
sider substituting less persistent additives in the recycle
cooling water system,
7. Effluent concentrations for chloride were generally below
drinking water objectives, but the total point source load-
ing to the system very large (356 tonnes/day), Most was
from facilities in the Sarnia area. The extreme loadings
may be affecting aquatic organisms downstream of these faci-
lities. Chloride concentration and loading limitations
should be considered for those facilities discharging sig-
nificant amounts of chlorides,
8, All potential sources of releases of heat exchanger fluids
should be identified and controlled.
9, The Sarnia WWTP should be expanded and upgraded to secondary
biological treatment with phosphorus removal. In conjunc-
tion with the upgrading, the Point Edward WWTP (a primary
plant) should be considered for use as a pretreatment facil-
ity which would discharge to the Sarnia Plant, The loading
of ammonia-nitrogen, total phenols, heavy metals, and or-
ganics to the St. Clair River would be significantly reduced
by this action.
10. American Tape in Marysville should be evaluated to ensure
compliance with their KPDES permit, Michigan Water Quality
Standards and BAT requirements for toluene and xylene in its
discharge.
11, The City of Marysville should be evaluated to ensure com-
pliance with their NPDES permit and Michigan Water Quality
Standards for toluene in its discharge,
12, The National Pollution Discharge Elimination System permit
for the Marine City WWTP should be evaluated to ensure com-
pliance with Michigan Water Quality Standards for cyanide.
The pretreatment program should be reviewed to ensure that
cyanide is adequately regulated. Acute and chronic bio-
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assays for cyanide may be required at this facility.
13. A survey should be conducted at the St. Clair County-Algonac
WWTP to evaluate the efficiency of the treatment system. An
ammonia-nitrogen effluent limitation should be considered
for the facility. Nitrogen loading to the river and Lake
St. Clair may be reduced by these actions.
14. The City of St. Clair WWTP should be resurveyed to ensure
that the expanded plant is operating effectively.
15. A study of industrial contributors to the Port Huron WWTP
should be undertaken to identify the source or sources of
CN- and PCBs to this facility. Pretreatment requirements
for all industrial contributors should be examined, and
modified if needed. Effluent requirements for CN- and PCBs
should be considered for inclusion in the facility's NPDES
permit.
16. Biomonitoring studies should be conducted at the major
dischargers to determine whole effluent toxicity at these
facilities. This study evaluated the point sources only on
a parameter-by-parameter basis, with no attempt made to
determine the impact of any additive or synergistic effects
the parameters may exhibit.
B. Nonpoint Source Remedial Recommendations
17. Sources of PAHs and total cyanide to the Cole Drain, Sarnia,
should be identified. If the sources are exceeding applic-
able effluent guidelines, they should be remediated.
18. The loadings via surface water runof.f and groundwater dis-
charge from landfills in the Scott Road area to the Cole
Drain need to be determined and treated as necessary.
w
19. Licensing requirements for sludge disposal facilities should
ensure that surface water and groundwater are properly moni-
tored and treated.
20. A and B Waste Disposal, Hoover Chemical Reeves Company, and
Wills St. Dump Site were all scored under the Superfund
Hazard Ranking System (MRS) apparently without consideration
of groundwater quality information. The State of Michigan
should determine, based upon USGS chemistry information, the
State priority for action at each site. Development of more
complete groundwater information on-site would allow the
State the options of pursuing Federal action under Superfund
by rescoring the site under the new HRS (when it is approv-
ed) , or pursuing remediation under Act 307 (MERA). Further-
more, the facilities needs for RCRA permitting need to be
assessed, or reassessed.
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21. The proximity of Eltra Corp. Prestolite to the St. Clair
River, and the nature of wastes on site call for careful
evaluation of impacts on groundwater and on the St. Clair
River prior to facility closure under RCRA authorities. In
the event that a satisfactory evaluation of groundwater
contamination and runoff impacts upon the St. Clair River
are not secured, a Site Investigation (SI) under Superfund
authorities should be undertaken. The SI should include
assessment of both groundwater and surface runoff impacts
upon the St. Clair River.
22. The State of Michigan needs to restrict access of dumpers to
Winchester Landfill. The State's development of groundwater
information for this site would assist in scoring by the
HRS.
23. Michigan and Ontario municipal combined sewer overflows
should be intensively surveyed to determine their contri-
bution of pollutant loadings to the river. In the long term
(due to the enormous cost), combined sewers in all munici-
palities should be eliminated. In the interim, the munici-
palities should institute in-system controls to minimize the
frequency and volume of overflows.
24. The Michigan Pollution Emergency Alerting System and spill
reports from the Ontario Spills Action Centre should be
improved so that all information on recovery, volume (if
known) , and final resolution are fed bacJc to the central
reporting system to complete each report for inventory pur-
poses .
25. Spill management programs at all facilities should be re-
viewed and enhanced to reduce the frequency and magnitude of
spills to the St. Clair River with the goal of eventually
eliminating all spills.
«*
26. Aggressive educational programs on the use of conservation
tillage techniques and pesticide, fertilizer, and manure
application techniques should be provided to farmers to
reduce rural runoff contaminant contributions. Stricter
legislation to control such application should be developed
and enforced.
C. Surveys, Research and Development
27. Water quality guidance needs to be developed binationally
for OCS, individual or total PAHs, hexachloroethane and
chlorides. In addition, Canada needs to develop guidance
for hexachlorobutadiene, and the U.S. needs water quality
guidance for hexachlorobenzene, phosphorus and pentachloro-
benzene. The Great Lakes Water Quality Agreement needs to
develop specific objectives for all of these parameters.
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Fish consumption and sediment guidance are needed for HCB,
OCS, PAHs, alkyl lead, and other chemicals found to be of
concern in this study.
28. More data are needed to assess the impact of PAHs on the St.
Clair River. Ambient water concentrations, and point and
nonpoint source loadings should be measured. Monitoring
should be detailed enough to allow for the finger printing
of sources.
29. The importance of contaminant loadings during rainfall
events needs to be evaluated.
30. The loadings of all chemicals with high bioconcentration and
bioaccumulation potential should be reduced to minimize
contaminant body burdens in resident and spawning fish.
31. Assess the significance of mercury contamination to biota
from sediments relative to ongoing discharges and develop
remedial actions as necessary.
32. Industrial and municipal facilities discharging to St. Clair
River tributaries should be surveyed to determine their
contribution of contaminants to the St. Clair River. In
particular, contaminant loadings from Talfourd Creek in
Ontario and the Black River in Michigan should be deter-
mined.
33. The potential PCS source in the vicinity of the Lambton
Generating Station should be investigated and quantified.
34. The loadings and sources of PCBs, PAHs, oil and grease,
lead, ammonia, and phosphorus from the unnamed creek in
Michigan across from the Lambton Generating Station should
be determined and controlled to ensure compliance with
Michigan Water Quality Standards.
35. The lead source to the Black River in Michigan should be
located and controlled.
36. Sources of bacterial contamination to the river should be
traced and eliminated.
37. A waterfowl consumption advisory should be considered by
Ontario and Michigan for the St. Clair River.
38. A study on the magnitude of contaminant input to the St.
Clair River from Michigan urban runoff should be undertaken,
and an additional, more refined study on Canadian urban
runoff should also be performed. Management control options
for urban runoff should be developed.
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39. Contamination from waste disposal sites, identified as high.
priority by the Nonpoint Source Workgroup (88), need to be
further investigated with regard to contaminant pathways,
including surface water runoff and groundwater seepage, and
environmental impacts.
40. Continued monitoring of water levels and water quality in
the freshwater aquifer in the Sarnia area is required.
41. The potential for transboundary migration and contamination
of the St. Glair River and/or the fresh water aquifer in the
Sarnia area from industrial waste in. the 74 m and 123 m
depth limestone layers of the Hamilton Group should be in-
vestigated. Of particular concern, is the 74 m depth hori-
zon which likely flows into the fresh water aquifer in the
deeper sections of the bedrock valley.
42. To understand the fate of the industrial waste disposed to
the Detroit River Group, additional deep boreholes to the
disposal formation are required to quantify the current
directions and rates of groundwater movement,
43. Michigan should co-operate with Ontario in the deep well
studies. A number of deep wells are needed in St. Clair
County to supplement the information from the Ontario
studies. If evidence of impacts upon Michigan groundwater
is developed, a variety of authorities, including Superfund,
may be applicable for remediation of identified problems.
44. The potential biological consequences of increased chloride
concentrations in the St. Clair River and downstream should
be examined.
45. Better methods for analysis of PCBs in the St. Clair River
need to be undertaken.
46. Studies on the bioavailability of particle-bound contamin-
ants , and contaminant desorption from suspended and bottom
sediments are required to make a better assessment of the
impact of in-place pollutants.
47. Studies on the effects of multicontaminant exposure to
aquatic life.
48. Studies to better understand the fate and transport of sedi-
ment-borne contaminants are needed. These studies should
include profiling the age and contamination of sediments in
St. Clair River and delta depositional areas.
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I. LONG TERM
1. Purposes for Monitoring and Relationships Between UGLCCS and
Other Monitoring Programs.
A presentation of the purposes for monitoring and surveillance
activities is included under Annex 11 of the 1978 GLWQA, and a
discussion of considerations for the design of a long term mon-
itoring program can be found in Chapter 7 of the Report of the
Niagara River Toxics Committee (1984). Because the focus of the
UGLCC Study was toward remedial actions to alleviate impaired
uses of the Connecting channels System, long term monitoring
recommendations will likewise focus on the evaluation of trends
in environmental quality in order to the effectiveness of
remedial actions. In general, post-UGLCCS monitoring should be
sufficient to 1) detect system-wide trends in conditions noted by
the OGLCCS, and 2) detect changes in ambient conditions which
have resulted from specific remedial actions. Monitoring
programs should be designed to specifically detect the changes
intended by the remedial actions so as to ensure relevance in
both temporal and spatial scales.
Two major programs sponsored by the IJC also contain plans for
long term monitoring; the Great Lakes International Surveillance
Plan (GLISP) and the Areas of Concern Remedial Action Plans (AoC-
RAPs), The GLISP for the Upper Great Lakes Connecting Channels
is presently incomplete, pending results of the UGLCC Study, but
it is expected to provide monitoring and surveillance guidance to
U.S. and Canadian agencies responsible for implementing the pro-
visions of the WQA that Include general surveillance and research
needs as well as monitoring for results of remedial actions.
The St. Clair River is of the AoCs, and a RAP is being devel-
oped jointly by Michigan and Ontario. The RAP will present
details of uses impaired, sources of contaminants, specific reme-
dial actions, schedules for implementation, resources committed
by Michigan and Ontario to the project, target clean-up levels,
and monitoring requirements. Results recommendations coming
from the UGLCC Study will be incorporated extensively into the
RAP, which will then be the document that influences State and
Provincial programs in the St. Clair River. The recommenda-
tions for long term monitoring that are presented below are in-
tended for consideration and incorporation into either or both
the GLISP and RAP for the St. Clair River,
2. System Monitoring for Contaminants
Water
Knowledge of the concentrations of the principal contaminants in
the water of the St. Clair River should be used to indicate
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general exposure levels for the biota, to identify changes and
trends over time in the concentration levels, and to be used for
general assessment of contaminant impacts. The parameters to be
monitored include HCB, OCS, total phenols, cyanide, mercury,
lead, total volatiles and chlorides. Monitoring stations should
be located where elevated concentrations of the contaminants are
known or predicted from dispersion models. Suggested locations
include the head of the St. Clair River and at Port Lambton,
particularly on the Canadian side. Sampling frequency should be
influenced by the variability in contaminant sources. Spring
high flow conditions and late summer low flow conditions would be
expected to bracket the normal seasonal variability in flow that
could influence measured contaminant concentrations.
A mass balance approach to contaminant monitoring will help to
identify any changes in the contaminant mass over time, and it
will provide the basis for targeting future remedial actions by
providing a comparison of the magnitude of the sources. A mass
balance analysis should be conducted approximately once every
five years, assuming that some effective remedial action has been
implemented against one or more sources such that the total load-
ings of contaminants, or the relative contribution of the sources
to the loading, has changed. The sources to be measured should
include:
1) Head and mouth transects. The number and location of sta-
tions should relate to measured and predicted plume dis-
tributions. Suggested locations include the head of the St.
Clair River and at Port Lambton. The Port Lambton transect
will be consistent with past dispersion measurements and
modeling work, and will help delineate contaminant loading
into Lake St. Clair. Both dissolved and particulate frac-
tions should be analyzed. The quantity of suspended
sediment flux should also be measured.
2) Municipal and industrial point sources. During the
survey, the sampling must be frequent enough to ac-
curately reflect the likely loading fluctuations from
the major point sources. The sources include the major
outfalls of Sarnia WWTP, Cole Drain, Polysar Sarnia,
Polysar Corunna, Dow Chemical, suncor, Ethyl Canada,
CIL Inc., Port Edward WWTP, and Marine City WWTP.
3) Tributaries. Efforts should be focused on seasonal and
storm event loadings of contaminants to the St. Clair
River from Talfourd creek and the Belle, Pine and Black
Rivers. A channel near Fawn Island also diverts some
of the Sydenham River drainage to the St. Clair River
during severe spring runoff events. Tributary mouth
stations should be sampled and analyzed for both dis-
solved and sediment-associated contaminant loadings.
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4} CSOs and Urban Runoff, To provide an estimate of con-
taminant mass loadings expected during storm events,
occasional studies on selected urban drainage areas
should be conducted. Some estimates have been for
Sarnia, Ontario, similar estimates should be for
other urban areas along the river,
5) Groundwater inflow. The quantity and quality of poten-
tial contaminant releases from waste disposal sites
adjacent to the St. Clair River or its tributaries
should be determined. Permits should require ground-
water monitoring, an assessment of surface water runoff
and determination of overall loadings to surface water.
Characterize the distribution, composition and movement
of deep well injected waste. Evaluate the impacts of
Michigan and Ontario injection pressure regimes on the
movement of the waste.
6) Sediment transport. Preliminary studies indicate that
less than 1% of the contaminants in the St. Clair River
are transported by bed-load sediments movement. How-
ever, the quantity of contaminants being desorbed from
the sediments should be determined in order to assess
loadings from these in-place polluted sediments.
7) Atmospheric deposition. Direct atmospheric deposition
Of contaminants to the St. Clair River is expected to
be minor. Deposition to the drainage basin and sub-
sequent runoff into the river or its tributaries,
however, could be an important source for con-
taminants. Estimates of contaminant mass in both wet
and dry deposition to the drainage basin should be
when unidentified non-point sources are found to be a
major contributor of any o£ the contaminants of
interest.
Sediments^
Monitoring of sediments for concentrations of contaminants should
be conducted periodically throughout the St. Clair River in order
to assess both the trends in surficial contaminant concentrations
and the movement of sediment-associated contaminants within the
River, grid used by the U.S. Fish and Wildlife Service dur-
ing the 1985 survey would be appropriate for consistency in sam-
pling sites and sediment composition. An analysis of sediment
chemistry including bulk chemistry, organic and inorganic con-
taminants , and particle size distribution should be conducted
every 5 years, in conjunction with a biota survey {see "habitat
monitoring" below), In the St. Clair River, particular attention
should be given to sediment concentrations of chlorinated or-
ganics (PCBs, HCB, OCS, HCBD), benzene, phenols, oil and grease,
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and heavy metals, including mercury.
Because the grid stations are distributed throughout the river
reach and are associated with appropriate habitat for a sensitive
benthic invertebrate (Hexagenia), the periodic survey will allow
assessment of 1) contaminant concentrations in the river sedi-
ments throughout the river reach, 2) relative movement of the
contaminants within the river sediments between surveys, and 3)
correlation of contaminant concentrations with benthic blotic
communities,
The sediments at any stations established at the mouths of tribu-
taries to the St. Glair Elver should be monitored for organic and
inorganic contaminants on an annual or biannual basis when sig-
nificant remedial actions are implemented within the watershed of
the tributary. In order to trigger the more frequent sediment
monitoring program, the remedial actions should be expected to
measurably reduce loadings of or more particular contaminants
via the tributary,
Biota
Long term monitoring of concentrations of contaminants in biota
will provide a time series useful to track the bioavailability of
contaminants to selected representative organisms, Three long
term monitoring programs are already in place in the Great Lakes
basin and should be expanded into the St. Clalr River.
i) Annual or Bi-Annual Monitoring of Sport Pish,
This program should focus especially on PCBs, mercury and/or
other contaminants (e.g. dioxins and dibenzofurans) that are
considered to be known or suspected health hazards. Because many
of the fish species in the river are transitory, efforts should
be to identify sample those species that have an ex-
tended residence time in the river as well as those that are most
sought by anglers. The monitoring should be continued regardless
of the differences that may be observed between acceptable con-
centrations or action levels that may be established by govern-
ment agencies and the measured contaminant concentrations in the
fish flesh. As a link between human health concerns and integr-
ated results of remedial programs to reduce contaminants in the
UGLCC System, this program is critically important.
ii) Spottail Shiner Monitoring Program.
This program is designed to identify source areas for bioavail-
able contaminants. In locations where spottail shiners or other
young-of-the-year fish contain elevated levels of contaminants,
additional studies should be conducted to identify the sources of
the contaminants. Some upstream studies in tributaries may be
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required. Spottails should also be employed to confirm that
remedial actions upstream to a previous survey have been effec-
tive in removing or reducing the loading of one or more contamin-
ants.
iii) Caged Clams Contaminants Monitoring.
Caged clams should continue to be used at regular time intervals,
perhaps in conjunction with spottail shiners, to monitor in-
tegrated results of remedial actions to reduce contaminant load-
ings to the water. Clams may be located at tributary mouths and
downstream of suspected source areas. Repeated assays from the
same locations should confirm results of remedial actions.
3. Sources Monitoring for Results of Specific Remedial Actions
Remedial actions intended to reduce concentrations and/or load-
ings of contaminants from specific point sources generally re-
quire monitoring for compliance with the imposed criteria or
standards. The monitoring may be conducted by the facility or by
the regulating agency, whichever is applicable, but attention
must be given to the sampling schedule and analytical methodology
such that mass loadings of the contaminants can be estimated, as
well as concentrations in the sampled medium. Monitoring of the
"nearfield" environment, i.e., close downstream in the effluent
mixing zone, should be conducted regularly to document reductions
in contaminant levels in the appropriate media and to document
the recovery of impaired ecosystem processes and biotic com-
munities . Such monitoring may be required for a "long time", but
over a restricted areal extent, depending on the severity of the
impact and the degree of reduction of contaminant loading that is
achieved.
For the St. Clair River, eleven actions were recommended that
would affect specific sources of contaminants, and that would
require site specific monitoring for compliance or other effects
of the action at the following locations: Marine City WWTP
(cyanide concentration), St. Clair County-Algonac WWTP (ammonia-
nitrogen limits), American Tape in Marysville (xylene and
toluene), City of Marysville WWTP (toluene), Sarnia WWTP
{phosphorus, ammonia-nitrogen, total phenols, heavy metals and
organics), Cole Drain, Sarnia (PAHs, cyanide, oil and grease),
Polysar Sarnia (benzene, phenols), Dow Chemical (several organic
chemicals), Ethyl Canada (lead, volatile organics, mercury, and
chloroethane), and Polysar Corunna {chromium and 2inc).
Other recommendations for specific contaminant sources involve an
assessment of the present conditions or a study to quantify con-
centrations or loadings: survey the St. Clair County-Algonac WWTP
and the City of St. Clair WWTP to document the efficiency of the
treatment system, intensively survey CSOs in Michigan and Ontario
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for determining the contribution of pollutant loadings to the
River, establish biomonitoring studies at a major point source
contributors, assess impact of PAHs on St. Clair River and es-
timate their loadings, measure contaminant loadings during rain-
fall events, obtain better estimates of the mercury losses from
the Dow site, quantify loadings of contaminants from urban non-
point sources, evaluate contamination from waste disposal sites,
etc. Each of these items requires a specific program of data
collection and analysis. Additional needs for longer term monit-
oring may be identified as a result of these studies.
4, Habitat Monitoring
Habitat monitoring should be conducted to detect and describe
changes in the ecological characteristics of the St. Clair River
through periodic analysis of key ecosystem elements. The
following items are recommended:
a) The abundance and distribution of the mayfly Hexagenia
should be determined every five years. The grid used
by the U.S. Fish and Wildlife Service during the 1985
survey would be appropriate for consistency in sampling
sites each survey. An analysis of sediment chemistry,
including bulk chemistry, organic and inorganic con-
taminants, and particle-size distribution, should be
conducted for samples taken concurrently with the Hexa-
genia survey. These data will provide information on
the quality of the benthic habitat for a common pollu-
tion-sensitive organism that would serve as an indica-
tor species of environmental quality.
b) Quantification of the extent of wetlands along the St.
Clair River should be conducted every five years, in
conjunction with the Hexagenia survey. Aerial photog-
raphy or other remote sensing means would be appro-
priate to discern both emergent and submergent macro-
phyte beds that are important as nursery areas for
larval fish and other wildlife. Verification of areal
data should be conducted by inspection of selected
transects for plant species identification and abun-
dances. Changes in wetland areas should be correlated
with fluctuating water levels and other natural docu-
mentable influences so that long term alterations in
wetlands can be tracked and causes identified.
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J. REFERENCES
1. Edsall, T.A., B.A. Manny, and C.M. Raphael. 1988. The
St. Clair River and Lake St. Clair, Michigan: an ecologi-
cal profile. U.S. Fish and Wildlife Service, Biol. Rep,
85 (7.3). 130 pp.
2. Edsall, T.A., P.B. Kauss, D. Kenaga, T. Kubiak, J. Leach,
T. Nalepa, and S. Thornley. 1988b. St. Clair River biota
and their habitats; A geographic area report of the Biota
Work Group, Upper Great Lakes Connecting Channels Study
(Typescript), pp.42 plus 5 tables and 26 figures.
3. Korkigian, I.M. 1963. Channel Changes in the St. Clair
River since 1900. J. Waterways Harbors Div., Proc. Am.
Soc. Civil Eng. 89:1-14.
4. Muth, K.K., D.R. Wolfert, and M.T. Bur, 1986. Environ-
mental study of fish spawning and nursery areas of the
St. Clair - Detroit River system. U.S. Fish and Wildlife
Service, Draft Final Report, Sand'usky, Ohio, U.S.A.
5. Herdendorf, C.E., C.N. Raphael, and W.G. Duffy. 1986.
The ecology of Lake St. Clair wetlands: A community prof-
ile. National Wetlands Research center, U.S. Fish and
Wildlife Service Biological Report 85(7.7). U.S. Govern-
ment Printing Office, Washington, D.C. pp.187.
6. Quinn, F.H., and R.N. Kelly. 1983. Great Lakes monthly
hydrologic data. National Oceanic and Atmospheric
Administration. ERL GLERL-26. Ann Arbor, Michigan.
PP.79.
7. U.S. Army Corps of Engineers. 1968. Provision for
alternate disposal methods for Detroit River, Michigan
COS, Detroit District.
8. Kauss, P.B., and Y.S. Hamdy, 1985. Biological monitoring
of organochlorine contaminants in the St. Clair and
Detroit Rivers using introduced clams, Elliptic
complanatus. J. Great Lake Res. 11:247-263.
9. Thornley, S. 1985. Macrozoobenthos of the Detroit and
St. Clair Rivers with comparisons to neighboring waters.
J. Great Lakes Res. 11:290-296.
10. Chau, Y.K., R.J. Maguire, P.T.S. Wong, andM.E.
Sanderson, (eds.). 1985a. Detroit River - St. Clair River
Special Issue. J. Great Lakes Research 11:191-418.
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11. Chau, Y.K., P.T.S, Wong, G.A. Bengert, J.L. Dunn, and B.
Glen. 1985b. Occurrence of alkyl lead compounds in the
Detroit and St. Clair Rivers. J. Great Lakes Res.
11:313-319.
12. Oliver, E.G., and R.A. Bourbonniere, 1985. Chlorinated
contaminants in surficial sediments of Lake Huron, St.
Clair and Erie: Implications regarding sources along the
St. Clair and Detroit Rivers. J. Great Lakes Res.
11:366-372.
13. United States Environmental Protection Agency and
Environment Canada, 19S7. The Great Lakes - An
environmental atlas and resource book. EPA-9G5/9-87-QQ2,
GLNPO No. 2. pp.44 with attachments.
14. Jaworski, E. , and C.N. Raphael. 1978. Pish, wildlife,
and recreational values of Michigan's coastal wetlands.
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pp. 209.
15. Raphael, C.N. , and E, Jaworski. 1982. The St. Clair
River Delta, a unique lake delta. Geograph. Bull.
21(2) :7-28.
16. Bricker, K.S., F.J. Bricker, and J.E. Gannon. 1976.
Distribution and abundance of zooplankton in the U.S.
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17. Munawar, M. 1988. Report to UGLCCS Biota Workgroup (see
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18. Watson and Carpenter. 1974. Cited by Edsall et al, ,
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20. Hudson, P.L., B.M. Davis, S.J. Nichols, and C.M. Tomcko.
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21. Schloessar, D.W. , and B.A. Manny, 1982. Distribution and
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22, Schloesser, D.W. 1986. A field guide to valuable
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24. Dawson, S.A. 1975. Waterfowl food production and
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characteristics; The St. Clair Flats, Michigan. M.S.
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26. Lyon, J.G. 1979b, Remote sensing analysis of coastal
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27. Hatcher, C.O., and R.T. Nester, 1983. Distribution and
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28. Goodyear, C.D., T.A. Edsall, D.M.O. Dempsey, G.D. Moss,
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29. Hamilton, J.G. 1987. Survey of critical habitat within
International Joint Commission designated areas of con-
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30, Rodgers, P.W., M.S. Kieser, and G.W. Peterson. 1985.
Summary of the existing status of the Upper Great Lakes
Connecting Channels data. Limno-Tech, Inc., Ann Arbor,
Michigan, pp.156 plus appendices.
31. Haas, R.C.. M.G. Galbraith, andW.C, Bryant. 1983. Move-
ment and harvest of fish in Lake St. Clair, St. Clair
River, and Detroit River. 1983 Annual Report, Winter
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32. Eichenlaub, V.L. 1979. Weather and climate of the Great
Lakes region. University of Notre Press, South Bend,
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328
33. Sanderson, M. 1980. The climate 'of the Essex region -
Canada's southland. Dept, of Geography, University of
Windsor, Windsor, Ontario, pp.105,
34. International Joint Commission. 1946. Pollution of the
St. Clair River, Lake St. Clair, Detroit River and St.
Marys River. Document No. 54-R.
35. Water Resources Branch, Ontario Ministry of the
Environment. 1977. Mercury content of sediments in the
" St. Clair River - Lake St. Clair system. Unpublished
report.
36. Environment Canada and Ontario Ministry of the
Environment. 1986. St. Clair River pollution
investigation (Sarnia area).
37. Chan, C.H,, Y.L. Lau, and B.C. Oliver. 1986. Measured and
modeled chlorinated contaminant distribution in St. Clair
River water. Water Poll. Res. J. Canada. 21:332-343.
38. Kauss, P.B., and Y. Hamdy, 1987. PAH Concentrations in
caged clams from st. Clair and Detroit Rivers, 1984.
OMOE Report in preparation.
39. Prank, A.P., P.P. Landrum, and B.J. Eadle. 1986.
Polycyclic aromatic hydrocarbon rates of uptake,
depuration., and biotransformation by Stylodrilus
Heringianus of Lake Michigan. Chemosphere 15:317-330.
40. Oliver, B.G. 1987. Partitioning relationships for
chlorinated organics between water and particulates in
the St. Clair, Detroit and Niagara Rivers. In: QSAR in
Environmental Toxicology II. K.L.3. Kaiser (Ed). D.
Reidel Publishing Co., Dordrecht, Holland.
41. Johnson, G.D., and P.B. Kauss. 1987. Estimated
contaminant loadings in the St. Clair and Detroit Rivers,
1984. Ontario Ministry of the Environment Report ISBN
0^7729-3264-6, Toronto.
42. Oliver, B.G., and K.L.E. Kaiser. 1986. Chlorinated
organics in nearshore waters and tributaries of the St.
Clair River. Water Poll. Res. J. Canada. 21:344-350.
43. Winner, J.M., A.J. Oud, and R.G. Ferguson. 1970.
Plankton productivity studies in Lake St. Clair, Proc.
13th Conf, Great Lakes Res., Int. Assoc. Great Lakes Res,
pp. 640-650.
44. Haas, R.C., W.C. Bryant, K.D. Smith, and A.J. Nuhfer.
1985. Movement and harvest of fish in Lake St. Clair, St.
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Clair River, and Detroit River. U.S. Army Corps of
Engineers, Detroit, Michigan, pp.141.
45. Ontario Ministry of the Environment. 1977. Great Lakes
water quality data summary, St. Clair River, 1976. Great
Lakes Survey Unit, Toronto, pp.57.
46. Ontario Ministry of the Environment. 19*79. St. Clair
River organics study; Biological surveys 1968 and 1977,
Water Resources Assessment Unit, Technical Support
Section, Southwest Region, pp.90.
47, Hlltunen, J.K. 1980, Composition, distribution, and
density of benthos in the lower St. Clair River,
1976-1977. U.S. Fish and Wildlife Service, Great Lakes
Fish. Lab., Ann Arbor, Mich., Aotm, Report 80-4. pp.27,
48. Hiltunen, J.K., and B.A. Manny, 1982. Distribution and
abundance of macrozoobenthos in the Detroit. River and
Lake St. Clair, 1977, U.S. Fish and Wildlife Service,
Great Lakes Fish. Lab., Ann Arbor, Mich. Adm, Report
80-2. pp.87.
49. Griffiths, R.W. 1917. Environmental quality assessment
of the St. Clair River in 1985 as reflected by the
distribution of benthic invertebrate communities.
Aquatic Ecostudies, Ltd., Kitchener, Ontario, pp.51.
50, Persaud, D,» T.D, Lamas, and A, Hayton, 1987, The
in-place pollutants program. Vol. III. Phase I studies,
Ontario Ministry of the Environment Report. October
1987, Toronto, Ontario,
51. Hamdy, Y., B. Hawkins, M. Jackson, G, Johnson, W.
Schneider, S. Thornley. 1987. Preliminary report
St. Clair River MISA pilot-site investigation. Vol. 1:
Part 1. Ontario Ministry of the Environment, Toronto,
52. Pugsley, C.W., P.D.N. Hebert, G.W. Wood, G. Brotea,
T.W. Obal. 1985. Distribution of contaminants in clams
and sediments from the Huron - Erie corridor, I - PCBs
and octachlorostyrene. J. Great Lakes Res. 11:275-289.
53, Suns, K., G. Crawford, and D. Russell. 1985.
Organochlorine and mercury residues in young-of-the-year
spottail shiners from the Detroit River, Lake St. Clair
and Lake Erie. J. Great Lakes Res, 11:347-352,
54, The Great Lakes Institute, University of Windsor, 1987.
Organochlorinated compounds in duck and muskrat
populations of Walpole Island, Report prepared for
Walpole Island Band Council, pp.31.
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55. Weseloh, D.V., and J. Struger. 1987, Contaminants in
wildlife in the Upper Great Lakes Connecting Channels.
UGLCC Study Report. Canadian Wildlife Service,
Burlington, Ontario Typescript, pp.9.
56, Smith, V. E., Spurr, J.M., Pilkins, J.C., Jones, J.J«
1985. Organochlorine Contaminants of Wintering Ducks
Foraging on Detroit River Sediments. Journal of Great
Lakes Research, 11:231-246.
57. Ministry of the Environment/Ministry of Natural
Resources. 1987, Guide to eating Ontario sport fish.
58, Rukavina, N.A. 1986. Bottom sediments and morphology of
the upper St. Clair River. Water Poll. Res. J. Canada.
21:295-302.
59. Mudroch, A., and K. Hill. 1988. Distribution of mercury
in Lake St. Clair the St. Clair River sediments. J.
Great Lakes Res. In press.
60. Ontario Ministry of the Environment. 1987. Data report
on the 1985 St. Clair River bottom sediment survey.
61. Oliver, B.C., and C.w, Pugsley. 1986. Chlorinated
contaminants in St. Clair River sediments. Water Poll,
Res. J. Canada. 21: 368-37i.
62, Bertram, P., T.A, Idsall, B.A. Manny, S.J. Nichols, and
D.W. Schloesser, 1987, Physical and chemical
characteristics of sediments in the Upper Great Lakes
Connecting Channels, 1985. J. Great Lakes Res,
(Submitted.)
63. Lawrence, J. {ed.}, 1986, it, Clair River pollution,
Special Issue. Water Poll. Res. J. Canada. 21s283-459,
64, Oliver, B.C. 1987, St. Clair River sediments. Level II
report for the Upper Great Lakes Connecting Channels
Study,
65, Point Source Workgroup, 1981. Geographic area report.
St. Clair River. Typescript.
66. Canviro Consultants. 1987, Sampling analysis of
refinery effluents to assess variations in trace
contaminant concentrations. Report pp 46, ISBN
0-7729-2786-3.
67. Carey, J.H,, J.H. Hart, and N.A. Rukavina, 1987,
Occurrence of diphenyl ether and biphenyl in the St.
Clair River, sediment contamination by heat transfer
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fluids. Environ, Sci. Technol. (submitted.)
68. Ontario Ministry of the Environment. 1987. Data report
on 1984- 1985 tributary study.
69. Pranckevicius, P.E. 1987. Upper Great Lakes Connecting
Channels tributary sediments (a preliminary data report).
U.S. Environmental Protection Agency. Great Lakes
National Program Office, Chicago.
70. Edwards, C.J., P.L. Hudson, W.G. Duffy, S.J. Nepszy, C.D.
McNabb, R.C. Haas, C.R. Listen, B. Manny, and W.D. Busch.
1988. Hydrological, morphemetrical, and biological
characteristics of the connecting rivers of the
international Great Lakes: A review. Can. J. Aquat. Sci.
In press.
71. Tuchman, M.L. 1982. Effects of conservative ions on
algal assemblages. Doctoral dissertation. The
University of Michigan, School of Natural Resources.
72. Sdwardson, D.C. 1988. Ontario Ministry of the
Environment, Sarnia Office, private* Communication.
73. Kaiser, K.L.S., and M.E. Comba, 1986. Volatile
hydrocarbon contaminant survey of the St. Clair River.
Water Poll. Res. J. Canada. 21:323-331.
74. Comba, M.S., and K.L.E. Kaiser. 1987. Benzene and
toluene levels in the upper St. Clair River. Water Poll.
Res. J. Canada, 22: 468-473.
75. Oliver, B.G., and A.J. Niimi. 1983. Bioconcentration of
chlorobenzenes from water by rainbow trout: Correlations
with partition coefficients and environmental residues.
Environ. Sci. Technol. 17:287-291.
76. Thomas, R.L., and A. Mudroch. 1979. Small craft harbours
- sediment survey Lakes Ontario, Erie and Lake St. Clair,
1978. Report to Small Craft Harbours Ontario Region.
77. Oliver, B.C., and K.D. Nicol, 1988. Analysis of
polychlorinated biphenyls (PCBs) in St. Clair River sedi-
ments by capillary GC/SCD and GC/MS: Determination of
potential SCD interferences. Report to Ontario Ministry
of the Environment by ELI ECO Laboratories, Inc.
Typescript, pp.17.
78. Dochstader, J.M. 1984. Remedial measures for the control
of industrial discharges to the St. Clair River.
presented at 27th Conference on Great Lakes Research, St.
Catherines, Ontario (May, 1984) .
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79. Chan, C.H., and J. Kohli. 1986. A report on the St.
Clair River trace contaminants survey 1985. Water
Quality Branch, Ontario Region, Burlington.
80, Derecki, J.A. 1985. Effect of channel changes in the St.
Clair River during the present century. J. Great Lakes
Res. 11:201- 207,
81. Michigan Department of Natural Resources. Undated. Un-
titled. Study report related to stormwater discharges.
Typescript. Unpaginated.
82. Marsalek, J. , and H.Y.F. Ng. 1987. Contaminants in urban
runoff in the Upper Great Lakes Connecting Channels area.
Environment Canada, National Water Research Institute.
NWRI #87-112. pp.54 plus appendices.
83. U.S. Army Corps of Engineers, 1977. Urban stormwater
runoff: STORM generalized computer program 723-58-L 2520.
Davis, California.
84. Wall, G.J., E.A. Pringle, and W.T. Dickinson. 1987a.
Nonpoint Source Workgroup agricultural sources of
pollution, St. Clair River Land Resource Research centre,
Guelph, Ontario. Typescript, pp.12 (unpaginated),
85. Wall, G.J., E.A. Pringle, and W.T, Dickinson. 1987b.
Upper Great Lakes Connecting Channels Study. Nonpoint
Source Workgroup agricultural pollution sources, St.
Clair River — Canada. Land Resource Research Centre,
Research Branch, Agriculture Canada, Guelph, Ontario.
pp.27 plus appendices.
86. McCorguodale, J.A., K. Ibrahim, and E.M. Yuen. 1986b.
Final report on transport and fate modeling of
hexachlorobenzene (HCB) in the St. Clair River to the
Ontario Ministry of the Environment, The Industrial
Research Institute of the University of Windsor.
Typescript, pp. 46.
87. International Joint Commission. 1987. Summary report of
the workshop on Great Lakes atmospheric deposition.
Windsor, Ontario, pp.41.
88. Nonpoint Source Workgroup. 1988. Upper Great Lakes Con-
necting Channel Study. Waste disposal sites and poten-
tial groundwater contamination, St. Clair River, pp.72.
89. United States Environmental Protection Agency. 1985. A
standardized system for evaluating groundwater pollution
potential using hydrogeologic settings. Cooperative
agreement CR- 810715-01, U.S.EPA and Natural Water Well
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333
Association, pp.163.
90. Intera Technologies Ltd. 1989. Hydrogeologic study of
the fresh water aquifer and deep geologic formations
Sarnia, Ontario. Kept to OMOE, Detroit/St. clair/St,
Marys Rivers Proj., Sarnia, Ont., 3 vol.
91. Nettleton, P., and Y.S. Hamdy. 1988. St. Clair River
spill manual. Water Resources Branch, Ontario Ministry of
the Environment. ISBN-Q-7729-2670-Q.
92. Hamdy, Y.S. and J.D. Kinkead. 1979. Waste dispersion in
the St. Clair River. Ontario Ministry of the
Environment, Water Resources Branch, Great Lakes Unit,
Typescript, pp.27.
93. Akhtar, W. and G.P. Mathur. 1974. Models for dispersion
of soluable wastes in the St. Clair River. Fourth Annual
Environmental Engineering and Science Conference,
Louisville, Kentucky.
94. McCorquodale, J.A. and J.K. Bewtra. 1982a, Users guide
to computer programme for the convection - dispersion and
decay of a vertically mixed pollutant with multiple out-
falls. In: Simulation of Phenol concentrations in the
St, Clair River. A report to the Ontario Ministry of the
Environment. The Industrial Research Institute of the
University of Windsor, pp. 8- 15.
95. McCorquodale, J.A., and J.K. Bewtra. 1982b. Simulation
of phenol concentrations in the St. Clair River. A
report to the Water Resources Branch of the Ontario Mini-
stry of the Environment; Toronto Ontario. The Industrial
Research Institute of the University of Windsor.
Typescript, pp. 1-7.
96. Nettleton, P. 1988. St. Clair River modeling and mass
balance considerations. Great Lakes Section; Water
Resources Branch; Ontario Ministry of Environment.
Typescript. Unpaginated.
97. Ambrose, R.B., S.I. Hill, and L.A. Mulkey. 1983. Users
manual for the chemical transport and fate model
TOXIWASP. U.S.EPA., ORD, Environmental Research
Laboratory, Athens, Georgia.
98. Derecki, J.A., L.L. Makuch, J.R. Brook, 1988. Unsteady
flow model of entire St. Clair River. Typescript.
Unpaginated.
99, Muldoon, P., and M. Valiante. 1988. Zero Discharge. A
strategy for the regulation of toxic substances in the
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Great Lakes ecosystem. Canadian Environmental Law
Research Foundation Report, pp. 79.
100. Ontario Ministry of the Environment and Environment
Canada. 1988. Implementation of recommendations of the
1986 St. Clair River pollution investigation report.
Report pp. 30 ISBN 0- 7729-3531-9.
101. Canadian Council of Resource and Environment Ministers.
1987, Canadian water quality guidelines. Water Quality
Branch, Environment Canada, Ottawa, Canada.
102. World Health Organization. 1984. Guidelines for drinking
water quality: Vol.1, Recommendations. Geneva.
103. Oliver, E.G., and A.J. Niimi. 1985. Bioconeentration
factors of some halogenated organics for rainbow trout:
Limitations in their use for prediction of environmental
residues. Environ. Sci. Techno!. 19:842-849.
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CHAPTER VIII
LAKE ST. GLAIR
A. STATUS OP THE ECOSYSTEM
1, Ecological Profile
Watershed Characteristics
The St, Clair system including the St. Clair River and Lake St.
Clair is a significant waterway economically, biologically and
physically. Together with the Detroit River, the system forms
the connecting channel between Lake Huron and Lake Erie,
Located on the international boundary between the United States
and. Canada, Lake St. Clair borders Lambton, Kent and Essex
counties in Ontario, and Macomb and Wayne counties in Michigan.
It has a shoreline length of approximately 272 km plus the delta
shoreline area. It possesses a maximum natural depth of 6,5 m, a
maximum length of 43 km, a width of 40 km and an area of about
1,115 km^. in Ontario, wetlands and agriculture dominate the
shoreline, while in Michigan the entire shoreline is highly
urbanized. Because of its modest depth, the lake has no commer-
cial harbors. To accommodate heavy commercial marine traffic,
however, a navigation channel has been dredged to a depth of 8.3
m running in a northeast-southwest direction between the St.
Clair cutoff in the St. Clair River Delta and the head of the
Detroit River (Figure 11-4}.
The eastern shoreline of the lake is low lying and characterized
by agricultural and recreational land uses. Low barrier islands
less than 170 m in width and probably not more than 1 m above
lake level parallel the shoreline and are colonized by marsh
vegetation. The wetland zone, which is approximately 1 km wide,
extended farther inland (east) in the past. Approximately 40% of
the low plain has been ditched and drained since 1916. The
coastal barriers provide a line of defense from wave attack to
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336
the lagoon and wetland zone. The annual net erosion rates on the
south shore of Lake St. Clair are in excess of 2 m/yr (1). How-
ever, other coastal reaches on the south shore are actually
accreting at rates of up to 0.4 m/yr.
On the western shore, permanent residential homes occupy about 30
km o£ lake shoreline, with industrial and commercial uses occupy-
ing only 2 km of shoreline. Most of the shoreline is in private
ownership, but 12 km is publicly owned and dedicated to recrea-
tion and wildlife preserves.
Despite the various intensive and conflicting land and water uses
to which the St. Clair system is subjected, the system continues
to provide recreation to many Americans and Canadians, Typically
more walleye, bass, muskellunge and centrarchid panfish are taken
from Lake St. Clair each year than from any of the Great Lakes or
other Great Lakes connecting channels. These anglers boaters
are served by more than 140 commercial, municipal and private
marinas in Michigan and Ontario.
The physics of Lake St. Clair is Important in determining the
distribution and fate of contaminants and other substances in the
sediment and water column. The St. Clair River contributes 98%
of the water to the Lake St. Clair basin, with the remaining 2%
being contributed by other lake tributaries, including the Clin-
ton, Thames and Sydenhaii Rivers. The average discharge of the
St. Clair River from 1900 through 1981 was 5,200 m3/s with a
range from 3,000 m3/s to 6,700 ni3/s. Outflow from the lake,
which is through the Detroit River to Lake Erie, is only about 3%
greater than the inflow from the St. Clair River. Average flush-
ing times for the St. Clair River, Lake St. Clair the Detroit
River are 21 hours, 5-7 days and 19 hours respectively (2).
Plows in the system are controlled principally by the inflows
from Lake Huron and the outflows to Lake Erie, which in turn
depend largely on the difference in water levels between these
two lakes. Fluctuations of water levels and flows do occur at
the head and mouth of both the St. Clair and Detroit Rivers in
response to seasonally fluctuating water levels in the upstream
and downstream lakes as well as wind set-ups on each of the lakes
during periods of high winds and storms. Ice jams are a common
occurrence on the St. Clair River and often reduce the river
flow, thereby both raising the level of Lake Huron and lowering
the level of Lake St. Clair. For example, in 1984 an ice 3am
reduced the monthly average flow to about 2,520 m3/s, which
caused a drop of 0,4 m in lake level.
Lake St. Clair has an established elevation of 174.65 m above
level, but the average lake level from 1900 through 1983 was
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337
174.87 m. The lake had a maximum elevation of 175.64 m, and a
minimum elevation of 173.71 m.
The St. Clair River empties into Lake St. Clair through a large
delta consisting of three main channels in the upper delta (North
Channel, South channel and Chenal Ecarte) and a number of secon-
dary channels in the lower delta. The delta area, commonly
referred to as the St. Clair Flats, extends 18 km from the open
waters of Lake St. Clair towards the St. Clair River. Channel
depths are extremely variable, but the three active distribu-
taries average 500 m wide and 11 m deep. At the mouths of the
channels, depths decrease abruptly due to river mouth bars 2 to
4 m below mean lake level. The North Channel, the South Channel
and the Chenal Ecarte contribute 53%, 42% and 5% of the river
flow to Lake St. Clair respectively (3).
Wind forces largely determine the water mass distribution and
circulation patterns in the lake. In general, the main surface
movement to the lake's outflow in the Detroit River appears to be
along the south shore for southwest to north winds, and along the
west shore of the lake for northeast to south winds. Two dis-
tinct water masses have been identified: a northwestern mass
consisting primarily of Lake Huron water flowing from the main
channels of the St, Clair River, and a southwestern mass of more
stable water enriched by nutrient loadings from Ontario tribu-
taries and shoreline development. The margins of the masses may
shift according to wind direction and speed, but the overall
discreteness of the distributions is maintained.
Habitats and Biological Communities
The St. Clair system contains one of the largest coastal wetlands
in the Great Lakes. Topographic maps and navigation charts indi-
cate there are 13,230 ha in Lake St. Clair and the St. Clair
Delta. The wetlands include the following major types:
1. Open water wetlands have variable water depths and thus
support submersed plants in deeper waters and emergent
aquatic macrophytes in more shallow water. They commonly
occur in interdistributary bays and shallower waters along
the perimeter of Lake St. Clair.
2. River channel wetlands are composed largely of submersed
species but occasionally emergent macrophytes occur on point
bars.
3. Beach and shoreline wetlands are represented by a mix of
species.
4. Cattail marsh wetlands colonize broad zones located at
the lower St. Clair Delta and at the mouth of the Clinton
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338
River, Stands of hybrid cattails (Typha x glauca) are
associated with clayey and organic sediments. Shallow open-
ings are colonized by floating and submersed species.
5. Sedge marsh wetlands are mainly composed of tussocks of
sedges,
6. Abandoned river channel wetlands support emergent and
submersed aquatics.
7. Wet meadow wetlands contain low, woody plants inter-
spersed with grasses.
8. Shrub wetlands are dominated by mixed shrubs, water tole-
rant trees, and understory plants typical of wet meadows.
In general, all wetland types occur in the St. Clair Delta area,
A sedge marsh wetland dominates the shallow regions. Where water
depths exceed 0.3 m the sedges are replaced by cattail marsh,
which is extensive, especially in Ontario, In deeper water, the
cattail marsh gives way to open water wetlands dominated by the
hardstem bulrush. This zone of emergents is less dense lakeward,
where submersed macrophytes occur in bays at low density. The
size, location and structure of the wetland plant communities
shift in response to the periodic changes in water levels of Lake
St. Clair.
Benthic macroinvertebrates also exhibit spatial zones within Lake
St. Clair, In one recent study of benthic invertebrates and
sediment chemistry, six community assemblages were identified.
Two communities were associated with the periphery of the lake
and in Anchor Bay, three communities were found in the deeper
waters, 2 to 7.5 m deep, and one grouping was found in the lower
reaches of the St, Clair River and Thames River.
Local Ecological Relationships
i) Nutrient Cycling
Lake St Clair is a highly productive north-temperate lake. The
distribution of nutrients and chlorophyll within the lake are
influenced primarily by lake currents and the flow of Lake Huron
water through the delta system. Concentrations of chemical vari-
ables and chlorophyll tend to increase across the lake from
northwest to southeast. Because of nutrient inputs from agricul-
tural drainage, sewage discharge and greater stability in water
mass, the southeastern area is more eutrophic than the remainder
of the Ontario section of the lake. The northwestern water mass
consists primary of Lake Huron water flowing from the main chan-
nels of the St. Clair River. The southeastern water mass con-
sists of more stable water enriched by nutrient loadings from
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339
Ontario tributaries, and can be considered to be mesotrophie,
bordering on eutrophic.
Thermal and chemical stratification do not occur and oxygen con-
centrations remain near 100% saturation throughout the lake.
Moderate alkalinity, low specific conductance and low pH vari-
ability indicate Lake St. Clair is a well-buffered, hard water
lake. The input of high quality water from Lake Huron, through
the St. Clair River, maintains the water quality and the biota in
the open waters of Lake St. Clair similar to conditions in south-
ern Lake Huron.
iij Food
The primary producers in the St. Clair system are phytoplankton
and iiacrophytes. At least 71 species of phytoplankton and 21
taxa of submersed macrophyte have been identified from the St.
Clair system. According to Edwards et al., (2) about 215,330
tonnes of plant biomass are produced in the St. Clair system each
year, of which about 25% and 75% originates in the St. Clair
River and in Lake St. Clair respectively. The estimated phyto-
plankton biomass, 96,900 tonnes, represents about half the total
plant biomass produced in the system. Because of the short
flushing time of the system, however, most of the phytoplankton
probably passes into Lake Erie before it is utilized by other
trophic levels. Most of the periphyton and macrophytic biomass
dies back in the fall, over-winters on the bottom, and moves
downstream in spring just after ice break-up. Additional alloc-
thonous organic matter which is added to Lake St. Clair from
municipal sewage treatment plant equals approximately 25% of the
total annual primary production of all vegetation in Lake St.
Clair.
Lake it. Clair relatively low densities of limnetic zooplank-
ton, In general, cladocera (28 species) are present in higher
densities than cyclopoid copepods (5 species), and cyclopoids are
more abundant that calanoid (7 species) or harpacticoid (4 spe-
cies) copepods. The overall low abundance of limnetic zooplank-
ton in Lake St, Clair been attributed to we11-developed
macrophyte and the rapid flushing time of Lake St. Clair.
In excess of 300 taxa of macrozoobenthos have reported from
Lake St. Clair, Oligocheata, Chironomidae, Gastropoda, Ephemer-
optera, Trichoptera and Amphipoda comprise the most significant
biomass of macrozoobenthos. Nymphs of the mayfly Hexagenia may
reach densities up to 3,000 nymphs/m2. Species richness is
greatest among the Chironomidae, Trichoptera and Oligochaeta.
-------
340
iii) Trophic Relationships
Details of the relationships between the flora and fauna in the
St. Clair system, beyond the generalized liinnological interac-
tions commonly thought to occur, have yet to be determined. The
St. Clair River and Lake St. Clair are major sources for sub-
mersed and emergent plants that provide substrate for periphyton
and for invertebrates that are fed upon by fish and waterfowl.
They also provide cover for young fish. As detritus, the plants
serve as food for macrosoobenthos, Poe et al., (4) showed that a
percid-cyprinid-cyprinodontid fish community was dominant in Lake
St. Clair in vegetatively complex areas occupied by many plant
species, and that a less diverse, centrarchid community dominated
in the areas with fewer plant species.
High productivity of benthic macroinvertebrates in Anchor Bay and
around the delta of the St. Clair River in Lake St. Clair is
probably related to the large accumulations of macrophytes in
those areas. The macroinvertebrates are probably not food limit-
ed for at least half the year.
iv) Links to the Great Lakes
The St. Clair system provides important spawning and nursery
habitat for fishes that are permanent residents and for others
from Lake Huron and Lake Erie which enter the system to spawn.
Of the approximately 70 species of fish recorded as residents or
migrants in Lake St. Clair, at least 45 have spawned in the St.
Clair system. Large numbers of lake herring and lake whitefish
from Lake Erie historically migrated into Lake St. Clair to
spawn over the large Chara beds along the western side of the
lake.
Lake sturgeon were also historically abundant and supported a
commercial fishery, but overfishing reduced the population and
now only a limited recreational fishery is permitted. The shal-
low marshes of the St. Clair Flats are the only known nursery
areas for the species in Lake St. Clair.
Walleyes and yellow perch spawn in Anchor Bay of Lake St. Clair,
along the south shore of the lake, in the Clinton, Sydenham and
Thames Rivers, and in the St. Clair delta, stocks that were
depressed from historical levels have rebounded in the past
decade and major spawning runs now occur in the St. Clair system.
Yellow perch populations of southern Lake Huron and the St. Clair
system are closely linked. Many of these fish apparently over-
winter and spawn in Lake St. Clair and the St. Clair delta, and
then spend the rest of the year in the St. Clair River and Lake
Huron.
Smallmouth bass and muskellunge support important recreational
fisheries in Lake St. Clair and have extensive spawning grounds
-------
341
in the lake. Smallmouth bass spawn along the shoreline of the
lake from the Thames River and the southeast edge of the lake,
north into the St. Clair delta, and along the north and west
shorelines of the lake to the head of the Detroit River. Virtu-
ally all of the delta and the shoreline of Anchor Bay are also
nursery areas for smallraouth bass. Muskellunge spawning areas
extend more or less continuously along the shoreline of the lake
across the St. Clair delta, into Anchor Bay, and intermittently
along the west shoreline to the head of the Detroit River.
Marshes of the St. Clair delta are the only recorded muskellunge
nursery areas.
Exotic fish species which now inhabit Lake St. Clair, as well as
the Great Lakes, include the common carp (Cyprinus carpio), the
alewife (Alosa pseudoharengus), the rainbow smelt (Osmerus mor-
dax) and the white perch {Morone__ajnericana) , The carp have re-
cently made up much of the commercial fish catch, and the smelt
plus alewife together are the most abundant fish larvae in the
St. Clair system. The white perch, first captured in Lake St.
Clair in 1977, now provide an important recreational fishery.
The extensive wetlands of Lake St. Clair are also an important
concentration and nesting area for waterfowl. Major concentra-
tion areas extend from the lower St. Clair River to the middle of
Lake St. Clair, The coastal wetlands and shallow waters of Lake
St. Clair make it a critical resting and feeding habitat. Spe-
cies whose primary migration corridor traverse Michigan with a
resting stopover in the vicinity of lake St. Clair include the
American goldeneye, bufflehead, canvasback, hooded merganser,
ruddy duck and Canada goose. Important species of ducks that
nest in the St. Clair area include mallards, blue-winged teal,
black ducks, redheads and wood ducks.
Climate_
The climate of the region is characterized by mild summers and
cold winters. Average annual air temperatures range from a high
of 23.6°C in July to a low of -4.4°C in January. Monthly precip-
itation ranges from a high of 8.10 cm to a low of 3.6 cm. In
winter, temperatures are commonly below Q°C and ice occurs oa
most of the lake. Water temperatures during the summer months
are near 21°C. Precipitation is mainly rain and is evenly dis-
tributed throughout the year.
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342
2. Environmental Conditions
Water Quality
i) Tributaries
Because the St. Clair River provides 98% of the water to Lake St.
Clair, the mass loading of contaminants to the Lake is mainly
from this single input. Additional loadings from other tribu-
taries do occur, however, and local impacts have been observed
due to degraded tributary water quality. In the following dis-
cussions, references to Lake St. Clair tributaries exclude the
St. Clair River.
Tributary water quality data from six tributaries (Thames,
Sydenham, Puce, Belle and Ruscom Rivers in Ontario, and the
Clinton River in Michigan) in 1984 and 1985 indicated the
presence of eight pollutants (PCBs, HCB, OCS, P, Cd, Cl, N and
Pb) that were designated as parameters of concern for the UGLCC
Study. In these streams, P, Cd, Pb and Cl concentrations ranged
from 0.014-0.94, 0.002-0.0022, 0.003-0.58 and 11-349 mg/L respec-
tively (Table Vlll-l). Estimated daily loadings from each river
are presented in Table VTII-2. Expression of loadings on a daily
basis is somewhat artificial, since true loadings from tributar-
ies have been shown to be strongly flow-dependent and seasonal.
However, expression in this manner should facilitate comparison
with other sources of loadings presented in this report.
The organic contaminants, PCBs, HCB and OCS were usually not
found in quantifiable concentrations in unfiltered water samples
(5). PCBs associated with suspended sediments from the Belle,
Sydenham and Thames Rivers were found in concentrations up to
1,560 ng/g, 60 ng/g and 61,190 ng/g respectively. Suspended
sediments were not sampled from the other rivers.
The phosphorus concentration in water from all six tributaries
exceeded the Ontario Provincial Water Quality Objective (PWQQ) of
30 ug/L for rivers in all samples, except for some samples from
the Sydenham River. Estimates of loadings from the tributaries
ranged from 23.5 kg/d from the Puce River to 2,021 kg/d from the
Thames River. All sampled Canadian tributaries together provided
a loading of 3,052 kg/d, while the Clinton River contributed an
additional 340 kg/d (Table VIII-2).
The largest nitrate +• nitrite loadings to Lake St. Clair came
from the Thames River (31,435 kg/d), Sydenham River (4,542 kg/d)
and Clinton River (2,186 kg/d).
Concentrations of chlorides in unfiltered water ranged from 11
mg/L in the Sydenham River to 349 mg/L in the Clinton River. The
Clinton River concentrations exceeded the 250 mg/L concentration
set as the U.S.EPA Secondary Maximum Contaminant Level for aes-
-------
TABLE VIII-!
Comparison of Canadian and U.S. tributary pollutant concentrations and loads for the study area 11984-19851,
Canadian Tributaries* U.S. Tributary1'
Combined Drainage Areas (hai
Percent of Study area
Parameter
1 u n i t s 1
PCBs ng/L
HCB "
ncs "
P mS/L
N "
a "
Ph "
Cd "
atrazine ng/L
alachlor "
die to 1 ach 1 or "
cy anaz i ne '*
Oanadi an
Tri butarieS
Monitored
T.S.B.K
T,S,B
T,S,B
T , S , B , R , P , K
T,S,B,R,P
T , S,B, R,P,K
T,S,B,K
T,S,B,K
T
T
T
T
567,310<=
47
Onneentrat ions
Wate r
^<^LD
0.32 " b
0.4? " "
Suspended
SedtBent
im/i)
X
X
X
X 0
X
X
X
X 0
X
X
X
X
Average
Loads
{annual 1 .
X
X
X
.653kg/h.
4.1 "
360.5 kg/ha
0 . 03
.0016 "
0.28 g/h*
0.08 "
0.01 "
0.048 "
NOTE:
NS
Six Canadian tributaries include the Thanes IT}] Sydenhauil S I , Belle (B), RusconlHI, Puce (P) and Pike (K! Rivera
U.S. tributary ia Clinton Kiver
Excluding Pike Creek
U.S. pesticide data for the period April 15 to August 15, 19M5 only
Average Sydenham and Thames Rivers only
Concentrations exceeded water quality standards
Concentrations exceeded one or more proposed water quality standards for drinking water
Time weight mean concentrations
No data available
Less than quantitative limits of detection
1 riant t i c 1 till duLn for loud calculations
-------
TABLE VI11-2
U.S. and Canadian tributary loading of UGLCCS parameters into Lake St. Glair (kg/d).
TrlbutanY
Belle River (Canada)
Puce River (Canada)
Ruscon River (Canada!
Sydenham River (Canada!
Thames River (Canada)
Clinton River (U.S.)
NO3-N
516
282
647
4542
31,463
2186
Cadmium Chlorides Lead
600?
4535
4984
0.696 50,483 11.2
1.82 180,318 123.1
0.83 187,661 li.6
phosphorus
fl
23
43
893
2021
340
Note;
Values are presented here in rounded form and may differ from that in
the text. Loadings for other U.S. tributaries mentioned in the text
were not calculated
U)
-------
345
thetic effects, the Health and Welfare Canada Maximum Acceptable
Concentration, and the Ontario Maximum and Maximum Desirable
Concentration for aesthetics. The greatest loadings were provid-
ed by the Thames River (190,318 kg/d), Clinton River (182,661
kg/d) and Sydenham River (50,483 kg/d).
The range of cadmium concentrations in unf iltered water were 0 . 2-
0.4 ug/L in the Belle River, 0.2-0,7 ug/L in the Sydenham and
Thames Rivers, and 0.1-2.2 ug/L in the Clinton River. These
concentrations were generally greater than the Great Lakes Water
Quality Agreement (GLWQA) specific objective and PVQQ of 0,2
ug/L, and some were greater than the chronic AWQC of 1.1 ug/L
(assuming water hardness of 100 mg/L) . Estimated loadings from
the Clinton, Thames and Sydenham Rivers were .83 kg/d, 1.82 kg/d
and 0.696 kg/d respectively.
The Belle, Sydenham and Thames Rivers all contained concentra-
tions of lead in some samples that exceeded the chronic AWQC of
3.2 ug/L (assuming a hardness of 100 mg/L-). The Thames River
contained concentrations which also exceeded the acute AWQC of 82
ug/L, as well as the GLWQA specific objective and PWQO of 25
ug/L. Major loadings of lead were provided by the Thames River
{123.1 kg/d), Clinton River (15.6 kg/d) and Sydenham River (11.2
The pesticides atrazine, cyanazine, metolachlor and alachlor were
detected in Thames River water samples between 1981 and 1985 with
a frequency of occurrence of 99%, 16%, 7% and 4% respectively at
concentrations from less than detection limits to 3.0, 5.0, 8.0,
and 3.0 ug/L respectively (Table VIII-1) . In the Clinton River
in 1985, the pesticides as ordered above were observed with fre-
quencies of 95%, 73%, 2.7% and 21.6% respectively at concentra-
tions from less than detection limits to 1.9, 0.2, 0.2 and 0.9
ug/L respectively.
Some U.S. agencies have proposed drinking water standards for the
four pesticides discussed above. None of the measured concen-
trations of the pesticides in either of the rivers exceeded the
proposed standards, except for the State of Wisconsin standard
for alachlor (0.5 ug/L).
ii) Open Lake St. Clair Water
Water temperature in Lake St. Clair is determined in part by the
shallow depth and short hydraulic retention time of the water.
Highest temperatures are reached in August, and average about
22.5°C. Temperatures may be 2 to 4°C lower in Anchor Bay because
of the greater inflow from the St. Clair River, and they may be 5
to 6°C higher in the coastal wetlands. The lake is too shallow
to stratify thermally, and dissolved oxygen concentrations are
usually at saturation.
-------
346
In general, surface water temperatures at the outflow of Lake St.
Glair exceed the upper limit (19°C) of the range selected for
residence by adult rainbow trout from about late June through
mid-September, and they exceeded the upper limit of the range
(17°C) selected for residence by juvenile lake whitefish in Lake
Huron from about mid-June through late September. Thus, Lake St,
Clair may provide optimum thermal habitat for indigenous Great
Lakes cold water fishes only during the cooler months of the
year. Anchor Bay may contain suitable thermal habitat for cold-
water fishes for a slightly greater portion of the year than the
rest of the lake.
Because of the large contribution of water from the St. Clair
River into Lake St. Clair and the relatively short residence time
of water in the lake (5 to 7 days), the water quality of Lake St,
Clair largely reflects that of the St, Clair River.
Concentrations of contaminants within the water may be inferred
by comparing those in the incoming water with those in water at
the head of the Detroit River. Studies of water from the St.
Clair and the Detroit Rivers were conducted in 1935, with samples
analyzed for a number of chemical parameters, including organo-
chlorine pesticides (OCs), PCBs, and a variety of other chemicals
of industrial origin including chlorobenzenes (CBs), hexachloro-
butadiene (HCBD), hexachloroethane (HCE) and octachlorostyrene
(OCS). Details of the analytical procedures were provided by
Chan et al., (6).
Organochlorine Pesticides and PCBs:
Concentrations of total PCBs in unfiltered water at the head of
the Detroit River averaged 0.0014 ug/L from two surveys. This
concentration was slightly above the Ontario Provincial Water
Quality Objective (PWQO) of 0.001 ug/L. The difference in con-
centration of PCBs between the mouth of the St. Clair River and
the head of the Detroit River was not significant, i.e., less
than detectable and 0.0014 ug/L in two surveys of the St. Clair
River, 0.00139 ug/L and 0,00144 ug/L in two surveys of the
Detroit River. Because the concentrations of other organic com-
pounds (HCBD, HCB, OCS and HCE) were lower at the Detroit River
than at the mouth of the St. Clair River (7), however, a source
of PCBs may exist within the Lake St. Clair basin. At the head
of the Detroit River, the concentration of PCBs was greater on
the U.S. side than on the Canadian side, suggesting that a source
of PCBs may exist on the western shore of Lake St. Clair.
Concentrations for the organochlorine pesticides in the dissolved
phase were in the low ng/L range or less along the St. Clair
River, while there were some seasonal variations noted, no
marked spatial variation was observed, either downstream or
cross-river. Because concentrations were also similar at the
head of the Detroit River, an argument similar to that for PCBs
-------
347
above can be made for the possible existence of a source for
these pesticides in the Lake St. Clair basin.
