EPA-905/9-74-011-A
VOLUME 1
m
US WV1ROHMBITAL PROTHTOH ACDKY
REGION V BffOKBMBff ENVISION
GREAT LAKES MIIAIIVE OOHTRAa PROGRAM
OCTOBER, 1974
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WATER POLLUTION INVESTIGATION: CALUMET AREA
OF LAKE MICHIGAN
VOLUME 1
by
Richard H. Snow
IIT RESEARCH INSTITUTE
In fulfillment of
EPA Contract No. 68-01-1576
for the
U.S. ENVIRONMENTAL PROTECTION AGENCY
Region V
Great Lakes Initiative Contract Program
Report Number: EPA-905/9-74-011-A
EPA Project Officer: Howard Zar
October 1974
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This report has been developed under auspices of the Great
Lakes Initiative Contract Program. The purpose of the
Program is to obtain additional data regarding the present
nature and trends in water quality, aquatic life, and waste
loadings in areas of the Great Lakes with the worst water
pollution problems. The data thus obtained is being used
to assist in the development of waste discharge permits
under provisions of the Federal Water Pollution Control
Act Amendments of 1972 and in meeting commitments under
the Great Lakes Water Quality Agreement between the U.S.
and Canada for accelerated effort to abate and control
water pollution in the Great Lakes.
This report has been reviewed by the Enforcement Division,
Region V, Environmental Protection Agency and approved
for publication. Approval does not signify that the contents
necessarily reflect the views of the Environmental Protection
Agency, nor does mention of trade names or commercial products
constitute endorsement or recommendation for use.
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BIBLIOGRAPHIC DATA
SHEET
1. Report No.
EPA-905/9-74-011-A
3-NUec ipient's Accession No.
.. Title and Subtitle
Water Pollution Investigation: Calumet Area of Lake Michigan
Volume 1
5. Report Date
October 1974
6.
Author(s)
Richard H. Snow
8. Performing Organization Rept.
No.
9. Performing Organization Name and Address
IIT Research Institute
10 West 35th Street
Chicago, Illinois 60616
10. Protect ''Task/Work Unit No.
11. Contract 'Grant No.
68-01-1576
12. Sponsoring Organization Name and Address
J.S. Environmental Protection Agency
Enforcement Division, Region V
230 S. Dearborn Street
Chicago, Illinois 60604
13. Type ot Report £ Period
Covered
Final Report
14.
15. Supplementary Notes
EPA Project Officer: Howard Zar
16. Abstracts An investi gation of the Calumet area of Lake Michigan was conducted. The ob-
jective was to determine trends in water quality, to determine effluent loads entering
the Lake, and to predict reductions in effluents needed to achieve Lake water quality
standards. The report describes the status of industrial and municipal effluent sources
Effluent data were compiled from NPDES permit applications and operating reports. These
were checked by a field sampling program.
Water quality data were compiled from several sources. We also conducted field
measurements in the Indiana Harbor Canal (IHC) and at 16 Lake stations. We located the
plume from the IHC by aerial observation and by measurements using existing pollutants
as tracers. Current meters installed in the Lake for one month allowed us to describe
the mechanisms that appear to govern dispersion of the IHC plume. The report contains
chapters assessing the impact of each of the more important pollutants, and gives rec-
ommendations for reduction of some effluent loads. Appendices are included on the
biological impact of pollutants on the Calumet area of Lake Michigan.
17. Key Words and Document Analysis. 17a. Descriptors
Water Quality Aquatic Biology, Water Pollution
17b. Identifiers/Open-Ended Terms
Calumet Area, Indiana Harbor Canal, Lake Michigan, Great Lakes,
Chemical Parameters, Biological Parameters
17c. COSATI Field/Group ] 33
18. Availability Statement
19. Security Class (This
Report)
UNCLASSIFIED
20. Security Class (This
Page
UNCLASSIFIED
21. No. of Pages
22. Price
FORM NTIS-35 (REV. 3-72)
THIS FORM MAY BE REPRODUCED
USCOMM-DC '.4952-P72
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TABLE OF CONTENTS
VOLUME 1
PAGE
1. Introduction, Summary and Reconunendatiorts 1
2. Description of Area and Watershed 6
3. Flow Data of Tributary Streams 11
4. Industrial Waste Sources, Outfalls and Effluent Data 24
5. Municipal Sources and Combined Sewer Overflows 44
6. Water Quality Data 46
7. Sediment Pollution and Benthic Organisms 57
8. Impact of Pollutants on Quality and Use of Water 65
9. Biological Indicators of Water Quality 74
10. Lake Currents 79
11. IITRI Field Sampling Program and Data 86
12. Dispersion of Effluents from Indiana Harbor Canal (IHC) 127
13. Ammonia-Nitrogen 149
14. Phenols 183
15. Oil and Grease 199
16. Bacterial Pollution 205
17. Phosphorus 222
18. Chloride and Sulfate 253
References 293
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TABLE OF CONTENTS (cont.)
VOLUME 2 (APPENDICES)
Appendix A - A Review of Selected Research on the Biology
and Sediments of Southern Lake Michigan with Particular
Reference to the Calumet Area
Appendix B - The Ecology of Lake Michigan Zooplankton - A
Review with Special Emphasis on the Calumet Area
Appendix C - Description of Industrial Effluent Sources and
Comparison of Effluent Data
Appendix D - Municipal Sources and Combined Sewer Overflows
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'TABLE OF CONTENTS
Page
Abstract ' ill
Acknowledgments xv
1. INTRODUCTION, SUMMARY AND RECOMMENDATIONS 1
1.1 Introduction 1
1. 2 Summary 1
1.3 Recommendations 4
2. DESCRIPTION OF AREA AND WATERSHED 6
3. FLOW DATA OF TRIBUTARY STREAMS 11
3.1 Flow Data 11
3.2 Conclusions 19
3.3 Other Stream Flows 21
4. INDUSTRIAL WASTE SOURCES, OUTFALLS AND EFFLUENT DATA . 24
4.1 Description . 24
4.2 Identification of Outfalls 25
4.3 Effluent Loads Other Than via IHC 30
4.4 Effluent Loads to Lake Michigan via IHC 30
4.5 Conclusions and Recommendations 40
5. MUNICIPAL SOURCES AND COMBINED SEWER OVERFLOWS .... 44
6. WATER QUALITY DATA 46
6.1 Availability of Data 46
6.2 U.S. EPA - Generated Data 46
6.3 Indiana Water Quality Data 49
6.4 The Metropolitan Sanitary District of Greater
Chicago 52
6.5 Chicago City Raw Water Data 52
6.6 State of Illinois Data 53
6.7 Additional Data Sources Surveyed 55
IV
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TABLE OF CONTENTS (cont. )
10
I
SEDIMENT POLLUTION AND BENTHIC ORGANISMS
7.1 Transport of Sediments in IHC
7.2 Composition of Suspended Solids and Sediments
from IHC
7 . 3 Relation to Dredging •
7.4 Lake Michigan Sediments and Relation to
Pollution
7.5 Sediment Pollution from IHC and Other Sources . .
IMPACT OF POLLUTANTS ON QUALITY AND USE OF WATER . . .
8.1 Water Pollution Problems
8.2 Phosphorus Pollution
8.3 Bacterial Pollution
8.4 Safety of Water Supplies
8.5 Chemical Pollution
8.6 Oxygen Depletion
8.7 Thermal Pollution
BIOLOGICAL INDICATORS OF WATER QUALITY
9.1 Phytoplankton
9 . 2 Zooplankton
9.2.1 Lake-Wide Effects
9.2.2 Calumet Area
LAKE CURRENTS
10.1 Thermal Structure
10.2 Causes of Lake Currents
10 . 3 Current Data and Trends
10.4 Summary of Currents .....
10.5 Diffusion Coefficients
10.6 Current Measurements During This Program
'age
57
57
58 *
*
60
62
63
65
66
67
68
68
69
70
72
74
74
76
76
77
79
79
80
81
82
83
83
v
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, TABLE OF CONTENTS (cont.)
Page
11. IITRI FIELD SAMPLING PROGRAM AND DATA 86
11.1 Objectives and General Plan 86
11.2 Water Sampling and Boat Measurements ...... 88
11.2.1 Location of Sampling , . . . 88
11.2.2 On-Board Instrumentation . 93
11.2.3 Shore Sample Treatment 93
11.2.4 Analytical Methods 93
11.3 Chemical Results 96
11.4 Aerial Observations I . .. . . .. \i .- . 96
11.5 Flow Measurements . . . . . ... ;.-'.. j . .: ,• , 116
11.6 Lake Current Measurements : . . . .'.•„ 117
12. DISPERSION OF 'EFFLUENTS FROM INDIANA HARBOR CANAL
(IHC). .'....- ! . ... 127
12.1 Behavior of IHC Plume ......... ;: ... 128
12.2 Estuary Mixing at Canal Mouth .' . . . ' . .' . . . 130
12.3 Gravity Spreading Mechanism . : . . . . ''! . . . 132
12.4 Behavior of Plume in Lake Just Outside IHC;•'::-.? •
Mouth 136
12.5 Rate of Gravity Spreading in Lake . . , . ... . 139
12.6 Measured Dilutions . , ,. 142
12.7 Interpretation of Dilutions in Terms of:•_•
Dispersion Mechanisms. 143
13. AMMONIA-NITROGEN . .' 149
13.1 Water Quality Standards -..".. .... 149
13.2 Background NH3-N Concentrations '..''."' 151
13.3 Water Quality Data ............... 152
13.4 Behavior of IHC Plume . . . . . . V . .' . .' . l. 160
13.5 IHC As an Ammonia Source ........ 161
13.6 Other Ammonia Sources .... / ..;.-.;:. . . .. 168
13.7 Required Reductions in NH3-W from IHC 170
13.8 Recommended Implementation of Reductions . . , . 171
VI
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TABLE OF CONTENTS (cont.)
Page
14. PHENOLS 183
14.1 Water Quality Standards 183
14.2 Phenol Sources 183
14.3 Water Quality Data 185
14.4 Effluent Loads 190
14.5 Conclusions and Recommendations 190
15. OIL AND GREASE 199
16. BACTERIAL POLLUTION 205
16.1 Introduction and Summary 205
16.2 Water Quality Standards 205
16.3 Water Quality and Violation of Standards in
Lake Michigan 206
16.4 Sources of Bacterial Pollution 209
16.5 Combined Sewer Overflows 217
16.6 Conclusions 218
17. PHOSPHORUS 222
17.1 Introduction 222
17.2 Effluent and Water Quality Standards 223
17.3 Water Quality and Violations of Standards in
Lake Michigan 223
17.4 Background Phosphorus Values 227
17.5 Sources of Phosphorus 233
17.6 Effect of Bottom Stirring on Phosphorus
Concentrations 237
17.7 Recent Phosphorus Trends and Models 245
17.8 Conclusions and Recommendations 246
18. CHLORIDE AND SULFATE 253
18.1 Introduction 253
18.2 Water Quality Standards 253
18.3 Water Quality Data 254
18.3.1 Chloride 254
18.3.2 Sulfate 257
Vll
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TABLE OF CONTENTS (cont.)
Page
18.4 Effluents from IHC 258
18.5 Water Quality Violations 262
18.6 Sources of Effluents 262
18.7 Lake Michigan Water and Chloride Model 271
REFERENCES 293
VOLUME 2
Appendix A - A Review of Selected Research on the Biology
and Sediments of Southern Lake Michigan with Particular
Reference to the Calumet Area
Appendix B - The Ecology of Lake Michigan Zooplankton - A
Review with Special Emphasis on the Calumet Area
Appendix C - Description of Industrial Effluent Sources and
Comparison of Effluent Data
Appendix D - Municipal Sources and Combined Sewer Overflows
Vlll
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LIST OF TABLES
Table
3.1 Calumet Area Surveillance Stream Flow Data ....
3.2 Velocity and Flow Survey of October 1-4, 1973 . .
3.3 Summary of Flow Data IHC and Grand Calumet River .
3.4 Selected Low Flow and Other Data for -Stream
Gaging Stations 23
4.1 Listing of Industrial Effluent Sources in
Calumet Area 28
4.2 Effluent Concentrations and Loads from Industries
in Calumet Area Draining into Lake Michigan
Directly or via Little Calumet River and Burns
Ditch 31
4.3 Location and Description of Discharges to Grand
Calumet River and IHC 35
4.4 Measured Effluent Concentrations and Load per Day
in Indiana Harbor Canal at Columbus Drive Bridge
(Station IHC3S) 41
4.5 Measured Effluent Concentrations and Calculated
Loads at Mouth of Indiana Harbor Canal
(Station CAL06) 42
6.1 U.S. EPA Water Quality Monitoring Stations in
Calumet Area 48
6.2 Indiana Water Quality Monitoring Stations .... 51
6.3 Listing of Data Sources Surveyed 56
7.1 Composition of Sediments Dredged from Indiana
Harbor 59
8.1 Summary of Water Quality Measurements Station 6
Indiana Harbor at East Breakwall Inner Light ... 71
10.1 Current Meter Measurements at 68th St. Crib
(CAL17) 85
11.1 Water Sampling Stations - Calumet Area 91
11.2 Analytical Methods for General Analysis of
Water Samples 94
11.3 Water Quality Data in IHC and Calumet Area of
Lake Michigan Measurements from IITRI Field
Sampling Program 97
IX
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LIST OF TABLES (cont.)
Table Page
12.1 Measured Flows at Mouth of IHC - llTRI Data. . . . 131
12.2 Current Meter Measurements at Mouth of IHC
(CAL06) ". 133
12.3 Gravity Flow at IHC Mouth (CAL06). ... r .... 134
13.1 Ammonia-Nitrogen in Lake Michigan, IITRI
Measurements 154
13.2 In-Stream Water Quality, 1973 162
13.3 Ammonia-Nitrogen, mg/£ 163
13.4 Summary of Existing Ammonia Effluent Loads to IHC. 165
13.5 Inventory of NH3-N Discharges to IHC 166
14.1 Phenol, yg/£ 186
14.2 In-Stream Water Quality 187
14.3 Discharges of Phenol into the IHC 191
15.1 Oil and Grease, mg/£ 201
15.2 Summary of Effluent Loads, IHC 201
16.1 Water Quality Standards Fecal Coliform (MPN or
MF/100 mil 207
16.2 Bacteria Counts at Hammond and Whiting Beaches
in 1972 211
16.3 In-Stream Water Quality - Fecal Coliform, 1973 . . 214
16.4 Water Quality Measurements Near Municipal Sewage
Treatment Plants 216
17.1 Water Quality Standards, Phosphorus, Total ..... 225
17.2 Total Phosphorus Loading to Lake Michigan 234
Tributary Contributions 234
17.3 Estimated Phosphorus Sources for Lake Michigan . . 235
17.4 In-Stream Water Quality, 1973 239
17.5 Phosphorus Discharges to IHC 240
17.6 Phosphorus Concentrations, Chicago South Works
Filtration Plant, November - December, 1973, and
and Parameters Indicating Correlation with
Bottom Stirring 242
x
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LIST OF TABLES (cont.)
Table Page
18.1 Water Quality in IHC and Grand Calumet River . . . 261
18.2 Inventory of Chloride Discharges on IHC and
Tributaries 264
18.3 Inventory of Sulfate Discharges on IHC and
Tributaries 266
18.4 Chloride Model for Lake Michigan 275
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LIST OF FIGURES
Figure
2.1
2.2
3.1
3.2
3.3
4.1
Calumet Area of Lake Michigan Basin Showing
Stream Flow Directions
Drainage Basin of Calumet Area Tributary Streams
Grand Calumet River Inflow Investigation ....
Flow Survey of October 1-4, 1973
Flow Measurements Hear Burns Harbor, Indiana . .
Location Map Showing Major Industrial and
Municipal Plants
Page
7
10
12
18
22
26
6.1 Location Map EPA Water Quality Sampling Stations
CAL01-CAL17 47
6.2 Indiana Water Quality Monitoring Stations in
Calumet Area 50
6.3 South Water Filtration Plant Radial Survey .... 54
11.1 Detailed Map of Stations for IITRI Field Sampling. 89
11.2 Map of Stations for IITRI Field Sampling 90
11.3 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, November 12 and 13, 1973 . 105
11.4 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, November 14, 1973 .... 106
11.5 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, November 16, 1973 .... 107
11.6 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, November 17, 1973 .... 108
11.7 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, November 18, 1973 .... 109
11.8 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, November 19, 1973 .... 110
11.9 Sketch Showing Visual Appearance of Effluents
by ..erial Observations, November 29, 1973 .... Ill
11.10 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, November 30, 1973 .... 112
11.11 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, December 7, 1973 113
11.12 Sketch Showing Visual Appearance of Effluents
by Aerial Observations, December 8, 1973 114
11.13 Steady-State Calibration Curve for Modified Meter. 118
XII
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LIST OF FIGURES (cont.)
Figure Page
11.14 Current Meter Records at 68th St. Crib Showing
Current Direction, Wind Direction from National
Weather Service, Temperature of Water, and
Current Speed 120
11.15 Current Meter Records off Inland Steel Landfill,
Showing Current Direction, Wind Direction at
Hammond Water Laboratory, and Current Speed . . . 123
12.1 Schematic Representation of Salinity Intrusions
in Estuaries 130
12.2 Cross-Flow of Lake Current and Gravity Spreading
of Plume 138
12.3 Spread Diagram 141
12.4 Nonviscous Spread Diagram 141
12.5 Dilution of IHC Effluent at Lake Michigan Stations
Based on Water Quality Measurements by IITRI,
November 14, 1973 144
12.6 Dilution of IHC Effluent at Lake Michigan Stations
Based on Water Quality Measurements by IITRI,
November 19, 1973 145
12.7 Dilution of IHC Effluent at Lake Michigan Stations
Based on Water Quality Measurements by IITRI,
December 7, 1973 146
13.1 Ammonia-Nitrogen Annual Average and Maximum, mg/£. 153
13.2 Skylab Photo Showing Plumes from IHC and
Calumet River 156
13.3 Radial Survey of Ammonia Nitrogen Concentration,
1971 157
13.4 Radial Survey of Ammonia Nitrogen Concentration,
1972 158
13.5 Radial Survey of Ammonia Nitrogen Concentration,
1970 159
13.6 Annual Average Ammonia Nitrogen Weekly
Sanitary Surveys 164
13.7- Storet Water Quality Plot 174
13.17
14.1 Annual Average Phenol Weekly Sanitary Surveys . . 184
14.2 Phenol Annual Average and Maximum, yg/& 188
14.3 Radial Survey of Phenol Concentration, 1972 ... 189
14.4- Storet Water Quality Plot 193
14.9
Xlll
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LIST OF FIGURES (cont.)
Figure
Pa
15.1- Storet Water Quality Plot. . ..... ...... 202
15.6 .
16.1 Fecal Coliform Annual Average and Maximum,
No./lOO mi .................... 208
16.2 Hammond and Whiting Beach Sampling Stations
Showing Location of Three Combined Sewer
Outfalls .............. . . ,, . . • • • 210
16.1 Annual Average Coliform Organisms per 100 m£
Weekly Sanitary Surveys ...... ....... 213
16.4- Storet Water Quality Plot ....... ..... 220
16.5
17 .1 Phosphorus Annual Average and Maximum, ppm .... 226
17.2 Radial Survey of Total Phosphorus Concentration,
1970 .............. ......... 228
17.3 Radial Survey, of Total Phosphorus 'Concentration,
1971 ............. .......... 229
17.4 Radial Survey of Total Phosphorus Concentration,
1972 ............ ... • • • ..... 230
17.5 Total Phosphorus Concentration, 1956-1973 ..... 231
17.6 Annual Average Phosphorus Concentration in
Indiana Harbor Canal at Dickey Road . . . ... . . 238
17.7- Storet Water Quality Plot ..... ., -. . . . . . 249
17.12
18.1 100 Year Record of Chloride and Sulfate Increase
at Dunne Crib - 68th St ......*.. ..... 255
18.2 Changes in Concentrations of Dissolved 'Chloride
Sulfate, Calcium and TDS in Lake Michigan .... 256
18.3 Annual Average Sulfate Concentration in Indiana
Harbor Canal at Dickey Road ..... ....... 259
18. '4 Annual Average Chloride Concentration iii Indiana
Harbor Canal at Dickey Road . . . ; . j • t, . - „ . . 260
18.5 Radial Survey of Total Chloride, 1971 . ..... 268
18.6 Radial Survey of Total Chloride, 1970 ...... 269
18.7 Radial Survey of Total Chloride, 1972 ....... 270
18.8 Lake Michigan Modelled as a Stirred Tank to
Determine Chloride Build-up ........... 272
18.9- Storet Water Quality Plot. . ........... 277
18.29
xiv
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ACKNOWLEDGMENTS
IITRI personnel who contributed to this project are Ernest ;
Dunwoody, Nagaraja Rao, Gayle Marks, Carl Swanstrom, Dr. Walter
Wnek, and Henry Duncan. The project manager was Dr. Richard Snow.
Edward Fochtman and Dr. Morton Klein provided consultation and »
supervision.
This report contains contributions from a subcontractor,
Citizens for a Better Environment. Dennis Adamczyk prepared a
draft of Chapter 4 and Appendix C. Dan Sweeney prepared a draft
of Chapter 5.
Argonne National Laboratory provided a boat and crew for
field sampling, installed current meters and processed the current
data by computer. Sam Zivi, Dr. John Tokar, and Dr. Anthony
Policastro contributed to planning of the field measurements and
.discussed dispersion of the IHC plume. John Frye, Larry Van Loon
and Conrad Tome participated in the field measurements.
Two biologist consultants provided advice on biological
aspects and contributed to the report. Appendix A was written
by Dr. Richard Howmiller, University of California at Santa
Barbara. Appendix B was written by Dr. John Gannon, University
of Michigan Douglas Lake Biological Station, Pellston, Michigan.
The Hammond Water Dept. very kindly provided the use of their
laboratory for preparation of water samples. Mr. A. G. Gianinni
and Emmett Sutliff were very helpful. The following other water
departments allowed us to take raw water samples and to inspect
their water analyses: Chicago South Water Filtration Plant,
Morris Kaplan; Whiting Water Plant, Albert Odlivak; East Chicago
Water Plant, Mr. Kowal; Hobart Water Co. (Gary, Indiana), Keith
Young.
*
In addition, the Chicago Water Dept. provided copies of
their reports, access to data in their library, and help in
xv
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finding data. Those who helped include Commissioner Richard
pavia, Philip Reed, Barbara Fox, Mr. Davoust and Mr. MacDougal.
The project was monitored for EPA by Howard Zar. He and
Gary Milburn provided continuing aid concerning sources of
information and advice on planning and carrying out the work.