Chlorobenzenes, Octachlorostyrene:
In contrast to the behaviour of the pesticides and PCBs noted
above, increases in the concentration of HCBD, HCB, and OCS indi-
cate significant sources of inputs of these industrial compounds
to the St. Clair River, but the plume of contaminants remains
close to the Canadian shore and does not disperse uniformly
across the river. In the upper delta, concentrations were high-
est in the Channel Ecarte, which receives Canadian nearshore
water. Because this stream contributes only 5% of the total
river flow to Lake St. Clair, however, the major loading of these
substances to the lake would come from the South Channel.
Diminished, but measurable concentrations of these chemicals in
the dissolved phase were observed at the head of the Detroit
River in 1985, showing that some contaminant carryover from the
St. Clair River occurred, but also that some significant loss
processes occurred within the lake. Similar findings were re-
ported for a survey conducted in 1984 (8). For example, loss
processes in Lake St. Clair may account for up to 95% reductions
in HCB and OCS between the St. Clair and Detroit Rivers (8).
Phosphorus, Chlorides and Metals;
Concentrations of total phosphorus, chlorides and metals in whole
water and suspended solids from the mouth of the St. Clair River
and the head of the Detroit River in 1984 are presented in Table
VIII-3. All measured concentrations in water were below the
relevant surface water standards or guidelines except for some
observations of excessive iron in the Detroit River. Similarly,
the mean concentrations of the following parameters that were
measured at the head of the Detroit River, in 1985 were below all
relevant criteria, objectives or guidelines: total phosphorus,
8.6 ug/L; cadmium, 0.023 ug/L; zinc, 1.217 ug/L; mercury, 0.008
ug/L; copper, 1.29 ug/L; and nickel 0.966 ug/L. A significant
increase (71%) in phosphorus concentration in both whole water
and suspended sediments was observed between the mouth of the St.
Clair River and the head of the Detroit River, thereby indicating
that Lake St. Clair and/or its basin are a net source for
phosphorus.
The metals and chloride exhibited variable responses across Lake
St Clair in 1984. The concentration of total iron in both whole
water and in suspended solids was greater at the head of the
Detroit River than at the mouth of the St. Clair River, while
that of zinc was greater only associated with suspended solids.
Lead and mercury concentrations tended to be greater in the
Detroit River than in the St. Clair River, but cross channel
differences were detected. Chloride concentrations were not
observed to be different in the two river reaches.
-------
348
TABLE VIII-3
Concentrations of total phosphorus, chlorides and metals in whole water and
suspended solids from the mouth of the St. Clair River and the head of the
Detroit River, 1384, range and (mean)a,
Whole Water
Fe Pb Hg Zn TP Chloride
Location mg/L ug/L ug/L ug/L ug/L mg/L
St. Clair River
North Channel 0.054-0.220 <3 <0.01 0.5-3.0 6-12 5.77- 6.82
(0,130) (1.5) 18,8) (6.30)
South Channel 0.063-0.170 <3 <0,01 0.5-5,0 7-10 7,82-10.94
(0.0851* (2.4) (8.5! (9.06!
Detroi_t__Eiver
West side 0.088-0.380 <3 <0,0l 0.3-3.0 9-21 7.09-12.45
U4.0) J9.Q)
East side 0.130-0.920 <3 <0.01 0.5-1.0 12-20 7.34-11.93
(15,5 )* (9.1!
Suspended Solida
Fe Pb Hg Zn TP Sus.Solids
mg/g ug/g ug/g ug/g mg/g Eg/L
St. Clair River ~"'
North Channel 16-22 10-26 0.03-0.14 74-86 0,5-1.0 5,6-12.7
(19.0) (20.5) (0.09! (81.0) (0.8) {8.3J*
South Channel 14-18 25-49 0.16-0,35 70-110 0.8-1.0 5.6-11.1
(16) (40! {0.27} (81,5) (0.8S (7.1)
Detroit River
West aide 21-31 39-62 0.06-0,17 110-130 1.2-1.8 4.6-22.2
(25.3) (52.5) {0.1S> (120) (1.4) (5,5)*
East aide 21-34 36-40 0,17-0.47 93-130 1.2-2.2 5.3-16.3
(26.0) (38.3) !0.32) (111) (1.5) (6.9)*
a from Johnson and Kauss (8),
* denotes median value instead of mean.
-------
349
Biota
i) Plankton
In 1984, relatively high biomass concentrations of phytoplankton
were recorded during early June (1.17 g/m^) compared to that in
late July (0.27 g/m^)(9) . In spring, the species composition was
dominated by Diatomeae (67-90%), with significant contributions
from Chrysophyceae and Cryptophyceae phytoflagellates. During
summer, the community structure was equally composed of Chryso-
phyceae (34%) and Diatomeae (34%)« From May through September,
Chlorophyta (greens) contributed only once substantially, during
late July (24%). The contribution from cyanophyta (blue-greens)
was relatively low.
Eooplankton abundance in Lake St. Clair in June and July, 1984,
ranged from 35 to 93 organisms/!, and from 500 to 1,500 ug/L in
total biomass (10). These densities are among the highest
reported for the Great Lakes. Cladocerans were proportionately
dominant in both numbers biomass. This pattern of cladoceran
predominance is in contrast to the other Great lakes in which
copepods routinely dominate to a much greater extent. Lake St.
Clair is a more typical cladoceran habitat than the other lakes,
because it is shallow, more productive, and may not contain dense
populations of planktivorous fish to which cladocerans are
particularly vulnerable. In addition, the high flushing rate of
Lake St. Clair may favor species with shorter generation times.
Large zooplankters such as Holopedium and Leptodora were not
abundant. Copepods comprised approximately 1/3 numerically and
40-50% by biomass of the zooplankton community,
ii) Macrophytes
At least 12 submersed plant taxa occur in Lake St. Clair (11,12).
Common native taxa are Chara sp, (macroalga), Vallisneria amer-
icana, Potamogeton richardsonii, Elodea canadensls, Potamogeton
sp, (narrow-leaved forms), Najas. flexllls. Chara sp. in-
cludes Nitella sp, and muskgrass, both of which overwinter as
green plants. Nitella is often found in deeper water to a depth
of 27 m where few other plants are present. Submersed plant
stands in the lake are usually composed of 2-3 species, most
occur at depths less than 3,7 m. The 0.0 to 3,7 m depth interval
in Lake St. Clair covers approximately 628 km2, an^ plant cover-
age of the bottom within this depth interval is 35%, Estimated
annual production of submersed aquatic plants in Lake St. Clair
is 13,780 tonnes ash-free dry weight (13).
No detailed studies on species composition, distribution and
relative abundance of emergent macrophytes in Lake St. Clair have
been completed. The estimated total areai extent of emergents in
the lake in the late 1970s was 9,170 ha (14). Estimated produc-
tion o£ emergent aquatic plants in Lake St. Clair is 60,990
-------
350
tonnes ash-free dry weight/yr (13).
The drift of live (chlorophyllous) submersed plant matter out of
Lake St. Clair in the surface waters was measured in 1986 (15) .
Of the 6 submersed plant and macroalgae taxa present in drift
samples collected from April through October 1986 immediately
below Belle Isle near the head of the Detroit River, Vallisneria
americana, Potamogeton richardsonii, and Myjriophyllum spicatum
occurred most frequently. Substantial drift occurred in all
months. Drift biomass was lowest in April and highest in
September at 14 and 1,183 g wet weight/1000 m^ filtered). The
submersed plant biomass leaving Lake St. Clair as surface drift
during April to October, 1986, was calcul-ated to be 32,052 tonnes
wet weight or about 1,602 tonnes ash-free dry weight. This cal-
culation may underestimate the biomass of macrophyte drift
because the Detroit River discharge in 1986 was probably greater
than the 1900-1980 average that was used for river flow. Concern
exists that the drift of plant material containing contaminants
may facilitate the dispersal of contaminants within the UGLCC
Study area, including western Lake Erie.
iii) Benthos
Lake St. Clair supports a healthy and diverse community of ben-
thic fauna. Nematoda, Amphipoda, Diptera (Chironomidae), Ephem-
eroptera, Trichoptera, Gastropoda, and Pelecypoda are abundant in
the St. Clair River system. The taxonomic diversity of macro-
zoobenthos in Lake St. Clair (65 taxa) was lower than that in the
St. Clair River (98 taxa) and the Detroit River (80 taxa}, how-
ever (12) .
In 1985, a total mean density of mayfly (Hexagenia) nymphs of 194
nymphs/m2 was found throughout the UGLCC Study area, including
279 nymphs/m2 in Lake St. Clair. The maximum density was also
found in Lake St Clair at 3,099 nymphs/m2. Nymphal production
ranged from 165 to 2,321 mg dry wt./m2/yr in the study area, with
a maximum rate of 4,011 mg dry wt,/m2/yr at the single location
studied in Lake St. Clair. The river production values were
similar to the range of values reported in the literature, but
production in Lake St. Clair was about twice the highest pub-
lished value.
Macroinvertebrate taxa were identified at 47 sampling stations in
Lake St. Clair in 1983 (16). Six benthic invertebrate commun-
ities were identified with different species assemblages (Table
VIII-4). Two communities occurred generally in the shallow peri-
phery of the lake, three communities were found in the deeper
waters, and one was present in the St. Clair River and mouth of
the Thames River {Figure VIII-1). Discriminant analysis sug-
gested that the six communities were associated with different
environmental conditions. The "shallow periphery" communities
occurred at sites with coarser, sandy sediments and lower con-
-------
TABLE VII I-4
Species composition (mean number per 51*5 cm!J) of benthic communities in Lake St. Ciair, May 1983. P denotes a we*n
density of less than one individual per sample. Coavunitiea are grouped by habitat type (16),
AQUATIC CATERPILLARS!
Pyral idae
BEETLES:
Dubi raph i. a
TRUE BUGS;
Carixidae
CADDISFLIES:
Che hi ui A to pyyche
Hyd ropsyc he
Cerac lea
Hystac idea
Owce t i a
?><; lod«ia
Hu I nima
Neu etc i ip& i s
Phylocentropus
MAYFLIES:
Baet isca
Caenia
Eury loph^l la
Serratol i a
Ephenern
Hexugcnia
£tenone»a
S 1
LAKE— SHALLOH
P
P
1 ,3 P
P
P
P
P
P
P
P
P
P P
P P
P P
BENTHIC COMHUNITY
4 Z t, 3
LAKE --DEEP RIVEK
P P
P P
P
P
P
P • P
P P P
P
P
P P P
1.7
P
P
Itt.y 17.0 44.2 3.3
P
Ul
-------
TABLE VIII-4. (cont'd 2)
TKUE FLIES:
Ceratopogonidae
Chaot>o rus
Ch i ro jiomus
Cl aduptoo^ 1 ad i us
Heterotrxssocladius
Hyd robaenus
Cricotopub/Orthociadius
Parkiet'teriel la?
Monod UiEne au
Abl abu Hniy i a
Cl inotany[>i^a
Coelotanypua
IB
P
P
1,
P
13
1J
P
P
P
P
P
P
P
i 1
LAKE—SHALLOW
.3 P
P
P
P
a 2,4
P
P
.0 2. a
,2 P
7,5
P
4.0
P
P
P
1.5
P
P
P
1 .1
BENTHIC
4
P
5.4
1.3
P
P
P
2,2
3.3
7.2
5.7
P
P
P
1.1
P
P
Z,Z
COKM UNITY
2
LAKE— DEEP
2.1
1.5
P
P
P
P
P
P
P
P
P
2.0
P
6.0
a
1.0
1.3
7.2
27.2
ib.a
1.7
13.5
6,2
H.8
P
P
1.0
P
P
3.7
P
1.5
3
RIVEh
3.2
P
2,8
P
P
P
ZS.3
2 ,U
24.9
44.7
ys.5
p
7,3
P
P
P
LJ
cn
-------
TABUS VII 1-4* (cont'd
Djalniabat i sta
Pruo J Hd i us
Th 1 enemaruilBy ja-gp
Eap i d i ilae
CRUSTACEANS:
Gamma rus
HvalelJa ait ecu
Asel lus
L i rceus
CLAMS;
fisidium
Sphii^r ium
Uni on Idae
SNAILS:
Bithynia
Amn i co 1 a
Pi-obythinel 1&
Soir.ato^ yrus
Fo s s a r i a
Lymnaea
Physa
Gon iobtis i &
Pleu rocc ra
Valvata
LEECHES:
Cr[Jtii>dell idae
Glossiphonidae
5 1
LAKE- -SHALLOW
P P
P
P
3.4
p
Z .8
1 .2
P
P
P
P
P
P
P
2.4
P
P
BENTHIC
4
P
6.8
14 .5
2.1
4.4
P
P
1.3
P
P
1 .9
P
P
P
i.o
p
p
p
COMMUNITY
2 6
LAKE --DEEP
P
5.2 18. T
P 2.0
t.l 6.5
P P
P
P
P P
P
p
P
P
3
RIVER
7.6
P
22.7
2.6
1.2
5.3
4.8
P
P
10.3
P
P
P
P
u»
Ul
-------
TABi.E Will-*, (conl'tf 4t
POLVCHAETES :
ManaynuntciB specioaa
WORMS;
Lumtjrlcidae
Stylodrilus herringtanus
N»ididae
Aulodrilus americanua
A. pleuriseta
Bronehiura sowberbyi
Jsochoet ides curvisetosua
Ilyodriius lempletoni
lsochoet.es freyi
Lianodrilus angustipenia
L . ee rv i x
L. elttparedianus
L. Hoffmeisteri
L. Baumeensis
L, udekemiAnus
Potaoothrix noldaviensis
P. vejdovskyi
Oui stadrilus mu J-tiaetosus
Spiroaperaa ferox
NEHATOfiES
FLATHORHS
MEAN NUMBEH OP TAX*
MEAN DKNSITV OP OHGANISMS
» 1
LAKE — SHALLOW
P
P
P P
P
P
P
P
P P
P 1.8
P
P
3,1 P
P P
P 8.4
P 3.4
P
6.8 10.4
60.3 6U.9
BENTHIC
4
2.2
P
P
P
P
P
3,6
5.1
P
21.7
11.2
P
15.4
141. a
COMMON II V
LAKE— DEEP
P P
P
P
P 1.3
P
P
2.4
P
P
P P
4.Z 14.5
5.7
3.0
P 1.2
V.8
P 2.tt
11. S 12.2
1.1 2. a
10. z IB. a
BO. 4 253.3
3
RIVER
2.6
1.8
P
1,3
P
P
P
3.9
1.0
10.1
P
1.0
S.5
10. 'i
12.4
P
13. 9
20.9
369. &
01
-------
355
St, CMr River
Michigan
Detroit River
Ontario
£
FIGURE VIII-1. Distribution of benthic invertebrate communities in Lake St.
Clair, Anchor Bay and the St. Clair River, May 1983 (16).
-------
356
Generations of metals, organic carbon and nutrients relative to
the "deeper water" communities (Table VIII-5). Poor correlations
were found between the measured physieochemical variables and the
community separations, however, implying that one or more addi-
tional variables were influencing the community structure.
Based on the distribution of the benthic communities, mesotrophic
conditions prevailed in the central basin of the lake and Anchor
Bay and in the lower part of the St. Clair River, while oligo-
mesotrophic conditions were present in the shallower nearshore
areas of the lake and Anchor Bay. Neither the St. Clair or
Thames rivers had any perceivable effect on the environmental
quality of the lake. Impairment of environmental quality was
observed at the mouths of the Puce, Belle, and Ruscora rivers and
near a sewer outfall from St. Clair Shores, Michigan. The local-
ly impaired environmental quality may be related to the discharge
of oils and, grease into the lake. In addition, reduced environ-
mental quality related to organic matter enrichment was observed
in deeper parts of the study area near the St. Clair River delta.
Concentrations of lead (up to 40 ppm), cadmium (up to 19 ppm) and
octachlorostyrene (QCS, up to 0.15 ppm) in Lake St. Clair clams
were generally highest in that portion of the lake which receives
the majority of the St. Clair River discharge, i.e., adjacent to
the South Channel outlet. There are no Michigan or Ontario
guidelines or objectives for DCS or Cd in fish.
In contrast, the concentration of PCBs in clams, up to 0.7 ppm
exhibited a different distribution with highest concentrations
along the southwest shore of. the lake rather than in the St.
Clair River (17), By comparison, the GLWQA includes a specific
objective of 0.1 PCBs in whole fish. A positive correlation
between clam tissue and sediment concentrations observed only
for PCBs and OCS, however, suggesting that sediment distribution
patterns of lead and cadmium may not provide much information on
contaminant exposure of clams.
iv) Pish
The fish community of Lake St. Clair is diverse and abundant,
consisting mainly of warm-water and mesothermic species. Cold-
water species are found in the lake, but not as year-round resi-
dents. Of the more than 70 species recorded as native or mi-
grants, 34 use the lake for spawning (18) . Most of the 28 native
species spawn in shallow water along the delta (St. Clair Plats)
or other shoreline areas or in tributaries to the lake. Of the
exotic species, rainbow smelt and lamprey spawn in tribu-
taries, and alewives, carp, goldfish and gizzard shad spawn in
bays, marshes and other shallow areas,
Because of the proximity of Lake St. Clair to large urban popula-
tions, recreational fisheries are active year-round. In Michigan
-------
TABLE VTTI-5
Mean values {geometric mean} of physi cocheroif^ai sediment variables associated with the benthic
communities in Lake St. Glair, May 1983. All units are expressed as rag/kg unless otherwise
stated. Communities are grouped by habitat type (16>.
5
1
BENTHIC
4
Lake- Shallow
Fe (g/kg)
Al Ig/kg)
Cd ,'
Cr
Cu
Hg
Ni
Pb
7,n
Oil and Grease (g/kg)
Loss-On-Igni tion( % )
TotaJ Organic Carbon
Total-P (g/kg)
Total Kjeldahi-N tg/kg>
Grain Size (phi units)
6.
2.
0.
8.
2 .
0,
4 .
2.
13.
0.
0.
1 .
0.
0,
1 .
14
31
10
75
89
01
26
35
69
59
65
42
20
22
58
6.
2,
0.
9.
3.
0,
4.
3.
20.
0.
0.
2.
0.
0.
1 .
79
73
12
6?
81
07
61
62
33
31
59
36
21
22
86
8
5
0
15
10
0
9
13
41
0
1
11
0
0
3
.96
.43
,28
. 2%
.24
, 17
.26
.69
. 17
.53
.62
.50
.25
.51
.90
COHMUNITY
2
6
Lake-Deep
14. 16**
8.87
0.41)
23,89
17.86
0.49**
15.69
23.11
62.03
0.79
2.45
15.62
0,48*
0.79
4.65
12
6
O
24
22
0
15
24
65
1
3
24
0
1
4
. S6**
.65
.50
.42
.56
.32**
,97
.46
.68
.09*
.77
.82
.44*
.18*
.30
3
River
9
4
O
12
15
0
9
15
50
0
3
19
0
1
.43
.83
.38
.93
.06
.23
.68
.07
.92
.26
.30
.87
.38
.05*
3.76
Based on the U.S. EPA Guidelines for Pollution Classification of Great Lakes Harbour
Sediments (22):
* Means that the sediment is considered moderately polluted
** Means that the sediment concentration exceeds the Ontario Ministry of the
Environment's Guidelines for Open Water Disposal {22}.
Ul
en
-------
358
waters, yellow perch (59%) and walleye (18%) were the main spe-
cies harvested by boat anglers in 1983-1984. In Ontario waters
in 1986, the main species 'were walleye (59%), yellow perch (24%)
and smallmouth bass (4.6%). Yellow perch dominated the ice
fishery.
PCS concentrations in edible portions of walleye and yellow perch
were approaching 0.25 ppm and 0.05 ppm, respectively, in 1985
(7). These concentrations are below the U.S.Food and Drug Admin-
istration (U.S.FDA) action level of 2 ppm, but the concentration
in walleye exceeded the GLWQA specific objective of 0,1 ppm for
whole fish.
The concentration of mercury in the edible portions of walleye,
northern pike, white bass and yellow perch were approaching 0.3
to 1.0 ppm in 1985. These concentrations of mercury do not
exceed the U.S.FDA action level of 1 ppm, but they do in some
cases exceed the Ontario objective.
Habitat Alterations
Of an estimated 22,366 ha of wetlands that existed in Lake St.
Clair in 1873, more than 9,000 ha were lost to shoreline develop-
ment by 1968. Losses are most evident in the Clinton River, the
St. Clair delta and the eastern shore of the lake. In all three
areas, the margins of the wetlands have been modified. On the
eastern shoreline the wetlands at one time were approximately 2.5
km wide, but now they are about 0.8 km in width.
In Ontario, wetlands are currently being lost to agriculture.
The wetlands from the Thames River north to Chenal Ecarte dwin-
dled from 3,574 ha in 1965 to 2,510 ha in 1984 (19) Draining for
agriculture accounted for 89% of the wetland loss, whereas marina
and cottage development consumed the remaining 11%. During the
record high lake level in the early 1970s, about 1,000 ha of
emergent shoreline marsh from Mitchell Bay southward to the
Thames River were also temporarily lost (20). This loss was
tempered in part by the flooding of transition vegetation which
occurred on the upland (east) margin of the wetlands.
The St. Clair delta and the Anchor Bay area in Michigan are also
subject to flooding, but the recent wetland losses there are due
mainly to diking and filling for urban development. In the
Clinton River area, wetland losses occurred from both landward
and lakeward boundaries and the remaining wetlands are now iso-
lated from Lake St. Clair.
Navigation-related dredging has also altered aquatic habitat
within Lake St. Clair. In the 1950s, the minimum channel depth
in the St. Clair River, South Channel and Lake St. Clair was
dredged to 8.2 m as part of the Great Lakes-St. Lawrence Seaway.
-------
359
Navigation dredging projects have altered the flow regimes of
Lake St. Clair and replaced productive shoal water habitat with
less productive channel habitat, Bulkheading, dredging and back-
filling by landowners has also resulted in the loss of signifi-
cant amounts of littoral habitat in the system. The loss of
shoal and littoral waters, along with the removal of gravel and
the lack, of delta growth represent loss of habitat that is uti-
lized by many Great Lakes fishes to satisfy spawning and other
early life history requirements,
Bottom Sediments
i) Physical Characteristics
The thickness and grain size distribution of bottom sediments is
an important aid to understanding the transport, accumulation and
resuspension of polluted sediments in Lake St. Clair. Based on a
coring survey completed in 1986, the modern sediment thickness
corresponds roughly with lake depth (21). The maximum thickness
of over 30 cm is generally confined to the St, Clair River delta
and a narrow band extending from the delta southwest toward the
head of the Detroit River (Figure VIII-2).
Analysis of grain size distribution, based on 1984 data (21),
indicated the most common size interval in sediment samples to be
0.063 to 0,125 mm (3-4 PHI units). This size particle occurred
as a band trending NW-SE across mid-basin and in the north and
eastern portions of Anchor Bay. Coarser unimodal sediment (0.125
to 0.500 mm, 1-3 PHI units) was present opposite the Chenal
Ecarte and Clinton River mouths on the northeast and west coasts,
and in the central portion of Anchor Bay. Coarser bimodal sedi-
ments with gravel and sand modes occurred along the south and
southwest shores. Size modes finer than sand (0.063 mm, 4 PHI
units) were found only in a small area in the western part of the
central basin.
The distribution of sediment composition based on percentage
gravel, sand and silt-clay (mud) was similar to that observed for
the modal size distribution. Gravel content was generally less
than 1% with the exception of the south and southwest margin of
the lake where it ranged from 5 to 45%. Sand was the major com-
ponent of the surface sediments and ranged from 30 to 100%. The
highest percentages of sand occurred at the mouths of the delta
distributary channels and in the south and southwest area of the
lake. Percent silt and clay (muds) ranged from 1 to 68% with
highest percentages in the west-central part of the basin (Figure
VIII-3).
-------
360
t
FIGURE VIH-2. Thickness of modern sediment (cm).
-------
361
FIGURE VTII-3. Distribution of sediment types.
-------
362
ii) Evidence of Historical Inputs of Contaminants
Organic Contaminants:
Distributions of hexachlorobenzene (HCB), octachlorostyrene
(OCS), polychlorinated biphenyls (PCBs}, hexachlorobutadiene
(HCBD), pentachlorobenzene (QCB) and total DDT plus degradation
products in Lake St. Clair surficial sediments (0-1 cm) in 1985
are shown in Figure VIII-4, The data were derived from the sam-
pling pattern identified in Figure VIII-5. The highest contamin-
ant concentrations were found near the centre of the lake in the
region of greatest water depth, thickest layer of recent sedi-
ments over glacial clay, and greatest accumulation of fine-
grained sediment. Some minor accumulation of contaminants also
was found in Anchor Bay at the northern end of the lake. For the
most part, the sediments in the rest of the lake were sandy, and
contained low concentrations of organic contaminants. Although
the mean contaminant concentrations were not particularly high
compared to other areas in the Great Lakes Basin, with the
possible exception of HCB, the maximum concentrations reached
significant levels for many of the Sarnia-source contaminants
(Table VIII-6).
In most, but not all, instances, higher concentrations of PCBs
were found at greater depths in the sediments in 1985, corre-
sponding qualitatively with the loading history of PCBs, The
highest concentrations, 0,06 ppm, exceeded the Ontario Ministry
of Environment (OMOE) Guidelines for Dredged Spoils for Open-
Water Disposal and the IJC Guidelines for In-water Disposal of
Dredged Materials of 0.05 ppm. However, these concentrations did
not cause the lake to be classified as "polluted" by U.S.EPA
Pollutional Classification Guidelines for Great Lakes Harbour
Sediments where sediments containing greater than 10 ppm PCBs are
classified as "polluted". PCBs were also found in the cottrell
Drain and at the mouth of the cutoff channel of the Clinton River
at concentrations of 2.0 and 0.6 ppm, respectively. Up to 0,03
ppm PCBs were found in the Sydenham River, based on two samples.
Two localized areas of high HCB sediment concentrations were
found in Lake St. Clair in 1985. One was in the central portion
of the lake, and another was in the eastern section, northwest of
the mouth of the Thames River. The maximum concentration found
was 0.17 ppm. HCB was also detected in sediments of the Milk
River (0.003 ppm), Marsac Creek (0.002 ppm), Swan Creek (0.002
ppm}, Sydenham River (0,007 ppm) and the Thames River (0.001
ppm). No specific guidelines exist for HCB in sediments.
The highest concentration of OCS, 0.021 ppm, was found in the
central portion of the lake. OCS was detected in sediments of
the Sydenham River (0.001 ppm), but information on OCS in sedi-
ments of U.S. tributaries is not available. No specific guide-
lines exist for OCS in sediments.
-------
HCBD
DCS
QCB
Total DDT
HCB
Total PCB
UJ
a\
FIGURE V1IJ-4. Distribution of contaminants in Lake St. Clair surficial
sediments (mg/kg).
-------
364
LAKE SI CLA1R
FIGURE VIII-5. 1985 Lake St. Clair sediment core stations.
-------
365
TABLE VIII-6
Chlorinated organic compounds in surficial !0-1 cm) sediments of
Lake St. Clair ( ug/kg) .
Compound Ranee Mean
Hexachlorobenzene (HCB) 0.4-170 32
Octachlorostyrene (OCS ) ND-2I 4.8
PCBs ND-Z1 19
Hexachlorobutadiene (HCBD) XD-32 5.4
Pentachlorobenzene {QCB5 ND-8.7 3.2
Total Trichlorobenzene (TCB ) ND-28 4.3
Total Tetrachlorobenzene (TeCB5 ND-20 3.7
Total DDT and metabolites (SDDT) ND-12 3.8
-------
366
Information on PAHs in Lake St. Clair sediments or in Canadian
tributaries was not available. In U.S. tributaries, PAHs were
found in surficial sediments at concentrations ranging from 0.4
to 14.3 ppm. The highest concentrations were found in the Milk
River (14.3 ppm.), Cotrell Drain (13.8 ppm), Clinton River (12.1
ppm) and Frog Creek (10.7 ppm). No specific guidelines exist for
PAHs in sediments.
Cyanide of a concentration up to 0.7 ppm was found in the Clinton
River sediments. In Lake St. Clair sediments, three samples near
the southeast shore and one sample south of the Clinton River
were reported to contain 0.5 to 0.8 ppm cyanide, although these
values were reported to be below the analytical criterion of
detection. These concentrations exceed the OMOE and IJC Guide-
lines of 0.1 ppm, and cause a classification of "heavily pol-
luted" by U.S.EPA classification guidelines. Information on
cyanide in Canadian tributaries was not available.
High concentrations of oil and grease (up to 3,700 ppm) were also
found in the Clinton River. This concentration exceeds the OMOE
and IJC Guideline of 1,500 ppm, and causes a classification of
"heavily polluted" by U.S.EPA Classification Guidelines. Of 45
stations sampled in Lake St. Clair in 1985, the sediments in only
3 contained between 597 and 637 ppm oil and grease. The rest
contained less than 343 ppm, causing a classification of "unpolr
luted" by U.S.EPA classification Guidelines. Oil and grease re-
sults from 1984 indicated levels between 635 and 707 ppm for
Canadian tributaries. Somewhat elevated levels were determined
from 1985 samples, with a peak of 3,131 ppm obtained from
Sydenham River sediments. Concentrations from the Belle and
Thames Rivers and Pike Creek were 433, 792 and 1,018 ppm, respec-
tively.
Metal Contaminants:
Concentrations of metals measured in surficial (0-1 cm) layers of
the sediment samples collected in 1985 (Figure VIII-5) indicated
that some enrichment of cadmium and zinc has occurred over the
average concentrations of metals in surficial sediments in Lake
Huron (22), For Cd and Zn, 22 and 21 samples respectively, of 36
samples collected, had concentrations elevated above the Lake
Huron averages of 1.4 and 62 ug/g respectively (Table VIII-7).
The concentrations generally remained below OMOE, IJC and U.S.EPA
guidelines, however, except for the region near to the mouth of
the Clinton River. Sediments from the Clinton River were found
to contain up to 6.3 ppm Cd and 430 ppm Zn, both of which exceed
U.S. Classification Guidelines for heavily polluted sediments of
6 ppm and 200 ppm respectively. The Milk River sediments also
exceeded the guidelines with 380 ppm Zn.
Concentrations of chromium, copper, nickel and lead were mostly
below the Lake Huron averages, and below OMOE, IJC and U.S.EPA
-------
TABLE VIII-T
Concentrations of n«tal* (ng/kg} and total carbon (weight percent! in aurfieial se16
. 130
.109
. 146
.0578
, ISO
.0921
. 137
. 168
. 226
.0687
. 152
.0921
.0644
,0734
, 119
.126
.0382
.114
. 122
.131
. 125
Total
Carbon Cadmium
3
4
4
4
4
3
4
3
4
4
3
4
3
1
2
-
3
4
2
5
3
2
3
5
2
5
2
1
3
t
2
2
2
4
.94
.84
.42
.73
.02
.89
, 36
.75
.74
.86
,27
.61
, 78
.06
.96
0
.11
.76
.38
.IB
.30
,96
.62
.27
.75
. 13
.48
.970
965
.76
.45
.27
.87
.96
.32
.89
z
2
3
2
2
I
2
t
2
2
2
3
1
1
1
2
2
2
1
2
1
1
1
2
2
1
I
i
1
1
2
1
3
2
2
1
.70
.22
,71
.87
. to
.35*
. 34
.93
. 11
.23
.60
.25
.86
.48*
.48*
.23
.23
.OB
.<>7*
. 74
. 16»
.66*
. 66*
. 44
. 25
.02*
.22*
. 3S*
.23*
.48*
.38
.66*
.04
.20
. 2S
.36*
Chromium
43.
61 .
54 .
39.
36.
34 ,
30.
39.
as.
41 .
38.
41 .
38.
17.
22.
28.
25.
24.
16.
34.
23 .
22.
20.
36.
17.
23.
18.
18.
IB.
2J .
21 .
16.
18.
24.
24,
"'
1
3
2
4
a
3
i
7
2
5
2
4
0
7
9
11
6
<)
3
9
8
6
9
3
4
4
7
2
4
0
1
y
9
1
9
*
Copper
23.8
34 .2
26.4
2(> . 1
2tt.7
23.5
24.6
19. 1
32.2
29.5
20.4
23.3
20. 1
5. 10
9.46
16.4
14.6
24.5
9.08
33.0
14.5
12.9
23.3
33.0
10. 1
20.6
11.2
6.86
8.63
10.3
1 3 .8
5, 11
14.0
13.8
12.1
15.1
Nickel
32
34
40
33
32
29
25
33
33
32
30
32
32
14
20
25
22
23
15
31
HO
22
26
29
15
21
IB
14
15
17
18
9.
19
14
Itt
19
.6
.0
.8
.3
.4
.3
.7
.2
.5
.0
.3
.0
.0
.7
,4
.8
.4
. 1
.2
, 2
.8
.9
. 1
. 8
.2
,9
.8
.7
.9
.4
.8
74
-Z
-5
.9
.6
Lead
34
31
at
37
30
35
40
13
41
46
28
29
29
12
11
26
19
32
8 ,
33
21
25
29
33
20
24
11
12
17
13
17
,3
.6
.0
.8
,6
.2
.0
.6
. 1
.0
.8
.3
.8
. 2
. 8
.7
.5
,0
42
,4
.0
.2
.5
,2
,9
.5
.4
,1
.5
.0
.4
-.525*
13
16
14
32
.e
. 5
.4
.6
Ant imony
.180
.254
,281
. 182
.126
. 170
.160
,234
,173
,287
.156
. 116
.151
,0707
.0796
.132
.OH35
.155
.0921
.211
, 173
.129
.230
.236
.0689
.197
.122
.0645
.0052
.0858
,148
.0481
.138
.162
. 144
.110
/Inc
84.9
130.
103.
90. 7
81 .8
84.4
80.4
60.0
92.8
91,8
83.6
B3.1
82. 1
41.4
39.7
71.7
62.9
73.8
41 .5
89. 1
62,0
57 . 7
IB. 2
90.7
47 .6
82.0
47,4
38.0
50.4
41.8
55.7
31 .8
84.7
67.0
49. 1
S3. 7
-------
368
Guidelines, except for an area near to the mouth, of the Clinton
River, The distribution o£ the metals in Lake St. Clair sedi-
ments did, however, indicate greater concentrations in the
central, south and southeast areas than in the north and west
areas. Concentrations of lead and copper in the Clinton and Milk
Rivers, and of Ni in the Clinton River exceeded the OMOE and IJC
Guidelines, and cause a classification of "heavily polluted"
according to U.S.EPA Classification Guidelines.
Mercury (Kg) enrichment in the surface sediments was confined to
central Late St. Clair, where up to 1.2 ug/g dry weight was
found. By comparison, surficial sediments in Lake Huron contain
an average of 0.22 ug/g (22). Except for the central area, most
of Lake St. Clair surficial sediments contained less than 0.3 ug
Hg/g, the value for and IJC Guidelines. The concentration
profiles of Hg in at least three cores in 1985 indicated lower
concentrations of Hg at the surface of the cores than at a depth
of 5-6 cm, thereby implying the deposition of less contaminated
recent material. The background concentrations deep in the core,
however, were less than 0.1 ug Hg/g. Concentrations of Hg in
Clinton River sediments were found up to 0.7 ppm, exceeding the
and IJC Guidelines, but not U.S.EPA Classification
Guidelines for "polluted" sediments.
The depth-integrated concentrations of metals in cores from the
same samples as above were generally similar to those in the
surficial sections, except for significantly greater concen-
trations of Cd in the composited samples (Table VIII-8). Using
the guidelines for OMOE evaluations of dredging projects for
sediment contaminated by metals, which are roughly equivalent to
U.S.EPA guidelines for moderately polluted sediments (22), the
guidelines ware exceeded in 100%, 75%, 36% and 8% of the cores
for Cd, Cr, Ni and Cu respectively,
in a separate study of surficial sediments conducted in 1985 in
which sampling sites were selected specifically to collect fine-
grained sediments capable of supporting mayfly (Hexagenia)
nymphs, sediment at only 2 of the 45 stations were heavily pol-
luted with mercury. Sediments at 2-9 (4-20%) of the stations
were moderately polluted with nickel, copper, chromium and zinc.
Five to 10 (11-22%) of the stations sampled contained mercury,
PCBs or copper in excess of OMOE guidelines for contaminated
sediments. Concentrations of contaminants were generally highest
in sediments at stations near L'anse Creuse Bay offshore of the
Clinton River Cutoff Canal. A 1984-85 study of Canadian tribu-
tary mouths indicated that Provincial dredging guidelines were
exceeded at a number of tributaries for chromium, copper, iron
and nickel. An assessment of heavy metal concentrations measured
on suspended solids (RSP) indicated a higher frequency of guide-
line exceedence.
-------
Concentrations of metals
TABLE VI Il-tt
in compoaite4 aediaent sanpl
«a Tram Lake St. Cluir.
Station
LSTri,-B5-04
LSTCL-85- 14
l.STCL-85-17
LSTCJ.-85-IB
LSTC1.-85-19
LSTCL-85 -20
LSTCL-B5-2I
l,STCL-tJ5-22
l,STCl,-B5-23
LSTCI.-8S-24
l.STCI. -85-25
LSTCI.-85-26
I.STCI. -85-27
I.STCL-85-2B
LSTCI.-8S-31
I.STOI, -85-36
I.STCL-85-37
1.STCI.-BS-38
LSTCI.-65-39
LSTOI. -85-64
I.STCL-85-65
t,STCL-85-$7
l.STCt-85-68
LSTCL-85-69
|,S1CL-ft5-70
LSTCL-85-71
LSTCL-85- 12
1.STCI.-B5-73
LSTCI.- 85- 15
l.STCL-85-83
I.S5TCL-B5-B*
LSTCL-B5-8S
LSTCI.-85-8?
t.STCi,-8S-8tt
l.STUL-85-89
LSTL'l.-85-JB
Bismuth
.231
, 194
. 16B
, 180
, 150
. 193
.173
, 179
. 175
,226
, 186
,132
, 148
. 158
.6906
. 133
, 172
. 113
,087
.243
.193
.1S9
. 148
.250
. 106
, 120
. lift
.144
. 135
.179
.116
.0822
.16?
.116
.221
,102
Calcium
48500.
47000.
49500.
54800.
67300.
47200,
42000.
634UO.
6-HiOO.
57200,
54700,
62200.
64700.
71000.
37000.
24500.
50700.
69800,
27000.
53400.
49HOO.
21000.
42200.
5370O.
49500.
52000.
21900.
33300.
34500.
20700.
37200.
144OO.
35800.
36500.
29BOO.
20KOO.
Cadmium
3.11
2.83
4,35
4.13
2.56
4.10
3.4S
3.46
3.72
4.63
3. 91
4.35
6,15
2.7*
3.01
4,00
4,43
4 .00
3.38
4 .00
3. 28
2.12
3.92
4 .90
3,72
3,27
3.45
4 .00
2. 92
;>.s.«
3.47
2.11
4.3G
4.65
3.20
3.56
ChroraiuB
47.0
42.8
34. 1
31.7
2H.5
33.1
30. 2
33.0
29 . 5
30. 7
33.0
28,1
31 .6
40. f,
14.8
23.4
35 .0
26.0
15.5
35. 1
37 . S
32 .«
2H.2
42 . 5
21 , 7
24.5
25. 7
28.8
23.6
39. J
18. 1
11.0
28,8
25.2
31.3
17.6
Copper
22.7
24.3
ia. i
17,4
16.5
16.5
19.1
19.1
22. 6
2O, £>
21,7
15.6
1H. 2
21.7
6, SB
13,9
18. 2
2U.B
7.77
25. Z
1»,1
IB. 2
15,6
40, 1
22.5
16.4
1 3. »
13.9
13.6
1H.2
13.9
5.12
16.5
14.5
15.7
10.4
Iron
32100,
2930O.
23500.
22400.
23BOO.
23900.
22900,
25000.
23500.
23HOO.
23800.
22300.
Z2600,
33000.
12600.
15600.
24400.
19000,
10500.
25400,
26900.
26SUO.
23000.
27800.
ItSiiUO.
1»«!00.
20100.
23500.
20200.
217 00 .
1481)0.
«590.
21 100.
1B100.
21200.
1 1400.
Hagnesiim
20100.
1520U.
2570O.
24UOO.
25500.
2 5 I OO .
2B100.
20700.
2330O.
2720O.
25500,
2 3 BOO.
24OOO.
15900.
] 3100.
SJ1900.
22500.
30100.
14300,
30000.
20700.
17900.
20500.
27700.
20400,
25700.
1 7700.
1 3200.
i:)800.
14500,
23000.
9710,
20000.
16200.
11900.
10500.
Manganese
42B.
392.
366.
367.
400.
34B.
360.
300.
339.
347.
353.
358.
373,
446.
260.
234.
33Z .
274,
147.
353.
347.
307.
294.
3BO.
213,
236.
239.
2S3.
306.
399.
ItH.
120.
240.
237.
281.
134.
Nickel
32. tt
31 ,2
25.0
24.5
24.2
23.8
2S.O
25.6
28. 1
29.6
27.7
25,8
25.0
30.2
13.3
18.8
27 .8
20.9
13,3
27.7
29.8
24.0
23.6
29,8
17.7
19.6
20.8
24.2
20.9
29.7
18.3
10.1
22.4
21 .6
23.0
15. B
Lead
24.3
24.2
17. 7
19.*
17.4
18.6
19.3
14 .9
23.4
23. (1
22.6
10.5
18.6
18.6
6,24»
20.2
18.9
3O. 3
9.69
27.1
12.5
14.5
9.29
34.8
21 .3
14-5
16.3
12.5
12.1
12,1
12.1
4.0*
13,7
13.5
32.8
19.0
Ant iaony
.149
.174
.151
.\titi
.161
.172
. 1S5
, 193
. 165
.140
,146
.184
.108
. 121
.078S
.104
.135
.187
,0625
,219
.220
.193
,152
.23)
.130
.182
,161
.133
,07§0
.0952
.119
.0407
.20ti
.08?
.173
.0887
Zinc
80.8
84. 3
67.1
£2.9
60.6
63.0
60.4
6Z.B
67.1
69. S
71,7
58.1
82. B
11.6
31. f
49.5
62.5
76-8
36.2
80.6
69, S
6*, 6
60.7
98. S
62.6
64.8
55.9
51.6
51 .6
56.0
60.8
29.4
62,8
61.9
58.5
47.4
ui
at
W3
» Below liait of detection
-------
370
Phosphorus Enrichment:
Total phosphorus concentrations in surficial sediments were
higher in three discrete areas during the 1983 survey: the mouth
of the cutoff channel of the Clinton river, the mouth of the
Thames River and the south-central portion of the lake. Con-
centrations were below OMOE and IJC Guidelines (1,000 ppm), but
are classified as either "moderately polluted" (420-650 ppm) or
"heavily polluted" (>650 ppm} by U.S.EPA Classification Guide-
lines . In tributaries, the highest concentrations were found in
the Clinton River (3,100 ppm), which exceeded all relevant guide-
lines .
iii) Evidence of Current Inputs of Contaminants
In sediment cores taken in 1985 from Lake St. Clair, PCBs, DDT
and DCS exhibit higher concentrations deeper in the sediment than
at the surface. Reduced surface concentrations apparently ref-
lect the decrease in loading of the chemicals which has likely
occurred in recent years. Both HCB and HCBD concentrations,
however, increased near the top of the cores. This suggests that
loadings of these chemicals to Lake st» Clair were evidently not
dropping, and may even had been increasing in 1935. These
results are consistent with those of a 1985 study within the St.
Clair River that showed HCB and HCBD, (hexoctilorobutadlene) con-
centrations in water to be elevated on the Canadian side of the
mouth of the river (7).
Studies of sediments from the St. Clair River have shown that the
ratios of HCB to DCS are useful for tracking the source of con-
taminants in that river (23). The HCS/OCS and HCB/QCB ratios
were 1.3 and 4,0, respectively, for sediments near the Scott Road
Landfill, a site which contains waste byproducts from Dow's early
production of chlorine and chlorinated solvents. The HCB/OCS and
HCB/QCB ratios in sediments just below Dow's outfall and where
nonaqueous wastes have leaked into the river were 16 and 23 res-
pectively. In sediment cores from the central area of Lake St.
Clair in 1985, the ratio of HCB/OCS changed from 2 lower in the
core to 9 at the surface, similarly the HCB/QCB ratio increased
from 4 near the bottom to 20 near the surface. These trends were
thus consistent with decreasing waste losses from the Scott Road
Landfill and an increase in the relative importance of Dow's
current effluent discharge and waste losses from the plant site.
Localized Hot Spots of In-place Pollutants:
A survey of metal contaminants in surficial sediments of Lake St.
Clair conducted in 1983 included sampling sites closer to the
nearshore areas than were the sites in the 1985 survey (24) . In
1983, near the Cutoff Canal of the Clinton River, relatively
elevated concentrations of Cu, 2n» Ni, Cd, cr, and Pb were
observed. Similar concentrations were also observed in the
-------
371
Chenal Ecarte near Mitchell Bay, Distributions and concentra-
tions of Cu, Zn, Pb and Cr across Lake St. Clair were similar to
the findings of the 1985 survey, the nickel and cadmium concentr-
ations were about half of those reported for 1985 sediments. The
reason for this discrepancy has not been defined.
iv) Sediment Transport
Due to the strong hydraulic circulations, sediments from either
tributary sources or from resuspension during severe storms are
generally transported considerable distances, on the order of
several km from their origin, before they either deposit to the
lake bed or enter the outflow. Besides direct sediment transport
by the lake circulation, it is possible that sediments are trans-
ported from nearshore zones to the open lake depositional basins
by gravity currents associated with heavier turbid water. A thin
layer of more turbid water was observed near the bottom at one
open lake observation site. Evidence supporting this method of
sediment transport is seen in the sediment concentration contours
of zinc, copper and organic carbon, which indicate a source of
these parameters at the mouth of the Thames River.
v) Sediment Burial
Since only 30 cm, at most, of sediment has accumulated in Lake
St. Clair in post-glacial times, the lake must be considered as
nearly nondepositional. However, the isotopic studies of bottom
sediments (25) suggest that the burrowing activities of such
organisms as Oligochaete worms can mix newly deposited sediment
to an average depth of around 5 cm. At that depth the sediment
could be buried for long periods of time. Mass budget studies of
various tracers indicate residence time of sediments ranging from
3 to 6 years with a mean of 4 +/- 1 year. In the contaminant
modeling studies, the burial process was quantified at a rate of
0.1 cm/yr throughout the lake. However, it should be noted that
this burial rate inferred from the modeling studies leads to a
sediment accumulation which is about two orders of magnitude too
large. On the other hand, it is possible that precultural rates
of burial were much less than the present rates of burial.
vi) Sediment Residence Time
Two sediment residence times are of concern: 1) the residence
time of newly suspended or tributary input sediment in the water
column, and 2) the sediment residence times of deposited sedi-
ments in the lake. Estimates of the time during which contamin-
ants bound to sediments could exchange with the water column are
based on measured and inferred settling rates of suspended par-
ticles in Lake St. Clair. The settling velocities of the fine-
sized components of suspended sediment which presumably originate
from nearby deposits range from 2 to 5 m/d, but are mainly about
4 m/d. Thus once suspended, particles remain in suspension for
-------
372
somewhat less than a day before being deposited. This is
probably a maximum residence time in the water column since the
particles were separated before analysis, Flocculation of par-
ticles could decrease the residence time of particles to several
hours. This notion is supported by the application of the simple
sediment model to five time series of suspended sediments,
neglecting horizontal transport. The mean settling velocity
inferred from the model was 21 m/d.
An approximate residence time for deposited sediments may be
estimated from the strength of the hydraulic flow and the
settling time. If, for example, fine sediment particles are
resuspended for 8 hours on the average, then they would be trans-
ported by the main hydraulic flow about 2 km towards the outflow
before being deposited as the storm event subsides. For par-
ticles deposited in the depositional basin, at least 12 storm
events would be required to move them a distance of 20 km to the
outflow area. Because the physical measurements of suspended
sediments were unable to distinguish between local resuspension
in deep water and the transport by the lake circulation from
shallower areas, it is impossible to estimate the number of
storms per year capable of resuspending fine sediments in the
deeper zones of the lake. It is probably safe to say that there
would be at least two storms per year of sufficient strength to
initiate sediment resuspension in the deeper area. Therefore,
one might conclude that strongly adsorbed contaminants would take
about 6 years to move to the outflow area.
There are several processes which could lengthen this residence
time. As the sediments travel towards the outflow, there would
be a progressively shorter wind fetch. Consequently, the wave
energy available for resuspension would decrease towards the
outflow region in the prevailing wind direction. This finding
was supported by the wave, wind and sediment data of Haniblin et
al., (26) who showed that suspended sediment levels are high in
the Detroit River inflow area only during major storms from the
northeast. Those storms which are from the prevailing wind
direction do not result in appreciable export of suspended sedi-
ment from the lake.
The one-dimensional bottom sediment model of Robbins and Oliver,
(27) shows erosion of sediment becomes progressively more dif-
ficult as erosion proceeds because of compaction. Therefore,
while there may be several storms per year capable of initiating
sediment resuspension, it is possible that major storms occurring
only once in 20 years or even 100 years can erode appreciable
amounts of bottom sediments.
Due to the many uncertainties at this time in the understanding
of the physical processes involved in estimating the residence
time for strongly attached contaminants on fine sediment par-
ticles, estimates of the residence times can be better achieved
-------
373
through budget methods.
Residence times for bottom sediments in Lake St. Clair baaed on
long term budgets of radioactive tracers, mercury and various
organic contaminants are given in Table VIXI-9. Residence times
range from 3 to 6,2 years with a mean of 4 +/- 1 years. Some of
these estimates were based on the assumption that there is no
exchange with the overlying water during resuspension events,
-------
314
TABLE VIII-9
Sediment reservoir residence times inferred from radiormclide
storage as of 1985 and changes in mean contaminant levels from
1970 to 1974 (25) .
Constituent Residence Time(yr)
Cesium-137 6.0
Excess lead-210 3.0
Mercury 4 .0
DDE 3,6
TDE 4.6
DDT 2 . 9
Total PCBs 6.2
Mean 4+/-1
-------
375
B. SPECIFIC
A summary of specific concerns for Lake St, Clair, based on the
following discussion may be found in Table VIII-10. Included are
the specific concerns, the use impairments prompting the con-
cerns, the media affected, and the geographic scope of the use
impairment,
1. Conventional Pollutants
Due to the agricultural base of the Lake St. Clair geographic
area's counties, the nonpoint source pollutants of greatest con-
cern are suspended sediments» nutrients and pesticides, These
concerns were documented in 1585 through the small watershed
assessment process (28), These pollutants can impair the use of
Lake St, Clair area resources for drinking water supplies, fish-
eries and wildlife, recreation, industrial shipping and agricul-
ture.
Nutrients and.. Eutrophication
Nonpoint source water quality problems aggravated or pro-
nounced by variations in stream-flow. During high flow periods,
most surface waters display their poorest quality, with signif-
icant increases in biological oxygen demand, nutrients, pesti-
cides and sediments from nonpoint sources, "When low flows occur,
the nonpoint source material deposited during high flow events
have an impact because they are no longer diluted. Scouring and
the deposition of sediments is also a significant nonpoint source
impact. Both water quality water quantity are therefore
important to consider in devising control and management plans.
The input of relatively clean, low nutrient water from Lake Huron
via the St. Clair River, and the short flushing time of Lake St,
Clair has prevented nutrient concentrations from increasing and
has kept eutrophication to a minimum.
Although phosphorus concentrations in Lake St, Clair per se do
not appear to be a problem, the lake basin contribute phos-
phorus to the water which enters Lake Erie via the Detroit River,
The Water Quality Agreement specifically calls for "improved
measurement of tributary loadings to the Lower Lakes for the
purpose of providing improved nonpoint source loading estimates".
Because tributary loadings of nutrients have been shown to exceed
those from atmospheric or point sources, accurate tributary load-
ing data are important to identify total loadings from the lake
basin, Michigan and Ontario have target nonpoint source loadings
of phosphorus to Lake Erie to meet as part of their phosphorus
loading reduction program, and the contribution from the Lake St,
Clair basin may be significant.
-------
376
TABLE VIII-10
Specific concerns in Lake St. Glair, uses impaired, media affected, and
geographic scope of the perceived problem.
CONCERN
Phosphorus
Pest icides
Oil and grease
Heavy metals
Mercury
POTENTIAL
USE IMPAIRMENT
use associated with
eutrophication of
Lake Erie
potential reduction of
plant productivity
toxicity to benthic
community
toxicity to benthic
community
toxicitv to biota
toxicity to biota
MEDIA
water
water
sediments
sediments
sediments
water
sediments
GEOGRAPHIC SCOPE
tributaries
wetlands
tributaries
whole lake
tributaries
whole lake
PCBs
PAH 5
Phthalate
esters
Habitat
alterat ions
human health hazard
(when consumed)
human health hazard
(when consumed)
toxicity to benthic
community
human health
hazard
human health
hazard
lowered wildlife
production
fish
fish
ducks
sediments
sediments
sediments
biota
sediments
water
whoie lake
whole lake
Walpole Island
tributaries
tributaries
tributaries
wetlands
-------
377
Beach Closings
In 1986, there were eight U.S. bathing beaches on Lake St. Clair
in Macomb and Wayne counties (29) . All were monitored, for water
quality, and none were temporarily closed due to water quality
problems. This issue does not appear to be a problem.
Aesthetics
In the nearshore regions, the water is brownish-green. Over the
navigation channel the water colour tends to cloudy-green, but
the water is clear green near the centre of the lake away from
the navigation channel. Noxious odors and floating mats of algae
are generally not present. Mid-summer water transparency ranges
from. 0.6 m near the shore to about 2.6 m near the open lake.
Aesthetics is therefore not a major issue concerning Lake St.
Clair.
2. Toxic Organics and Heavy Metals
Ambient__Waters
For compounds that persist and bioaccumulate, loadings into the
Great Lakes are of concern regardless of the concentrations at
which the compounds -are delivered. Even when loadings occur at
concentrations below detection limits, such compounds can bio-
accumulate and exert significant ecosystem effects. Such com-
pounds have received extensive study within the Great Lakes.
Most of the current generation of pesticides have short environ-
mental half-lives and have little tendency to bioaccumulate.
They are present, however, at much higher concentrations than
most of the persistent organics (30). Their ecological effects
have received very little study in comparison with studies of
persistent organics.
The most commonly applied agricultural pesticides were the herb-
icides atrazine, alachlor, metolachlor and cyanazine. Data and
tables have been provided (5,31). Maximum measured concentra-
tions of these pesticides in the Thames and Clinton Rivers in
1985 and unit area loads from the watershed to these rivers are
summarized in Table VIII-1. The 1985 Thames River estimated
loading rates for atrazine, metolachlor and alachlor were 6,892
kg (16 g/ha) , 2,875 kg (7 g/ha) , and 299 -kg (0.7 g/ha} respec-
tively (Table VIII-1}. Atrazine was detected in 93% of all sam-
ples. Alachlor, which was banned in 1985, was detected in
approximately 15% of the samples collected in 1984 to 1985.
During April through August, 1985, the Clinton River estimated
loading rates for atrazine, metolachlor, alachlor, and cyanazine
were 52.2 kg (0.28 g/ha), 1.3 kg (0.1 g/ha), 14.2 kg (0.08 g/ha) ,_
and 9,1 kg (0.05 g/ha) respectively. The unit area loadings of
-------
378
atrazine and metolachlor from the Thames River watershed were
therefore approximately 1 to 2 orders of magnitude greater than
those from the Clinton River watershed.
In general, the 1985 concentrations of pesticides observed in the
Michigan tributaries would have little effect on fish or aquatic
invertebrates, but could affect photosynthetic rates of some
algae and rooted aquatic plants. However, the 1985 pesticide
loads for the Clinton River is very likely to be significantly
less than the average load for this river, due to the near ab-
sence of runoff events following pesticide applications in this
watershed.
Biota
In edible portions of Lake St. Clair fish, PCBs have declined
generally and with the exception of carp, channel catfish and
muskellunge, all species have not exceeded the Health and Welfare
Canada guideline of 2.0 ppm. Mean PCB concentrations in mus-
kellunge have increased since 1980 (32).
Measurements of DDT in Lake St. Clair fish have not exceeded the
Health and Welfare Canada guideline of 5 ppm in any of the 13
species tested. As with the PCB data, highest concentrations
were detected in channel catfish and carp, and they were lowest
in yellow perch.
Concentrations of HCB and OCS in channel catfish from Lake St.
Clair are greater than those from southern Lake Huron, in carp,
OCS concentrations are greater in fish from Lake St. Clair than
in those from southern Lake Huron. Chlorinated dioxins and
dibenzofurans have been detected in Lake St. Clair channel cat-
fish and carp, but not in walleye.
A survey of contaminants in spottail shiners from 1977 through
1986 indicated that the highest contaminant burdens were assoc-
iated with the south channel of the St. Clair River. Shiners
from Mitchell Bay were less impacted, and those from the south-
eastern part of the lake near the mouth of the Thames River and
from the southern part of the lake near the mouth of the Detroit
River were not measurably impacted by contaminant loadings from
the St. Clair River. Concentrations of PCBs, HCB, OCS, DDT and
Chlordane in spottails from Lake St, Clair were generally similar
to those in southern Lake Huron, except for elevated levels of
PCBs and HCB in fish from the South Channel.
Current mean concentrations of mercury in walleye, northern pike
and carp fillets are less than 25% and yellow perch and white
bass less than 20% of 1970 levels (33) . Mercury concentrations
in muskellunge, however, did not decline between 1975 and 1985
(32) .
-------
379
Despite declining concentrations of contaminants in the fish, a
Public Health Fish Consumption Advisory exists for both U.S. and
Canadian waters. As of 1987, the Advisory included "No Consump-
tion" for largemouth bass over 14", muskellunge and sturgeon.
"Restricted consumption" of no more than one meal per week for
the general population was advised for larger specimens of
walleye, white bass, smallmouth bass, yellow perch, carp, rock
bass, black crappie, largemouth bass, bluegill, pumpkinseed,
freshwater drum, carp-sucker, brown bullhead, catfish and north-
ern pike. Nursing mothers, pregnant women, women who expect to
bear children and children age 15 and under were advised to not
eat the fish listed because of the potential for effects of con-
taminants on the infant or child.
For 1988, Michigan will retain the advisory as issued for 1987.
Ontario, however, will reduce the advisory such that no "No Con-
sumption" category will be issued. The advise toward pregnant
mothers and their children will still remain in effect.
A comparison of the abundance of mayfly (Hexagenia) nymphs in the
UGLCC Study area where visible oil did and did not occur in the
sediments indicated substantially lower densities (Sl/m^) in the
presence of visible oil than in the absence of visible oil
(224/m2).
The annual production of Hexagenia nymphs was measured in the
UGLCC Study area along with sediment concentrations of oil,
cyanide, Hg, Cd, Cr, Cu» Ni, Pb and Zn. Production averaged
2,086 mg dry wt./m^/yr at 3 locations where sediment levels of
contaminants were not in excess of guidelines established by the
U.S. and Canada for distinguishing polluted sediments. Elsewhere
in the study area, the guidelines for polluted sediments were
exceeded by as many as 7 contaminants at a single location, and
production averaged only 364 ing dry wt./m^/yr. In Lake St.
Clair, where production was highest, only Hg exceeded the guide-
line .
Wildfowl:
Recent analyses (34) have indicated elevated levels of penta-
chlorobenzene (QCB), PCBs, HCB and OCS in duck populations resi-
dent in the St. Clair River marshes near Walpole Island. Mean
OCS concentrations of 115 ppb and PCB concentrations ranging from
1.5 to 4 ppb were found in nonmigratory mallards in samples of
breast and liver tissue. At present no wildfowl consumptions
advisories exist for HCB, OCS and QCB. While a comparison of the
PCB concentrations with the Wisconsin guidelines (35) of 3 ppm do
not indicate a major health concern and consequent loss of use of
the wetland habitat, there is considerable evidence that organic
compounds moving down the St. Clair River are being trapped
within the wetland region. Wildfowl consumption advisories are
being considered by the appropriate governmental agencies in the
-------
380
Lake St. Clair region (Ontario Ministry of Natural Resources,
Michigan Department of Natural Resources and Canadian Wildlife
Service).
Sediments
Results of sediment surveys in Lake St. Clair that were conducted
within the last few years indicate that accumulation of
contaminants has occurred in the deeper, thicker bottom sedi-
ments, but no particular areas or hot spots o£ highly contamin-
ated sediments were located. The data showed that sediments in
several tributaries to the lake contained much greater concentra-
tions of pollutants than were found in the open lake deposits.
Therefore, the areas requiring further attention for possible
remedial actions were within the regions of tributary discharge.
In 1985, bottom sediments from 12 U.S. tributaries to Lake St.
Clair were analyzed for UGLCCS parameters of concern and other
contaminants. The data are presented in Table ¥111-11 and sum-
marized below.
1} Pesticides
DOT and its metabolites were found in 9 of the 12 tributary sedi-
ment samples. The maximum concentration found in the Milk
River (383 ug/kg). The p'p forms of DDT predominated, and DDT
and DDE generally were more prevalent than ODD. The p'p forms
were detected in 10% of sediment samples from the mouths of
Ontario tributaries.
Other chloro-organic pesticides were also found in 9 of 12 tribu-
tary sediment samples, Gamma-chlordane was the pesticide most
commonly found, ranging from 2 ug/kg in the Clinton Cutoff Canal
to 196 ug/kg in Cottrell Drain. The sample from the Milk Eiver
contained the greatest number of pesticide compounds identified,
including the only occurrence of Aldrin outside of the Detroit
River tributaries. With exception of a single sample containing
2, 4-D from Pike Creek no other pesticides or herbicides were
measured in bottom sediments from Ontario tributaries.
Hexachlorobenzene (HCB3 was found in only 6 samples at levels of
I to 7 ug/kg.
ii) Organic Contaminants
PCBs were found in 9 of 12 tributary samples with concentrations
up to 1,974 ug/kg in the Cottrel Drain, Most of the PCS was
found as aroclor 1254, although in the Cottrel Drain aroclor 1248
was dominant. Aroclor 1260 found only from the Milk River
sediments.
-------
i\iii.e viit-ii
C oriT aainants In Lake St. Clalr tributary sediaents Ing/kg 1, 1975.
L
scat isn
»
P«ra««ter CC"t- 1 1 Ct'f-12 CCT- 1 3A CCT- 1 4 A
Ca ic iui»
Magnesiirfc
Sodj iiia
Potassium
Arsenic
BariuM
Be ry 1 i uts
B i sntu t h
Cadffiiiim
Chromium
Cobalt
Copper
Lead
Manganese
Molybdenum
Nickel
Silver
Strontiu»
Van ad Ilia
2 i nc*
Tin
Aluminum
M thiuHi
S* ( en i KM
Iron
¥t triua
Nerctiry
COD
Oil and Grease
Ammonia
TKN
Phosphorus
Cyanide
To till Solids
Tot«i Volatilea
Total PCBs lug/ kg
Total PAHa "
Tot a 1 DDT "
HCB
<]. ChiorrtnnB
DK-Hiity 1 pht hulate
BISJ Z-El hyl benzy I
phthaiate lug /kg!
2 1 OOO
44OO
170
1400
9
l&Q
0, 1
9.5
2.2
63
11
110
410
400
1.6
Si
2,6
45
2S
380
15
120OO
23
l.l
24000
9.7
54000
3290
0. 1
45.85
B.07
1 198
14300
383
J
87
400
5600
3000O
4300
12O
700
7.S
4B
0. I
11
1 . 1
21
6
39
130
260
1 .2
20
0.3
39
15
160
6.6
5000
11
0,4
12000
5.8
0.2
14OOO
20JO
90
1:100
600
0.1
55. 4S
6.41
1974
I9ti
2000
4 ZOO
22000
4200
100
200
1.6
11
0.1
11
0.3
16
3.1
10
14
110
1
10
0,3
21
J.2
34
4
2000
5
0
4000
2.2
0.1
leooo
650
75
BOO
430
O.J
77.13
0.14
IM
1 3 BOO
271
2
200
3000
24000
4400
150
1100
7.5
89
O.I
12
1.9
68
1 13
68
130
610
1.2
83
1.2
S3
27
220
6
13000
26
0. 7
28000
11
i). 3
35000
1230
300
eaoQ
3000
0,2
J4.01
7,67
596
800
_
4000
34OO
CCT- 1 6
38OOO
4600
17U
2 UOO
6,5
93
0.1
11
1 ,3
45
11
78
110
460
1.2
40
1
52
25
190
4.5
14000
29
0.6
24000
11
0.3
B moo
2400
310
4300
1300
0,4
2». 12
8.37
226
1400
87
-
1600
44IIO
OCT-16A
36000
4700
170
1600
8.5
150
0, 1
10
B. j
140
15
130
240
670
2,1
100
3.5
53
2fS
430
11
13000
27
o.a
32000
11
0.7
38000
3700
2;io
2 a oo
3100'
0.7
41.1
7.8
185
I 2 1 00
30
If
-
16200
CCT-lflA CCT- 1 7 CCf-lHA
17000
41UO
mo
1400
a. 4
64
0. 1
B.8
0.2
21
1.S
22
58
360
I .2
31
0.3
32
20
140
4
9000
16
0
ifiooo
1
0.1
30OOO
K50
150
1700
2000
0. 1
53.2
4.7
3«00
MK
ti
200
BOO
17000
4300
22O
4500
4 .»
120
0.1
24
0.8
40
12
71
81
350
1 .4
37
0.6
46
51
140
4.9
24000
40
0.3
30000
13
0.2
61000
fl50
240
3600
1600
0.3
40.1
7.3
B5
HOO
72
2600
1200
20UOO
420O
2311
1BOO
5. 3
U4
0,1
26
O.S
32
7.4
48
140
270
1,7
19
1
42
27
170
5.5
11000
19
0.4
18000
a
0.4
30000
2250
190
1700
1500
0.3
44.4
8
635
41)0
H
is
laoo
10400
CCf-l9
31 OOO
4600
130
E10O
6.7
130
0, 1
0.7
0.2
32
15
28
36
650
2.6
43
0.4
66
38
110
4
19000
42
0.3
38000
13
0.1
33000
860
240
1900
1100
0, 1
45.1
4.6
31
10700
3:1
2
3
CCT- 20
1OOOO
4500
100
1400
s.s
6ft
0.3
0
0.4
21
11
42
40
310
1.8
29
o.a
22
26
100
4
12000
25
0.6
20000
11
0. 1
39OOO
650
70
3100
820
0.3
37.4
6.9
26
2
5
flCf-21
5000
3200
100
200
1,3
10
0.1
0
0.2
4.7
3
4.8
10
47
t
6
0.3
B.3
8.5
19
4
moo
3,5
0
3000
2.2
11 000
650
17
770
22-0
0.1
65.5
1 .8
CO
Mi-Milk River, bririgp, 12-Colt re I I drain, Nnrt.li fhannol, I :ift-i!l inton River cur off upstream, 14a-tfentr<* Beuf Druin/Blnck Creek,
16-0 lint on Hiver, t fin-Clint on kiver itftstrt-nm, IK-Vase <"r«»ek upstream, 11 -Ha It Hivftr. «t mouth, Ilia-Frog Creek, upstreiiB, 19-M»rs«c Creek
20-SwAn Creek, mouth, 21-llnnni»*rt trib. , R»st of St»«n C.Ten-k.
-------
382
PAHs were found In 9 of the samples, with the maximum total PAHs
being reported in sediments from the Milk River (14,300 ug/kg).
Elevated concentrations were found also in the Cottrel Drain
{13,800 ug/kg), Clinton River (12,100 ug/kg), and in Frog Creek
{10,700 ug/kg). Most samples were dominated by 3~, 4- and 5-ring
PAHs, Naphthalene found, only from the Clinton River,
Cottrel Drain, Milk River and Frog creek had the highest number
of individual PAH compounds with 11, 9 and 8 respectively.
Phthalate esters were found in 9 of 12 samples. Occurrences of
all the four phthalate esters that were found throughout the
UGLCC Study area were found in the Lake St. Clair tributary sedi-
ments, including the 4 highest concentrations of di-n-butyl
phthalate (in sediments from the Ventre Beuf Drain/Black Creek,
Salt River, Cottrel Drain and Frog Creek) and the only occur-
rences of diethyl phthalate in the UGLCC Study area. Bis(2-
ethyihexyl)phthalate was found in 9 of 12 samples with
concentrations up to 16,200 ug/kg in the Clinton River,
iii) Metals and Conventional Pollutants
Several tributary sediment samples contained concentrations of
metals and conventional pollutants in excess of U.S.EPA Guide-
lines (22) for nonpolluted sediments. These guidelines, number
of tributaries with exceedences of the guidelines, and the rivers
with maximum concentration of each parameter are presented in
Table VIII-12. Most of the maximum concentrations occurred in
either the Clinton River or the Milk River. The Ventre Beuf
Drain/Black Creek sediments contained elevated concentrations of
the agricultural contaminants, ammonia, TKN and phosphorus,
3. Habitat Alterations
The delta marshes, estuaries, lagoons and channel wetlands that
fringe the shores of Lake St, Clair in both Michigan Ontario
are among the most biologically productive areas in the Great
Lakes system. Because they occur in the proximity of a densely
populated, highly industrialized and intensively farmed region,
the wetlands have suffered losses in both quality and quantity
(36). The remaining wetlands perform many important hydrological
and ecological functions, including providing habitat for fish,
furbearers and waterfowl.
Although portions of the wetlands have been permanently lost or
severely degraded, the prospects for future preservation ot re-
maining wetlands and for at least partial rehabilitation of
selected areas are reasonable good. Wetland legislation and
other policies designed to protect the environment are in place
or under consideration. A comprehensive discussion of the Lake
St. Clair wetlands, including their ecological features, human
-------
383
TABLE VII1-12
Exeeedenees of U.S. guidelines for heavily polluted sediments for metals
and conventional pollutants in U.S. Lake St. Glair tributaries.
Parameter Guideline
Cd 6 ng/kg
Cr 75 mf/kg
Cti 50 mg/kg
Pb 60 mg/kg
Me SOO mg/kg
Hi SO mg/kg
Ag
Zn 200 mg/kg
Se 0,8 mf/kg*
Fe 15,000 mg/kg
As 8 mg/kg
8a 60 mg/kg
Bo
COD iO.OOO mg/tg
O*G 1,000 mg/kg
NH4 200 mg/kg
TKN X,000 mg/hf
* of tribs
with
exceedences*
1
1
4
7
3
3
1
4
1
§
I
i
i
S
inaxifiuit measured
concentration
6.3 mg/hf
140 aig/kg
130 tig/kg
410 mg/ki
670 mg/kg
100 ag/kg
3.8 mg/kg
430 mg/kg
1.1 mg/kg
3i,000 mg/kg
S.S mg/feg
ISO mg/kg
IS mg/kg
81,000 mf/kg
3,100 mg/kg
330 mg/kg
i,900 ng/kg
River with
maximum
Clinton
Clinton
Cl inton
Milk
Cl inton
Cl inton
Clinton
Cl inton
Milk
Marsmo Creek
Clinton
Clinton
Frog Creek
Salt River
Clinton
Clinton
Milk
Ventre Beyf
Drain/Black
Creek
p
CN
TVS
850 mg/kg
0,25 mg/kg
8 *
S
5
3
. 3,100 mg/kg
0.7 mg/kg
8.4 %
Cl inton
Cl inton
Clinton,
• U.S.EP4 Guidelines for the Pollution*! Classification of Great Lakes
Harbour Sediments (111,
h Lake Erie background concentration (221.
-------
384
impacts, and management issues has been presented by Herdendorf,
et al. (36), to which, the reader is referred for details beyond
the scope of the UGLCC Study.
-------
385
C. SOURCES
1. Municipal Point Sources
Ide n t i £ i c a t i o n
In 1986 there were 18 major (flow > 3.7 x 103 m3/d or 1.0 U.S.
MGD) municipal wastewater treatment facilities and 29 minor muni-
cipal facilities discharging to the basin (37). Only four of
these, however, discharged directly to Lake St. Clair. Several
of the U.S plants discharged to the Clinton River, Michigan, and
most of the Canadian plants discharged to the Syclenham and Thames
Rivers, Ontario. Total flow from municipal sources was 559 x 103
m3/d.
The major facilities were predominantly activated sludge systems
with phosphorus removal, while the minor .facilities were predom-
inantly lagoon systems or trickling filter plants. All U.S,
plants were served by separated sewer systems. Three of the
larger Canadian municipalities have some combined sewer systems
which represent varying percentages of the total serviced area in
each municipality (Chatham, Wallaceburg, and London).
The largest urban centre, London (population 277,000), has 25%
combined sewers. Chatham, population 36,000, and Wallaceburg,
population 12,000, each have 37% of their sewer systems combined.
In the U.S., five major municipal waste water treatment plants
(WWTP) were identified and selected for sampling; New Baltimore
WWTP discharges directly to Lake St. Clair, while the WWTPs at
Mt. Clemens, Pontiac, Rochester and Warren discharge to the
Clinton River. Three waste water treatment plants in Canada were
selected for study: The Belle River-Maidstone WWTP discharges
directly to Lake St. Clair, the Chatham WWTP discharges to the
Thames River, and the Wallaceburg WWTP discharges to the Sydenham
River. The sources were sampled for the 18 UGLCC Study param-
eters plus additional conventional pollutants, metals and organic
contaminants. One to six day surveys were conducted at each
facility between October 1985 and November 1986.
Based on the study of municipal dischargers, of greatest concern
were the Wallaceburg WWTP, the Mt. Clemens WWTP and the warren
WWTP. Trace organics, heavy metals, phenols, ammonia and phos-
phorus were the notable pollutants contributed by these plants.
All three received industrial wastewaters as a significant por-
tion of their influent.
Classification
In terms of effluent loading for the sources surveyed, the fol-
lowing facilities were considered to be major contributors of the
-------
386
parameters studied:
1, Wallaceburg WWTP: Total copper, total nickel, total Iron,
and ammonia-nitrogen.
2. Chatham WWTP; Chloride, ammonia-nitrogen, lead, total
suspended solids, and oil and grease,
3, Warren WWTP; PCBs, HCB, cyanide, total cadmium, total
chromium, total zinc, total nickel, total cobalt, chloride,
phosphorus, total organic carbon, and BOD,
4, Mt. Clemens WWTP; PCBs, phenols, oil and grease, total lead,
total mercury, total iron, phosphorus, ammonia-nitrogen,
total suspended solids and BOD.
All sources were in compliance with applicable guidelines or
site-specific limitations for the study parameters, except for
the Mt. Clemens WWTP which exceeded the Great Lakes Water Quality
Agreement effluent limitation for total phosphorus of 1.0 mg/L.
However, the following sources were discharging elevated con-
•centrations of contaminants which were not subject to site-
specific effluent limitations, requirements or guidelines;
1, Wallaceburg WWTP,' Total cadmium, total chromium, total
copper, total nickel, ammonia-nitrogen.
2. Mt. Clemens WWTP; PCBs, total phenols, total mercury.
3, Warren WWTP: PCBs,
The Warren WWTP and the Chatham WWTP, although classified as
major sources of the UGLCC Study parameters, were operating
efficiently and were discharging low concentrations of all para-
meters, except PCBs at the Warren WWTP, Their ranking as major
contributors was due to their flows being considerably larger
than most of the other sources. The municipal waste water treat-
ment facilities at Belle River, New Baltimore, Rochester and
Pontiac were considered to be minor contributors of the param-
eters studied.
Extent of Contributions to the Problems
A summary of the major municipal point source loadings of the
UGLCCS parameters to Lake St. Clair is presented in Table VIII-
13, Included is information on analytical detection limits,
flows, average concentrations, loads, and percentage of total
point source contribution for each facility for each parameter.
Municipal point source contributions of immediate concern were
identified;
-------
TABLE VJII-13
IIGI.CCS study paint source loadings of UGLCCS parameters4 to Lake St. Clair by *»ajor contributors.
PARAMETER
Total PCBs
NOLI a) FACILITY
lu^/Ll
0 . 00 1
0.001
Mt. Clemens WHTP
Warren WWTP
MICK/
ONT
M
H
OUTFAtl, NAWK(S)
10
P i n » J
Final
effluent
effluent
FI.OK
i*V4
13.3
109
AVERAGE kS/d * TOTAL POINT SOURCE
CONCENTRATION-' CONTRIBUTION
0.54
0.019
TOTAL
Hex ac hi oro™
0.001 Warren WWTP
0 .020 Chatham WPCP
0.00001 Mt. Clemens WWTP
N
Q
H
Final
Filial
Final
effluent
effluent
effluent
109
39. 4
13.3
0.0059
0.0051
O.0048
TOTAL
Octachloro-
st y rene
0.000001 ttt. cienena UWTP
M
Final
effluent
13
. 3
0. 002
0.0073
0.0033
o.ooosa
(1.00020
O. 00005
0.00084
0.000044 0,00000045
TOTAL 0.00000046
Total Plusnola
10
10
10
1
Mt. Cleraeni WWTP
Pontiac WWTP
Now Baltimore WWTP
Uatlaceburf WPCP
M
M
M
O
F 1 na 1
F i na 1
Ki nai
et fluent
effluent
effluent
effluent
13
4fi
ft .
7 .
. 3
. 9
J I
80
77
9
0.
.0
.6
.0
37
TOTAL
PAHs
Wallaceburg WPCP
O
Final
effluent
7.
H8
0.
4fi
TOTAL
Total
Cyanide-*
5
5
5
5
Warren HWTP
Mt . Clemens WWTP
Rochester WWTP
New Baltimore WWTP
M
H
M
M
Fi na 1
Filial
F i rm 1
Final
effluent
effluent
«ff tuent
effluent
109
13.3
B.7
5. 11
7
U
5
7
.0
.0
.0
.0
1 .03
0. 451
0. J 38
0. 030
1.73
0. 0036
0.0036
0. 76J
0.11
0.043ft
0.0358
78.6
21 .5
100
10.2
23,8
6.0
100
100
100
59.5
26.1
H.I)
6.4
100
100
100
80.0
11.6
4-6
3.8
(jj
00
-J
TOTAL
0.950
100
-------
TABLfr: Vlll-ia. Icont'd 21
PARAMETER HDLI 9 \
('
Total Mercurv <) .
0.
0.
0.
Total Copper 5,
1
1 ,
i .
S.
Total Nickel 4 ,
S,
5.
Total Cobalt 0.
0,
i|/Ll
,0001
,0001
, 025
.01! 5
0
,0
.0
,0
0
.0
(I
,0
.001
, 001
FACILITY
Mt. . Clenens WWTP
Warren HWTP
Chatham WPCP
Wallaceburg WPO!P
Wallaceburg WPCP
Warren WWTP
Pontiac WHTP
Mt . Clemens WWTP
Chatham WPCP
Warren WWTP
Wai lacettiirg WPCP
Chatham WPCP
Warren WWTP
Mt. Clemens WHTP
H1CH/
ONT
M
M
O
O
O
H
H
M
O
M
0
O
H
M
OUTFALL NAME! SI
!•' 1 IIH 1
Final
F i na I
Final
Final
Final
Final
FinaJ
Final
Final
Final
Final
Final
Final
effluent
of fluent
effluent
eft I uent
e f f 1 uent
e f f I uent
e t'f 1 uent
effluent
effluent
el'f 1 uent
effluent
effluent
ettl uent
effluent
FLOW
10*«-»/d
13,3
1O9
39. 4
7. B8
7.8B
109
46.9
13.3
3»,4
109
7.8H
3».4
10U
13.3
AVERACK
kg/d X
CONCENTRATION^
O.B78
0 . (12 7
0.033
O.02S
TOTAL
311
5.7
8.3
29. i
3. 6
TOTAL
28.4
309
!O.S
TOTAL
,.g
0,29
TOTAL
0,009
0. OOZ3
0.0013
0.0002
0.012ti
2.45
O.61 9
0,404
0.400
0,147
4.42
3.09
2.44
0, 42
5.95
0, 195
0.0041
0, 1991
TOTAL POINT SOURCE
CON TH I BUT TON
70.3
1H.O
10, a
1 .5
100
5B.
14 .
9.
9.
a.
95.
51 .
40.
7,
98.
97.
2.
5
8
6
5
5
9
0
3
2
3
5
6
100
Ul
CD
00
-------
TABLE ¥111-13. leant**! 3)
PAKAMETTEft
Oi 1 and Grease
i
i
Total CadmiuB
Total Lead
Total Zinc
MPLf a)
1 uf/U
100
! , 000
100
100
!,000
0,2
5.0
0.2
S
1
1
1
2
2
2
fi
Z
FACILITY
Chatham WPCP
Mt, Clemens
Wai laceburi
B«lle Hiver
WWTP
WPCP
HPOP
Rochester WWTP
Warren WWTP
Wai lacetmrg
Mt. Clemens
Chatham WPCP
WPCP
HHTP
Mt. Clemen WWTP
Warren WWTP
Pontiac WWTP
Warren WWTP
Pontiae WWTP
Mt-. Clemens
Wsi 1 J aeeburls
WWTP
WPCP
Rochester WWTP
MICH/
ONT
O
H
O
0
H
N
O
K
O
H
H
H
H
H
H
O
M
OUTFALL NANE(S)
Final
Fina 1
Final
f I na I
Final
F i na I
F i na 1
Fi na I
Final
Fi nal
Final
Final
Final
F i nal
V i n« 1
Final
Final
effluent
effluent
effluent
«f f luttnt
effluent
effluent
effluent
effluent
effluent
effluent
effluent
effluent
effluent
affluent
effluent
effluent
e f f 1 uent
FLOW
39.4
13.3
7.BB
6.47
8,7
109
7,88
13.3
33.4
13.3
108.8
46.9
109
46.9
13.3
7.88
8.7
AVERAOE Kg/d * TOTAL POINT SQyBOI
CONCENTRATION* CONTRIBUTION
(Mf/J, I
1.O90
3, BIO
2,190
3.8HO
a, 4 oo
TOTAL
0.6
2.82
0,7
TOTAL
11 .2
20.3
1.5
2.1
TOTAL
52.0
38.2
84,0
79.8
28. 8
82.2
4U.O
23.6
21 .1
20.0
196
0.0682
0.0189
O.OOS33
0.0844
0.443
0.271
0. 163
0.0986
O.U76
5.65
1 .79
3.12
0.629
0.28
41
21
12
10
10
.9
,5
,0
.H
.7
10O
69
21
9
.0
. 1
.3
100
42
25
15
9
93
56
17
11
6
•i
,3
.9
,S
.4
.1
.6
.9
.2
.3
,B
Ul
CO
TOTAL
9.45
84.6
-------
TABLE VIII-13. (cont'rt 41
PARAMETER
Amman i A as N
Hlll.l a 1
lug /I.)
1OO
10
100
10
FACILITY
Chatham
Mt. . Clem
Wn I tweet,
Roches te
WPCP
ena WWTP
uf«[ WPCP
r WWTP
MICH/
ONT
O
M
O
M
OUT FA I.
,1. NAME/d CONCENTRATION2
1 u^/1. )
Final
Finn)
F i na i
F > rta 1
effluent
effluent
effluent
ef fl uenl
39.4
i:i.3
7 . 88
8.7
5
t
IV!
<*
,710
,000
,HOO
,200
kg/tl % TOTAL POINT
SOURCE
CONTRIBUTION
22f> 41.5
133 24.5
101 18.B
54.0 10.0
TOTAL
&I3
94.6
Total 1 ran 14 .0
5.0
5,0
14 .0
14 .0
14 .0
5.O
Mt. Clemens WWW
HH) lacttburg WPCP
Chatham WPCP
Warren WWTP
Men Baltimore WWTP
Rochester WWTP
Belle Hiver WPCP
M
O
O
H
M
H
O
Final effluent
Final «ff)ti«nt
Final <*ffl**erit
Kin»l effluent
Final affluent
Final eft luent
Final effluent
13.3
7.88
It 3. 4
io»
&. 11
a, 7
7.4
1 ,030
1,410
23»
60.0
H 111
26S»
ii^O
13,7
11 .2
9.01
6.52
4.29
2. 34
1 , 13
27.2
22,2
17.9
12.9
8.5
4.6
3. 4
TOTAL
48.8
* "> 95X of total unless sources diffuse (katttl
* Flow wei ({hted .
3 Canadian sourcea not analyzed.
caftf-"ttd
96.7
Chloride
Phosphorus
aa P
I ,000
1 ,000
soo
1 ,0(10
1 ,000
500
10
10
1 0
100
100
10
Warren WWTP
Pontiac WWTP
Chatham WPCP
Rochester WWTP
Mt. Clemen* WWTP
Wai lacetmri WPCP
Wnrren WWTP
Mt . Clemens WWTP
Pontiar WWTP
Chatham WPCP
Kel l
460
32B
1 , 000
«ao
TOTAL
8,260
6 ,630
4 ,400
4,006
1 ,470
1.3ZO
25,000
4O. 2
32.0
21.6
12.9
7.9
5.9
121
31 .
21 .
17 .
15.
5.
5.
'Jti.
32.
25.
17.
10.
6.
4 .
97.
6
S
1
3
6
1
3
4
a
4
4
4
a
2
-------
391
i) Polychlorinated Biphenyls (PCBs); Although detected at
only two Michigan sources, Mt. Clemens WWTP and Warren
WWTP, the loading of 9,3 g/day to Lake St. Clair was high
compared to the loadings estimated for the other UGLCCS
areas, Both sources were discharging comparatively large
concentrations, 0,019 ug/L at Warren WWTP and 0.540 ug/L at
Mt, Clemens WWTP. Although PCBs were not detected in the
Canadian sources, the analytical method detection limit was
1,000 times less sensitive for Canadian samples than for
the U.S. samples.
ii) Total Phenols: The total loading was 1.73 Jcg/d. The
elevated concentration at Mt. Clemens WWTP, 77 ug/L,
much higher than a comparable objective in Ontario of 20
ug/L for industrial discharges.
iii) Total Cadmium; The Wallaceburg WWTP effluent exceeded the
Ontario Industrial Effluent Objective of 1 ug/L in two of
the three samples collected. The concentration in both
samples 4 ug/L. The total loading from, all sources
94.4 g/d.
iv) Total Mercury: Mt, Clemens WWTP had an unusually high
effluent concentration of 0.178 ug/L. The concentration
was more than four times the Great Lakes ambient water
quality objective for filtered mercury. The total loading
from all sources small, 12.8 g/d.
v) Total Copper; The Wallaceburg WWTP had effluent concen-
trations of 196 to 500 ug/L, 10 times larger than any
other point source and two orders of magnitude greater than
the Great Lakes Agreement ambient objective of 5 ug/L. The
combined loading from all sources was 4.18 kg/d.
vi) Total Nickel; The Wallaceburg WWTP had effluent concen-
trations of 225 to 452 ug/L, well above existing ambient
objectives such as the Great Lakes Agreement objective of
25 ug/L, The total loading from all sources 6.06 kg/d.
vii) Total Phosphorus; Mt. Clemens had an effluent concentra-
tion of 2.4 mg/L during the survey, above the 1,0 mg/L
permit limit and the Great Lakes Water Quality Agreement
Effluent Objective, Facility self-monitoring reports indi-
cated the 1,0 mg/L objective was frequently exceeded in
1986. The plant's interim permit did not contain a phos-
phorus limitation. Total loading from all sources surveyed
was 123 kg/d.
viii) Ammonia-nitrogen; The Wallaceburg WWTP had two of three
effluent concentrations above the Ontario industrial objec-
tive of 10 mg/L, i.e., 12,2 and 18.6 mg/L. The combined
loading from all sources was 541 kg/d.
-------
392
No significant contributions of non-UGLCCS parameters were iden-
tified.
2, Industrial Point Sources
There were 38 known point sources discharging to the Lake St.
Glair Basin in 1986, and all were minor facilities. All in-
dustries were indirect dischargers to Lake St. Glair, except the
Mt, Clemens, Michigan, water filtration plant, which discharged
filter backwash directly to the Lake. The total flow front
industries was not available. However, the majority of the in-
dustrial flow was once through cooling water or storm water.
The ten Canadian industries were predominantly food processors
and cement plants while the majority of the 28 Michigan plants
were automotive parts manufacturers, with process water usually
discharging to municipal 'WWTPs and cooling waters discharging to
surface waters. Because there were no direct industrial dis-
chargers to Lake St. Clair, no industrial sources were sampled as
part of the UGLCC Study.
3. Urban Nonpoint Sources
In.termittent Stormwater Diacharges
PCS concentrations on the U.S.(west) side" of the head of the
Detroit River were found to be greater than on the Canadian side
(28), This finding consistent with the observations of
Pugsley et al. (38) that the highest concentrations of PCBs in
clams and sediments from Lake St. Clair were found along the
western shore, Johnson and Kauss suggest that the single high
value of 1,630 ng/g that was observed on a single survey may be
related to an episodic point or nonpoint source discharge that
occurred during the survey. High total organic carbon (TOO
concentrations were also observed during the survey, which
may have resulted in increased adsorption of hydrophobia com-
pounds .
Some municipal storm drains exist in Michigan communities on Lake
St. Clair (39J. New Baltimore has a single 8" drain that enters
Prog creek, a minor tributary to the lake. In Mt. Clemens, 13
storm drains, ranging in size from 12" to 54'* in diameter, dis-
charge into the Clinton River. Impacts of these drains on the
receiving water quality have not been documented. However, seven
of the drains in Mt. Clemens have received a preliminary "high
priority" ranKing by Michigan Department of Natural Resources
(MDNR), Discharge priority ranking was based on indicators such
as basin land use, basin area, and diameter of discharge. The
process included many assumptions and estimation of relative
impacts, Therefore, the ratings should be regarded as only an
indication of potential impacts.
-------
393
Estimates of the annual contaminant loadings to Lake St. Clair
from Canadian urban runoff (stormwater and. combined sewer over-
flow) are presented in Table VIII-14. These estimates were based
on the mean measured concentration of contaminants in urban run-
off from April 1985 to November 1986 in Windsor, Sarnia and Sault
St. Marie, Ontario, and on previous estimates of the volume of
urban runoff in the Canadian Lake St. Clair basin. Because of
the uncertainties involved in the data used in the calculations,
these estimates should be considered only as approximations. No
similar loadings were calculated for the Michigan urban areas.
Combined Sewer Overflows
None of the U.S. municipalities have combined sewers, while three
of the larger Canadian municipalities do have combined sewer
systems. The larger urban centre, London (population 277,000) is
serviced by 25% combined sewers. Chatham (population 36,000) and
Wallaceburg (population 12,000) each have 37% combined sewers.
Chatham and Wallaceburg are the largest major urban centers on
the two largest Canadian tributaries of Lake St. Clair, Thames
and Sydenham Rivers, respectively. The impacts of either the
storm water discharge or of any combined sewer overflows on the
quality of the receiving waters have not been documented.
4. Rural Nonpoint Runoff
Nutrients
Major sources of nutrients within the Lake St. Clair drainage
area are fertilizer (commercial and manure spreading), livestock
operations and soil erosion. Nutrients removed by leaching or
transported by sediment and runoff may produce two pollution
problems; groundwater contamination and accelerated eutrophica-
tion of surface waters.
Commercial fertilizer (and to a lesser extent, livestock manure)
is applied to approximately 50% of the land in the Lake St. Clair
geographic area. Approximately 90% of this land is situated in
Ontario and receives approximately 300,000 tonnes (429 kg/ha) of
commercial fertilizer annually. Over-fertilization has been
identified for both Michigan and Ontario agricultural areas.
Analysis of soil fertility and crop nutrient requirements
relative to fertilizer applications reveal that many farmers are
applying up to 3 times more phosphorus fertilizer than required
in Canada, and up to two times the required rate in the U.S.
Livestock, operations in the Lake St. Clair geographic area
consist of dairy, beef, hog, sheep, chicken and horse operations.
Beef and dairy cattle are the biggest producers of phosphorus,
followed by hogs. A total of 61 tonnes/yr of phosphorus are
-------
TABLE VIIT-14
Estimate of contaminant loading to Lake St. Glair from Canadian urban
storm runoff* .
UGLCCS Parameter Loading kg/yr Loading kg/db
PCB
HCH
ocs
Pheno 1 s
PAHsl 17 I
Cyanide
Oil and Grease
Cadmium
Zinc
Mercury
Lead
Copper
Nickel
Cobalt
I ron
Chlorides
Phosphorus
Amman ia-N
219
15
10
2
1
378
7,995
12
24
6.4
0.06
0. 1 1
693
282
139
,000
320
,500
3.3
,700
,700
,BOO
1«7
,400
,000
,000
,000
0.02
0.0002
0.0003
1 .9
0.8
0.4
600
0,9
42.5
0.009
29.3
7.4
4.9
0.5
1036.7
21,904.1
32,9
65.7
I*)
Estimates calculated from average measured concentration in urban runoff
from Windsor, Sarnia and Sault Ste. Marie (51) and from estimated volume of
urban runoff in Lake St. CJair basin (521.
Expression of contaminant loadings from urban runoff on a daily basis is
somewhat artificial, since loadings are seasonally dependent. However,
expression in these terms allows comparison with daily point source loads.
-------
395
estimated to be delivered to the water courses from the livestock
operations, 65% of which comes from Ontario counties.
Soil erosion contributes approximately 3.2 tonnes/yr of phos-
phorus from Michigan to the water courses. Based upon the
percent of total cropland erosion occurring from wind, Macomb and
St. Clair Counties should be targeted for accelerated conserva-
tion assistance.
Pesticides
Lake St. Clair geographical area is a region of potential prob-
lems regarding the movement of pesticides into the water course.
These problems are a result of an estimated 3.5 million kg being
applied to land in both Canada and the U.S. which has a high
potential to transmit the chemicals via surface runoff, fine
particulate matter carried by wind or water, and infiltration to
groundwater. Based on soil texture and drainage, approximately
70% of the St. Clair geographical area in Canada has been iden-
tified as potential problem areas with respect to surface water
contamination, and approximately 60% of the area possesses a high
risk for pollutant transfer to groundwater systems (5).
5. Atmospheric Deposition
Loadings of contaminants to Lake St. Clair from the atmosphere
are a nontrivial portion of the total estimated load of lead and
phosphorus (see section E» modeling and mass balance considera-
tions, for further discussion). The major sources of phosphorus
are soil dust, leaf and insect debris, and industrial activity.
A large percentage of the loading may be derived from entrainment
of phosphorus -containing particles in agricultural areas. Lead
and cadmium are introduced through combustion of fossil fuel,
including exhaust from burning leaded gasoline in automobiles.
From measurements in urban and rural -locations close to Lake St.
Clair, atmospheric deposition of lead was estimated to range from
4 to 8 kg/d and for cadmium from 0.8 to 1.1 kg/d (17).
The atmospheric loadings of P, 1*103, tJEj, cd, Pb, Zn and Cl to
Lake St. Clair for the years 1982 - 1985 were estimated from data
collected at the Mt. Clemens station of the Great Lakes Atmos-
pheric Deposition network. The thirty-year mean precipitation
average was used to convert concentration values into loadings,
as displayed in Table VIII-15.
Quantitative estimates of loadings of organic contaminants to
Lake St. Clair are not available. Given the quantity of inor-
ganic materials introduced to the lake from the atmosphere, how-
ever, an atmospheric source for organic pollutants is also likely
to be important.
-------
396
TABLE VII1-15
Atmospheric loadings of selected parameters to Lake St. Glair for 1982 -
1985. Mt. Clemens OLAD station is the source of data. Lake surface area
is 1101.178 km2 (430 mi2).
1982
1983
1984
1985
AVISAGE
1982
1983
1984
1S85
AVERAGE
Nitratef NO
301,723
441,810
514,250
445,242
425,756
Cadmium
228
254
299
260
kg/yr
'j> Ammonia (NH
180
342
427
305
313
,593
,466
,257
,124 '
,860
Chloride
436,067
252
322
323
333
,170
,645
,492
,594
4) Total PhosphorusMTP)
3,402
5,952
5,102
3,928
4,596
Zinc Lead
30,909
14,773 5,179
23,393 5 , 509
13,769 3,825
20,711 4,838
-------
397
6. Groundwater Contamination/Waste Sites
Surface Waste Sites
Active and inactive waste sites within 19 km of the Connecting
Channels were identified as part of this investigation. The
majority of sites were landfills, hazardous waste disposal sites,
and regulated storage sites, other waste sites included trans-
portation spills, leaking underground storage tanks and contamin-
ated water wells. Underground injection wells were also iden-
tified.
Ranking of sites was based on their potential for contributing
contaminants to the Connecting Channels via groundwater. Sites
in the U.S. were ranked using the U.S.EPA DRASTIC System with
additions and minor modifications. This system assesses the
impact by evaluating the hydrogeology, waste material and the
distance from Lake St. clair for each site. Nine U.S. sites were
ranked as confirmed or possible contamination sites within the
Lake St. Clair groundwater discharge area (Table VIII-16). In
general, these sites are in areas of sandy unconsolidated sur-
ficial materials and are near to the Connecting Channels. The
water table is generally less than 4.6m below land surface and
priority pollutants and/or inorganic contaminants are on site or
in the groundwater.
Waste disposal sites in the Ontario study area were also iden-
tified. Emphasis was placed on identifying sites that require
monitoring or remedial investigations. Criteria for ranking and
prioritization of the sites included geologic, hydrologic, hydro-
geologic and geochemical information, on-site monitoring, waste
characterization and containment, and health and safety. No
sites in Kent County were identified that require immediate
investigation or that posed a definite potential for impact on
human health and safety. Three waste disposal sites in the area
contain only building refuse, domestic waste and commercial gar-
bage. These sites are small and not close to the lake. There-
fore, no significant impact is expected from them,
Deep.Well Injections
The Safe Drinking Water Act (SDWA) of 1974 requires U.S. SPA to
provide for the safety of United States drinking water. The act
contains a set of requirements which involves the protection of
underground sources of drinking water from contamination by in-
jection well activities. Seven U.S. injection facilities are
presently authorized in the Lake St. Clair area, five of which
are salt water disposal wells and two of which are hydrocarbon
storage wells. Of the salt water disposal wells, two are cur-
rently in operation: Consumers Power injects to the Dundee Forma-
tion at 957 m and Lakeville Gas Association injects to the
-------
398
TABLE VIII-16
Confirmed or possible con.ta.mination, sites in the U.S. within the Lake St,
Clair groundwater discharge areas.
1. Hwy M~29 and Michigan St. This site is a gas station with a leaking
underground tank on sandy materials near the St. Ciatr River and a shallow
water table.
2. C1ayTownship Sanitary Landfill This landfill has accepted household
and commercial wastesi and is near to the north Channel of the St. Clair
River distributary systea, sandy surficial deposits, and a shallow water
table,
3. Self ridge Air National..Guard Base (CERCLIS/RCRA/ACT 307) The Base site
consists of ? individual groundwater contamination sites: 3 landfills, 2
fire training areas and 2 ramps. The landfills contain residential and
industrial wastes, solvents, and waste oils. The fire training areas
contain flammable waste {JP-4 ) , solvents, strippers and thinners. Thera
have been fuel spills at the two ramps.
4* Metro Bea_ch ..Incinerator This closed incinerator handled general refuse
(most likely from the Metropolitan Beach Park), and is located on the
Clinton River Delta within one-half mile from Lake St. Clair over a shallow
water table and on silty—sandy surficial material.
5« G and L Industries (Act 307) Phthalate and lead are listed as
pollutants for this fiberboard manufacturer in Mount Clemens, Mi., and
groundwater contanination is indicated. The site is located on sandy soil
near to a shallow water table and aquifer.
6« County Line Landfill This landfill accepted household, commercial and
industrial wastes,
7. Henning_Road .Landfill (Act 307) The Landfill accepts domestic waste.
Groundwater contamination is not Indicated in the Act 307 listing.
8, 5ugarbush Road purapaite (CERCLIS/Act 307) This site is a solid waste
landfill with pollutants of concern being Pb, Ni, Cr, Cu and Zn. Surface
water, air and soil contamination are indicated in the Act 307 listing.
Groundwater contamination is not indicated, but there are no monitoring
wells.
9« Rosso Highwajf_SA_FB,_,- Avis Ford This landfill accepted foundry sand.
CERCLIS; Site is listed within the information system for Superfund and is
considered for ciean-up under the comprehensive Environmental
Compensation and Recovery Act of 1980 (CERCLA).
RCRA: Site has current activity under the Resource Conservation and
Recovery Act.
Act 307: Site is listed on Michigan's compilation of sitea of known and
possible environmental degradation.
-------
399
Sylvania Sandstone at 733 m in Oakland county. One additional
well is presently under construction in Oakland County. Two
wells are temporarily abandoned: one to the Detroit River Group
of formations at 276 m and one to the Sylvania Formation at 588 m
Consumers Power Co, operates the two gas storage caverns in the
Salina Formation Group.
Estimates,of Groundwater Discharge to__Lake St. Clalr
Groundwater discharges to Lake St. Clair from three hydrogeologic
units termed the shallow glacial (or shallow plus intermediate
units), glacial-bedrock interface (or regional, freshwater
aquifer), and bedrock units. The shallow glacial unit consists
entirely of Pleistocene Age glacial deposits. In southeastern
Michigan these are mostly silty-clay till and glaciolacustrine
deposits that contain discontinuous stringers of sand and gravel.
Base flow of perennial streams largely represents groundwater
discharge from this unit.
The glacial-bedrock interface unit occurs between the shallow
glacial unit and the bedrock. In general, the glacial-bedrock
interface unit discharges leas water to the Connecting Channels
than does the shallow glacial unit. Environmental concerns,
however, are that high head pressures from deep waste injection
practices could cause waste fluids to migrate through fractures
or more permeable horizons in the rock. The glacial-bedrock
interface unit could thus be pathway by which waste fluids
could reach the channels or contaminate adjacent groundwater. No
evidence exists at present that this has occurred in Michigan.
The bedrock unit is defined as the first bedrock aquifer lying
directly beneath the Connecting Channels. In the Lake St. Clair
study area, the bedrock unit includes all carbonate rocks of the
Traverse Formation which lie at depths of, 30 to 91 m beneath the
Antrim shale.
Total discharge from the three units to the Lake St. Clair study
area was estimated to be 1,315 L/s.
More direct measurement of groundwater flow to Lake St Clair was
also undertaken. Recognizing that all flow entering the lake
from groundwater must pass through its bed, the flow was calcu-
lated using the lakebed area, hydraulic gradients, and hydraulic
conductivities established by an electrical survey o£ the lake
sediments. The advantage of the electrical survey approach to
calculating groundwater flux is that it produces continuous meas-
urements of the hydraulic conductivity, as long as sediment is
present over the bedrock, allowing both detailed resolution of
the locations of groundwater inflow and an alternative method to
calculate the quantity. Summations of groundwater fluxes for the
entire lakeshore show a total groundwater discharge of 886 L/s,
-------
400
This estimate agrees well with that from above, estimated from
fluxes within geologic units,
Groundwater^ Contamination
In order to determine the concentration of contaminants in
groundwater in the Lake St. Clair area, and subsequently to cal-
culate loads from groundwater to the lake, eight monitoring wells
were installed in four groundwater discharge areas on the
Michigan shore of Lake St. Clair. Analyses of water from the
wells were for volatile, base neutral, acid extractable and
chlorinated neutral extractable hydrocarbons, trace metals, and
other chemical substances.
Volatile hydrocarbons, if present, were consistently less than
the detection limit of 3.0 ug/L. Benzene was detected in water
from one well near Mt. Clemens at a concentration of 3,1 ug/L,
Concentrations of base neutral and acid extractable compounds,
13 chlorinated pesticides, were also generally below the
analytical detection limits of 0,1 to 30 ug/L and 0.01 ug/L res-
pectively. Phthalates were found in the water from all but one
well, with concentrations up to 170 ug/L (for bis (2-ethyl hexyl)
phthalate).
Some pesticides were found in four wells at levels exceeding
U.S.EPA Ambient Water Quality Criteria for Chronic Effects and
the GLWQA Specific Objectives. Lindane and total DDT were found
down-gradient from the Clay Township Landfill near the St. Clair
River delta. DDT was found also in wells near New Baltimore and
St. Clair Shores. Heptachlor was found in a well near the
Selfridge Air National Guard Base (AWGB).
Most wells exceeded the GLWQA Specific Objectives, the Ontario
(Provincial) Water Quality Objectives or the U.S.EPA Drinking
Water Primary or Secondary Maximum Contaminant Levels for total
phenols, phosphorus, pH and some heavy metals. The elevated
metals concentrations may have been due to the inclusion of fine
particulate matter in the samples, and if so, the concentrations
of metals dissolved in the groundwater may be much lower than
those reported. The well near the Selfridge ANGB contained the
highest levels of phosphorus, phenols, dissolved solids and spec-
ific conductance.
A computation of the loading of chemical substances transported
by groundwater to Lake St. Clair does not seem feasible based
upon the data currently available. Concentrations of organic
compounds were generally less than their respective limits of
analytical detection, and concentrations of trace metals were
reported higher than they would have been had the finely divided
particulate matter been excluded from the analyses.
-------
401
7. Spills
Spills reports from Michigan and Ontario information systems were
reviewed and indicate that a limited number of spills to surface
water occurred in 1986, However, in many cases the volume of the
amount spilled was not known and it is no.t possible to compare
point source effluent loadings with the loadings due to spills.
8. Contaminated Sediments
Identification
i) Organics
Depth-integrated samples (interval composites) were prepared from
sediment cores collected in 1985 (Figure VIII-5) and analyzed for
organics in order to estimate the mass of contaminants stored in
the sediments. Horizontal distributions in total storage have
patterns which are essentially congruent with the thickness of
recent sediments and form the basis for estimating total storage
in the lake by contour integration. For the sandy nonaccumula-
ting area, where cores were not collected, a value of 5 ng/cm^
was used for PCBs and HCB, and a value of 0.5 ng/cm^ was used for
OCS. These approximations were not critical since the sandy
areas contributed less than 5% of the contaminant mass for these
chemicals. Lake St. Clair sediments presently contain about 960
kg of HCB, 870 kg of PCBs and 210 kg of OCS.
These values are much higher than the contaminant masses found by
Oliver and Pugsley (40) for the St. Clair River sediments (3 kg
HCB, 20 kg OCS) indicating that Lake St. Clair is a more signif-
icant repository for chemicals than the river itself, in part due
to the much greater mass of sediments in the lake. Recent load-
ing estimates for HCB and OCS in the combined dissolved and par-
ticulate fraction at Port Lambton in the St. Clair River were 180
kg/yr for HCB and 11 kg/yr of OCS. At these rates, Lake St.
Clair sediments contain the equivalent of 5 years loading of HCB
and 20 years loading of OCS. Thus, the sediments retain signif-
icant fractions of these chemicals and, given the uncertainties
in the calculation, accumulation is consistent with sediment
reservoir residence times derived from historical studies of
metal and organic chemicals in the system and from the response
of sediments to particle-associated radiomiclides.
ii) Metals
In order to estimate the total mass and anthropogenic mass of
each metal stored in Lake St. Clair sediments, the sediment cores
collected at each station in 1985 were designated to be repre-
sentative of a region of the lake. The anthropogenic mass of
each metal stored in each sediment type was calculated by sub-
tracting background metal concentrations from all concentrations
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402
in post-settlement sediments. In general, metal concentrations
increased above the glacial deposits.
Within the lake and its marshes, 30 to 64% of the mass of metals
stored in post-settlement sediments is anthropogenic, storage of
anthropogenic metals is highest in the silts and clays (48-70%),
second highest in the sands (32-35%), and lowest in the marshes
(5-29%). An exception to these general statements is the high
fraction of anthropogenic lead stored in the marshes (29%), based
on the one core used to represent the marshes,
Lake St. Clair appears to be a temporary trap for some metals
(Table VIII-9). Thus, sediments and their associated contamin-
ants, appear to be transient and will eventually be transported
down the Detroit River to Lake Erie.
Classification
Using the OMOE and U.S.EPA pollution guidelines, the sediments
underlying the open water of Lake St. Clair can be classified as
only lightly polluted. Sediments at the mouths of some tribu-
taries are more contaminated.
9. Navigation
As a result of the Rivers and Harbors Flood Control Act of 1970,
which authorized the U.S. Army Corps of Engineers to construct
facilities for containment of polluted dredge spoil from the
Great lakes harbors and waterways, two diked facilities were
constructed on Dickinson Island adjacent to North Channel in the
St. Clair delta. Both sites were located on the high pre-modern
delta deposit and did not infringe on the wetlands. These
disposal sites were designed to accommodate dredgings produced
during a 10 year period, and they presently receive the materials
dredged from the St. Clair system. Navigation-related dredging,
which removes contaminated sediments and deposits them in con-
fined disposal facilities could be considered beneficial in that
the total contaminant load within the system is reduced. Impacts
of the dredging due to resuspension of contaminated sediments
during the dredging operations, and the subsequent temporary
increase in bioavailability of the contaminants, have not been
documented.
Commercial vessel operations through the shipping channel are
also believed to cause some local sediment resuspension. The
extent of influence and effects of the contaminants associated
with the resuspended particles have not been documented.
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403
D. DATA LIMITATIONS
A detailed discussion of data quality management for the UGLCC
Study can be found in Chapter IV, The information presented
below reflects concern for some data quality pertaining specif-
ically to Lake St. Clair,
1. Sediment surveys
References in the text to a "1983 sediment survey" in Lake St.
Clair refer to a study conducted by the OMOE. The data have not
yet been published, nor have the methods, results or any inter-
pretation of the data been peer reviewed. Discussions with the
principal investigators, however, indicate that the samples were
obtained by bottom grab sampler, and the top 3 cm of each of 3
grabs were composited. The samples were then sent to a labora-
tory for analysis by "standard techniques". This study has the
appearance of being a valuable contribution to the knowledge of
the distribution of contaminants in Lake St. Clair sediments.
However, the data must be considered "preliminary" at this time,
and used only to support the findings of other documented
surveys, particularly the 1985 surveys conducted by Environment
Canada and by U.S. Fish and Wildlife Service.
2. Tributary Loadings
Accuracy of estimates of tributary loadings of chemical param-
eters is dependent on the responsiveness of the stream to storm.
events and on the frequency of sampling. Data from a program
employing infrequent sampling will generally be biased low for
substances which increase in concentration with increasing stream
flow, such as nutrients from agricultural runoff (41). Of
various sampling strategies, flow-stratified sampling, i.e.,
emphasizing storm events, and calculations provide the most ac-
curate results. Loading data for phosphorus, nitrogen,
chlorides, lead and cadmium from the Clinton, Thames and Sydenham
Rivers were based on a combination of monthly and storm-event
sampling and included from 15 to 72 samples per year. Data for
the Ruscom, Puce and Belle Rivers were based on only 14 or fewer
samples per year, and may therefore be subject to considerable
error.
A recent analysis of the flow responsiveness of Great Lakes tri-
butaries, i.e., their potential for change in rate of flow in
relation to storm events, indicated that the Clinton River was
"stable", the Sydenham River was "event responsive", and the
Thames was intermediate between the other two (42) Estimates of
loads of phosphorus, Cd and Pb for the Thames River, with the
greatest number of annual samples, and the Clinton River, with
the most stable flow, may be expected to have about the same
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404
accuracy, although confidence intervals were not reported. The
estimate for the sydenham, with the about the or fewer samp-
les and more variable flow response, may under represent the true
load by unknown amount.
The difficulty in calculating loads from small data sets created
the need to make loading calculations using several methods. For
Canadian tributaries, the Beale Eatio Estimator was used to ar-
rive at loads for P, Cd, Pb, and Cl, Loading calculations for
theie parameters plus NO3 were also made from, the data set
by plotting p concentration vs flow. A "best line fit" was then
drawn, and concentrations were then read off the graph for days
on which no samples were taken. Phosphorus loads on the remain-
ing Canadian tributaries were calculated using a two-strata
method. A "cut-off" line determined by doubling the annual
mean flow. An average concentration was found for days when flow
exceeded the cutoff, and another was found for days with flow
below that value, Loads for unsampled days were calculated by
multiplying the average concentration by the flow for that day,
The values presented in this report represent an arithmetic
average of results obtained by the two methods.
Concentrations of lead, cadmium, chloride and nitrogen in
Canadian streams did not exhibit a variation with respect to
flow. Therefore, loads were calculated by averaging all samples
and multiplying by the flow.
For the Clinton River, loads were calculated using the
Stratified Ratio Estimator (43). This method is essentially a
modification of the Beale Ratio Estimator.
The average annual loads for Canadian tributaries as displayed in
Table ¥111-I represents a mixture of included data. For P, the
average unit area load is based only on data from the Sydenhani
and Thames Rivers, which comprise 57% of the Lake St. Glair
watershed. Were an arithmetic average of all estimates of load-
ings front all Canadian tributaries to be used, the unit area
loading would have been reported as 3,18 kg/ha instead of 2,26
kg/ha.
For NOj and Cl, the loadings include an average unit area loading
from the Ruscom River, which was approximately 10 times that of
the other rivers in 1985, The average unit area loading for the
Sydenham and Thames Rivers combined for N03 and Cl was 20.5 kg/ha
and 160 kg/ha» respectively, instead of the reported 40 kg/ha and
287 kg/ha. The cause for the Ruscom River concentrations and
loads may need investigation, but the data should not be con-
sidered typical of the unit area loads for the Lake St. clair
watershed.
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405
3. Point Sources
The point source monitoring data in general were developed with a
rigorously defined quality assurance program. Due to constraints
on the sampling frequency and quantity, however, a number of
shortcomings in the point source survey data limit the inferences
that can be drawn from the results of the study. Most facilities
in the Lake St. Clair basin were not sampled. The major facili-
ties closest to the lake itself, as opposed to those furthest
upstream, were surveyed, however.
One deficiency, that of a small data base consisting of one day
sampling by the U.S. and 3 to 6 day surveys by Canada, prevents
precise determination of annual loadings. The timing of the
surveys reduced the comparability of the data. The U.S. surveys
were carried out during May and August of 1986, while the
Canadian data was collected on October 1985 and March and
November of 1986. The sampling methods were also different. The
U.S. composited four grabs (one per six hours) for each facility.
Canadian samples were collected by automatic composite samplers
(one portion per 15 min.}. Differences in the analytical methods
and the method detection limits used by the U.S. and Canada for
several parameters also reduced data compatibility. This defi-
ciency was particularly pronounced for PCB analyses.
Despite these limitations, the data were considered adequate for
identifying major sources of contaminants, and were used to make
conclusions and recommendations concerning specific point
sources.
4. Fish Consumption Advisories
The data upon which the fish consumption advisories for Lake St.
Clair are based were derived primarily from Canadian analyses of
samples of the edible portions of fish. This method generally
returns concentrations of contaminants less than those found in
larger skin-on fillets that the U.S. uses for its analyses of
contaminants in fish. One implication, therefore, is that if the
U.S. method for assessing contaminants in fish were used, the
fish consumption advisories may become more restrictive. Al-
though the impacts to humans of contaminants other than mercury
in fish flesh for commercially marketed fish are not quantified,
the advisories remain useful as a general guide for use by the
public who consume fish from Lake St. Clair.
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406
B. MODELING AND MASS BALANCE CONSIDERATIONS
1. Mass Balance Models
Pour days prior to the onset of the System Mass Balance measure-
ments in the Detroit River, measurements of contaminants entering
Lake St. Clair from the St. Clair River were initiated. The
intent of starting four days before making measurements on the
Detroit River was to allow for passage of most of the St. Clair
River water through the lake. By doing so, upstream and down-
stream contaminant fluxes could be compared and conclusions could
possibly be drawn concerning whether Lake St. Clair is a source
or a sink of contaminants. It must be emphasized that the valid-
ity of comparing upstream and downstream measurements in this
mass balance calculation depends on how well the same parcel of
water was sampled at the head and mouth of Lake St. Clair. Given
winds that existed during the sampling time, and output from a
particle transport model (developed at the National Oceanic and
Atmospheric Administration - NOAA) discussed below, we estimate
that 60-80% of the water that entered the lake, exited it on day
four. Therefore, downstream contaminant fluxes that are 20-40%
different from upstream fluxes cannot be argued to be signif-
icant. On the mass balance diagrams that follow (Figures VIII-6
through VIII-13), best estimates of point and nonpoint source
inputs have also been noted. If estimates were not available,
they are indicated with a "?" on a diagram. Loading information
was compiled with data provided by the Point and Nonpoint Source
Workgroups. Groundwater loading estimates are extremely prelimi-
nary and should be treated as such. These diagrams should there-
fore be used only to suggest possible issues that may require
further investigation. This is because of uncertainty about time
lags between the head and mouth of the Lake, and the "long term
average" character of some of loading information.
In most cases, the downstream contaminant fluxes do not differ
widely from the contaminant flux entering the lake via the St.
Clair River, In the cases of cadmium and particularly lead, it
appears that a significant portion of the lake's total load could
be coming from its tributaries. If the Thames River lead loads
are reasonably accurate, then a regulatory problem may exist.
Sediment records that indicate a net storage of lead over the
years would corroborate these observations.
A total phosphorus budget was developed for Lake St. Clair for
1975-1980 (Figure VIII-13). Phosphorus load estimates were made
for point sources and hydrological areas (Figure VIII-14).
During this period Lake Huron accounted for 52% of the total
annual load, while hydrologic area loads accounted for 43% (13).
The remaining load came from the atmosphere, shoreline erosion
and direct point sources. The Thames hydrologic area contributed
58% of the total hydrological area load, followed by the Sydenham
(17%), the Clinton (9%), the Ruscooi (7%), and the Black (6%),
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407
Atmosphere
,71
Upst ream
Input
12.3
Point
Sources
.073
.57-.77.
CHnton R.
Ground
H2Q
Lake
St.. Clair
.02
1.2-2.2
Point
Sources
Syden. R.
Thames R.
Ground
H20
14.3
Downstream output
QUt=14.3
slnk=l.l . 2.5?
FIGURE VIII-6. Lake St. Clair
total cadmium (kg/d).
Atmosphere
IIS.
Point
Sources
9.4-15.1
Clinton R."
Ground
H20
1.7
450.2
Upstream
Input
CANADA
Lake
St.. Clair
2.67
Point
Sources
Syden. R.
Thames R.
^ Ground
NH20
472. 3
Downstream output
ln=465.5-471.2
OUt=472.9
FIGURE VIII- 7. Lake St. Clair
total copper (kg/d).
Atmosphere
SJ.
Point
Sources _
Clinton R.
Ground
H2O
.219
Upst ream
Input
Lake
St.. Clair
CANADA
Point
-1— Sources
j? Syden. R.
_7 Thames H.
7 Ground
H2O
252
Downstream output
Ins,218
oyt=.2S2
source=.034
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408
Atmosphere
?
US.
Point
Sources _-°...
Clinton R. ?
Ground
H2O
Upst ream
input
Atmosphere
Lake
St.. Clair
CANADA
Point
- Sources
Syden. R.
Thames R,
Ground
H2O
Downstream output
ln=4.6
out=7,1
souree=2.3?
FIGURE VIII-10. Lake St. Glair
total mercury (kg/d).
Upstream
571 Input
US.
Point
Sources 3.2
24.9-16.4.
Clinton R.^^^
Ground
H2O
1.7
Lake
St.. CSair
CANADA
Point
Sources
Syden. R.
Thames R,
Ground
H20
499
in=59S.2-603.7
oul=499
sink=96-10S?
FIGURE vm-11. Lake St. Clair
total nickel (kg/d).
Atmosphere Upstream
S3 Input
Point
Sources
Clinton R. ?
Ground
H20
Lake
St.. Clair
CANADA
Point
Sources
Syden, R.
Thames R,
Ground
H2O
.85
Downstream output
!n=.89
out=.8S
stores.04?
FIGURE VIII-12. Lake St. Clair
total PCS (kg/d).
U.S.
Hydrologic
Areas
Atmospheric.
Erosion, Lake Huron
Direct Point 1.621
Slack
78
St. Clair
Complex 38,
LAKE ST. CLAIR
Net Loss = 15
Canadian
Hydrologic
Areas
L232 Sydertham
i 788 Thames
Detroit River OuWow 3.148
FIGURE VIII-13. Lake St. Clair average
phosphorus loads and losses
during 1975-80 (mt/yr).
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409
83W
Rouge
Complex'
42«30'
42*00*
FIGURE VIII-14. Hydrological areas used in determining mass balances.
-------
410
Over the six year period examined, the lake's total input and
output of phosphorus were nearly equal. Therefore, there was no
significant net source or sink of phosphorus in the lake during
that period.
2. Process-Oriented Models
Changes of water level caused by wind are most pronounced in
shallow lakes such as Lake St. clair. The ability to predict
wind-induced water level changes would therefore be useful, since
these changes can affect shorelines and contingent properties» A
hydrodynamic model was developed to investigate the effects of
bottom drag and wind stress on computed lake setup, and to deter-
mine the efficacy of hydro-dynamic or purely empirical approaches
to predicting water measurements. Empirical approaches by-pass
many of the calculations that are used in the hydrodynamic ap-
proach. No essential difference between the two approaches was
found, but for an empirical model to be developed, an adequate
historical data base for the site of interest must exist. The
strength of the hydrodynamic approach is that it is transferable
among lake systems.
To predict the fate and transport of contaminants in any body of
water, the movement of that water, as affected by winds or tribu-
taries, must be known or predictable. Because of this need,
several models were developed by Canadian and U.S. scientists to
predict and understand currents in Lake St. Clair. In addition,
models were developed for predicting and understanding wave dyna-
mics in Lake St. Clair since waves can resuspend sediments and
associated contaminants.
Simons and Schertzer, {Environment Canada - EC) developed a model
that predicts mean daily currents in Lake St. Clair. They found
that an important consideration in developing the model was ac-
counting for the effects of a shallow bottom on currents. Lack
of information regarding these effects has been a major impedi-
ment to the application of hydrodynamic models to shallow lakes.
They were able to develop a tentative relationship between eddy
viscosity and wind stress that aided in shallow water model
development.
Schwab and elites (NOAA) developed a particle transport model for
Lake St. Clair to answer the following questions: 1) What path
does water entering Lake St. Clair from one of the tributaries
follow through the lake before leaving the Detroit River? 2)
How long does it take? 3) How is the particle path changed by
wind-induced circulation in the lake? 4) For the meteorological
conditions during the summer and fall of 1985, what are the typi-
cal statistical distributions of these pathways? The model they
developed calculates currents on a 1.2 km grid and yields results
that are similar to those of Simons and Schertzer above. Their
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411
model can be used to mate preliminary estimates of the spatial
distribution, transport and residence times of conservative,
hazardous spills in Lake St. Clair. This model, however, only
tracks conservative, nondispersive tracers from the mouths of the
tributaries through the lake under various wind conditions.
Even though the average hydraulic residence time for Lake St.
Clair is about nine days, the residence time for conservative
particles entering the lake from the individual tributaries
ranges from 4.1 days for the Middle Channel to over 30 days for
water from the Thames River, depending on the wind conditions.
If significant contaminant loads were to enter the lake from
tributaries that have long residence times, the impact of these
contaminants might be greater than if they entered the lake from
other tributaries.
Most of the water from the St. Clair River enters the lake
through the North Channel (35%). According to the calculations,
this water tends to flow down the western shore of the lake and
never gets into the central or eastern parts of the basin. Water
from the Middle Channel tends to remain in the western third of
the lake, almost never entering the eastern half. Water from St.
Clair Flats and the St. Clair Cutoff can be dispersed almost
anywhere in the lake to the south of the shipping channel which
connects the St. Clair Cutoff with the Detroit River, A small
amount of the St. Clair inflow (5%) enters through Bassett
Channel. This water can pass through any part of the eastern
half of the lake depending on the wind conditions. The Thames
inflow tends to be confined to the eastern and southern shores
before reaching the Detroit River and it can take a very long
time to get there. Water from the Clinton River and the Clinton
Cutoff is most likely to follow the western shore of the lake
southward with the most probable paths within 3 km of the western
shore.
Water quality measurements made in Lake St. Clair by Leach (44,
45) showed two distinctly different areas in the lake, in the
southeastern part of the lake, the water quality was dominated by
the Thames inflow, which is a major source of phosphate and other
dissolved and suspended material. The central and western parts
of the lake possessed water quality similar to Lake Huron than to
the southeastern part of the lake. The pattern of water mass
distribution (45) is very close to the combined patterns of the
four main St. Clair River inflows and the Thames inflow, Bricker
et aJ. (46) examined the distribution of zooplankton in the
western half of the lake. They distinguished an area of biologi-
cal and physiochemical similarity along the western shore of the
lake that appeared to be influenced, more by the Clinton River
than the St. Clair River. The shape of this area matches quite
well with the modelled distribution pattern for water from the
Clinton River.
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412
To verify the circulation model and. lend credulity to currents
calculated by Schwab and elites, their model was tested by com-
paring model output to actual current data measured in Lake, St.
Clair in 1985. Two separate current data bases were gathered.
One involved the use of 5 drifting buoys which were repeatedly
launched and tracked in the lake. The other was the result of
several synoptic current surveys utilizing electromagnetic cur-
rent meters. Currents predicted by the circulation model were
used to simulate 16 drifter tracks. Most of the tracks were
about 2 days in length from various portions of the lake. In
most cases, the model simulated the tracks extremely well as did
a similar study by Hamblin et al.., (26). For the entire data
set, the mean root mean square {rmsj of the drifter 25% grea-
ter than that of the calculated current track. The directions
compared favorably except for a few tracks near the mouth, of the
Bassett Channel, where the model prediction over 90 degrees
different in direction when compared with the observed track.
The comparisons between current meter measurements and model-
predicted currents were even better. In nearly 100 comparisons,
60% of the variance is explained by the model prediction. The
model again to under-predict the current speeds, here by
about 30%.
Contaminant transport depends in large part on the movement of
suspended particles. Therefore, accurate computation of hori-
zontal sediment transport should rely upon the accurate simula-
tion of the vertical structure of the horizontal flow field.
Hamblin et al,, (26) developed such a three dimensional finite
element model for Lake St, Clair, Model agreement with observa-
tions was good near the lake bottom but poorer near the surface
and suggested that a more elaborate model would be needed to
accurately model vertical velocity profiles. The more elaborate
model would include the effect of surface waves.
An empirical model was developed to describe and understand the
relationship between waves and sediment settling and resuspension
(25). The importance of these relationships to our ability to
predict and understand the transport of contaminants is evident.
Statistical relationship between suspended matter and concentra-
tion and wave orbital velocity was computed. Integration of
computed resuspension rates provided an estimate of sedimentation
in sediment traps. The model-generated sedimentation rates com-
pared rather well with the sediment trap data.
Present Status of^Physical-Chemical-Biological Models
To predict the fate and behaviour of contaminants, models that
integrate physical, chemical, and biological processes are often
needed. Two such synthesis models were developed for predicting
contaminant fate in Lake St. Clair, Halfon (EC) utilized TOXFATE
and Lang, Fontaine and Hull (NOAA) utilized the U.S.EPA TOXIWASP
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413
model. TOXFATE was used to predict the spatial distribution of
seven halocarbons in Lake St. Clair, and the fate of perchloro-
ethylene in the St. Clair - Detroit River system. The TOXIWASP
model was used to predict and understand the fate of the contam-
inant surrogate Cs-137, as well as PCBs and DCS. Neither of
these models could be fully tested for Lake St. Clair applica-
tions due to a limited test data set. However, these models are
based on well documented cause and effect relationships, and as
such, could be used to forecast the fate and behaviour of con-
taminants introduced to the lake in the future. Representative
results of Halfon's Lake St. Clair TOXFATE model is demonstrated
in Figure VIII-15.
Lang and Fontaine (NOAA) developed a multi-segment, generic con-
taminant fate and transport model for Lake St. Clair. The
TOXIWASP code upon which it was based was- streamlined to make it
more specific to Lake St. Clair. Because evidence of biological
mixing in Lake St. Clair was extensive, this capability was added
to Lake St. Clair version of TOXIWASP. An extremely fast version
was created that calculates steady state contaminant concentra-
tions in seconds rather than hours. Numerous programming errors
in the original code were found, corrected and passed on to the
U.S.EPA-Athens modeling group.
Lang and Fontaine (NOAA) calibrated the transport mechanisms of
TOXIWASP using chloride and meteorological data that were col-
lected during a series of cruises in Lake St. Clair during 1974.
After obtaining reasonable agreement with the conservative
chloride ion, calibrations of contaminant dynamics was carried
out using Cesium-137. Cesium-137 was used to calibrate the
model's contaminant dynamics since Cesium-137 adsorbs to par-
ticles in a manner similar to that of many hydrophobic, organic
contaminants. Most importantly, the source function of Cesium-
137 to the lake is well known (Figure VIII-16). This informa-
tion, coupled with knowledge of the spatial and depth distribu-
tions of Cesium-137 in the sediments of the lake, provided an
excellent calibration and verification data set. Verification
results are acceptable (Figure VIII-17).
Having calibrated the TOXIWASP model for Lake St. Clair, it was
used to hindcast possible loadings of octachlorostyrene and PCBs
to Lake St. Clair. The model predicted that about 3.9 MT of OCS
had to have been loaded to the lake over a period of 12 years to
produce measured sediment concentrations (Figure VIII-18). This
finding implies that OCS was first loaded in the latter part of
1970 and is consistent with speculation to that fact. The model
also estimated that 3,400 kg of PCBs had to have been loaded to
produce measured PCS sediment concentrations (Figure VIII-19).
The model tended to under-predict the PCB values along the east-
ern and western segments of the main lake, which may indicate
additional or increased PCB sources in these areas.
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414
TRICHLOROETHYLENE
ng/L
OBSERVED JUNE 18-21
JUNE 21 f
PREDICTED
FIGURE VTII-15, Modelled and observed distributions of trichloroethylene
1984.
-------
Cs Loading to Lake Si Clair
Watershed
Watershed + Atmosphere
Watershed +Atmosphere
+Inflow from Lake Huron
1960 1970
Year
1980
*>.
»-»
tn
FIGURE VllI-16. J37Cs loadings to Lake St. Clair.