We thank all of the above individuals and organizations for
their contributions to the project.
xvi
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EFFLUENTS AHD WATER QUALITY IN THE CALUMET AREA
OF LAKE IOCHIQAN
I. INTRODUCTION. SUMMARY AND RECOMMENDATIONS
1.1 Introduction
An investigation of the Calumet area of Lake Michigan was
conducted for the U.S. Environmental Protection Agency. The area
extends from the 68th St. crib of the Chicago Water Dept. to
Burns Ditch in Indiana. The objective was to determine trends in
water quality in this part of the Lake and its tributary rivers,
to determine the loads of effluents entering the Lake from indus-
trial and municipal sources, and to relate the impact of effluents
on water quality so as to predict reductions in effluents needed
to achieve water quality standards in the Lake. The information
will be used by the EPA as a guide to setting effluent limitations,
1.2 Summary
The main source of effluents in the area is the Indiana
Harbor Canal (IHC), which carries effluents from the major steel
millsN refineries, and municipal sewage treatment plants into the
Lake. Effluent data were compiled from NPDES effluent permit
applications, and these were checked against monthly operating
data submitted by the industry to Indiana, and against effluent
24-hr sample data. A separate study on effluents, water quality,
and load allocations in the Grand Calumet River/IHC system was
done for the Indiana Stream Pollution Control Board by Combina-
torics (1974). We have made use of much of the data compiled by
Combinatorics (1974).
The permit data were found to be reasonably valid, but we
checked the data further by a field sampling program. A program
of field measurements was undertaken in November and December
1973, to fill gaps in the available data. Although the data
available from other agencies were extensive, the observations
did not locate the plume of effluents from the IHC with relation
to the sampling stations. Furthermore, the flow of the IHC and
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rthe effluent loads were not measured on the same days as the Lake
sampling. Our objective was to relate water quality measurements
to effluent loads, and to movement and dispersion of the IHC
effluents in the Lake, so that we could establish the sources of
pollution and the magnitude of their effects on the Lake.
To accomplish this, we sampled the IHC and measured its flow
at two points. This allowed us to check the reported effluent
loads, and we found that the measured values were on the high
side of the reported range for most pollutants. We analyzed the
samples for the following parameters: temperature, pH, dissolved
oxygen, chloride, conductivity, turbidity, fluoride, ammonia-
nitrogen, total phosphorus, total coliform bacteria, total organic
carbon, total solids, suspended solids, chlorophyll, volatile
solids, total iron and dissolved iron.
Our sampling in the Lake was accompanied by observation and
measurement of the water movement in the Lake, We found that the
plume from the IHC was visible because of its purplish-brown
color, so we chartered an airplane and observed and photographed
the plume on sampling days. We also subcontracted with Argonne
National Laboratory to install current meters in the Lake off the
mouth of the IHC and near the 68th St. crib. A month-long record
from these meters showed that the Lake currents flowed in a
northerly direction along the shore about half the time, in a
southerly direction along the shore nearly half the time, and on
a few occasions it flowed out toward the middle of the Lake. Our
observations allowed us to postulate mechanisms governing the
'flow and dispersion of the plume in the Lake, and to calculate
dilution ratios.
Argonne also provided a boat for sampling the Lake at 16
stations. This Lake sampling was done on three days, November 14,
November 19, and December 7, 1973. To obtain more continuity of
data, we also obtained samples from raw water intakes of five
municipal water treatment plants: the Chicago 68th St. crib, and
the intakes of Hammond, Whiting, East Chicago, and Gary, Indiana.
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I "I
We found that the plume could readily be followed both by
Visual observation and by plotting a combination of the following
pollutants which acted as tracers, and provided a signature to
positively identify the IHC effluents: total iron, conductivity,
ammonia-nitrogen, coliform bacteria, chloride, pH, temperature
and fluoride. Concentrations exceeding water quality standards
were measured as far as five miles from shore, particularly for
ammonia-nitrogen and bacteria. High chlorophyll measurements
.showed that the IHC effluent has a nutrient effect on algal growth.
This report contains an assessment of the previously avail-
able data, a description of our field sampling program, and
chapters assessing the impact of each of the more important
pollutants. The most noticeable and harmful pollutants are
ammonia-nitrogen and phosphorus. Ammonia-nitrogen can be toxic
to fish. Phosphorus, and to a secondary extent nitrogen, promote
eutrophication of near-shore waters, and result in extensive
growths of algae that clog water intake screens and form unpleasant
conditions on local bathing beaches; however, phosphorus effluents
from IHC have decreased 40% during the past four years, due to
improved treatment by Indiana municipalities and due to a phos-
phorus limitation on detergents in Indiana. An increasing trend
of phosphorus at the 68th St. crib was apparent for 15 years,
but there has been a 20% decrease in the last two years.
Other pollutants are suspended iron, which causes a colored
plume. Oil and phenol from steel mills and refineries cause
unpleasant tastes in local water supplies, and require extensive
.use of carbon for municipal water treatment. Oil causes surface
slicks that dirty pleasure boats. This oil and other organic
pollutants shift aquatic life towards species that usually live
in polluted waters.
Bacterial pollution from the IHC remains very high, and
beaches in the Calumet area are still closed for this reason.
Delays in municipal treatment construction and diversion of
industrial effluents to the municipal plants is causing these
difficulties.
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Although the IHC is the largest source of pollutants in the
Calumet area, not all of the pollution in the Lake can be traced
to it. Some of the phosphorus and ammonia-nitrogen pollution in
the near-shore waters could come from more distant sources,
1.3 Recommendations
The following recommendations are abstracted from specific
chapters in the report.
We recommend that industries discharging wastes to municipal
sewers be required to pretreat their wastes so as not to overload
the East Chicago, Gary, and Hammond sewage treatment plants.
The pretreatment should include provisions to prevent peak loads
from entering the plants and causing upsets. An alternative
solution would provide for increased capacity and additional
processes at the municipal plants to handle the industrial wastes,
with a sewerage charge to pay the costs. This should be under-
taken only if it is shown to be more cost effective, and if it
will not cause delay over the pretreatment approach.
We recommend that plans to solve problems of combined sewer
overflows and storm water overflows be implemented as soon as
possible. The municipalities have plans to construct detention
lagoons and increase the capacity of sewers and treatment plants.
Until these facilities are constructed, bathing beaches and water
intakes in the Calumet area will continue to be polluted.
Plans to increase capacity of overloaded municipal treatment
plants and to add AWT should be implemented as soon as possible.
,Funding of these construction plans should be given a higher
priority. This applies to the smaller plants in the eastern
Calumet region, as well as to East Chicago, Gary and Hammond.
We irecommend that some of the industrial and municipal
i
effluent load allocations be lowered to allow water quality
standards to be met in Lake Michigan, as well as in the Grand
Calumet River/IHC system. We recommend a reduction of a factor
of 7.7 in present loadings of ammonia-nitrogen. These
-------
Deductions should be accomplished in such a way as to prevent the
^resent harmful effects on ammonia on the operation of municipal
sewage treatment plants. Phenol load allocations should be
reduced to reflect the present improved phenol levels, to prevent
degradation of phenol levels back to earlier conditions. We
recommend that either the oil loads, or the BOD5 allocations be
reduced as a means to require the steel mills to drastically
reduce the amount of oil they discharge to the IHC.
We recommend that efforts to control phosphorus effluents,
which have shown some success, be continued, so that phosphorus
effluents can be further reduced to the levels recommended by
!the Phosphorus Technical Committee (1972). This will require
completion of some sewage treatment projects, monitoring of opera-
tion of sewage treatment plants, and control of combined sewer
overflows, as discussed above. It may also require further
control efforts by adjacent states to achieve the recommended
reductions.
We also recommend that a further study be undertaken to
determine the impact of IHC effluents on water quality over a
wider area than can be determined by tracing the IHC plume. This
would include a study of residence time of pollutants in the
Calumet area of Lake Michigan, as well as a study of the movement
of pollutants in a somewhat wider area using modern instrumen-
tation. The objective would be to determine whether the NH3-N
and P levels observed are entirely due to local sources, or
whether more distant sources can also contribute.
-------
2. DESCRIPTION OF AREA AND WATERSHED
The area included in this project extends from the 68th St.
Chicago water intake crib to Burns Harbor in Indiana, and the
tributary streams between these limits. The flow pattern in
these rivers is somewhat complicated, and only the portions
flowing into Lake Michigan are included. These are discussed
below.
Three streams connect directly with the Lake. These are the
Indiana Harbor Ship Canal (IHC), the Calumet River, and Burns
Ditch. See Figure 2.1.
The IHC normally flows toward the Lake, and it carries the
largest quantities of pollutants. The Calumet River is also
polluted, but its flow is reversed so that it does not normally
drain to Lake Michigan. Flow in the Calumet River is controlled
by the O'Brien Lock and is directed to the Gal-Sag Channel
except during periods of heavy flooding or very low lake levels.
Outward flow can also occur if effluent from Lever Bros, through
Wolf Lake exceeds the flow through O'Brien Locks. Just at the
mouth of the Calumet River the flow is usually outward, because
U.S. Steel Co. discharges water from the Lake into the south slip
just inside the River mouth (Technical Committee 1970).
There are two streams that run parallel to the shore. They
are the Grand Calumet River and the Little Calumet River. The
directions of flow are indicated by arrows on Figure 2.1. The
west end of the Grand Calumet River flows to Illinois through the
Gal-Sag Channel, and is not included in this study; however, the
Grand Calumet River also connects to the Indiana Harbor Canal.
The east portion of this river flows outward to the Lake through
this canal, and is included. The east branch originates at the
east edge of the U.S. Steel Company property in Gary as seepage
from fresh water lagoons. The west branch is divided into two
segments which are normally separated by a natural divide located
near the east edge of the Hammond municipal sewage treatment
-------
M I C H I \\6 A H
ILL. | MICH.
IND.
n
LEGEND
EH— BEACHES
ES — PARKS
X — MARINAS S LAUNCHING RAMPS
-"$— DIRECTION OF FLOW
WATERSHED BOUNDARY
Figure 2.1
CALUMET AREA OF LAKE MICHIGAN BASIN
SHOWING STREAM FLOW DIRECTIONS
(Technical Committee on Water Quality 1970)
-------
plant grounds. Water in the east segment of the west branch
normally joins the east branch to form the IHC.
The Illinois segment of the west branch normally flows west-
ward into Illinois; however, the entire flow in the Indiana
portion of the stream is usually to Lake Michigan via the IHC.
Flow into Illinois is possible on occasions, as a result of
weather conditions on Lake Michigan, We have not seen this
happen, though it is mentioned by the Technical Committee (1970) .
The Grand Calumet River and the IHC drainage system consti-
tute the largest source of pollutants to the Lake in the area
(Figure 2.1). These streams, which have a combined length of
approximately 13 miles, drain an area which contains a population
approaching one-half million and one of the most concentrated
steel and petroleum manufacturing complexes in the nation. In
excess of 907o of the water flowing in these streams enters via
sewers as treated waste water, cooling water or as storm water
overflow. This description is from the Indiana Stream Pollution
Control Board (1973).
The IHC has been dredged to a 28-ft depth as far as Columbus
Drive, and its sides are quite steep. Water level is essentially
at base level with Lake Michigan. Flow in the Canal is normally
to the Lake, because of the large rate at which Lake water is
pumped into the IHC via the Grand Calumet River by U.S. Steel
Gary Works.
The Grand Calumet River is a shallow stream, which in most
;areas is bordered by 20 to 50 ft of cattail marsh. The bottom of
the stream is covered with a mixture of organic debris, mud and
sludge. Although the velocity of flow in the stream is generally
slow enough to permit deposition, after locally heavy rains the
'velocity is increased to the point that bottom deposits may be
iresusperided.
i
; Further inland is the Little Calumet River. The portion of
this river west of Hart ditch generally flows west to the Gal-Sag
8
-------
(Channel, and it is excluded from this study. Hart ditch is just
jeast of the Illinois-Indiana boundary (see Figure 2.2); however,
'the headwaters of the Little Calumet River and its tributaries,
which drain the eastern portion of the basin, enter Lake Michigan
via Burns Waterway, a man-made outlet, and are included.
In general then, the area included is the Lake itself between
68th St. in Chicago and Burns Harbor, and the eastern portion of
the drainage basin outlined by a heavy dashed line in Figure 2.2.
-------
M I C H I 6 A N
— LAKE
CALUMET AREA SURVEILANCE PROJECT
LOCATION MAP
CALUMET AREA
U.S.DEPARTMENT OF THE INTERIOR
FEDERAL WATER POLLUTION CONTROL ADMIN.
Graat LoKes R*gion Chicago,Illinois
Figure 2.2
DRAINAGE BASIN OF CALUMET AREA TRIBUTARY STREAMS
-------
3. FLOW DATA OF TRIBUTARY STREAMS
It is important to know the flow rates of tributary streams,
to relate the effluent loads (Ib/day) to concentrations in the
streams. This information would then allow one to determine the
reductions in loads necessary to achieve a given stream water
quality. This is the approach that was taken by Combinatorics
(1974) for the Grand Calumet River/IHC system.
Our main concern is with the water quality in Lake Michigan,
as discussed in Chapter 1. We need flow data so that we can use
measurements of pollutant concentrations in the streams to check
the effluent load data from permit applications. The result of
this checking process is a better estimate of the actual loads
of effluents impacting the near-shore waters of the Lake. Our
main concern is with the Grand Calumet/IHC system, because these
tributaries have the largest sources of effluents in the Calumet
area. We also obtained some flow data on other streams.
The Grand Calumet River is not an ordinary drainage stream,
and its flow does not present the usual seasonal highs and lows
that result from natural drainage. Most of the flow that enters
the Grand Calumet River and the IHC comes from industrial or
municipal discharges, and this water is taken from Lake Michigan,
This situation is further described by Combinatorics (1974) and
is made clear by the data presented below.
3.1 Flow Data
The most extensive data are those measurements made by the
U.S. Geological Survey (1964). Figures 3.la and 3.1b show
gaging locations of the Geological Survey, and Figure 3.1c shows
the flows they measured. The flow at stations 5B and 7 measure
the contribution from the east branch of the Grand Calumet
River, mostly coming from U.S. Steel Gary works and the Gary
STP. It varies from 600 to 1000 cfs. The flow at Dickey Rd.
includes most of the industrial effluents into the IHC except
11
-------
Figure 3.la
GRAND CALUMET RIVER INFLOW INVESTIGATION
Water Resources Division
U.S. Geological Survey
-------
Figure 3.1b
GRAND CALUMET RIVER INFLOW INVESTIGATION
Water Resources Division
U.S. Geological Survey
-------
Site
No.
1A
1
2
3
3A
4
4A
5
5A
5B
6
6
7
8
9
10
11
Nov.
1954
_
52.2
89.5
265
-
512
-
564
-
-
734
-
870
785
117
-
-
581.68
Flow i
May
1955
31.3
69.0
104
256
344
491
559
582
649
725
-
-
726
657
181
-
-
581.50
* Approximate
n Cubic Feet per Second
Aug.
1955
_
-
-
329
-
591
-
723
769
810
783
-
1010
977
209
-
-
581.21
elevat ion.
Sept.
1955
_
-
-
-
-
565
587
640
735
824
813
-
844
933
57.1
1040
-
580.70
Mar.
.1956
_
-
-
225
-
490
-
492
609
722
653
-
806
855
58.0
1128
-
579.67
Mar.
1964
_
-
-
297
-
507
-
657
749
718
848
808
894
1010
20.1
1450
16.0
577 A *
Locat ion
Virginia Street
Broadway Street
Buchanan Street
U.S. Highway 12
Kennedy Avenue
151st Street
Calumet Avenue
Dickey Road
Burnham Avenue
Monthly mean levels of
Lake Michigan-Datum 1929
Figure 3.1c
GRAND CALUMET RIVER INFLOW INVESTIGATION
Water Resources Division
U.S. Geological Survey
-------
for some outfalls of Inland and Youngstown Steel Cos. It amdunts
to 1000 to 1500 cfs.
More recent data from other sources give similar or slightly
higher flows. Flows were measured by U.S. EPA in 1971 and 1972
(Table 3.1). The measurements at Kennedy Avenue represent the
contribution of the east branch of the Grand Calumet River. The
flow is between 900 and 1100 cfs, and is almost the same as the
flow in the IHC at 151st St. The flow near the mouth of the IHC
was not measured. The flow in the west branch of the Grand
Calumet River was measured at Indianapolis Blvd., but this does
not include the outflow from the East Chicago STP.
Table 3.2 locates the gaging stations used by Combinatorics
(1974) in early October 1973. Their average measurements are
.given in Figure 3.2. Although there is some variation from point
to point, the flow in the east branch of the Grand Calumet River
is about 800 cfs. In the IHC it is about 900 to 1400 cfs. Flows
from the permit data amount to about 900 cfs, but of course actual
flows can vary from this depending on industrial operations at
the time. The flow near the mouth of the IHC is higher, amounting
.to 2290 cfs. This includes some but not all of the inputs from
Inland and Youngstown.
IITR.I also measured the flow at two points on the IHC in
November and December 1973. The methods of measurement are
described in Chapter 11. The measurements at Columbus Drive are
given in Table 4.4, Chapter 4. They range from 880 to 2200 cfs.
There were no substantial rainfalls during the measurements. A
'representative flow would be about 1200 cfs. These variations
could represent changes in industrial pumping rates, or reactions
to fluctuations in level. Combinatorics (1974) also noticed that
flow measurements varied in the IHC.
i Level fluctuations occur in the dredged portion of the IHC,
I
land even in its source, the Grand Calumet River. Continuous level
monitoring records taken at Chicago Avenue on the IHC (Bowden
1974) show a fluctuation of the IHC water level of 1 ft with a
15
-------
Table 3.1
CALIJMET AREA SURVEILLANCE STREAM FLOW
Q = Discharge in Cubic Feet Per Second
V - Velocity in Feet Per Second •
(U.S. EPA, Region V. ILDO
January 8, 1973)
Date
8/6/71
8/12/71
8/13/71
8/22* /71
8/30/71
9/1/71
9/8/71
9/20/71
9/21/ri
9/22/71
9/23/71
-. /,o /—.
9/^;./ M.
n '27/71
9/28/71
11/3/71 •
12/28/71
(4. /I*. IT?
.-1/11/T2
'I-/17/72
5/9/7-
5/10/72'
5/11/72
10/11/72
10/12/72
10/27/7?
10/31/7.?
-1/3/'-.?
.11/13/72
11/17/72
Kituber of
Ktasurcrsen
Mean
Maximum
''IT1-™"!
Grand Calxmet
Grand Calumet Grand Calumet River @ Grand Calumet Indiana Harbor
River $ River @ Indianapolis River <3 Canal (3
Penn RR Kennedy Ave. Blvd * Hohman Ave. 151st St.
Q
U20,
650,
760,
710^
760,
690,
770,
7^0,
730,
730,
720,
BlO,
770,
790,
tu
720,
810,
1*20,
V
1.5
2.2
2.3
2.3
2.2
2.3
2.0
2
2
2
2
2
2
2
2
15
2
2
1
.3
• 3
.2
.2
.3
A
.3
.3
.2
A
• 5
Q
910,
900,
870,
o^'O,
990,
980,
1,000,
1,000,
1,103,
1,100,
920.,
7'tO,
920,
1*
9<»0,
1,100,
7*iO,
1
1
1
1
1
1
1
1
1
1
1
1
0
1
1
1
0
V
.2
.2
.2
.2
.2
.6
A
.3
A
•3
A
.1
.88
.2
• 3
A
.88
Q
21W,
70-.-',
0.0,
67B,
6E,
56E,
172,
^92,
30W,
9
.
-
•
V Q V
»*, 1.5
0.08
ItO, 1.5
in, lA
37, 1 A
0.32 !A, lA
0.0
0.36
0.03 •
0.27
0.05
0.20 59, 1-7
5^, 1-7
0.24
7
46, 1.5
59, 1.7
37, lA
Q
760,
730,
720,
850,
670,
9^0,
kko,
900,
850,
830,.
980,
970,
920,
1,100,
1,100,
1,200,
870,
890,
8cO.
720,
900,
21
870,
1,200,
Wo,
V
0
0
0
1
0
1
0
1
1
1
1
1
1
1
1
1
1
1
3
0
1
1
1
0
.97
.OS
.88
.2
.5*
.2
.2
.2
A
.it
^0
A
A
.6
.1
.1
.8.5
.1
.1
.6
,5'1
* Flow cnn be to eart or vest.
Flows on 4/11/72, 5/9/72, and li/17/72 ave
portion to west.
net flove; portion of stream flowed to
16
-------
Table 3.2
VELOCITY AND FLOW SURVEY OF OCTOBER 1-4, 1973
(Combinatorics 1974)
East Leg Grand Calumet River
2
Station Cr o s s.-sect ion ^ ft Mile
CRE-1
CRE-2
CRE-3
CRE-4
CRE-5
555
5.97
4.65
4.19
2.62
.63
Description of Location
200 ft. U.S. of Bridge St.
600 ft. D.S. of Perm Central R.R.
Bridge near Gary S.T.P.
1,000 ft. D.S. of Industrial
Highway (U.S. 12)
200 ft. U.S. of Cline Ave.
200 ft. D.S. of Kennedy Ave.
West Leg of Grand Calumet River
CRW-1 2.00
CRW-2
DRW-3
352
249
1.42
.50
At culvert crossing of Columbia
Ave. (tentative)
900 ft. west of Toll Road.
600 ft. east of Indianapolis Blvd.
Indiana Harbor Canal
HCX-1
HCX-2
HCX-3
HCX-4
HCX-5
HCX-6
3.86 100 ft. U.S. of 151st Street
3.10 200 ft. D.S. of B&O Railroad
2.35 1,032 ft. D.S. of Columbus Drive,
between first and second Shell
tanks nearest west bank.
1.94 , , 300 Jt. UT,S. of^rbor Belt R.R.
1.25 300 ft. U.S. of Dickey Road
. .60 Canal entrajhge, ,500 ft. D.S.
from last of triple railroad
bridges.
Lake George Canal
LG-1
.5
100 ft.,U.S. of Indianapolis Blvd.
U.S. » Upstream
D.S. = Downstream
17
-------
o.o
00
715
ID
30
w*jT
6. C.. R.
EAST BRANCH G. «• /?.
-Zo
MH.g-+
46
Figure 3.2
FLOW SURVEY OF OCTOBER 1-4, 1973
(Combinatorics 1974)
-------
period of 1 hr. This appears to be due to natural resonance of
'the IHC geometry. The level is affected a few inches as far
'upstream as the Grand Calumet River. The level records also show
a fluctuation with a period of 12 hr, which is the same period as
north/south Lake Michigan oscillations (Mortimer 1968). The
calculated volume of water associated with a level fluctuation
of 1 ft is sufficient to explain the variations in flow rate that
we measured at Columbus Drive, as shown in Table 4.4. Unfortunately
we did not fully appreciate the nature of the flow fluctuations
at that time, and did not measure the IHC level simultaneously
with the flow measurements. Nevertheless the average flow data
in Table 4.4 should be valid, and can be used for the purpose of
checking the average effluent loads.