-------
Scale HI Kilometers
I i I M
4
0
8
13/Cs Concentration 1985
Surlicial (0-2 cm) Sediments
<0.5 dpm/g
0.5-1 dpm/g
1-2 dpm/g
2-3 dpm/g
FIGURE VIIM7. 137Cs concentration 1985 surficial (0-2cm) sediments.
-------
OCS Concentration 1983
Surficial <0-10 cm) Sediments
FIGURE VIII-18. OCS concentrations J983 surficial (0-JOcm) sediments.
-------
Scale in Kilometers
I I I I 1-M
0 4 B 12
•4 2" 30'
PCS Concentration 1974
Sudicia! (0-2 cm) Sediments
82°30'
Not Sampled
<5/;g/kg
5-10
10-20
20-30
OQ
FIGURE VIII-19. PCB concentration 1974 surficial (0-2cm) sediments.
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419
TOXIWASP assumes a local equilibrium between the dissolved, par-
ticle-adsorbed and bio-adsorbed chemical. Hull, Lang and
Fontaine (NOAA) modified the TOXIWASP model so that kinetic,
instead of equilibrium, reactions were simulated. This was done
to determine whether the equilibrium approach was valid in all
circumstances. Equilibrium models assume implicitly that incom-
ing contaminant loads are at local equilibrium between dissolved,
adsorbed, and bioaccumulated phases. When the same load
conditions were assumed for the kinetic model, greatest devia-
tions between the two models occurred when predicting the fate of
highly hydrophobic contaminants (Kow>106)» The kinetic model not
only required a longer time to reach steady state contaminant
concentrations, but also required a longer time to flush out the
resident contaminant mass after the input load was shut off.
Generally, one would expect problems with an equilibrium approach
when the time to equilibrium is longer than the residence time of
the water body in question.
Halfon (EC) used TOXFATE to predict the fate of perchloroethylene
(PERC) in the St. Glair - Detroit River system. The model sug-
gested that about 82% of the PERC would be volatilized, and the
remainder, less 1% that would remain in sediments, would enter
Lake Erie. Comparison of simulated and measured PERC concentra-
tions show reasonable agreement. Since so much of the PERC is
volatilized before it reaches the open lake, Halfon's model does
not realistically demonstrate what may happen to a nonvolatile
spill entering the lake.
In the case of a nonvolatile spill travelling the lake from the
St. Clair River to the Detroit River outflow, the dilution of the
concentration would be determined mainly by the strength of
horizontal turbulent mixing. There were no direct measurements
of horizontal diffusion in Lake St. Clair reported by any of the
UGLCCS activities. However, two investigations (17,53) have
employed a vertically integrated model of transport and diffusion
of a conservative substance, chloride, to infer an effective
horizontal diffusion coefficient of 10"1"5 cm2/s. Because this
quantity has been deduced from vertically averaged concentration
in the possible presence of current shear over the water column,
these authors have termed the diffusion coefficient as a disper-
sion coefficient.
The particle trajectory measurements and models reported for
August 12, 1985 by Hamblin (47) and by the Modeling Workgroup
Report (53) for September 1985 demonstrated that particles would
take about four days to cross the lake. If a slug of contamina-
ted river water had dispersed longitudinally to a length of 5 Km
in the St. Clair River, then in the four day transit to the out-
flow region it would have grown by about 7 km to a characteristic
patch size of 12 km under the assumptions of average mete-
orological conditions and horizontal Gaussian diffusion. In
turn, this patch would take about two days to pass across the
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420
water intakes near the outflow. Finally, the average concentra-
tion would be about 20% of the original concentration entering
the lake.
3. Summary
The modeling work on Lake St. Clair has made much progress during
the study period from the water level fluctuation models (storm
surge) to the coupled contaminant-circulation models. However,
more work is required before the models could be used as
effective water management tools. Testing of the models with
parameters additional to PCS and OCS, more realistic treatment of
sediment water interaction, and linkage of the models to lake
biota are as necessary steps before the models can reliably
assess the ecological responses to reductions in loadings to the
lake. Although not developed for operational purposes, the mod-
els TOXFATE and TOX1WASP, with additional effort, could be
used to predict the trajectories and dilutions of spills of
either volatile or nonvolatile substances occurring on the lake
or entering from the rivers,
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421
P. OBJECTIVES AMD GOALS FOR REMEDIAL
The following objectives and goals are grouped according to
media, However, remedial actions are likely to have multimedia
effects. For example, elimination of point and nonpoint sources
of contaminants can be expected to reduce concentrations in
water, sediments and biota, even though direct remediation of
contaminated sediments or biota may be infeasible. Some objec-
tives may be reached, therefore, upon attainment of one or more
others.
1, Water Quality
Since the water quality of Lake St. Glair is dominated by that of
the St. Clair River, remedial programs directed towards the St.
Clair River will also improve water quality in Lake St. Clair,
Objective 1. Full implementation of recommendations for the St.
Clair River presented in Chapter ¥11 of this
report for the elimination of industrial, munici-
pal and. nonpoint sources of contaminants to the
St. Clair River, particularly HCB, HCBD, OCS, Hg,
and. Pb.
Excluding input from the St. Clair River, phosphorus loadings to
Lake st, Clair are dominated by nonpoint sources. For example,
in the'Thames River 93% of the loading of the nonpoint source
type. In water samples from Lake St. Clair tributaries, nearly
all contained phosphorus in of the PWQO of 30 ug/L.
Improved agricultural practices such as conservation tillage,
elimination of over-fertilization and control of feedlot
effluents are identified as actions relevant to reduction of
nonpoint source loadings,
Objective 2. Reduction, of phosphorus loadings from point and
nonpoint sources in Michigan and. Ontario to assist
in meeting target load reductions for Lake Erie,
The Mt. Clemens WWTP identified as having average phosphorus
concentrations in its effluent exceeding the GLWQA objective of
1,0 mg/L for municipal water treatment facilities. Municipal
treatment plants discharging to the Thames River in excess of
this guideline in 1986 were Chatham, Ingersoll (new), City of
London (Adelaide, Greenway, Oxford, Pottersburg Vauxhall) and
the Strathroy Town Plant.
Objective 3. Necessary and sufficient technology and operation
procedures at all wastewater treatment facilities
to meet the target concentration of phosphorus in
the effluent of no more than 1.0 mg/L.
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422
Excessive unit area loading of pesticides from agricultural lands
into tributaries of Lake St. Clair was identified. Some areas
were identified to be of particular concern.
Objective 4. Reduction in the loadings of pesticides from all
tributaries.
Objective 5. Identification and elimination of the source of
DDT and metabolites to the Milk River.
water quality in several tributaries was reduced by the presence
of heavy metals. Cadmium concentrations generally exceeded the
GLWQA specific objective and PWQO of 0.2 ug/L, and some were
greater than the chronic AWQC of 1.1 ug/L in the Belle, Sydenham,
Thames and Clinton Rivers. Also, some lead concentrations were
in excess of the chronic AWQC of 3.2 ug/L in the Belle and
Sydenham Rivers, and in the Thames River some exceeded the acute
of 82 ug/L.
Objective 6. Identification and elimination of all point
sources of Hg, Pb and Cd in the watersheds of the
Clinton, Thames and Sydenham Rivers.
Objective 7. Elimination of combined storm sewer overflows
which will reduce contributions of P, Pb, Cd, Hg
and PCBs to Lake St. Clair tributaries.
2. Sediment Quality
Reductions in industrial loadings of mercury in the St. Clair
River have resulted in dramatic improvements since 1970 in the
bottom sediments. However, surface concentrations in bottom
sediments still exceed the IJC and OMOE guidelines of 0,3 ppm and
contain values classified as "polluted" by the U.S.EPA Classifi-
cation Guidelines. Since recent mercury concentrations of bottom
sediment samples do not appear to be reducing as quickly as in
the earlier studies there is some concern that unknown tributary
sources exist. The mass balance studies of Section E indicate a
net outflow of mercury from Lake St. Clair. Since the tributary
loadings are not known, it is impossible to determine the source
of the mercury.
Objective 8. Identification and elimination of continuing
sources of Hg to the St. Clair River.
Objective 9. Identification and elimination of point and non-
point, sources of Hg to Lake St. Clair tributaries.
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423
Of the other metals, only zinc and copper exceed the OMOE guide-
lines in the sediments of the open lake and would result in a
classification of sediments as moderately polluted.
Objective 10. Reduction in heavy metals concentrations in sur-
ficial sediments of Lake St. Clair to levels sup-
porting a classification of "not polluted" by
OMOE. U.S.EPA and IJC Guidelines.
The sediment surveys revealed that PCBs did not exceed the guide-
lines in the open lake. However, guideline concentrations were
exceeded in some of the tributary sediments including the Cot-
trell Drain, the mouth of the cutoff channel of the Clinton River
and the Sydenham River. Other organic contaminants with specific
guidelines such as BCD, OCS and pesticides were identified in
sediments from the open lake and tributaries. In general, the
sampling of all tributary sediments was incomplete, so there
could be cases of excesses of certain compounds not reported or
cases of compounds that were sampled which have no guidelines.
Objective 11. Elimination of DDT in sediments at the mouth of
the Milk River.
Objective 12. Identification and elimination of sources of PAHs
in sediments from the Milk River, Cottrel Drain,
Clinton River and Frog Creek.
Objective 13. Reduction in PCS concentrations at the mouths of
Lake St. Clair tributaries such that the sediments
would be classified as "not polluted" by OMOE,
U.S.EPA and IJC Guidelines.
3. Biota and Habitat
The most significant impaired use of Lake St. Clair waters is the
restriction in the consumption of sports fish. A joint fish
consumption advisory between Ontario and Michigan remains in
effect for the larger specimens of 18 species of sports fish
(33). Levels of mercury in excess of Canadian governmental
guidelines have been identified as the main contaminant respon-
sible for restricted fish consumption. Because the concentra-
tions of mercury in the tissues of sports fish have declined
dramatically since 1970, programs to control the major historical
sources of mercury appear to be satisfactory. However, since
tributaries were not monitored, smaller, uncontrolled sources
could be contributing to the loading.
Objective 14. Reduction in mercury concentration in Lake St.
Clair fish to less than 0.5 ntg/kg, and subsequent
elimination of the fish consumption advisory based
on mercury contamination.
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424
Objective 15. Continued reduction in PCB concentrations in fish
to meet the GLWQA specific objective of 0,1 mg/kg
for protection of birds and animals which consume
fish.
In addition to being an important sports fishery, Lake St. Clair
is a major duck: hunting area. The habitat necessary for wildfowl
resting, feeding and breeding is provided by the extensive wet-
lands around Lake St. Clair particularly in the Lake St. Clair
Delta. More than 9,000 km of wetlands were lost to shoreline
development in Lake St. Clair between 1873 and 1968. Losses are
most evident in the Clinton River, the St. Clair River Delta and
the eastern shore of the lake. In 1979 the state of Michigan
prohibited the modification of a wetland over 5 acres in size to
restrain encroachment into the wetland areas. In Ontario, sub-
sidies for engineering projects still encourage drainage of wet-
lands and their conversion to agricultural use. However, tax
relief that favors retention of the wetlands has recently (1987)
been granted to wetland owners. Although diked Ontario wetlands
are effectively managed for waterfowl hunting, there is a loss of
other wetland functions, particularly those related to fish prod-
uction.
Objective 16. Preservation of remaining wetlands surrounding
Lake St. Clair, and protection of then from
further diking, filling or other forms of destruc-
tion.
4. Management Issues
In the Clinton River, the concentration impact of contamin-
ants are sufficiently severe for the area to be recognized as an
IJC "Area of Concern", A Remedial Action Plan is in the process
of being developed by the State of Michigan for restoring benefi-
cial uses of the area. This plan will contain details of the
problems, their extent and causes, a schedule for remedial
actions to be implemented. Plans for further monitoring for
results of the actions will also be included.
Objective 17. Pull implementation o£ the Remedial Action Plan by
Michigan and other responsible agencies for clean-
up and restoration of uses in the Clinton River.
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425
Although the Thames River is not presently one the IJC Areas of
Concern, many agricultural and industrial contaminants have been
identified in the water and sediments, and impaired uses were
identified that are similar to those for 'the Clinton River. The
absence of the Thames River on the AoC list should not imply that
the area is contaminant-free.
Objective IS. Preparation and implementation by Ontario of a
Plan for the restoration of impaired uses in. the
Thames River. The Plan should address issues of
agricultural runoff of nutrients and pesticides,
CSOs in the watershed, and sources of heavy metals
in the tributary.
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G. ADEQUACY OF EXISTING AND OPTIONS
1. Projection of Ecosystem Quality Based on Present
Control Programs
In general, the ecosystem quality In Lake St. Clair is adequate
for the maintenance of a desirable biological community that
includes the production of sport fish. Impairment of the bio-
logical communities due to contaminants appears to exist only in
localized areas around the mouth of tributaries (although
some contaminant levels in fish are sufficient to force the is-
suance of a fish consumption advisory by Michigan and Ontario),
and the loadings of agricultural nutrients have not caused severe
eutrophication problems. Loss of habitat due to wetlands de-
struction, however, has been extensively documented.
The specific concerns addressed in Section B, above, relate most-
ly to contaminants in the Lake St. Clair basin, can be
grouped into three major categories: nonpoint source loading of
contaminants and nutrients, contaminants in tributary water and
sediments, and contaminants in fish. Of these categories, insuf-
ficient data exist to determine trends in the loading of con-
taminants from nonpoint sources, including tributaries. However,
the concentration of mercury in the edible portions of northern
pike, white bass and yellow perch from Lake St. Clair, and of
PCBs in walleye from 1970 through 1984 have been declining at a
geometric rate {7), indicating that control programs for these
two contaminants have been at least partially effective. Evi-
dence for continuing loadings of nutrients, pesticides, PCBs, and
heavy metals implies that the rate of decline in contaminant
burdens in fish could be greater were no additional contaminants
entering the system.
Although the impact of the loading of the UGLCCS parameters to
Lake St. Clair directly may appear to be minimal, consideration
musn be given to the ultimate impact on Lake Erie populations.
Lake St. Clair may be storing HCB and HCBD, but it is a source
for PCBs and total phosphorus, These contaminants are then
transported through the Detroit River and should be accounted as
loadings to Lake Erie,
2, Assessment of Technical Adequacy of Control Programs
Present Technology
In 1985, inputs of nine of the UGLCCS parameters were determined
to be significant, resulting in impacts to either water, sediment
or biota quality. These were cadmium, copper, cyanide, lead,
mercury, nickel, PCBs, phosphorus and sine. In general, dis-
charge of these parameters from point sources was not controlled
by limitations or objectives. All of the surveyed point sources
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427
were municipal facilities, and all were subject to discharge
limitations mainly for conventional parameters. However, for
many of the parameters, point sources were not the most signifi-
cant contributors. Rather, the largest loading was obtained from
unidentified sources discharging through tributaries.
The control of phosphorus has been the main approach of the U.S.
and Canada to remediating the eutrophication of the Great Lakes.
All municipal plants surveyed in the Lake St. Clair basin had
average concentrations less than 1 mg/L, except the Mt. Clemens
WWTP. The GLWQA Objective, the Canadian Municipal effluent Ob-
jective, and the standard Michigan permit limit for phosphorus is
1.0 mg/L monthly average in sewage plant effluent. The Mt.
Clemens WWTP exceeded the 1 mg/L average frequently in 1986 ac-
cording to self-monitoring data. An expansion and improvement of
the facility is underway (1987) which will enable the plant to
meet the limitation.
Excluding input from the St. Clair River, the Thames River
provided the largest loading of phosphorus to Lake St. Clair,
exceeding the contributions made by the point sources by a factor
of about 16. Similarly, the Sydenham and Clinton Rivers exceeded
the point source loadings by factors of 7 and 3 respectively.
Atmospheric loading to the lake was less than 5% that from the
Clinton River. This indicates that these rivers were receiving
substantial inputs of phosphorus from other sources, and that
controls were not adequate or effective. The most probable route
is drainage of phosphorus from agricultural uses and livestock
operations. The application rates in Michigan and Ontario were
found to be 2 and 3 times the recommended rates, respectively,
and the use of conservation tillage techniques were not
widespread.
Likewise, excluding input from the St. Clair River, the Thames
River provided the largest loading of cadmium to Lake St. Clair,
almost twenty times greater than all point sources combined. Of
the three point sources that were found to discharge cadmium,
none did so to the Thames River. The loading from the Sydenham
River was 34 times greater than accounted for by the Wallaceburg
WWTP, and the loading from the Clinton River was 11 times that of
the two WWTPs that discharged Cd. None of the facilities had
site-specific permit limits or objectives for Cd. However, the
evidence indicates that all three rivers were receiving signifi-
cant inputs of cadmium from other sources, perhaps from air depo-
sition or use of cadmium-contaminated phosphate fertilizer (48).
Estimated loading of Cd to Lake St, Clair from the atmosphere was
approximately the same at that from each of the Sydenham and
Clinton Rivers.
The Thames River also provided over 100 times the loading of Pb
than all the surveyed point sources combined, and three times the
loading from the St. Clair River. The Clinton and Sydenham
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428
Rivers each contributed more than 10 times the quantity of lead.
than did the point sources, and the atmospheric loading was es-
timated to be similar to that of the Clinton and Sydenham Rivers.
Clearly the loading of lead to Lake St. Clair from unidentified
sources in the tributary basins was more significant than from
the point sources, which did not have effluent limitations or
objectives for lead,
Mercury contamination in Lake St. Clair has resulted largely from
historical inputs through the St. Clair River, However, inputs
may still be occurring, as evidenced by sediment surveys and by
the mass balance calculations presented in Section E, above.
Although none of the point sources surveyed had effluent limita-
tions or objectives for the discharge of mercury, point source
loadings accounted for only 0.015? Kg/6, of an estimated 2.3 kg/d
source in the Lake St. Clair basin. The source could include the
contaminated sediments themselves. Loading estimates from the
tributaries and atmosphere were not available for this study.
The Clinton River also contributed significant loads of PCBs to
Lake St. Clair. Both the Warren WWTP and Mt. Clemens WWTP serve
large communities with substantial industrial bases, and both had
industrial pretreatment programs in place. Neither reported
specific sources of PCB in their service areas, and neither had
permit limits for PCB at the time of the survey. PCBs were not
found in three Ontario WWTPs. Although the Canadian MDL was
1,000 times greater than that in the- U.S.,, the PCB concentrations
in the U.S. sources were much higher than the Canadian MDL.
Michigan and Ontario both recommend zero discharge of PCB.
Michigan is now using a water quality based effluent limit of 1.2
X 1Q~5 ug/L in some NPDES permits, the allowable effluent guide-
line calculated using the state's Rule 57(2). The level is below
any current MDL, so the permits also contain an interim limit of
detection at 0,2 ug/L, the MDL commonly achieved with routine
monitoring methods. The permittee is further required to develop
a plan to meet the water quality based limit.
The Warren WWTP, Mt. Clemens WWTP, Rochester WWTP and Pontiac
WWTP all operate an industrial pretreatment program, receiving
waste water from industries in their area. Due to the quantities
of contaminants coming from these facilities, however, the pre-
treatment requirements of these facilities and/or the compliance
by the contributing industries with the requirements may be
suspect.
Similarly, the Chatham WWTP receives industrial waste water, and
it provided the largest loading of oil and grease and the third
largest loading of nickel to the Lake St. Clair Basin. The
quality of the waste water it receives may also be suspect and
not in compliance with the Ontario By-Law to control the receipt
of contaminants from industrial sources.
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429
Best Available Technology
Discussions concerning the adequacy of "best available
technology" (BAT) for reducing or eliminating loadings of con-
taminants to Lake St. clair are premature until specific sources
of the loadings are defined. No direct industrial discharges
occur to Lake St. Clair, but elevated levels of contaminants were
found in the water and sediments of many tributaries, implying
that sources may exist upstream. Should specific sources of
contaminants be identified, then an assessment of the impact of
BAT may be Made for that industry on the receiving stream and on
Lake St. Clair.
Because phosphorus is found to be coming from agricultural prac-
tices, the implementation of conservation tillage and reduced
fertilizer application rates should greatly reduce the magnitude
of the loadings of P to the system. Likewise, reductions in
phosphorus loadings from municipal and industrial effluent, if
needed, can be achieved with improved facility design and opera-
tions. Urban nonpoint source runoff, however, may be more dif-
ficult to control.
Additional efforts are needed to identify the sources of mercury
loadings to Lake St. Clair, If internal loadings from the con-
taminated sediments are found to be significant, active control
technology might be infeasible. Techniques for dealing with in-
place polluted sediments is a topic for current research, and
demonstration projects are expected to be established within the
next several years by U.S.EPA. However, technology for treating
contaminated sediments is expected to be applicable to localized
areas, including harbors and restricted tributary mouths, but not
appropriate for a whole lake basin. Given the rather short resi-
dence time of sediments in Lake St. Clair, in the order of 10
years, the problem o£ contaminated sediments could be resolved
for Lake St. Clair through natural processes. However, continued
problems would be expected in the western basin of Lake Erie.
3. Regulatory Control Programs Applicable to Lake St. Clair
A detailed discussion of regulatory programs in the UGLCCS
regions may be found in chapter III. The following programs have
particular impact on Lake St. Clair. The Clinton River is one of
the Areas of Concern as designated by the International Joint
Commission. As part of the effort to develop and implement a
Remedial Action Plan (RAP) for the river basin, the State of
Michigan has begun intensive remedial activities in the area
(49). All major NPDES permits in the Clinton River basin were
reviewed and new water quality based or technology based effluent
limits (whichever was more restrictive) were developed in 1985.
Metals, organics and conventional pollutants were included. A
pretreatment program for process industrial wastewater was im-
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430
plemented. throughout the Clinton River basin as of 1987, and
upgrades to four WWTPs were completed in 1986 and 1987. Pull
details of the remedial programs and schedule for implementation
will be included in the RAP, which is expected to be submitted to
the IJC in 1988.
Where stormwater is determined to impact water quality in
Michigan, the stormwater provisions (section 405) of the U.S.
Water Quality Act of 1987 will be implemented to correct the
problem. The State 305 (b) report will be reviewed in 1988 to
determine if any of the Upper Great LaM.es connecting Channels
areas are impacted by stormwater runoff.
Some technical and educational programs for farmers are in exis-
tence. For example, a Canadian Federal and Provincial effort
called the Soil and Water Environmental Enhancement Program
(SWEEP) encompasses all aspects of soil and water conservation.
Within the SWEEP program, a provincial program called the Ontario
Soil Conservation Environmental Protection Assistance Program
exists which will financially assist the farmer in implementing
soil and water conservation practices with up to 67% funding, A
Land Stewardship Program has also recently been announced to
assist farmers in the implementation of conservation techniques.
All of these programs should assist in achieving reduced phos-
phorus and pesticide contamination in streams.
The preservation of wetlands in Lake St. Clair has been assisted
by three relatively recent laws enacted by the State of Michigan:
1) The Great Lakes Submerged Lands Act (1955) which prohibits
constructing or dredging any artificial body of water that would
ultimately connect with a Great Lake, and which requires a permit
from to fill any submerged lands, including Lake St. Clair;
2) Shorelands Protection Management Act (1970) which desig-
nates wetlands adjacent to a Great Lake as environmental areas
necessary to preserve fish and wildlife,- and 3) The Goemaere-
Anderson Wetland Protection Act (1979) which regulates wetlands
through several laws relating to Shorelands submerged lands
(36) ,
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431
H.
A. Industrial and Municipal Point Source Remedial Recommendations
1. Ontario and Michigan should incorporate the Great Lakes
Water Quality Agreement's goal of the virtual elimination
of all persistent toxic substances into their respective
regulatory programs.
2. The City of Mt. Clemens should determine the source of
PCBs, total phenols and mercury in the WWTP effluent and,
through pretreatment or In-plant controls, reduce the con-
centrations of these pollutants to acceptable levels,
Effluent limitations for these parameters should be con-
sidered. Phosphorus concentrations in the effluent should
be lowered to meet the 1 mg/L Great Lakes Water Quality
Agreement objective,
3. Site specific effluent limitations for total cadmium, total
copper, total chromium and total nickel to protect the
water quality for the Sydenham River and Lake St. Clair
should be developed for the Wallaceburg WWTP. The opera-
tion of the plant should be optimised to meet the Ontario
industrial effluent objective of 10 mg/L for ammonia,
4, The Warren WWTP should determine the source of PCBs in its
effluent and take the necessary steps to reduce the con-
centration to acceptable levels,
8, Nonpoint Source Remedial Recommendations
5, Agricultural areas with high rates of wind erosion need to
be targeted for assistance due to the characteristics of
wind transported soil (fine textured, high enrichment
ratio, and high organic matter content) its ability to
transport nutrients and mgriehemicals, The relatively low
erosion rates and high percentage of wind erosion in com-
bination conservation tillage the most practical con-
servation practice to be recommended. The primary reasons
for this are the effectiveness of residue cover in reducing
wind erosion the low cost of implementing the practice.
Conservation tillage is recognized as being highly cost-
effective and physically effective in areas of sandy soils
where wind erosion is a problem. If conservation tillage
were applied to all cropland eroding over the soil toler-
ance level, with a resulting compliance with the tolerance
level, a 32% reduction in phosphorus loading from cropland
could be achieved,
6. Rural landowners need to implement,' with the assistance of
Federal, State and Provincial governments, a comprehensive
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432
soil and water management system in order to control, at
source, the contribution of conventional and organic pol-
lutants including manure and pesticides to surface and
groundwater. Specifically:
a. Agricultural and conservation agencies need to accele-
rate the implementation of control technologies through
technical, financial and information/education
programs. There is a need for extension, education and
incentives to persuade farmers to implement conserva-
tion management systems including cropping, tillage and
structural practices, nutrient and pesticide management
technology, thereby reducing the movement of soil,
conventional pollutants and contaminants off their land
into the waterways.
b. Environmental and agricultural agencies should assess
the ade<|uacy of existing controls, regulations and
permits for the use of fertilizer and pesticide
products.
c. Specific programs, especially in Macomb County, MI,
should be directed at reducing the excessive levels of
phosphorus fertilization, improving the management of
animal waste disposal and storage, and educating pest-
icide users with respect to handling, application and
storage of pesticide products.
7. Future assessment and control of agricultural nonpoint
sources of pollution would be facilitated by compatible
Federal, State and Provincial monitoring data and more
frequent flow-weighted tributary monitoring data. The
small water quality monitoring data set available for tri-
butaries indicated the need for increased sampling for all
parameters, especially flow weighted data. The lack of
samples in high flows created difficulty in calculating
representative loads as well as understanding seasonal
patterns of pollutant transport. More samples on high flow
days would improve the basis for pollution control strat-
egies .
8. Macomb and St. clair Counties, Michigan, should be targeted
for fertilizer management. U.S.EPA Region V has requested
the USDA-SCS Michigan State Office to develop standards and
specifications for a nutrient, best management practice
that would protect ground and surface waters as well as
sustain crop production. The Michigan Departments of Agri-
culture and Natural Resources are developing a joint action
plan to manage livestock waste problems that includes best
management practices for proper animal disposal that gives
attention to air and water pollution from concentrated
animal operations. This program may require a system of
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433
permits for concentrated feeding operations,
9. The CSOs from municipal wastewater treatment plants should
be intensively surveyed to determine their contribution of
pollutant loadings to the surface waters. In the long term
(due to enormous cost) combined sewers in all munici-
palities should be eliminated. In the interim, the munici-
palities should institute in-system controls to minimize
the frequency and volume of overflows.
10. The Michigan Pollution Emergency Alerting system and the
Ontario Spills Action Centre spills reports should be im-
proved so that all information on recovery, volume (if
known) and final resolution are fed back to the central
reporting system to complete each report for inventory
purposes.
11. The Superfund Site Investigations to be undertaken at
Selfridge ANGB should focus on groundwater and surface
water runoff impacts upon Lake St. Clair and the Clinton
River, In the event that this site is not included on the
U.S. National Priorities List, the 'State of Michigan should
place high priority upon cleanup on this site,
12. Michigan should require groundwater monitoring as a permit
condition for the Sugarbush solid waste landfill.
13. Michigan should include groundwater monitoring as part of
the RCRA Generators permit for G and L Industries,
C. Surveys, Research and Development
14. Data interpretation would be facilitated by the development
of more complete water quality objectives for the organic
pollutants pesticides that are used extensively by the
agricultural industry. Currently, water quality objectives
do not exist for many parameters that are measured. Al-
though meeting water quality objectives does not guarantee
"no impact" of a contaminant, the objectives do provide a
point of reference for assessing the relative potential for
negative impacts of various contaminants in the aquatic
system.
15, The presence of organic contaminants (PCBs, HCBs DCS)
in the Canadian tributaries illustrates the need to locate
the contaminant sources.
16, The cadmium content of the phosphate fertilizer that is
being used on agricultural lands should be determined.
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434
17. A study of atmospheric deposition of organic contaminants,
particularly PCBs, to Lake St. Clair and to the tributary
watersheds would provide quantitative information on load-
ing of these contaminants to the lake. The loading esti-
mates are Important for mass balance calculations and the
identification of unknown sources of the contaminants,
18. Urban runoff was identified as being a potentially major
nonpoint source of many parameters,including PCBs, oil and
grease, zinc, mercury, copper and nickel. The loadings
from urban runoff, however, were based on contaminant con-
centrations from Canadian urban areas outside of the Lake
St. Clair basin. Therefore, the loading information
provide only a general potential for urban runoff to con-
tribute contaminants to Lake St. Clair. A study should be
performed to determine the contribution actually by
urban runoff on the Michigan shore where the shoreline is
more urbanized than is that of Ontario,
19. The sediments near the mouth of the Clinton, sydenham and
Thames Rivers contain contaminants that may be impairing
benthic communities. Studies are needed to document
possible impairment of benthic communities of these sites.
Appropriate actions to remedy any observed, problems will
need to be defined. Techniques technologies for remedi-
ating in-place polluted sediments should be developed.
20. Recognizing that the biological effects of a substance are
dependent in part on the chemical species of that sub-
stance, studies should be conducted' to identify the
chemical species and valances of the heavy metals in Lake
St, Clair and its tributaries. For those forms which are
present but Jor which toxicity information is lacking in
the literature, toxicity and bioaccumulation experiments
should be conducted on appropriate target organisms*
21. The evaluation of the point source data has been conducted
on a parameter by parameter basis. In order to assess the
quality of whole effluents, it is recommended that biomon-
itoring studies, both acute and chronic, be conducted at
the major facilities (Wallaceburg WWTP, Chatham WWTP,
Warren WWTP, and Mt. Clemens WWTP).
22. An inventory of all point sources, hazardous waste sites,
urban and rural runoff, and spills discharging or poten-
tially discharging to the Clinton River should be col-
lected. These facilities, sites or incidents should then
be examined for their potential to contribute chemicals to
the Clinton River.
23. A more complete analysis of sediment, water and biota
quality along the entire stretch of the Clinton River is
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435
needed. Such information would establish the locations of
sources of contaminants,
24. The Thames and the Sydenham Rivers were found to be major
contributors of phosphorus, ammonia, lead and cadmium. An
inventory of all point sources, hazardous waste sites,
urban and rural runoff and spills discharging to these
rivers should be collected. These facilities, sites or
incidences should then be examined for their potential to
contribute chemicals to the rivers.
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436
I. LONG TERM MONITORING
1. Purposes for Monitoring and Relationships Between UGLCCS and
Other Monitoring Programs
A presentation of the purposes for monitoring and surveillance
activities is included under Annex 11 of the 1978 GLWQA, and a
discussion of considerations for the design of a long term moni-
toring program can be found in Chapter 1 of the Report of the
Niagara River Toxics Committee (50)« Because the focus of the
UGLCC Study was toward remedial actions to alleviate impaired
uses of the Connecting Channels System, long term monitoring
recommendations will likewise focus on the evaluation of trends
in environmental quality in order to assess the effectiveness of
remedial actions. In general, post-UGLCCS monitoring should be
sufficient to 1) detect trends in system-wide conditions noted by
the UGLCCS, and 2) detect changes in ambient conditions which
have resulted from specific remedial actions. Monitoring pro-
grams should be designed to specifically detect the changes in-
tended by the remedial actions so as to ensure relevance in both
temporal and spatial scales.
Two major programs sponsored by the IJC also contain plans for
long term monitoring: the Great Lakes International Surveillance
Plan {GLISP) and the Areas of Concern Remedial Action Plans (AoC-
RAPs). The GLISP for the Upper Great Lakes Connecting Channels
is presently incomplete, pending results of the UGLCC Study, but
it is expected to provide monitoring and surveillance guidance to
U.S. and Canadian agencies responsible for implementing the pro-
visions of the GLWQA that include general surveillance and
research needs as well as monitoring for results of remedial
actions.
Lake St. Clair is not one of the AoCs, although the Clinton River
in Michigan is, and a RAP is being developed by Michigan for the
Clinton River. The RAP will present details of uses impaired,
sources of contaminants, specific remedial actions, schedules for
implementation, resources committed by Michigan to the project,
target clean-up levels, and monitoring requirements. Results and
recommendations coming from the UGLCC Study will be incorporated
extensively into the RAP, which will then be the document that
influences Michigan programs in the Clinton River. The recommen-
dations for long term monitoring that are presented below are
intended for consideration and incorporation into either or both
the GLISP for the Upper Great Lakes Connecting Channels, and the
RAP for the Clinton River.
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43?
2. System Monitoring for Contaminants
Water
Knowledge of the concentrations of the principal contaminants in
the water of Lake St. Clair should be used to indicate general
exposure levels for the biota, to identify changes and trends
over time in the concentration levels, and to be used for general
assessment of contaminant impacts. The parameters to be moni-
tored include phosphorus, PCBs, mercury, lead, and cadmium, Hear
tributary mouths, concentrations of ammonia, total phenols, pest-
icides, Cu, Ni and PAHs should also be determined. Monitoring
stations should be located to coincide with identified water use
areas, such as biota habitat, and with contaminant entry points
to the lake. Suggested locations include the mouth of the St.
Clair River at Port Lambton, around the St. Clair Delta, at the
mouth of the Clinton, Sydenham, and Thames Rivers, and at the
head of the Detroit River. Sampling frequency should be
influenced by the variability in contaminant sources. Spring
high flow conditions and late summer low flow conditions would be
expected to bracket the normal seasonal variability in flow that
could influence measured contaminant concentrations.
A mass balance approach to contaminant monitoring will help to
identify any changes in the contaminant mass over time, and it
will provide the basis for targeting future remedial actions by
providing a comparison of the magnitude of the sources. A mass
balance analysis should be conducted approximately once every
five years, assuming that some effective remedial action has been
implemented against one or more sources such that the total load-
ings of contaminants, or the relative contribution of the sources
to the loading, has changed. The sources to be measured should
include:
1) Head and mouth transects. The number and location of
stations should relate to measured and predicted plume
distributions. Suggested locations include the mouth of
the St. Clair River at Port Lambton and the head of the
Detroit River. Dispersion modeling and past sampling
results should be used to predict contaminant concentra-
tions and therefore to establish appropriate collection and
analytical methodology. Both dissolved and particulate
fractions should be analyzed. The quantity of suspended
sediment flux should also be measured.
2) Municipal and industrial point sources. No direct in-
dustrial sources are considered to be major contributors of
contaminants to Lake St. Clair. The principal municipal
sources all discharge to tributaries. Thus, special moni-
toring consideration should be given to the Sydenham,
Thames and Clinton Rivers to fully address municipal load-
ings of the contaminants.
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438
3) Tributaries. Efforts should be focused on seasonal and
storm event loadings of contaminants to Lake St. Clair from
the Clinton, Sydenham and Thames Rivers. Tributary mouth
stations should be sampled and analyzed for both dissolved
and sediment-associated contaminant loadings.
4) CSOs and Urban Runoff. To provide an estimate of con-
taminant mass loadings expected during storm events, oc-
casional studies on selected urban drainage areas should be
conducted, particularly for the Michigan shoreline.
5) Groundwater inflow. The quantity and quality of potential
contaminant releases from waste disposal sites adjacent to
Lake St. Clair or its tributaries should be determined.
6) Sediment transport. Efforts to mea.sure and model sediment
transport to, within and from Lake St. Clair should be
continued. The quantity of contaminants being desorbed from
the sediments should be determined in order to assess load-
ings from these in-place polluted sediments.
7) Atmospheric deposition. Monitoring of wet and dry atmos-
pheric deposition to Lake St. Clair should continue, and
should be expanded to include organic contaminants, vola-
tilization losses of organics should also be quantified.
Sediments
Monitoring of sediments for concentrations of contaminants should
be conducted periodically throughout Lake St. Clair in order to
assess both the trends in surficial contaminant concentrations
and the movement of sediment-associated contaminants within the
Lake. The grid used by the U.S. Fish and Wildlife Service during
the 1985 survey would be appropriate for consistency in sampling
sites and sediment composition. An analysis of sediment chem-
istry including bulk chemistry, organic and inorganic contamin-
ants, and particle size distribution should be conducted every
five years, in conjunction with a biota survey (see "habitat
monitoring" below).
In Lake St. Clair, particular attention should be given to sedi-
ment concentrations of PCBs and mercury. Additional stations
should also be established at the mouth of the Clinton, Sydenham
and Thames Rivers and at Chenal Ecarte to track effects of
remedial actions in the tributary watersheds to reduce loadings
of these materials.
Because the grid stations are distributed throughout the river
reach and are associated with appropriate habitat for a sensitive
benthic invertebrate (Hexagenia), the periodic survey will allow
assessment of 1) contaminant concentrations in the river sedi-
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439
merits throughout the river reach, 2) relative movement of the
contaminants within the river sediments between surveys, and 3)
correlation of contaminant concentrations with benthic biotic
communities.
The sediments at any stations established at the mouths of tribu-
taries to Lake St Clair should be monitored for organic and
inorganic contaminants on an annual or biannual basis when sig-
nificant remedial actions are implemented within the watershed of
the tributary. In order to trigger the more frequent sediment
monitoring program, the remedial actions should be expected to
measurably reduce loadings of one or more particular contaminants
via the tributary.
Biota
Long term monitoring of concentrations of contaminants in biota
will provide a time series useful to track the bioavailability of
contaminants to selected representative organisms, Three long
term monitoring programs are already in place and should be con-
tinued :
i) Annual or Hi-Annual Monitoring of £port Fish,
This program should focus especially on PCBs, mercury and/or
other contaminants {e.fl*. dioxins and dibemof urans) that are
considered to be known or suspected health hazards. The monitor-
ing should be continued regardless of the differences that may be
observed between acceptable concentrations or action levels that
may be established by governmental agencies and the measured
contaminant concentrations in the fish flesh. As a link between
human health concerns and integrated results of remedial programs
to reduce contaminants in the UGLCCS system, this program is
critically important.
ii) Spottail Shiner Monitoring Program,
This program is designed to identify source areas for bloavail-
able contaminants. In locations where spottail shiners contain
elevated levels of contaminants, additional studies should be
conducted to identify the sources of the contaminants,
upstream studies in tributaries may be required, Spottails sho-
uld also be employed to confirm that remedial actions upstream to
a previous survey have been effective in removing or reducing the
loading of one or more contaminants.
iii) Caged Clams Contaminants Monitoring,
Caged clams should continue to be used at regular time intervals,
perhaps in conjunction with spottail shiners, to monitor inte-
grated results of remedial actions to reduce contaminant loadings
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440
to the water. Clams may be located at tributary mouths and down-
stream of suspected source areas. Repeated assays from the same
locations should confirm results of remedial actions,
3, Sources Monitoring for Results of Specific Remedial Actions
Remedial actions intended to reduce concentrations and/or load-
ings of contaminants from specific point sources generally re-
quire monitoring for compliance with the imposed criteria or
standards for permitted contaminants. The monitoring may be
conducted by the facility or by the regulating agency, whichever
is applicable, but attention must be given to the sampling
schedule and analytical methodology such that mass loadings of
the contaminants can be estimated, as well as concentrations in
the sampled medium. Monitoring of the "nearfield." environment,
i.e., close downstream in the effluent mixing zone, should be
conducted regularly to document reductions in contaminant levels
in the appropriate media and to document the recovery of impaired
ecosystem processes and biotic communities. Such monitoring may
be required for a "long time", but over a restricted areal
extent, depending on the severity of the impact and the degree of
reduction of contaminant loading that is achieved.
For Lake St. Clair, seven actions were recommended that would
affect specific sources of contaminants, and that would require
site-specific monitoring for compliance or other effects of the
action at the following locations; Macomb and St. Clair Counties,
Michigan (fertilizer management); Mt. Cleiaens WWTP (PCBs,
phenols, mercury, phosphorus); Wallaceburg WWTP (Cd, Cu, Cr, Mi,
ammonia); Warren WWTP (PCBs); Selfridge Air National Guard Base
(several contaminants); Sugarbush landfili, Michigan (groundwater
monitoring); and G and L Industries, Michigan {groundwater moni-
toring) .
Other recommendations for specific contaminant sources involve an
assessment of the present conditions or a study to quantify con-
centrations or loadings; quantify CSOs from municipal waste
water treatment plants, identify sources of organic contaminants
in tributaries? determine Cd content of phosphate fertilizer,
measure atmospheric deposition of organic contaminants; measure
loadings of contaminants from urban runoff; conduct biomonitoring
studies at WWTP's; inventory point sources and waste sites dis-
charging to the Clinton River,* analyze sediment, water and biota
quality along the Clinton River; and inventory point sources and
waste sites discharging to the Sydenham and Thames Rivers. Each
of these items requires a specific program of data collection and
analysis. Additional needs for longer term monitoring may be
identified as a result of these studies.
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441
4. Habitat Monitoring
Habitat monitoring should be conducted to detect and describe
changes in the ecological characteristics of Lake St. Clair
through periodic analysis of key ecosystem elements. The follow-
ing items are recommended;
aj The abundance and distribution of the mayfly Hexagenia
should be determined every five years, The grid used by
the U.S. Pish and Wildlife Service during the 1985 survey
would be appropriate for consistency in sampling sites each
survey. An analysis of sediment chemistry, including bulk,
chemistry, organic and inorganic contaminants, and par-
ticle-size distribution, should be conducted for samples
taken concurrently with the Hexagenia survey. These data
will provide information on the quality of the benthic
habitat for a common pollution sensitive organism that
would serve as an indicator species of environmental
quality.
b) Quantification of the extent of wetlands along Lake St.
Clair should be conducted every five years, in conjunction
with the Hexage_ni_a survey. Aerial photography or other
remote sensing means would be appropriate to discern both
emergent and subiaergent macrophyte that are important
as nursery areas for larval fish and other wildlife. Veri-
fication of areal data should be conducted by inspection of
selected transects for plant species identification and
abundances. Changes in wetland areas should be correlated
with fluctuating water levels and other natural documented
influences so that long term alterations in wetlands can be
tracked and causes identified.
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442
J,
1. (Ontario Ministry of the Environment) 1975. Great Lakes
Shore Damage Survey, Toronto, Ontario 97 pp.
2. Edwards, C.J., P.L. Hudson, W.G. Duffy, S.J. Nepszy, C.D.
McNabb, R.C. Mass, C.R. Listen, B. Manny and W.D. Busch.
1986. Hydrological, morphemetrical, and biological
characteristics of the connecting rivers of the
International Great Lakes; a review, contribution XXX.
National Fisheries Centre-Great Lakes, U.S. Pish and
Wildlife Service. Ann Arbor, Michigan
3. Quinn, F.H. 1976. Detroit River flow characteristics and
their application to loading estimates. J. Great Lakes Res.
2(1):71-77»
4. Poe, T.P., C.Q, Hatcher, C.L. Brown and D.W. Schloesser.
1986. Comparison of species composition and richness of
fish assemblages in altered and unaltered littoral habitats.
J. Freshwater Ecol, 3(4); 525-536
5. Wall, G.J., E. A. Pringle and w.T. Dickinson. Agricultural
Pollution sources Lake St. Clair - Canada, UGLCC Study Non-
point Source Workgroup Level 2 report,
i. Chan, C,H._, Y.L. Lau and E.G. Oliver. 1986. Measured and
modelled chlorinated contaminant distributions in St. Clair
River water. Water Poll, Res. J. Can. 21(3};332-343.
7. EC/MOE (Environment Canada/Ontario Ministry of the
Environment), 1986. Sty Clair River Pollution Investigation
(Sarnia area). Canada/Ontario Agreement Report, January 28,
1986. Toronto, Ontario. 135 pp.
8. Johnson, G,D. and P.B. Kauss. 1987. Estimated Contaminant
Loadings in the St.. Clair and Detroit Rivers - 1984. OMOE,
Great Lakes Section, Water Resources Branch, November 1987.
Toronto, Ontario.
9. Munawar, M, and I.F. Munawar, 1987. Phytoplankton of Lake
St. Clair, 1984, Great Lakes Laboratory for Fisheries and
Aquatic Science Report. Fisheries & Oceans Canada, Canada
Centre for Inland Waters. Burlington, Ontario.
10. Sprules, W.G. and M. Munawar. 1987, Plankton spectrum and
zooplankton of Lake St. Clair, 1984. Great Lakes Laboratory
for Fisheries and Aquatic Sciences Report, Fisheries and
Oceans Canada. Canada Centre for Inland Waters. Burlington,
Ontario.
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443
11. Schloesser, D.W. and B.A. Manny. 1982. Distribution and
relative abundance of submersed aquatic raacrophytes in the
St. Glair-Detroit River ecosystem. U.S. Fish Wildl. Serv.,
Great Lakes Fish. Lab., USFWS-GLFL/AR-82-7. Ann Arbor, Mich.
49 pp.
12. Hudson, P.L., B.M. Davis, S.J. Nichols and C.M, Tomcko.
1986. Environmental studies of macrozoobenthos, aquatic
macrophytes, and juvenile fish in the St. Glair-Detroit
River system. U.S. Fish Wildl, Serv,, Great Lakes Fish. Lab.
Admin. Rep. 86-7. 303pp.
13. Edwards, c.J., P.L. Hudson, W.G. Duffy, S.J. Nepszy, c.D.
McNabb, R.C. Hass, C,R, Liston, B. Manny and W-D Busch.
1988, Hydrological, morphometrical, and biological charac-
teristics of the connecting rivers of the International
Great Lakes: a review. Can J. Fish, Aquat. Sci, 44. (In
press).
14. Lyon, J.G. 1979. Remote sensing analyses of coastal wetland
characteristics: The St. Clair Flats, Michigan. Proc, 13th
Symp. Remote Sensing of Environment, Mich, Sea Grant Rep.
MICHU-56-80-313.
15. Manny, B.A,, D.W, Schloesser, S.J. Nichols and T.A. Edsall.
1988. Drifting submersed macrophytes in the upper Great
Lakes Channels. U.S. Fish and Wildlife Service, National
Fisheries Centre-Great Lakes.
16, Griffiths, R.w. 1987. Environmental quality assessment of
Lake St. Clair in 1983 as reflected by the distribution of
benthic invertebrate communities. Aquatic Ecostudies, Ltd.
Kitchener, Ontario 35 pp.
17, GLI (Great Lakes Institute). 1986. A case study of selected
toxic contaminants in the Essex Region. GLI, Univ. of Winds-
or. Vol. 1: Physical Sciences. Parts One and Two, July,
1986. Windsor, Ontario.
18. Goodyear, C.D., T.A. Edsall, D.M.O. Demsey, G.D, Moss and
P.E. Polanski. 1982. Atlas of spawning and nursery areas of
Great Lakes fishes. U.S. Fish Wildl. Serv, Ann Arbor, MI
FWS/OBS-82/52, 164 pp.
19, McCullough G.B. 1985. Wetland threats and losses in Lake
St. Clair. pages 201-208 in H.P Prince and P.M. D'ltri,
eds. Coastal Wetlands, Lewis Publishing Co., Chalsea,
Michigan.
20. McCullough, G.B. 1982. Wetland losses in Lake St. Clair and
Lake Ontario, pages 81-89 in A. Champagen, ed., Proc.
Ontario Wetlands Conf., Ryerson Polytech. Institute.
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444
Toronto, Ontario September 1981.
21. Rukavina, N.A. , 1987, Status report of UGLCCS, Lake St.
Clair Bottom Sediment data. Level I, Report to the IJC.
22. International Joint Commission. 1982. Guidelines and Regis-
ter for Evaluation of Great Lakes Dredging Projects. Report
of the Dredging Subcommittee to the Water Quality Programs
Committee of the Great Lakes Water Quality Board, 365pp.
23. Oliver, B,G, and R.A. Bourbonniere, 1985. Chlorinated con-
taminants in surficial sediments of Lakes Huron, St. Clair
and Erie; implications regarding sources along the St. Clair
and Detroit Rivers. J, Great lakes Res. 11:366-372,
24. OMOE, Unpublished.
25. Sediment Workgroup Report, 1987 Geographical area report,
Lake St. Clair. OGLCCS Level II Report.
26, Hamblin, P.P., P.M. Boyce, F. chiocchio and D. s. Robertson,
1987. Physical measurements in Lake St. Clair: Overview and
preliminary analysis. National Water Research Institute
Contribution 87-76
27. Robins, J.A, and B.C., Oliver, 1987. Accumulation of fall-
out cesium-136 and chlorinated organic contaminants in
recent sediments of Lake St. Clair. In Modeling Workgroup
Report (53).
28, MDNR (Michigan Department of Natural Resources), 1985. Non-
point Assessment for Small Watersheds. Staff report, Surface
Water Quality Division, Lansing, Michigan,
29. Leuck, D. and B. Leuek, 1987, survey of Great Lakes Bathing
Beaches 1986. No. 2090-003, U.S.EPA, Great Lakes
National Program Office, Chicago.
30. Baker, David B. 1987. Pesticide Loading into the St. Clair
River and LaJce St. Clair in 1985, Final Report. U.S.E.P.A,
Grant R005817-01. Great Lakes National Program Office,
Chicago.
31, Wall, G,J,» E.A. Pringle and T, Dickinson. 1587.
Agricultural Sources of Pollution, Lake St. Clair, Executive
Summary of the Nonpoint Source Workgroup, Level 2 reports.
32. Lundgren, R.N,, editor. 1986. Pish contaminant monitoring
in Michigan, Report of EPA 205j Grant, Michigan Dept. of
Natural Resources, Lansing, Michigan.
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445
33. OMOE/OMNR (Ontario Ministry of the Environment/Ontario Mini-
stry of Natural Resources). 1987. Guide to eating Ontario
sport fish. Ministry of the Environment, Ministry of Natu-
ral Resources, Toronto.
34. GLI (Great Lakes Institute), 1987. Organochlorinated com-
pounds in duck and muskrat populations of Walpole Island.
University of Windsor, Ontario,
35. Amundson, I.E. (UNDATED). Environmental Contaminant Monitor-
ing of Wisconsin Wild Game 1985-86, Bureau of Wildlife
Management, Wisconsin Department of Natural Resources,
Madison, Wisconsin,
36. Herdendorf, C.E., C.N, Raphael and E, Jaworski, 1986. The
Ecology of Lake St. Clair Wetlands: A Community Profile.
U.S. Fish Wildlife Service. Biol. Report. 1985 (7.7). 187
PP.
37. Point Source Workgroup. 1988. Geographic Area Report - Lake
St. Clair. UGLCCS Level 2 report.
38. Pugsley, C.W., p.p.N. Herbert, G.w. Wood, G. Brotea and T.W.
Obal. 1985. Distribution of contaminants in clams and sedi-
ments from the Huron-Erie corridor, I. PCBs and octachloro-
styrene. J. Great Lakes Res. 11(3):275-289.
39. MDNR (Michigan Department of Natural Resources). Undated.
Progress Summary-Activity E.8. Draft UGLCC Study report,
Nonpoint Source Workgroup Level 2 Report for Lake St. Clair.
40. Oliver, B.G. and C.W. Pugsley. 1986. Chlorinated Contamin-
ants in St, Clair River sediments. Water Poll. Res. J, Can.
21:368-379.
41. Richards, R,P. and J. Holloway, 1987. Monte Carlo studies of
sampling strategies for estimating tributary loads. Water
Resources Res. 23(10):1939-1948.
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classification of Great Lakes tributaries. Report, U.S.EPA
Great. Lakes National Program Office, Chicago 40 pp.
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load estimation methods for total phosphorus. J, Great Lakes
Res. 7(3):2Q7-214.
44. Leach, J.H. 1972. Distribution of chlorophyll a_ and related
variables in Ontario waters of Lake St. Clair. pp 80-86.
In Proc. 15th conf. Great Lakes Res., Inst. Assoc, Great
Lakes Res.
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446 -
45. Leach, J.H. 1980, Limnological sampling intensity in Lake
St. Glair in relation to distribution of water masses, J.
Great Lakes Res. Vol 6 141-145.
46. Bricker, K.S., Bricker F.J., and J.E. Gannan, 1976. Dis-
.tribution and abundance of zooplankton in U.S. waters of
Lake St. Clair, 1973. J. Great Lakes Res 2:256-271.
47. Hamblin, P.P., P.M., Boyce, J. Bull, F, Chiocchio and D.S.,
Robertson, 1987. Reports to UGLCCS Workgroups. National
water Research Institute Contribution 87-87.
48. Hammons, A.S., J.E. Huff, H.M. Braunstein, J.s. Drury, C.R.
Shriner, E.B. Lewis, B.L. Whitfield and L.E. Towill. 1978,
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Cadmium. EPA Publication No. SPA-600/1-78-026. Office of
Research and Development, Cincinnati, Ohio.
49. GLWQB (Great Lakes Water Quality Board). 1987. 1937 Report
to Great Lakes Water Quality Board, Appendix A, Progress in
Developing Remedial Action Plans for Areas of Concern in the
Great Lakes Basin. Report to the International Joint Com-
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Niagara River Toxics Committee to U.S. U.S.EPA, Environment
Canada, OMOE and N.Y. DEC.
51. Marsalek, J. and H.Y.F. Ng. 1987. Contaminants in Urban
Runoff in the Upper Great Lakes Connecting Channels Area.
NWRI contribution No. 87-112, National Water Research In-
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CHAPTER IX
THE DETROIT RIVER
A. STATUS OP THE ECOSYSTEM
1. Ecological Profile
Watershed Characteristics
The Detroit River makes up the lower 51 km of the connecting
channels between Lakes Huron and Erie. An international boundary
divides the Detroit River about equally into United States
(Michigan) and Canadian (Ontario) waters (Figures II-5 and IX-1).
The Detroit River is a hydrologically and ecologically distinct
ecosystem compared to Lake St. Clair and the St. Clair River (1),
It is limnologically mesotrophic and supports cold water fish
from September to June. The Detroit River provides important
habitat for fish, birds and the bottom dwelling life on which
they feed. It is also an important source of potable water, with
drinking water intakes near Belle Isle, Windsor, Amherstburg and
Wyandotte (2). Water is also used to supply a major industrial
complex consisting of automobile, steel and chemical companies.
The St. Lawrence Seaway utilizes the Detroit River for commercial
shipping. This portion of the Seaway is presently the busiest in
the upper Great Lakes, involving shipments of iron ore, coal,
limestone, gypsum, oil, and wheat.
The topography of the Detroit River basin is flat, broken only by
the valleys of the Rouge River and a few lesser tributaries. Low
moraine deposits and beach ridges of ancestral Lake Erie provide
slight relief. Land elevations range from 214 m above sea level
near the tributary head waters to approximately 174 m along the
Detroit River. The relative relief of the lake plain is 1 to 5
m/km^, and most slopes are less than 3%.
The Detroit River courses through Pleistocene glacial drift
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448
Port
Huron
Mar ys vine
Marine
. •" City
MICHIGAN
ST. CLAIR
UPPER
DETROIT*-*
RIVERA
W ind s or ; • ' • •" •
ONTARIO
Statute Mnes
0510
0 51015
K il omettf
FIGURE IX-1. The Huron-Erie corridor.
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449
underlain by Paleozoic sedimentary rock. The sedimentary rock
beneath the river is the Detroit River Formation (primarily dolo-
mite) which outcrops intermittently in the navigation channels
east of Grosse lie. On top of the bedrock is a mantle of glacial
drift 0 to 30 m thick.
Lake plain soils are poorly drained loam and clay loams, which
developed on former lake bottoms or lacustrine clay sediments.
Sandy ridges mark former shorelines, and on the Michigan side, an
isolated sand sheet marks remnants of the glaciofluvial delta of
the post-glacial Huron River. When drained and tiled, the loamy
lake plain soils are agriculturally productive. Many surface and
subsurface soils are moderately permeable (0.25 and 1.27 cm/hour)
with high surface runoff coefficients causing the local streams
to be storm event responsive.
The Ontario shoreline, except for the City of Windsor and its
docks, is less disturbed than the Michigan shoreline. North of
the Canard River there are scattered marinas, canals, and private
boat slips. In places, Ontario farmers have encroached upon the
wetland margins of the Detroit River and its tributaries. Thus,
a green buffer zone exists only intermittently between the farm
fields and the riverine ecosystem. Access to the water for com-
mercial navigation, business, pleasure boating, fishing and hunt-
ing is important locally on both sides of the river.
Hydrology
Nearly 98% of the Detroit River flow enters from Lake Huron via
the St. Clair River and Lake St. Clair. The river discharge
averages 5,300 m^/sec and ranges from a low of 3,200 m^/sec to a
maximum discharge of 7,100 m^/sec. The Fleming Channel in the
upper Detroit River, north of Peach Island, accounts for 77% of
total river flow. Flow distribution in the lower river is rela-
tively complex downstream of Fighting Island, as several channels
separate or combine the flow (2,3,4).
Flow velocities average 0.49-0.88 m/sec, but mid-surface veloci-
ties can be nearly twice that rate. Surface currents near the
Ambassador Bridge and in the Amherstburg channel reach 1.2 m/sec,
while the Trenton Channel flow averages 0.6 m/sec.
Detroit River water depth and velocity are directly affected by
water levels in Lakes St. Clair and Erie, which vary seasonally
and annually. Lake Erie seiches and Lake. St. Clair ice jams may
also produce changes in Detroit River water levels and currents.
The river slope is relatively uniform, and falls 0.9 m over its
51 km length. The average time of passage for water through the
Detroit River is about 19 to 21 hours.
-------
450
Tiie Rouge River, the main tributary to the Detroit River, drains
about 121,000 ha in Michigan, and consists of upper, main, middle
and lower branches. The stream is very event-responsive and.
frequent flooding occurs along the middle Rouge . Its mean annual
discharge is 26 m^/sec, with over 75 percent of it draining
through urban areas, collecting considerable stormwater runoff,
overflow from combined sewers during wet weather, and over 500
million gallons per day (mgd) of waste water from municipal and
industrial facilities. The lower Rouge is partially lined with
concrete, so runoff rapidly reaches the Detroit River during
storms.
Other tributaries include the Ecorse, Canard and Little rivers
and Turkey Creek. The Ecorse River tributary drains 11,556 ha in
Michigan, occupied by 2 communities with a total population of
198,000 in 1980. The Ecorse River has two open channel tributa-
ries, the North Branch and the South Branch (or Sexton-Kilfoil
Drain) . These branches join approximately 1 km upstream from the
confluence of the Ecorse and Detroit rivers near Mud Island.
Ontario's Little River empties into the Detroit River at its
mouth, by Peach Island. It drains approximately 5,750 ha of
agricultural and industrial land. Turkey Creek enters the
Detroit River just north of Fighting Island, draining 2,960 ha of
primarily agricultural land in Ontario. The Canard River enters
the Detroit River in Ontario, south of Windsor and east of Grosse
lie. It is a turbid, slow moving stream which discharges into
diked wetlands just north of its mouth, and drains approximately
20,000 ha of primarily agricultural land (5). Other minor tribu-
taries also exist, such as Monguagon Creek (in Michigan, by the
northern end of Grosse lie) and Conners Creek (in Michigan, by
the eastern end of Belle Isle) .
Effluent from the Detroit area wastewater treatment plants
(WWTPs) discharge over 32 m3/sec (1985) , a volume equal to the
combined tributaries flowing into the Detroit River. The Metro-
politan Detroit WWTP alone discharges 30 m^/sec near the mouth of
the Rouge River (6) .
Habitats,, and Biological
The Detroit River ecosystem can be divided into an upper stretch
(upstream of the Rouge River) and a lower river stretch. The
Detroit River's biologic zones include deep channels, shallow
water/nearshore zones, and terrestrial zones. Deep channel
environments generally have water depths exceeding 7 m, relative-
ly high flow velocities, and coarse sediments. Since the river
channels are also used for shipping, the high sediment load and
lack of anchorage prevent macrophyte growth. Macrophytes and
associated periphyton and invertebrates are most abundant in the
shallow water-nearshore zone, seldom occurring at depths greater
than 4 m. The terrestrial biological zone includes undeveloped
-------
451
island habitat, coastal wetland and riparian environments along
such less developed tributaries as the Canard River. The
Wyandotte National Wildlife Refuge is located in the Detroit
River, off the northern tip of Grosse lie. This Refuge encour-
ages shorebirds and waterfowl feeding, nursery and nesting activ-
ities. Stony, Celeron, Grassy and Mud Islands provide shoretdrd
habitat.
The coastal wetlands and large, emergent and submersed macrophyte
beds along the Detroit River were nearly continuous in colonial
times. They now exist only in 31 small isolated remnants cover-
ing 1,382 ha (7). Most of the remaining vegetation along the
river consists of submersed macrophytes because the land formerly
occupied by the swamp-scrub-meadow communities along the ter-
restrial river margin has largely been converted to other uses.
Fifty-four percent (748 ha) of the remaining wetlands are in
Ontario. The single largest wetland, immediately north of the
Canard River, is functional only along its outer, undiked mar-
gins. Functional wetlands also exist along the open water mar-
gins of a few islands.
A number of biological surveys have documented the biotic com-
munities in the river (7,8,9,10,11,12,13,14,15,16). Although it
is not well understood how the various trophic levels relate to
one another, enough information exists to describe species com-
position, standing crop and biomass for a variety of primary and
secondary producers.
i) Macrophytes
At least 21 submersed macrophyte taxa occur in the river, domin-
ated by Vallisnera, Chara, Potamogeton, Myriophyllunx and Heteran^
thia. Stands are typically composed of 2 or 3 species but as
many as eleven have been recorded in a single stand. Chara is
the only taxon consistently occurring in monotypic stands. The
lower depth limit for plant colonization is not established, but
most stands occur in water less than 3.7 m deep. In the Detroit
River, the area of the river bed between shoreline and the 3.7m
depth contour is about 99 km^, 72% of which is occupied by sub-
mersed plants. The wetlands and submersed macrophyte beds con-
stitute the most critical areas for primary and secondary produc-
tion for plants, fish and birds, and are the most stable habitat
in the ecosystem (17). Their invertebrate populations include
clams, snails, midges, caddisflies, mayflies, amphipods, spring-
tails, and worms. Juvenile yellow percti and adult northern pike
have been observed feeding along the wetland shoreline among the
submersed macrophytes. These areas are also heavily used for
spawning by numerous fish species. No detailed studies of spec-
ies composition, distribution, and relative abundance of emergent
macrophytes have been completed, although wetland communities
have been mapped by remote sensing. Over 95% of the emergent
beds occur in the lower river.
-------
452
The St. Clair-Detroit River system produces about 264,000 tons of
plant biomass each year, of which 19% originates in the Detroit
River. Most of the plant biomass in the Detroit River is pro-
duced by submersed macrophytes.
ii) Phytoplankton
Phytoplankton standing crop and production values is assumed to
have phytoplankton biomass and daily production similar to Lake
St. Clair. Eighty two phytoplankton species are present in the
river at low density (about 500 cells/ml), and are dominated by
diatoms that are common in Lake Huron in July and August, Blue-
green algae that are common in Lake St. Clair at that time domin-
ate the Detroit River phytoplankton. No periphyton studies have
been conducted to date, but a recent study in a wave exposed
breakwater in western Lake Erie indicates that diatoms, green
algae and red algae may be common over-wintering taxa in the
Detroit River. Filamentous green algae can be expected to domin-
ate during summer months.
Current information is inadequate to determine how much of the
planktonic production of the river is used by river biota. If
only moderate amounts of this biomass is retained, then the
littoral plant complex of emergent and submersed macrophytes and
macrozoobenthos are the main standing stock in the river. From
calculations of drifting macrophytic plants, it appears that the
Detroit River is a large source of detrital organic matter that
supports productivity in western Lake Erie.
iii) Zooplankton
Detroit River zooplankton studies are not yet completed, but
zooplankton composition and abundance seem to resemble those
found in Lake St. Clair. Cladocera and several species of Cyc~
lops and Diaptomus dominate the zooplankton in Lake St. Clair.
Difflugia is the most common protozoan, and Conochilus, Keratel^
la, Polyarthra, Synchaeta, and Brachionus are the most common
rotifers. Maximum numbers of zooplankton may be expected between
June and September. A study of foods eaten by larval yellow
perch during passage through the Detroit River revealed that
zooplankton, including copepod nauplii, older cyclopoids and
copepods, cladocera and rotifers were eaten. Hence, zooplankton
are likely the critical food resource for larval fish.
iv) Macroinvertebrates
The Detroit River benthic macroinvertebrate community includes
over 300 species. Oligochaetes, chironomidae, gastropoda, ephem-
eroptera, trichoptera and amphipoda dominate the biomass. Chir-
onomidae are common throughout the system while oligochaetes are
dominant in the lower river. Hydropsychid caddisflies are the
dominant trichoptera and Hyalella is the most common amphipoda.
-------
453
Hexeigenia is the most common mayfly, but density is lower in the
Detroit River (88/m2) than the St. Clair or the St. Marys Rivers
(95/m2 and 199/m^), respectively. Detroit River benthic produc-
tion (5.4 g ash-free dry weight/m3/yr) is lower than the St.
Clair River and Lake St. Clair (7,0 and 6.8 g ash-free dry
weight/m^/yr) with the annual production (440 metric tons ash-
free dry weight/yr) equal to about 2% of the combined annual
Detroit River phytoplankton, periphyton, maerophyte and zoo-
plankton production {7,14,16),
v) Pish
The present Detroit River fish populations are a mixture of
natural and introduced (exotic) species. Among the exotic fish
is the common carp, which introduced in 1883 in western Lake
Erie. Prom there, it spread through the Detroit River to the
upper Great Lakes, destroying beds of wild celery and wild rice,
the preferred food of native waterfowl. Large carp populations
continue to inhabit the Detroit River. Rainbow smelt and ale-
wife, introduced in 1932, spread through the Detroit River and
upper lakes. Alewives now comprise the bulk of forage fish in
all the Great Lakes. The lamprey spread through, the Detroit
River to the upper Great Lakes in the 1940s, greatly reducing
populations of desirable fish, such as the lake trout. The most
recent exotic Detroit River fish, the white perch, introduced
into Lake Erie in 1953 and now hybridizes with native white bass.
The Detroit River fish community presently has approximately 60
resident or migrant species, 32 of which use mainly the lower
river along the islands and the mainland shoreline for spawning
(18,19,20,21,22).
The Detroit River and its tributaries are, important spawning,
feeding and nursery areas for many species that support major
fisheries in the river and Lakes Huron and Erie. There are 60
recorded resident or migrant fish species in the Detroit River,
32 of which spawn in the river. Townet catches of larval fish in
the Detroit River in 1977-1978, 1983-1984 and 1986 show that the
river is a nursery ground for at least 25 species of fish. Most
abundant were alewife, rainbow smelt, and gizzard shacl. Other
species were much less abundant.
The river is part of a complex migration route for walleye and
yellow perch, important recreational fish species, which move
between Lake St. Clair and Lake Erie, Large walleye spawning
runs once occurred in the lower river, the reduction of which is
attributed to pollution and sedimentation. In the 1970s, spawn-
ing was again documented, and walleye larvae were collected in
several locations in the lower 16 km of the Trenton Channel and
the main river. Recently, yellow perch spawning has been ob-
served in the Trenton Channel and near the mouth of the Detroit
River in areas previously used by walleye.
-------
454
The Detroit river once supported a large commercial fishery for
lake whitefish, lake herring, walleye, lake sturgeon, black bass,
northern pike, muskellunge and carp. Overfishing, pollution and
dredging contributed to the Detroit River commercial fishery
decline (23,24,25).
Sport fishing is still an important activity in the Detroit
River, In 1985, an estimated 1.4 million hours were spent har-
vesting approximately 1.4 million fish (22). The lower river
harvest was 980,200 while the upper river was 440,600 annually,
Dominant species were white bass (63%), walleye (12%), yellow
perch (10%), and freshwater drum (7%).
A larval fish passage study from Lake St. Clair to Lake Erie was
conducted along the Detroit River at 17 transects, 2.5 km apart
(Figure IX-2)(22). Thirteen larval fish taxa were observed.
Larval fish densities of walleye, yellow perch and white bass/
white perch greatly increased in the mid-Trenton Channel (tran-
sect 12-13), suggesting spawning and rearing activities in the
vicinity. Yellow perch showed a strong lateral distribution with
greatest densities along the western near-shore, decreasing
toward the main channel with lowest densities along the eastern
shore. Surprisingly, the area containing the highest density of
larval yellow perch coincides with the highest concentration of
environmental contaminants in water or sediments. White
bass/white perch and rainbow smelt did not exhibit significant
east-west density gradations. Longitudinal distribution patterns
were evident for larval bloaters, burbot and deep water sculpin.
Deep water densities of these species were greatest in the upper
Detroit River, but were present throughout, probably being trans-
ported from Lake Huron and Lake St. Clair. walleye and white
bass/perch were not found, and yellow perch and rainbow smelt
exhibited relatively low abundances in the upper river. Yellow
perch, white bass/white perch, rainbow smelt and walleye larval
densities were greatest in the lower river.
vi) Waterfowl
At least 3 million waterfowl migrate annually through the Great
Lakes region, which, is situated at the intersection of the Atlan-
tic and Mississippi flyways. An estimated 700,000 diving ducks,
500,000 dabbling ducks, and 250,000 Canadian geese migrate across
Michigan each fall (1).
Important species of nesting ducks in the Detroit River wetlands
include mallards, blue-winged teal, black ducks and, if nesting
boxes are provided, wood ducks. In the past, 24 species of ducks
regularly fed in the river. Each year, thousands of waterfowl,
including scaup, goldeneyes, canvasbacks, black ducks, redheads,
and mergansers congregate on the river to forage sediments.
Major concentrations of feeding ducks are often found in littoral
waters around Belle Isle, Grosse lie and Mud, Fighting, Sugar and
-------
455
MICHIGAN
FIGURE IX-2. Detroit River water sampling transects and 24-hour
sampling locations.
-------
456
Celeron islands. Preferred foods vary among species. Mergansers
feed primarily on fish, whereas American goldeneyes prefer crayf-
ish, clams, and other invertebrates. Many diving ducks feed on
submersed aquatic plants and their associated communities.
A recent survey of eelgrass tubers, a preferred food of many
waterfowl, indicated that over the past 35 years, tuber densities
have decreased substantially, resulting in a net loss of 4.6 x
10^ tubers in the lower river. This large loss of eelgrass
tubers in the Detroit River explains in part why fewer waterfowl
now use the Michigan migration corridor. ••
Climate
The Detroit River area enjoys a mid-continental climate, with
cold winters and relatively short hot summers, moderated somewhat
by the Great Lakes. The average first frost is on October 21 and
the average last freezing temperature is on April 23, with an
annual growing season of 180 days. Precipitation averages about
76 cm. per year, including 40 cm of snow. Prevailing winds are
from the southwest, and average 16 tan/hour.
During late autumn and early winter, water from Lake Huron cools
rapidly as it flows through shallow Lake St. Clair. As a result,
ice often enters the Detroit River from Lake St. Clair before it
begins to form in the Detroit River itself. Before the 1930s,
most of the Detroit River was ice covered in winter, but now
large volumes of heated effluents entering the river usually
prevent the upper river from freezing over, except between Belle
Isle and the Michigan mainland. Extensive slush ice still devel-
in the lower river, especially in the broad shallow expanses
adjacent to the islands. In general, ice may now be found in the
river from early December to mid-March, but main navigation chan-
nels remain ice-free. Minor ice jams occur in the Detroit River
with the breakup ice moving south from Lakes Huron and St. Clair
from late March to early May. Easterly winds can also cause Lake
Erie ice to reverse into the lower Detroit River. Monthly water
temperature data show that the highest water temperatures occur
in August, with an average of 22.2°C. In the shallow nearshore
areas of the lower river, water temperatures may attain 25.2°C.
Lowest temperatures occur in January-February, sometimes reaching
0°C.
2. Environmental Conditions
Water _Quality
The Detroit River area is heavily industrialized and densely
populated. Industrial and municipal raw water is taken from the
river then returned after use. Due to its varying channel width
-------
457
and depth, berms and islands, the Detroit River is hydrologically
complex, a fact which influences water quality and modifies the
human impact on the Detroit River system.
Information on water quality was obtained as part of this study
(26). To obtain a reliable data set which could provide a mean-
ingful interpretation while minimizing the need for analyses,
water sampling transects across the river were used. Figure IX-3
shows the location of the upper (DT 30.8W and DT 30,7E) and lower
(DT 8.7W and DT 9.3E) transects and the major tributaries. The
upper transects are at Peach Island near Lake St, Clair, upstream
of Detroit and Windsor. The lower transects are near Grosse lie,
upstream of the Livingston Channel and Stoney Island in the east,
and near the lower end of the Trenton Channel on the west. The
lower transect was designed to avoid the influence of Lake Erie,
and in the process was located upstream of two industrial facili-
ties. General Chemical at Amherstburg and McLouth Steel, Gibral-
tar, Therefore, water quality data for the lower transect does
not reflect these facilities. In addition, loadings from Frank
and Poet Drain, which serves several permitted Michigan industri-
al discharges, were also excluded (26). Figure IX-4 describes
the flow distribution in the channels of the Detroit River, and
shows that approximately 21% of the total Detroit River flow
passes through the Trenton Channel and approximately 26% and 47%
through the Livingston and Amherstburg channels, respectively
{27} ,
Three additional, partial river width water quality monitoring
transects were established in the Trenton Channel between Grosse
lie and the Michigan shore at Point Hennepin (A), just south and
parallel to the Grosse lie toll bridge (C), just south and paral-
lel to the Grosse lie Parkway Bridge off the Monsanto Breakwall
(D). Michigan's monthly Detroit River water sampling transect at
the mouth of Detroit River between Bar Point and Maple Beach (DT
3.9) is also shown (Figure IX-3).
i) Cross-Channel Variations in Water Quality
Cross-channel variation of water quality occurs where large
volumes of low concentrations or smaller volumes of higher con-
centrations of substances are discharged to the river. Cross-
channel variations were demonstrated by dye studies below the
Detroit WWTP outfall (Figure IX-5) (283 . The upper Detroit River
between Belle Isle and Fighting island has a relatively constant
channel width and depth where little or no cross-channel mixing
occurs. In contrast, the lower river section is broken up into
three major channels and several shallow embayments, There, and
downstream of these islands and structures, increased cross-chan-
nel mixing may occur due to the generally lower current veloci-
ties, eddies below these structures, and wind driven currents
cross and counter to the normal current direction.
-------
458
DT30.8W
Michigan
USA
Rouge
River
Little
River
Ecorsa
River
Ontario
CANADA
DT12.
Monguagon
Creek
N
DT8.7W
•DT3.9
FIGURE IX-3. Detroit River mass balance sampling transects.
-------
459
77%
DETROIT
Ambassador Bridge
51%
26%
Navigation
Channel
36%
FIGURE IX-4. Flow distribution in the Detroit River (27),
-------
FIGHTING ISLAND
DWSD I ,
PLANT 1 /
PEERLESS CEMENT
(REMOTE 72)
WYANDOTTE
GENERAL HOSPITAL
(REMOTE 74)
PLANT FLOW
RIVER FLOW
C0
WIND
1108 CFS
221.097CFS
3t.0ppb
SW AT 22 MPH
FIGURE IX-5. Plume from the City of Detroit WWTP, March 1985 (28).
-------
461
Cross-channel variation in concentrations of some organochlorine
contaminants (for example PCBs and chlorobenzenes) between water
in the upper Detroit River and the Detroit River mouth has been
shown (Figure IX-6). Organochlorine concentrations are similar
at the head of the river along both the Michigan and Ontario
shores (about 0,5 ng/L at stations 399 and 379, respectively)
(29). Proceeding downstream, higher levels are found along the
Michigan shore, with levels up to 209 ng/L (station 346), com-
pared with 0.5 ng/L across the river, station 269 (17 ng/L), on
the Canadian side, may be influenced by U.S. sources as this
station is well within the 50% flow panel of the Detroit River.
ii) Longitudinal Variations in Water Quality
The flow of the Detroit River ranges from 3,200 m3/sec to 7,100
iti^/sec, constituting a large water mass. To detect statistically
significant changes in water quality between the river head and
mouth, inputs or sinks of such substances must be substantial.
Due to natural fluctuations between seasons, shipping and dredg-
ing activities and both natural and man-induced fluctuations of
in-coming water quality, any quantitative and even qualitative
interpretation of data is difficult. Only a statistical evalua-
tion of many samples will allow definite conclusions. That sam-
pling intensity was not achieved in this study for most data, and
comparisons made are primarily relative comparisons. Evaluation
of relative changes in water quality parameters does not require
absolute values, but compares the relative abundance or absence
of materials, and may indicate temporal or spatial differences.
Polychlorinated Biphenyls (PCBs):
Qualitatively, the composition of PCBs in Detroit River water
changes from the upper to the lower Detroit River transects (Fig-
ure IX-7). For nine commonly observed PCS homolog series {com-
prising approximately 100 of the theoretically possible 210 PCB
isomers), a decrease of the lower chlorinated homologs (with one
to four chlorines per biphenyl molecule) and an increase of the
higher chlorinated homologs (6 to 10 chlorines per molecule) is
observed as one moves downstream. Considering the stability of
PCBs, it can be concluded that the observed change in PCB homolog
distribution is due to inputs of higher chlorinated PCBs along
the river stretch (26).
The observed qualitative changes in PCB composition are also
supported by quantitative observations. PCB concentrations in
water averaged approximately 0.6 ng/L at four stations above and
below Belle Isle on both sides of the river from a 1985 survey
(26). Downstream, at several locations along the Ontario side,
PCB concentrations increased to approximately 1.0 ng/L, while PCB
concentrations on the Michigan side in and downstream o£ the
Trenton Channel increased to levels as high as 3.4 ng/L« In the
-------
462
ill JM J3O 3«* JSJ 3B« Ml
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STATION MUMBEfl
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STATK3N NUMBER
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Mivtr. Concentrations in IV mf til' (mtffmtmut, IV ng *f ' (suipmtitd mIMU, anil IVitfL' (mmrf, fttptctivtty.
2M 313 37Q
STATION NUMBEIt
FIGURE IX-6. PCBs, CBs, PAHs and DCS in Detroit River water, suspended solids and
surficiaJ sediments (29),
-------
463
STATION NUMBER
2SS '." 31* 3M
353 370 -!A!
STATION NUMBEfi
Polrcltlnrlnailli bipiltntk (PC3s) in waler, susptmjtd lelldi, and surfitiat srttimmil of fhr Octrair River.
fatitini in 10* tig kf * iufdimtnts, sujptndtd satidll iwd Wl If L t (water), respectively.
STATION NUMB£fi
213 3M 211 223 724 2H 3-1 JM
352 364 3M
Q »-
S 14-
!0-
»-
B WATER
G3 SUSPEhOEO 3 nt ki'1 (tnHmrMt. lufptndnf salids) taut Iff' if I. ' Svaitti,
FIGURE IX-6. (Cont'd.) PCBs, CBs, PAHs and OCS in Detroit River water,
suspended solids and surficial sediments (29).
-------
30-
sft
0
0.
25-
B
"- 20
i
t
UJ
15-
O
d
2
O
I
Q
Ul
10
5-
I
6
8
9
10
HOMOLOG
UPPER TRANSECT LOWER TRANSECT
FIGURE 1X-7. PCBs iii Detroit River water.
-------
465
Detroit River System Mass Balance Study (30), total PCB concen-
trations averaged 1.4 ng/L {plus or minus 0,6 ng/L) at the head
of the river and 3,3 ng/L (plus or minus 1.3 ng/L) at the mouth,
based on composite samples across the entire river at each re-
spective transect. Total PCB concentrations in whole water sam-
ples from tributaries averaged 45,4 ng/L in the Rouge River, 47.9
ng/L in Turkey Creek, 33.3 ng/L in the Ecorse River and 7,6 ng/L
in the Little River {Table IX-1). In the Trenton Channel
Balance Study (31), total PCBs in whole river water ranged from 1
ng/L to 385 ng/L. The highest concentrations were found along
the western shore of the Trenton Channel, with daily variations
ranging from 6.8 ng/L to 15.7 ng/L.
PCB concentrations throughout the Detroit River exceeded
Michigan's Rule 57(2) allowable level of 0.02 ng/L, the Ontario
Provincial Water Quality Objective (PWQO) of 1 ng/L and the
U.S.EPA Ambient Water Quality Criteria (AWQC) for Human Health
(based on fish and water consumption} of 0.079 ng/L, and
locations (e.g., Trenton Channel) exceeded the U.S.EPA chronic
AWQC of 14 ng/L.
In suspended solids, PCB levels were at or below 50 ng/g at most
locations on both sides of the river, except at two stations on
the Michigan side, below Belle Isle and at the lower end of the
Trenton Channel, where they reached 280 ng/g. Concentrations
measured on suspended solids at the head of the Detroit River
averaged 428 ng/g, largely due to elevated measurement, A
single suspended sediment sample collected in 1S85 from the
Canard River had a very high PCB concentration of 11,760 ng/g,
but other data suggest that the Canard River is only an intermit-
tent PCB source {32).
Chlorobenzenes;
Several of the 5 possible chlorobenzene homologs are commonly
found in aquatic systems, of which hexach'lorobenzene (HCB) is
probably the most widely distributed congener. In Detroit River
water, chlorobenzenes ranged from 0.3 to 1.0 ng/L at stations
above Bells Isle and at all but two Ontario stations (maximum
approximately 2 ng/L, Figure IX-6). On the Michigan side, chlor-
obenzene levels were somewhat higher, particularly at the mouth
of the Rouge River, where chlorobenzene levels reached 25.9 ng/L
(Figure IX-6). However, HCB concentrations were only 0.28 ng/L,
indicating other chlorobenzenes are present. In a later study,
concentrations of HCB remained virtually the from the head
(0.31 ng/L) to the mouth {0.33 ng/L) of the Detroit River (Table
IX-1), In another survey, HCB in water and/or suspended particu-
lates showed essentially the HCB concentrations on both
shores and at upstream and downstream transects. These results
indicate small or intermittent sources of HCB along the Michigan
side of the Detroit River, perhaps from the Rouge River, with
important background concentrations of HCB entering the Detroit
-------
TABLE IX-1
Mean concentrations of polychlorififtted blphenyl, hexachlorobenzene» Major trace »ctnla, phoaphorua and choride at the
Detroit River head and mouth, and major tributary noutha (1984-1S86)*«
LOCATION
Detroit-Head
Detroit-Mouth
Ecors* River
Rouge River
Turkey Creek
Little River
Canard River
i
Z
l
TOTAL TOTAL TOTAL
CADMIUM COPPER MEfiCtJRY
lug/L) (ug/LJ
0.023 1.29
O.Q3S 1.64
0.084 2.83
2. OBI 7.09
0.196 4.38
(0.2-3H
0.058 6.14
(0.2-0.4J'
0.2-0,4'
0.008
0.008
0.002
0.017
0.016
0.018
-
From U.S. EPA an reported in the Water Quality
Quality Workgroup report for reported valuer,
Upper and lower values reported by Wall e_t fl_L
ND = not detected.
TOTAL
NICKEL
<»8/L)
0.9?
1.18
2.62
TOTAL
ZINC
(ug/L|
1 .22
3.30
14.2
3.30 167.3
6.70
NO*
-
Workgroup
aanpi ing
. { 6 >.
21.2
73.7
-
TOfAl TOTAL TOTAL
CHLORIDE PHOSPHORUS . tEAD PCB»
(mg/tJ (ug/L) (ug/L) Ug/L)
6.7
8.4
37.7
69.2
106.6
(61-880
93.8
U6-21S
27-12S*
i.6 - 1.4*
15.7 ' - 3,3*
88.0 - 33.3*
102.0 - 46.4*
361.0 3-33* 47.9*
>* < 47-7000)*
473.0 3-13* t.5
)J JS2-2400)2
B7-S601 3-30*
Report 126), except *a noted. Valuea are rounded.
methodology and statistical information.
No average value reported.
HCB
0.31*
0.33*
0.38*
0.28*
0.24*
1.01
-
See Water
£>•
m
a\
Average of two surveys [28>«
-------
467
River from upstream. Data from a 1984 study, however, indicated
increased HCB concentrations on suspended sediments, from ap-
proximately 3,5 ng/g at the river head to approximately 15 ng/g
at the Detroit River mouth.
Other Organochlorine Compounds: •* - ~
A variety of additional organochlorine contaminants (OCs) are
frequently observed in Detroit River water and seston samples.
Among these are DDT and its environmental metabolites, commonly
referred to as total DDT, hexachlorocyclohexane (three isomers)»
chlordane (two isomers}, heptachlor epoxide, endosulfan (two
isomers}, dieldrin, endrin, methoxychlor, and octachlorostyrene
(OCS}. These compounds, collectively referred to as DCs, were
found at concentrations of 0.3 to 0.5 ng/L in upper Detroit River
water on both shores (Figure IX-6}. Significantly higher OC
concentrations were observed at many downstream stations on the
Michigan side, with values as high as 20 ng/L at the mouth of the
Rouge River, OCS levels, however, were virtually constant
throughout the river at 0.005 to 0.008 ng/L in water and at 2.0
to 4.3 ng/g on particulate matter as found in another survey.
These data indicate sources of OCS are primarily upstream of the
Detroit River but important loadings of other OC compounds occur
along the Michigan side of the Detroit River (26,32,33).
Polynuclear Aromatic Hydrocarbons:
Polynuclear aromatic hydrocarbons (PAHs} are byproducts of incom-
plete combustion of fossil energy resources. PAHs are also as-
sociated with petroleum refining and steel-making operations
(coking, in particular). Consequently, their presence in air and
water in urban and industrial areas is not surprising. At the
head of the Detroit River, PAH concentrations of 100-200 ng/L
were found in water. Higher concentrations were observed at
several downstream stations along the Ontario, and particularly,
the Michigan side of the river, with values as high as 6,100 ng/L
(Figure IX-6). Based on the high concentrations of PAH that were
found at the mouth of the Rouge River and sampling locations
immediately downstream, large sources for PAHS appear to exist in
the Rouge River area (26,30,31). Water samples from the Ontario
tributaries (Turkey Creek, Little River and the Canard River)
obtained during 1984 revealed no PAHs were present at the limit
of detection used (34). There is no appropriate ambient water
quality guideline with which to compare PAH concentrations in
Detroit River water.
Total Trace Metals, Total Phosphorus and Filtered Chlorides:
A 1987 survey of selected trace metals (copper, cadmium, mercury,
nickel, and zinc), phosphorus and chloride concentrations result-
ed in the following general conclusions (.Table IX-1) (26,30).
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468
Total cadmium concentrations increased from the head to the mouth
of the Detroit River from a mean of 0.023 ug/L to a mean of 0.035
ug/L. In general, Detroit River water concentrations were below
relevant ambient water quality guidelines. The Trenton Channel
Mass Balance Study found total cadmium concentrations ranging
from 0.7 ug/L to 0.77 ug/L (data not shown in Table IX-1) in the
vicinity of the Grosse lie free bridge along the western shore of
the Trenton Channel, three of the four times it was sampled.
These concentrations exceeded Michigan's Rule 57(2) allowable
level of 0.4 ug/L (assuming a water hardness of 100 mg/L calcium
carbonate). High cadmium concentrations were found in the Rouge
River (2.06 ug/L}, the Canard River (0.2-0.4 ug/L), Turkey Creek
(0.196 ug/L in one study and up to 3 ug/L in another), the Ecorse
River (0.084 ug/L) and the Little River (.0.058 ug/L in one study,
and up to 0.4 ug/L in another). Concentrations in the Rouge
River, Turkey Creek and the canard River exceeded the Great Lakes
Water Quality Agreement (GLWQA) specific objective and the PWQO
of 0.2 ug/L, and concentrations in the Rouge River and Turkey
Creek exceeded Michigan's Rule 57(2) allowable level.
Total copper concentrations were slightly higher at the Detroit
River mouth than at the river head (1.64 ug/L vs. 1.29 ug/L),
Total copper concentrations in the tributaries were between two
and six times higher than in the Detroit River, with the Rouge
River levels highest at 7.1 ug/L. In general, both Detroit River
and tributary copper concentrations were below relevant guide-
lines, with the exception of the Rouge and Little rivers, which
slightly exceeded the GLWQA specific objective and the PWQO of
5 ug/L.
Total mercury concentrations in Detroit River water did not show
any change between river head and mouth (both 0.008 ug/L}« Total
mercury concentrations in the Detroit River and in the Trenton
Channel ranged from O.Q24 ug/L to 0.449 ug/L. Tributary mercury
concentrations were approximately double those in the Detroit
River, except in the Ecorse River, where they were lower. These
concentrations generally exceeded the U.S.EPA chronic AWQC of
0.012 ug/L.
Total nickel concentrations in the Detroit River showed little
change between upper (0.97 ug/L) and lower (l.l ug/L) Detroit
River transects. Nickel concentrations in the Ecorse and Rouge
rivers, and Turkey Creek were from two to eight times the Detroit
River level, with the highest concentration in Turkey Creek (8.8
ug/L). Especially high concentrations of nickel were noted in
the Little River (676.2 ug/L)(26). With the exception of the
Little River, all Detroit River and tributary concentrations of
nickel were below ambient water quality guidelines. Little River
exceeded U.S.SPA chronic, Ontario and Michigan ambient water
quality guidelines.
-------
469
Total lead concentrations were all below the method detection
limit (MDL) of <0.1 ug/L in the Detroit River head and mouth
transects. Several locations in the Trenton Channel contained
total lead concentrations ranging from 3.24 ug/L to 10.61 ug/L,
which exceeded Michigan Rule 57(2) allowable levels (3.0 ug/L)
and the U.S.EPA chronic AWQC (3.2 ug/L). The highest concentra-
tion was upstream of the Grosse lie toll bridge along the western
shore of the Trenton channel (transect A, Figure IX-3). Tran-
sects C and D also have total lead concentrations exceeding
guidelines along the western shore of the channel. Total lead
concentrations in Ontario tributaries were determined for the
Little River (3-13 ug/L), the Canard River (3-30 ug/L) and Turkey
Creek (3-33 ug/L}. These tributaries all contain total lead
concentrations above guidelines (26,35). Concentrations of total
lead in Michigan tributaries were not available for this report.
Total zinc concentrations increased between upper (1.2 ug/L) and
lower (3.3 ug/L) Detroit River transects. Each of the tributar-
ies also had high mean zinc concentrations, with the Ecorse River
having the least (14 ug/L) and the Rouge River the highest (167
ug/L) total zinc concentrations. With the exception of the Rouge
River and the Little River (74 ug/L), water concentrations were
below ambient water quality guidelines. Little River concentra-
tions of total zinc exceeded GLWQA specific objectives (30 ug/L).
Rouge River total zinc concentrations exceeded this guideline and
also the U.S.EPA chronic and acute AWQC.
Total phosphorus concentrations were nearly twice as high at the
Detroit River mouth (15.7 ug/L) compared to the river head (8.6
ug/L). Total phosphorus concentrations in the major Detroit
River tributaries were much higher than concentrations in the
Detroit River.
Filtered chloride concentrations increased from 6.7 mg/L to 8.4
mg/L between upper and lower Detroit River transects. The lower
Detroit River transect was located above General Chemical, a
major chloride loading source discussed later, and therefore this
loading was not reflected in the Detroit River mouth transect
value shown in Table IX-1. The filtered chloride concentrations
in the Detroit River tributaries were one to two orders of mag-
nitude greater than the Detroit River head. Total chloride con-
centrations (not shown) did not increase between the head and the
mouth. The drinking water guideline for chlorides (250 mg/L) was
exceeded in Turkey Creek and North Drain.
Nutrients, Dissolved Gases and Microorganisms:
The basic plant nutrients in the Detroit River include
phosphates, nitrates, and silicates. Dissolved oxygen and the
metals iron, sodium, calcium, magnesium, manganese and aluminum
are also present in sufficient quantities. The oversupply of
phosphate, chloride and ammonia has decreased substantially over
-------
470
the past 20 years.
Dissolved organic carbon (DOC) and particulate organic carbon
(POC) are often many times greater than the organic carbon found
in living plankton, macrophytes, and fauna produced in streams,
DOC measurements available from Lake Huron, the St. Clair and
Detroit Rivers are in the range of 2-3 g/m^. The POC entering
the St. Glair-Detroit liver system from Lake Huron is about 0.7
g/m3. An average of 1.4 g/rn^ was measured at the mouth of the
St. Clair River, and up to 2.0 g/m? were found in Lake St. Clair.
A single POC sample from the mouth of the Detroit River was 3.8
g/m.3, Suspended solids increased by a factor of six between Lake
Huron and Lake Erie, and bed load POC has not been studied, so
3.8 g/m3 may underestimate POC in the Detroit River.
Although not measured during these studies, fecal conform bac-
teria are of concern in the Detroit River because fecal coliform
bacteria standards and criteria have been violated on both sides
of the river. The Ontario objective is 100 counts/100 ml and the
Michigan standard is 200/100 ml fecal coliform bacteria. Beaches
have been closed or not developed because of this continuing
problem.
Water Bioassays;
Seven day chronic bioassays measured the impacts of Detroit River
near-bottom water on Ceriodaphnia. Reproductive success was
significantly reduced (mean young produced/female) relative to
Lake Michigan controls at all four test sites, Station 83 near-
bottom water collected along the southwestern shore of Fighting
Island produced the greatest reduction in the number of young
produced/female (70 to 100% reduction) followed by stations 34
{along the west shore of the Trenton channel)» 53 (at the south-
ern tip of Grosse He and 3OCR (in Monguagon Creek), These re-
ductions were most severe from July to September (36).
Considering both exceedences of water quality and impacts on
biota, the pollutants of concern in water of the Detroit River,
or that of its tributaries, include PCBs, chlorobenzenes, PAHs,
total cadmium, total mercury, total lead, total zinc, and total
phosphorus, in addition to fecal coliform bacteria.
Biota
i) Phytoplankton, Macrophytes and Zooplankton
Detroit River phyt©plankton communities consist of low densities
(500 cells per ml) of 82 species dominated by diatoms (8,10,37).
Summer blue-greens contribute to phytoplankton community, but
Detroit River picoplankton, a large component of the phytoplank-
ton biomass, were not surveyed.
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471
Activity causing habitat loss, such as filling or dredging, water
or sediment contaminants or simply continuous elevated suspended
solids that reduce macrophyte production, reduces desirable fish
and wildlife production in the Detroit River and western Lake
Erie. Macrophyte production was estimated at 16,410 metric tons
of ash-free dry weight/yr (12) . Only 25% is from emergents re-
flecting the limited habitat presently available.
Detroit River zooplankton populations (potential larval fish
food) were 85% copepods with other zooplankton populations at
very low relative abundances. Zooplankton densities were greater
during the night than the day with typically patchy distribution
with peak numbers between June and September (36,38). Zooplank-
ton are a critical component in the diet of many larval and some
juvenile fish. Poor diversity or depressed zooplankton produc-
tion is likely to result in poor fish year classes during natur-
ally occurring or contaminant related stressful conditions.
ii) Benthic Macroinvertebrates
Diversity and abundance of benthlc macroinvertebrates are lower
in the deep, fast flowing areas of the river because the sub-
strate is either difficult to adhere to or burrow into. Shal-
lower, uncontaminated zones containing macrophytes are likely to
yield the greatest diversity. The greatest densities are reached
in strongly enriched, unconsolidated sediments where oligochaetes
are often monotypic.
The Detroit River benthic community upstream of Zug Island is
diverse and dominated by pollution intolerant organisms with the
exception of the Windsor shoreline. Adjacent to Zug Island, the
community is severely impacted, and downstream, especially in the
Trenton Channel, the community is dominated by pollution tolerant
oligochaetes (13,15,39). The Ontario shoreline is considerably
better as evidenced by the presence of pollution intolerant may-
flies (11,15),
Schloesser, et al. (40) demonstrated an inverse relationship
between Hexagenia abundance and visible oil in sediments of the
Connecting Channels, Edsall et al. (41) found Hexagenia averag-
ing 2,086 mg dry wt/m3/yr at three locations where sediment con-
taminants did not exceed sediment guidelines, but only 364 mg dry
wt/m-vyr where as many as seven contaminants exceeded these
guidelines.
Native Detroit River Lampsilis radiada siliquoidea, at 4 stations
along the Ontario shore, contained lead and cadmium ranging from
3 to 9 and 3.5 to 6.2 mg/kg respectively (42). PCBs ranged from
73 to 196 ug/kg at these same locations. Octachlorostyrene (OCS)
in clams ranged from 31 to 57 ug/kg, 70 to 285 times higher than
sediment concentrations.
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472
Caged Elliptic compalanta placed in the Detroit River for 18
months accumulated HCB and QCS and a variety of organochlorine
pesticides (43) . Highest levels were found along the western
Detroit River shore near Conners Creek, the lower Trenton Channel
and the Rouge River, PCBs were the major organochlorine clam
contaminant, ranging from 20 to 293 ug/kg along the Michigan
shore; clams from the Ontario shore had much lower concentrations
(Figure IX-8),
Polynuclear aromatic hydrocarbons (PAHs) were also reported in
caged clams at elevated levels along the Michigan shoreline and
downstream in the Trenton Channel ranging from 136 to 772 ug/kg.
Along the Ontario shoreline PAHs ranged from 52 to 274 ug/kg,
ill) Fish
Five fish species were collected from six sites in the lower
Detroit River and examined for external lesions, necropsied for
internal abnormalities and tissues removed for histological
examination (Figure IX-9) (44), Several neoplasms and pre-neo-
plastic lesions were found in Detroit River brown bullhead,
walleye, redhorse sucker, white sucker and bowfin. Bullhead and
walleye were the only two species exhibiting dermal/oral neo-
plasms at 14,4 and 4.8 %, respectively, other species exhibited
liver neoplasms with highest incidence observed for bowfin at
15,4%. In bullhead, no relationships between dermal/oral and
liver tumors were found. Tumor incidence age/size related
since tumors were present in bullheads over 25 centimeters and in
walleye over 50 centimeters. Of the six sites examined, bull-
heads at Point Hennepin Gibraltar Bay, exhibited the greatest
tumor incidence at 36.4% and 33.3%, respectively. Bullheads near
Mud Island north of the Trenton Channel and in the lower end of
the Trenton Channel did not exhibit tumors.
In this study (44), bile analyzed for ben2o(a)pyrene (BaP)
and its metabolites. All species had BaP or its metabolites in
their bile. Walleye and redhorse sucker contained the greatest
BaP concentrations, with concentrations in bullhead substantially
lower. The greatest BaP concentrations were in bowfin red-
horse sucker from Point Hennepin and in brown bullhead, walleye,
and white sucker from Mud Island.
Contaminants exceeding relevant guidelines were found in the
flesh of fish in the Detroit River, PCBs were found in carp,
with concentrations exceeding the Ontario' Ministry of Environment
(OMOE) and Ontario Ministry of Natural Resources fish consumption
guidelines and the U.S. Pood and Drug Administration action level
of 2 ppm, as well as the GLWQA specific objective of 0.1
(Figure IX-10). PCBs in young-of-the-year spottail shiners were
found at significantly (p<0.01) higher concentrations along the
Michigan shoreline than along the Ontario, suggesting Michigan
inputs of PCBs (45). High concentrations of mercury were found
-------
473
629
294
552
Michigan
58
695
N
Total PCS
Concentrations
ng/g. wet wt.
FIGURE IX-8. Total PCB concentrations in Detroit River caged clams.
-------
474
Michigan
Fish Sampling
Locations
n
FIGURE IX-9. Fish sampling locations for tumor analysis.
-------
475
PCB^ppm
Carp 6.7
^_.__ —— Spottail .006
_ — _—..—.. — • — • Spottail .007
Spottail 03
Carp 10.7
Spottail ,007
Spottail .009
Spottail 2.6
FIGURE IX-10. PCBs and HCB concentrations in Carp and Spottails shiners.
-------
476
in the edible portion of several species of fish (rock bass,
freshwater drum and walleye). Concentrations were above both the
GLWQA specific objective and the Ontario fish consumption ad-
visory of 0.5 (46,47). Other chemicals, such as HCB, OCS,
chlordane and DDT metabolites, were uniformly distributed in
Detroit River spottail shiners, suggesting a diffuse source (45).
iv) Birds
Thirteen wintering lower Detroit River diving ducks (7 lesser and
3 greater scaups and three goldeneyes) were analyzed for organic
chemical contaminants (48). Total PCBs ranged from 2 to 20
mg/kg, indicating significant bioaccumulation. Highest mean
concentrations of other residues in ducks were 1.7 mg/kg hexa-
chlorobenzene in goldeneyes, and trans-nonachlor {0.33 mg/kg) and
4,4' DDE (1.3 mg/kg) in greater scaups. Similar chemical resi-
dues were also found in some tern species. concentrations of
total PCBs in Detroit River seston {5.2 mg/kg} and oligochaete
worms (0.44 mg/kg) mg/kg) were also noted.
Herring gull eggs from Fighting Island contained high PCS and HCB
concentrations in 1985 and 1986 studies. Detroit River herring
gull eggs contained the lowest concentrations of dieldrin, hepta-
chlor epoxide, photomirex, oxychlordane and alpha hexachloro-
cyclohexane in the Great Lakes {49).
Detroit River waterfowl surveys completed in 1982 showed dramatic
declines in merganser and black ducks, and dramatic increase in
canvasbacks and redheads since 1974 {50). It was postulated that
loss of emergent macrophytes caused by high Great Lakes water
levels caused this reduction in dabbling ducks,
In summary, the pollutants of concern in Detroit River biota
include PCBs, PAHs, HCB, OCS, mercury, lead, cadmium and oil and
grease. Other biota concerns include habitat alteration and fish
tumors.
S e diment_ _Qual_ity
i) Sediment Characteristics
Sediments in the Detroit River are generally sandy, consolidated
clay or bedrock because of the relatively high flow velocities.
Sediment particle size analysis conducted in 1980 revealed that
surficial sediments were generally sand, but gravel dominated
areas of high velocity along the Detroit waterfront, the entrance
of the Trenton Channel and the upper Amherstburg Channel. Fine-
grained samples were collected in slow waters near tributary
mouths. Silts and clays were found downstream of zug Island, in
the Rouge River, the Trenton Channel near Trenton and the Detroit
River mouth (51,52).
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477
Detroit River sediment thickness over bedrock, revealed a maximum
sediment thickness of 33 m near Belle Isle, which declined stead-
ily southward to nearly zero in the Trenton Channel and zero in
the main channel (53). The outer and Amherstburg Channel silt
layer averaged 0.45 to 0.50 m near Lake Erie and zero in the
Amherstburg Channel at Bois Blanc Island and in the Ballard Reef
Channel.
The Michigan Detroit River tributaries which were not sampled in
1982 were sampled in 1985, revealing fine-grained, anthropogenic
sediments frequently of sludge-like consistency (54,55). Samples
in Monguagon Creek and downstream of the Rouge River contained
very fine sands, silt, and coarse sand and gravel. The upper
Rouge River sediments were coarser than elsewhere, consisting of
medium to fine sands with little very fine sand sediments.
Conners Creek sediments also had only minor amounts of fine to
very fine sands. Studies conducted in 1986 at 47 sites (56,57),
generally confirmed the earlier findings.
ii) Sediment Transport
Detroit River average main channel velocities are 0.49 to 0.88
m/sec, but surface velocities may be nearly twice that rate in
the main channels (0.9 to 1.2 m/sec)(58), Sand is transported in
the main channels when the velocity exceeds 0.42 m/sec, while
along the shore and in shallow water areas, where velocities may
drop to 0.25 m/sec or less, sand deposition occurs. Navigation
channel bottoms are scoured by currents leaving few sediments to
resuspend, and no significant relationships between ship passage
turbidity has been found (59).
A field portable shaker device was used to measure sediment
resuspendability at eight Trenton Channel locations from Mon-
guagon Creek to Celeron Island. Lick et al. predicted that
resuspension could occur regularly in the Trenton channel (60).
Direct instantaneous measurements of flow velocity, turbidity and
sediment concentration at four locations in the Trenton Channel
using instrumented towers assisted the above researchers (61).
iii) Navigation and Dredging
Until recently, the entire Detroit River commercial navigation
system was dredged by the U.S. Army Corps of Engineers (USCOE) to
a depth of 8.2 m below low water datum. At present, the Ontario
portion of these channels are dredged by Public Works Canada
under contract to Transport Canada. Before enactment of the
Rivers and Harbors_Act of 1970, nearly 3 million m3 of dredged
materials were disposed of in the open lake at two sites in Lake
Erie south of the Detroit River mouth (62). In addition, an
unknown amount of Detroit River dredged materials were placed in
Lake St. Clair, near the head of the Detroit River. Since 1970,
about 30,100 m.3 of polluted dredged materials were placed on
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478
Grassy Island. From 1979 to 1984, 3.1 million m^ of dredged
material were deposited in the Pointe Mou-illee confined disposal
facility (CDF) near the Huron River mouth (58), In 1985, 814,000
m-3 of polluted Detroit River material was scheduled for disposal
in the Point Mouillee CDF. Rouge River sediments, since 1950,
have been placed on Grassy Island (62) . Some polluted dredged
materials were also disposed of along the lower Raisin River
prior to 1979. Mud Island, a small containment site near Grassy
Island, was also used for dredged material disposal.
iv) Sediment Contamination
Results of the six major surveys conducted since 1982 include
contaminant chemistry at approximately 135 sites (51,54,55,63,64,
65,66,67,68,69,70,71,72,73). For ease of presentation, the
Detroit River was divided up into seven subareas (Figure IX-11).
Because the purposes for the survey, sampling gear, analytical
methods, depth of sample collection, compositing techniques and
sampling locations varied considerably between the studies, com-
parison of these data from, year to year may not be entirely
valid. However, an attempt was to make comparison.
Organics - Polychlorinated Biphenyls:
High total PCS concentrations were found by six surveys in all
subareas except subarea 7 (Table IX-2, Figure IX-11). The high-
est mean sediment PCS concentrations were found in subarea 2,
just below Belle Isle, where 5 of 10 samples exceeded 10,000
ug/kg in 1986. These were associated with sewer system outfalls,
and indicate that combined sewer overflows have historically
been, and may still be, an important source of PCBs (64),
The 1984 analyses of Oliver and Pugsley (74) noted localized
areas of high concentrations of PCBs downstream of the Detroit
WWTP and the Rouge River (in subarea 3), at concentrations higher
than reported in 1980 (75), assuming the methodologies of the
1980 and 1984 studies were comparable. Comparison of 1982
1985 collections are supportive of the conclusion that subarea 2
sources were more significant than the Rouge River. Rouge River
sediments collected at the mouth in 1986 revealed total PCBs up
to 3,500 ug/kg (76). Samples collected downstream of the Detroit
WWTP outfall and off the Rouge River mouth in 1985 and 1986
revealed PCBs up to 2,840 ug/kg near Zug Island (28). Concentra-
tions up to 3,800 ug/kg were found in the Ecorse River (subarea
4). The highest concentrations in the navigation channel (sub-
area 4) was 140 ug/kg, between Grosse lie and Fighting Island
(77). Sediments analyzed from along the Windsor waterfront
showed PCS concentrations ranging from less than 1 ug/kg to 370
ug/kg.
Sediment collections made in 1982 and 1985 also indicate PCB
sources in subarea 6, the Trenton Channel. Highest levels were
-------
479
FIGURE IX-11. Detroit River sub-areas for sediment sampling.
-------
TABLt IX-2
Po I jr chlorinated biphamjrl IPCB1 concentrations in Patreit River i«diiment» lug/kg)* "*«
SUI-AREA-1
1 MAX
MIN
MEAN
n
SD
S MAX
MIN
ME AM
n
SP
3 MAX
MIN
MEAN
n
SD
4 MAX
MIN
MEAN
n
SD
5 MAX
MIN
MEAN
n
SD
6 MAX
MIN
MEAN
n
SD
7 MAX
MIN
MEAN
n
SD
HDHB
2900
100
874
9
608
4000
1910
147
10
10561
4800
870
3007
7
1357
1000
290
64S
2
355
OM0g
420
35
110
7
624
1815
25
551
8
524
11780
40
5900
2
5860
BP482
• 133
1 16
2361
7
2704
12010
6200
9638
3
2705
B647
1229
3901
8
2609
12810
0
4095
25
3815
13870
2350
7526
6
9988
2B27
22
98B
a
1303
EjEAJiJi
2020
9b2
I4il
2
S2i
2213
968
1538
7
399
588
206
417
3
158
1590
149
1090
2
440
604
368
80ft
8
10218
DOE
470
0
91
6
no
ISO
190
190
1
0
1900
7
1506
to
2921
8000
41
1462
6
2927
320
3
86
8
107
1400
29
642
6
437
51O
10
188
6
188
U.S. FNS
358
0
79
a
111
6410
163
1494
4
2261
4000
135
1166
4
1637
1038
0
274
8
367
957
0
U61
10
31i
9130
336
2471
6
3093
369
154
281
7
87
= number of samples.
Kizlatiskas and Pr«nnk*vieiM8 I S3 I.
The six surveys were performed by th« Michigan D*$»t,
«*
CD
O
of Natural
IMDNR), Ontario Ministry of the
-------
481
in Monguagon Creek (13,870 ug/kg}, although very high PCS con-
centrations were found near BASF/Federal Marine Terminal Prop-
erties and below McLouth Steel, near Trenton, Tributary data
collected in 1985 also targets Monguagon Creek as a PCS source,
with concentrations in the creek of up to 1,530 ug/kg (55),
Since PCB concentrations of up to 9,130 ug/kg were reported in
the Trenton Channel proper, other sources are contributing PCBs
to the Trenton Channel in addition to Monguagon Creek (56) .
Bottom sediments from Ontario tributaries obtained during the
1984-1985 survey revealed PCB concentrations of 1,305 ug/kg, 248
ug/kg and 20 ug/kg at the mouths of Turkey Creek, the Little
River and the Canard River, respectively (5) ,
Many of these PCB sediment concentrations in the Detroit River
and its tributaries , in Michigan and Ontario (particularly ad-
jacent to and downstream of Detroit, Windsor and Ambers tburg and
in the Trenton Channel J , exceed dredging guidelines. Guidelines
exceeded include the OMOE dredging guidelines (50 ug/kg) , the
U.S. EPA dredging guidelines (10,000 ug/kg) are higher than
the guidelines recommended for Lake Erie by the Dredging Sub-
committee of the Great Lakes Water Quality Board (up to 252
Hexaehlorobeniene ;
Sediments collected in 1982 and 1985 in subareas 3, 6 and 7 con-
tained hexachlorobenzene (HCB) exceeding 100 ug/kg. Concentra-
tions of HCB in 1985 downstream of Monguagon creek ranged from 26
to 140 ug/kg. Inputs from the St. Clair River are probably minor
since loadings between the St. Clair River mouth and the head of
the Detroit River were reduced at least 95%, Increases noted
within the Detroit River may arise through diffuse or unknown
minor inputs. The highest concentrations of HCB were found, in
Michigan at the mouth and downstream of the Rouge River in
the Trenton Channel; in Ontario adjacent to AmJaerstburg and
east of Fighting Island, There are no dredging guidelines for
HCB,
Polynuclear Aromatic Hydrocarbons:
Polynuclear aromatic hydrocarbon (PAH) analyses were performed on
Detroit River sediments in 1982 and 1985, Total PAH values
ranged from 620 to 265,000 ug/kg along the Michigan shore down-
stream of Belle Isle, High total PAH levels (up to 125,000
ug/kg) were also reported in the lower Rouge River, In 1985,
PAHs were reported in the Detroit Dearborn Channel all
Michigan Detroit River tributaries, ranging from a low concentra-
tion of 600 ug/kg to a high concentration of 600,100 ug/kg in
Monguagon Creek, Most tributary PAH samples were dominated by
3-, 4-, and 5-ring PAH compounds. Two-ring naphthalenes were
found in appreciable quantities only in the Monguagon Creek and
-------
482
the Rouge River. There are no dredging guidelines for total
PAHs.
Phenols:
Phenols ranged from, nondetectable to 44,000 ug/kg in localized
areas within subarea 6 along the Michigan shore. High levels
were generally found in subareaa 1, 2, and 3 near the Edward C,
Levy Company. There are no dredging guidelines for total phen-
ols.
DDT and Metabolites:
DDT analyses were performed on Detroit River sediments collected
in 1982 1985. In 1982, the highest total concentrations
were found near Belle Isle (2,265 ug/kg}. In 1985, total DDT was
highest in subarea 1. DDT and metabolites were found in all 1985
samples ranging from 7 to 482 ug/kg (Conners Creek}. High levels
of total DDT were also found in the Rouge River mouth and Trenton
Channel, suggesting recent additions that have not been degraded.
Sediments from the mouths of Ontario tributaries generally con-
tained less than 5 ug/kg p'p'-DDT, while breakdown products p'p1-
DDE and p'p'-DDD approached maximum levels of 36 ug/kg and 20
ug/kg, respectively. There are no dredging guidelines for DDT or
its metabolites.
other Pesticides;
Approximately 34 other pesticides were analysed in sediments in
1985, 14 of which were found in bottom sediments, Alpha-chlor-
dane, gamitia-ehlordane, dieldrin and methoxychlor were most com-
monly found. Highest dieldrin levels were found in subarea 5, at
the Canard River mouth (30 to S5 ug/kg). Methoxychlor and gamma-
chlordane were highest in sub-area 3, Maximum levels in bottom
sediments for methoxychlor were 86 ug/kg while ganraaa-chlordane
levels were 10 ug/kg.
Several chlorinated pesticides were found in the Detroit River
sediments collected in 1985 with highest levels in Monguagon and
Conners Creek sediments. Highest levels of trifluralin (19
ug/kg) were present in the Frank and Poet Drain and the only
occurrences of DCPA (Daethai) were in the Ecorse River and the
Detroit River Dearborn Channel, a tributary to the Rouge River,
Dieldrin (14 ug/kg) was highest in the Detroit-Dearborn channel,
while aldrin was found primarily in the Rouge River and Conners
Creek sediments.
Beta-BHC concentrations were elevated at Belle Isle (170 ug/kg)
and near the Ecorse River (195 ug/kg) in 1982 collections.
Gamma-chlordane was found throughout the study area with peaks at
Conners Creek and the Ecorse River, Concentrations of other
-------
483
pesticides in sediments showed no distinct relation to potential
sources.
Phthalate Esters:
Phthalate esters were found in 14 of the 20 Detroit River tribu-
tary samples in 1985. Highest levels were found on the Michigan
side in Conners Creek, the Rouge River and near the Federal
Marine Terminals and BASF properties (17,600 ug/kg), There are
no dredging guidelines for phthalate esters.
Volatile Organic Compounds:
Volatile organic compounds were found in 15 of 20 sediment samp-
les analyzed from the Detroit River tributaries in 1985. Di-
chloromethane appeared in 9 of the 20 samples ranging from 0.8 to
6.9 ug/kg in Monguagon Creek where the great variety of volatile
organic compounds were found. Highest concentrations were found
in subarea 7, in the Prank and Poet Drain. There are no dredging
guidelines for specific volatile compounds.
Metals - Mercury:
Mercury analyses were performed on sediments collected in 1982,
1985 and 1986. The highest levels in subarea 6 (Trenton Channel)
were located below the mouth of Monguagon Creek near the Edward
C. Levy Company (55.8 ing/kg) . However, a 1985 sample in Mon-
guagon Creek {1.5 nig/kg) indicated that Monguagon Creek was not a
prominent mercury source. Mercury analyses of sediments in sub-
area 6 exceeded 3.0 mg/kg, while bottom sediments in subarea 1
exceed 2.5 mg/kg. U.S.EPA and Ontario dredging guidelines for
mercury were exceeded at many sampled locations along the
Michigan and Ontario shores throughout the length of the river.
Lead:
Lead concentrations exceeded 200 mg/kg in subareas 1, 2 and 6 in
1982 and 1985. Tributary sediment levels were highest in Conners
Creek and the Detroit-Dearborn Channel of the Rouge River, rang-
ing from 500 to 750 mg/kg, but declined downstream to less than
100 mg/kg in subarea 1. Sediment lead concentrations for samples
collected in 1982 and 1985 were similar at subarea 6 above Eliza-
beth Park Canal {1,750 mg/kg). Dredging guidelines were exceeded
along most of the Michigan shore and downstream of Windsor and
Amherstburg in Ontario.
Arsenic:
Sediment data for 1982 and 1985 indicate that Detroit River sedi-
ments contain approximately 10 mg/kg arsenic throughout, with
elevated levels of 36 and 54 mg/kg found at Elizabeth Park Canal
and the Rouge River, respectively. The uniformity of the data
-------
484
suggests no major point or nonpoint sources of arsenic to the
Detroit River; however, dredging guidelines for arsenic were
exceeded.
Cadmium:
Peak cadmium concentrations were in subareas 1, 3" and 6, ranging
between 25 and 96 mg/kg. Cadmium concentrations in suspended and
bottom sediments were approximately equal, perhaps indicating a
persistent local source. Dredging guidelines for cadmium were
exceeded along the full length of the Michigan shore (especially
adjacent to Detroit and in the Trenton Channel) and adjacent and
downstream of Windsor and Amherstburg,
Copper:
Sediment data from 1986 show copper peaks exceeding 100 mg/kg in
subareas 2,3,4, and 6. Sediment data for 1985 showed generally
higher copper levels in subarea 1 and 3, than in 5 or 7 (approxi-
mately 100 mg/kg versus approximately 50 mg/kg), In 1982 and
1985, copper values exceeded 700 mg/kg in subarea 3, Turkey Creek
and the Rouge River. Dredging guidelines for copper were ex-
ceeded along the Michigan and Ontario shores, specifically ad-
jacent to the cities of Detroit, Windsor and Amherstburg and in
the Trenton Channel.
Zinc:
Sediment data for 1986 indicate levels of zinc exceeding 500
mg/kg in subareas 2 and 6. The 1982 and 1985 sediment data show
zinc exceeding 1,000 rag/kg in subareas 1, 2, 3 and 6. The Rouge
River, Conners, Turkey and Monguagon Creeks all appear to be
contributing zinc to the Detroit River. Dredging guidelines for
zinc were generally exceeded at the same locations as Cor copper.
Chromium:
Sediment data for 1986 indicate chromium levels exceeding 100
rag/kg in subareas 2 and 6. The 1985 sediment data show tributary
sediments as chromium sources in subareas 1 and 3, where suspen-
ded and bottom sediments contained greater than 300 mg/kg total
chromium, indicating a continuing source. Chromium levels were
nearly twice as high in the Detroit Dearborn channel of the Rouge
River as the lower Rouge River sediments. The 1982 chromium
peaks were not apparent in the 1985 subarea 6 sediments samples,
perhaps indicating some source control. Dredging guidelines were
exceeded at several locations in the Detroit River (as per cop-
per) ,
-------
485
Nickel:
High nickel levels {500 mg/kg) were found in bottom sediments
from the Ontario tributary in subarea 1, the Little River. Sedi-
ment nickel levels exceeded 50 mg/kg in subareas 2, 3 and 6 in
1986, while 1985 data indicate subareas 1 and 3 as having high
nickel contamination. The high nickel levels found during the
1982 survey in subareas 4 and 6 were not evident in 1985 data.
Dredging Guidelines were exceeded at several locations (as per
copper),
Manganese;
Manganese levels exceeding 1,000 mg/kg were found in subareas 3,4
and 6 (the Rouge and Ecorse Rivers and Monguagon Creek) in 1985,
which about the same as in 1982. High manganese in subarea 7
in 1982 was not reported in 1985, but 5,000 mg/kg manganese was
reported in the Ecorse River in 1985 that was not noted in 1982.
Dredging guidelines for manganese were exceeded along the
Michigan shore. Manganese concentrations in Ontario sediments
were not determined.
Iron:
Sediment concentrations of iron from the 1982 survey reached
180,000 mg/kg above Elizabeth Park (subarea 6), Iron levels
along the Michigan shore were very high in 1982, with some sta-
tions in all subareas exceeding 25,000 mg/kg. The highest iron
concentration found during the 1985 survey was 120,000 mg/kg from
the Ecorse River. Dredging guidelines were exceeded along the
Michigan shore. Iron concentrations were not determined for
sediments along the Ontario shore.
Cobalt:
Cobalt was analyzed in 1982, 1985 and 1986. The 1986 cobalt
concentrations were relatively uniform with a slight increase
downstream. Highest levels (over 10 mg/kg) were found in subarea
6. The 1982 samples were also relatively uniform, although
slightly higher than 1986 samples. The highest cobalt levels
were found in the 1985 tributary samples in subarea 3 in the
Detroit Dearborn Channel (17 mg/kg). No exceedences of dredging
guidelines were noted.
Nutrients and Conventional Pollutants - Cyanide:
In 1982, cyanide levels exceeding 10 mg/kg were present in sub-
areas 1,3 and 6. in 1985, high cyanide concentrations were pres-
ent in subareas 1 and 3 (Conners Creek and Detroit Dearborn
Channel). Lower levels were found in the Lower Rouge and
Monguagon Creek, indicating that sources other than Monguagon
Creek were responsible for high levels found in subarea 6 in
-------
486
1986. Exceedence of dredging guidelines for cyanide occurred in
Michigan and Ontario adjacent to Detroit, Windsor and Aniherstburg
and in the Trenton Channel.
Oil and Grease:
The highest oil and grease levels found during the 1986 survey
were reported in subarea 6 with concentrations over 24,000 mg/kg.
In 1985, oil and grease levels were highest in subareas I (44,800
mg/kg) and 3 (28,600 mg/kg), and generally decreased downstream
from the Detroit River head to its mouth. In 1982, peak oil and
grease levels exceeding 30,000 mg/kg were present in subareas 1,
2,3 and 6. Dredging guidelines for oil and grease were exceeded
in many areas, primarily along the Michigan shoreline adjacent to
and downstream of Detroit and in the Trenton Channel, as well as
adjacent to the cities of Windsor and Aniherstburg.
Total Phosphorus:
Most total phosphorus concentrations in sediments were lower than
5,000 mg/kg. Along the Michigan side, phosphorus levels up to
6,200 mg/kg in 1982 were found in subarea 6, whereas the highest
level in 1985 (6,200 mg/kg) was found in the Detroit Dearborn
Channel. Exceedences of phosphorus dredging guidelines were
noted in the majority of samples analyzed in both Michigan and
Ontario.
Ammonia:
The 1982 concentrations of ammonia exceeded 500 mg/kg in subareas
1,3,4, and 6 with highest levels (1,400 mg/kg) in the Rouge
River. In 1985, ammonia levels were below 500 mg/kg in all sub-
areas except subarea 1, where 900 mg/kg was found in Conners
Creek, Dredging guidelines for ammonia were exceeded along the
Michigan shore. Ammonia concentrations were not determined for
sediments from the Ontario shore.
v) Sediment Bioassays
Certain Detroit River depositional zone sediments have demonstra-
ted a range of toxicity to various forms of aquatic life, and
some Detroit River sediments have been tentatively classified as
hazardous waste. Figure IX-12 shows the status of macrobenthic
communities along the Detroit River. Bacterial bioluminescence
IPhosphobacterium phpsphoreum) assays (MicrotoxR) conducted on
Detroit River sediment porewater provided dose-response relation-
ships with degree of toxicity inferred by a decrease in light
emission. Figure IX-13 indicates that localized western near-
shore Trenton Channel stations caused a 50% reduction in bio-
luminescence with less than 100% porewater while other stations
elicited lesser responses and 30 percent of the stations were
nonresponsive (78).
-------
487
Status of M a cro b e ntft o s
Commortlt les
FIGURE IX-12. Macrobenthos distribution in the Detroit River.
-------
488
rl
ra
o
a
f">
CD i
^_
s
n
03
o
o
— 42*15'
DETROIT
RIVER
1986
Microtox
Toxicity
Sjmbol Statement
>
•
*
Great
Moderate
Slight
None
— 42°05
FIGURE IX-13. Detroit River sediments porewater Microtox toxicity.
-------
489
Mutagenic potential of sediment extracts were measured by the
bacterial Salmonella/microsome assay (Ames test) . Some mutaeren-
icity was noted at 28 of 30 Detroit River stations, with the most
strongly mutagenic sediments from the Trenton Channel (Figure IX-
14}. Moderately mutagenic sediments were primarily concentrated
in the lower river near Lake Erie (44),
Bacterial and phytoplankton bioassays were conducted on control
sediments and water along the west end of Fighting Island and the
southern end of Grosse lie, measuring changes in the rate of food
uptake in bacteria and phytoplankton photosynthesis. Bacterial
uptake rates were suppressed by control and contaminated sedi-
ments when sediments exceeded 12 to 1,200 ppm of suspended sol-
ids. At 120 ppm suspended solids, control sediments inhibited
uptake by 50% whereas contaminated Trenton Channel sediments
inhibited uptake by 75%. The impact of sediments on phytoplank-
ton was similar to bacteria, but less accentuated (36).
Daphnia pulicaria feeding was generally inhibited 50 to 75% by
Detroit River elutriate with an approximately three fold decrease
in ingestion rate at station 34, downstream of McLouth Steel near
Trenton. Slight feeding suppression of the control at stations
33 (along the west shore of Fighting Island) and 53 (at the
southern tip of Grosse lie) were reported at high elutriate con-
centrations (363 ,
The acute toxicity of Detroit River sediment porewater to Daphnia
magna was demonstrated in a study where ten of the thirty sta-
tions in the Trenton Channel caused 50% mortality in a 96-hour
exposure to 50% or less concentration of porewater (IB).
Ten day Chironomus tentans growth tests using whole sediments
found the greatest growth inhibition (up to 95%) along the west-
ern near-shore Trenton Channel. Growth rates for these stations
ranged from 0,02 to 0.08 mg/day, whereas reference stations
three other stations ranged from 0.48 to 0.53 mg/day (36),
Stylodrilus used to determine avoidance response to Detroit
River sediments. In control sediments, all worms burrowed and
remained buried with no mortality. At other stations, 70% of the
worms remained buried, but a slight increase in mortality rate
was evident. At station 34, downstream of McLouth Steel near
Trenton, only 10% remained buried, with a 53% mortality (36),
Chironomus tentans respiration, undulation, turning and crawling
movements and rest responses to Detroit River sediments showed
significant differences in escape, respiration and rest respon-
ses , relative to Lake Michigan control sediments. Escape time
was higher and respiration and rest time were lower at these
stations compared to the Lake Michigan sediments (36).
-------
490
Michigan
Mutaaenic Potential
Strongly mutagenic
Weakly mutagenic
v Non mutagenic
FIGURE IX-14. Mutagenic potential of Detroit River sediments (Ames test).
-------
491
Feeding rates of larval channel catfish exposed to Detroit River
contaminated and control sediments and sediment porewater indi-
cate the greatest inhibition of feeding rates occurred from ex-
posure to Trenton channel sediments. There were no differences
in feeding rates when porewater and water column assays were
completed on Trenton Channel stations (36).
Late-eyed stage rainbow trout eggs were injected with serial
dilutions of Detroit River sediment extracts; all sediment ex-
tracts increased embryo mortality two to three fold relative to
the solvent carrier control. Incubated eggs and fry were moni-
tored but increased mortality was not evident in the early sac
fry stages. One year after injection, 3% of the survivors'
livers exposed to Monguagon Creek sediment extract at 100 ug/egg
had liver neoplasms (44).
Schloesser et al. (40) demonstrated an inverse relationship bet-
ween Hexagenia abundance and visible oil in Detroit Eiver sedi-
ments. Edsall et al. {413 found Hexagenia averaging 2,086 mg dry
wt/m^/year at three locations where sediment contaminants did not
exceed dredging guidelines, but only 364 mg dry wt/m^/year where
as many as seven contaminants exceeded these guidelines. Both
studies indicate that sediment contaminants had notable negative
impacts on the benthie community.
In summary, sediments of the Detroit River were found to be
severely impacted by a variety of compounds, including PCBs, HCB,
PAHs, total phenols, total cyanide, oil and grease, total phos-
phorus, ammonia and metals (total mercury, total lead, total ar-
senic, total cadmium, total copper, total line, total chromium,
total nickel, total manganese, total iron). In addition,
non-uGLCCS parameters were also found in sediments (pesticides,
phthalate esters and volatile organic compounds), Several tribu-
taries appear to be sources of many of these contaminants. Toxic
effects of the sediments and sediment porewater on benthic biota
were also noted by a variety of toxicity tests.
-------
492
B. SPECIFIC
The specific chemicals which are impacting the Detroit River
ecosystem, as determined in this study, and other concerns, are
identified in this section. They are summarized in Table IX-3.
1. Conventional Pollutants
In the past, severe oxygen depletion in the Lake Erie hypolimnion
was associated with, excessive inputs of phosphorus, and correct-
ive action was undertaken by most Jurisdictions to reduce phos-
phorus loadings. Since the Detroit River Is the major tributary
to Lake Erie, all phosphorus loadings from the Detroit River are
considered important. Concentrations of total phosphorus in the
Detroit River have steadily decreased since the late 1960s and
are presently below 20 ug/L. Tributary concentrations, however,-
still currently exceed ambient water quality guidelines.
Chloride concentrations in the Detroit River water were relative-
ly constant, and not excessive,' however, industry which
found to be discharging high levels of chlorides (i.e., General
Chemical) was not represented by the water quality survey. High
chloride levels may encourage the growth of halophilie phyto-
plankton in the Great Lakes which could cause a shift in the
phytoplankton, community and upper trophic levels.
Fecal coliform bacteria are of concern because fecal collform
bacteria standards criteria are routinely violated on both
sides of the river. Beaches along both shores have been closed
or not developed because of this continuing problem. Although
not demonstrated in this study, ammonia is also problematic,
since calculated levels of nonionized ammonia have periodically
exceeded the chronic criteria for coldwater fisheries (0.02 mg/L)
along the western Detroit River shoreline.