Changes of level as much as 3 ft are said to occur occasionally
(Winters 1973; Bowden 1974). Such a change could result in a
sudden outflow from the IHC; this could flush a slug of polluted
water into the Lake, and produce concentrations higher than the
usual plume. We did not observe any noticeable changes in the
level of the IHC, but we believe they could occur.
IITRI also measured the flow on three days at the mouth of
the IHC, at station CAL06. These are the only measurements we
know of at this point. The measurements were made with a current
meter by the method described in Chapter 11. The results are
given in Chapter 12, Tables 12.1 and 12.2. At this point, the
flow comes largely from upstream sources, including outfalls from
Inland and Youngstown Steel Cos. below Dickey Road. The outflow
also includes some Lake water that intrudes in a colder layer
under the outflowing surface layer, as is described in Chapter 12.
3.2 Conclusions
Table 3.3 summarizes the flow data from all the data sources
described above. The range of values given represents the range
: of usual values given in each report. The typical value is our
own estimate. It is a rough average of the measured values. The
typical values given in the table are in reasonable agreement
19
-------
Table 3.3
SUMMARY OF FLOW DATA IHC AND GRAND CALUMET RIVER
(data from various sources)
Flow, cfs
Location
Grand Calumet River,
east branch
Grand Calumet River,
west branch
IHC, Columbus Drive
IHC, Dickey Rd.
IHC mouth, upstream
sources
IHC mouth, total
Typical value
800
70
1200
1500
2200
3500
Range
600 to 900
- 40 to 90
800 to 2200
1500 to 3800
3150 to 4200
Flow, m /sec
Typical value
23
2.0
34.
42.
62.
100.
20
-------
with the flow data from permit applications. These are compared
in Chapter 4. Our typical values are slightly higher than those
estimated by Combinatorics (1974). We feel that the permit data
may not be as reliable as the stream measurements, and we put
more reliance on the stream measurements than Combinatorics (1974)
did.
3.3 Other Stream Flows
Figure 3.3 presents the flow measurements in streams near
;the Burns Harbor area in Indiana. For historical background, the
,stream flow data for some years in earlier decades are shown in
Table 3.4.
The flow in the Calumet River was qualitatively described
in Chapter 2. During our field sampling program we observed that
there is usually a sluggish flow from the Calumet River into
Calumet Harbor. We have not measured the flow, nor do we know
of measurements (except an observation in Appendix D, Section 9).
From available information it is reasonable to assume that the
effluent from South Works goes into the Lake, and effluents fror,
sources further inland normally go westward to the Cal-Sag channel
(Technical Committee 1970).
21
-------
BURIES DJTC3 © US 12
mat
DATE I'ltfE (Cfn)
2/27/T3 1100 falo
3/2/73 11CX) 520
CCMBINEjD
FROM
STSKL
S/i-itiELSOH ROAD
DATS
2735773 i'?J^ 320
T3ME
2/21773
2/27/73 1030 1»«)
3/2/73 0830 150
2/27/73 0900 360
2/27/73 0830 330
« j*.
3/2/73 1000 370
Figure 3.3
FLOW MEASUREMENTS NEAR BURNS HARBOR, INDIANA
Z. 2-
-------
with the flow data from permit applications. These are compared
[in Chapter 4. Our typical values are slightly higher than those
estimated by Combinatorics (1974). We feel that the permit data
may not be as reliable as the stream measurements, and we put
more reliance on the stream measurements than Combinatorics (1974)
did.
3.3 Other Stream Flows
Figure 3.3 presents the flow measurements in streams near
ithe Burns Harbor area in Indiana. For historical background, the
,stream flow data for some years in earlier decades are shown in
Table 3.4.
The flow in the Calumet River was qualitatively described
in Chapter 2. During our field sampling program we observed that
there is usually a sluggish flow from the Calumet River into
Calumet Harbor. We have not measured the flow, nor do we know
of measurements (except an observation in Appendix D, Section 9).
From available information it is reasonable to assume that the
effluent from South Works goes into the Lake, and effluents fron
sources further inland normally go westward to the Gal-Sag channel
(Technical Committee 1970).
21
-------
J ,'
"^y^'fa .*:•..i,
.»•: l~//-fe'••/,
S:«f^^
•V-H* •/? ' • I
f^^rL!U^^
'} <• ~- I '"*••• ~-t«™«,_. J>, , *• . ±-- -
-------
Table 3.4
SELECTED LOW FLOW AND OTHER DATA FOR STREAM GAGING STATIONS1
River
Lake Michigan Basin
Little Calumet
Little Calumet
Little Calumet
Burns Ditch
Hart Ditch
Deep River
Salt Creek
Station
location
Munster
Gary
Porter
Gary
Muncster
Lake George
Outlet
McCool
Drainage
area,
sq. miles
-
-
62.9
160.0
6-9.2
125.0
78.7
Gage datum
above M.S.L. ,
ft
-
-
603.48
577.04
591.27
-
594.10
Bankful
stage,
ft
-
-
7.0
-
7.0
-
10.0
7-day
10-yr
low flow,
cfs
3.7
0.0
19.9
5.6
3.2
4.9
21.0
Min.
day
flow,
cfs
2.0
0.0
18.0
2.6
2.8
4.2
19.0
Records
•tace,
Comments yr
-
1945
Above confluence 1944
with Little Cal.
1943
1947
1945
Source: "Low Flow Characteristics of Indiana Streams" U.S.G.S. and State of Indiana, 1961.
Second Source: Lake Porter Regional Transportation and Planning Commission Report: "Water and waste water, a component
of the regional plan."
-------
4. INDUSTRIAL WASTE SOURCES. OUTFALLS AND EFFLUENT DATA
4.1 Description
The major population centers in the area are East Chicago,
Gary, Hammond and Whiting, in Indiana; and a part of the south
side of Chicago in Illinois. The area is highly industrialized.
There are ten major steel mills including the United States Steel
Corporation's Gary Works, Gary Sheet and Tin Mill, Youngstown
Sheet and Tube Company, and Inland Steel Company in Indiana and
United States Steel's South Works in Illinois. There are four
petroleum refineries including the American Oil Company, the
Cities Service Refinery (now closed), the Mobil Oil Company, and
the Arco Refinery, in Indiana. Other industries include Lever
Brothers, Union Carbide Chemicals, E.I. DuPont, Blaw Knox,
American Maize and a large number of smaller concerns.
These industries are located in four major groups. One
group is concentrated along the Calumet River in Illinois. Of
these, only U.S. Steel discharges to the Lake under normal con-
ditions. Another is along the Indiana Harbor Canal (IHC). The
third is in Gary, Indiana, and discharges to the headwaters of
the Grand Calumet River and to the Lake via the IHC. A fourth
includes several steel mills, municipalities and smaller indus-
tries in the Burns Harbor basin. These groups make the Calumet
area one of the most important industrial centers in the nation.
The largest sources of pollution are industries along the
IHC. There are currently seven major industries discharging
into the Grand Calumet River and IHC, and several other indus-
tries with minor discharges. These are mainly steel mills, oil
refineries, a chemical company, and municipal sewage treatment
plants. The main pollutants are ammonia, oil, iron sediments,
BOD, fecal bacteria, phenol, cyanide, and some heavy metals.
;The amounts of these effluents are assessed in this chapter, and
idetailed analyses of individual parameters are given in Chapters
13 to 18. All of the major discharges currently provide some
treatment to their waste water, but in some cases current
24
-------
treatment is inadequate. Law suits are pending against several
steel mills to force them to provide better treatment.
There are some outfalls along the Lake shore, primarily from
American Oil Co. in the Whiting area, and from U.S. Steel Co. at
Gary. There are also a number of combined storm-sewage overflow
outfalls, both along the Lake and in tributary streams. Plans
to treat these overflows are scheduled for 1977„
The Indiana Stream Pollution Control Board has reported to
the Lake Michigan Enforcement Conference that a number of indus-
tries on the Little Calumet River are meeting Indiana effluent
requirements. The Conference Proceedings (1970) lists these
sources, the flow volumes, and the type of treatment used. In
the Burns Harbor area are two steel companies that have new
effluent treatment facilities. Permit and water quality data
for these sources are discussed in Appendix C.
4.2 Identification of Outfalls
Figure 4.la and 40lb present a location map of the various
important industries and sewage treatment plants in the Calumet
area which are the principal sources of wastes. Detailed maps
showing the locations of outfalls are given in Appendix C. A
listing of the outfalls is given in Table 401.
The sources for developing the outfall identification maps
are NPDES Permit applications, Indiana State Pollution Control
Board 24-hr effluents sampling program data and site visits by
the personnel of Citizens for a Better Environment (CBE) and
Businessmen and Professionals in the Public Interest (BPI). CBE
was our subcontractor for this part of the work, and information
was taken from a previous study by Businessmen in the Public
Interest (1972). Data were current as of fall 1973.
Appendix C contains a description of each of the industries
that discharge in the area, with additional information about
the discharges„
25
-------
N3
cn
LAKE
MICHIGAN
Figure 4.la
LOCATION MAP SHOWING MAJOR INDUSTRIAL AND MUNICIPAL PLANTS
IN THE CALUMET AREA
-------
LAKE
M I C H 4 Q A N
lit
Figure 4.1b
LOCATION MAP CONTINUED
-------
Table 4.1
LISTING OF INDUSTRIAL EFFLUENT SOURCES IN CALUMET AREA
CO
BASIN
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Lake Michigan
Little Calumet
NAME OF COMPANY
US Steel - South Works
Commonwealth Edison -
State Lino
American Maize
American Oil
Union Carbide -
Whiting
Universal Atlas Cement
Division US Steel
NIPSCO - Mitchell
Station
Marblehead Lime Co.
Union Carbide
T-1200 Linde Division
US Steel - Gary
Midwest Steel
Burns Ditch
Bethlehem Steel -
Burns Harbor
NIPSCO Bailey
Station
Bethlehem Steel
DATL NPD? # MAJOR PERMIT # OUTFALLS FLOW
6-18-71 2720612 Yes N° 6 241.24 NGD
7-1-71 2720443 Yes Ho 1 1000 MGE
6-22-71 2720034 Yes No 1 9-7 MGD
6-7-71 2720170 Yes No 2 130 MGD
6-4-71 2720011 YeG No 1 47.54 MGD
Two possible unre ported discharges
6-30-71 2720201 YSS No 1 457 MGD
2720485 No No 2 130,000 GPD
6-18-71 2720042 Yes No 1 100 MGD
7-1-71 2720608 Yes No & 251.5 MGD
6-30-71 2720355 Yes No 5 11.923 MGD
8-25-71 2720246 , Yes N° 1 104 MGD
6-30-71 2720202 YeG No 1 456 MGD
8-25-71 2720246 Yes No 1 154 MGD
TYPE OF WASTE
Cool ing water
Cooling water
Process water
Process scooling
water
Cooling water
Cooling water
Water runoff
Cooling water
Cooling & process
water
Cooling & process
water
Treated process
water
Cooling water
Treated process
water
-------
Table 4.1 (cont.)
LISTING OF INDUSTRIAL BFFLDEHT SOURCES
CALUMET STUDY AREA
BASIN
Grand Calumet River
Grand Calumet River
Grand Calumet River
Grand Calumet River
Grand Calumet River
Indiana Harbor Canal
S3
VO Indiana Harbor Canal
Indiana Harbor Canal
Indiana Harbor Canal
Indiana Harbor Canal
Indiana Harbor Canal
NAME OF COMPANY DATE NPDES # PERMIT MAJOR # OUTFALLS FLOW
US Steel - Gary 7-1-71 272060S No Yes 34
US -Lead Refinery 6-30-71 2720393 No ? 150,000 CPD-
US Steel - American Bridge Two possible unreported discharges
E.I. DuPont de Nemours 4-17-72 2720889 No Yes 9 9850 GPM
Harrison-Walker 6-14-71 2720462 No No 1 140,000 GPD
Refractories
Blaw-Knox 6- -71 2720710 No NO 2 207 MGD
Union Carbide-Linde 6-15-71 2720043 No Yes 1 150,750 GPD
Air Products
General Transportation 6-28-71 2722502 No No 1 30,000 GPD
Corp .
Atlantic Richfield 6-25-71 2720045 No Yes 1 4.75 MGD
Phillips Pipeline 6-30-71 2720563 No So 1 48,000 GPD
American Steel Corp. 6-25-71 2720242 No No 1 230,000 GPD
TYPE OF WAST1
Process & coaling
Cooling water
very high trap.
3 Outfalls proposed
at flow
Non-contact sooling
2 Outfalls - stora
drainage only
Process mt*r
Process water
Submerged outfall
data rev. 7-16-73
Process water
Contact-cooling
quench water for
heat-treated steel
castings
Indiana Harbor Canal
Indiana Harbor Canal
Indiana Harbor Canal
Union Carbide - Whiting 6-4-71 2720011
Inland Steel
Youngstown Steel
6-21-71 2720129
7-1-71
11
216,000 GPD
865 MGD
290 MGD
Process water
Process s cooling water
Process & cooling water
-------
4.3 Effluent Loads Other Than via IHC
Table 4.2 gives a more detailed list of outfalls to Lake
Michigan (other than those entering via the IHC). The table
also gives the flows, concentrations and loads of the most impor-
tant pollutants. This information is taken primarily from permit
applications. In Appendix C additional information is given,
comparing the permit data with data from Indiana 24-hr sampling
of the industry outfalls. The sampling was done on February 2-3,
1973, and June 19-20, 1973. The State of Indiana also obtains
daily operating reports on a monthly basis from major industries.
The data from these three sources of information are compared in
Appendix C; the conclusion is reached that most of the permit data
are of the correct order of magnitude, although numerous discre-
pancies are pointed out.
Most RAPP documents were submitted in the summer of 1971,
and data included could represent analysis taken as much as one
year previously. Some industries have installed pollution control
equipment and made other changes in their processes. Most of
these have been reflected in changes in the permit application
data in U0S. EPA files. Appendix C represents the available
data in December 1973. In the case of DuPont and U.S. Steel
South Works, the information in the Appendix has been updated
based on court decrees.
4.4 Effluent Loads to Lake Michigan via IHC
The sources that discharge into the Grand Calumet River and
the IHC were investigated by Combinatorics (1974). Their infor-
mation is partly from permit applications, partly from data in
Indiana files, and partly from information supplied to Combina-
,torics by industry. A descripton of the status of each industry
:in this group is also given in the Combinatorics (1974) report,
jtogether with projections for the future.
i
| A list of the major outfalls in this group is given in
:Table 4.3. The flow rates, concentrations of each pollutant and
30
-------
Table 4.2
EFFLUENT CONCENTRATIONS AND LOADS FROM INDUSTRIES IN CALUMET AREA
DRAINING INTO LAKE MICHIGAN DIRECTLY
OR VIA LITTLE CALUMET RIVER AND BURNS DITCH
Average values (maximum values in parenthesis)
Source: NPDES data compiled by Citizens for a Better Environment
as of December 1973
FlOW
Source and outfall
NIPSCO Bailly
001
Bethlehem Steel
001
002
Midwest Steel
001
002/003
004
005
Cool ing
456
treated
104
154
0.023
Cooling
4.76
9.06
Cooling
1.08
3
m /sec
20.
process
4.6
6.7
0.001
0.2
0.40
0.047
Chloride
3
(8)
30
(140)
8
16
-
_
20
(25)
Ib/dav
30,448
(31,220)
25,821
(139,864)
10,219
(23,665) '
-
_
1,512
(2,168)
Total organic
Ammonia-Nitrogen carbon Fluoride
mg/l
(0.03)
0.1
(1.4)
0.1
(1.4)
0.65
(0.65)
.
O.O185
(0.035)
Ib/dav mq/i
(117)
86
(1,998)
127
(2,070)
(0.271)
_ _
1.4
(2.64)
Ib/dav ma/1
-
0.43
(1.42)
0.13
1.0
-
_
1.00
(3.0)
Ib/dav
370
(2,027)
166
(1,479)
-
—
76
(260)
006/STP
U.S. Steel Gary
0.0007
035
036
037
038
039
Marblehead Lime
007
008
76.3
28.2
7.0
10
71.3
0.07
0.06
3.36
1.24
0.307
0.44
3.12
0.003
0.003
12 7,686 0.3 132
11 2,587 -
11 642 0.2 12
Recently became operational; no data available
12 7,136 0.3 178
0.05
small
0.2
0.2
128
47
-------
Table 4.2 (cont.)
Total
LO
to
Total iron
Source
NIPSCO
and outfall
Bailly
001
Bethlehem Steel
001
002
JHZ^_
2.358
(9.6)
1.339
7.0
Ib/dav
2,030
(13,705)
1,710
(10,353)
Midwest Steel
001
002/003
004
005
006/STP
0.5
(0.7)
-
_
38
(60.67)
-
-
Total solids
mq/i
182
(165)
286
(450;
214
(300)
170
(170)
957
(823)
-
-
Ib/dav
692,692
(643,919)
246,163
(656,696)
273,357
(443,718)
32
(71)
72,350
(62,233)
-
-
suspended solids
mq/2
20
(3)
16
(74)
16
(209)
(3)
10.7
(11.0)
-
7.7
Ib/dav
76,120
(11,708)
13,771
(105,642)
20,437
(309,123)
(11,708)
809
(833)
-
small
Total phosphorus
(0.27)
0.37
(3.0)
0,21
(2.0)
0.15
(0.15)
0.1
(0.1)
-
-
Ib/dav
(1,054)
318
(4,282)
263
(2,958)
<1
(0.063)
8
(7.55)
-
-
Total coli
mq/l
642
(642)
60
-
:
(540)
-
-
Ib/dav
24.2xl06
-
-
-
-
-
-
U.S. Steel Gary
035
036
037
033
039
Marblehead Lime
007
008
0.1
1.1
1.8
9
64
64
155
168
165
226
952
987
99,920
39,512
9,633
134,339
556
494
3
10
6
21
0
0
1,192 0.42
2,352 0.02
350 0.02
12,487 0.01
0
0
0.6
12.8
4.7
1.2
6.4
small
-------
Table 4.2 (cont.)
Flow
Source and outfall mad
NIPSCO Mitchell
Cooling
457
o
m /sec
20.
Chloride
mg/l
(sTs)
Ib/dav
(43,921)
Ammonia-Nitrogen
mq/i
0.04
(0.04)
Ib/dav
152
(207)
Total organic
carbons
mg/l
-
Ib/dav
-
Fluoride
ma/* Ib/dav
Amoco
001
002
29.17
Cooling
99
1.28
4.3
44 -
(54)
5.3
10,672
(13,121)
4,327
5.43
(20.0)
0.06
1,319
- (4,665)
48
36
(44)
20
' r. •
8,748
(10,692)
16,327
_ _
_
Union Carbide Whiting
001
American Maize
Com.
U.S.
EDI Stateline
Steel S, works
001
002
003
004
005
006
47.54
Process
9.7
Cooling
1000
:
110.9
12.96
16.56
2.1
0.43
4.4
4.9
0.57
0.73
8
(12)
11
(12)
11
11
13
-
3,174
(22)
890
(971)
91,806
10,181
1,406
-
.
-
1.57
(1.96)
0.11
-
0.3
0.4
_
-
127
(245)
0 (net)
-
32
55
392
-
13
(14)
-
2.1
8.5
2.6
15,562
1,052
(1,133)
-
1,944
919
359
0. 15 60
— _
-
-
•
0.2 185
0.4 43
_ _
Stream overflow - - -
3.74
97.36
0.16
4.3
12
14
375
11,374
1.5
0.09
47
73
9.8
8.0
306
6,500
0.3 -9
0.5 406
-------
Table 4.2 (cent.)
Total
Source and outfall
NIPSCO Mitchell
Amoco
001
002
Union Carbide Whiting
001
American Maize
Com. EDI Stateline
U.S. Steel S. Works
001
002
003
004
005
006
Total
ma/A
(274)
0.357
(580)
0.230
0.2
(0.45)
-
0.097
(0.58)
4.0
1.6
1.1
2.6
20
iron
Ib/dav
(1,416)
87
(141)
190
30
_
810
3,702
173
152
81
1,625
Total
mq/l
208
(208)
360
(406)
208
2.4
(17.3)
285
(718)
175
(2)
184
206
194
203
320
solids
Ib/dav
793,312
(1,074,782)
87,475
(101,459)
171,185
950
(31.1)
23,056
(89,822)
1,460,550
(670)
170,305
22,281
25,813
6,336
259,968
suspended
10
(10)
20
(78)
12
(17.3)
23
(76)
6
0
6
14
14
33
28
solids
Ib/dav
38,140
(51,672)
4,860
(19,472)
9,876
(31.1)
1,860
(9,508)
50,076
5,553
1,514
1,934
1,030
22,747
Total
0.14
(0.14)
0.03
tO. 22)
0.01
0.05
(0.19)
0.52
(0.73)
0.10
(0.07)
0.03
0.04
0.02
0.05
0.05
phosphorus
Ib/dav
723
(723)
3
(56.8)
8
small
(0.33)
41
(91)
41,793
(2.81)
28
4
3
2
41
Total coll
mq/1 Ib/dav
546 2xl07
-------
Table 4.3
LOCATION AND DESCRIPTION OF
Source
CO
Ul
Discharge
Designation
U.S. Steel
GW-1
GW-2
GW-2A
GW-3
GW-3A
GW-4
GW-5
GW-6
GW-7
GW-7A
GW-9
GW-10A
GW-11A
GW-1 3
NPDES
Permit
Design.
002
007
009
010
Oil
015
017
018
019
020
021
028
030
032
Location
(River
Mile)
East Branch
9.30
9.20
9.08
8.83
8.73
8.50
8.35
8.31
8.21
8.07
7.94
7.78
7.36
7.30
DISCHARGES TO GRAND CALUMET RIVER AND IHC
: Combinatorics (1974)
Description of Discharge
Process water from tube operation; non-contact water
from coke plant.
Non-contact water from distillation plant; misc.
Process water from blast furnaces.
Non-contact water from No. 1 battery air compressor; misc.
Process water from blast furnaces.
Non-contact water from No. 3 sinter plant.
Process water from blast furnaces.
Non-contact water from blast furnaces, No. 2 sinter plant, and
No. 4 boiler house.
Non-contact water from No. 2 sinter plant, No. 4 boiler house.
Non-contact water from No. 1 Basic Oxygen Process (BOP) shop
and No. 4 boiler house.
Non-contact water from No. 3 and No. 4 open hearth operation*.
Process water from bar mills, wheel mill, billet mill,
rail mill, blooming mills, slabbing mill, *nd plate mill.
Non-contact .water from bar mills and rail mill.
Same as 10A.
Non-contact water from bar mill.
-------
Table 4.3 (cont.)
Discharge
Designation
ST-14
ST-17
Gary
GSTP-1
NPDES
Permit
Design.
033
034
N/A
Location
CRiver
Mile)
6.50
5.04
4.60
Description of Discharge
Non-contact water from atmosphere gas plant.