Phosphorus and ammonia concentrations in sediments exceeded
dredging guidelines at a number of locations in the Detroit River
and in tributaries.
2, Organic Contaminants
Polychlorinated biphenyl (PCS) concentrations in the Detroit
River were found at concentrations exceeding guideline levels.
Although the levels are below acutely toxic concentrations, high
persistence and bioaccumulative properties of PCBs may (and in
fact has) resulted in bioaccumulation of PCBs in aquatic organ-
isms. Similar findings are for several organochlorlne
compounds, including hexachlorobenzene, dieldrin, heptachlor,
heptachlor epoxide, chlordane and endosulfan. The effects of
these contaminants may not be found in the Detroit River itself
-------
493
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-------
494
but in Lake Erie, particularly its Western Basin. Significant
concentrations of polynuclear aromatic hydrocarbons (PAHs) enter
the Detroit River at and near the Rouge River mouth. There is no
water quality guideline for PAHs for aquatic life; however, many
of these compounds are known or suspected animal or human car-
cinogens .
Fine-grained sediments in the river are excessively contaminated
by a variety of organic contaminants. Several areas along the
Michigan shore contain excessive PCB concentrations. Organo-
chlorine contaminants other than PCBs are also found in most
Detroit River and tributary sediments. DDT and its metabolites,
dieidrin, methoxychlor, chlordane, trifluralin, hexachlorocyclo-
hexane and hexachlorobenzene are present. Polynuclear aromatic
hydrocarbons (PAHs) have been found at high concentrations in
Detroit River sediments. Excessive phenols were present in sedi-
ments of the Trenton Channel. High concentrations of phthalates
were present in many sediment samples from Detroit River tribu-
taries, particularly Conners Creek and the Rouge River. Exces-
sive concentrations of oil and grease are present in many Detroit
River depositional zone sediments, and have degraded benthic
macroinvertebrate communities (24).
Fish from several stations in the lower Detroit River had ele-
vated levels of certain organic chemicals. PCB concentrations
exceed consumption guideline levels in the edible portion of
Detroit River carp. Consequently, the Michigan Department of
Public Health has issued a consumption advisory for these fish.
Several Detroit River fish species exceed the GLWQA objective of
0.1 mg/kg (wet weight) total PCBs in whole fish tissue. OMOE has
also issued a fish consumption advisory for Detroit River carp
because of elevated body burdens of PCBs.
Waterfowl contain elevated PCB levels and other persistent or-
ganic chemicals. There are no existing criteria for a consumption
advisory to protect children and women of child-bearing age from
the potential effects resulting from consumption of these birds.
Herring gull eggs collected from Fighting Island in 1985 and 1986
contained high concentrations of PCBs and PAHs, and contained
several other organochlorine pesticides.
Native and caged Detroit River clams showed increased levels of
PCBs, PAHs and several organochlorine pesticides. Some PAHs
found in Detroit River sediments are probable human carcinogens,
and are thought to be responsible for some liver, lip and dermal
tumors in fish.
3. Metals
Concentrations of metals measured in water during the study were
generally all below the ambient water quality guideline, with the
-------
495
exception of mercury, which, exceeded Michigan's Rule 57(2) allow-
able levels throughout the river. Generally, water in the
Trenton Channel was of a poorer quality than other portions of
the river. During the 1986 Detroit River System Balance Study,
some localized areas exceeded water quality guidelines for iron
(GLWQA specific objective) cadmium, lead and mercury (Michigan's
Rule 57(2} allowable level). Water quality in the Little River,
Rouge River, Turkey Creek, the canard River and Ecorse River is
impaired with respect to certain metals.
Heavy metal contamination of Detroit River sediments is found in
most depositional areas, with concentrations of many metals ex-
ceeding guidelines. Lead, cadmium, copper and zinc levels are
significantly elevated in the Rouge River and Turkey Creek, and in
Detroit River sediments downstream of their confluences. High
levels of chromium and nickel are present in the Little River,
Manganese and especially iron are strongly elevated in Trenton
Channel sediments and other Michigan nearshore and sedimentary
zones,
Overall, certain Detroit River sediments are severely degraded by
heavy metals, especially in the Trenton Channel. This contamina-
tion may reduce or eliminate the viability of Detroit River and
Lake Erie sediments as substrate for benthic organisms, Desorp-
tion of contaminants and re-solubilization through chemical and
biological processes make an unknown portion of these chemicals
available to higher aquatic organisms.
OMOE has issued a fish consumption advisory on several fish
species because mercury concentrations exceed 0.5 mg/kg in the
edible portion of the larger sizes of these fish. Native and
caged Detroit River clams showed increased levels of several
metals, particularly lead and cadmium.
4. Habitat Alterations
Eighty-five percent of the wetlands and littoral zones along the
Michigan Detroit River shoreline have been eliminated by filling,
dredging and bulkheading. Aquatic plants which live only in the
littoral zone provide food, substrate, cover and nursery produc-
tion for aquatic organisms, and drive the production and energy
flow through the aquatic ecosystem. Loss- of the littoral zone
results in the loss of large segments of the upper trophic lev-
els, including fish. Habitat loss was the major factor, along
with pollution and overfishing, in the demise of the Detroit
River commercial fishery around the turn of the century. Large
areas of shallow water and marshes associated with tributaries
are still found on the Ontario shore, below Fighting Island.
Seventy percent of the remaining littoral zone is occupied by
submerged plants, macrophytes and other wetland plants.
-------
496
In the Detroit River, upstream of Eug Island, the benthic com-
munity is diverse and dominated by pollution intolerant organ-
isms, except along the Windsor shoreline. Adjacent to Zug Island
the community is severely impacted, and downstream, especially in
the Trenton Channel, the benthos is dominated by pollution toler-
ant oligochaetes.
Overall, aquatic biota, especially benthos, show detrimental
responses to contamination of Detroit River sediments with or-
ganic and inorganic substances, particularly in the lower river
and in the Trenton Channel. Laboratory tests with sediments and
sediment extracts indicate higher toxicity and increased mutagen-
icity on a variety of native species. Fish species diversity and
fecundity may also be negatively affected in some areas.
-------
497
C. SOURCES
This section discusses contaminant inputs from point and. non-
point sources in the Detroit River which were analyzed between
1984 and 1987.
1. Point Sources
Introduction, Qualifications and Criteria
During 1985, 1986 and 1987 the Michigan Department of Natural
Resources (MDNR), OMOE, U.S.EPA and Environment Canada collec-
tively monitored flow and effluent quality of major direct and
indirect point source dischargers to the Detroit River (direct
sources are those which discharge directly to the river and in-
direct sources discharge to the river via tributaries or drains),
Nine municipal treatment plants and 20 industrial facilities were
sampled over a 24 hour period (Michigan sources) or 3 to 6 days
(Ontario Sources) during 1985 and 1986. Composite samples were
analyzed for conventional pollutants, metals and trace organics,
including the list of contaminants chosen for the UGLCC Study
(Chapter I, Table 1-1)- Table IX-4 presents the industries sur-
veyed and the parameters which are regulated in their effluent.
Table IX-5 presents the municipal facilities and their regulated
parameters. Figures IX-15 and 16 show the locations of these,
and other, industrial and municipal facilities along the Detroit
River.
Shortcomings limit the inferences that can be drawn from the
survey, including the small data base, differences in survey
timing, and differences in sampling and analytical methods. The
U.S. surveys were performed in May, and July through September,
1986, while the Ontario data were collected between October and
December, 1985. The U.S. composited four grab samples (1 every 6
hrs), while Ontario samples were collected by automatic composite
samplers (1 portion every 15 min).
Differences in detection limits further hinder comparisons. The
U.S. generally used lower detection limits than did Canada, al-
lowing calculated loadings from Michigan facilities with no cor-
responding loadings from Ontario facilities for some parameters
(e.g., OCS and HCB). Consequently, the percent of the total
point source loadings to the Detroit River for some parameters
(depending on corresponding flow volumes) may be skewed towards
Michigan dischargers.
Flows
There were a total of 75 known point sources discharging 9,233 x
103 m3/d) to the Detroit River basin in 1986. Three Detroit
-------
TAHLE IX-4
Surveyed U.S. and Canadian industrial facilities in the Detroit River area and regulated paraisetera >•*.
y r s ,_£A_C
BASF Corporation
Chrysler Chemical-Trenton
Chrysler-Trenton Engine
Detroit Coke Corp.
Double Eagle Steel
Ford-Wayne Assembly
Great Lakes Steel
(National Steel florpl
BO" Mill
(ireat Lakes Steel
Ecorae Plant
Great Lakes Steel
?,ug Island Plant
McLouth Steel-Gibralter
HoLout.h Steel-Trenton
Monsanto Inorganic
Chemical Corp
Pennwa1t
Rouge Steel
Che «ica1 produc t i on
Chemical compounding
Auto engine manufacture
Coke production
Steel galvanization
Auto assembly plant
Steel »fg t processing
Steel mfg and processing
Pig iron, coke and coke-
by—products production
Steel processing
Steel & pi^ iron production
Food-grade specification
products manufacture
Chemical production
Steel and auto mfg
BEOU M1'EB_ PABAHETEftS3
TSS, TOO, alkalinity", aowioni a-N* , temperature*, 1,2-
dichloroethane*f I,2-dichloropropane*, bis(2-
chloroisopropyjiether*
TRC, pH, oil and grease, teaperature*
BODs , TSS, total phosphorus, pH, oil and grease,total
phenol
pH, temperature, oil and grease*
TSS t noncoiapl i ant 1 , oil and grease, total zinc (noncoeipl iant |,
dissolved oxygen, total toxic organica, pH inoncoBpliantI¥
temperature*. Kntered into Consent decree in October 1986.
no NPDES pernit
TSS, e>il and grease
TSS, total lead, total zinc, acrole in (22/365), oil and
grease
pH, oil and greaset ai&nonia-N, cyanide, total phenol•,
total lead, totai zinc, TRC, TSS
TSS, oil and grease, total lead, total zinc, total Iron*
pH> TSS, oil and grease, temperature* t unionized aumonia*f free
cyanide*, total phenol*
TSS, phosphorus, arsenic, amnonia-N, temperature*
alkalinity*, total cadniiun* , hexavnlent chroniiia* , amenable
cyanide" , total lead* , total usercury" , total silver*
TSS (lti/365), BORs, total zinc, TRC, total phenols, chloride,
annonia-N, total copper, total lead, oiJ and greaae, pH, COD,
temperature*,
TSS, total lead, total zinc, oil and grease, aamonia-N, total and
oxidizabie cyanide, total phenol, TRC, temperattire*
M3
do
-------
TABLE IX-4- Icont'd).
U.S. FACILITIES
OPERATION
BiflUUTEP
St. M»ry"8 Peerless Ce»ent
Company-Foreman Plant
St. Mary'n Peerless Cement
Company-Brennan Plant
Union Carbide-Linde Div.
Cement production
pH, te»pe r a tu re*
Clay slip production pH, TSS, temperature*
Nitrogen * argon production Phosphorus I3/12|, TSS (3/12), TRC, oil and grease, temperature*
CANAPIAM PACTLITIES
OPERATION
PARAMETERS*
Ford Hotor Company
fie«er»l Chemical
(All led Chemical>
Hi ekes Manufacturing
TSS I 23/24 ] )
Auto parts) manufacture
Chealcal *anufacture
Auto/truck bumper ofg
No regulated parameter* (exceeded TSS and phenol abjective* in
198S and 1986 I.
TSS, chloride*, BBBonia-N, fluoride*
No regulated paraaetera (exceeded objectives for nickel [8/24] and
indicates that Monitoring of the parameter is required! however, there IB no concentration or loading limit.
From th* UGI.CCS Point Source Workgroup Report {£}.
Exrwetiences of I i*ii tntiona during 1S1H6 for Michigan facilities and 1985-1988 for Ontario facilities are denoted in
parontheites. For example I IB/365) indicated that parameter's daily limitation *>aa exceeded IB days of 366.
Parameters listed comprise the total regulated by all NPDES permits for all otitfalla. Not nil outfalls «t a facility are
necessarily regulated for all parameters. The Point Source Workgroup Report should be consulted for a BOP* thorough and
comprehensive description of the f»<-iIity'a discharge requirenenta.
All Onturio industrial facilities are encouraged to conply with t,h* Ontario Indu»trial Effluent Objective*, which are
described in Chapter III of this report.
-------
TABLE IX-5
Surveyed U.S. arid Canadian Municipal facilities in the Detroit River area and regulated parameters '•2 .
U.S. FACILITIES
REGULATED PARAHETF.RS
City of Trenton WWTP
Detroit WWTP
BQJH (6/12), TSS (5^121, pH, FC, DO [8/121, TRO, total phonphorun
(5/12), ansBionia-N, cadmiu», silver, mercury, chloroform
BODs, TSS, pH, FC, DO,
total phosphorus, temperature
Grosse He Township WWTP
Walled Lake-Novi WWTP
Wayne County-Trenton WWTP
Wayne County-Wyandotte WWTP
CANADIAN FACILITIES
Amhersthurg WPCP
Little River WPCP
West Windsor WPCP
BODs, TSS (11/12 removal; 4/12 loading), pH, FC, DO, TRC, total
phosphorus, ammonia-N
BODs, TSS, pH, FC, DO, total phosphorus, arowonia-N (9/ti), CBODi
BODs, TSS (9/121, pH, PC 18/12tt total phosphorus (6/12», oil and
grease
BODs, TSS (4/12), pH, FC (12/12), DO, TRC, total phosphorus, aiwonia-N,
phenol, oil and grease
BODs (removal in 1S85), TSS (removal in 1985 and 1986), total
phosphorus fIB/24)
BODs, TSS, total phosphorus J4/241
BODs, TSS, total phosphorus (2/24)
Abbreviations: BODs = 5-day biological oxygen demand; TSS - total suspended solids; FC = fecal coliform
bacteria; DO = dissolved oxygen; TRC = total residual chlorine; CBODs = 5-day carbonaceou«
biological oxygen demand; COD = chemical oxygen demand.
From the UGLCCS Point Source Workgroup Report .
Exceedencs at timitat iona during 1986 for Michigan facilities and 1385-19B6 for Ontario facilities are
denoted in parentheses. For example, 12/24} indicated that a monthly limitation was exceeded 2 times in a
24 mot)til period.
m
o
o
-------
501
MICHIGAN
*MS»G*N MMCUJUtM.
CHCMCAL.
IV— *UJS3 CWf iMC*L Of
I CULVERT HSTILLEFIIII OO.
Stem
FIGURE IX-15. Industrial dischargers to the Detroit River.
-------
502
MIC H IQ A N
CONNCRS
CHEEK•
W 1 N 0 i 0 R
ormorrsTp
AUXIUARV OUTFALL
HIVEfi ROUGE
WIST WINOSOR STP
T STP OUTFALL
ONTA H 1O
Eeacae River
WAYNE COyNTY
WYANOOTTI
STP etrrewj.
RIVEBVIiW
THiNTON
OUTfMJ.
PQNTWCS
LITTLE BSViR STP
5km
•STP 1EVWOE TiREATMfNT PLANT OUTFALLS
— COMBNiO iEWEfi OVEHMWS
• SEVM«3i TSEATMENT PLANT LOCATIONS
B SPOIL AflEA
$MUNtC«U. WATER INTAKiS
FIGURE IX-16, Municipal dischargers to the Detroit River,
-------
TABLE IX-B. (cont'd 21.
PARAMKTER
Cobalt
Phenols
Cadmium
Lead
Zinc*
MKTHOD
DKTKCTION
LIMIT
ug/L
5 .0
O.O01
5 . 0
0.001
5.0
1 .0
10.0
10.0
10.0
10.0
10.0
0.2
0.2
5.0
0.2
0.2
s.o
1 .0
1 .0
1 .0
2.0
2.0
5.0
2.0
2.0
FACILITY
General Chemical
Detroit WWTP
West Windsor WPCP
(H.S-Zug Island
Little River WPCP
Ford Canada
Detroit WWTP
Rouge Steel
Wayne Co-Wyandotte WWTP
McLouth Steel -Trenton
GLS-Zug Island
Wayne Co-Wyandotte WWTP
Detroit WWTP
Ford Canada
Rouge Steel
McLouth Steel -Trenton
Ford Canada
Rouge Steel
Detroit WWTP
McLouth Steel -Trenton
Detroit WWTP
McLout.h Steel -Trenton
Ford Canada
Rouge Steel
Wayne Co-Wyandotte WWTP
FLOW
10s in3 /d
18.8
2! 60
142
as. a
52.5
71 . 3
216012695 1
1810
268
227
99.8
268
21601 2695 I
71.3
iaio
60
71 ,3
1810
21602685
227
2160(26951
227
71.3
1810
268
AVKRAGi
COMC .
ug/L
300
1 . 20
14.0
19.0
S.O
Total ;
«58
21.0(141
a. 53
36 .0
24.0
32 .0
Total :
22.8
0.65(5)
11.2
0.3
O.i
Total :
425
4 .7
3.3(511
16.6
Total:
103! 1061
603
1«50
41 .1
120
LOADING
kg/d
5. §4
2. 59
1 .96
1 .9
0.53
12.61
48. 2
45. 4(39>
17.3
9.7
5.4
3.2
129.2
6.1
1.4(13)
0. 797
0. 55
0.136
8.983
30.3
tt.53
7.13 ( 137 1
3.77
49.73
223 |2«3)
137
132
74 ,B
32.3
% TOTAL
POINT SOURCE
CONTRIBUTION2
43.7
20.1
15.1
14.7
4.1
97.7
35.7
33.6
12.8
7.2
4.0
2.4
95,7
67.0
15.4
B.8
B.O
1.5
98.7
58.2
IB. 4
13.7
7.2
95.5
34.8
21.4
20.6
11.7
5.0
Ul
o
Ul
Total:
599. 1
93.5
-------
TABLE TX-fi. (cont'd 31.
PARAMETER
- .._.....;
Copper
Iron
Chloride
Ammon i a-N
Phosphorus-P
Oi l&Urease
METHOD
DETECTION
LIMIT
ug/L
5.0
1 .0
1 .0
1 .0
5.0
5.0
14
14
14
14
5.0
14
500
1000
1000
10
10
10
10
10
2000
2000
2000
2000
2000
too
2000
FACILITY
General Chemical
Rouge SLeel
Detroit WWTP
Wayne Co-Wyandotte WWTP
Ford Canada
West Windsor WPCP
Rouge Steel
Detroit WWTP
MeLouth Steel-Trenton
Wayne Co-Wyandotte WWTP
Kord Canada
GLS-80" Hill
General Chemical
Detroit WWTP
Rouge Steel
Detroit WWTP
Wayne Co-Wyandotte WWTP
Detroit WWTP
Wayne Co-Wyandotte WWTP
West Windsor WPCP
Detroit WWTP
Rouge Steel
MoLouth Steel-Trenton
GLS-80" Mill
GLS-Ecorse
West Windsor WPCP
Wayne Co-Wyandotte WWTP
FLOW
1 0J m-» /U
174
1B1O
21604 26951
268
71 .3
142
1810
2160( 2695 )
227
268
71 .3
223
18.9
2160
1810
21«0(i!695 J
2BS
2160( 2695 )
268
142
216012695)
1810
227
223
29.1
142
26H
AVERAGE
CIONC.
ug/L
99
8.3
3.3{3.3>
IB. 4
48
24
Totals
850
274(700)
2380
887
470
863
Total:
5.6%
130,000
20
Total:
9100(2458)
12,000
Total :
430(750)
910
1060
Total :
4200( 52081
7080
31 ,100
19,000
125,000
7900
2700
LOADING
k«/d
17.2
IS. 1
7.13(92.0)
4.95
3.44
3.43
51 .25
1550
592(1887)
545
239
222
215
3363
I ,050,000
281 ,000
36,400
1,3H7,400
19,700(6628)
3230
22,930
930(2023)
245
150
1325
9090114,042)
8090
7060
4260
3850
) 130
727
X TOTAL
POINT SOURCE
CONTRIBUTION*
31 ,4
27.6
13.0
y.o
6.2
6,2
93.4
43.4
16.6
15.3
6.7
6,2
6.0
94.2
73.3
19.3
2.5
95.1
79.0
13.0
92.0
63.3
16.7
10.2
90.2
25.7
22,9
19.9
12.0
10.3
3.2
2.1
ut
o
-------
TABLE IX-ti. (cont.'d 4K
PARAMBTEH
METHOD
DETECTION
LIMIT
FACILITY
FLOW
AVERAGE
CONO.
ug/L
LOADING
kg/d
X TOTAL
POINT SOURCE
CONTRIBUTION*
Cvanide
Total PAH
Chromium
5.0 Detroit WWTP
5.0 Rouge Steel
5.0 Wayne Co-Wyandotte WWTP
1.0 Ford Canada
1-15 Rouge Steel
1-2 Ford Canada
1-2 West Windsor WPCP
3.0
6.0
Detroit WWTP
Wickea Manufacturing
2160(2695 I
181(1
268
71.3
1810
71 .3
142
216012695)
2.6
49!22 J
3.32
21
20
Total
Total
106 (59J
6.12
5.6
2.28
120.0
5.90
7.1(30 )
3800-6700
Total :
1&,3 (80.8 )
13.8
29,1
87.6
5.1
4 .«
1.9
99.2
2.0
tj .0
2.0
5.15
0.44
0.311
85.0
7 .0
6.0
98.0
29.8
26.8
ft6.6
From Table 3-4 of the Point Source Workgroup Report <6J (
>95* of identified point source total unless multiple diffuse sources.
Values in parentheses are based on the City of Detroit 1987 Annual Self-Monitoring Report; see text
more inforrnation.
Does not include zinc loadings from Double Eagle Steel. Tf Double Eagle Steel average loading of 312
kg/day (from 4/86 to 2/87 se!f-monttori rig data) la included, Double Eagle Steel becomes the major
contributor at 33%, with Detroit WWTP's contribution falling to 23%. For the period July 1 to December
3), 1987, Double Eagle Steel discharged an average of 0.§8 kg/d total zinc.
-------
508
are placed in parentheses' to set them apart from the point source
survey data. in the text, these data are referred to as "SMR"
data.
Parameters which were "of concern", (by virtue of media guide-
lines being exceeded or by impacts upon biota)» and the point
sources which provided inputs, are discussed below.
i) Conventional Pollutants
i) Total Phosphorus: The total loading for the UGLCCS survey
was 1,470 kg/d, contributed primarily by the Detroit WWTP
(930 kg/d; self monitoring report for 1987 (SMR) indicates
loading of 2,023 kg/d), the Wayne County-Wyandotte WWTP (245
kg/d) and the West Windsor WWTP (150 kg/d). The Wayne
County-Trenton WWTP (1.6 mg/L) and the City of Trenton WWTP
(4.7 mg/L), discharged concentrations in excess of the GLWQA
effluent objective of 1.0 mg/L. Both the Detroit and Wayne
County-Wyandotte facilities are generally in compliance with
their permitted concentrations for total phosphorus.
ii) Ammonia-nitrogen: The total loading was 25,000 kg/d, con-
tributed primarily by the Detroit WWTP (19,700 kg/d;
SMR=6,628 kg/d) and the Wayne County-Wyandotte WWTP (3,230
kg/d; 12 mg/L). General Chemical (14.3 mg/L) discharged
ammonia in excess of the Ontario Industrial Discharge Objec-
tives of 10 mg/L. The Wayne County-Trenton WWTP effluent
concentration for ammonia-nitrogen was 15 mg/L.
iii) Chloride: The total point source loading was 1,440,000
kg/d, contributed primarily by General Chemical (1,050,000
kg/d). Concentrations in the General Chemical North Drain
ranged from 5.5 to 6.6% (55-66 gm/L). No effluent guide-
lines exist for chlorides; but these concentrations do grea-
tly exceed drinking water recommendations of 250 mg/L. The
Detroit WWTP and Rouge Steel discharged 281,000 kg/d and
36,400 kg/d of chloride, respectively, to the Detroit River.
ii) Organic Pollutants
i) Polychlorinated Biphenyls (PCB): The total loading was
0.296 kg/d, contributed primarily by the Detroit WWTP (0.2
kg/d; SMR=0.256 kg/d) and by Ford Canada (0.039 kg/d).
Elevated concentrations were found above the method detec-
tion limit (MDL, which was 0.0001 ug/L for Michigan and 0.1
ug/L for Ontario), at Ford Canada (0.55 ug/L) and the Wayne
County-Wyandotte WWTP (0.088 ug/L).
ii) Hexachlorobenzene (HCB): The total loading was 0,0024 kg/d,
contributed primarily by the Detroit WWTP (0.001 kg/d;
SMR=0.011 kg/d). HCB was not detected at Ontario sources at
their MDL of Q.02 ug/L. Pennwalt discharged the highest
-------
509
concentrations (0.012 ug/L).
iii) Qctachlorostyrene (OCS): The loading from the seven Michigan
sources surveyed was 0,000087 kg/d, and only detected at or
near the MDL (0.000001 ug/L), Wayne County-Wyandotte had
the highest concentration (0.21 ng/L) and loading (45 mg/d).
OCS was not found in Ontario effluents (MDL 0.02 ug/L).
iv) Polynuclear Aromatic Hydrocarbons (PAHs): The total loading
was 6.0 kg/d, contributed primarily by Rouge Steel (5,2
kg/day), at a concentration of 2 ug/L. Other point sources
contributed PAHs at loadings over an order of magnitude
less.
v) Total Phenols: The total loading was 135 kg/d, contributed
primarily by Ford Canada (48,2 kg/d; 658 ug/L), the Detroit
: WWTP (45.4 kg/d; 21 ug/L) and Rouge Steel (17.3 kg/d).
Concentrations for the Wayne County-Wyandotte WWTP, MeLouth
Steel-Trenton and Great Lakes Steel-Zug Island were 36 ug/L,
24 ug/L and 32 ug/L, respectively. The Ontario Industrial
Discharge Objective is 20 ug/L.
vi) Oil and Grease: The total loading was 35,400 kg/d, con-
tributed primarily by the Detroit WWTP (9,090 kg/d, 4.2
mg/L; SMR=14,G41 kg/d, 5.2 mg/L), Rouge Steel (8,090 kg/d, 7
mg/L) and McLouth Steel-Trenton (7,060 kg/d, 31.1 mg/L).
Great Lakes Steel-Ecorse (125 mg/L), Great Lakes Steel-80"
Mill (19 mg/L), and Mclouth Steel-Trenton (31 mg/L) dis-
charged elevated concentrations of oil and grease through
their combined outfalls.
iii} Metals
i) Total Cadmium: The total loading was 9.1 kg/d, contributed
primarily by the Wayne County-Wyandotte WWTP (6.1 kg/d, 23
ug/L) and the Detroit WWTP (1,4 kg/d, 0.65 ug/L; SMR=13
kg/d, 5 ug/L). Elevated concentrations were also discharged
from Ford Canada (11.2 ug/L) and General Chemical (10-21
ug/L). The Ontario Industrial Effluent Objective for total
cadmium is 1 ug/L.
ii) Total Copper: The total loading was 54.9 kg/d, contributed
primarily by General Chemical (17.2 kg/d, 99 ug/L), Rouge
Steel (15 kg/day, 8.3 ug/L) and the Detroit WWTP (7.1 kg/d,
3.3 ug/L; SMR=92 kg/d).
iii) Total Cyanide: The total loading was 121 kg/d, contributed
primarily by the Detroit WWTP (106 kg/day; SMR=59 kg/d).
This facility also discharged the highest concentration of
cyanide in effluent (49 ug/L; SMR=22 ug/L). Other facili-
ties contributed loadings over one order of magnitude less
than the Detroit WWTP.
-------
510
iv) Total Iron: The total loading was 3,570 kg/d, contributed
primarily by Rouge Steel (1,550 kg/d, 850 ug/L), the Detroit
(592 kg/d, 274 ug/L,- SMR=1,887 kg/d) and McLouth Steel-
Trenton (545 kg/d, 2,400 ug/L), Wayne County-Trenton WWTP
discharged concentrations of 6,960 ug/L.
v) Total Lead: The total loading was 52,1 kg/d, contributed
primarily by Ford Canada (30.3 kg/
-------
511
iii) Total Volatiles: The total loading was 220 kg/d, contrib-
uted primarily by the Wayne County-Wyandotte WWTP (94 kg/o%
348 ug/L), the Detroit WWTP (85.4 kg/d, 39.5 ug/L) and the
West Windsor (37.6 kg/d, ND-298 ug/L}.
Maj or Loading_ Contributors
Summarized below are eleven point source facilities which were
found to be major contributors of chemicals of concern in the
Detroit River, contributing 10% or more of the total identified
point source load. Primary contributors Indicate the parameters
for which the identified facility is the largest single source,
based on the UGLCCS point source data.
i) Michigan Facilities
Detroit WWTP
Primary contributors
Additional;
Total PCBs, HCB, total mercury, total
nickel, total chromium, total zinc,
ammonia-nitrogen, total phosphorus, oil
and grease, total cyanide, suspended
solids
OCS, total cobalt, total phenols, total
cadmium, total lead, total copper, total
iron, chlorides, total volatiles
Wayne County-Wyandotte WWTP
Primary contributor: OCS, total cadmium, total volatiles
Additional:
HCB, total mercury, ammonia-N, total
phosphorus -. \
McLouth Steel-Trenton
Primary contributor:
Additional:
None
HCB, total zinc, total iron, oil and
grease
Rouge Steel
Primary contributor;
Additional:
Total iron, PAHS
Total phenols, total lead, total zinc,
total copper, oil and grease, suspended
solids
Great Lakes Steel-Ecorse
Primary contributor: None
-------
512
Additional: OCS, oil and grease
Great Lakes Steel 80" Mill
Primary contributor: Hone
Additional; Oil and grease
Monsanto
Primary contributor: None
Additional; HCB
ii) Ontario Facilities
Ford Canada
Primary contributor: Total phenols, total lead
Additional: PCBs, total zinc
General Chemical
Primary contributor: Total copper, chlorides
Additional: Suspended solids
Wickes Manufacturing
Primary contributor: None
Additional: Total chromium
West Windsor WWTP
Primary contributor: None
Additional; Total phosphorus, total volatiles
Loading estimates are based on limited sampling, contain
inherent uncertainty, Comparisons based 'on these estimates con-
tain that uncertainty, as well.
A summary of parameters considered in the National Pollution
Discharge Elimination System (NPDES) permit effluent limits for
major Michigan Detroit River dischargers were presented in Tables
IX-4 and 5. For a more in-depth description of the permit lim-
itations Cor each facility, the Point Source Workgroup Report (6)
should be consulted. Also shown are the effluent requirements
for Ontario facilities. Ontario industrial facilities are also
encouraged to comply with the Ontario Industrial Effluent Objec-
tives, discussed in Chapter III. Most facilities have only a few
-------
513
constituents which they are required to measure. Most
constituents monitored are conventional pollutants, although some
monitor regularly for metals. Only a few have monitoring re-
quirements for organic contaminants.
An effort was made to determine if the facilities surveyed were
in compliance with the appropriate effluent requirements, by
comparing the effluent with such requirements, occurrences of
effluent limitation exceedences are noted for the appropriate
parameters in Tables IX-4 and 5.
2. Urban Nonpoint Sources
United States Storm and Combined Sewer Overflows
Stormwater reaches the Detroit River directly through storm
sewers and CSOs or through tributaries receiving storm and CSO
discharges. Contaminant loading from stormwater and CSOs dis-
charging directly to the Detroit River were measured or est-
imated. Contaminant loadings from storm water and CSOs to tribu-
taries are reflected by the contaminant loading of the tributar-
ies themselves.
There are 243 CSOs discharging to the Detroit River from Michigan
and Ontario. Seventy-six discharge directly to the river and 167
discharge indirectly via tributaries. There are 45 directly
discharging CSOs along the Michigan shoreline and 28 discharging
to the Rouge River (Figure IX-17), and a few others discharging
to small creeks, such as Conners and Fox creeks. The mean con-
centration and loading of selected chemical constituents from the
discharge of 42 City of Detroit CSOs to the Detroit River and
three City of Detroit CSOs to the Rouge River {downstream of the
tributary monitoring location) are shown in Tables IX-7 and 8,
respectively. Major loadings are from the Lieb (4,957 million
gal/yr) and Conners Creek/ Freud/Pairview (2,766 million gal/yr)
overflows located near Belle Isle along the western shore, and
the First Hamilton/ Bates/Woodward (386 million gal/yr) and Sum-
mit CSOs located approximately 1 km up and downstream, respect-
ively, of the Ambassador Bridge (79).
As an illustration, (79) , in the late 1970s Detroit CSOs
accounted for 13% of the total phosphorus, 15% of the suspended
solids, 21% of the oil and grease, 25% of the cadmium, 29% of the
chromium, 20% of the copper, 32% of the lead, 96% of the mercury
and 34% of the total PCB loading to the Detroit River. Subse-
quent more restrictive controls as well as industrialization
changes are believed to have reduced these contributions, how-
ever, this has not been documented.
There are no documented direct stormwater discharges to the
Detroit River from the municipalities of Detroit, River Rouge,
-------
514
» Outfall location
FARMINGTON
NORTHHELD
PLYMOUTH
CSICHOLS
IQHENCS
PURITAN
SNKiLL
LYNDON
CHOOLCHAfT
FIGURE IX-17, U.S. Combined sewer overflows discharging to the Detroit and
Rouge Rivers,
-------
TABLE IX-7
Mean contaminant concentrations measured in stormwater and combined sewer overflows in Windsor I1SBS-1986) and
Detroit )197SH.
WINDSOR*
Storm Water
Parameters
Ammonia
Tot a t Phosphorus
Chloride
Units
mg/L
ng/I.
mg/L
Residential
0
0
.28
. 24
-
Commercial
0.
0.
12
30
17
»J
Industrial
0
0
.43
.31
-
Combined
Sewer
Overflows
2
0
26
.5
.54
.0
DETROIT*
Combined
Sewer
Overflow*
3
44
.9
.0
240->
Susp. Solids
Arsen ic
Cadmi DDI
Chromium
Cobalt
Copper
I ron
Lead
Mercury
Nickel
Silver
Zinc
Oi I/Grease
Pheno 1 s
Cyanide
HCB
OOS
Total PCBs
PAHa (171
mg/L
mg/L
mg/L
og/L
mg/L
mg/L
mg/L
mg/L
ug/L
mg/L
mg/L
mg/L
mg/L
mg/L
mg/L
ng/L
ng/L
ng/L
ug/L
0
0
0
0
0
s
0
0
0
0
0
0
0
1
0
0
1
31
1
1
-
-
.00
.01
-
.00
.02
.01B
.8
. 1 3
.018
,oe
. 008
,021
-
.16
,25
.4
.0025
.003
.4
-
.a
.1
.6
-
-
0.
0,
0.
-
0.
0.
0.
0.
3.
0.
0.
0.
-
0.
2.
0.
0.
0.
0.
-
26.
2.
2.
001
ooa
008*
0014
017
0035*
03
0
184
03
026
23
3
004
003
0
4
8
1
6
O
0
0
0
0
B
0
0
0
u
0
0
1
5
0
0
0
0
109
4
5
-
-
.0008
.0086
-
.0004
.017
.048
.9
.21
.043
.05
.017
.028
-
.30
.7
.B
.008
.003
.2
.92
-
.0
.15
•7
ti
0
0
0
0
0
0
1
0
0
0
0
0
0
12
0
12
1
100
4
4
-
-
.001
.0072
.008*
-
.0006
.017
.003*
. 10
.2
.05
.043
.010
.044
-
.34
.60
. 3
.008
.003
.09
-
.0
.0
.4
205
0
U
0
0
2
0
45
0
0
0
94
0
2
.069
.041
.129
-
.218
.2?
.447
.0
.139
,038
.555
.0
.017
-
-
-
.4
-
1 From Maranleh and Ng (80).
^ From Giffles fit ai. t?9l.
3 Equivalent mean concentration.
* Mean of eoncentrationa detected in ail thr*e suhareas.
tn
-------
TAULK £X-8
Contaminant, loadings to the Detroit Rivar from stormwater and combined sewer overflow from th*
citiea of Detroit and Windsor Ikf/yrl,
WINDSOR1
DETROIT*
Parameter
Ammonia las HI
Total Phosphorus
Chloride
Cadmium
Stormwater
7,
5,
2,550,
200
600
000
e.5
133. a3
Cobalt
Chromium
Copper
I ron
Lead
Mercury
Nickel
Zinc
Oil and Grease
Total Phenols
Cyanide
HCB
OCS*
Total FCBs
PAHs 1 111
Susp, Solids
420(
127,
3,
4,
35,
59,
0,
0,
0.
6
78)3
-
613
600
539
0.6
1.1
285
624
600
700
700
75
67
021
026
045
0.5
1.1
49
63
-
Combined Total
Sewer Overflows
13,000
2 , 800
135,000
5.2
41. ti3
3
88116)3
-
520
6,200
260
830
0.2
52
228
1 ,770
2,600
64,000
42
16
0.006
0.010
0.5
21
23
-
20,200
8,400
2,685,000
11.7
175, 4a
9
508(94 >3
-
1,133
133,800
3,790
4,360
0.8
1.3
337
753
6,370
7,200
89, 700
123,700
117
83
0.027
0.032
G.QS5
1.0
1.6
70
86
-
Combined
Sewer Overflow!
11B,
1 ,545,
1,
4,
7,
79,
15,
1,
4,
19,
3,302,
84
7,201,
514
713
440
-
532
858
745
703
581
883
437
206
S8?
-
-
-
,31
_
609
111
t-1
Ch
1 From Marsalek and Ng 1801,
z From Giffles et al. 1781.
•* Calculated from data above detention limit,
* Baaed on Sarnia data ISt. Clair River areal.
-------
517
Ecorse, Lincoln Park, Grosse lie or Gibraltar. Stormwater from
these cities enters the combined sewer system and is treated at
the Detroit WWTP, or is discharged directly through CSO outfalls
to the Detroit River. The municipalities of Wyandotte and
Trenton have 13 and 18 direct Stormwater discharges to the
Detroit River, respectively. Riverview has 17 and Trenton has 19
Stormwater discharges through Monguagon Creek and Frank and Poet
Drains. The contaminant loadings from these outfalls are un-
known.
Ontario Storm and Combined Sewer Overflows
Mean concentration and loadings of selected chemical constituents
discharged in Stormwater and CSOs in Windsor are shown in Tables
IX-7 and 8 (80). Windsor has 28 CSOs which discharge directly to
the Detroit River, these are shown in Figure IX-18. Industrial
runoff and CSOs contained higher concentrations of most con-
stituents than commercial and residential land use areas. Some
constituents (ammonia and lead) were an order of magnitude lower
in residential than in other areas. Approximately 72 to 94% of
the Windsor loads occurred during storm events (about twice a
month and 20 to 42 hours per event). sixty-five percent of the
load occurred in February, March and April with the greatest
loads during March. Mixed stormwater/sanitary waste water dis-
charges to the river whenever flow in the combined sewers ex-
ceeded 2.5 times the dry weather flow, otherwise the mixed waste
water discharges to one of the two Windsor WWTPs. Based on these
data, Windsor CSOs contribute from less than 1 to 9% of the
conventional, metal, and organic contaminant loading to the
Detroit River.
3. Groundwater Contamination/Waste Sites
Groundwater movement was investigated in an area extending 19 km
(12 mi) along the Detroit River, which is about 50 km {31 mi)
long. Factors which control and influence groundwater movement,
such as geological formations, were investigated for this study
(53,70,71,81,82,83).
In Michigan, general groundwater flow is east towards the Detroit
River, Locally, the direction of groundwater flow is influenced
by surface water drainage, dewatering projects (such as in the
Sibley Quarry in Wayne County) and glacial landforms. Ground-
water discharges to the Detroit River from two hydrogeologic
units: a shallow glacial unit and a bedrock unit. The shallow
glacial unit consists of mostly silty-clay till and glacio-
lacustrine deposits with discontinuous stringers of sand and
gravel. In the upper river (down to about Fighting island), the
bedrock unit is comprised of carbonate rocks of the Traverse and
Dundee formations, overlain by at least 15 m of glacial deposits.
-------
Detroit, Michigan
ui
t-»
03
Legend:
o 8 45 - Michigan CSO s
* 30 » Canadian CSO s
FIGURE IX-18. Detroit and Windsor combined sewer overflows to the upper
Detroit River.
-------
519
South of Fighting Island, the bedrock is comprised of limestone,
dolomite and sandstone of the Detroit River Group, overlain by
about 8 m of fine-grained glacial deposits. Near the mouth of
the river, the Detroit River Group forms the river channel.
In Ontario, the groundwater flow is generally west towards the
Detroit River. Three levels of groundwater discharge exist:
local, intermediate and regional (or bedrock). The local unit is
contained in surficial sands and gravels, and the weathered and •
fractured zone of lake clay and clay tills. Similar to the
Michigan surficial unit, flow in this system is influenced
strongly by local surface events and conditions. The intermedi-
ate unit is comprised of intact lacustrine clay and clay till,
ranging from less than 3 meters to 40 meters in thickness. It is
believed most of the groundwater flow from this unit is downward
towards the bedrock unit. The bedrock unit is comprised primar-
ily of carbonate rocks of the Hamilton and Dundee Formations and
the Detroit River Group. Flow in this unit is towards the
Detroit River and Lake Erie.
The estimated total discharge of groundwater from the Michigan
side of the Detroit River study area (from Belle Isle to Point
Mouillee) is between 1.5 m3/sec (54 ftVsec) and 3 m^/sec (107
ftVsec)(82,83), Rates of groundwater seepage are highest in the
northern portion of the Detroit River, in the vicinity of Belle
Isle, and generally decrease downstream, increasing again below
the Ecorse River mouth. Groundwater and surface water systems
are highly interconnected in the Trenton Channel and the lower
Detroit River, due to thin or absent sediments overlying bedrock.
Estimates of groundwater seepage to the Detroit River from
Ontario were not made. In relation to the flow of the Detroit
River, the groundwater discharge to the river is approximately
0.05%; therefore, quantitatively, contributing a very small
amount to the total river flow.
Waste_Disposal Sites
An inventory of active and inactive waste sites within 19 km of
the Detroit River was conducted as part of this investigation.
Ninety four sites of known and potential groundwater contamina-
tion have been found in Monroe and Wayne counties as of January
1987. The majority of sites are solid waste landfills, hazardous
waste disposal sites, regulated storage sites and spills. Twenty
three sites along the Ontario side of the Detroit River were also
identified (84,85). Locations of selected Michigan waste sites
and monitoring wells are shown in Figure IX-19.
Sites which are located in groundwater discharge areas directly
discharging to the Detroit River were ranked and prioritized for
potential impacts upon the Detroit River. Ranking of sites was
based on their potential for contributing contaminants to the
-------
520
Government monitoring well
Private monitoring well
Waste Sit*
FIGURE IX-19. Sites of known or suspected groundwater contamination and
private wells located near the Detroit River,
-------
521
G1SI
72O
41
O
89 O
GS
Government monitoring well
Private monitoring well
(WA)5
O Wast* Site
42 O
WINDSOR
FIGURE IX-19. (Cont'd.) Sites of known or groundwater contamin-
ation and private well located near the Detroit River.
-------
522
Detroit River via groundwater. Sites were ranked by the United
States Geological Survey (USGS) using the U.S.EPA'S DRASTIC
system, with additions and minor modifications. The USGS ranking
system assesses the potential impact of a site by evaluating the
hydrogeology, nature of the waste material and the distance to
the Detroit River, Table IX-9 lists the 16 highest ranked sites
of the 94 sites considered in the Detroit River area. In, gener-
al, theae sites are in areas of sandy, unconsolidated surficial
materials, and are located adjacent to, or near, the Detroit
River. The water table at the highest ranked sites is generally
less than 4.5 m below land surface.
i) Michigan Waste Sites
Analysis of groundwater quality from eight wells (5 observation
and 3 private) within the Michigan Detroit River discharge area
was obtained. Of these eight wells, three were located down-
gradient of 3 of the 15 top ranked waste sites; Michigan Con-
solidated-Riverside Park (PI on Figure IX-19), Pennwalt Corpora-
tion (P2J and Petro-Chem Processing (G17). Unfiltered ground-
water i amples from these wells were found to contain concentra-
tions of organic and inorganic constituents suggesting ground-
water contamination, as shown below;
PI: Total volatiles 1,440 ug/L; total PAHs 287 ug/L; dissolved
barium 2,000 ug/L; total cadmium 40 ug/Lj total arsenic 58
ug/L,' total chromium 120 ug/L; total cobalt 160 ug/L,* total
copper 6iO ug/L; total lead 2,500 ug/L,' total mercury 55
ug/L. ~-
P2; Total volatiles 5.9 ug/L,* total 269 ug/L; total phthal-
ates 150 ug/L; total phenolics 95 ug/L; total copper 530
ug/L; total lead 800 ug/L; total nickel 1,500 ug/L,
G17; Total PAHs 58 ug/L; total phthalates; 364 ug/L; total copper
2,500 ug/L; total lead 4,700 ug/L; dissolved barium 2,400
ug/L,- dissolved beryllium 13 ug/L; total cobalt 50 ug/L;
total iron 570 ug/L; total mercury 2,2 ug/L,
Other wells located downgradlent of other lower-ranked waste
sites also showed some contamination, On-site monitoring wells
at each waste site generally revealed much higher concentrations
of metal and organic contaminants. These data are provided in
the Nonpoint Source Workgroup Report (86}, The contaminant con-
centrations of the analyses are based on unfiltered samples and
are not indicative of contaminant loadings to the Detroit River
from groundwater discharge. However, it is clear that ground-
water at of these locations contain high chemical concen-
trations. This suggests that important loadings of contaminants
to the Detroit River may be occurring through contaminated
groundwater discharge, A quantitative estimate of such input
cannot be determined with the present data.
-------
TABLE TX-i
Oonfirued or Possible Michigan Contamination Sites Within Detroit River Groundwater Discharge Areas*,
1. I&lAn
dichloropropane, 1,2-dichloroethane, phenol and benzene.
-------
TABLE IX-i, Jtont'd 21.
7, UMEa.H-.-¥ alley— St.ee I Oorponati^a I RCRA I
The Huron Valley Steel Corporation Bite is a RORA-perini tted facility that itores emission control dust/ sludge
I from the primary production of steel in electric fyrnaeessl in tanks. There are no monitoring wella,
a, gdMard_C._. Levy Co. Plant No. 3 ( RORA I
The Edward 0. Levy Co. Plant No. 3 site is a RGRA transporter and treatment /storage /disposal facility. This
plant stores and treats spent pickle liquor from steel finishing operations. There are 4 monitoring wells,
i, Edward C. Levy Co, Trenton Plant (RCRA)
The Edward C, Levy Co, Trenton Plant site is a RCRA transporter and treatnent/storage/disposai facility.
This plant stores and treats spent pickle liquor from steel finishing operations. There are 4 monitoring
we I la ,
1 0 . Mel. filith. Steel Products Corporation I RC R A )
The Edward C. Levy Trenton Plant is located on the property of MeLouth Steel Products Corporation. The
facility is located in a mainly heavy industrial area. There is a small strip of residential land within
1000 feet of the facility to the west. The Detroit River borders the facility on the east. Inspection of
tanks storing spent pickle liquor ( KQBSJ ) indicate that releases to the surrounding soils have occurred. The
company has not performed closure including cleanup of their releases. No known hydrogeologicai information
on the site exists.
1 1 . Diversey Corporation ( CERCLI S/RCRA )
The Diversey Corporation site is a generator and treatment, storage and/or disposal facility. There are no
monitoring wells.
The site received a high modified DRASTIC score due to a shallow water table, sandy aurficial material and
close proximity, within one-half mile of the Detroit River.
12.Pennwa.lt Corporation (CERCLIS/RCRA/Aet 30? J
The Pennwalt Corporation site is a RCRA generator and treatment, storage and/or disposal facility. The
Pennwalt property east of Jefferson Avenue consists of SOS fill which was placed along the Detroit River.
The nature of the material used for filling is not known. Oroundwater contamination is not indicated in the
Act 30? listing.
1 a. Monsanto Company < CERCLlS/HCRA I
The Monsanto Company site is a RCRA generator and a treatment, storage and/or disposal facility located on
the shore of the Trenton Channel of the Detroit River. One— half of the site property is composed of fill
which was placed in the river, A monitoring systen consisting of twenty wells have documented groundwater
contamination with arsenic.
Wonaanto has been on location since 1941. The 176 acre facility, which is bounded on the east, by the Detroit,
River produces, or has produced phosphate for industrial metal cleaning, food-grade inorganic chemicals and
plastic sheet for safety glass. Like virtually all industrial riverfront sites in the down-river area, land
facing the river has been considerably modified by fill, much of which came from industrial sources. Ground-
water here contains elevated levels of arsenic, as well as elevated pH , sodium, and sulphates, Groundwater
elevations are significantly affected by recharge from waatewater ponds. Oroundwater discharge is to the
Detroit River and Elizabeth Park Canal,
-------
TAfcLE IX-9. (cont'd 3>.
14.Jones Chemicals Inc. (RCRA>
The Jones Chemicals Trie, site is a RCRA transporter and treatment, storage and/Of disposal facility.
Corrosive wastes are treated, or stored in tanks. There are no monitoring wells.
I 5.PetyorShem Processing Inc. (RCRA»
The Petro-Chetn Processing site is a RCRA generator, transporter, and treatment, storage and/or disposal
facility. This company processes petroleum products, the primary product produced is Cbem-Rtiel #5. The site
is underlain by 6 to 10 ft of heterogeneous fill which overlies 1 to 5 ft of peat, and a thick layer of clay.
Groundwater chemical analysis revealed only trace levels of petroleum—related cheosicais despite nearly a
century of heavy industry in the area. There are no underground storage tanks and the above ground tanks are
diked. There are 6 monitoring wella. Petro-Chem has only been in operation since 198U, but previous site
owners have carried out fuel blending since 1976 (KOI Petroleum) and petroleum distribution activities for
many years prior to that (Amoco).
16.Chrysler Trent.&n_Elftflt (RCRA/Act 30? >
A MDNR site inspection discovered 3000 drums of solvents on site aa well as saturated, ignitable soils.
Wella are located on-site.
ui
K>
u\
1 From the addendum to the Nonpoint Source Workgroup Report (86),
CERCLIS: Site is listed within the information system for Superfund and is considered for clean-up under
the Comprehensive Environmental Response, Compensation and Liability Act of 1980 (CERCLA), aa
amended.
RCRA: Facility has a Resource Conservation and Recovery Act IHCRA) identification number.
ACT 307: Site is listed on Michigan's compilation of sites of known and possible environmental
degradat ion.
-------
526
ii) Ontario Waste Sites
One Ontario waste disposal site was determined to have potential
for impact on human health and safety. This site, used by Wickes
Manufacturing Ltd., is located near the Little River and had
elevated levels of chromium and iron in the groundwater. The
waste ponds were drained, in 1985 and the materials moved to a
certified disposal site in 1986. Subsequent tests indicate
limited remaining groundwater contamination. This site is pres-
ently under investigation. Little information on other Ontario
waste disposal sites in the Detroit River area was available.
iii) Island waste Sites
In addition to shoreline waste sites, two waste disposal sites
are located on islands in the Detroit River; Fighting Island
(Ontario) and Point Hennepin, Grosse lie (Michigan).
Fighting Island, the second largest island in the Detroit River,
has an area of approximately 3 km.2. Except for its northern tip,
the entire island was used by BASF tfyandotte Corporation (Worth
Works) to dispose of chemical process wastes. Samples from 51
test sites on Fighting Island were collected between 1982 and
1984, Groundwater and leachate samples contained high levels of
zinc, cadmium, phenols, phthalates, and other chemicals (87).
Compared to groundwater contaminant levels at Michigan waste
sites, the Fighting Island concentrations are low and the volume
of leachate is small, but all the leachate groundwater will
eventually reach the Detroit River.
Point Hennepin, on Grosse lie, has an area of approximately 1
km^. This site was an industrial waste lagoon/disposal site by
BASF Wyandotte {South Works). Little is known about the type and
quantity of wastes disposed here, but other waste sites operated
by this corporation (eg., site 5, Table IX-9) contain high con-
centrations of zinc, copper, lead, chromium, mercury, and several
organic compounds including tetrachlorobutadienes and trichloro-
ethylenes. Also, large sinkholes exist on this peninsula which
may provide a connection between the surface water and ground-
water aquifers, A surface leachate sample taken on the eastern
side of the peninsula in 1983 was highly toxic in the Microtox
toxicity bioassay (88). More detailed investigations of this
site appear warranted.
Underground Injection Wells
Pressurized injection of industrial liquid wastes has occurred in
the Detroit River watershed for many years at depths ranging from
200 m to over 1,200 m and injection pressures ranging from 580 to
1,600 psi (approximately 20 to 50 kBar), There are five classes
of injection wells regulated by U.S. law. Class I wells are
-------
52?
industrial and municipal wells which discharge below the lower-
most formation containing an underground source of drinking water
(USDW). Class II injection wells are associated with oil and gas
production and liquid hydrocarbon storage. Class III wells are
special process wells used in conjunction with solution mining of
minerals. Class IV wells, which were banned in 1985, are hazard-
ous waste wells which inject into or above a USDW, and Class V
injection wells are those not fitting into any of the above cate-
gories, such as cesspools and heat exchange wells.
On the Michigan side of the Detroit River, 234 Injection wells
have operated or are currently operating. Of the six Class I
wells, three are plugged and abandoned and three are currently
operating at the Detroit Coke facility. The facility disposed of
waste that contained chloride, ammonia, phenols, cyanide and
sulfide. Class II well records indicate a total of 12 wells
operating near the Detroit River, and consist of six salt water
disposal wells and six hydrocarbon storage wells. Two Class III
facilities (Pennwalt and BASF-Wyandotte) operated a total of 150
wells, of which only five are still active, and are scheduled to
be plugged and abandoned soon. Approximately 66 Class V wells
are presently operating in the Detroit River area. The impact of
these underground injection wells on the Detroit River and its
ecosystem is unknown, and warrants investigation.
It is beyond the scope of this investigation to determine the
environmental soundness of the injection well disposal method.
Historically, there is evidence for problems resulting from such
wastes. In general, there is little knowledge of the pathways
and fates of injected solutions.
4. Spills
An inventory of Michigan and Ontario spills occurring in or to
the Detroit River in 1986 is contained in Table IX-10. A variety
of chemical, oil and raw sewage spills occurred during 1986 (pre-
sumably indicative of present day spill events). Since insuf-
ficient information was available from spill reports on all spill
events, such as volume or constituents of spills, no contaminant
loading estimates were made. It is difficult to ascertain the
impact of spills to the Detroit River ecosystem relative to point
source inputs, but what is known suggests that contaminant load-
ing from spills may be important.
5. Rural Runoff and Tributary Input
Land use determines the type, quantity and quality of chemical
constituents present in tributaries which contribute approximate-
ly 117,900 million gal/year to the total Detroit River flow.
-------
TABLK IX-H)
Reported U.S. and Canadian spill incidents to the Detroit River (J98B11.
u.s. SPILLS
Constituent
Unknown
Metal finishing
wash solution
Raw sewage
Raw sewage
Raw sewage
Raw sewage
Raw sewage
Raw sewage
Raw sewage
Raw sewage
Raw sewage
Raw sewage
Ferrous chloride
Tri v«l ent chromi um—
containing water
cone : 3 ug/L
Xylene waahwater
Hydrochlori c ac i d
Ammonia and
Source
Pennwalt Corp.
GMC Truck & Bus
Detroit Boat Club
Beverly Hills
Water Department
Michigan Industrial
Mechanical Co.
Hubble So. Field
I nterceptor
Trenton WWTP
Detroit Boat Club
Trenton WWTP
City of Farmington
Wayne Co-Wyandotte WWTP
Wayne Co-Wyandotte WWTP
Pennwalt Corp.
Detroit Diesel
Ford Motor Co.
Pennwalt. Corp,
Pennwalt Corp.
Vo 1 ume
850 barrels
40,000 gal
5000 gal/min
unknown
68 gal
unknown
unknown
unknown
7200 gal/min
1000 gal
130x10* gal
140x10* gal
unknown
10,000 gal
500-750 gal
10 gal
10 gal
Rece i ving
«ater
Detroit River
Upper Rouge
Detroit River
Houge River
Rouge River
Rouge River
Detroit River
Detroit River
Rouge River
Rouge River
Detroit River
Detroit River
Detroit River
Rouge River
Rouge River
Detroit River
Detroit River
Amount Recovered
unknown
30,000 gal
none
none
none
non«
non*
none
none
none
none
none
none
none
none
none
8 gal
cn
N
CD
mono-ethvIene
-------
TABLE 1X-1U. (cont'dj.
Constituent
Qi 1*
OH
Oil
Oi 1
Oil
Oil
CANADIAN SPIU.S
Oil
Oil
Chromic acid and
nickeI saIta
Source
Volume
Unknown 100 gal
Trailer Park 300 gal
Mctouth Steel unknown
Unknown unknown
Orosse Tie Airport. 2-3 gnl
Consolidated Freight 230 gal
Ford Engine Plant unknown
Allied Chemical I5~«!ft gal
Kieneral Chemical)
VJickea Manufacturing unknown
Receiving
Nater
Rouge River
Detroit River
Detroit River
Trenton Channel
Trenton Channel
Rouge River
Detroit River
Detroit River
Little River*
Amount Recovered
unknown
none
none
1 From the Point Source Workgroup Report tfi).
2 "Oil" refers to non-PCB-containing oil-
* per R. Bowen, OMOE (Point Source Workgroup Report" reports «s occurring to Detroit River>.
ui
to
-------
530
Land use in the Detroit River area is almost equally divided
between urban/residential/industrial and agriculture (5,86,89).
Forty six percent of the approximately 200,000 hectare watershed
is intensively farmed, primarily for corn and soy beans. Beef
and swine are the dominant livestock, but dairy cattle are also
raised. Fertilizer and manure have the potential to be a major
nitrogen and phosphorus source to the Detroit River since ap-
proximately 17,100 tons per year (11,355 in Ontario and 5,755 in
Michigan} are applied within the Detroit River watershed. This
could be substantially reduced, since phosphorus and fertilizer
application rates are generally more than twice the required
amount in these areas, and only 8% of the Michigan and 10 to 20%
of the Ontario Detroit River watershed farms use recommended
agricultural soil and water conservation practices (5,86).
Michigan applies about 37,000 kg and Ontario applies about 53,000
kg of pesticides annually, including atrazine, alachlor, cyan-
azine and metolachlor. Reports indicate that 60% of the Detroit
River watershed has a high potential for pesticide transport to
the surface and groundwater systems. Instantaneous pesticide
loadings were calculated for all Ontario tributaries for total
atrazine, lindane, and p'p-DDE. Loadings were estimated at 33
ug/sec, 13.4 ug/sec and 4.4 ug/sec, respectively (34),
Tributary contaminant loadings were determined for the Ecorse and
Rouge rivers in Michigan, and Turkey Creek and Little and Canard
rivers in Ontario. Selected chemical constituents were measured
every 12 hours for two 1 week periods during 1986. Concentra-
tions multiplied by tributary flow determined chemical mass load-
ings to the Detroit River. Calculated contaminant loadings for
these tributaries are shown in Table IX-11 (5,30). Tributary
loadings generally account for only a minor portion of that con-
tributed by point sources. However, for some parameters, tribu-
tary loadings (when expressed as kg/d), approach some point
source loadings.
6. Atmospheric Deposition
No data were obtained for direct atmospheric deposition of con-
taminants to the Detroit River by this study. Contaminant load-
ings from indirect atmospheric deposition to the watershed are
reflected in tributary contributions. Air concentrations of
selected constituents for Wayne County are shown in Table IX-12,
and sampling locations are shown in Figure IX-20. The highest
concentrations of these constituents are near Zug Island, Areas
located 2 to 3 km north of Zug Island generally had the lowest
concentrations. Total suspended particulates exceeded the pri-
mary annual geometric mean of 75 ug/m3 at station 5 just north of
Zug Island during the 1980 to 1986 period. Cadmium and chromium
also exceeded the primary annual geometric mean at all three
stations monitored.
-------
TABLE IX-11
Comparison of U.S. artd Canadian Detroit River tributary contaminant loadings, 1984-1986 (kg/yr),
CANADIAN TRIBUTARIES
Tributaries Sampled
LittJe,
Little and
U.S.
Rouge
Canard and Turkey
Year Sampled
Number of Samples
X of Drainage Basin
Reported by r
Chemical Const i tuents
Total Phosphorite
Nitrate-N
Chloride
Suspended Solids
Total Lead
Total Cadmium
Total Copper
Total Iron
Total Mercury
Total Nickel
Total Zinc
Total PCBs
1 From Wall et al. (
* From Detroit River
3 Michigan DNR data
* Th i a vnlii«» Httoliesi
Turkey
1984 * 1
7-31
20X
Wall et
103,689
628,404
7,334,728
-
836
-
-
-
-
-
-
«•
5 I.
System Mass Balance
from high flow event
t.ft Tur-kp-v nr«»**k on 1
985 1986
2-28
4X
fll . * Richardson2
15,547
-
3,579,338
1 , 103,445
-
3.4
178
1,313
O.i
17 ,941
1,947
0.36*
Study {30).
monitoring, 1984-1986
v .
TRIBUTARIES
Rouge and
K'corae
1984-1986 1906
3B-167
54X
MDNR*
151 ,718
720,267
7(j,771 ,600
28,944,500
9,624
740
9,587
-
-
7,373
53,582
~
( unpubl i ah*d 5 »
2-28
77X
Richardson^
109,903
-
76,564,047
30,231,356
-
2, 151
7 ,4»fi
41 ,394
18.2
3,541
174,896
55. 1
-------
TABLE IX- 1 2
Mean concentrations of selected chemical constituents in air of Wayne County, Michigan, within four miles of
the Detroit Kiver,
CONSTITUENT
Benzol a )pyrene ng/tn3
Beryllium ug/m-*
Cadmium \i%/m3
Carbon Monoxide ug/ma
Chromium ug/m1
Iron ug/m3
Lead ug/mj
Mercury ug/m-*
Nickel Mg/jnJ
Nitrogen Dioxide ug/m-1
Ozone ppm
Sulfur Dioxide ug/m3
Total Susp. Particles ug/m3
Zinc ug/m3
STATION NUMBER
2 60/81 4
1.27 - 1.
0.
0.
1 .
- - 0.
«.«.(}
0.
- - 0.
__ — A
65 51
0.
16 34
6? 66
_ _ f)
5 9 8 10 34
50 3.48 - I. 10
0004 0.0003 - 0.0007
027 0.058 - 0.0038
IB - - 1.00
007 0.012 - 0.009
89 1.53 - 1.21
24 0.27 - - - 0.14
0003 0.0003 - 0.0004
015 0.013 - 0.010
_
022 - - 0.019
39 24 18
89 B8 59 52
24 0.33 - 0.37
Ul
UJ
From Michigan DNR, Wayne County yearly air quality data.
-------
533
HARPfR WOODS
GRQSSE POINT WOODS
GROSSE POINT
SHORES
GRQSSE POINT FARMS
gROSSE POINT
\GflQSS£ POINT PARK
WINDSOR, CANADA
Air Quality Monitoring Station
FIGURE IX-20. Wayne County air quality monitoring network.
-------
534
7. Integrated Contaminant Input
The total measured loadings of UGLCCS parameters from all point
source facilities were added to the combined measured loadings of
stormwater, combined sewer overflows and tributary loadings to
determine the total measured loading of each UGLCCS parameter
discharged to the Detroit River. These loadings and their re-
spective percentages by various categories are shown in Tables
IX-13 and 14.
Michigan's point sources contribute 49% or more of the measured
ammonia, total phosphorus, oil and grease, cadmium, chromium,
cobalt, iron, nickel, zinc, cyanide, total phenols, HCB, PCBs and
PAHs. Ontario point sources contributed 64% of the measured
chlorides. Michigan CSOs contributed a substantial proportion of
total phosphorus, suspended solids, oil and grease, cadmium,
chromium, copper, lead and mercury loadings as of 1979. There
are no data on contaminant loadings from Michigan CSOs more
recent than 1979.
An attempt was made to determine' changes in concentrations of
UGLCCS parameters between the Detroit River head and mouth during
the Detroit River System Mass Balance Survey, described in a
later section. Most parameters measured had higher concentra-
tions at the mouth than the head, indicating input of these
materials along the river. Measured point sources, tributaries
and CSO loadings accounted for 50% or more of these increases
(30). These data suggest that other sources, possibly including
atmospheric deposition, direct shoreline runoff, groundwater
discharge, spills and sediments may be contributing to increases
in these chemical constituents between Lake St. Clair and Lake
Erie. Uncertainty in the measurements resulting from limited
sampling may also play a part. These data also suggest that the
Detroit River corridor is a source for waterborne phosphorus,
copper, zinc, suspended solids, chloride and PCB, but is a sink
for waterborne mercury, nickel, iron and cadmium. These latter
metals may be adsorbing or chemically bonding to particulate
matter which settles in Detroit River depositional zones. Some
portion of these substances probably settle out, but during this
study their export exceeded the measured .input.