Process water and non-contact water from galvanizing line,
hot strip mills, pickle lines, CR mills, CA lines, tin
mills, and annealing operations.
Gary's wastewater treatment facility discharge.
E.I. duPont
001 001
002-004
005
007-010
1.40
002-004 1-38
005 1-16
007-010 -85
Process and non-contact cooling water from the production
of inorganic chemicals.
Same.
Same.
Same.
U.S.S. Refinery Inc,
USL-1 001
,25
Non-contact cooling water discharge from blast furnace
and casting mold.
Hammond
HSTP-1
N/A
West Branch
1.90 Hammond's wastewater treatment facility discharge.
East Chicago
ECSTP N/A
.55
East Chicago's wastewater treatment facility discharge.
-------
NPDES Location
Discharge Permit (River
Designation Design. Mile)
Atlantic Richfield
Oil Company
ARCO 001
Union Carbide
Linde Division
UC-1
Youngstown
YS-20
001
001
Lake Geon
Branch
1.00
IMS Canal
2
1
.65
.81
American ''
Steel Foundries
AS-1
Inland
IE-2
Youngstown
YS-2
YS~4
YS-8
YS-11
Inland
4E-1
001
001
002
003
004
005
002
1
1
1
1
1
1
1
.70
.50
.20
.16
.00
.00
.00
Table 4.3 (cont.)
Description of Discharge
Oil refinery discharge.
Process and cooling discharge from production of industrial
gases.
Process water from continuous pickling, cold rolling and
finishing operations.
Process and cooling waters from a foundry.
Process and cool ing water from an electric furnace steel
shop and bar mill.
Cooling water from cold rolling and finishing operations.
Cooling water from finishing operations at No. 1 tin mill.
Cooling water from cold rolling operation at No. 1 tin mill.
Cooling water from continuous pickling operation at No. 1
tin mill.
Process water, contact and non-contact cooling water from
blast furnace; non-contact cooling water from a coke plant;
and power house cooling water.
-------
CO
oc
Discharge
Designation
5E-1
5E-2
Youngstown
YS-12
Inland
5E-3
Youngstown
YS-13
Inland
6E-1
Youngstown
YS-22
YS-14
Inland
7E-1
Youngstown
YS-15
Inland
10E-1
NPDES
Permit
Design.
003
004
006
005
007
006
008
009
007
010
008
Location
(River
Mile)
.95
.94
.90
.87
.83
.78
.78
.65
.64
.63
.20
Table 4.3 (cont.)
Description ofDischarge
Process water and non-contact cooling water from a plate
mill, spike mill and continuous hot dip galvanizing lines.
Process and non-contact cooling water from a spike mill.
Cooling and process water from a coke plant operation.
Process and non-contact cooling water from a bar mill and
blooming mill.
Cooling and process water from a coke plant operation.
Discharge from auto tunnel sump-pumps.
Cooling and process water from a coke plant operation.
Power house and sinter plant cooling water.
Non-contact and contact cooling water from blast furnaces.
Power house and blast furnace cooling water.
Non-contact condenser cooling water from power house.
-------
CO
VD
Discharge
Designation
Youngs town
YS-18A
Inland
13G-1
13H-1
14H-TT
15H-TT
16H-1
16H-2
16H-3
16F-1
NPDES
Permit
Design.
Oil
Oil
012
013
014
015
016
017
018
Location
(River
Mile)
Harbor
West Side
Harbor
East Side
Harbor
East Side
Harbor
East Side
Harbor
East Side
Harbor
East Side
Harbor
East Side
Harbor
East Side
Harbor
East Side
Table 4.3 (cont.)
Description of Discharge
Process water and cooling water from blooming, hot strip,
billet, bar, and buttweld mills; process and cooling water
from boiler house, open hearths, and basic oxygen furnace;
cooling water from blast furnace. *
Non-contact and contact cooling water from blast furnaces;
non-contact cooling water from sintering plant and power
house.
Gas scrubber water from blast furnaces, cooling water from
coke plant and open hearth and a sanitary sewage plant
effluent.
Process water from a coke plant, hot rolling mills, and
cold rolling mills; coil picklers rinse water.
Process water from a coke plant, hot rolling mills, and
cold rolling mills; coil picklers rinse water.
Non-contact cooling water from an open hearth furnace and
a small sanitary sewage plant effluent.
Non-contact cooling water from an open hearth furnace and
mold foundry operation.
Process water from hot and cold rolling mills. Non-contact
cooling water from hot strip rolling mills, cold rolling
mills, and coil picklers.
Grit water from basic oxygen furnace. Contact and non-contact
cooling i/ater from basic oxygen furnace; power house cooling
water.
-------
loads are not given in this table; instead, separate tables for
each'pollutant are given in Chapters 13 to 18.
A check of the accuracy of the load data for this group of
industries is given by instream measurements done by IITRI during
our field sampling program. The field sampling program is
described in Chapter 11„ The measured concentrations, measured
stream flows, and calculated loads are presented in Tables 4.4
and 4.5. The data in Table 4.4 at the Columbus Drive bridge
measure the loads of pollutants from sources upstream of this
point. Also given in the table are the sums of the average loads
from outfalls above this point estimated by Combinatorics (1974)„
Similarly, the data in Table 4.5 measure the loads from all out-
falls on the IHC/Grand Calumet River system. The Combinatorics
estimates tend to be at the low end of the measured range. The
loads of many of the pollutants vary from day to day by a factor
of about 3. The best measure of the actual effluent loads at
this time (November to December 1973) would be an average of the
measured loads in Tables 4.4 and 4.5.
Combinatorics (1974) reported effluent loads for some
parameters in addition to those shown in Tables 4.4 and 4.5.
These parameters are BOD, phenol, and cyanide.
4.5 Conclusions and Recommendations
This chapter summarizes the industrial effluent sources and
loads; but the impact of particular pollutants on water quality
in Lake Michigan is assessed in Chapters 13 to 18. These chapters
conclude that substantial quantities of pollutants are going into
Lake Michigan from industrial sources on the IHC; and that the
present inadequate municipal sewage treatment is in large part
due to overloading of municipal sewage treatment plants by indus-
trial effluents to municipal sewers.
A few industrial companies have substantially reduced their
effluents, as a result of settlement of court suits. These
include U.S. Steel Corp. South Works, where decreased effluents
40
-------
Table 4.4
MEASURED EFFLUENT CONCENTRATIONS AND LOAD PER DAY
IN INDIANA HARBOR CANAL AT COLUMBUS DRIVE BRIDGE (STATION IHC3S)
IITRI data
Measured flow (IITRI)
Chloride
i Concentration,
Date
11/12/73
11/13/73
11/14/73
11/15/73
11/16/-73
11/17/73
11/18/73
11/19/73
11/20/73
11/29/73
11/30/73
12/07/73
12/08/73
cfs mgd m /sec
.
1409 906
1051 679
-
-
2200 1422
2200 1422
880 569
880 569
1100 711
1035 669
1470 950
- " -,
.
40
30
62
62
25
25
31
29
42
mg/1
55
65
59
54
65
84
46
72
45
70
60
71
76
Anmonia -Ni t roKen
Load, Concentration,
Ib/day
_
491,496
334,349
-
-
999,913
545,928
341,919
213,699
415,380
335,008
562,938
-
mg/1
5.3
4.6
4.5
5.2
5.4
6,8
3.7
5.7
,3.4
4.8
4.3
6.3
6.7
Total organic carbon
Load, Concentration.
Ib/day
.
34,783
25,501
-
-
80,702
43,912
27,069
16,146
28,483
24,010
49,951
-
mg/1
_
15.0
14.5
12.0
15.5
17.0
10.0
, 14.5
11.0
18.6
13.0
18.5
15.0
Fluoride
Load, Concentration
Ib/day
__
113,422
82,170
—
—
201,756
118,680
68,859
52,238
106,812
72,585
146,680
--
mg/1
0.87
0.76
0.86
1.00
1.30
1.07
1.00
0.93
0.78
1.07
1.02
1.34
0.68
Load,
Ib/day
_
5,476
4,874
.
.
12,699
11,868
4,416
3,704
6,349
5,695
10,624
.
Combinatorics (l974) estimate:
11/12/73
11/13/73
11/14/73
11/15/73
11/16/73
11/17/73
11/18/73
11/19/73
11/20/73
11/29/73
11/30/73
12/07/73
12/08/73
962.5 622
Total iron
Concentration,
OK/1
1.30
1.32
1.00
0.86
0.78
0.98
0.58
1.47
0.88
0.77
0.74
0.66
27
Load,
Ib/day
-
9,981
5,667
-
-
11,631
2,754
6,981
5,222
4,299
5,869
-
Total
Concentration
mg/1
-
-
297
312
376
261
283
215 '
246
344
374
287
202,603
solids
, Load,
Ib/day
-
-
-
-
-
4,462,372
3,097,551
1,343,931
1,030,506
1,459,765
1,920,715
2,965,334
-
Total
23,561
phosphorus
Concentration, Load,
mg/1 Ib/day
- •
-
-
0.18
0.25
0.24
0.18
0.16
0.14
0.23
0.25
0.18
0.15
-
-
-
-
-
2,848
2,136
760
665
1,365
1,396
1,427
-
Total conform
Coli/100 ml
A
24x10^
A
22x10
./.
19x10
Total No.
1 c
6.2x10°
1 ^
4.9x10 "
1 S
10.8x10
Suspended
Concentration
mg/1
19.8
20.7
16.2
14.3
12.9
13.5
10.6
9.4
18.5
19.9
11.7
15.7
14.6
4,087
solids
Load,
lb/d«y
-
•
91,804
-
-
160,218
125,800
44,639
87,854
118,086
65,327
124,480
-
Combinatorics (1974) estimate
7,431
209
127,668
-------
Table 4.5
MEASURED EFFLUENT CONCENTRATIONS AND CALCULATED LOADS
AT MOUTH OF INDIANA HARBOR CANAL (STATION CAL06)
IITRI data
Chloride
•* Concentration.
Date
11/14/73
11/19/73
12/07/73
cfs mgd
3153 2057
3591 2320
4226 2731
m /sec
90
102
120
mg/1
31
40
28
Ammonia -Nitrogen
Total organic
Load Concentration, Load, Concentration,
Ib/day
526,584
774,508
638,201
mg/1 Ib/day
2.7 45,900
2.8 54,218
1.5 34,191
mg/1
10.0
11.5
9.5
carbon
Fluoride
Load, Concentration,
Ib/day
170,002
222,681
216,544
mg/1
0.48
0.61
0.30
Load,
Ib/day
8,159
11,810
6,838
Combinatorics (l974) estimate:
1395 902
40
Total iron
11/14/73
11/19/73
12/07/73
Concentration,
mg/1
0.67
0.48
0.98
Load,
Ib/day
11,365
9,245
22,338
Total
Concentration
mg/1
165
208
226
393,537
solids
, Load,
Ib/day
2,805,504
4,027,630
5,151,480
33,271
Total phosphorus
Concentration, Load,
mg/1 Ib/day
-
0.06 1,161
0.07 1,596
Total
Coli/100 ml
26xl03
30xl03
4.8xl03
coliform
Total No.
2.0xl015
2.6x10 D
5-OxlO15
Suspended
Concentration,
mg/1
7.8
8.1
9.6
6,477
solids
Load,
Ib/day
133,908
156,838
218,812
Combinatorics (1974) estimate
22,343
389
382,795
-------
[indicated in Appendix C have improved the parameters at the
Calumet River mouth as indicated in Chapters 13 to 18. Effluents
from DuPont Co. on the IHC are also improving as a result of a
settlement of a suit, as indicated in Appendix C. A few other
companies on or near the IHC are believed to have improved their
effluents, although an evaluation of the waste treatment programs
of industrial companies was beyond the scope of this project, and
our efforts were limited to examination of permit data. An
industrial parameter in the IHC that has improved substantially
since the Technical Committee (1970) report is phenol (Chapter 14).
Some observers have stated that the amount of floating oil on
the IHC has also decreased, and the load data in Chapter 15
indicate a 50% effluent decrease. Water quality measurements do
not show a trend, perhaps due to the difficulty of sampling and
measuring oil. Other parameters in effluents of the major indus-
tires in the IHC area have shown little improvement. The major
change has been a shifting of effluents to the municipal sewage
treatment plants, where it has caused new problems. Enforcement
action is needed to decrease the loads of specific pollutants,
as indicated in Chapters 13 to 18.
43
-------
5. MUNICIPAL SOURCES AND COMBINED SEVJER OvL ,,
The three main municipal sources are the sanitary districts
of Gary, East Chicago, and Hammond. There are. rvumr rr-i;.<; sn^ller
sources in the eastern part of the Lake Miciii^•-± • ;- • > wt. i.i3
Appendix D describes these facilities and gives data on their
effluent concentrations and loads,, Effluents from these main
sources discharge to the Grand Calumet River. -; .. - . '. •- ''i-,.-
to Lake Michigan via the IIIC. The locations ,,. •, ,.iaL.e treatment
plants of these municipalities are shown in Figure 4.1. Effluents
from the smaller municipalities in the eastern f,orr.',,.; of the
basin discharge to the Little Calumet River, Dt^-i, ,,i\,- Salt
Creek, and flow to the Lake via Burns Ditch, Son*.-, i. r>lT,rmation
is presented on these smaller municipalities, b'(] uiit f.e
plants, but especially that of East Chicago -> - , . , /,-rLeauiug
by industrial effluents going to municipal sewers . ''.l.is situation
is documented in Chapters 13, 16 and 17 as well as Appendix i) „
Pretreatment guidelines of the U.S. EPA (1974) :M •,; Mi :i
industries discharging to municipal sewers must f . •,. i r^v t. their
wastes so as not to interfere with municipal L cea i.rnenl plant
operation, and we recommend that such pretreatr em i.-t. required.
It might be feasible for the municipalities to accept the indus-
trial wastes on a charge basis if they expand on- nuHcioal treat-
ment plants and include the necessary process^ \.. • < . ' the
1 increasing loads. If this were to be serious] y ;,,,• -..; Jered, a
study would be needed of the technology and economics of these
two alternatives, including an estimate of the time delay to fund
the municipal plant construction.
44
-------
) Another major problem concerns the pollution entering the
Lake from combined sewer and storm water overflows. Locations
of these overflows are shown in a map in Appendix D, Figure D-2.
Only Hammond measures these overflows; the indications are that
this source of pollution amounts to half of the treatment plant
effluents. Evidence presented in Chapter 16 shows that three
outfalls directly to the Lake in Whiting and Hammond are respon-
sible for some of the very high coliform counts at the Whiting
water intake. The municipalities have plans to solve the overflow
problems by constructing detention lagoons and increasing the
'capacity of sewers and treatment plants. A few of these projects
have actually been constructed, but most are planned for comple-
tion in 1977.
There are a number of smaller waste treatment plants in the
eastern portion of the' Lake Michigan basin, and their effluents
enter the Lake via the Little Calumet River and Burns Ditch. The
operating reports of these plants are summarized in Appendix D.
In general, the effluent levels of these plants are high enough
to cause very poor water quality conditions in the receiving
streams. This is also indicated by benthic studies in Appendix A;
however, the loads are small enough so that the effect on Lake
Michigan is moderate. Some plans to improve these plants by
adding AWT and phosphorus precipitation are summarized in
Appendix D.
Recommendations for improving the effluents from municipal
plants include requiring pretreatment of industrial effluents;
'hastening the funding of treatment plant improvements, which are
behind schedule; hastening construction of sewer and detention
lagoon projects; and improving operation and monitoring of treat-
ment plants.
45
-------
6. WATER QUALITY DATA
6.1 Availability of Data
Extensive water quality data are contained in reports
included in the proceedings of both the Lake Michigan Enforcement
Conference and the Conference on the Interstate Waters of the
Calumet Area. A report to the Conference of the
Technical Committee on Water Quality, issued September 1970,
contains extensive tables of water quality parameters at
the sampling points located on Figure 6.1 and Table 6.1. Data
taken by the U.S. EPA through 1973 are available through Storet.
In addition, Illinois has a water quality network. Computer
print-outs are available for recent years through 1972. Indiana
has a reasonably extensive water quality monitoring program.
The data are available at Indianapolis and data through 1971 are
in Storet.
In addition to the water monitoring stations, there have
been several field data programs conducted to sample bottom
sediments and analyze them.
The following sections discuss the individual data sources
and point out the gaps in the data insofar as the present project
Is concerned, in order to plan supplemental sampling program for
the purpose of filling those gaps.
6.2 U.S. EPA - Generated Data
The major internally generated U.S. EPA water quality data
consist of measurements at sampling stations designated as CAL01
through CAL17 in the Calumet area. (See Figure 6.1 and Table
6.1 for station positions.) These are located along the Grand
Calumet River, Little Calumet River, Wolf Lake and some near-
shore areas of the southern part of Lake Michigan. These data
are available for the years 1965 through 1973 and are in Storet.
The most extensive EPA measurements were conducted from 1966
through 1969. Since then sampling has been done only during
46
-------
B o
en
z
o
o
o
Figure 6.1
LOCATION MAP EPA WATER QUALITY SAMPLING STATIONS CAL01-CAL17
47
-------
Table 6.1
U.S. EPA WATER QUALITY MONITORING STATIONS
IN CALUMET AREA
Station No.
CAL' 01 (170 141)
CAL 02 (170 160)
CAL 03* (170 149)
CAL 03A (170 153)
CAL 04
CAL 05
CAL 06
CAL 07
CAL 08
CAL 09**
CAL 10
CAL 11
CAL 12
CAL 13
CAL 14
CAL 15
CAL 16
CAL 17
(170 150)
(170 152)
(170 198)
(160 177)
(160 147)
(160 189)
(160 188)
(160 178)
(160 141)
(170 197)
(170 117)
(170 201)
(170 200)
(160 650)
Station location
Grand Calumet River & Penn-Central R.R.
Indiana Harbor Canal & 151st St.
Indiana Harbor Canal & Dickey Road
Mouth of Lake George Branch, Indiana
Harbor Canal
Indiana Harbor Canal Mouth pier Head Light
Indiana Harbor breakwater Inner Lights
Indiana Harbor Breakwater Inner N-E Light
Grand Calumet Control Park Indiana Harbor
Belt R.R.
Little Calumet Point & Wentworth Avenue
Wolf Lake Control State Line Culvert
Wolf Lake Channel at Carondolet Avenue
Calumet Harbor Mouth North Pier Light
Calumet Harbor Mouth of River
Calumet Harbor Midchannel Outer
Gary-West Water Plant Intake
East Chicago Water Plant Intake
Hammond Water Plant Intake
Chicago South Water Plant Intake
Note: U.S. EPA Agency No. is 1115G050 for Storet
*CAL 03 corresponds to Indiana Station IHC-1, Agency No. 21 IND
for Storet
**CAL 09 corresponds to Indiana Station W6-SL Agency No. 21 Ind
for Storet.
48
-------
brief periods in each season. Plots of these data through 1973
have been obtained and are presented in Chapters 13 through 18.
Our main use of the Storet plots was to help relate the
pollutant concentrations in the Lake waters to the corresponding
concentrations flowing from the major input source, which is the
Indiana Harbor Canal.
A predecessor to the U.S. EPA was the U.S. Public Health
Service and the Federal Water Pollution Control Administration.
Extensive surveys of the quality of Lake Michigan waters were
contained in Physical and Chemical Quality Conditions (FWPCA 1968),
and in Report on Water Quality of Lower Lake Michigan (FWPCA 1966),
as well as published summaries by Risley and Fuller (1965, 1966).
Also in Storet are water quality data obtained in 1963 for
more than 150 stations located in open water near the shore of
the southern part of Lake Michigan. We were not able to relate
these data to flow of effluents from IHC or ether sources.
6.3 Indiana Water Quality Data
In 1957, the State of Indiana initiated a water quality
monitoring program. The original sampling network included two
stations on Lake Michigan. At the present time, there are 16
sampling stations located on tributaries to Lake Michigan. In
addition, five water treatment plant intakes on Lake Michigan
are sampled as part of the program (Table 6.2 and Figure 6.2).
These data are in Storet through 1971 and applicable plots are
included in Chapters 13 to 18. This sampling program provides
data that are used to measure general characteristics of Indiana
waters in the Lake Michigan Basin at important locations and to
record trends in water quality. No other data are available for
the eastern portion of the Calumet area.
The Indiana program has been expanded to include the collec-
tion of samples from various industrial outfalls and run-off from
landfills. For the most part, these samples are collected during
49
-------
Ln
O
Illinois 1
Indiana
Michigan
I *" - T • « *,'S.**%f' ? "*,
-
Figure 6.2
INDIANA WATER QUALITY MONITORING STATIONS IN CALUMET AREA
-------
Table 6.2
INDIANA WATER QUALITY MONITORING STATIONS
Great Lakes Drainage Basin
Sampling Frequency: Biweekly
Station No. Station location
BD 0 Burns Ditch at Mouth (Midwest Steel Co. Catwalk)
BD 1 Burns Ditch at Midwest Steel Truck Bridge
BD 2E Burns Ditch East Branch at Chrisman Road
BD 3W Burns Ditch West Branch at Portage Boat Yard
GCR 34 Grand Calumet River in Hammond
GCR 36 Grand Calumet River in East Chicago at
Indianapolis Blvd.
GCR 37 Grand Calumet River in East Chicago at
Kennedy Avenue
GCR 41 Grand Calumet River at U.S. 12 in Gary
IHC 1 Indiana Harbor Canal at Dickey Road in
East Chicago
IHC 3S Indiana Harbor Canal, South Branch at Columbus
Drive in East Chicago
IHC 3W Indiana Harbor Canal, West Branch at
Indianapolis Blvd
LRC 39 Little Calumet River, East leg at SR 149 in
Porter
LM EC Lake Michigan at East Chicago water intake
LM G Lake Michigan at Gary water intake
LM H Lake Michigan at Hammond water intake
LM M Lake Michigan at Michigan City water intake
LM W Lake Michigan at Whiting water intake
51
-------
comprehensive 24-hr surveys of point discharges. These data are
available at Indianapolis, and were used by CBE to check permit
application data (Appendix C), but are not yet available through
Storet, Water quality data and effluent loads in the Grand
Calumet R.iver/IHC system were recently compiled for the State of
Indiana by Combinatorics (1974), including Indiana State data.
6.4 The Metropolitan Sanitary District of Greater Chicago
Data
The Metropolitan Sanitary District of Greater Chicago (MSDGC)
has conducted several studies of water quality, sediments and
benthic organisms in Calumet Harbor and the IHC and the adjacent
Lake since 1967, but the data are mostly not available to this
project. The measurements were made in support of lawsuits that
are still pending against several steel companies in the area,
primarily Inland, Youngstown, and U.S. Steel. Samplings comprise
24-hr composite effluent samples, water quality samples and bottom
sediment analyses.
605 Chicago City Raw Water Data
The city of Chicago has conducted intake water analysis since
1880, and detailed records of the raw water quality are available
from 1945. The data include detailed daily analyses of raw water
from both the south and central water intake cribs. Extensive
data are also available for samples taken from the Hammond water
intake on a daily basis from 1967 through 1971, and less frequently
since then; and from samples taken about weekly from East Chicago
and Gary during the same period. These data are in the Chicago
Water Department library; aside from examining them to determine
that they show pollutant peaks similar to those exhibited by
Storet plots, we were not able to make as much use of them as
they deserved, due to their sheer magnitude. The South Water
Intake data are the most extensive, and have been plotted over a
period of years. We updated the available plots, and used them
in Chapters 13 to 18 to establish trends of water quality in the
Lake.
52
-------
Since 1966 the Chicago Water Dept. has had a program of
water sampling from a boat. The four surveys are called the
North Shore Survey, the South Shore Survey, the Central WFP Radial
Survey and the South WFP Radial Survey. The South WFP Radial
Survey stations are shown on Figure 6.3. We made extensive use
of the two south surveys, and plotted much of these data to show
that peaks of pollutant concentrations in the Lake could be
related to likely locations of the plume from IHC (Chapters 13
to 18). Not all the peaks or unusual high values can be definitely
tied to particular sources because data are not available to
determine the motion of the plume from IHC or other sources.
Furthermore the concentrations and flow of the IHC were not
measured on the same days as the Lake surveys. (On a few days
the reports of these survey's contain sketches showing observations
of the plume. Some reports contain wind observations.) The
annual reports of these surveys are in the Chicago Water Dept.
Library.
The Chicago Water Dept. also conducts weekly samplings and
analysis of stations in the tributary waters of the IHC, Grand
Calumet River, and Calumet River. This is called the Calumet
Area Industrial Survey. We used some of these points to measure
the trends in water quality in these tributaries, and selected
data are plotted in Chapters 13 to 18. Some of the other stations
were of limited value because we could not relate them to effluent
sources. In particular, flow data would be needed on the sampling
dates to establish stream loadings. We have keypunched a few
recent years of the Radial and Calumet Industrial Survey data
for Storet, but mostly we relied on hand-generated plots of data
averages.
6.6 State of Illinois Data
The State of Illinois has conducted a shore survey since
1970 (Illinois EPA, Lake Michigan Open Water and Lake Bed Survey,
1970, 1971, 1972). Beach water samples, bottom samples, and
water samples taken one mile from shore were reported. Since
most of the data lie outside the Calumet area, we made little use
of these data except for comparison with Calumet area data. The
53
-------
Figure 6.3
SOUTH WATER FILTRATION PLANT RADIAL SURVEY
-------
Illinois water quality network is a computer print-out of
measurements in inland streams (available from Illinois Environ-
mental Institute Library). It contains practically no data
applicable to the Calumet area of Lake Michigan.
6.7 Additional Data Sources Surveyed
Table 6.3 lists organizations that were contacted either by
IITRI or CBE with requests for available data. Most of these
supplied some information in the form of reports and other docu-
ments. The applicable information is either summarized in this
report or mentioned in the list of references.
55
-------
Table 6.3
LISTING OF DATA SOURCES SURVEYED
U.S. Army Corps of Engineers, Chicago District
U.S0 Department of the Interior - EROS Data Center
U.S. Environmental Protection Agency - Region V Laboratory
Illinois Environmental Protection Agency
Illinois Water Survey
Illinois Natural History Survey
City of Chicago - Department of Water and Sewers
Metropolitan Sanitary District of Greater Chicago
Businessmen for the Public Interest
Lake Michigan Federation
Great Lakes Research Division, University of Michigan
Great Lakes Basin Commission
Great Lakes Commission
Great Lakes Fishery Laboratory, U.S. Buruea Sports Fisheries
& Wildlife
Center for Great Lakes Studies, University of Wisconsin-Milwaukee
Environmental Research Institute of Michigan, University of
Michigan
Indiana Stream Pollution Control Board
Indiana State Board of Health
Regional Transportation and Planning Commission (Indiana)
Industrial Bio-Test Laboratories, Inc.
Combinatorics, Inc.
Commonwealth Edison Company
Northeastern Indiana Public Service Company
United States Steel Corp.
Youngstown Sheet and Tube Company
Inland Steel
Bethlehem Steel
Midwest Steel
Union Carbide
E. I. DuPont de Nemours and Company
Mobil Oil
Shell Oil
Atlantic Richfield
Illinois Geological Survey
56
-------
7. SEDIMENT POLLUTION AND BENTHIC ORGANISMS
Sediments play a role both in carrying pollutants from the
tributary rivers into the Lake, and in the exchange of pollutants
from the near-shore waters to the bottom.
Suspended solids in the tributaries can come from steel
mills in the form of iron particles or precipitates, from sewage
treatment plants in the form of organic particles or from soil
erosion in the form of minerals. These particulates can be
combined with oil from steel mills and refineries.
Polluted sediments affect the aquatic life in the water, and
studies of benthic organisms can be used to measure pollution.
These subjects are discussed in the following, as well as in
Appendix A.
7.1 Transport of Sediments in IHC
Not all of the pollutants which enter the Grand Calumet
River and IHC are carried directly to the Lake. Some of them
are deposited on the bottom; this is evident from the fact that the
Corps of Engineers finds it necessary to dredge the navigation
channel of the IHC about every two years. The next dredging is
planned for 1974 (Corps of Engineers, impact statement, 1973).
There are two questions to be answered with regard to sedi-
ments in the present study. One is whether the deposition of
sediments is important enough to affect our assessment of
effluent loads. The other is whether the deposited sediments'
can be resuspended during heavy rainfall periods, resulting in
peak pollution loads to the Lake that may not have been measured
by previous sampling programs.
Concerning the first question, Table 4.4 in Chapter 4 shows
that the suspended solids load measured by IITRI at Columbus
Drive is in reasonable agreement with Combinatorics (1974) load
estimates. On the other hand, the composition of the sediments
reported in the Corps of Engineers (1968) study (Appendix A25-V)
indicates that the sediments are primarily of clay or other
57
-------
materials originating from soil erosion; it would therefore be
difficult to use a sedimental material balance to check the point
source effluents. The quantity of sediments dredged in 1967 was
estimated at 72,000 cubic yards (Appendix A25-V). The composition
of the sediments discussed in the next section indicates that
they do contain appreciable amounts of various industrial pollu-
tants, particularly oil and grease. It was also estimated (Corps
of Engineers 1968, p. 103) that the dredging company removed
1750 tons of oil and grease contained in dredging spoils.
To answer the second question would require a very detailed
study of flows and sediment compositions during dry and wet
weather; however, since the flow in the IHC comes mainly from
industrial water pumped from Lake Michigan, we might expect
rainfall to have less effect than it does in other natural streams.
We made one measurement at 8 PM on December 4, 1973, after a rain-
fall of 1.19 in. as recorded at Midway Airport. The measured
flow was 1570 cfs at station IHC3S; this value is within the
normal range of flow for dry weather. The turbidity of a sample
was 23, which is above the normal range of 9 to 15 shown in
Table 11.3 for IHC3S. This suggests that resuspension is not an
overpowering effect. Also, the Corps of Engineers (1968) study
generally concluded that resuspension of sediments during dumping
in landfill lagoons produced less effluents than were contained
in the IHC plume.
7.2 Composition of Suspended Solids and Sediments from IHC
Some data on the composition of suspended solids from IHC3S
can be found in Table 11.3. Suspended solids range from 10 to
20 mg/&. About half of the suspended solids is volatile on
ignition, and less than 19% of the solids is iron. Three samples
from station CAL06 show lower concentrations due to dilution,
but show similar ratios of these components.
Table 7.1 summarizes sediment composition data from the Corps
of Engineers (1969) study. The composition is not unlike that of
tho suspended solids just mentioned, except that the nonvolatile
58
-------
On
Table 7.1
COMPOSITION OF SEDIMENTS DREDGED FROM INDIANA HARBOR
Source: Corps of Engineers (1969), Vol. I., p. 6.45
Lake
George,
Parameter branch
Total solids, % 42.5
Volatile solids, % 20.7
Oil and grease, 70 14.2
BOD, mg/£ 6.24
COD, mg/£
NH3-N, mg/fc
Organic - N, mg/£
Phosphorus - P, mg/a
Main Canal
Grand Penn RR Bridge
Calumet Station nuTnbers
River, T- ~-
branch5 21° I-5C
40.9 73.6 47.5
15.2 9.0 16.1
5.92
4.17 5.25
461
0.07
2.98
1.05
Harbor Channel
Outer Light
Station numbers
18b 12-0
60.5 37.
6.1 6.
0.32 2.
1.13
261.
0.
0.
0.
a
9
6
79
5
26
76
79
1-1
45
6
-
-
117
0
1
0
c
.0
.1
.09
.68
.48
*FWPCA 1967 data, Appendix A7, Appendix A.
•'Lake Survey 1967 data, Appendix A25, Table 3, all values are averages.
'University of Wisconsin data, Appendix C5, Tables A-21 and A-25.
-------
portion is somewhat higher.
Howmiller (Appendix A) reviewed data on the composition of
sediments, both in the IHC and in the Lake. IHC sediments were
reported to have oil and grease contents ranging from 3 to 1770.
Some data on the composition of sediments in the inner harbor
are shown in Figure A-10 of Appendix A.
Howmiller (Appendix A, p„ A-33) reviewed evidence that the
sediments of IHC and Calumet harbors are toxic to certain organisms,
The data are given in more detail by Gannon (Appendix B). It was
concluded that these sediments are so toxic that dredging spoils
should not be dumped into the open Lake. Oil appeared to be the
component in largest concentration, but it has not been established
what substance or combination of substances is most toxic in the
sediments„
7.3 Relation to Dredging
The Corps of Engineers (1973) is required to dredge the
navigation channel of the IHC as far upstream as Columbus Drive.
Dredging can have both harmful and beneficial effects as far as
Lake pollution is concerned.
During the actual dredging operations, stirring up of the
sediments can resuspend pollutants and cause peak loads into the
Lake0 Even more important over the long term is the method of
disposing of the dredging spoils. The disposal can result in
another pollution source.
On the other hand, by removing polluted material from the
channel, dredging can be considered as a way of ridding the
tributaries of polluted matter that might eventually reach the
Lake. This is no substitute for effluent controls, but it might
1 be a way of purging the river of polluted sediments after effluent
i loads have been reduced.
The proposed method of disposing of spoils (Corps of
Engineers 1973) is by barging it to a landfill constructed in
the Lake by Inland Steel Co. This fill is 1 mile by 2 miles in
60
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size, and is presently filled with water enclosed by a revetment.
The revetment is made of cells constructed of steel piling filled
with slag and capped with concrete (Santina and Bochantin,
personal communication 1974). It is not completely impermeable,
especially to fluctuations in Lake level. The amount of exchange
with Lake water is not known.
The Corps of Engineers (1969) study showed that there was
some exchange of polluted water from the lagoon during deposition
of spoils, although the impact on the Lake was less than that of
the plume from the IHC. The effluents from the lagoon were sub-
stantially less after deposition of spoils was completed.
Investigations are underway at the Waterways Experiment
Station (Corps of Engineers, WES Newsletter, 1973, 1974) to
determine better ways of disposing of spoils and to assess their
pollutional impact.
61
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7.4 Lake Michigan Sediments and Relation to Pollution
Sediments in southern Lake Michigan are surveyed by Howmiller
(Appendix A). Figure A7 shows that the coarser sands and gravels
tend to lie in the shallower areas near shore, especially in the
southwestern corner of the Lake. Fine sand particles lie along
the eastern shore, while fines and silt are found in the deeper
central region. Sediment transport is known to occur, and to have
built the dunes in the southern and eastern shores of the Lake.
Shimp and coworkers (1970, 1971) sampled and analyzed the
bottom sediments over the whole southern basin of Lake Michigan.
Few of their samples were taken in the Calumet area. Shimp
(personal communication, 1973) suggested that Lake currents have
a size-classifying action, depositing silts in the central region
(See Figure A7, Appendix A). Presumably the finely-divided
pollutant silts are eventually deposited here as well.
The turbidity of near-shore waters of the Lake increases
noticeably after a storm, indicating that bottom sediments have
been resuspended. Some data showing this effect are given in
Table 17. 6, Chapter 17.
Suspended solids in the Lake include phytoplankton, as well
as solids from the rivers. The role of phytoplankton in extracting
dissolved nutrients from the water has been discussed by Robert-
son and Powers (1965). As the phytoplankton die, they settle to
the bottom, carrying the phosphorus and nitrogen to the bottom
sediments. Mortimer (1971) discussed the exchange of chemicals
between sediments and water in the Great Lakes. The release of
nutrients from sediments is expected to be small, so long as
dissolved oxygen content at the sediment surface does not fall
below 1 to 2 mg/ji . In Lake Michigan the dissolved oxygen content
usually does not fall to low values even in the hypolimnion.
A number of studies have shown that burrowing benthic
invertebrates can have important effects upon the structure of
sediments and upon exchange of materials between sediments and
62
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water. Howmiller (Appendix A, p. A61) mentions such effects
including mechanical overturn of sediments, chemical transfor-
mation of sediment within the gut of the animal, or irrigation of
burrows with consequent changes in the stratification of redox
potential. Laboratory experiments with Lake Michigan sediments
showed that benthic organisms promoted release of phosphorus
from sediments. Research has been insufficient to allow quanti-
tative estimates of exchange rates under actual Lake conditions.
7.5 Sediment Pollution from IHC and Other Sources
Studies done in 1967 of the distribution of polluted sedi-
ments in the Calumet area (Appendix A, Figure AlO) indicated
that the Calumet River and the IHC were the major sources of
polluted sediment in the area. The most recent studies have not
been released for publication, but improvements in steel mill
effluents from the Calumet River are likely to leave the IHC as
the major source polluting the bottom sediments.
The types and species of benthic organisms have been used
to measure the state of pollution in the Calumet area. Howmiller
reviews in detail the available data on the distribution of
benthos (Appendix A, p. A35). Studies based on absolute counts
of various types such as clams or worms generally indicate that
the near-shore areas are particularly polluted, especially those
areas that are close to major effluents, such as the Calumet area;
however, attempts to assess em'ironmental quality through numbers
of organisms of major groups are limited in sensitivity and scope,
because other affects besides pollution have an influence.
Instead, Howmiller (Appendix A, p. A43) shows that by measuring
ratios of the numbers of species within one type, one can rate
the pollutional level of the area sampled. This procedure
normalizes out other factors that affect absolute population
numbers, e.g., type of substrate, scouring of bottom by currents,
etc. Several types of organisms could be considered, but How-
miller considers that Oligochaete worms appear to offer particular
promise for the bioassessment of environmental quality in Lake
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Michigan. He ranks the species of the oligochaetes according to
their tolerance of enrichment or pollution of the environment in
Table A2 (Appendix A). A few studies have been done to assess
the condition of parts of the Calumet area. These are summarized
by Howmiller (Appendix A, p. A49).
Sediments from the Little Calumet River and Burns ditch
showed highly polluted sediments, with paucity of benthos. This
condition appears to be related to the inadequate municipal
sewage treatment reported in Appendix D. In shallow water in the
nearby Lake at Bailly, benthic organisms were found which are
tolerant of pollution. It was concluded that the bottom fauna
of this in-shore region was dominated by forms characteristic of
eutrophic regions of the Great Lakes, but not of highly polluted
regions.
The oligachaete fauna of the Calumet and IHC harbors were
examined by Howmiller in 1967 and 1968. Table A4 (Appendix A)
indicates that this inner harbor region is dominated by a species
that is tolerant of extreme pollution. The composition of the
worm fauna in this region is much like that found in lower Green
Bay, an area which vies with the Calumet area for the distinction
of being the most severely degraded portion of Lake Michigan.
The distribution pattern of benthos clearly reflects the impor-
tance of the IHC as a source of pollution in this part of the
Lake. Any changes in status since 1968 are not known at present.
Howmiller (Appendix A) proposes additional measurements, including
sampling further out into the Lake to gain information on the
extent of the IHC effect.
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:8. IMPACT OF POLLUTANTS ON QUALITY AND USE OF WATER
The presence of a Great Lake is an accident of nature that
makes life more pleasant for millions of people that live along
its shore. The kinds of water-related activities are documer^ed
in a report by the FWPCA (1966), and by the Corps of Engineers
(1969).
The Lake Michigan Basin is abundantly endowed with natural
terrain making it one of the major water oriented recreation
areas in the nation. The preservation and improvement of the
water quality within the Basin is imperative to maintain this
status. The United States Bureau of Outdoor Recreation (1965)
report "Water Oriented Outdoor Recreation - Lake Michigan Basin,"
presents most of the facilities that are available, the problems
that are developing, and the action that must be taken to pre-
serve this natural heritage. There are a total of 625 public
recreation areas in the Basin. Of these, 536 are water oriented.
There are 74 recreational harbors on Lake Michigan. Recreational
areas are scattered throughout the Basin, although the major
concentration of population is in the southern portion. This,
combined with the closing of some facilities due to pollution,
has resulted in crowding of the facilities in the southern portion
of the Basin.
In 1960, there were a total of 82 million activity days of
water-oriented recreation and 94 million activity days of water-
related recreational activities. It is estimated that the demand
for water-oriented activities could increase to 247 million
activity days by the year 2010, if adequate facilities are pro-
vided. The largest activity is swimming. For this purpose, the
waters in the Calumet area are already too polluted, and the
Whiting and Calumet beaches are closed. The problems are caused
.by excessive coliform counts from inadequately treated sewage,
i and combined sewer overflows. Chicago beaches are polluted with
'algal growths. The over-fertilization of the Lake results in
algal growth which makes the water objectionable for body contact.
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Sport fishing is the second largest form of water-oriented
recreation. The Fish and Wildlife Service (1966) estimates
19 million angler days per year are spent in the Lake Michigan
Basin, and expects this number to triple by 2010. The quality
and species of fish depend on the quality of the waters. In
addition, pollution can impair the spawning grounds of fish0
Perhaps the most important use of Lake water is for municipal
water supplies of cities along the shore„ The increasing problems
of treating Lake water to overcome effects of pollution are well
documented by reports of Vaughn (1969) and Vaughn and Reed (1972),
and of course these treatments do not restore the water to its
unpolluted state, and residual tastes remain.
The FWPCA Report (1966) continues: "The value of the Lake
Michigan Basin for recreation and plain aesthetic enjoyment, which
is part of most recreational uses, is difficult to measure. It
is, however, recognized as a significant portion of the economy
of the basin. One only has to look at the premium prices paid
for purchases and rental of apartments or cottages with a lake
view or observe the number of people who will go out of their
way to take a lake shore drive, as opposed to a more direct route,
to get an indication of the esthetic value of Lake Michigan. A
more indirect way of measuring its value is by the amount that
is spent annually for recreation in the basin -- for lodging,
food and recreational equipment such as boats and fishing tackle.
There is no detailed tabulation on this available, but one need
only visit several of the prime recreation areas in the Basin to
see the investment in recreational facilities."
8.1 Water Pollution Problems
The National Academy of Sciences (1969) defines eutrophica-
tion as a state of increased nutrient supply. Lake Michigan is
•now exhibiting some eutrophication of the near-shore waters, as
I evidenced by excessive algal growth. The accompanying changes in
zocplankton and benthic organisms are reviewed in subsequent
sections of this report (Chapter 9, Appendix A, B).
66
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' Evidence for recent changes in species of algae are reviewed
in Appendix A. These may be early hints that the Lake is being
abused by man. Of more direct concern is the excessive growth of
a particular algae, Cladophora, which grows on rocks, breaks up
by wave action, and washes ashore to litter the beaches in slimy
windrows. Cladophora clogs water intake screens and makes swim-
ming unpleasant. When it decays it produces a putrid odor and
provides a breeding place for flies. These effects are documented
in the FWPCA Report (1966).
8.2 Phosphorus Pollution
Many experiments have demonstrated that the growth of algae
can be controlled by limiting the phosphorus nutrient in the water
(Thomas 1972; Schindler 1974). Chapter 17 is devoted to phosphorus
pollution.
The report of the Phosphorus Technical Committee (1972)
analyzes the available data concerning excessive phosphorus
concentrations in near-shore waters and suggests that 0.02 mg/£
total P might be a desirable goal for shore waters. This amount
has been exceeded frequently in measurements near the Calumet
area (Chapter 17).
The most feasible direct action that can be taken is to
prevent the escape of phosphorus from municipal treatment plants.
These are the main sources of phosphorus in the Calumet area.
Indiana has agreed to an effluent limitation of 1 mg/£, which
would reduce P effluents by 90%. Chapter 5 documents the progress
of municipal treatment plants to achieve this reduction. In
addition, Indiana has set limits on phosphorus in detergents.
Chicago's experience with this approach proved that it is
effective (personal communication, MSDGC Stickney plant personnel
1972) . Chapter 17 shows that there has been a 40% reduction in
P effluents in the IHC in the past four years, and the 15-year
upward trend at Chicago SWFP crib appears to have reversed, with
a 20%, decrease in the last two years.
67
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8.3 Bacterial Pollution
The coliform bacteria counts in the IHC are generally at
the level of 100,000 to 1,000,000 per 100 m£, a level which makes
it similar to an open sewer and dangerous to health. A major
reason is that the NH3-N loads on the East Chicago STP from steel
mill discharges are so high that adequate chlorination of the
effluent from the plant would require an excessively costly
amount of chlorine. (See Chapters 5 and 16.) Another reason is
that several of the sewage treatment plants are operating above
capacity and plant improvements have been delayed. Combined
sewer overflows also contribute, especially in the Whiting area.
The Report of the Technical Committee on Water Quality (1970)
documents the closing of the beach at Hammond, Indiana, for many
years, and the frequent occurrences of excessive bacterial counts
at all of the Calumet area beaches at least as far as Rainbow
Beach at 77th St. in Chicago. More recent criteria violations are
presented in Chapter 16.
8.4 Safety of Water Supplies
The reason for concern over coliform bacterial pollution is
that it is an indicator that other sewage pathogens may be
expected. Data are also given in Chapter 16 on the presence of
other sewage bacteria, such as fecal streptococcus and salmonella.
In addition, if parameters such as bacteria, NH3-N, and oily odor
indicate the presence of sewage and industrial effluents, then
there is more likelihood of the presence of other toxic materials
such as PCB's and heavy metals, which were not specifically
investigated in this project.
It is generally assumed that municipal water treatment plants
can be completely relied on to eliminate bacteria and other dangers
that may come from drinking water. An article by Harris and
!Brecher (1974) reviews U.S. Public Health Service reports and
, indicates that some of these plants are not adequately funded,
especially by the smaller municipalities, and are not completely
68
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reliable. We repeatedly visited the five municipal water plants
in the area, and in general, were favorably impressed. The plants
in this area use three treatment methods: coagulation and filtra-
tion to remove suspended solids; chlorination or ozonation to
sterilize, and carbon treatment to remove tastes and odors, we
did notice that the amount of monitoring of plant performance,
especially during off-hours does seem to depend on the size of
the plant. For safety's sake it would seem best to have more
than one line of defense, and cleaning up the effluents to which
the plants are exposed would be very desirable from this point of
view.