-------
TABLE IX-13
Total loadings of selected chemical constituents of the Uetroit River tran
sources measured between 1979 ttnd 1386 (kg/yrl.
Michigan and Ontario point and nonpoint
PARAMETER
TOTAL
MEASURED
LOADING
MEASURED
MICH IGAM
POINT
SO11RCK
LOADINGS1
MEASURED
ONTARIO
POINT
SOURCE
LOADINGS2
MEASURED
DETROIT
QSO
LOADINGS*
MEASURED
WINDSOR
STORMWATER
& cso
LOADINGS*
MEASURED
MICHIGAN
TRIBUTARY
LOADINGS
MEASURED
ONTARIO
TRIBUTARY
LOADINGS
Ammonia
Phosphorus
Chloride
Susp. So I ids
OiI/Grease
Cad01 i urn
Cobalt
Oh rom inn
Copper
Iron
Lead
Mercury
Nickel
Zinc
Total Phenols
Cyanide
HCB
Total PCBs
17 PAHa
11 ,692,656
915,821
623,207,041
57,607,849
15,719,506
5 ,681
IT
15,774
38,554
1,560,852
49,490
1 ,642
74,005
316,006*
50,061
44,361
0.9
249
2,281
»,
134,
19,
12 ,
1,
088
452
320
199
227
2
1
1 I
10
182
a
36
172
32
43
1
,500
,600
,000
,000
, 500
, 9fl6
, 737
,242
. 548
,600
,067
39.4
,865
,280
,047
,435
0.9
94
,891
617,
82,
398,000,
66,
9,
122,
10,
6,
61 ,
17,
000
900
000
-
80O
337
8
-
450
000
900
2
190
500
300
843
-
14
304
618
166
1,545
8,360
3,302
1
4
7
79
15
1
4
19
,285
,514
,713
,i>04
,206
,440
-
,532
,658
,745
,703
,581
,B83
,497
&97
-
-
84 .3
_;.
20,200
a,400
6,235,000
123,000
176
9
1 ,133
133,800
4 ,360
1
753
7,200
117
83
0.03
1.6
86
720,267*
151,718s
76,771,600s
30,231,356*
740*
8,587s
41,394*
9,6245
18. 2»
7,373s
53,582s
55.1s
628,404*
103.8B9*
7,334,728*
1, 103,445"
3.4'
178'
1.3137
8361
0.6'
17,941'
1,947'
0.3610
I
1
a
4
s
•
i
8
II
1 0
Baaed
Baaed
Based
Based
Based
Based
Based
Based
Does
Based
on
on
on
on
on
on
on
on
not
on
UGLCCS 1986 Point Source Survey J6>.
UGLCCS 1985 Point Source Survey (ft).
City of Detroit CSOs (1979), from Giffles et aj. (79(.
Windsor storrawater and CSOs 1985-1986, Marsalek and Ng (80).
Rouge River loadings, 1984-1986, Michigan DNR, unpublished, data, 1988.
loadings from the- Little and Canard rivers and Turkey Creek, 1984-138S.
loadings from the Little River and Turkey Creek, I98<> (301.
loadings from the Rouge and Er.orse rivers, 19H6 (30),
include loadings from Double Engie Steel.
loadings from Turkey Creek only, 1985. Wall et al. { 5 !.
Well et ai. ( 5).
-------
TABLE IX-14
Kstimntpd flfiniial contaminant loadings to the Detroit fiiver based on measured point and nonpoint sources between 1979 and
198fi, find the percent, of" This total loading contributed by the sources compared with pleasured increased loadings between the
head »nd the mouth of the Detroit River,
Parameter Total Michigan Ontario Detroit Windsor Hichigan Ontario
Measured Point Point CSOs* Storm- Tribu- Tribu-
l.oading Source1 Source* \ water & taries taries
kg/yr X X CSOs-t % %
X
Ammonia 11.692,656 77.7 5,3 5.3 0.2 6.2* 5.4?
Phosphorus 915,821 49.4 9,1 12.1 1.0 IB. 6* 11.3'
Chloride 623,207,041 21.6 63.9 0.2 O.B 12.3* 1.2'
Susp. Solids 57,fi07,849 33.9 NM 14.5 NN 5O.2 1.9s
Oilifireaae 15, 719, SOS 77. U 0,4 21,0 O.B NM NM
Cadmium 5.6H1 52.6 5.9 25.3 3.1 13,0* 0.1s
Cobalt 17 99.0 0.5 NH 0,5 NM NM
Chromiu* 15,774 71.3 NM 28. 7 KM NM NM
Copper 38,554 27.4 24.5 19.9 2,9 24.9* 0.5*
Iron 1,560, HS2 75. a 7,8 5.1 B.B 2 . 7» 0.1*
Lend 49,490 16.3 22. Q 3t.7 6.8 18,4* 1,7"
Mercury 1,642 2.4 0.1 96.3 0,1 1.1* 0.1"
Nickel 74,005 49.6 8.4 6.6 1.0 10,0* 24.3*
Zinc 316,006** 54.5 19.5 6,2 2.3 17.0* 0,6»
Tot.il Phenols 50,061 ti4.0 34.6 1.2 0.2 NM NM
Cyanide 44,361 97.9 1,9 NM 0,2 NM NM
HCB 0.9 96.7 NM 3.3 NM N« NM
Total PCBs 249 37. ft 5,6 33.9 0.6 22,1* O.H«
17 PAHs 2,281 82,9 13,3 NM 3.B NH NM
Changes Between
Head 4 Mouth
kg/yr
+ 1,460,656
+ 729,625,072»«
+ 527,6«O,352
t 2.5B6
+ 73,006
1 99 , 7 1 7
+ 45.4
+ 37,149
* 429,835**
+ 364
NM Not Measured
1 Based on 1966 Point Source Surveys (6).
1 Based on 1985 Point Source Surveys (6).
J Baaed on City of Setroit CSOs, 1979 and Oifflcs et aj. (791.
* Based on Windsor Stormwater and CSOs in 19S5-l9rt6. Nnrsatek and Ng 180*.
s Rawed on U . S . EPA ' a System Mass Balance ( 30 > . Measured loading changes between thft Detroit Rt
ambient monitoring. (+1 equals mouth loading greater than the head value shown; (-) equals •
vu 1 ue shown .
* Bas«d on loadings from the Rouge River, 1984-198K. MDtJR unpublished data, 19B8.
' BuKed on loadings from the Li tt. 1 e ftiver. Canard River and Turkey Creekj 19H4 and 1 985 1 S |.
* Based on loadings from the Little River and Turke-y Creek, ) 984 and 1 985 ( 5 3.
' Based on lonfiings From the Rouye River and Ecorse River, 1 UXti j 3O ( ,
1 * Includes the discharge from Oeneral Chemical (390,550,00(1 kg/yri discharging below the Octroi
lower t. ransept.
11 Does not include loadings from double Fagle Steel.
12 Tricluiies loading from Double Raijle Steel.
1J JPh i s is uncertain due to footnotes 11 *md 12.
11 Based on loadings from Turkey Creek only, 19B& 1 5 J.
Percent Change
Accounted for
by Heasured
Point £ Non-
Point Sources
63
85
1 1
220
53
3,617
200
741*
68
Source
or
Sink
Source
Source
Source
Sink
Source
Sink
Sink Ul
Source** CtS
— m
Source
ver head and BOuth frois
outh loadings less than
t River System HSSK Balance
-------
537
D. DATA QUALITY ASSURANCE AND CONTROL
1. Limitations
A total of 13 interlaboratory performance evaluation studies were
conducted for the UGLCC Project, All laboratories supplying
analytical data participated in at least one of these round-robin
studies. The parameters tested in the interlaboratory studies
were: PCBs, PAHs, organochlorine pesticides, chlorinated hydro-
carbons, total phenol, chlorophenols, trace metals, major ions,
nutrients, and cyanide (see Chapter IV).
2. General Observations
The Michigan Department of Natural Resources laboratory results
for the UGLCC studies were compared with similar effluent and
surface water samples collected in years in other river systems.
Point sources were evaluated based on field blanks replicates,
reagent blanks, duplicates, sample spikes, annual laboratory
precision and accuracy summaries and UGLCCS interlaboratory com-
parisons (round robin). Field blanks contained only a few con-
stituents and did not impact loadings estimates. Field repli-
cates, describing the relative system variation, varied by less
than 20% for all parameters with three or more field replicates.
Accuracy, described as the percent recovery, was 80 to 100% for
most organic compounds, and 70 to 130% for most conventional
compounds. Precision control (duplicate analyses) showed recov-
eries of 98 to 100% with a mean of 99%.
The U.S.EPA Large Lakes Research Station Laboratory, also did
quality control analysis for PCBs and metals. For PCBs, average
blank concentrations were substantially less than the concentra-
tions observed in the samples. The duplicate analyses were
within 17%. Additionally, the analyses of the 111 prepared labo-
ratory standards were within 20% of the known concentration.
Based on this summary, the PCS data are considered adequate. For
metals, blanks were all less than the river or point source
samples. Duplicate analyses were within 16%. Replicate analyses
were within 27%. Reference standards were within 16% of known
concentration except for chrome which was within 30%. Based on
this information, the point source workgroup concluded the data
were adequate and within the confines of the quality control-
quality assurance management plan for the UGLCCS.
-------
538
E. MODELING AND MASS BALANCE CONSIDERATIONS
Mass balance and process oriented models were developed for the
Detroit River. These are identified in Chapter ¥ along with an
explanation of mass balance and process modeling.
1. Mass Balance Models
Mass balance models permit the evaluation of whole rivers or
river segments as a source or sink of measured contaminants.
Mass balance studies were conducted for the entire Detroit River
system and a section of the lower Detroit River, the Trenton
Channel. These studies represent snapshots of contaminant con-
ditions. Figure IX-21 shows the relative importance of loads in
the Detroit Systems Mass Balance (DRSMB) including Michigan and
Ontario tributaries and the Detroit WWTP (90) . Figure IX-22
shows the same relationship for the Trenton Channel Mass Balance
(TCMB) but also includes some tributaries and point sources. The
arrow shaft width indicates the importance of the average con-
taminant load or loss. Estimates marked with a ^?' denote data
unavailability. At the bottom is a mass balance interpretation
with statistical conclusions. Diagrams for each contaminant
during the DRSMB periods and diagrams for each contaminant during
the TCMB periods can be compared directly. Missing data for the
Detroit River System Mass Balance include loadings from the
Canard River, all direct point sources except the City of Detroit
WWTP, nonpoint sources including CSOs, storm water, atmospheric
deposition, groundwater, sediment fluxes, and contaminants as-
sociated with floating aquatic macrophytes. Missing data for the
Trenton Channel Mass Balance include all of the above except
direct point source discharges within the Trenton Channel.
Errors in these calculations may be due to 1) insufficient temp-
oral or spatial sampling, or 2) analytical analysis. Concentra-
tions less than the analytical detection level are particularly
difficult to incorporate into modeling efforts. In the Detroit
River Systems Mass Balance (30) and Trenton Channel Mass Balance
(31), these errors were minimized by using only data generated by
the U.S.EPA Large Lakes Research Station (LLRS) for the Detroit
River, the tributaries and point sources, and city of Detroit
WWTP daily monitoring data for the precise days of each survey.
The method of managing values at less than detection is called
the maximum likelihood method of singly censored data and has
been applied to all U.S.EPA-LLRS results.
-------
539
SMB 1 - SUSPENDED SOLIDS (mt/d>
Upstream input
4847
US.
Rouge R.
WWTP £L
Ecorse R.
1.4,
Detroit
River
-^- Turkey C.
apparent
surplus=i297
(21%)
6292
Downstream output
Area is a statistically significant source
(1445 MT/d) of suspended solids.
2 - SUSPENDED SOLIDS (mt/d)
Upstream input
46
SIS.
Rouge R. 32,0.
WWTP 27.7
Ecorse fl. "
Detroit
River
CAMADA
- Little R.
0.5
Turkey C.
apparent
surplus=1i71
(30%)
6673
Downstream output
Area is a statistically significant source
(2033 MT/D) of suspended solids.
SMB1 ZINC. TOTAL fKg/d>
Upstream input
689
US.
Rouge R.
WWTP
Ecorse R.
478
1,6
Detroit
River
CANADA
. Little R.
Turk«y C,
apparent
surplus=347
(19%)
1840
Downstream output
Area is a statistically significant source
(1151 Kg/d)otzinc.
SMB2 ZINC. TOTAL (Ke/d)
Upstream input
644
Rouge R.
WWTP
Ecorse R.
70.:
7
Detroit
River
CANADA
1,4
Little R,
Turkey C,
apparent
surplus=300
(30%}
1016
Downstream output
Area is a statistically significant source
(372 Kg/d) of zinc.
FIGURE IX-21. Detroit River mass balance resula.
-------
540
gMBl NICKEL. TOTAL
Upstream input
548
SIS.
Rouge R.
CANADA
Little R.
Turkey C.
apparent
'dcHcIt = 137
(-21%)
644
Downstream output
Area is a statistically significant source of
nickel (96 Kg/d} although accumulation may
be occuring.
SMB2 NICKEL. TOTAL (Kg/dl
Upstream input
502
US.
Rouge R.
WWTP
Ecorse R.
~0
Detroit
River
CANADA
2.1
Little R,
0,2
Turkey C.
apparent
surplus=23S.2
(32%)
747
Downstream output
Area is a statistically significant source
(245 Kg/d) of nickel.
SMB1 PCP, TOTAL
Upstream input
0.77
Rouge R.
WWTP
Ecorse R.
CANADA
Little R.
Turkey C.
apparent
deficits.29
(-18%)
1.63
Downstream output
Area is a statistically significant source of
PCS (.86 Kg/d) although accumulation
may be occuring.
§]VIB2PCB. TOTAL
Upstream input
.85
US.
Rouga R.
WWTP
•corse R.
,08
Detroit
River
CAHAPA,
- Little H.
- Tyrkey C.
epparent
-surplus=.61
(30%)
2.09
Downstream output
Area is a statistically significant source
{1.24 Kg/d) of PCS,
FIGURE IX-21. (Cont'd.) Detroit River mass balance results.
-------
541
LEAD. TOTAL
pstream input
79.7
US.
Rouge R.
WWTP
Ecorse R.
i- Turkey C,
apparent
deficit = 173,6
(-185%)
93,9
Downstream output
Area is a of
(14,2 Kg/d) accumulation
may be oeeuring.
SMB2 LEAD. TOTAL
Upstream input
58.0
WWTP
teorsa R, 0,1
CANADA
- Little B.
Turkey C,
apparert
•diffcit=220.7
l-23S%|
92,6
Downstream output
Area is a statistically significant source
(34,6 Kg/d) of accumulation
may be occuring.
MERCURY. TOTAL
Upstream input
4,7
'as.
Rouge R.
WWTP
Eeorsa R. — • • »
-o
m
Detroit
River
CANADA
Llltle R.
Turkey C.
apparant
d*flcit=O.S
(-10%)
4.8
Downstream output
Area is not a significant source
of mercury; accumulation may be occuring.
§MPi MERCURY.TOTAL
Upstream input
7.1
III,
Turkey C,
apparent
iurpluszt.1
(13%)
8.7
Downstream output
Area is a significant source
{1.6 Kg/d) of mercury,
FIGURE IX-21. (Cont'd.) Detroit River balance results.
-------
542
TOPPER. TOTAL (Kg/
Upstream input
472
US.
Rouge R,
9.1
52,2
WWTP
Ecorse R. -~.V.
Detroit
River
~0
~0
Ulile R,
Turkey C.
apparent
surpjus=130
(20%)
663
Downstream output
Area is a statistically significant source
(191 Kg/d) of copper
OS.
Rouge R.
WWTP
Ecorse R.
SMB1 HCB (KeAft
Upstream input
.11
SMB1 HfB
Detroit
River
untie R.
Turkey C.
apparent
surplus=.009
(7.5%)
.12
Downstream output
Area is a not a statistically significant
source of HCB.
Upstream input
0.26
Rouge R.
WWTP
Ecorsa R.
~0
-0
1
Detroit
River
Llttto R.
Turkey C.
0.26
Downstream output
Area is a not a statistically significant
source of HCB.
FIGURE IX-21. (Cont'd.) Detroit River mass balance results.
-------
543
CADMIUM. TOTAL
Upstream input
11.1
US.
5.9
Rouge R.
WWTP
fieorm R.
CANADA
Little R.
• Turkey C.
apparent
12.S
(•69%)
21.7
Downstream output
Area is a lignifieant of
cadmium (10.6 Kg/d),
may ba occuring.
SMB2 CADMIUM. TOTAL fKg/d)
Upstream input
8.9
112.
WWTP
CAMRD&
LIHI* R.
Turkey C.
apparent
'deficit s S.3
(-58%)
14.3
Downstream output
Area is a significant of
cadmium (5,4 although accumulation
may be occuring.
§PB1 CHLORIDE. FILTERED
Upstream input
3784
ES.
Rouge R.
WWTP
Seers* R,
201
8.4
Detroit
River
CANADA,
6.§. mil* H.
-LiZ Turkey C.
if>par«rrt
"surj»lus=712
(15%)
4713
Downstream output
Area is a statistically significant of
chloride (929 MT/d).
SMB2 CHLORIDE. FILTERED (mM)
Upstream input
3872
Rouge R,
WWTP
lews* R.
71
-0
Detroit
River
CANADA
Little R.
Turkey C.
apparent
'surplus s 748
4695
Downstream output
Area is a source
(823 of chloride.
FIGURE IX-21. (Cont'd.) Detroit River balance results.
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544
SMB1 PHOSPHORUS. TOTAL fmt/di
Upstream input
4.9
US.
Rouge R.
WWTP
Ecorse R. ~0
Detroit
River
CANADA
.03
Little R.
Turkey C,
apparent
..— surplus -1.4
(16%)
8,9
Downstream output
Area is a statistically significant source
(4 MT/d) of total phosphorus.
S|VtB2 PHOSPHORUS. TOTAL
Upstream input
4.4
Rouge R, Q.2
,1.3.
WWTP
EcorsB R.
Detroit
River
CANADA
Little R.
Tyrkey C,
apparent
surplusafl.6
<§%)
6.5
Downstream output
Area is a statistically significant source
(2.1 MT/d) of total phosphorus.
SMB1 SILICA JILTERED_frnt/dl
Upstream input
565
Rouge R.
WWTP
Ecorse R.
6.6
.37,
Detroit
River
CANADA
.35
.13
Littlo R.
Turkey C.
apparent
deHcUs-43.5
(-8.%)
530
Downstream output
Area is a statistically significant sink
(35 MT/d) of silica.
SMBj_§j[LICA. FILTERED fmt/d^
Upstream input
672
05.
Rouge R.
WWTP
f cors*
3.0
~0
Detroit
River
..04
CANADA
Little R.
Turkey C,
apparent
surp(us=21
(3.0%)
696
Downstream output
Area is a statistically significant source
(24 MT/d) of silica.
FIGURE IX-21, (Cont'd.) Detroit River mass balance results.
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545
THENTQN CHANNEL 3UR¥gY II
Suspended Solids (MT/d)
TRENTON CHAKMEL SURVEY III
Suspended Solids (MT/d)
Upstream
input
11
Point
sources
Downstream
output
832
918
892
apparent
C surptys=75
CB%)
D
-apparent
deficit«3 I
downstream - upstream = 60 HT/d
Entire is not a statistically significant
source of TSS.
Up 31 r earn
input
Point
sources
Downst ream
output
1660
apparent
C surplus=196
(108)
apparent
defiat=78
1798
downstream - upstream *!38 MF/d
Entire area is not a statistically significant
source of TSS.
TliBlTTQIf CHAMHEL
II
Zinc, Total (Kg/d)
634,3
Upstream
input
134.6
Point
5 5
Downstream
output
986.6
apparent
C surpius=2Q8.7
D
apparent
def»cit=255.2
738
downstream - ypstream =94,7 Kg/d
Entire area is not a statistically significant
source of zinc although the C-A area is a
significant source and the D-C area is a
sign if leant sink.
TRENTON CHAMNEL SURVEY III
Zinc, Total (Kg/d)
1073
Upstream
input
Point
sources
apparent
C surplus-1 4f .6
(10%)
Downstream
output
1024
downstream - upstream = 49
apparent
deficit=330.7
Entire area is not a statistically significant
source of zinc although the C-A area is
a signifcant source.
FIGURE IX-22. Trenton Channel mass balance results.
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546
THEHTOM CHANNEL SUHYEY II
Lead, Total (Kg/d)
Upstream
input
Point
sources
Downstream
output
59.5
apparent
C 3urpl«s=8.8
CI2X)
apparent
deffcit-13.4
60.5
dawnstriam - upslrtam =1 A Kg/d
is not a
soured of although the C-A is a
significant source,
TRENTOM CHANNEL SUHTHY III
Lead, Total (Kg/d)
Upstream
input
Point
sources
Downstream
output
170
apparent
C surplus-29,3
U4X)
apparent
deficits 75.3
downstream - ypslream • 36 Kg/d
Is not a significant
source of the C-A is
a significant source.
TM1TTON CHANMEL JUOTET II
Mercury, Total (Kg/d)
Upstreaa
input
Point
sources
apparent
Downstream
output
downstream - upstr«am "O.I Kg/d
Entire is not a significant
source of mercury.
THEHTOM CHAMMEL iTJBTET III
Mercury, Total CKg/d)
1,84
Upstremii
input
,04
Point
sources
1,66
Downstream
output
appartnt
syrplus*,02
(1%)
—,,. apparent
dtfic»l=.Q4
1.83
downstream - ypslream - .01 Kg/d
Entire is not a significant
source of mercury.
FIGURE IX-22. (Cont'd.) Trenton Channel balance results.
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547
TREKTON CHANNEL 5URYBY II
Cadmium, Total (Kg/d)
Upstream
input
Point
sources
Downstream
output
apparent
C deficit'2.3
apparent
deficit-1.8
downstream -upstream »1.1 Kg/d
Entire area is not a statistically significant
source of cadmium.
TREHTON CHANNEL SURVEY III
Cadmium, Total (Kg/d)
9.3
Upstream
input
Point
sources
Downstream
output
10.1
apparent
C surptus-4.I
(508)
apparent
deficit=8.4
downstream - upstream =08 Kg/d
Entire area is not a statistically significant
source of cadmium although C-A area is
a significant source.
TREMTON CHAHMEL SURYBT II
Chloride, filtered (MT/d)
TREHTOM CHAMMEL SURTET III
Chloride, Filtered (MT/d)
Upstream
input
Point
sources
Downstream
output
1307
apparent
C syrpius* 1 1.7
apparent
deficit=42.0
1321
downstream - upstream -14 MT/d
Entire area is not a statisticalty significant
source of chloride although the C-A area
is a significant source.
Upstream
input
42
Point
sources
Downstream
output
1198
1264
C
apparent
(2%)
D
apparent
deficit=45.0
1222
downstream - upstream =24 MT/d
Entire area is not a statistically significant
source of chloride.
FIGURE IX-22. (Cont'd) Trenton Channel mass balance results.
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548
TBEHTOH CHAHHEL SURVEY II
Nickel, Total (Kg/d)
TREHTOH CHAHHEL SUKYEY III
Nickel, Total (Kg/d)
2588
Upstream
input
Point
sources
334.4
Downstream
output
apparent
C surplus=2 1
apparent
deficit=23.2
243.1
downstream - upstream =15.7 Kg/d
Entire area is not a statistically significant
source of nickel.
Upstream
input
Point
sources
5.4
0.3
Downstream
output
apparent
C surplus^ 15.5
apparent
dericit-37.9
317.7
downstream - upstream - 16.7 Kg/A
Entire area is not a statistically significant
source of nickel.
TREHTOH CHAHHBL SURVEY II
Total PCB's (Kg/d)
TREHTOH CHAHHEL SURREY III
Total PCB's (Kg/d)
Upstream
input
Point
sources
.02
~Q
1 48
1
745
1.29
apparent
C deficit=0.21
Downstream
output
1.54
downstream - upstream = .06
apparent
surplus=.25
Entire area is not a statistically significant
source of PCS.
Upstream
input
Point
sources
Downstream
output
apparent
C deficit=1.09
apparent
'deficit=.57
5.85
downstream - upstream =1.6 Kg/d
Entire area is not a statistically significant
source of PCS.
FIGURE IX-22. (Cont'd.) Trenton Channel mass balance results.
-------
549
TREMTOtf CHANNEL SURTET II
Copper, Total (Kg/d)
TREMTOM CHANNEL SUBTEY III
Copper, Total (Kg/d)
184.5
213.1
Upstream
input
Point
sources
Downstream
output
apparent
C surp)ys=1GS,7
(35?,)
apparent
deficit-107,5
114.3
downstream - ypstrsam =9,8 Kg/d
Entire is not a statistically
source of copper. Significant
accumulation oceured in the D-C area.
Upstream
input
Point
sources
Downstream
output
apparent
apparent
dericil-88,3
172,1
downstream - ypstream =40.5 K
-------
550
TRENTOH CHANMEL SURVEY U
Phosphorus, Total (Kg/d)
TREHTOH CHAHHBL SURYgy III
Phosphorus, Total (Kg/d)
Upstream
input
3853
Point
sources
3685
Downstream
output
apparent
C deficit=163
apparent
deficit.'184
3788
downstream - upstream = 65 Kg/d
Entire area is not a statistically significant
source of phosphorus.
Upstream
input
Point
sources
Downstream
output
apparent
C surpius=424
4061
downstream - upstream = 376 Kg/d
Entre area is not: a statistically significant
source of phosphorus although the C-A
area is a significant source.
TKEMTON CHANNEL SURTEY III
Silica, Filtered (MT/d)
TRENTOH CHAKMEL SURVEY II
Silica, Filtered (MT/d)
207
184
Upstream
input
Point
sources
3.2
0.4
Downstream
output
208
apparent
C deficTt'0,2
apparent
dericit-2.4
downstream -upstream =1.0 MT/d
Entire area is nota statistically significant
source of silica.
Upstream
input
Point
sources
Downstream
output
185
apparent
C surpius=! .2
(0.68)
apparent
^.3
downstream - upstream = 1.0 MT/d
Entire area is nota statistically significant
source of silica.
FIGURE IX-22, (Com'd.) Trenton Channel mass balance results.
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551
Detroit River System Mass....Balance l_and 2
The Detroit River system Mass Balance studies 1 and 2 were con-
ducted between April 21 to 29, 1986, and July 25 to August 5,
1986, respectively (30). Sampling transects were located at the
head of the Detroit River at Peach Island and the mouth of the
Detroit River just downstream of the Grosse lie bridge (see
Figure IX-3}. The results of these analyses indicate that the
Detroit River is statistically significant source of several
heavy metals (Cd, Cu, Pb, Ni and zn) total phosphorus and PCBs.
These data also suggest that some contaminants may be continuing
to accumulate in the sediments.
Trenton Channel Mass_ Balance
The Trenton Channel Mass Balance II and III were conducted be-
tween May 6 and 7, 1986, and August 26-27, 1986 (31), Results of
these analyses are shown in Figure IX-22. Letters on the right
hand side of the diagrams refer to the transects indicated in
Figure IX-23. These data suggest that lead and zinc enter the
Trenton Channel in significant amounts. The data also suggest
that cadmium and copper may also enter the Trenton Channel in
significant amounts between certain transects. During the TCMB
II, zinc was a source in segment A-C and a sink in segment C-D
indicating rapid loss of zinc from the water column, probably to
the sediments.
2. Process Modeling
Process oriented models investigate the relative importance of
the processes controlling the simulated system to identify needed
field measurements and experimental studies. Process models
developed for the Detroit River range from physical water move-
ment models to temporal and spatially complex contaminant fate
and behaviour models. Verification is difficult without the
necessary data, but these models can be used to speculate upon
the contaminant fate and organism exposure. Process model output
is uncertain because loading information, boundary conditions,
initial conditions, and parameter estimates are uncertain. Un-
certainty analyses were not completed for these data. Sensiti-
vity analysis helped to identify some parameters and processes
needing further research to improve contaminant fate models.
Detroit River, Detroit WWTP Plume Model
A two dimensional hydrodynamic and water quality model of the
Detroit River was developed to simulate the impact of the Detroit
WWTP effluent on water quality (28). The model contains two
independent finite elements, a hydrodynamic model which predicts
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552
Transact A
WYANDOTTE
Penwalt Chemical Corp,
Wayne County Wyandotte WWTP
•n
Transect B
Monguagon Creek
Crysler Corp,
Trenton Motor Plant
Trenton WWTP
Wayne County
Trenton WWTP"
Monsanto Chemical Co.
Detroit Edison
Transect D
McLouth Steel Corp.
TRENTON
Mobil Oil Co.
FIGURE IX-23, Major point source dischargers and Trenton Channel mass
balance sampling transects, Detroit River (1986).
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553
the two dimensional flow field, and river water concentrations and
a finite element transport and kinetic model.
The two dimensional model was used because the river is not
laterally mixed, has rapidly changing bottom geometry, and flow
is divided by islands. The NELEUS TM model simulates and asses-
ses environmental impacts under varied ambient and effluent con-
ditions including 1) two dimensional velocity flow fields,* 2)
free surface elevations; and 3) flow distribution in individual
panels and branches. The contaminant transport component simu-
lates the temporal and two dimensional contaminant concentration
distribution using the predicted flow field.
This model was validated with intensive water quality surveys and
could provide a basis for evaluating water quality issues from
upstream of the Detroit WWTP discharge downstream to the Trenton
Channel. The NELEUS TM contaminant transport model was calibrat-
ed and verified using survey data from both dye and water quality
surveys. Model coefficients were developed for longitudinal and
lateral diffusion partitioning coefficients describing the dis-
tribution of contaminants between particulates and dissolved
fractions, characteristic suspended solids concentrations, set-
tling velocities and decay rates for each contaminant.
Eight effluent management scenarios were chosen by the Detroit
WWTP for model evaluation of environmental fate. Results indi-
cate incremental impacts of Detroit WWTP effluent on the Detroit
River and the water quality responses to various management al-
ternatives . Although the model made these predictions, unfor-
tunately the results were not compared to Michigan Rule 57(2)
allowable levels. Mercury and PCB concentrations would both
exceed these levels at all points in the river. In addition, the
size of the mixing zone for the Detroit WWTP is currently under
review. A reduction in its size will alter the interpretation of
model conclusions.
Trenton Channel Transport Model
A transport model is being developed and calibrated for the
Trenton Channel using specific conductance as a tracer for
toxics, when completed, it will calculate the probability dis-
tribution of toxicity in water due to sediment resuspension. The
model requires specific locations of toxic sediments, time bet-
ween resuspension events, magnitude of sediment resuspension and
toxicity associated with resuspended materials.
A hypothetical application was developed to predict water column
toxicity resulting from sediment resuspension in the Trenton
Channel near Monguagon Creek. Introduced toxicity was assumed to
remain in the water with no settling occurring. The time between
resuspension events were assumed to follow a Poisson distribu-
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554
tion. During resuspension, both porewater and suspended solids
are scoured into the water column. Resuspension magnitude was
assumed to be a random variable described by a log-normal dis-
tribution with a median resuspension volume of 4,300 cubic meters
of bed material (the top 3 cm).
Toxic unit concentrations were assigned to the resuspension
volume. The equivalent mass input of toxicity to the water
column was the product of a toxic unit concentration and the
resuspension volume. A single sediment concentration determined
from the dose response analyses of bioassays from the site were
used to describe the site,
Model results for this hypothetical application indicate that
sediment resuspension below Monguagon Creek will increase water
column toxicity along the western shore of the channel. Toxicity
increased as the time between events decreased or as the sediment
toxicity increased. An approximately 1:1 relationship existed
between sediment toxicity and water column toxicity. Toxicity
ranged over several orders of magnitude as a consequence of the
large resuspension variability. Resuspension frequency had the
largest impact on the aquatic toxicity.
The model predicted a slight overall decline in toxicity between
Monguagon Creek and the end of the modeled segment near the bot-
tom of the Trenton Channel.
-------
555
F. OBJECTIVES AND GOALS FOR REMEDIAL PROGRAMS
By evaluating the specific concerns in the Detroit River identi-
fied by this survey, in light of the contaminant input provided
by point and nonpoint sources, an overall approach to addressing
contaminant inputs can be derived. Remedial programs are to be
developed in areas that fail to meet the general or specific
objectives of the Great Lakes Water Quality Agreement of 1978, as
amended (1987), where such failure has caused or is likely to
cause a change in the chemical, physical or biological integrity
of the Great Lakes. The general goals and objectives for remedi-
ation of the Detroit River and contaminant sources are discussed
below. Specific recommendations are provided in Section H,
1. Water Quality
Water quality in the Detroit River, as determined by this study,
is generally better than applicable water quality guidelines for
most parameters measured. However, there are some exceptions,
PCB concentrations exceeded various water quality guidelines
throughout the river, Homologue analysis suggests that an active
source of PCB exists in the river. Chlor'obenzene concentrations
in the Detroit River are below the Ontario water quality objec-
tive for hexachlorobenzene. However, concentrations of chloro-
benzenes at the mouth of the Rouge River exceed this and other
guidelines for HCB. A substantial increase in PAH concentration
from the head of the Detroit River to the mouth, especially along
the Michigan shoreline, indicates an input source. No appropri-
ate ambient water quality guideline exists for total PAHs, Sever-
al metals exceeded water quality guidelines throughout, or at
specific locations, in the Detroit River, specifically mercury,
lead and cadmium.
Objective 1: Reduction, with the goal of virtual elimination,
of industrial and municipal point source inputs of
contaminants to the Detroit Eiver which are resul-
ting in exceedences of ambient water quality
guidelines.
Objective 2: Development of ambient: water quality guidelines
for contaminants without such guidelines, which
are present in the Detroit River water.
Tributaries of the Detroit River exceeded applicable water qual-
ity guidelines for several parameters: the Rouge River (total
cadmium, total phosphorus, total zinc, total mercury), the Canard
River (total cadmium, total phosphorus, total mercury, total
lead), Turkey Creek (total cadmium, total phosphorus, total lead,
total mercury, chlorides), the Little River (total cadmium, total
phosphorus, total lead, total mercury, total zinc) and the Ecorse
River (total phosphorus, total mercury). These tributaries
-------
556
provide inputs of these parameters approaching that provided by
point sources. Of all Detroit River tributaries, the Rouge River
provides the largest loading of most contaminants.
Objective 3: Identification of contaminant input sources to
tributaries of the Detroit River, and reduction,
with the goal of virtual elimination, of such
inputs.
Contaminants in the Detroit River may have occurred, in part,
through the discharge of groundwater contaminated by waste dis-
posal sites or underground injection wells. Actual loadings of
contaminants from groundwater were not obtained. However, con-
firmed or possible contamination sites within the Detroit River
groundwater discharge areas were identified. The information was
inadequate to assess the impact of the site on the Detroit River,
Objective 4: Verification of groundwater contamination from
waste sites or underground injection wells which
threaten the ecosystem quality of the Detroit
River, and removal or control of wastes and. re-
sulting contaminated groundwater.
Detroit WWTP combined sewer overflows (CSOs) were a major con-
tributor (>10%) of PCBs, total mercury, oil and grease, total
cadmium, total chromium, total lead, total copper and total phos-
phorus to the Detroit River, About 55% of the CSOs discharge
directly into the Detroit River and about 40% discharge to the
Rouge River.
Objective 5; Eliminate the impact of City of Detroit CSOs on
water quality of the Detroit River and its tribu-
taries .
Limited information on Windsor urban runoff to the Detroit River
suggests that urban runoff (stormwater) may be a source of cer-
tain contaminants. While stormwater runoff from many municipal-
ities in and around Detroit is treated at the Detroit WWTP
through its combined sewer system, other municipalities (Wyan-
dotte, Trenton and Riverview) have numerous stormwater discharges
to the Detroit River or its tributaries,
Objective 6: Determine the significance of Michigan urban run-
off through monitoring and sampling. Remedial or
management action may be required.
Numerous spills of chemicals, oil and raw sewage to the Detroit
River or its tributaries were reported during 1986, which is
presumably representative of present day spill incidents, Penn-
walt Corporation experienced several chemical spills during 1986;
Wickes Manufacturing experienced a spill of nickel salts and
chromic acid; large volumes of raw sewage were spilled from
-------
557
Michigan, as well. Information regarding spills is inadequate
and incomplete, providing no information on spill volume or con-
stituents, making impact assessment difficult.
Objective 7:
Ensure that accurate and complete spill incident
reports are maintained at the appropriate agen-
cies, to allow proper remediation, enforcement and
preventive measures to be tafcen.
To protect human health, there are periodic beach closings along
the Detroit River, due to elevated bacterial concentrations,
Standards and guidelines for fecal coliform bacteria concentra-
tions have been exceeded in the Detroit River,
Ob j ective 8:
Ensure that the Detroit River water is of high
quality to permit total body contact without
deleterious human health impacts.
2. Sediments
Detroit River sediments, especially on the Michigan side and
particularly in the Trenton Channel, contain elevated concentra-
tions of several contaminants. Concentrations of PCBs, cyanide,
oil and grease, cadmium, line, mercury, lead, copper, nickel,
iron, chromium, arsenic, manganese, total phosphorus and nitrogen
exceed dredging guidelines at various river locations. Sediments
also contain concentrations of contaminants, such as total phen-
ols and total PAHs, for which no guidelines exist. Other chemi-
cals, such as pesticides, phthalates and volatile chemicals, were
also found.
Objective i;
Objective 10:
Objective 11:
Objective 12:
Reduction, with virtual elimination as a goal, of
industrial and municipal point source inputs of
contaminants resulting in sediment contaminant
concentrations exceeding dredging guidelines.
Reduction, with virtual elimination as a goal, of
nonpoint sources of contaminants (tributaries,
urban runoff, waste sites, CSOs, spills) resulting
in sediment concentrations; exceeding dredging
guidelines.
Determination of the areal and vertical extent of
seriously contaminated sediments, to permit class-
ification and prioritization of sediment remedia-
tion,
Development of sediment criteria based on aquatic
life health effects and other pertinent parameters
for contaminants found in the Detroit River which
do not currently have such guidelines.
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558
Certain Detroit River sediments, sediment porewater and. near-
bottom water were toxic to benthie and/or pelagic organisms.
Nearshore Trenton Channel sediment porewater was toxic in bac-
terial luminescence assays. Sediment extracts were mutagenic in
the Ames test, particularly those from Trenton Channel and the
lower river, near Lake Erie. Comparable toxicity was demonstra-
ted in Daphnia pulicaria feeding studies, PaBhnia magna acute
toxicity tests, Ceriodaphnia reproduction assays, Chironomujs
tentans growth tests, and others. Studies on the effect of
Detroit River sediments and sediment porewater on feeding rates
of larval channel catfish and on toxicity to rainbow trout eggs
confirms sediment toxicity to fish species, as well. The great-
est degree of toxicity invariably found in Trenton Channel
sediments.
Objective 13; Eliminate sediments in the Trenton channel and
elsewhere in the Detroit River which are toxic to
benthic and pelagic organisms. Work presently
taking place to determine the specific reasons for
degradation and toxicity to benthic organisms
should be supported,
Contaminated Detroit River dredged materials require disposal in
confined disposal facilities and, in cases, hazardous waste
landfills. Costs for such disposal are high, and may result in
future restrictions on recreational and other uses of the Detroit
River,
Objective 14; Anticipate future dredging rates through planning
and. priorxtization, and identify potential dis-
posal sites,
3, Biota and Habitat
There is currently a Michigan consumption advisory for carp due
to elevated body burdens of PCBs, OMOE has also issued a fish
consumption advisory for certain sizes of rock bass, freshwater
drum, and walleye for mercury, and carp for PCBs. PCBs were
found in young-of-the-year spottail shiners at highest concentra-
tions in the lower, western reach of the river (Trenton Channel
and below) and near Grassy Island {by the Ecorse River), indicat-
ing localized Michigan inputs.
Objective 15; Reduction of contaminant concentrations in Detroit
River fish tissue to eliminate all fish consump-
tion advisories.
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559
Objective 16; Reduction, with the goal of virtual elimination,
of industrial and municipal point sources of con-
taminants to the Detroit River which are bioae-
cumulative in aquatic biota, and have or may
result in fish consumption advisories»
Objective 17; Elimination of nonpoint sources of PCB, mercury
and other persistent, bioaccumulatlve compounds to
the Detroit River which have or may result in fish
consumption advisories.
Caged and native clams in the Detroit liver contained elevated
concentrations of several contaminants: PAHs, HCB, DCS, lead and
cadmium. No consumption advisories or other guidelines exist for
these chemicals in aquatic biota tissue, except for lead
(Ontario). Although Detroit River clams are not a common food
source for humans, they are for certain wildlife.
Objective 18; Detelimination of the importance of clams as a
wildlife food source and the impact of contamin-
ants contained in clam tissue on wildlife health.
Serious impacts to waterfowl, wildlife and fish, and their habi-
tats, have occurred in the Detroit River. Waterfowl, tern
species, and their eggs contain high concentrations of persistent
compounds {PCB, DDT and other organoehlorine compounds)» affect-
ing organism health, reproduction survival. Oral/dermal
tumors and liver tumors are present in brown bullhead, walleye,
white sucker and other species in the lower Detroit River,
Objective li: Identification of the chemicals responsible for
such Impacts on fish, wildlife and aquatic life,
and the virtual elimination of point and nonpoint
source inputs of these contaminants.
Objective 20: Development of consumption advisories for water-
fowl and wildlife to protect human consumers of
these organisms,
Bulkheading and/or backfilling of wetlands, littoral zones,
bayous and small embayments in the Detroit River, especially in
the Trenton Channel, have resulted in extensive losses of spawn-
ing grounds and nursery areas for desirable fish, and has preven-
ted use by waterfowl, aquatic mammals and other aquatic organ-
isms. The fish community changed ovejr time resulting in
losses of coldwater species. Channel dredging near the turn of
the century destroyed whitefish spawning habitat near the mouth
of the Ecorse River, In addition to providing habitat, wetlands
also serve to remove contaminants by natural filtering.
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560
Objective 21: Preservation and enhancement of existing fish and
wildlife habitats, and development of new habi-
tats , Maintenance of the Wyandotte National Wild-
life Refuge and protection of Grassy Island need
to be enhanced to encourage wildlife, especially
waterfowl,
4, other Issues
The contribution made by atmospheric deposition of contaminants
to the Detroit River system was not examined by this study.
Certain contaminants affecting the Detroit River system may be
contributed, in part, through atmospheric deposition, such as
lead (auto exhaust) and cadmium (steel industries), Loadings of
these contaminants were often relatively high for rural and urban
runoff, suggesting a diffuse source.
Objective 22: Determine the significance of atmospheric depo-
sition as a contaminant input mechanism in the
Detroit River system, identification of contamin-
ant origins and reduction of such input to its
lowest achievable level,
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G. ADEQUACY OF EXISTING PROGRAMS AND REMEDIAL OPTIONS
1, Projection of Ecosystem Quality Based on Present Control
Programs
Trend Analysis
The general media quality and aesthetics of the Detroit River
have improved over recent years. However, a number of particular
concerns remain.
Generally, water in the Detroit River is of a higher quality than
in the recent past. However, in the present survey, concentra-
tions of a number of contaminants and conventional pollutants
increased from the head to the mouth of the Detroit River, al-
though the statistical significance of these increases is not
known. Other conventional water quality parameters, including
ammonia and phenols, were found to have declining trends. Am-
monia concentrations have decreased by approximately 50% between
1969 and 1981. Data on chloride concentration in the river indi-
cate that although sources still exist on both sides, especially
in the lower river, concentrations and loadings have declined
from 1969 to 1981 (30).
Sediment contamination in the Detroit River is continuous along
the Michigan shoreline and appears to be localized near known
sources along the Ontario shoreline (39). Trend data from 1970
to 1980 indicate levels of mercury in sediments have decreased,
in part a result of improvements in industrial treatment facili-
ties (e.g. replacement of mercury cells by diaphragm cells at
chlor-alkali plants at Wyandotte) (39). Results of two sediment
studies indicated that mercury contamination is higher in sur-
ficial sediments than in the deeper layers, suggesting that there
may still be active sources (76). Significant increases in sedi-
ment levels of cadmium, chromium, copper, lead, nickel, and zinc
were noted near the mouth of the Rouge River from 1970 to 1980,
suggesting recent inputs.
Data on contaminant levels in fish from the Detroit River is
insufficient to determine trends for many chemicals; however,
some research has been done with young-of~the-year spottail
shiners, which are sensitive biomonitors for organochlorine com-
pounds . High PCB residue accumulations were found in spottail
shiners along the Michigan shoreline in the lower Detroit .River,
suggesting the continuing presence of inputs of biologically
available PCBs to the river. DDT residues were found, but con-
sisted of metabolites only, indicating that use restrictions have
effectively reduced DDT inputs to the river. Chlordane residues
were elevated in all spottail shiner samples from urban areas
compared to rural collections (45).
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Fish consumption advisories are currently in effect for rock
bass, freshwater drum, walleye and carp due to mercury or PCB
contamination (46,47), Population studies of bottom fauna have
shown organisms characteristic of higher water quality are in-
creasing in some areas, but degraded benthic macroinvertebrate
populations are present especially on the Michigan side of the
river (39).
2. Assessment of Technical Adequacy of Control Programs
Adequacy of Present Technology
i) Municipal Wastewater Treatment Facilities
There are five municipal waste water treatment plants in Ontario
and six in Michigan which discharge into the Detroit River, The
levels of treatment vary, but all have phosphorus removal. The
facilities which provided inputs of contaminants of concern are
discussed below.
The Detroit WWTP provides secondary treatment (activated sludge)
for up to 3,047 x 10^ m^/day of wastes tributary to the combined
sewer system. During wet weather periods', incremental flows
above 3,047 x 10^ m-Vday ar© provided primary treatment and
disinfection prior to discharge to the Detroit River. Secondary
effluent is coiabined with any primary effluent and discharged to
the Detroit River at a rate determined by river elevation and the
portion of flow receiving secondary treatment. Combined sewers
discharge directly to the Rouge and Detroit rivers when the
hydraulic capacity of the system is exceeded. About 284 x
itwday of wastewater flow is generated by industrial indirect
dischargers. Presently, there are no data available on the per-
centage of industries which are in compliance with the Industrial
Pretreatment Program since the program is new. The Detroit WWTP
facility was generally in compliance with its NPDES permit during
1986, which was confirmed by 1986 wastewater survey. The present
technology is adequate to control the facility's regulated, and
monitored parameters based on existing water quality criteria.
The Detroit WWTP's permit is scheduled for reissuance in 1989 and
some facility upgrading may be required.
The Wayne County-Wyandotte WWTP is a pure oxygen, activated
sludge facility with a design capacity of 375 x 103 m3/day. The
Wayne County-wyandotte WWTP and the South Huron Valley WWTP
{which discharges into Lake Erie) jointly have an Industrial
Pretreatment Program. In 1986, the facility exceeded its NPDES
monthly average permit limitation for total suspended solids (4
of 12 months), and exceeded its fecal coliform monthly average
limitation for all 12 months of the year. A 1986 wastewater
survey indicated the facility was in compliance with NPDES permit
at the time of the survey. For the purposes of controlling the
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563
facility's regulated parameters, the present technology is not
adequate, since exceedences of permit limitations have occurred.
As of December 1988, this facility is being sued in federal court
for permit and schedule violations. A consent decree is being
negotiated. The facility has begun construction on two new
clarifiers in its treatment system and is planning additional
repairs.
The Wayne County-Trenton WWTP is operated as a primary treatment
facility with a design capacity of 13 x 103 m^/day. Treated
wastewater was discharged to the Elizabeth Park. Canal, a tribu-
tary of the Trenton Channel, This facility served a separate
sewer system, with no combined sewer discharges to the Detroit
River. This facility was in significant noncomplianee with its
total suspended solids monthly average loading limitation (5 of
12 months), total phosphorus monthly average concentration limit
(6 of 12 months) and fecal coliform monthly average concentration
limit (8 of 12 months) during 1986, The 1986 wastewater survey
indicated the facility met the NPDES final effluent limitations
at the time of the survey. For the purposes of controlling the
facility's regulated parameters, the technology was not adequate.
This facility has been decommissioned (as of December 1988}.
Flows are being directed to the new South Huron Valley WWTP,
which discharges directly into Lake Erie.
The City of Trenton WWTP is an activated sludge secondary treat-
ment system with an average daily flow of 22 x 10^ m-vday, 3nd is
discharged to the Elizabeth Park Canal. The City of Trenton has
an approved Industrial Pretreatment Program with 9 major par-
ticipants. Wastewater flow generated by these industries is
approximately 5.3 x 10^ m-Vday. In 1986,, this facility was in
noncomplianee for BOD concentration and loading limits (5 of 12
months), total suspended solids concentration and loading limits
(5 of 12 months), total phosphorus monthly average concentration
(5 of 12 months)/ and dissolved oxygen minimum concentration (8
of 12 months). A wastewater survey conducted in 1987 showed this
facility to be in noncomplianee with its NPDES permit limitations
for dissolved oxygen, and concentrations of other parameters
(8005, phosphorus, suspended solids and fecal coliforms) were
higher than would be desired (the permit does not have daily
maximum limits for these parameters, so noncomplianee cannot be
construed). For the purposes of controlling the facility's regu-
lated parameters, the present technology is not adequate, since
exceedences of effluent limitations have occurred. No federal
action has been taken against this facility, as of December 1988,
however, the state has notified the facility of its noncomplianee
status.
The West Windsor WWTP currently uses a physical-chemical treat-
ment process with a capacity of 160 x 10^ m3/day. The Windsor
catchments receive a large quantity of industrial wastewater.
However, sampling data indicate concentrations compare favorably
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with concentrations in less industrialized catchments. This
facility was in compliance with its effluent requirements for
BOD5 and suspended solids during 1985 and 1986.
ii) Industrial Point Sources
The UGLCCS Point Source Workgroup identified seventeen Michigan
and four Ontario industries as major point source dischargers
into the Detroit River (directly or indirectly). These indus-
tries include automotive, chemical, cement and steel, and were
presented in Table IX-4.
It is not practicable to discuss the technology used at each
industrial facility. The Point Source Workgroup Report (6)
should be consulted for such detail. However, the attainment {or
lack) of effluent limitations provides insight into the adequacy
of the technology used. Eleven of the Michigan facilities were
in general compliance with their 1986 NPDES Permits (Table IX-4)»
one facility did not have a permit (Ford-Wayne Assembly Plant;
but institution of one is being considered), and another facility
began discharging to a sanitary sewer as a result of problems
meeting its permit effluent limits (Chrysler-Trenton Engine
Plant). For the purposes of controlling contaminants at regu-
lated levels, the technology employed at most Michigan industrial
facilities appear to be adequate.
Of the three Ontario industrial facilities surveyed, only one
fully met the Ontario Industrial Effluent Objectives during 1985
and 1986. Ford Canada exceeded total suspended solids and phenol
objectives, and Wickes Manufacturing exceeded total suspended
solids and nickel objectives. The present technology at Wickes
Manufacturing and Ford Canada does not appear to be adequate to
control certain parameters with industrial effluent objectives.
Adequacy of Best Available _Technology
The best available technology economically achievable (BAT) for
every industrial and municipal sector has. not yet been defined,
although some U.S.Industries have BAT in place. The U.S.EPA and
the OMOE (through its MISA program) are currently developing BAT
for various sectors.
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3, Assessment of Regulatory Adequacy
Adequacyof Present Laws and Regulations
Existing legislation in the United States, Canada, Michigan and
Ontario addressing ecosystem quality of the Detroit River has
been discussed elsewhere in this report (Chapter III).
acts, regulations, and programs are currently in place, addressing
the control of point and nonpoint sources of contaminants, man-
agement of solid and hazardous waste, acceptable contaminant
concentrations in various media, and other environmental con-
cerns. Despite the considerable, and often complex, collection
of laws and regulations, serious contamination is apparent in the
Detroit River system, and exceedences of requirements and guide-
lines have been documented. This may indicate that the existing
legislation is inadequate, or is not properly enforced,
Michigan industrial and municipal point source dischargers in the
Detroit River area are generally meeting the effluent limitations
set by the state government. Michigan effluent limits address
conventional pollutants, such as total suspended solids, and
nonconventional or toxic parameters. Unless the facility is out
of compliance with effluent limits, contaminants are discharged
at concentrations within discharge limits. However, the large
volume of effluents results in very large total loadings of con-
taminants to the river. NPDES permits are reviewed every five
years, providing the opportunity to address specific concerns
highlighted by the UGLCC Study.
All Michigan municipal facilities impacting the Detroit River
receive waste water from industrial facilities. All have
regulatory mechanism for controlling the input of contaminants
from industries (the Industrial Pretreatment Program - IPP).
However, pretreatment requirements may have not addressing
all contaminants being introduced to the municipal facility, or
controlling them adequately, as evidenced by the large loadings
of some parameters by the municipal facility. From a practical
viewpoint, controlling the influx of contaminants to the munici-
pal facility from industrial facilities is the most effective
method of preventing ultimate discharge. The IPP program at each
Michigan facility to be examined for adequacy compli-
ance,
Only one Ontario industrial facility studied in the Detroit River
area has effluent requirements (General Chemical); the others are
encouraged to attain Provincial Industrial Effluent Objectives.
The Objectives are nonenforceable goals in and of themselves,
although they can be made enforceable through incorporation into
Control Orders or Certificates of Approval. Effluent objectives
are not consistently being met by all Ontario industrial facili-
ties. In other instances, these Objectives were met, yet impacts
in media were seen. For example, General Chemical, Amherstburg
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was identified as a major contributor of copper to the Detroit
River, yet discharged copper at concentrations below the Provin-
cial Industrial Effluent Objective of 1 mg/L. However, high
copper concentrations, exceeding dredging guidelines, were found
in sediments along the Amherstburg shoreline. This suggests that
the Objectives may not be stringent enough, particularly for
compounds with sediment binding capabilities.
The West Windsor WWTP was the only Ontario municipal facility
identified as a major discharger of contaminants to the Detroit
River (total phosphorus). This facility receives industrial
waste water, and adheres to the Windsor By-Law (#8319) which
regulates the discharge of conventional pollutants, metals and
total phenolics to sanitary sewers. Since its total phosphorus
discharge was less than 1 mg/L (annual average) in 1985 and 1986,
it appears that the By-Law regulations are adequate and effec-
tive, in the context of this study,
The new MISA program being implemented by Ontario should improve
discharge regulations in the province. Identification of ef-
fluent contaminants in specific municipal and industrial sectors
will enable the instatement of limits for all potentially harmful
contaminants. To be effective, it is necessary for sector re-
quirements to contain both concentration and mass loading limits.
Customizing of regulations to fit the industrial sectors should
reduce treatment costs and the associated analytical costs for
monitoring.
Present regulations and guidelines, particularly in Ontario, are
media-specific in scope and do not offer the flexibility needed
to address multimedia contamination, as found in the Detroit
River system.
Adequacy of Enforcement Authority and Programs
Michigan and Ontario programs which regulate discharges require
monitoring and reporting. Facilities are required to inform the
regulating agency of all effluent limit exceedences. In addi-
tion, audit samples may be obtained by the regulating agency,
often with the facility's pre-knowledge. Violations of effluent
limitations can be handled in a variety of fashions, ranging from
monetary fines to criminal prosecution, criminal prosecution
rarely occurs. Civil and administrative enforcement actions,
often involving negotiations between the facility and the regula-
ting agency, are undertaken to ensure future compliance.
Adequate enforcement authority for point sources appears to
exist; however, strengthening of penalties and an increase in
self-monitoring and auditing actions may prevent or hinder ex-
ceedences which are occurring.
In the Detroit River, the majority of point source dischargers
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are in compliance with effluent limitations. The weakness,
therefore, does not lie with the authority of the regulatory
agencies to enforce effluent limitations. It is more the result
of the traditional reliance on concentration based water quality
guidelines rather than on total loadings as well as, in many
cases, the limited number of parameters with which each facility
is legally bound to comply or monitor,
Ontario industrial point sources are experiencing exceeden-
ces of the Provincial industrial Effluent Objectives, which are
nonenforceable goals for the industrial facilities. Requiring
the attainment of the Objectives (or a more stringent value) is a
mechanism by which to gain more control over the discharges. The
new MISA program will establish effluent requirements which are
specific to each industrial sector. Until these become effec-
tive, regulation through requirement of effluent objectives ap-
pears needed.
Regulations and enforcement authorities are limited or absent for
contamination resulting from nonpoint sources.
Adequacy of_Goye^nmejital.__an<3^.ln3ti_tutional Authority and Juris-
dactions
Federal, state, provincial, and municipal governments have the
authority to regulate chemical discharges to the Detroit River.
Thus, the lack of authority is not the problem. Ongoing environ-
mental concerns related to chemical contaminants result, in part,
from a fragmented approach to controlling discharges. Different
priorities among agencies result in a lack of co-ordination and
proper long-term planning.
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H. RECOMMENDATION'S:
Actions which, can result in improvements in ecosystem quality in
the Detroit River system are many and varied. Generally, recom-
mendations made for the Detroit River are in four forms: recom-
mendations directed at specific sources which can be implemented
with existing regulatory authorities, recommendations which may
require process or treatment changes, management issues and ap-
plications or other voluntary (as opposed to regulatory) meas-
ures, and recommendations which identify further needed research
and study.
A, Industrial and Municipal Point Source Remedial Recommendations
1. Ontario and Michigan should incorporate the Great Lakes
Water Quality Agreement's goal of the virtual elimination of
all persistent toxic substances into their respective regu-
latory programs.
2. The Detroit WWTP was a major discharger of numerous com-
pounds which impact water, sediment and biota quality in the
Detroit River. Contaminant loadings from this facility
should be evaluated to ensure compliance with Michigan water
quality standards.
a) In general, contaminant concentrations in the effluent of
the Detroit WWTP are low; major loadings result from the
•large volume and rate of effluent discharged. Control of
contaminants may be obtained through the Industrial Pre-
treatment Program (IPP). The IPP of the Detroit WWTP should
be examined and compliance of contributors of industrial
waste water should be determined. The adequacy of the pre-
treatment requirements should be assessed. Pretreatment
requirements should be assessed to determine if parameters
of concern in the Detroit River system are adequately regu-
lated. A notice of violation was issued (September 1988) to
the Detroit WWTP for problems found in its IPP program.
b) The Detroit WWTP currently performs secondary treatment on a
large portion of its effluent. During wet weather flow,
some effluent receives only primary treatment prior to being
mixed with secondary treated effluent and discharged. Met-
als and organics which may be contained on suspended solids
not removed in primary treatment are of concern. The City
of Detroit should complete its studies of treatment plant
capacities started in 1985 and upgrade its treatment process
to provide secondary treatment for all effluent.
c) The effluent limitations contained in the Detroit WWTP NPDES
permit should be re-examined in light of the findings of
this study to ensure compliance with Michigan water quality
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standards. Consideration should be given to increasing the
number of parameters monitored by the permit. All effluent
limitations should be the lowest technically feasible.
Bioassays of the effluent to determine both acute and
chronic impacts to aquatic organisms should be considered as
a condition of the permit. The Detroit WWTP NPDES permit is
scheduled for reissuance in 1989.
3. The Wayne County-Wyandotte WWTP was a major discharger of
numerous compounds which impact water, sediment and biota
quality in the Detroit River. Although the facility was
generally in compliance with its effluent limitations, the
NPDES permit monitors very few parameters found to be of
concern in the Detroit River.
In general, contaminant concentrations in the effluent of
the Wayne County-Wyandotte WWTP are low; major loadings
result from the large volume and rate of effluent dis-
charged. Control of contaminants may be obtained through
the Industrial Pretreatment Program (IPP). The IPP of the
Wayne County-Wyandotte WWTP should be examined. The com-
pliance of industrial contributors should be determined, and
the adequacy of the pretreatment requirements should be
assessed. Pretreatment requirements should be considered
for all parameters of concern in the Detroit River system
which are being discharged by the industrial dischargers.
Contaminant loadings from this facility should be evaluated
to ensure compliance with Michigan water quality standards
and BAT requirements.
4, The City of Trenton WWTP exceeded its permit limitations for
regulated parameters. The treatment provided by this facil-
ity should be examined and upgraded to ensure compliance
with effluent requirements.
5. Several industrial facilities were identified as major dis-
chargers of parameters that impact media quality in the
Detroit River. These facilities are presented below with a
discussion of facility-specific issues.
a) Rouge Steel was a major contributor of total iron, total
copper, total lead, total zinc, and oil and grease to the
Detroit River, chemicals which were present in the sediments
at concentrations exceeding dredging guidelines. Rouge
Steel was the major contributor of total PAHs and a source
of total phenols which were found in sediments, but have no
sediment dredging or quality guidelines. Rouge Steel's
NPDES permits do not regulate total PAHs nor monitor iron or
copper. The discharge of these 3 parameters should be eval-
uated to ensure compliance with Michigan water quality stan-
dards and BAT requirements. Rouge Steel was in compliance
with its permit limitations for total lead (applicable at 3
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570
of 11 outfalls), total zinc (applicable at 3 outfalls),
total phenols (applicable at one outfall) and. oil and. grease
{applicable at two outfalls). Considerable amounts of
phenol were discharged from outfalls not monitored for phen-
ol, and oil and grease were also discharged from nonregu-
lated outfalls. Discharge of total phenols and oil and
grease from all outfalls should be reduced to ensure com-
pliance with Michigan water quality standards and BAT
requirements,
b) Ford Canada was a major contributor of total lead, total
zinc, PCBs and total phenols, chemicals which impact the
Detroit River system. The stretch of river downstream of
Ford Canada (sediment subarea 2) had the highest average
sediment concentration of PCBs, Sources other than Ford
Canada were suggested, but Ford Canada cannot be ruled out
as a source. All sources of PCBs should be identified and
eliminated. High total phenol, total lead and total zinc
concentrations in sediments were also found in subarea 2,
This facility met the Ontario Industrial Effluent Objective
for lead and zinc of 1 mg/L, but exceeded the Ontario In-
dustrial Effluent Objective of 20 ug/L for total phenols by
a substantial amount during the survey (almost two orders of
magnitude). Discharge of total phenols should be reduced to
ensure compliance with the Ontario Industrial Effluent Ob-
jective. Discharges of PCBs should be reduced to the lowest
level technologically achievable.
c) Wickes Manufacturing was a major contributor of chromium to
the Detroit River, and discharged nickel, as well. High
bottom and suspended sediment concentrations of chromium
were found in Little River, to which Wickes Manufacturing
discharges. Wickes Manufacturing did not meet the Ontario
Industrial Effluent Objective for chromium during the sur-
vey. Nickel impacted Detroit River sediments in the upper
(as well as lower) Detroit River. High water concentrations
of nickel were also found in the Little River. Wickes
Manufacturing did not achieve the effluent objective for
nickel eight times during 1985 and 1986, in addition to
exceeding it during the survey. Discharges of chromium and
nickel should be reduced to ensure consistent attainment of
the Ontario Industrial Effluent objective. An effluent
requirement should be developed, for Wickes Manufacturing at
the lowest level technologically feasible.
d) McLouth Steel-Trenton was a major contributor of zinc, iron,
HCB and oil and grease, chemicals which impact the Detroit
River system. Of these, McLouth Steel-Trenton has an ef-
fluent limitation for oil and grease, with which it was in
compliance. This facility has no effluent monitoring re-
quirements for zinc, iron or HCB. Such effluent monitoring
should be considered for McLouth Steel-Trenton.
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e) General Chemical, Amherstburg was a major discharger of
copper to the Detroit River. High copper sediment concen-
trations were found adjacent to Amherstburg. Since the time
of the point source survey/ General Chemical has split into
two distinct companies, Allied Chemical and General chem-
ical. The two new companies should be surveyed to determine
the extent of present day copper discharge, and contingent
upon the results, remedial action taken. General Chemical
was also a major source of chlorides to the Detroit River;
however, the lower Detroit River transect measuring water
quality was upstream of General Chemical and did not reflect
the facility's impact on water quality. Although no impacts
due to elevated concentrations of chlorides were noted dur-
ing this study, the potential for an increase in halophilic
organisms exists. Additional surveys downstream of the
General Chemical complex outfalls should be performed to
determine if such a shift in organisms has occurred.
f) Great Lakes Steel-Ecorse and Great Lakes Steel-80" Mill both
contributed large loadings of oil and grease to the Detroit
River, pollutants found to be impacting sediments in the
Detroit River. Both facilities have effluent limitations
for oil and grease; both were in compliance with these
limits in 1986. Consideration should be given to institut-
ing more stringent effluent limitations for oil and grease
at these facilities.
B. Nonpoint Source Remedial Recommendations
6, The extent of contaminant input to the Detroit River system
resulting from Detroit WWTP combined sewer overflows is
largely unknown, although some estimates have been made.
Information available suggests that contaminant inputs may
be substantial. The required study on the Detroit WWTP CSOs
(order issued September 1938) should be expedited, and an
area-wide remediation plan should be developed. Upgrading
of the Detroit sewer system by increasing treatment capaci-
ties of the facility and eventually separating storm and
sanitary sewer to eliminate CSOs should be undertaken.