8.5 Chemical Pollution
The sources of chemical pollution in the Calumet area are
primarily the steel mills, the oil refineries, and the chemicals,
food, and miscellaneous mineral industries in the area. The
sources and major quantities of chemicals were identified in
Chapter 4. A major source is waste pickle liquor from the steel
mills. This contains iron, both in suspension and solution,
either sulfate or chloride, and large quantities of oil. The
iron forms sediments in the Canal. Phenolic compounds, ammonia,
and cyanides come from coke manufacture by the steel mills. They
are washed into the water from coke quenching and water used for
scrubbing air pollution.
The cyanide level in the IHC is harmful to aquatic life, but
it is quickly diluted in the Lake. Phenols, however, have a
deleterious effect on water quality for municipal use, and Vaughn
(1969) has demonstrated the effect of phenols and refinery odors
(which might include oil) in water at the Chicago 68th St. crib.
See Chapter,14.
Fluoride concentrations in the Canal are high, but concen-
trations in the Lake usually do not exceed standards.
The Canal regularly has slicks of oil, although the amount
of oil is said to be decreased. Some of this oil comes from
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present or past oil refining operations. Oil slicks are fre-
quently seen in the Lake waters outside the harbor. A rain of
coal dust from inefficient coking operations and blast furnaces
regularly occurs over land or water, contributing unknown quan-
tities of organic matter to the Lake. In addition, oil spills
by cargo ships are still being observed, in spite of police action.
The oil pollution directly affects boating in the Harbor
area, but its further effects are hard to document; however, oil
is organically biodegradable, and must stimulate the growth of
bacteria and lower forms of aquatic life that feed on polluted
conditions. Heavy metals are also present, which likely come
from industrial sources, including airborne sources„ Coal is a
known .source of heavy metals, and coal is used in large quantities
by the steel mills. Other parameters are summarized in Table 8.1.
8 o 6 Oxygen Depletion
Whenever organic pollutants are dumped into a stream, such
as thousands of pounds of oil per day, the effect is usually to
stimulate growth of organisms that thrive on pollutants, and
deplete the oxygen level of the stream. Oxygen depletion kills
fish and eliminates desirable species. Examination of Storet
data indicates that there are days when the oxygen content of
Indiana Harbor Canal is essentially zero, but there are also days
when it is close to saturation. This subject is further analyzed
by Combinatorics (1974). Indiana data show pronounced improve-
ments in dissolved oxygen.
Howmiller (Appendix A, Table A- 3 ) indicates that bottom
studies in the IHC in 1965 and 1966 found a paucity of benthic
organisms, and at some stations none at all. (More organisms
are found in the turning basin, because the bottom there is
overlain by less polluted Lake water, as shown in Chapter 12„)
Apparently the conditions in the IHC are highly toxic to most
'kinds of life, except bacteria (Chapter 16). Whether occasional
days of oxygen depletion cause the paucity of life, or whether
there are other causes, has not been determined. In any case,
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Table 8.1
SUMMARY OF WATER QUALITY MEASUREMENTS
STATION 6 INDIANA HARBOR AT EAST BREAKWALL INNER LIGHT
Parameter
Temp. °C
Total Col I.No./IOCM
Fee. Strep. "
Fee. Col i. "
PH
00 mg/l
'BD "
COD "
Ch'orides "
Sulfa+e
NH3-N "
N02-N03-N "
Or^.N i troqen "
Total Phos. "
Sol.Phos. "
D is. Iron "
Total Iron "
Phenol ug/l
0 i I &Greose mg/ 1
Cyanide "
Susp.Sol ids "
Dis.Solids
Conductivity umho/cm
M3AS mg/ 1
Color units
Turbidity "
Number of Samples
Dec 1965
Max. Min. f'leon
10 9 1
22M IM 1 IM
530 310 3bO
_
6.9 6.7 6.8
7.7 7.0 7.5
3.4 2.9 3.1
131 13 87
- - -
61 56 64
1.7 1.5 1.6
.60 .30 .46
0.5 0.2 0.4
.120 .026 .062
.059 .033 .036
-
3. 1 1.5 2.2
24 18 21
0. 18 0 0.06
28 10 17
225 210 220
420 390 400
-
- - -
3
Jan-Dec 1966
Max. Min. l-teon
29 6 16
350V I y 33'-'
1 600 ! 0 1 ;<0
23?-' 10 2'/)0
8.0 6.6
8.0 I.I 5.o
13 1.2 3.7
72 4 16
5.i 921
77 22 51
2.8 .19 1.7
.80 .10 .45
2.7 0 0.6
.456 .026 .061'
.09C .003 .023
_
15 I.I 3.4
422 1.4 21
.35 0 .OP
119 7 23
266 128 225
470 310 372
.35 .05 .15
-
55 1.6 16
51
1
'•' !X. Min. >',< ,jr,
24 3 1 6
'. I'lM 300 55M
B75 2't 200
97r 1 u ) 1 2"
'i.O 6.0
9i o. i ;. :
r. . 8 1.5 4.5
', \ \
40 II .".
V'J 1 ' <.3
4.1 .34 1.7
.i>5 .Q~> .32
r..4 0 1.2
P. 15 .033 . 244
3.26 .006 .0°t.
-
7.7 .7o 2.8
675 0 53
3.3 0.5 1.4
.36 0 .10
28 2 14
274 164 228
500 275 366
.26 .05 .17
703
25 0.2 12
42
J.^n-po,- l«,8
Max. Mi n . Me^r>
27 9 18.6
800S' 400 I22M
900 10 200
II C« 40 9300
« . 2 6.5 7.4
4.T 1.8 5.8
1 1 1.6 3.6
2?Z 1.5 22
39 15 23(1)
61 21 .37
2.5 I.I 1.5(1)
0.6 .24 .-15(1)
0.6 0.2 C.4CI)
.491 .025 .136
.035 .006 .024( 1 )
.33 0 .13
9.0 .83 2.18
33 0 7,4
13 0 2.7
.23 0 .06
34 1 12
267 158 223
420 300 340
.46 .08 .15(1)
802
\9 .15 7.3
37
Jdn-Jjne 1969
N'ax. f-'i n. !/ean
21 5 13
I80M 1800 32M
1600 ;? 260
6300 300 1700
8.5 7.0 7.4
10.0 3.9 6.8
9.1 2.8 4.7
100 3 22
34 21 28(1)
4H 15 32
2.9 I.I 2.2(1)
0.4 O.I 0.3(1)
0.6 0.3 0.4(1)
2.19 .06 .23
_
.45 .06 .17
7.8 .94 2.3
34 7 15
15.8 0 4.6
.79 0 .15
105 2 19
323 200 247
470 309 388
.21 .10 .17(1)
25 0 4.1
7.8 .2 2.0
25
Jan 1971-Jan 1973
Max Min Mean
24 3 14.0
-
-
-
7.8 6.8 7.4
-
21 2 9.1
50 12 25.6
58 31 39.2
27 0.6 2.8
-
_
_
_
..
_
39 1 8.2
13 5 5.8
0.31 0.01 0.096
20 6 18.1
270 170 209
670 295 514
_
20
Crlt»rla"_
Max. Min. MMM
32.3 - *
5000 - *••
100
_
9.0 7.0 7-*58a5
- 2.0 4. IT
_
_
35 - 25
75 - 6°
1.5 - '-°
_ ' -
.
.033 - .016
» — ""
0.30 - °'IS
10 ' - '
— ~ ""
0.10
_
275
05 - 0.3
30 - '0
_ — *
"Indiana Regulation SPC-7
'1)6 samples
(1)6 samples
-------
one can not rely on the dissolved oxygen measurements to indicate
the state of life in the IHC, as can be done in a stream where
BOD is the main form of pollution.
The loading of organic pollutants from the Canal into the
Lake should also result in a decrease of oxygen content of the
near-shore waters due to BOD. Storet data at water intake cribs
does not indicate oxygen depletion, but measurements closer to
the mouth of the Canal might do so. Oxygen depletion near the
polluted bottom sediments is another possible effect. Normally
Lake Michigan does not become anaerobic, even at the bottom in
winter (FWPCA 1968).
8.7 Thermal Pollution
Thermal pollution is not a main subject of this study,
because there are other programs studying thermal pollution of
Lake Michigan; however, there are thermal effects in the Calumet
area. The IHC water is taken from the Lake for industrial and
municipal uses, and is heated by an increment of up to 10°C when
it is returned at the Canal mouth. The resulting buoyancy of
the warmer Canal water affects the motion of the heated plume.
See Chapter 12, where the mechanism of gravity spreading is
discussed. The increased temperature should also increase the
rate of biological activities in the IHC. Temperature measurements
in the plume were conducted during our field sampling program,
and are presented in Chapter 11.
In addition to the IHC, there is also a thermal plume from
the State Line power plant of Commonwealth Edison Co. A few
measurements of the thermal plume from this plant were documented
by Frigo and Frye (1972). A thermal plume is also produced by
cooling water emissions from the U.S. Steel South Works at the
mouth of the Calumet River. The plant takes cooling water from a
slip just inside the breakwater on the Lake shore, and discharges
it into the river close to its mouth and also directly to the
Lake. Other cooling water uses in the area are at Burns Ditch,
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ifrom Bethlehem Steel and Midwest Steel Companies. The Bailly
•nuclear power plant planned at Burns Harbor proposes to use a
cooling tower, and will cause a small thermal plume in the Lake
(AEG Environmental Statement 1973). The existing Bailly fossil
plant causes a somewhat larger thermal plume.
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9. BIOLOGICAL INDICATORS OF WATER QUALITY
Because the biota of lakes and rivers changes gradually with
increasing pollution and eutrophication, it is possible to assess
the quality of the aquatic environment through a study of the
biota. Much publicity is currently being given to constant
monitoring apparatus for chemical parameters. Biologists have
made use of a natural integrating monitoring system for many
years, viz: the community of plants and animals living in the
water.
This chapter summarizes reviews of phytoplankton and zoo-
plankton communities in Lake Michigan in general and the Calumet
area in particular. The summaries are based on the more detailed
reviews by Howmiller and Gannon given in Appendices A and B.
Chapter 7 contains a summary of the benthic organisms, again
based an the Appendix by Howmiller. Chapter 16 contains a brief
summary of the bacterial flora of Lake Michigan, based on How-
miller's review in the Appendix. It also contains an assessment
of bacterial pollution from sources in the Calumet area.
9.1 Phytoplankton
Howmiller (Appendix A) reviews the trends in quantity and
composition of algae in Lake Michigan. Several maps (Figures A2
to A4-) show that the abundance of algae is substantially greater
in the near-shore waters than in the main body of the Lake,
especially near large sources of pollution. The Calumet area is
one of these. Furthermore, the total plankton counts at the
Chicago water intake has been increasing regularly as shown in
Figure A5 from 1926 to 1958. Further increases since then have
been reported by Vaughn (1969). This is a further
indication that the nutrient level of this area has been increas-
ing.
Further evidence of deterioration is shown by changes in
the dominant species and types of flora. There are definite
differences between the in-shore and off-shore species, which are
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related to abundance of nutrients in the in-shore waters. There
are changes in the composition of the diatom population as well
as increases in the proportion of blue-green algae to diatom.
Species of diatoms which are favored by eutrophic conditions have
increased in relative abundance in recent years. Changes in the
diatom flora of the Lake appeared first in near-shore waters and
virtually all near-shore waters now have a flora radically
different from that indicated by the earliest samples taken 90
years ago. Collections from the Chicago area in 1876-1881 con-
tained most of the species which now are found exclusively in
the open Lake, although some of the species which are now
characteristic of in-shore waters were also present. This pattern,
of new introductions to the flora appearing first in near-shore
waters and later spreading to the open Lake, was taken as evi-
dence that the changes are caused by nutrient pollution and not
natural phenomena. (See Appendix A.)
There is also recent evidence that silica is sometimes
limiting the growth of diatoms in Lake Michigan. This is due to
added amounts of phosphorus, presumably the usual limiting
nutrient at most times in the past, allowing diatoms to use up
the available silica. Thus, it can be expected that the compo-
sition of the planktonic flora will shift from near complete
dominance of diatoms to a greater proportion of the less desir-
able nonsiliceous green and blue-green algae. Major changes
appear to be happening first in the southwestern section of the
Lake. Abundant plankters of certain taxa have caused problems
for water supply around southern Lake Michigan. Problems include
fishy odors and filter clogging, and even carbonate turbidity.
Howmiller (Appendix A) also reviews the problems resulting
from increased growth of macroscopic algae. These green fila-
mentaceous algae grow on rocks, then break off and are washed up
on beaches. Among these the most prevalent is Cladophora. Its
distribution is correlated with nutrient-rich water. Phosphorus
75
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is considered to be the limiting nutrient in most situations.
We can expect continuing problem growths of Cladophora in direct
proportion of the input of nutrients, especially phosphorus.
9.2 Zooplankton
Gannon (Appendix B) has reviewed available information on
the ecology of Lake Michigan zooplankton. These tiny animals are
part of the food chain, since they feed on phytoplankton, and are
themselves food for fish. These fauna can be used as indicators
of pollution and nutrient enrichment; however, they have been
inadequately investigated in Lake Michigan as a whole, and
investigations in the Calumet area are even more rare. There is
enough information to observe some general trends, and to confirm
other indicators of pollution in the Calumet area.
Extreme reduction or absence of zooplankters in a given area
will be a good indication of toxic pollutants. On the other
hand, numbers of a few species in a certain region will be a good
indication of nutrient enrichment (Appendix B, p. 48).
9.2.1 Lake-Wide Effects
To obtain a general picture of the zooplankton, Gannon con-
sider studies throughout the Lake. Comparative studies over a
long period of time would show long-term trends in pollution, but
early studies are incomplete„ Some extensive studies (Appendix B,
p. 7) were done in 1955. Later studies in 1966 and 1968 showed
changes, but these could be due to alewife predation as well as
to pollution occurring in the meantime.
Another comparison is between in-shore and mid-Lake (or
off-shore) waters. In general (Appendix B, p. 12) it was noted
that oligatrophic off-shore waters of Lake Michigan contain high
ratios of calanoid copepods relative to cladocerans and rotifers,
.and the opposite is true for the more eutrophic in-shore waters.
In the Milwaukee harbor region (Appendix B, p. 8, 16) it was
noted that higher numbers of zooplankton reflect a response to
76
-------
nutrient enrichment of the near-shore waters by the discharge of
municipal sewage, industrial wastes, and storm water run-off from
the Milwaukee River watershed. Green Bay represents another
polluted area, which nay indicate the pattern of changes likely
to occur in the Calumet area. The large biomass of zooplankton
in Green Bay is partly attributed to nutrient-laden waters from
the Fox River, and partly to zooplankters that are carried into
the Lake by the River. This last effect is very unlikely in the
vicinity of the IHC, because the IHC has not been reported to
harbor any zooplankton life.
The most extensive data on plankton in the Calumet area are
those of the Chicago Water Dept. Measurements were made as far
back as 1879, and have been made regularly since 1926. Unfor-
tunately, zooplankton were not usually separated from phyto-
plankton. If zooplankters are mentioned at all, only data for
the most common genera of rotifera, copepoda, and clodocera are
mentioned. Although these data have been adequate for purposes
of water filtration plant operations, they are not adequate for
detecting long-term changes in zooplankton species composition
and abundance commensurate with changes in water quality. Never-
theless, examination of the raw data might be a worthwhile
project.
9.2.2 Calumet Area
A few Lake-wide studies (Appendix B, p. 24) include measure-
ments in the Calumet area, including Gary and Michigan City.
The abundance of zooplankton at all stations in Indiana waters
were considerably higher than values reported for elsewhere in
Lake Michigan. In fact, the biomass in 1972 was ten times higher
than values reported elsewhere. Comparable numbers have been
reported only in Milwaukee harbor and in Green Bay (Appendix B,
p. 31). The zooplankton Crustacea community in the Indiana
waters was characterized by low numbers of calanoid copepods
relative to cyclopoid copepods and cladocerans. A number of bar
77
-------
graphs showing these ratios are included in the Appendix. These
ratios indicate a response by the zooplankton community to
nutrient enrichment of the Indiana waters of Lake Michigan. A
similar response by rotifers is reported (Appendix B, p. 40).
The question may be asked why we should be concerned if one
form of zooplankton supplants another due to increasing pollution
of the water by man. One reason is that we can use these changes
to measure the general level of pollution in an area such as the
Calumet, both over time and in relation to cleaner portions of
the Lake. Another reason is that the plankton serve as food for
fish (Appendix B, p. 18). Changes in the composition of the
plankton population are known to result in changes in fish popu-
lations. This has not been a part of the present study, but it
would be of concern to the many people who make use of the Lake
for sport fishing. Another concern is that toxic materials may
be carried along the food chain and be concentrated in fish. The
Calumet effluents have not been implicated as an important source
of toxic materials in fish, but the subject has not been studied
to our knowledge. The bottom sediments of the IHC area have
been shown to be toxic to zooplankton, however (Appendix B, p. 42).
Gannon (Appendix B) concludes that our knowledge of the
zooplankton ecology of the Calumet area is woefully incomplete.
To estimate general patterns, it is necessary to reason by
analogy with similar waters elsewhere. There is insufficient
data on zooplankton in the Calumet area to demonstrate water
quality degradation. Gannon (Appendix B, p. 49) recommends field
studies to analyze zooplankton community structure, including
taxonomic identification to the species level. He also recommends
laboratory bioassay studies using zooplankton to determine response
to effluents in the Calumet area.
78
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LAKE CURRENTS
The currents in Lake Michigan have been extensively studied.
They are complex, and a number of controversies persist; yet the
major outlines are known. These are set forth in reports by
FWPCA (1967), by Mortimer (1968, 1971), and by Noble, Huang and
Saylor (1968). Although we are concerned primarily with the
southern tip of Lake Michigan, most of the work describes the
main body of the Lake. In fact, little is known about the currents
in the southern tip.
10.1 Thermal Structure
The seasonal structure of temperatures underlies the current
behavior (Noble, Huang and Saylor 1968). During summer the Lake
is stratified; the depth of the warmer epilimnion increases with
the season. The thermocline is a density barrier that prevents
mixing (except for up-welling) with the winter-cooled water below.
In September the surface begins to cool, and by late autumn the
thermocline becomes so weak that vertical mixing is possible.
Temperatures become uniform near 4°C, the temperature of maximum
density. In winter, the surface falls close to 0 C, but the
smaller winter density gradient is a less effective barrier to
mixing.
The warming process, beginning in April-May, is most noticea-
ble near the shore. The shore heating results in a cellular
convection effect that has been named the "thermal bar." The
shore water, heated above 4°C, meets very cold surface water
further out; at some distance from shore, this produces a mixture
at 4°C. This maximum density water sinks, setting up a warm
convection cell near the shore, and a cold one over the remaining
stratified surface water. There is no vertical stratification
to prevent mixing; the shore water leads the rest of the lake in
temperature, and there are vertical isotherms. Eventually, the
bar extends to mid-lake. As summer approaches, the surface waters
are again heated, and the strong summer thermocline develops over
the whole Lake.
79
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10.2 Causes of Lake Currents
There are several major forces that result in Lake currents
(Mortimer 1971). The first of these is thermal convection,
resulting from the greater rate of temperature rise of near-shore
water. The second is the surface stress of wind acting on the
water, The third is the Coriolis force, or the inertial effect
of water currents resisting change of direction resulting from
the earth's rotation. A fourth results fron the flow-through from
tributaries to the outlet at Lake Huron, but this is negligible.
In addition to these forces, the currents are dominated by
boundary effects due to the shores, the thermocline, and topo-
graphical features„ A persistent feature is the strong currents
that flow along both eastern and western shores (Ayers 1959).
Convection currents of warmer shore waters flow outward in
spring, but the Coriolis effect turns Lake currents to the right
(Mortimer 1971; 1959)„ The amount of deflection due to the
Coriolis effect is a function of the boundary stress, i.e., depth.
Consequently, the deflection may approach 45 in deep waters, be
closer to 30° in moderately shallow water, and there may be little
or no deflection in shallow areas (Beeton 1974). Thus convection
can cause currents along the shore. Huang (in Ayers, Huang and
Saylor 1968) proposed a mathematical model including these effects,
but excluding wind stress. This model explains many persistent
features of currents, but it cannot explain the daily changes in
current pattern that are observed. To explain these, one must
invoke wind stress.
Mortimer (1968, 1971) has given the best picture of currents
including wind effects. Wind tends to blow warm water off one
shore toward the other. Because of the Coriolis effect, winds
from the north and east move warmer water to the western shore;
those from south and west move water to the eastern shore.
Extensive bathythermograph data by Mortimer (1968) show that such
winds tip the thermocline, and if winds are strong enough they
80
-------
cause upwelling of cold bottom water to the left of the wind
direction. Another effect is the piling up or "set-up" of wind-
driven water on the opposite shore. There may be downwelling,
as well as flow along the shore toward the end of the Lake.
10.3 Current Data and Trends
In the south basin the shore set-up results in a character-
istic gyre (Ayers et al. 1958; Ayers 1959), which can give rise
to one or two large eddies, driven like gears in the Calumet
region. Likewise typical eddy patterns arise in the north basin
as a result of its special shape. These shore and eddy currents
can go in directions opposite to the wind, but Ayers (1971) claims
to be able to explain the primary currents in terms of the wind
vector modified by the Coriolis angle, plus the shoreline set-up.
Very close to the shore, inside of these major currents, there
is often a local current that follows the normal wind direction
along the shore, opposite to the direction of the larger gyre or
eddy further out (Ayers 1959).
Several experimental techniques have been used to gather
current data. Drift bottles containing a return postal card were
used by Harrington (1895), Van Oosten (1963) and Johnson (1960).
These studies showed the persistent northward current along the
east shore, and are consistent with the picture of gyres and shore
currents described above. Mortimer (1968) described bathythermo-
graph data obtained from rail ferry crossings in 1964. Ayers
(1959) carried out extensive similar measurements using eight
boats to make simultaneous crossings. These gave a picture of
the thermocline and its tilt due to winds.
Noble et al. (1968) also deduced the currents from the
thermal data. The method is based on a plot of geopotential, or
dynamic height. A region of colder, higher density water near
the surface is like a local hill, and must indicate flow ax^ay
from this point. Although the data are indirect, Ayers et al.
(1958) used it to construct current charts that agree reasonably
well with those prepared by other methods.
81
-------
FWPCA (1967) set a grid of water current meters at numerous
depths in the Lake (but not in the top 10 m). These meters
recorded local currents over a period of months including winter.