1. Due to the significance of the Rouge River as a source o£
loadings of organic and inorganic substances to the Detroit
River, the Rouge River Remedial Action Plan should be devel-
oped and implemented as expeditiously as possible. The
implementation of recommendations for the Clinton and St.
Clair Rivers' RAPs will also assist remediation efforts for
the Detroit River, •
8. Confirmed or possible groundwater contamination sites within
the Detroit River discharge area were identified for this
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study. Extensive recommendations were made for these sites
by the Nonpoint Source Workgroup. The main focus of the
Workgroup's recommendations are;
a) Zug Island Great Lakes steel: MDNR should perform a site
visit to clarify the facilities' proper RCRA status, to
perform sampling of monitoring wells, to determine the con-
taminant release to groundwater and to provide information
for rescoring of the site for the National Priorities List
(NPL) using the new Hazard Ranking System (HRS).
b) Federal Marine Terminal Properties: ' U.S.EPA should monitor
site closure to assess closure impacts and to study ground-
water discharge to surface water.
c) Industrial Landfill (Firestone); This site should be re-
scored for the NPL using data generated by the UGLCC Study
and other current studies.
d) Michigan Consolidated Gas-Riverside Park: Remedial action
proposed by the company should be reviewed to assess its
adequacy in controlling groundwater discharge Co surface
water.
e) BASF/Wyandotte South Works and Chrysler-Trenton: Prompt
assessment of site waste operations should be performed by
MDNR. Determination of any contaminant releases to ground-
water and/or surface water should be .
f) BASP/Wyandotte North Works, Monsanto Company, Huron Valley
Steel Corp and Jones Chemical; Prompt performance of a RCRA
Facility Assessment should be undertaken by the U.S.EPA,
utilising data generated by the UGLCC Study and other cur-
rent studies.
g) Edward C, Levy Co, Trenton Plant Plant #3; The U.S.EPA
should monitor the Consent Agreement and Final order signed
by the facility to ensure compliance. Data generated for
the UGLCC study should be used in the evaluation of the
recently performed RCRA Facility Assessment.
h) Pennwalt and Petrochemical Processing: Data generated for
the UGLCC Study should be used in the evaluation of the
recently performed RCRA Facility Assessment,
9, The integrity of the abandoned underground injection wells
at Pennwalt and BASF/Wyandotte should be evaluated through a
U.S.EPA inspection to determine if injection of spent waste
into caverns at Grease lie has led to releases.
10. Michigan and Ontario should develop a five year strategy
aimed at reducing spill occurrences and improving spill
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responses within their jurisdictions. Spill reports from
the Michigan Pollution Emergency Alerting System (PEAS), the
Ontario Spills Action Centre (SAC) and other agencies should
be enhanced to provide accurate information on spill volume
and composition, recovery and resolution. Facilities which
experience frequent spills should be required to develop
stricter spill management plans. Michigan and Ontario
should prepare a yearly spill report for public release and
for submission to the IJC, to stimulate interaction and
follow-up, and to ensure appropriate enforcement and preven-
tive measures,
11. Use of phosphorus and nitrogen fertilizers on agricultural
lands and handling of livestock manure in both Ontario and
Michigan need to be conservatively managed. Federal, state
and provincial environmental and agricultural agencies need
to collaborate to develop a comprehensive soil and water
management system to reduce impacts on ecosystem quality
from these activities. Education on, the proper use and
application of fertilizers should be provided to farmers,
and measures, such as conservation tillage and proper live-
stock waste management, should be encouraged to ensure mini-
mal loss of phosphorus, nitrogen and other associated chemi-
cals from agricultural lands.
12. The extent of required dredging and remediation of sediments
in the Detroit River and its tributaries should be planned
and prioritized. To do this, estimations of the volume of
sediments required to be removed should be , and an
overall plan for handling these materials should be develop-
ed. Financial requirements for such plans should be ana-
lyzed, and incorporated into future agency commitments,
C, Surveys, Research and Development
13. Tributaries to the Detroit River were found to provide major
loadings of several contaminants, particularly metals and
total phosphorus (not all UGLCC Study parameters were ana-
lyzed) , A thorough investigation of the Rouge, Little,
Canard and Ecorse Rivers, Turkey and Monguagon Creeks, and
the Frank and Poet Drain, if not presently being performed,
should be undertaken. An inventory of all point source
dischargers to the tributaries, and an assessment of all
nonpoint contaminant inputs (urban and rural runoff, waste
sites/contaminated groundwater, spills, CSOs, etc.) should
be performed. Water, sediment and biota quality in these
tributaries should be determined for the full stretch of the
tributary. For tributaries where extensive investigation is
presently being undertaken, information provided by this
study should be used to supplement ongoing work.
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14. A study of the significance of atmospheric deposition of
contaminants as a contaminant input mechanism should be
undertaken, in conjunction with a survey and evaluation of
point sources of atmospheric emissions to the Great Lakes
basin.
15, Ambient water quality guidelines for total PAHs need to be
developed and adopted, along with guidelines for specific
PAH compounds (e.g., benzo[ajpyrene) known to be of impor-
tance. Further research on the effects of individual and
total PAHs in water on a variety of aquatic species is
needed for guideline development.
16. The importance of clams as a food source for wildlife and
waterfowl, and the effect of clam flesh contaminants on such
wildlife should be studied.
17. Consumption advisories for waterfowl and wildlife should be
developed as necessary by federal, state and provincial
public health agencies, for the protection of human con-
sumers of these animals.
18. Contaminant concentrations in other biota, such as muskrats
which are consumed by native populations, should be
determined, and the need for consumption advisories con-
sidered.
19. Studies to determine the cause/effect linkages of Detroit
River contaminants to waterfowl and fish need to be per-
formed .
20. Fish and wildlife habitats along the Detroit River should be
protected to the greatest extent possible. The extent of
filling or bulkheading of wetlands should be reduced. Reme-
dial plans should be developed for those habitats which are
severely impacted, and/or alternative habitats developed to
accommodate displaced wildlife.
21. Sediment bioassays should be used to make site-specific de-
terminations of sediment quality. Dischargers responsible
for contaminated sediments should be required to conduct
bioassays of these contaminated sediments to determine
possible impacts. The need for acute and chronic bioassays
on the effluent should be considered for all point source
discharges to the Detroit River.
22. Development of sediment criteria for organic contaminants
found in Detroit River sediments, specifically total phenols
and total PAHs, is needed to assess the level of sediment
contamination. The U.S.EPA is intending to develop such
criteria; such development should be expedited.
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575
23, A study of the significance and impact of urban runoff from
Michigan municipalities should be performed. The study
should be performed in a manner similar to that of the
Ontario study, for comparability purposes. Contingent on
the results, remedial and management action may be neces-
sary.
24. The role played by sinkholes and carbonate solution channels
on Point Hennepin in the transport of contaminants from
these disposal sites should be investigated.
D. Management Strategy for Remedial Programs
25, Further regulatory actions in this Area of Concern must be
co-ordinated among the various agencies and governments
responsible. They should also be developed utilizing a
long-term planning framework.
26. Regulatory actions must take multi-media and synergistic
concerns into account with regard to contaminant management.
The correction of long-term contamination requires that contamin-
ant sources be significantly controlled by requiring a reduction
in the use of hazardous materials, or by ceasing to use hazardous
materials altogether. However, limited control provided by regu-
lation over many of the sources of contamination prevents this
encompassing approach. Although regulations provide limited
control over permitted discharges of industrial process and cool-
ing water, minimum or no legal control over sources such as
stormwater, combined sewer overflows, tributary loadings, con-
taminated ground-water, atmospheric deposition, contaminated sedi-
ments, spills from vessels, "midnight dumpers", hidden outfalls
and others, is provided.
In the past, attempts to control most contaminants originating
from point sources have relied upon NPDES permits, certificates
of Approval, control orders, notices of noncompllance or court
orders, and have partially succeeded. For other chemicals,
elimination or restrictions on production, use or sales (e.g.,
PCBs, DDT) have been implemented. These control methods have
resulted in varying degrees of reduction of these chemicals in
the environment. Once persistent and bioaccumulative chemicals
are in the environment, options for control are limited to remed-
iation or isolation of the contaminated medium, and monitoring of
the environmental effects.
For the Detroit River and its tributaries, loading data dictate
that the highest priority for contaminant source control is the
direct regulation of point sources through NPDES permits and the
MISA program. More stringent and extensive effluent limits need
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576
to be placed upon those facilities impacting the Detroit River
system, to reduce the discharge of toxic chemicals, and should be
expressed in terms of both concentrations and mass loadings.
The second priority is urban combined sewer overflow (CSO) con-
trol, as CSOs discharge untreated industrial and sanitary waste
directly to sensitive areas of the river. Combined sewer systems
in the Detroit River area receiving industrial process wastewater
need to be controlled so that contaminants do not reach the river
untreated.
Containing, purging and treating contaminated groundwater before
discharge to the Detroit River or its tributaries is the third
priority. Groundwater contaminant loadings to the river were not
determined, but based on the number of Michigan contaminated
groundwater sites along the Detroit River and its tributaries,
Michigan is likely a major source of contaminants through ground-
water inputs. A plan must be developed to identify, isolate and
treat these contaminated groundwater discharges.
The fourth priority is identification and reduction of atmospher-
ic loadings of contaminants from all sources.
The remaining sources mentioned above (other than sediments) are
more difficult to control, since they are generally nonpoint in
origin, and are less amenable to immediate, regulatory control.
However, control of nonpoint sources of contaminants is an equal
priority.
The extent of contaminant transfer from sediments to the water
column and biota is unknown, since complex chemical, physical and
biological factors influence these interactions. However, ad-
verse impacts on biota have been shown. Remediation of contamin-
ated Detroit River sediments is a difficult task. Detroit River
depositional sediments have a pudding-like consistency and are
not amenable to burial or coverage. Solidification and chemical
treatment are also not practical alternatives for in-place sedi-
ment control. Although expensive and having the potential to
release contaminants to the environment during the process,
dredging of severely contaminated sediments may be the only
method to reduce sediment contaminant loadings to the water col-
umn and biota and to restore impaired use.s in the Detroit River.
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577
I. LONG TERM MONITORING
1. Purposes for Monitoring and Relation-ships Between UGLCCS and
Other Monitoring Programs,
The purposes for monitoring and surveillance are included under
Annex 11 of the GLWQA, and considerations are found in Chapter 7
of the Report of the Niagara River Toxics Committee (91) . The
focus of the UGLCC Study was to determine where problems in the
ecosystem exist and how to remedy the problem. Long term moni-
toring recommendations focus on trends in environmental quality
to assess the effectiveness of remedial actions. Monitoring
should be sufficient to 1) detect system-wide trends noted by the
UGLCCS, and 2} detect changes resulting from specific remedial
actions.
The Great Lakes International Surveillance Plan (GLISP) and the
Remedial Action Plans (RAPs) also contain plans for long term
monitoring. The GLISP for the Upper Great Lakes Connecting Chan-
nels is incomplete, pending results of the UGLCC Study. The
Detroit River RAP being developed jointly by Michigan and Ontario
will list impaired uses, sources of contaminants, specific
remedial actions, schedules for implementation, resources per-
mitted by Michigan and Ontario,'target cleanup levels and moni-
toring requirements. Results from this study will be incorpor-
ated into the RAP, and will influence state and provincial
Detroit River programs.
2. System. Monitoring for Contaminants
Water
The principal Detroit River contaminants indicate general trends,
exposure levels and contaminant impacts on biota. Parameters to
be monitored include PCBs, chlorobenzenes (HCB), PAHs, oil and
grease, total phenols, total volatiles, mercury, cadmium, chrom-
ium, cobalt, copper, iron, nickel, lead, zinc, total phosphorus,
ammonia, suspended solids and chlorides. Monitoring stations
should be located where elevated concentrations are known or
predicted, including downstream of the Detroit WWTP, and Rouge
River, Little River,- Turkey Creek, Canard River, Ecorse River and
within the Trenton Channel, sampling locations may include hori-
zontal and vertical distributions. Sampling frequency should
bracket contaminant variability and flow fluctuations.
A mass balance approach will help identify changes in the con-
taminant masses over time, and target future remedial actions.
It should be conducted about once every five years, assuming
remedial actions have been implemented. Locations to be measured
should include:
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578
1) Head, and mouth transects. The dissolved and particulate
fractions and quantity of suspended sediment flux should be
measured. Chemical water monitoring locations in the
Detroit River should be expanded as needed for conventional
pollutants, to isolate localized significant sources.
Metals and organic contaminants should be added to the list
of parameters measured, and appropriately low detection
levels should be used. Detroit River shorelines, beaches
and marinas should be monitored for evidence of human sani-
tary waste. The present human health sanitary waste in-
dicator is fecal coliform bacteria, but development of a
better indicator of human health wastes is needed.
2) Municipal and industrial point sources. Monitor frequently
enough to calculate accurate loadings from the major point
sources, including the Detroit WWTP, Wayne County-Wyandotte
WWTP, McLouth Steel, Rouge Steel, Ford Canada, General
Chemical, West Windsor WWTP, and Wickes Manufacturing,
3) Tributary monitoring efforts should focus on seasonal and
storm event loadings from the Ecorse, Rouge, Canard and
Little Rivers and Turkey Creek for dissolved and sediment
associated contaminants. Best management practices should
be initiated in the Detroit River tributary watersheds to
more effectively manage flow, contaminants and sediment
sources.
4} CSOs and urban runoff. Estimates of CSOs and contaminant
loadings from Detroit and Windsor urban runoff should be
repeated. Contaminant loadings should be estimated for the
Riverview and Trenton storm sewers. Sewer sediments should
be monitored to locate significant PCS sources to the
Detroit WWTP and CSOs. Track PCBs upstream within the
sewer system to isolate areas or facilities contributing
PCBs. Monitor outfalls and overflows to determine loading
reductions.
5} The quantity and quality of groundwater Inflow from waste
disposal sites adjacent to the Detroit River and its tribu-
taries should be determined. The well drilling initiated
during the UGLCCS should be expanded to determine the
amount and severity of contaminated groundwater entering
the Detroit River from identified CERCLA and 307 sites.
The study should be designed to measure contaminated
groundwater entering the river without requiring access to
the shoreline property. Studies should be initiated to
determine the types and amounts of materials disposed of in
the Point Hennepin and Fighting island sites, and their
effects on the Detroit River. Eliminate (excavate and/or
secure) the sources of ground and surface water contamin-
ation in these landfills.
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579
6) Studies indicate that bed load sediments carry contaminant
masses similar to other sources, and that mass flux should
be quantified. The quantity of contaminants being desorbed
from sediments should also be quantified.
7) Direct atmospheric deposition to the Detroit River is
minor, but deposition within the drainage basin could be an
important source of wet and dry contaminants, and estimates
should be made. Expand and enforce local air monitoring
efforts in the Detroit River watershed to isolate local
sources.
Sediments
Sediment monitoring should be conducted every five years in con-
junction with the biota survey to assess trends and movement of
contaminants within the river. Analyses should include bulk
chemistry for organic and inorganic contaminants and particle
size distribution. Particular attention should be given to PCBs,
PAHs, phenols, phthalates, oil and grease', and heavy metals.
Sediment stations at tributary mouths should be monitored for
organic and inorganic contaminants on a biannual basis if remed-
ial actions occur. A suite of bioassays should be performed in
conjunction with these chemical analyses to determine the impact
these sediments are having on Detroit River biota, A map of the
areal extent of Detroit River sediment contamination and one
characterizing areas that are or may be toxic to aquatic life
need to be developed. These maps will allow identification of
areas needing to be dredged.
Biota
Long term monitoring of contaminants in biota will track con-
taminants in representative organisms. Three programs already
exist in the Detroit River:
i) Sport fish monitoring
This program should focus on persistent, bioaccumulative chemi-
cals, such as PCBs, mercury and other contaminants (e.g. dioxins
and dibenzo£urans) known or suspected of being human health
hazards. Important sport species that have an extended river
residence time should be sampled. Monitoring should continue
beyond the point that action levels are met. Monitoring of
chemical contaminants in fish livers and recording of tumors and
other deformities should be done while making fish community and
chemical contaminant assessments. Studies to determine the
causes of tumors and reproductive problems need to be initiated
for the Detroit River.
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S80
11) Spottail shiner monitoring
This program is designed to Identify local sources of bioavail-
able contaminants. Where spottail shiners contained elevated
levels of contaminants, sources of the contaminants should be
identified. Spottails should also be used to demonstrate results
of remedial actions.
ill) Caged clams monitoring.
Caged clams should be used to monitor results of remedial ac-
tions. Clams may be located at tributary mouths and downstream
of suspected source areas. Repeated assays at the locations
should confirm the results, A series of caged fish or darns
should be placed along the Detroit River to identify inputs of
persistent, bioaccumulative contaminants.
iv) Benthie Macroinvertebrate Community
The Detroit liver benthic community should be quantitatively
assessed every five years to monitor results of remedial actions,
Sampling should be based on grid or sediment type patterns to be
consistent between years. Selected persistent compound levels in
benthic organisms should be monitored.
v) Waterfowl and Wildlife
Waterfowl and wildlife communities should be monitored for
lowered reproduction rates, tumors and other deformities. The
causes of any deformities or tumors need to be determined. Con-
taminant levels in flesh, livers, and/or young should be
determined,
vi} Ecological significance and interaction
Biological surveys should be designed within each tributary
watershed or ecoregion to determine if there are ecosystem prob-
lems. Biological monitoring should be performed to isolate prob-
lem areas within the ecoregion, and efforts should be focused
where problems have been identified. Studies should be designed
to determine fish and wildlife species composition, life history,
habitat requirements, movement, and spawning and nesting sites
for fish and wildlife in the Detroit River ecosystem, and inter-
actions and, interdependency among these communities should be
defined.
3, Habitat Monitoring
Habitat monitoring should detect and describe changes in the
Detroit River ecological characteristics through periodic analy-
sis of key ecosystem elements. The following items are recom-
mended:
-------
581
a) The abundance and distribution of Hexgtgenia should be
determined every five years. The U.S. Fish and wildlife
Service grid used during 1985 would be appropriate. Bulk
sediment chemistry, organic and inorganic contaminants,
particle size analyses and a suite of bioassays should be
conducted on samples taken concurrently with the Hexagenia
survey.
b) Quantification of the extent of Detroit River wetlands
should be conducted every five years, along with the Hexa-
genia survey. Aerial photography or remote sensing could
discern emergent and submergent macrophyte beds important
to larval fish and wildlife. Verification of aerial data
should be conducted by inspection of selected transects for
plant species identification and abundance. Changes in
wetlands should be correlated with water level fluctuations
and other natural documentable influences so that long term
alterations in wetlands can be tracked and causes iden-
tified.
4. Sources Monitoring for Results of Specific Remedial Actions
Remedial actions intended to reduce contaminants from point
sources require compliance monitoring. Attention must be given
to sampling schedules and analytical methods. Nearfield monitor-
ing should be conducted regularly to document contaminant reduc-
tions and recovery of impaired communities. Monitoring may be
required for a "long time" in a limited area, depending on impact
severity and degree of contaminant reduction that is achieved.
The following ten specific sources are recommended for contamin-
ant monitoring:
Detroit WWTP (PCBs, heavy metals, volatile organics,
phenols, ammonia, oil and grease, cyanide, total phosphorus)
Wayne County-wyandotte WWTP (PCBs, heavy metals, volatile
organics, ammonia, total phosphorus, total suspended solids,
fecal coliform bacteria)
City of Trenton WWTP (suspended solids, BOD, total phos-
phorus, dissolved oxygen)
West Windsor WWTP (total phosphorus)
McLouth Steel-Trenton (oil and grease, zinc, phenol, iron)
Great Lakes Steel-Ecorse Mill (oil and grease)
Ford Canada (phenols, heavy metals, PCBs)
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582
wick.es Manufacturing (chromium, nickel)
General Chemical (chloride, copper)
Rouge steel (heavy metals, PAHs, phenols, oil and grease)
-------
583
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Mechanical and Environmental Engineering, University of
California, Santa Barbara, CA.
61. Bedford, K.W. , C.M. LiMcki, G, Koltun R, Van Evra,
1987, The development testing of a stochastic/-
deterministic methodology for estimating resuspension
potential and risk,
62, Rafael, C.M, and Jaworski, E. 1976. Delays in the Combined
Dredges Spoil Dispersal Program of the Great Lakes, Coastal
Zone Management Journal 3(1): 91-96.'
63. Kizlauskas T. and Pranckevicius P.E. 1987, Sediments of the
Detroit River,
64. Kenaga, D, and Crum, J, 1987. Sediment PCS concentrations
Along the U.S. Shore of the Upper Detroit River, and
-------
589
Sediment and Water PCS concentrations in Two City of Detroit
Combined Sewers With Overflows to the Detroit River, July
and October 1986, and January 1987. Mich. Dep. Nat. Res.,
Surf. Water Qual. Div. Unpub. Report.
65. Oliver, E.G., and Bourbonniere, R.A. 1985. Chlorinated con-
taminants in surficial sediments of Lakes Huron, St. Clair
and Erie; implications regarding sources along the St. Clair
and Detroit Rivers. J.Great Lakes Res. 11(3);366-372.
66. Oliver, B.C. 1987. Partitioning relationships for chlor-
inated organics between water and particulates in the St.
Clair, Detroit and Niagara Rivers. In: QSAR in Environmen-
tal Toxicology - II, Kaiser, K.L.E, (ed), D, Reidel, Publ.
Co., Dordrecht, 251-260pp.
67. Platford, R.F., Maguire, R.J., Tkacz, R.J., Comba, M.E., and
Kaiser, K.L.E., 1985. Distribution of hydrocarbons and
chlorinated hydrocarbons in various phases of the Detroit
River. J. Great Lakes Res. 11:379-385.
68. Pugsley,C.W,, Herbert, P.D.N., Wood, G.W., Brotea, G., and
Obal, T.w. 1985, Distribution of contaminants in clams and
sediments from the Huron Erie corridor. I. PCB's and
octachlorostyrene. J. Great Lakes Res. 11(3): 275-289.
69. Maguire, R.J., TXacz, R.J., and Sartor, D.L. 1985. Butyltin
species and inorganic tin in water and sediments of the
Detroit and St. Clair Rivers. J. Great Lakes Res_._ 11:320-
327.
70. Lum, K.R., and Gammon, K.L. 1985. Geochemical availability
of some trace and major in surficial sediments of the
Detroit River and western Lake Erie. J.__G_reat_Lake Jles.
11:323-338.
71. Limno-Tech, Inc. 1985. Field Methodology and Results for
Detroit River, Michigan. Sediment sampling report for
USACE, Detroit District.
72. Holdrinet, F.R., Braun, H.E., Thomas, R.L., Kemp, A.L.W.,
and Jaquet, J.M. 1977. Organochlorine insecticides and
PCB's in sediments of Lake St. Clair (1970 and 1974) and
Lake Erie (1971). Sci. Total Environ. 8:205-227,
73. Fallon, M.E., and Horvath F., 1985. Preliminary Assessment
of the Contaminants in Soft sediments of the Detroit River.
J. Great Lakes Res. 11(3):373-378.
74. Oliver, B.G, and Pugsley, C.W. 1987. PCBs, HCB and DCS in
Detroit River Bottom Sediments. (unpublished).
-------
590
75. Harr.dy, Y. , and Post, L. 1985, Distribution of rr.ercury,
trace organics, and other heavy metals in Detroit River
sediments. J. Great Lakes Res. 11 (3):353-365.
76. Hart, V, 1987. Draft Rouge River Sediment Quality Staff
Report. Michigan Department of Natural Resources Surface
Water Quality Division Report.
77. U.S. Army Corps of Engineers, 1935. Tennessee-Tombigbee
Corridor Study, Main Report, Mobile District, Mobile, AL.
78. Giesy, J.P., R.L. Graney, J.L. Newsted. and C.J. Rosiu. 1987,
Toxicity of In-place Pollutants to Benthic Invertebrates,
Interim Report of U.S.EPA/LLRS, Grosse lie, MI. April 15,
1987. Michigan State University, East Lansing, Michigan.
79. Giffels, Black and Veatch, 1980. Quantity and Quality of
Combined Sewer Overflows Volume II Report. CS-8Q6, Final
Facilities Plan, Interim report, City of Detroit Water and
Sewage Department.
8Q. Marsalak, J. and Ng, H.Y.F.,1987. Contaminants in Urban
Runoff in the Upper Great Lakes Connecting Channels Area.
National Water Research Institute, River Research Branch.
CCIW, Burlington, Ontario. NWRI #87-112.
81. UGLCCS Waste Disposal Sites and Potential Groundwater
Contamination -Detroit River. Nonpoint Source Workgroup
Report, January 1988 (see volume III this report).
82. U.S. Geological Survey, 1987. Interim Report on Groundwater
Movement Near the Upper Great Lakes Connecting Channels,-
unpublished draft report, Lansing, Michigan, March 1987,
83. Mazola, A.J. 1969. Geology for land and groundwater
development in Wayne County, Michigan: Michigan Geological
Survey Investigation, No,3, 1984.
84. Intera Technologies Ltd., 1986. Detroit, St. Clair, St.
Marys Rivers Project Waste Site Ranking and Prioritization,
Ontario Ministry of the Environment, Sarnia, Ontario March,
1986.
85. Intera Technologies Ltd., 1986. Detroit, St. Clair, St.
Marys River Project Regional Characterization and Waste Site
Inventory, Volumes I and II, Ontario Ministry of the
Environment, Sarnia, Ontario, March 1986.
86. Edwardson D., Saada C., Pranckieviclus P.E., Cummings T.R.,
Gillespie J., Dumouchelle D., Humphrey S., Sherbin G.,
Shanahan M., Jackson D. 1988. Upper Great Lakes Connecting
Channels Study, Waste Disposal Sites and Potential Ground-
-------
591
water Contamination - Detroit River, in Nonpoint Source
Workgroup Report (see volume III this report).
87. Teasell, s. 1986, Environmental Data on Fighting Island,
Ontario, 1982 - 1984. Environmental Protection - Ontario
Region, Environment Canada, unpub, rep.
88, Ribo, J.M. , ZaruJt, B.M., Hunter, H., and Kaiser, K.L.E.,
1985, Microtox Toxicity Test Results for water Samples from
the Detroit River. J. Great Lakes Res. 11:297-304.
89. U.S. Army Corps of Engineers. 1982. Reconnaissance report
for flood, protection in the Ecorse Creek, drainage basin,
Wayne County, Michigan. Appendix D, Environmental Considera-
tion, Detroit District, Detroit, MI.
90. Fontaine, T.D. 1988. Modeling Workgroup Geographical
Synthesis Report. Upper Great Lakes Connecting Channels
Study (see volume III this report).
91. Report of the Niagara River Toxics Committee, 1984. N.Y.
State Dept Env, Cons., Env. Can., U.S.EPA, and Ont. Min.
Env. 63Op.
-------
APPENDIX 1
Lists of Committee, Workgroup, Task Force
and Area Synthesis Team Members
Upper Great Lakes Connecting Channels Study
1984 to 1988
-------
594
MANAGEMENT COMMITTEE
United States
Mrs. Carol Finch, Co-chair*
Great Lakes National Program
Office, U.S. Environmental
Protection Agency
Dr. Alfred M. Beeton**
NOAA-Great Lak.es Environmental
Research Laboratory
Mr. David Cowgill
North Central Division
U.S. Army Corps of Engineers
Mr. Richard Powers***
Surface Water Division
Michigan Department of
Natural Resources
Dr. Khalil Z. Atasi****
Detroit Water and Sewerage
Department
Mr. Larry Sisk
Pish and wildlife Enhancement
Region, 3, U.S. Fish and
Wildlife Service
Canada
Mr. Ron Shimizu, Co-chair
Great Lakes Environment Office
Environment Canada
Mr. Tony Wagner
Inland Waters, C&P Ontario
Region, Environment Canada
Mr. Fred Fleischer"*"
Water Resources Branch
Ontario Ministry of Environment
Mr. Douglas A. McTavish
London Regional office
Ontario Ministry of Environment
Mr, Ken Richards++
Intergovernmental Relations Office
Ontario Ministry of Environment
Mr. Kim shiJcaze
Environmental Protection, C&P
Ontario Region Environment Canada
Mr. Dave Egar
National Water Research Inst.
Environment Canada
George Ziegenhorn++-«-
Great Lakes National Program office - U.S.EPA
Technical Secretary to
the Management and Activities Integration committees
International^ Joint Commission (IJO
(Observer)
Frank J. Horvath
Michigan Department of Natural Resources
* * *
* * * *
Replaced Mr. Peter L. Wise
Replaced Dr. Eugene J. Aubert/
Dr. Brian J. Eadie
Replaced Mr. William D. Marks
Replaced Mr. Darrell G. Suhre and
Mr. James W. Ridgeway
+ Replaced Mr.
Schenk
++ Replaced Mr.
Moore
+++ Replaced Mr.
Burkhart
Carl F.
John
Lawrence
-------
595
ACTIVITIES INTEGRATION COMMITTEE
United States
Mr. Vacys J. Saulys, Co-chair
Great Lakes National Program
Office, U.S. Environmental
Protection Agency
Mr. Tom Edsall
Chairperson-Biota Workgroup
Great Lakes Fishery Laboratory
Dr. Thomas Fontaine
Chairperson-Modeling Workgroup
NOAA-Great Lakes Environmental
Research Laboratory
Mr. Paul Horvatin
Chairperson-Point Source
Workgroup, Great Lakes National
Program office, U.S. Environ-
mental Protection Agency
Mr. Richard Lundgren
Michigan Representative
Michigan Department of
Natural Resources
Canada
Mr. Daryl Cowell, Co-chair*
Great Lakes Environment Office
Environment Canada
Dr. Alfred S.Y. Chau
Chairperson-Data Quality
Management Workgroup, National
Water Res. Institute, Environment
Canada
Mr. Yousry Hamdy
Chairperson-Sediment Workgroup
Water Resources Branch
Ontario Ministry of Environment
Mr. Wayne Wager**
Detriot/St, Clair./St. Marys
Rivers Project
Ontario Ministry of Environment
Mr. Griff Sherbin
Chairperson-Nonpoint Source
Workgroup, Environmental
Protection (Ontario Region),
Environment Canada
Mr. Donald J. Williams
Chairperson-Water Quality Work-
group, Inland Waters, (Ontario
Region) Environment Canada
Scientific and Technical Co-ordinators
Mr. William Richardson
Large Lakes Research station
U.S. Environmental Protection
Agency
Dr. G. Keith Rodgers
National Water Research Inst.
Environment Canada
* Replaced Mr. Gregory Woodsworth
** Replaced Mr. John Moore
-------
596
BIOTA WORKGROUP
united States
Canada
Thomas A. Edsall, Chairperson
Great Lakes Fishery Laboratory
U.S. Fish and wildlife Service
David Kenaga
Water Quality Surveillance
Michigan Department of Natural
Resources
Thomas Nalepa
NOAA-Great Lakes Environmental
Research Laboratory
Peter B, Kauss
Water Resources Branch
Ontario Ministry of Environment
Joseph Leach
Lake Erie Fisheries station
Ontario Ministry of Natural
Resources
Mohinddin Munawar
Great Lakes Fisheries Research
Branch, Department of Fisheries
Oceans
Dr. G. Keith Rodgers
National Water Research Ins.
Environment Canada
Stewart Thornley
London Regional Office
Ontario Ministry of Environment
-------
597
DATA QUALITY MANAGEMENT WORKGROUP
United States Canada
James H. Adams, Jr. A.S.Y. Chau, Chairperson
Quality Assurance Office National Water Research Inst.
U.S. Environmental Protection Environment Canada
Agency
Warren R. Faust Peter Fowlie
NOAA-Great Lakes Environmental Waste Water Technology Centre
Research Laboratory Environmental Protection
Environment Canada
George Jackson Donald King
Environmental Services Division Laboratory Services Branch
Michigan Department of Natural Ontario Ministry of Environment
Resources
James J. Lichtenberg
Environmental Monitoring and Support
Lab, U.S. Environmental Protection
Agency
Michael Mullin
Large Lakes Research Station
U.S. Environmental Protection
Agency
Godfrey Ross
Analytical Laboratory
Detroit Water and Sewerage
Department
CONSULTANTS
Jerry Zar Keijo I. Aspila
Biology Department National Water Institute
Northern Illinois University Environment Canada
Abdel El'Shaarawi
National Water Research Inst.
Environment Canada
-------
598
POINT SOURCE WORKGROUP
United states
Canada
Paul Horvatin, chairperson
Great Lakes National Program
Office, U.S. Environmental
Protection Agency
Khalil Z. Atasi
Detroit Water and Sewerage
Department
Richard Lundgren
Surface Water Quality Division
Michigan Department of Natural
Resources
William Stone
Surface Water Quality Division
Michigan Department of Natural
Resources
James Young
Surface Water Quality Division
Michigan Department of Natural
Resources
Dean C. Edwardson
Detroit/St. Clair/St. Marys
Rivers Project
Ontario Ministry of Environment
Lawrence King
Environmental Protection
(Ontario Region)
Environment Canada
-------
599
NQNPOINf SOURCE
United States
Canada
Prank Belobraidich
Ground Water Quality Division
Michigan Department of Natural
Resources
James H, Bredin
Michigan Department of Natural
Resources
Ralph Christensen
Great Lakes National Program
Agency, U.S. Environmental
Protection Agency
T. Ray eumrnings
U.S. Geological Survey
Thomas Davenport
Planning and Standards Section
Water Quality Division
U.S. Environmental Protection Agency
T.J. Millar
East Lansing Field Office
U.S. Fish and Wildlife Service
Pranas Pratickevicius
Great Lakes National Program Office
U.S. Environmental Protection Agency
Griff Sherbin, Chairperson
Environmental Protection
(Ontario Region)
Environment Canada
Dean C, Edwardson
Detroit/St, Clair/St. Marys
Rivers Project
Ontario Ministry of Environment
Greg Wall
Land Resource Research Inst.
Agriculture Canada
-------
600
WORKGROUP
United States
Canada
Thomas Fontaine, Chairperson
NQAA-Great Lakes Environmental
Research Laboratory
Khalil Z. Atasi
Detroit Water and Sewerage
Department
William L. Richardson
Large Lakes Research Station
U.S. Environmental Protection
Agency
Jeff weiser
Detroit District, U.S.
Army Corps of Engineers
Richard Hobrla (Observer}
SWQ/WQSC, Michigan Department
of Natural Resources
Paul Rodgers (Observer)
Ann Arbor, Michigan office
Limno-Tech Inc,
Dave Dolan
Great Lakes Regional Office
International Joint commission
Efraim Halfon
National Water Research Inst.
Environment Canada
John A. McCorquodale
Great Lakes Institute
University of Windsor
Peter Nettleton
Water Resources Branch
Ontario Ministry of Environment
-------
601
SEDIMENT WORKGROUP'
United States Canada
David C. Cowgill Yousry Hamdy, Chairperson
North Central Division Water Resources Branch
U.S. Army Corps of Engineers Ontario Ministry of Environment
Nathan Hawley Barry Oliver
NOAA-Great Lakes Environmental National Water Research Inst.
Research Laboratory Environment Canada
Robert Hessleberg Ian Orchard
Great Lakes Fisheries Lab Environmental Protection
U.S. Fish and Wildlife Service (Ontario Region)
Environment Canada
Anthony Kizlauskas
Great Lakes National Program Office
U.S. Environmental Protection Agency
John Robbing
NOAA-Great Lakes Environmental
Research Laboratory
-------
602
WATER QUALITY
United States
Canada
Khalil 2. Atasi
Detroit Water and Sewerage
Department
Paul Bertram
Great Lakes National Program.
Office, U,S. Environmental
Protection Agency
Peter Landrum
NCAA-Great Lakes Environmental
Research Laboratory
Richard Lundgren
Surface Water Quality Division
Michigan Department of Natural
Resources
Michael Mullin fPro Tern)
Large Lakes Research Station
U.S. Environmental Protection
Agency
Donald Williams, Chairperson
Inland Waters
(Ontario Region)
Environment Canada
Klaus Kaiser
National Water Research Inat,
Environment Canada
Peter B. Kauss
Water Resources Branch
Ontario Ministry of Environment
Prank J. Horvath
Michigan Department of Natural
Resources
Trefor B, Reynoldson
Great Lakes Regional Office
International Joint Coronission
-------
603
LONG TERM MONITORING WORKGROUP
United States Canada
Paul Bertram, Co-chairperson Peter Nettleton, Co-chairperson
Great Lakes National Program Water Resources Branch
Office, U.S. Environmental Ontario Ministry of Environment
Protection Agency
Frank j. Horvath
Michigan Department of Natural
Resources
-------
604
REGULATORY
United States
Canada
Cynthia Puller*
Great Lakes National Program
Office, U.S. Environmental
Protection Agency
Frank Baldwin
Michigan Department of Natural
Resources
Susan Humphrey*
Environmental Protection
(Ontario Region)
Environment Canada
Ray E, Bowen
Southwest Region
Ontario Ministry of Environment
CO-QRDINATQRS
Paul Horvatin
Great Lakes National Program
Office, U.S. Environmental
Protection Agency
Griff Sherbin
Environmental Protection
(Ontario Region)
Environment Canada
* Replaced Larry Fink
* Replaced Mary Shanahan
-------
605
AREA SYNTHESIS TEAM MEMBERS
United States Canada
ST. MARYS RIVER
Diana Klemans Yousry Hamdy
Michigan Department of Natural Water Resources Branch, Ontario
Resources Ministry of Environment
ST. CLAIR RIVER++
Pranas Pranckevicius* Griff Sherbin
Great Lakes National Program Environmental Protection
Office, U.S. Environmental Environment Canada
Protection Agency
LAKE ST. CLAIR
Paul Bertram Paul Hamblin*
Great Lakes National Program National Water Research Inst.
Office, U.S. Environmental Environment Canada
Protection Agency
DETROIT RIVER
David Kenaga Klaus Kaiser
Water Quality Surveillance National Water Research Inst.
Section, Michigan Department Environment Canada
of Natural Resources
* Replaced Larry Fink * Replaced G. Keith Rodgers
++ St. Clair River (level 3) geographic report was written by
B. G. Oliver and W. R. Swain, Eco Logic Inc.
-------
APPENDIX II
GLOSSARY AND UNITS OF MEASURE
-------
608
MEASUREMENTS & UNITS
mg/L
ug/L
ng/L
pg/L
ug/g
mg/kg
ug/kg
ng/kg
L/d
m3/d
mgd
cfs
m3/s
kg/d
Ibs/d
kg/yr
t/yr
uS/cm
milligram per liter = part per million (ppm) *
luicrogram per liter = part per billion (ppb) *
nanogram per liter = part per trillion (ppt)*
(one trillenth part of a gram)
picograms per litre = part per quadrillion (ppq)
microgram per gram = part per million (ppm)
milligram per kilogram = part per million (ppm)
microgram per kilogram = part per billion (ppb)
nanogram per kilogram = part per trillion (ppt)
liter per day
cubic meters per day
millions of gallons per day
cubic feet per second
cubic meters per second
kilograms per day
pounds per day
kilograms per year
tonnes per year
microsiemens per centimeter (conductivity)
-------
609
EQUIVALENT UNITS
meter » m
kilometer = km
gram = g
tonne = t
liter = L
(Can.)
1m
1 km
1000 g =
It
1 L ~
3.281 feet
0,621 miles
1 kg * 2.205 pounds
2,205 pounds
0,2642 gal (U.S.) = 0.2200 gal
To Convert
acres
acres
centimeters
centimeters
feet
gallons (Imp.)
gallons (U.S.)
gallons (U.S.)
gallons (Imp.)
grams
grams
grams
hectares
inches
kilograms
kilograms
kilograms
kilometers
kilometers
kilometers
Multiply By
4.047 x 10"1
4,047 x 103
3.937 x 10"1
1,094 x 1G~2
3.048 x 10
-1
1.20095
8.3267 x ID'1
3.785
4.542
1.0 x 1Q~"3
3.527 x 10~2
2.205 x 103
2.471
2,540
1.0 x 103
2.2046
3.5274 X 101
6.214 x 1Q~1
1.0936 x 103
3.2808 x 103
To Obtain
hectares
sq. meters
inches
yards
meters
gallons (U.S.)
gallons (Imp,)
liters
liters
kilograms
ounces
pounds
acres
centimeters
grams
pounds
ounces
miles
yards
feet
-------
610
To Convert
liters
(U.S.liquid)
liters
meters
meters
meters
miles
milligrams/liter
ounces
ounces (fluid)
parts/million
gal,
pounds - -
pounds
square
square
square
square
square
square
feet
inches
kilometers
kilometers
kilometers
meters
temperature °C
temperature °P
yards
yards
yards
Multiply By
2.642 x 1Q-1
2,201 x ID-1
3.281
6.214 x 1CT4
1.094
1,609
1.0
2.8349 x 101
2.957 x 1Q~2
8.354
"4.535i x 102
4,536 x 1Q-1
9.29 x 10~2
6,452 x 1Q2
2,471 x 102
1,076 x 107
3.861 x 10"1
2.471 x 1Q~4
(°C x 9/53+32
(°F-32) x 5/9
9,144 x 101
9,144 x W~4
9.144 x 1Q-1
To Obtain
gallons
gallons (Imp)
feet
miles
yards
Jcilometers
parts/million
grams
liters
pounds/million
grams
kilograms
sq. meters
sq millimeters
acres
sq. ft,
sq, miles
acres
temperature °P
temperature °C
centimeters
kilometers
meters
-------
611
ACRONYMS
ADI Acceptable Daily Intake: The dose that is
anticipated to be without risk to humans when taken
daily. It is not assumed that .this dose guarantees
absolute safety. The determination of the ADI is
often based on the application of laboratory animal
toxicity data concerning chronic (long-term) doses to
the environmental doses to which humans are exposed.
AOCjs) Areas of Concern: Geographic locations recognized by
the International Joint Commission where water,
sediment or fish quality are degraded, and the
objectives of the Great Lakes Water Quality Agreement
of local environmental standards are not being
achieved.
Bag Benzo-a-Pyrene
BAT Best Available Technology/Treatment
BATEA Best Available Technology/Treatment Economically
Achievable
BCF Bioconcentration Factor; the ratio of the
concentration of a particular substance in an
organism to concentration in water.
BCT Best Conventional Technology, •
BEJ Best Engineering Judgement.
BHC Benzene Hexachloride or Hexachlorocyclohexane. There
are three isomers; alpha, beta, and gamma. Gamma-BHC
is the insecticide lindane.
BOD Biochemical Oxygen Demand: The amount of dissolved
oxygen consumed during the decomposition of organic
nutrients in water during a controlled period and
temperature.
COA Canada-Ontario Agreement Respecting Water Quality in
the Great Lakes.
COP Chemical Oxygen Demand: The amount of oxygen
required to oxidize completely by chemical reagents
the oxidizable compounds in an environmental sample.
CofA Certificate of Approval
-------
612
CSO
DCB
ODD
DDE
DDT
DPQ
DQA
DOE/EC
EC-50
GLISP
HCBD
HCE
IJC
Combined sewer Overflow,' combined storm and sanitary
sewer systems.
Diehlorobenzene
A natural breakdown product of DDT.
Dichlorodiphenyldichloroethylene. A natural
breakdown product DDT.
Dichlorodiphenyltrichloroethane: A widely used, very
persistent chlorinated pesticide (now banned from
production and use in many countries)«
Department of Fisheries and Oceans (Canada)
Department of Agriculture (Canada)
Department of Environment/Environment Canada
Effective concentration of a substance producing a
defined response in 50% of a test population. The
higher the EC-50, the less effective the substance is
because it requires more material to elicit the
desired response.
Environmental Protection, Ontario Region, Environment
Canada
United States Environmental Protection Agency
Great Lakes International Surveillance Plan. It
provides monitoring and surveillance guidance to U.S.
and Canadian agencies responsible for implementing
the provisions of the GLWQA that include general
surveillance and research needs as well as monitoring
for results of remedial actions.
Great Lakes Water Quality Agreement
Hexachlorobenzene
Hexachlorobutadiene
Hexachloroethane
International Joint Commission; A binational
organization established in 1909 by the Boundary
Waters Treaty, Through the IJC, Canada and the
United States cooperatively resolve problems along
their common border, including water and air
pollution, lake levels, power generation and other
issues of mutual concern.
-------
613
MDHR
MIS A
NGAA
NPDES
NTU
OCS
OMNR
OMOE
PAH
PBB
PCB
Lethal concentration (by volume) of a toxicant or
effluent which is lethal to 50% of the test organism
over a specified time period. The higher the LCsp,.
the less toxic it is becauee it takes more toxicant
to elicit the response.
Lethal dose which is lethal to 50% of the test
organism over a specified time period. The higher
the L-DSQ, the less toxic it is because it takes more
toxicant to elicit the response.
Michigan Department of Natural Resources
Municipal-Industrial Strategy for Abatement: The
principal goal of this program is the virtual
elimination of toxics discharged from point sources
to surface waters in Ontario.
National Oceanic and Atmospheric Administration
National Pollutant Discharge Elimination System,' a
permit system limiting municipal and industrial
discharges, administered by O.S.EPA and the states,
Nephelometric Turbidity Unit
Octachlorostyrene
Ontario Ministry of Natural Resources
Ontario Ministry of the Environment/Environment
Ontario
Polynuclear Aromatic Hydrocarbons, also known as
Polycyclic Aromatic Hydrocarbons or Polyaromatic
Hydrocarbons. Aromatic Hydrocarbons composed of at
least 2 fused benzene rings, many of which are
potential or suspected carcinogens.
Polybromated biphenyl; used primarily as a fire
retardant.
Polychlorlnated biphenyls,- a class of persistent
organic chemicals with a potential to bioaccumulate
and suspected carcinogens; a family of chemically
inert compounds, having the properties of low
flammability and volatility and high electric
insulation quality. Past applications include use as
hydraulic fluids, heat exchange and dielectric
fluids,' plastisizers for plastics.
-------
614
QCB
POTW
PTS
RAP
SPDES
STP
TCB
TCDD
TCDF
TOTAL DDT
UGLCCS
U.S.EPA
WHO
WPCP
WTP
WWTP
The negative power to the base 10 of the hydrogen ion
concentration. A measure of acidity or alkalinity of
water on a scale from 0 to 14; 7 is neutral; low
numbers indicate acidic conditions, high numbers,
alkaline.
Pentachlorobenzene
Publicly Owned Treatment Works
Persistent Toxic Substance: Any toxic substance with
a half-life in water o£ greater than eight weeks.
Remedial Action Plan: This is a plan to be developed
with citizen involvement to restore and protect water
quality at each of the 42 Areas of concern in the
Great Lakes Basin. The RAP will identify impaired
uses, sources of contaminants, desired use goals,
target clean-up levels, specific remedial options,
schedules for implementation, resource commitments by
Michigan and Ontario as well as by the federal
governments, municipalities and industries, and
monitoring requirements to assess the effectiveness
of the remedial options implemented.
State Pollutant Discharge Elimination System; a state
administered permit limiting municipal and industrial
dischargers.
Sewage Treatment Plant
Trichlorobenzene
Tetrachlorodiebenzo-p~dioxins
Tetrachlorodibenzofurans
Sum of DDT isomers and metabolites
Upper Great Lakes Connecting Channels Study
United States Environmental Protection Agency
World Health Organization
Water Pollution Control Plant
Water Treatment Plant (for drinking water)
Waste Water Treatment Plan
-------
ABSORPTION
ACCLIMATION
615
TERMINOLOGY
Penetration of one substance into the body of
another.
Physiological and behavioural adjustments of an
organism in response to a change in environment.
See also Adaptation.
ACCLIMATIZATION Acclimation of a particular species over several
generations in response to marked environmental
changes.
ACCUMULATION Storage and concentration of a chemical in tissue
to an amount higher than intake of the chemical.
May also apply to the storage and concentration of
a chemical in aquatic sediments to levels above
those that are present in the water column.
ACUTE Involving a stimulus severe enough to rapidly
induce a response; in bioassay tests, a response
observed within 96 hours is typically considered
an acute one.
ACUTE TOXICITY Mortality that is produced within a short period
of time, usually 24 to 96 hours.
ADAPTATION
ADSORPTION
AEROBIC
ALGA(E)
ALGICIDE
ALKALINITY
AMBIENT
AMBIENT WATER
Change in the structure forms or habits of an
organism to better fit changed or existing
environmental conditions. See also Acclimation.
The taking up of one substance at the surface of
another.
The condition associated with the presence of free
oxygen in the environment.
Simple one celled or many celled micro-organisms,
usually free floating, capable of carrying on
photosynthesis in aquatic ecosystems.
A specific chemical highly toxic to algae.
Algicides are often applied to water to control
nuisance algal blooms.
A measurement of acid neutralization or buffering
capability of a solution (See pH).
An encompassing atmosphere.
The water column or surface water as opposed to
groundwaters or sediments.
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616
AMPULES A sealed glass container of a know concentration
of a substance,
ANADRQMOUS Species which migrate from salt water to fresh
water to breed.
ANAEROBE An organism for whose life processes a complete or
nearly complete absence of oxygen is essential.
ANOXIA The absence of oxygen necessary for sustaining
most life. In aquatic ecosystems this refers to
the absence of dissolved, oxygen in water.
ANTAGONISM Reduction of the effect of one substance because
of the introduction or presence of another
substance; e.g. one substance may hinder, or
counteract, the toxic influence of another. See
also Synergism.
APPLICATION FACTOR A factor applied to a short-term or acute
toxicity test to estimate a concentration of waste
that would be safe in a receiving water.
AQUATIC Living in water.
ASSIMILATION The absorption, transfer and incorporation of
substances (e.g. nutrients by an organism or
ecosystem).
ASSIMILATIVE CAPACITY The ability of a waterbody to transform
and/or incorporate substances (e.g. nutrients) by
the ecosystem, such that the water quality does
not degrade below a predetermined level.
BEMTHig Of or living on or in the bottom of a water body,*
benthic region, benthos.
BEKTHOS Bottom dwelling organisms, the benthos comprise:
1) sessile animals such as sponges, of the
worms and many attached algae,' 2) creeping forms
such as snails and flatworms, and 3) burrowing
forms which include most clams and worms, mayflies
and midges.
BIOACCUMULATION Uptake and retention of environmental substances
by an organism from both its environment (i.e.
directly from the water) and' its food,
BIOASSAY A determination of the concentration or dose of a
given material necessary to affect a test organism
under stated conditions.
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617
BIOCONCENTRATION The ability of an organism to concentrate
substances within its body at concentrations
greater than in its surrounding environment or
food.
BIOCONCENTRATION FACTOR The ratio of the measured residue within
an organism compared to the residue of the
substance in the ambient air, water or soil
environment of the organism.
BIOLOGICAL MAGNIFICATION The concentration of a chemical up the
food chain.
BIOMASS Total dry weight of all organisms in a given area
or volume.
BIOMONITORING The use of organisms to test the toxic effects of
substances in effluent discharges as well as the
chronic toxicity of low level pollutants in the
ambient aquatic environment.
BIOTA
CARCINOGEN
CHIRONOMID
CHRONIC
Species of all the plants and animals occurring
within a certain area or region.
Cancer causing chemicals or substances.
Any of a family of midges that lack piercing mouth
parts.
Involving a stimulus that lingers or continues for
a long period of time, often one/tenth of the life
span or more.
CHRONIC TOXICITY Toxicity marked by a long duration, that
produces an adverse effect on organisms. The end
result of chronic toxicity can be death although
the usual effects are sublethal; e.g. inhibits
reproduction or growth. These effects are
reflected by changes in the productivity and
population structure of the community. See also
Acute Toxicity.
COMMUNITY
CONGENER
Group of populations of plants and animals in a
given place; ecological unit used in a broad sense
to include groups of various sizes and degrees of
integration.
A member of the same taxonomic genus as another
plant or animal: Also a different configuration
or mixture of a specific chemical usually having
radical groups attached in numerous potential
locations.
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CONTAMINANT
CONTAMINATION
618
A substance foreign to a natural system or present
at unnatural concentrations.
The introduction of pathogenic or undesirable
micro-organisms, toxic and other deleterious
substances which renders potable water, air,
soils, or biota unfit for use.
CONTROL ORDER/REQUIREMENT AND DIRECTION ORDER
in Ontario.
Enforceable orders
CONVENTIONAL POLLUTANT A term which includes nutrients,
substances which pollutant consume oxygen upon
decomposition, materials which produce an oily
sludge deposit, and bacteria. Conventional
pollutants include phosphorous, nitrogen, chemical
oxygen demand, biochemical oxygen demand, oil and
grease, volatile solids, and' total and fecal
coliforni, chlorides, etc.
CRITERIA
Numerical limits of pollutants established to
protect specific water uses.
CRITERION, WATER QUALITY A designated concentration of a
constituent based on scientific judgments, that,
when not exceeded will protect an organism, a
community of organisms, or a prescribed water use
with an adequate degree of safety.
CRITICAL LEVEL See Threshold.
CRITICAL.JRANGS In bioassays the range of magnitude of any factor
between the maximum level of concentration at
which no organisms responds (frequently mortality)
to the minimum level or concentration at which all
organisms respond under a given set of conditions.
CUMULATIVE
Brought about or increased in strength by
successive additions.
CUMULATIVE ACTION increasingly severe effects due to either
storage or concentration of a substance within the
organism.
DENSITY
DETRITUS
DIATOM
Number of individuals in relation to the space.
A product of disintegration, defecation,
destruction, or wearing away.
Any of a class of minute planktonic unicellular or
colonial algae with silicified skeletons.
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619
DIPXIN A group of approximately 75 chemicals of the
chlorinated dibenzodioxin family, including 2, 3,
1, 8 - tetrachlorodibenzo-para-dioxin (2,3,7,8 -
TCDD) which is generally considered the most toxic
form.
DISSOLVED OXYGEN The amount of oxygen dissolved in water.
DRAINAGE BASIN A waterway and the land area drained by it,
DREDGE SPOILS The material removed from the river, lake, or
harbour bottom during dredging operations.
DREDGING GUIDELINES Procedural directions designed to minimize
the adverse effects of shoreline and underwater
excavation with primary emphasis on the
concentrations of toxic materials within the
dredge spoils.
The interacting complex of living organisms and
their non-living environment; the biotic community
and its abiotic environment.
Contaminated waters discharged from facilities to
either wastewater sewers or to surface waters.
All the biotic and abiotic factors that actually
affect an individual organism at any point in its
life cycle,
A plant that grows, flowers, and dies in a few
days.
Invertebrates (mayflies) that live as adults only
a very short time.
The warm, upper layer of water in a lake that
occurs during summer stratification.
The wearing away and transportation of soils,
rocks and dissolved minerals from the land
surface, shorelines, or river bottom by rainfall,
running water, wave and current action.
EUTROPHICATION The process of nutrient enrichment that causes
high productivity and biomass in an aquatic
ecosystem. Eutrophication can be a natural
process so it can be a cultural process
accelerated by an increase of nutrient loading to
a waterbody by human activity.
ECOSYSTEM
EFFLUENT
ENVIRONMENT
EPHEMERAL
EPHEMERA
EPILIMNION
EROSION
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620
EXOTIC _SPECIES Species that are not native to the Great LaK.es
and have been intentionally or inadvertently
introduced into the system.
FACULTATIVE
FOODCHAIN
GOAL
Exhibiting a broad lifestyle which allows it to
survive under a broad range of environmental
conditions.
The process by which organisms in higher trophic
levels gain energy by consuming organisms at lower
trophic levels; the dependence for food of
organisms upon others in a series, beginning with
plants and ending with the largest carnivores.
An aim or objective towards which to strive; it
may represent an ideal condition that is
difficult, if not impossible to attain
economically.
GREAT LAKES BASIN ECOSYSTEM The interacting components of air,
land, water and living organisms, including man,
within the drainage basin of the St. Lawrence
River at or upstream from the point at which this
river becomes the international boundary between
Canada and the United States (from Article 1 of
the 1978 GLWQ Agreement).
GREATLAKES WATER QUALITY AGREEMENT (GLWQA) A joint agreement
between Canada and the United States which commits
the two countries to develop and implement a plan
to restore and maintain the many desirable uses of
the waters in the Great Lakes Basin. Originally
signed in 1978, the Agreement was amended in 1987.
GROUNDWATER
GUIDELINES
HALF-LIFE
Water entrained and flowing below the surface
which may supply water to wells and springs.
Any suggestion or rule that guides or directs;
i.e. suggested criteria for programs or effluent
limitations.
The period of time in which a substance loses half
of its active characteristics (used specifically
in radiological work); the amount of time
required for the concentration of a pollutant to
decrease to half of the original value through
natural decay or decomposition.
HAZARDOUS SUBSTANCES Chemicals considered to be a threat to man
in the environment, including substances which
(individually or in combination with other
substances) can cause death, disease (including
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621
cancer), behavioural abnormalities, genetic
mutations, physiological malfunctions or physical
deformities,
HYDROLOG1C__CYCLE The natural cycle of water on earth, including
precipitation as rain and snow, runoff from land,
storage in groundwaters, lakes, streams, and
oceans, and evaporation and transpiration (from
plants) into the atmosphere to complete the cycle.
HYPOLIMNION
ICHTHYOLOGY
The cold, dense, lower layer of water in a lake
that occurs during summer stratification,
A branch of zoology that deals with fishes.
INCIPIENT LC^n The level of the toxicant which is lethal for 50%
of individuals exposed for periods sufficiently
long that acute lethal action has ceased.
Synonymous with lethal threshold concentration.
INCIPIENT LETHAL LEVEL That concentration of a contaminant
beyond which an organism could no longer survive
for an indefinite period of time.
INSECTICIDE
LACUSTRINE
LEACHATE
LETHAL
LIPOPHILIC
LITTORAL
LOADINGS
MACROPHYTE
Substances or a mixture of substances intended to
prevent, destroy or repel insects.
Formed in, or growing in lakes.
Materials dissolved or suspended in water that
percolate through solids such as soils, solid
wastes and rock, layers.
Involving a stimulus or effect directly causing
death.
Having an affinity for fats or other lipids.
Productive shallow water zone of lakes, rivers or
the seas, with light penetration to the bottom;
often occupied by rooted aquatic plants.
Total mass of pollutant to a water body over a
specified time; e.g. tonnes per year of
phosphorus,
A member of the macroscopic plant life (i.e.
larger than algae) especially of a body of water.
MACR0200BENTHOS The distribution of macrozoobenthos in an
aquatic ecosystem is often used as an index of the
impacts of contamination on the system.
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MALIGNANT
MASS BALANCE
622
Resistant to treatment, occurring in severe form
and frequently fatal.
An approach to evaluating the sources, transport
and fate of contaminants entering a water system,
as well as their effects on water quality. In a
mass balance budget, the amounts of a contaminant
entering the system less the amount leaving the
system. If inputs exceed outputs, pollutants are
accumulating and contaminant levels are rising.
Once a mass balance budget has been established
for a pollutant of concern, the long-term effects
on water quality can be simulated by mathematical
modelling and priorities can be set for research
and remedial action.
Any substance or effect which alters genetic
characteristics or produces an inheritable change
in the genetic material,
The ability of a substance to induce a detectable
change in genetic material which can be
transmitted to progeny, or from one cell
generation to another within an individual.
NONPOINT SOURCE Source of pollution in which pollutants are
discharged over a widespread area or from a number
of small inputs rather than from distinct,
identifiable sources.
MUTAGEN
MUTAGENICITY
NUTRIENT
A chemical that is an essential raw material for
the growth and development of organisms.
QRGANOCHLORINE Chlorinated hydrocarbon pesticides.
PATHOGEN
PERIPHYTON
A disease causing agent such as bacteria, viruses,
and parasites.
Organisms that live attached to underwater
surfaces.
PERSISTENT TOXIC SUBSTANCES Any toxic substance with a half-life
in water and greater than eight weeks.
PESTICIDE
PHENOLICS
Any substance used to kill plants, insects, algae,
fungi or other organisms; includes herbicides,
insecticides, algicides, fungicides.
Any of a number of compounds with the basic
structure of phenol but with substitutions made
onto this structure, Phenolics are produced
during the coking of coal, the distillation of
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623
wood, the operation of gas works and oil
refineries, from human and animal wastes, and the
microbiological decomposition of organic matter.
PHOTOSYNTHESIS A process occurring in the cells of green plants
and some micro-organisms in which solar energy is
transformed into stored chemical energy.
PHYTOPHAGOUS Feeding on plants.
PHYTOPLANKTON Minute, microscopic aquatic .vegetative life; plant
portion of the plankton; the plant community in
marine and freshwater situations which floats free
in the water and contains many species of algae
and diatoms.
POINT,SOURCE A source of pollution that is distinct and
identifiable, such as an outfall pipe from an
industrial plant.
POLLUTION (WATER) Anything causing or inducing objectionable
conditions in any watercourse and affecting
adversely the environment and use or uses to which
the water thereof may be put.
POTABLE WATER Water suitable, on the basis of both health and
aesthetic considerations, for drinking or cooking
purposes.
PRECAMBRIAN
The earliest era of geological history.
PRIMARY,TREATMENT Mechanical removal of floating or settable
solids from wastewater.
PUBLIC Any person, group, or organization.
RADIQNUCLIDE A radioactive material.
RAPTORS
RAW WATER
RESUSPENSION
RIPARIAN
Birds of prey.
Surface or groundwater that is available as a
source of drinking water, but has not received any
treatment,
(of sediment} The remixing of sediment particles
and pollutants back into the water by storms,
currents, organisms and human activities such as
dredging.
Living or located on the bank of a natural
watercourse.
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624
SCAUP
A diving duck.
SECONDARY TREATMENT Primary treatment plus bacterial action to
remove organic parts of the waste.
SEDIMENT
SEICHE
SELENIUM
SESSILE
The fines or soils on the bottom of the river or
lake.
An oscillation in water level from one end of a
lake to another due to wind or atmospheric
pressure. Most dramatic after an intense but
local weather disturbance passes over one end of a
large lake.
A nonmetalllc element that chemically resembles
sulfur and is obtained chiefly as a by-product in
copper refining, and occurs In allotropic forms of
which a gray stable form varies in electrical
conductivity with the intensity of its
illumination and is used In electronic devices.
An animal that is attached to an object or is
fixed in place (e.g. barnacles).
SIGMOID CUR¥E S-shaped curve (e.g. the logistic curve)
SLUDGE
SOLUBILITY
STABILITY
The solids removed from waste treatment
facilities.
Capability of being dissolved.
Absence of fluctuations in populations; ability to
withstand perturbations without large changes in
composition.
STRATIFICATION {or layering) The tendency in deep lakes for
distinct layers of water to form as a result of
vertical change in temperature and therefore, in
the density of water.
SUBACUTE
8UBCHRQNIC
SUB-LETHAL
Involving a stimulus below the level that causes
death.
Effects from short-term multiple dosage or
exposure; usually means exposure for less than
three months.
Involving a stimulus below the level that causes
death.
SUSPENDED SEDIMENTS Particulate matter suspended in water.
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SYNERGISM
SYNERGISTIC
SYNTHESIS
TAXA
625
The joint action of two or more substances is
greater than the sum of the .action of each of the
individual substances. The improvement in
performance is achieved because two agents are
working together. See also Antagonism.
Interactions of two or more substances or
organisms producing a result such that the total
effect is greater than the sum of the individual
effects.
The production of a substance by the union of
elements or simpler compounds.
A group of similar organisms.
TAXONOHICALLY To identify an organism by its structure.
TERATOGEN A substance that increases the incidence of birth
defects,
TERATOGENICITY The ability of a substance to produce
irreversible birth defects, or anatomical or
functional disorders as a result of an effect on
the developing embryo.
THERMOCLINE
THRESHOLD
A layer of water in lakes separating cool
hypolimnion (lower layer) from the warm epilimnion
{surface layer).
The chemical concentration or dose that must be
reached before a given reaction occurs.
TOXIC, SUBSTANCE As defined in the Great Lakes Agreement, and
substance that adversely affects the health or
well being of any living organism.
TOXICITY Quality, state or degree of the harmful effect
resulting from alteration of an environmental
factor.
TRANSLOCATION Movement of chemicals within a plant or animal;
usually refers to systemic herbicides and
insecticides that are moved from the point of
contact on the plant to other regions of the
plant.
TROPHIC ACCUMULATION Passing of a substance through a food chain
such that each organism retains all or a portion
of the amount in its food and eventually acquires
a higher concentration in its flesh than in its
food. See also Biological Magnification.
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626
TROPHIC LEVEL Functional classification of organisms in a
community according to feeding relationships; the
first trophic level includes green plants, the
second level includes herbivores; etc.
TROPHIC STATUS A measure of the biological productivity in a
body of water. Aquatic ecosystems are
characterized as oligotrophic (low productivity),
mesotrophic (medium productivity) or eutrophic
(high productivity),
TUBIFICID
TURBIDITY
Of aquatic oligochaete or sludge worms which is
tolerant to organically enriched waters.
Deficient in clarity of water.
WATER QUALITY OBJECTIVES Under the Great Lakes Water Quality
Agreement, goals set by the Governments of the
United States Agreement, goals set by the
Governments of the United States and Canada for
protection of the uses of the Great Lakes.
WATER QUALITY STANDARD A criterion or objective for a specific
water use standard that is incorporated into
enforceable regulations.
WIND SET-UP
A local rise in water levels caused by winds
pushing water to one side of a lake. (See seiche)
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