The most prominent features were the cyclic and rotating currents
representing the passage of internal waves on the thermocline,
with periods of 2 to 17 hr. These waves are a separate subject
that have only secondary effects for our purposes. They compli-
cate the interpretation of current meter data as well as data
from vessel traverses. FWPCA (1967) used time-series methods to
average out the wave effects. The report presents maps that show
currents averaged over several months in summer and winter with
H/E winds or S/W winds. These are valuable because they repre-
sent true average data, not generalizations from a few cases;
however, they do not show the variations that occur in the currents
although this information was undoubtedly recorded. Also, only
a few current meters were located in the Calumet area of interest
to us, and these were considerably off-shore. Therefore, the
maps do not reveal local conditions in the Calumet area.
10.4 Summary of Currents
From the above discussion, we can conclude a thermocline
should seldom be formed in the Calumet area of Lake Michigan,
because it is too shallow, being only 7-15 m depth out to a
distance of 10 km. Currents can be either north or south along
the shore. They will tend to be as indicated on the FWPCA (1967)
maps, but can be in any direction. Flow out from the shore has
even been observed at Chicago, and may be possible in the Calumet
area. A wind-driven current close to shore can even move in a
direction opposed to a larger gyre several km out from shore.
Current velocities of 5 to 15 cm/sec (0.2 to 0.5 ft/min)
' are typical in Lake currents„ Fifty cm/sec currents have been
recorded, and near-zero velocities occur as well. Saylor (1968)
: reported currents off Calumet Harbor of 18 and 15 cm/sec.
82
-------
10.3 Diffusion Coefficients
A few measurements have been made of turbulent diffusion
coefficients in Lake Michigan. Huang (in Noble, Huang and Saylor
1968) reported experiments on the dispersion of rhodamine red
dye off Benton Harbor, which gave diffusion coefficients around
500 cm/sec2 in the horizontal direction. Coefficients in the
vertical direction are expected to be 1/100 to 1/1000 as large.
Unfortunately the weather and current regime at the time of the
test was not reported. It should be clear that wind and currents
will lead to rapid mixing, or a high diffusion coefficient; other
conditions such as thermal stratification tend to prevent mixing.
Conditions of very slow currents will result in little mixing.
Conditions of high shear, where one current deflects from another
or from the shore, or conditions of cellular convection, should
give rapid mixing. Since there are few data on diffusion coeffi-
cients and wide variations are possible, one should try a range
of diffusion coefficients in our model that are consistent with
expected or known current conditions.
10.6 Current Measurements During This Program
Currents were measured for a period of one month at two
locations as part of our field study. The methods of measurement
and the resulting data are presented in Chapter 11. The conclu-
sion was reached that the currents near shore do not follow the
same rules as for currents far out in the Lake, because of the
influence of the shore. Generally the currents travel along the
shore either in a northerly direction, or in a southerly direc-
tion. The direction depends on the wind, but is not necessarily
in the wind direction; any wind to the north will tend to cause
a current to flow to the north. When the wind is to the ..orth
east there may be a slight off-shore component of the current,
but this is difficult to determine because of the possible effect
of the Calumet harbor breakwater. The current at 19 ft depth is
in nearly the same direction as the current at 9 ft.
83
-------
On November 14 and 19 the current was measured vs depth at
68th St. crib (see Table 10.1). The data check the moored current
meter. The data for November 19 show only slight variation of
direction with depth. The data of November 14 show larger varia-
tion with depth; this may be related to the observation that the
current was changing direction at that time.
The current generally drops to zero speed when it changes
direction in response to a wind direction change. On a few
occasions the current was observed to travel directly off-shore
for a few hours, and this occurred at a time when the current
was shifting direction. The observed direction of the plume of
effluents from IHC was the same as the direction indicated by the
current meters.
In general, the currents in the Calumet area appear to mainly
follow the shore, in the general direction of the wind.
84
-------
Table 10.1
CURRENT METER MEASUREMENTS
AT 68th ST. CRIB (CAL17)
Depth,
m
1
2
3
4
6
8
10
1
2
3
4
6
8
10
Speed,
knots
November 14, 1973
0.1
0.11
0.09
0.06
0.09
0.10
0.08
November 19, 1973
0.1
0.1
0.1
0.07
0.07
0.03
0.01
Direction,*
degrees
9:40 A.M.
330
315
320
305
290
270
270
9:15 A.M.
170
190
170
180
180
160
160
^Direction parallel to shore is 335° or 155'
85
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11. IITRI FIELD SAMPLING PROGRAM AND DATA
11.1 Objectives and General Plan
During the period from November 5, 1973 to December 8, 1973,
IITRI conducted a program of field sampling in the Calumet area
of Lake Michigan. The purpose was to obtain data on near-shore
water quality, simultaneously measuring currents and locating
the plume from the Indiana Harbor Canal. This allowed us to
relate the water quality to the Canal effluents, and thus fill a
gap in the data.
It was apparent that a comprehensive file of water quality
data was already available from other agencies, and the objective
was not merely to add to it. In analyzing available data via
Storet, we found it difficult to relate the near-shore water
quality to the known effluent sources, because hydrodynamic
conditions in the Lake were not measured simultaneously with the
water' quality. Consider for example the region near Indiana
Harbor, where the main source is the Indiana Harbor Canal. On
any particular sampling day the Lake currents could carry the
plume from this canal either up-shore toward.Chicago, or down
toward Gary, or even out into the Lake. Without knowing the
direction of movement of the plume, it is difficult to say
whether data measured at some station represents pollution coming
directly from the Canal, or from some other source such as the
Calumet Harbor, or even represents the general level of the near-
shore waters built up over time from a number of sources.
We also noted that available measurements of water quality
in the Lake were often not combined with measurements of the
flow and quality of water into the Lake at the mouth of major
tributaries. This information was needed to relate water
quality to effluent loadings.
36
-------
In addition, there is a lack of direct measurements of
currents and dispersion parameters needed for any model of
pollution dispersion in the near-shore Calumet area. Only a
few current measurements are reported by Saylor (1968). Other-
wise, one must extrapolate from measurements made further out in
the Lake, for example by FWPCA (1967). Our objective was to
obtain as much data as possible to tie together these effects of
water quality, effluents, and Lake currents or dispersion,
within the available budget.
It appears that there is also a gap in the biological data,
in that the species have not been analyzed to indicate the state
of pollution in the area. Biological sampling was planned at
the same time as chemical sampling, to give an independent
measure of the state of pollution. This was not done because
we were not able to arrange for a suitable boat for biological
sampling.
Our objective was not merely to add data to the compre-
hensive data file already obtained by other agencies, or being
obtained. We did not attempt to measure all parameters, but
concentrated our efforts on a few representative parameters of
each type. We included types that would have different dis-
persion behavior, such as dissolved, suspended, biologically
active and inert; and also tried to include pollutants most
important for their effects on the Lake.
The study area includes several streams tributary to the
Lake, as well as the southern part of the Lake from the 68th St.
Chicago water intake crib to Burns Harbor, Indiana. Sampling of
these tributary streams was currently being done by the State of
Indiana, more extensively than we could do. In addition, the
U.S. EPA takes samples at infrequent intervals. Therefore, we
did not plan detailed sampling at points along the streams.
37
-------
The objectives of the program are related to the importance
of the various portions of the waters in the region. Some of the
streams are of very poor quality, with high bacteria counts and
conditions toxic to life. Their improvement to reasonable
aesthetic quality is very important; however, these streams are
limited in extent, and are not so important as the Lake itself.
The alarming deterioration of the Lake, especially its near-shore
waters, is documented in a report of the U.S. FWOA (1968). For
these reasons, it is important to determine the response of the
near-shore waters to immediate pollution sources, both by modelling
and by sampling. This will help the EPA and the State of Indiana
to determine either effluent limitations, or water quality require-
ments in the Indiana Harbor Canal that will lead to restored
Lake conditions.
In planning the field studies, we received excellent advice
and cooperation from personnel of the Argonne "lational Laboratory,
who worked for us on a subcontract relating to the field sampling.
(See Acknowledgments.) Various means for measuring, the IHC plume
were considered, such as dye injection, drogue measurements, and
continuous monitoring at the mouth of the IIIC. TIe finally
selected the following methods: (1) sampling of water at pre-
determined Lake stations from a boat, (2) in-situ measurements at
various depths at the same locations, (j) sampling from public
water supply intakes in the area, (4) visual and photographic
observations of the plumes from an airplane, and (5) measurement
of currents in the Lake by installing current meters at two
locations.
11.2 Water Sampling and Boat Measurements
11.2.1 Location of Sampling
Our plan was to concentrate our efforts on the effluents from
the IHC, and its impact on the near-shore waters of Lake Michigan.
Therefore, most of our measurements were made in the Lake in the
region where the plume was expected. See Figures 11.1, 11.2 and
Table 11.1 for sampling station locations. Some stations were
83
-------
Figure ll.l
DETAILED MAP OF STATIONS FOR IITRI FIELD SAMPLING
89
-------
CAL17
Water Intake •
NORTH
t
3 4
miles
AL13
CAU\ O 4J
Figure 11.2
MAP OF STATIONS FOR IITRI FIELD SAMPLING
-------
v£>
Table 11.1
WATER SAMPLING STATIONS - CALUMET AREA
GAL 17
GAL 13
CAL 11
CAL 06
CAL 16
CAL 15
CAL 14
LM 47A
SWFP 4J
SWFP 5J
SWFP 6J
SWFP 7J
LM 70
LM 68
LM 80
LM 102
IHC 3S
68th St. Crib
Calumet Harbor
Calumet R. mouth, north pier head light
Indiana Harbor breakwater inner NE light
Hammond water intake
East Chicago water intake
Gary West water intake
Whiting water intake
(American Oil intake)
Chicago Water Dept. open Lake
EPA open Lake stations
Indiana Harbor Canal at Columbus Drive
Current meter near Inland landfill
Current meter near 68th St. crib
Latitude
41 41 11
41 44 06
41 44 02
41 40 28
41 42 14
41 39 45
41 38 27
41 40 50
41 43 28
41 42 26
41 41 23
41 40 21
41 41 35
41 41 28
41 42 5
41 43 25
41 38 20.7
41 42 14
41 46 81
Longitude
87 32 22.5
87 31 16
87 31 45
87 26 20
87 29 49
87 24 18
87 20 28
87 28 22
87 28 17
87 26 31
87 24 45
87 23 00
87 27 15
87 25 42
87 24 55
87 23 15
87 28 16.8
87 24 34
87 31 84
-------
also located where they would measure the influence of other
sources, such as the Calumet River. Measurements were also made
at the mouth of the IHC and the Calumet River, to determine the
total amounts of effluents entering the Lake from these sources
and to check the information on loads obtained from the permit
applications. Measurements were also made at Columbus Drive on
the IHC, to measure the load of effluents from sources above
this point, particularly on the Grand Calumet River.
Most of the Lake samples were obtained from a boat. At
this time of year, the weather limits access to the Lake in a
small boat, and in fact there were only three suitable days in
a one-month period. So that we could have a more continuous
record of water quality, the boat samplings were supplemented by
samples obtained from five public water supply intakes in the
area. These are indicated on Figure 11.2 as
CAL17 Chicago SWFP
CAL16 Hammond WFP
LM047A Whiting WFP
CAL15 East Chicago WFP
CAL14 Gary WFP (Hobart Water Co.)
In each of these plants there is a tap, from which a sample can
be drawn of the raw water from the intake crib. We drew the
samples, and analyzed them.
In addition to taking samples from the boat, a Hydrolab
instrument was used for in-situ measurements. This instrument
permitted us to measure a few water quality parameters at various
depths, in addition to the more extensive measurements made on
a sample taken at 1-meter depth. The in-situ measurements were
temperature, pH, dissolved oxygen, conductivity, and chloride
ion concentration. The conductivity and chloride measurements
made in this way were calibrated by comparison with measurements
made in the laboratory on samples from 1-m at each station. The
92
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dissolved oxygen probe was calibrated against air-saturated
water.
All water samples were taken in 2.5-gal cubitainers.
Because the water was cold at this time of year,and the samples
were analyzed within a few hours, no attempt was made to preserve
them except to keep them in the dark.
11.2.2 On-Board Instrumentation
The Argonne boat used has a cathedral hull, is 18 ft long,
with two 25-hp motors. Position is determined by a Motorola
Miniranger. Two transponders were mounted at known points on
shore. Sampling positions were within 30 m of the station
location. Wind speed and direction were determined from the
boat. Also available was a Bendix Q15 current meter. This was
used to measure current vs depth at 68th St. crib, and also at
the mouth of the IHC.
11.2.3 Shore Sample Treatment
On-shore filtration and analysis of samples was done in
space provided by the Hammond Water Treatment Plant laboratory
by IITRI personnel (see Acknowledgments).
At this laboratory the following measurements were made:
pH, conductivity, turbidity, total coliform bacteria. Two por-
tions of each water sample were also filtered here. The residue
was analyzed at IITRI. Samples of the filtrate were preserved
and analyzed at IITRI. An untreated water sample was also
frozen and subsequently freeze-dried to determine total solids.
Some of these samples were analyzed for phosophorus at IITRI,
and they are preserved for later use.
11.2.4 Analytical Methods
Standard methods used for analyzing the samples are given
in Table 11.2.
93
-------
vd
Table 11.2
ANALYTICAL METHODS FOR GENERAL ANALYSIS OF WATER SAMPLES
Method of measurement
Storet
Temperature 00010
Conductivity 00095
pH 00400
Turbidity 00075
Dissolved 00300
oxygen
Chloride 00940
Fluoride 00950
Ammonia (NHj) 00610
13th Edition
Units of Standard Methods
•C 162
p. 348
umho/cm 154
p. 323
pH units 144A
p. 276
Jackson U3A
units p. 350
mg/1 218F
p. 484
(tentative)
mg/1
mg/1
mg/1
1971
EPA-MCA
296
284
&
230
231
308
60
to
63
-
72
to
75
-
Instrument
to be used
thermisters
Hydrolab
conductivity meter
Hydrolab
llach model 210QA
turbidimeter
Hydrolab
membrane electrode
DO analyzer
Hydrolab D6 with
selective ion
electrode
selective ion
electrode
selective ion
electrode
Sample
preservation
(if any)
none needed -
measure in situ
none - In situ
none - in situ
none - measure
on boat
none - in situ
none - in situ
check in lab
measure in
Hammond , Indiana
water dept. lab
filter & add NaOH -
at Hammond
Brief description of method
Thermisters mounted at various depths from the
sampling boat up to 30 ft.
Instrument standardized with KC1 solution;
values corrected to 25° C; the parameter Is related
pH is the logarithm of the reciprocal of the
measured.
Light -scattering is measured from a sample.
The probe is dependent on electrochemical
reactions. The current or potential is corre-
lated with DO concentrations.
Specific chloride ion electrode will be used to
measure porentiometrically chloride
cone en t rat ions .
Specific fluoride ions electrode will be used to
measure potentiometrically floride
concentrations .
Gas sensing ammonia electrode will be used to
measure ammonia present.
Coments or
other reference
ASTH Standard
ffethods Dim -64
ASTM Standard
(1970)
Sensitivity 0.01
°-1-'1
Sensitivity
0.27 mg/1
Sensitivity
0.019 Ng/1
Sensitivity
0.017 mg/1
-------
Table 11.2 (cont.)
Method of measurement
Storet
number
Units of
measurement
Phosphorus
(total)
Total coliform
Total organic
carbon
Nonfilterable
residue
(suspended
solids)
Chlorophyll
Volatile solids
Iron in
suspension
mg/1
MFIM ENDO/
100 ml
mg/1
00680
(total)
00681
(dissolved)
mg/1
mg/1
mg/1
13th Edition
Standard Methods
No.
223
p. 518
408A
p. 679
p. 287
602A
p. 746
p. 538
129A
p. 211
1971
EPA-MCA
235
to
238
-
221
to
229
278
to
281
-
282
to
283
108
&
109
Instrument
to be used
colorimetry
binocular
widefield
dissecting
microscope
infrared analyzer
Gelman glass
filter
spectro-
f luorimeter
(0.5-5 jm)
ignition
atomic absorption
spectrophotometer
Sample
preservation
(if any)
Freeze on same day
incubation
at 35 + 0.5°C
i 90X RH
2 ml H,SO, /I
(pH * 2}
7 days if
necessary
filter 1-liter
sample at Hammond
on same day
use residue from
above
use residue from
above
use residue from
above
Brief jescription of method
Free?e-dry 500-ml sample and analyze dry residue
for total phosphorus — Robbins, Landstrom &
Wahlgren, Proc. 15 Great Lakes Res. Conf.,
270-290, 1972
Comments or
other reference
Sensitivity
0.0005 mg/1
with precon-
centration
iliform membrane filter is used for filtration
)unt the total coliforms and reports density/
)0 ml >
A lOO-i'l sample is injected into a catalytic
combustion tube. CO, is measured and is directly
proportional t_o carbonaceous material. Subtract
inorganic blank.
Filter sample and dry to constant weight at
Kx tract chlorophyll in acetone from dried material
retained on Gelman filter. Extract and determine
chlorophyll .
Ignite at 550°C and determine weight loss
Dissolve ash in 10 ml 6N HCl.
Precision
1 "K/1
Sensitivity
O.OOl mg/1
0.11 mg/1
-------
11.3 Chemical Results
The results of chemical sampling are presented in Table 11.3,
The first six pages pertain to the three boat sampling days,
November 14, November 19, and December 7. For each station the
first line of data presents the laboratory analysis of samples
taken at the indicated depth of 1 m. Below this are listed the
results of Hydrolab measurements made at several depths as
indicated. Some of the stations were located at water supply
intakes. In this case the final line, identified with an * or
S, gives the analysis of a sample which we took from the intake.
The time at which each sample was taken is given after the data;
the time was different for the boat and intake samples.
Pages 7 and 8 of Table 11.3 present results of samples
taken from water intakes and the IHC station on the remaining
days, when there were no boat samples.
11.4 Aerial Observations
On each day that weather permitted during the sampling
period, one of the project personnel went up in a light airplane
to observe evidence of water pollution. Records were kept by
making logbook notes, making sketches on a map, and taking color
slide photographs. A log listing of the slides was compiled
later. The sketch maps have been redrawn by an artist, and are
reproduced in Figures 11.3 to 11.12.
The usual flight path started at Gary Municipal Airport.
The plane then flew along the Grand Calumet River until it was
over the junction with the IHC. At this point, the direction
of river flow could be seen by the streamlines of colored water.
In every case the flow of both branches was toward the IHC. The
plane then followed the IHC to Lake Michigan. Oily outfalls and
oil spills were noted. The plane then circled over the environs
of the IHC mouth, to observe the location of the plume in the
Lake. Outfall plumes in the turning basin of the IHC were noted.
96
-------
Table 11.3
WATER QUALITY DATA IN IHC AND CALUMET AREA OF LAKE MICHIGAN
MEASUREMENTS FROM IITRI FIELD SAMPLING PROGRAM
November 5 to December 8, 1973
Station
CAL 1 /
C«L17
CAL 17
SCAL1 1
S.FP.J
SWFI-4J
CWF t-i. 1
^fV" '
StoFfSJ
sv»F t-^J
i° CAL 11
CAL1 I
CAL 11
CAL11
C«L13
CAL1 1
CAL 1 3
CALI H
C4L10
CAL ! M
CALI*.
•C»L16
jCj:
L«0*7>
•LM047S
LH070
L«070
LM070
LM070
n£ H
rt C >* 3
"^Q X
731 1141' ItU
Ml ' 1 4 '4411
Mill-'""' 1
7 (|1 !•••"". <>
71 1 1 14111 1.1
7 M 1 1*. 1 1. J '
7 3 ' 11*1, Mil
7311 Ml "3,1
73111»lliHi
731 11-1 lo,|
7311141?4.I
731 1 141^41,
731 1 141?4'i
73ill41i.,|
731 1 141 1110
7311141 J,, o
731 1 1413 !1 1'
7J11141 J'lll
73i 1 l4l ^ « f 1
? - S 5 " g 5 2 . -1
r-< C ^ ^ y-^ T3 i, " .
0§ 5J^ =0 -H g ^^^
MOO CLo^^ -^ 3 ^^-^
« X — E X CE ^ 3 J° *i 76
_.Lj2C « r- ft 3 ^Og^
Qoan5u3 H fe SHS
11.* ".^ ^ /.-, I',-. • ,.1 .,M
1^ .<» " .^ M .•* f^.f Is-t . '1
«.'• '<..- l .-* •!,« /'Mi. ii
"".I I1.'1 '.> X^S..- H.M 0 . 1 ' . il."? .
U . ' • . ' •'' T.I "H . ' .,. 1 V) U.U 1
11. •> '«. j ".0 '.•• i, ......
il.J ..^ r.-* /.- -- i-», •'
U.S ... -.J /.- ,-..,
1 1 .x . -«.l 1 ,. < fl i. .
10. H T.I J,;.0 It.- i-ll, .11 . '•-, I
ll!i> ".1 111." i^.i. ^?n. I
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11.1- ^.? -. 1 ...1 111.,
"•• "" ••" -1 '-'•'
il:i ::i ?:i ':i 1-:' '•"" '•" •
it!.'1 ".^ ^.*» F , i •'a.i
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a.i ii.* ^./ ^ii ." •J-1 "*i<*' u.n^
1^.3 H.'* ••>.<- r-. £\ i. '
f.l M. ?./ ->K... /.S ^.1M < .''3 .
il.4 M.« -.1 -*.j <;iio.i) .1 . 1 1 < i . i t
!<*.<» ''.i *-.) /„. ^00 . '(
1^.* ~.^ /-.^ i" . . eMMj.''
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U C^- "3^ -»-t
_i a 00 H _i jj ^, R o "O
o M o-S 51 » S £
yO °J* « C^O- i-t " -H ?
-S -§ ^ a> S «-S - o^l
3W 3-S 3 § tf 3 "S 3 S?
oSoJ o w i oo o g
Inu.o rt.n , i.i'i ?.20 0.3 7o. y t'o.o
4 • 1.4i| 1.30 0.1 ?0.0 i»0.ll
^.o 11.11 1-j*.': £.?•» i.bo 0.3 Jo.o lo.O
is.!) M.,; 144.0 1.10 j.3o u.j to.u lu.o
»ul,UO.J ll.i . ?."H 4'.bO O.T 40.0 lo.O
* CRIB
S SHORE CRIB SWFP
-------
Table 11.3 Page 2
00
Station
1HC3S_
CAJ.06
CAL06
CAL06
CAL06
LM068
LM06H
(_M06S
LM068
IM06B
LMOHti
LMOHd
1 MO HO
LM080
LM102
LM102
LMlOi?
LM10?
SWKP6J
SHFP6J
SWFP6J
CUC pfc 1
5 wr " o
0
n
0
0
1
n
D
7
7
9
11
10
11
1 (•*
12
12
10
d
8
12
12
13
12
10
11
I?.
11
11
12
12
12
11
11
12
12
li
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.6
HH
7.6
f. J
7.J
7.-*
8.1
H.O
"•2
H.2
n.o
t'. . i
^ 2
-i.i
-t. J
H.i
H. J
H.J
y.o
H.u
H.2
rt.2
H.2
H.£
h.2
8.1
R.4
f>. J
H.3
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M.2
T
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1*.9
1 "3 . ty
l?.b
9.U
10.7
h. /
B.I
10. J
M.*
H.2
H.b
b..-t
b.-i
B.3
9.t5
9.5
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H.b
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223.
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220.
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215.
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21'J.
210.
210.
210.
10
0
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73111*1000 9.0
10.0
» . 1t0 u .0-1 .
2.7 0.0*0 0.0* .
o.uo j.ii
. O.fl90 O.()b .
COLI TOC T-SOL SSOL CHLP-1 V-SOL T-FE D-FE
2*0000.0 l
-------
CO
CJ
60
a
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r-l
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U U l_> U U
-------
Table 11.3 Page 4
Station Y MD HR D-M DO
f,L
CO M
I—1
O
O
CAL16
CALlb
CAL16
CALlb
•CAL16
LM047A
LM047A
I.M047A
LH047A
•LM047A
1HC35
CAL06
CALOft
CALC6
CALOb
LM068
LM068
LM068
l_MOf>8
SWFP6J
SWFP6J
SWFPbJ
SWFP6J
CAL15
CAL15
CAL15
CAL15
CAL15
•CAL1S
SWFP7J
SWFP7J
SWFP7J
SWFP7J
SWFP7J
7311191025
73111910?5
7311191025
7311191025
7311191200
731 1 191 15i>
7311191155
7311191155
7311191155
731 119113d
731119) 100
7311191300
7311191300
7311191300
7311191300
7311191345
7311191345
7311191345
7311191345
7311191545
7311191545
7311191545
7311191545
7311191630
7311191630
7311191630
7311191630
7311191630
7311191030
7311191610
7311191610
7311191610
7311191610
73111916.10
1.0
3.0
5.0
7.0
5.0
3.n
5. o
7.''
5.0
1.0
1.0
3.0
5.C
e.n
1.0
3."
5."
8."
1.0
3."
5.0
a.,,
1.0
3.r
5.0
8.0
10.0
9.0
1.0
3.0
5.0
8.0
10.0
11.5
12.2
12.4
12.6
12!3
12.3
8.0
8.4
9.1
10,7
10.7
11.4
12.2
12. S
10.7
11.6
12.2
12.5
10.9
11.5
11.7
12.5
12.5
11.7
12.4
12.7
13.2
13.3
8.7
B.ti
ft. 6
ft. 5
A.?
8.4
8.4
f',3
H.I
7.6
7.7
7.7
7.7
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H.O
*"* • •!
8.2
8.2
8.2
8.2
8.2
H.2
8.2
8.2
h.2
8.2
8.3
8.3
8.3
H.3
8.3
8.3
8.3
7
7
7
7
"
6
b
H
7
18
14
13
1 d
10
V
9
8
8
b
8
9
9
R
b
8
B
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7
7
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9
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72
40
4U
35
26
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8
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210
210
210
21 u
220
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220
220
2?(>
220
430
310
305
2'JO
255
2 t'O
200
1B8
188
205
2ir
20u
200
210
21?
212
210
205
220
190
190
190
190
190
.0 4.5 '1.120 0.05
.0
.0
.0
.0 S.5 0.1 30 0.07
.0 b.O 0 140 0 1)4
.u
.U
.0
.0 6.8 0.13u 0.11 .
.0 8.8 0.930 5.70 0.160
.0 7.9 u.bll) 2.80 O.UbO
.0
.0
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. 0
."
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.11
. 1;
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.0
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.0 5.6 0.130 0.22 .
.0 4.8 0.020 0.06 .
.0
.0
.0
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COL1 TOC 1-bOL SbOL CHLPH V-bOL T-FE 0-FE
38.u 7.0 133.u 6.^0 l.lo 2.4 130.U 20.0
fc.S 178.0 7.40 1.90 3.1 140.0 10.0
7.-3 124.0 B.O'i U.7o 1.9 60.0 20.0
120.0 7,0 144.0 11.30 1.70 2.7 260.0 10.0
^•20000.0 14.5 283.0 9.40 0.40 4.6 580.0 30.0
30000.0 11.5 216.0 8.10 0.30 3.S 480.0 20.0
3600.0 f*,0 164.0 b.30 2.00 2.JU- <"'n' '
lOO'l.O b.5 109.0 4.10 1.10 1.7 90.0 10.0
1700.0 7.5 14h.O 4.60 2.70 2.1 130.0 20.0
140.0 8.0 128.0 6.00 l.oO 2.7 20.0 10.0
21.0 8.5 168.0 5.80 1.10 1.7 bO.O 20.0
•CAL14
7311191000 9.0
9.0
8.1 215.0 5.1 0.110 0.02
5.0 d.O 158
.0 5.70 1.50 2.9 740.0 20.0
-------
Table 11.3 Page 5
Station Y MD HR
°"M
DO
CAL17 7312071420 l.o 12.0
CAL17 7312171420 H.II 14.(S
SCAL17 7312070900 6.0
SWFP4J
SWFP4J
731207)b4b l.i 11.S
73120Mb4b (<.<• In.b
'
CONO
. 6.U lu.ii 180.W 6.4 O.OSi'
. h.l( y.., 1*0.0
H.2 ">.'. V.b 20U.O?l.b .
6.b
171). 'I
IfO.I)
(i. (
NHH-u >> LOLl IOC I-'aOl. SSOL CHLPH V-SOL T-FE 0-FE
"•1-1 . 17.0 9.H 160.U 7.30 3.90 2.4 60.0 10.0
0.06 0.100 20.0 b.b 1/J.O 31.HO 5.BO 6.7 670.0 10.0
U.1"1 • 7.0 7.5 143.U 8.10 3.10 3.5 130.0 60.0
SWFPSJ
731^07103(1 l.i' 13. n
/31«!n71030 h.n I*./
1HO.O
40.0 'V.I/ 1^1.0 7.ZO ?.60 Z.S 60.0 10.1)
IM102
731i?07121b 1.'. 11.1
H.-i 13.7
h.b Ij.O 170.') h.3 O.IMO
(>..? 'y . 11 1 ? 0 . i)
.n 7.b
4.30 ^.30 2.6 70.0 10.0
LMOMO _731?0ni2!> 1.0 12.1
LMOBO 73j?n7112b 8.11 13.7
t,.b 10. 0 ISIb.O 6.2 O.IVO 0.0.S IVb.n
lb.0 H.O 179.0 S.70 2.20 2.5 60.0 10.0
LM070
LM070
73120M010 l.n 12.2 p.S 7.r 1H.C 200. o 7.J 0.i'40 0.10
7312071010 JI.P 15. n b.J b.b 13. J 190. u
4bO.U V.b 176.0 5.?0 3.00 3.4 130.0 10.0
CAL11
CAL11
73120714bb l.n 10.?
731207145-3 6.P 13.9
. lu.O Ib.n 200.0 *<.6 0.140 0.3*
. V.b 11.7 18b.O
700.0 9.0 130.0 6.10 3.20 J.2 120.0 10.0
CAL13
CAL13
73i207150b 1.0 11.8
731207150b 8.n 14.0
H.li 13.0 190.0 7.1 0.120 0.31
7.0 16.0 1HO.O
720.0 H.b 136.0 7.50 7.40 3.2 170.0 10.0
CAL16 7312071620 l.o 11.9 . 6.b 12. l> 180.0 6.7 0.040 0.14
CAL16 7312071620 H.n 14.0 . 6.b 10.b 180.0
•CAL16 731207UOO 5.0 H.I 10.0 11.0 2'lb.O fc.b 0.040 0.07
LM047A 7312071605 l.n 11.6
LM047A 7312071605 B.n 14.1
«LMO«7A 73)2071130 5.0
f>.b 12.0 IflO.O 9.9 0.080 0.16
. 6.3 9.0 180.0
S.O 7.0 l?.f> 190.0 13.5 0.040 0.09
720.0 9.0 137.0 8.90 b.20 3.1 110.0 10.0
bOO.O b.b 123.0 14.40 4.On 5.2 200.0 10*0
2000.0 11.0 116.0 12.10 4.60 3.O 200.U 10.0
10.0 9.0 144.0 21.00 2.20 5.8 300.0 10.0
-------
Table 11.3 Page 6
Station
1HC35
CAL06
CAL06
CALO*
CALOS
CAL.06
CAL06
CAL06
CAL06
„ wr. UT, 0-» DO PH T II. CO.MI) TUKfl F 'iJ-13-M P CULI TOC T-SOL SSOL CHLPH V-SUL T-FE D-FE
Y M D nR
7312071100 1.0 7.4 13." 71.ii 450.n j?.o 1.340 6.30 0.1SO l<»OUb(J.l> 1H.5 374.0 15.60 1.00 7.6 7400.0 60.0
7312070940 1.0 9.3 7.^12.528.0 270.0 ,1.0 P.JO., 1.30 0.070 4,00.0 9.5 ?2b.O 9.60 2.70 5.3 980.0 10.0
7312070940 2.r 9.? 1.6 13.3 31." 273.0
7312^70940 3.0 '->.? 1.6 13.0 32.0 275.0
7312070940 4,n *.fi 7.6 l?.b 32.0 270.u
7312070940 5.0 9.2 7.6 12.0 30.0 265.0
7312070940 6.C' 9.2 7.6 11.u 28.(i 25b.O
731207094U 7.0 9.t 7.6 10.5 24.0 250.0
731207094U B.n V.9 7 .*> 9.b 22.' 230.')
LM068 7312071045 l.f. 10.S 7.S 7.5 lb.0 220.0 7.5 ".170 0.47
LM06B 7312071045 8.0 14.3 R.O t.3 11.1 200.0
3200.0 9.S 223.0 8.20 2.70 3.5 250. U 10.0
SWFP6J
7313071105 1.0 10.2 . 6.3 12." 20b.J ".4 0.040 u.i
7312071105 8.0 U.7 . 6.3 13.H 203.0
500.0 11.0 170.0 10.30 3.50 4.5 90.0 10.0
SWFP7J 7312071250 l.n 11.5 . 6.5 11.0 195.u ?•" 0.040 0.13
SWFP7J 7312171250 B.O 14.0 . f>.5 7.9 Ihb."
bOO.O f).C 1H1.0 5.60 2.80 1 . Ft 1PO.O 10.0
CAL15 7312071405 1.0 11.3 . 6.3 12.0 195.U 6.7 0.100 u.17
CAL15 7312071405 8.n 13.S . 7.0 9.? 200.0
400.0 9.3 17H.O 7.5o 3.20 5.0 140.0 10.0
CAL14
CAL14
•CAL14
7312071330 1.0 11.5 . 6.5 12.0 ?00.o u.n n.oSu 0.11
7312071330 b.n 14.1 . 6.b 10.6 200.0
7312071000 9.0 H.2 b.O 11 . (j 200.0 9.H 0.0*0 O.Ob
1S.O 7.0 1H2.0 6.1,) 2.90 2.fl 60.0 10.0
0. 9.0 170.0 1 1.40 4.00 5.0 200.0 10.0
-------
o o o oo o o o o oooooo oooooo oooooo o o o o o
IkOOOOO O O O O OOOOOO OOOOOO OOOOOO OOOOO
U1O9OOO O O O 0 OOOOOO OOOOOO OOOOOO OOOOO
1^. • • • * • ••••' •»•*•» »*••** *•*••• •••*•
I O O O O O O O O O OOOOOO £» O O O O O OOOOOO O O 3 9 O
»- r* M oo •* ao ifi f- o o f> o 00 o v i1- P- <> ry o ® 5> m m r- o» * r\J
^ ,* _,* nw -H m •* r* »
(/> o m -* * in f^ o fu e B o «c CNJ •* — • ftJ •-• ^H «•* 3> — « -H o X -H m -« ao r- r- 2> ~* «• o -« co -o * x- -o •£> o M
x CD r- f*- *> <•> •-« o * r*> r*-n^c\jojf*i ro ~* ji •*•-«« h* m — < o IT r- *-« o f\j o <
O *- -^ -*
_JOO~^O OOOC- COOOCO OOOCO^ OOOOOO OOOO
_J
o
O o J" G c in .D IT. o oooooo Oin^iJiooooooo
!-*•.•• •••* ••»••• • ••••• •••••• •<••••
»-i cdoo 3 o oo oooooo 000^00000-30
o -po—< eorxi of\j oooooo oinooo\\jo(*>ooo
CJ XO •-« G ^iTOGMO '\J'^^Omooin
*~< ^ » • • • • •••<* ••*••• •••••• *••••• ••*••
rH :^*--.r\.f'*ric rni/1*!^: rxjr^^mrnrv /imo^oorn * ® »v air
0) *~ "^
r-l
•2 O crccoc oooooo ooocooooo^o
CD ^ . • • • • * • • * •••••• •*•••* *••••• •••••
C^ O"' »lf»f)J>OX OCOJ^OO OOOOOOOOOO3
(j t\iHio*vi'^'-« ^-» _H o ^ *-* ^ •-*^-t'-^H^^ *C J"l I/* *-i ^ O* sO IT- 1/1 "—• ^ O4 4) if) l/> <-^ O
cccoo ooc-c OGJOOO o o — o o o ooocoo ooooo
oon^no ooom oo^omo oofioroo oono«io ootnom
C^^JO^-'O J* OJ —< O O<\J*-<"~«OO ^{Nj^-^^^C-O ^ f\J -^ ^H O O O> CU —« *^ O
OOOOO ,-«,-»,-(,-*
§** " tT ^-^^tftj^* r-^r-i/iiT«* h-oh-i/»iA-* r^tcr^t/im
,-J ^^ ^^ *^-^^* p^ ^< fV; r^ ^* f-l *f (1) f* r~+ ^+ ^_, ^ f^ ^^ ^^ ^4 ^ ^ ff) ,_« ^ ^^ ^ ^ ^ ^^
,0_I>J-JC-) _/_l(J_l _I_IOU_I_' _)_i=>«J-J-l _J_J«=«J_1_J _l_JOO_l
% •*-a. « *.-a. < * **/*** ** W** **|
103
-------
Table 11.3 Page 8
Station Y MD HR n-M DO PH
CL
NH3-N
CO). I
TUC t-SOL SSOL CHLPH V-SOL T-FE D-FE
* CAL17
* CAL16
* LM047A
IHC3S
* CAL15
*CAL14
SCAL17
*CA|_16
*LM047»
IHC3S
*CAL15
*CAL14
S CAL17
*CAL16
X-LM047A
I-1 IHC3S
O *CAL15
•P- *CAL14
S CAL17
*CAL16
*LMO*7A
*CAL15
*CAL14
IHC35
*CAL17
*CAL16_
7311180900
73111H1200
73111B1130
7311181100
73111^103o
73111^1000
731 1200900
7311201200
7311201130
7311201100
7311201030
7311201000
7311290900
7311291200
7311291130
7311291100
7311291030
7311291000
7311300900
7311301200
7311301130
7311301030
7311301000
7311301100
7312080900
7312081200
7312081100
6.0
5,0
b.O
1.0
9.0
9.0
6.0
b.O
5.0
1.0
9.0
9.0
6.0
5.0
5.0
1.0
9.0
9.0
6.0
5.0
5.0
9.0
9.0
1.0
6.0
5.0
1.0
8.2
8.1
8.2
7.5
".2
8.1
d.l
8.0
7.4
8.2
8.2
H.I
8.1
H.O
1 .5
H.O
8.1
7.6
7.6
7.6
7.1
7.8
7.0
3.2
7.6
7.?
9.u
9.0
9.1
19.5
11.1
7.0
H.b
.
.
9.0
9.0
b.O
8.4
,
lo.O
9.4
9.0
5.8
9.0
9.1,
18.3
9
10.0
13. U
6. ii
9.0
11.0
46. 0
6 4
5.0
9.b
P.b
1 .<*
4S.C
7.0
10.0
lu.o
10.0
11..)
7U.O
12.0
12.0
11.0
11.0
11.0
10.0
11.0
60.0
11.0
11. u
76.0
ill'.O
230.0
380.0
j'jri n
220.0
210.0
2 1 U . 0
210.0
370.0
210.0
210.0
22U.O
230.0
220.0
43U.O
230.0
220.0
220.0
220.0
?30.0
230.0
220.0
41U.O
195.0
43b.O
4.8
5.7
10.0
4.6
7.8
•4.6
6.3
15.0
4.0
5.2
16.0
18.0
0.
0.
26.0
IH.O
18.0
6.2
7.2
7.9
7.9
5.0
5.3
0.120
0.110
0. 1 bO
1.000
o.iio
U.03,1
0.03 0
0 . 1 4 U
0.780
0.160
II.03U
O.ObO
0.110
0.100
1.070
0.140
0.110
0.120
O.OJO
0.040
0.110
1.020
0.030
0.03U
0.680
0.02 .
0. (J4 .
0.23 .
J.7o 0.160
0 . U 4 " .
0.02 .
0.02 .
O.Ob .
O.D3 .
3.40 U.140
0.10 .
0.06
0 . u 4 .
0.06 .
0. 1 J
4. BO 0.230
0.12 .
0.06
0.04' .
0.114 .
0 . 0 2 .
0.17 .
0.04 .
4. 3D 0.2bO
0.06 .
0.08 .
6.70 0.1SO
5.0
80.0
530.0
60000.0
22. 0
5.U
18.0
4.0
0. -
25000.0
.
50.0
70.0
?0.0
100.0
11000.0
80.0
900.0
6.0
0. '
0. "
100.0
6.0
160000.0
3.0
870.0
46000.0
9.0
7.0
7.5
10.0
7.5
8.0
9.b
v.b
7.0
11.1'
9.0
b.b
v.o
d.o
7.0
IH.O
B.O
6.5
6.b
7.5
7.0
8.0
6.0
13.0
V.b
V.5
15.0
184.0
172.0
174.0
261.0
128.0
170.0
163.0
174.0
192.0
215.0
1 6 / . 0
177.0
204. U
163.0
160.0
246.0
180.0
192.0
178.0
122.0^
167.0
162.0
157.0
344.0
147.0
145.0
287.0
4.50
5.20
6.50
10.60
6 . HO
5.20
14.70
P. 10
8.50
18.50
4.40
5.00
31.40
13.00
21.70
19.80
21.20
21.80
12.40
8.60
10.00
11.70
9.20
11.70
4.90
4.70
14.60
0.70
0.7(1
2.20
1.00
1 .30
1.30
5.20
3.80
1.70
5.60
3.50
3.50
4.20
3.30
3.20
1.60
26.20
1.80
20.00
2.20
0.70
4.80
1.80
2.30
2.80
2.30
1.80
1.8
2.8
4.2
0.
?. 1
C.I
1.9
0.9
1.3
1.1
6.4
0.4
0.4
6.0
2.5
7.6
9.4
4.1
3.1
4.3
4.?
3.3
4.0
4.0
4. r
2.7
2.2
6.0
60.0
90.0
130.0
0.
60.0
80.0
230.0
IbO.O
180.0
147U.O
12U.O
110.0
450.0
22U.O
400.0
880. 0
440.0
330.0
340.0
210.0
540.0
170.0
140.0
770.0
100.0
70.0
660.0
20.0
10.0
20.0
160.0
20.0
10.0
10.0
10.0
20.0
50.0
20.0
10.0
20.0
20.0
20.0
20.0
20.0
20.0
20.0
20.0,
20.0
20.0
20.0
50.0
30.0
10.0
ao.o
-------
Figure 11.3
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
November 12 and 13, 1973
Nov 12 and 13, 1973 11 AM
Wind 17-25 knots from 210 °
Overcast
Observer: R. H. Snow
Mater Intake •
NORTH
t
Density of crosshatching
represents observer's
estimate of plume
appearance.
Irregular crosshatching
represents splotchy
appearance or an Indistinct
boundary.
-------
Nov 14, 1973 11:30 AM
Wind calm
Clear, sunny
Observer: J. E. Dunwoody
Water Intake •
NORTH
t
Figure 11.4
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
November 14, 1973
-------
Nov 16, 1973 11:40 AM
Wind 18 knots from 315
Partly sunny
Oaserver: J. E. Dunwoody
Water Intake •
NORTH
t
Figure 11.5
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
Novembei 16, 1973
-------
OF
Figure I1? .6
SHOWING VISUAL APPEARANCE
Ss B? AERIAL OBSERVATIONS
November 17, 1973
1-7 1Q71 11:45 AM
Nov 17, ly/J
W:.nd 17 knots from 200
Partly sunny
Observer: J. E. Dunwoody
Vi/oter Intake •
NORTH
t
-------
Nov 18, 1973 1 FM
Wind 8 knots from 220 °
Occasional clouds
Observer: J. E. Dunwoody
Water intake •
NORTH
t
Figure 11.7
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
November 18, 1973
-------
Nov 19, 1973 11:00 AM
V'ind 4 knots from 20 °
Overcast sky
Observer: R. H. Snow
Water Intake •
NORTH
t
Figure 1].8
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
November 19, 1973
-------
68th St. Crib
Nov 29, 1973 11:45 AM
Wind 17 knots from 220 °
Bright sunlight
Observer: J. E. Dunwoody
Water Intake •
NORTH
t
Figure 11.9
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
November 29, 1973
-------
• 681h StCrib
Nov 30, 1973 12:15 PM
Wind 8 knots from 210
Clear sky
Observer: J. E. Dunwoody
Water Intake •
NORTH
t
NJ
Figure 11.10
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
November 30, 1973
-------
68th St Crib
Figure 11.11
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
December 7, 1973
Dec 7, 1973 11:15 AM
Wind 6 knots fro* 170 °
Cloudy
Observer: J. E. Dunwoodjp
Mater Intake •
NORTH
t
-------
Dec 8, 1973 2 PM
Wind 10 knots from 190 °
Cloudy, overcast
Observer: R. H. Snow
Water intake •
NORTH
t
Figure 11.12
SKETCH SHOWING VISUAL APPEARANCE
OF EFFLUENTS BY AERIAL OBSERVATIONS
December 8, 1973
-------
Flying north along the Calumet shore, outfalls of American Oil
Co. were observed, as well as any visible pollution along the
beaches. In the Calumet harbor, the colored plume from the
Calumet River and the U.S. Steel South Works was noted. There
was always a visible plume from this source, although its extent
varied, and it was usually smaller and less dense in color than
the plume from the IHC. The gap in the breakwater was checked
for evidence of flow, as a clue to the direction of Lake currents.
The northern limit of the flight path was the Calumet breakwater.
At our flight altitude of 2500 ft, we would have entered the
landing pattern for Meigs Field, Chicago, if we had gone further.
We then flew out over the Lake ar.d headed in the direction
of the IHC mouth, adjusting our course to best see the plume from
the IHC. We then usually circled the Inland Steel landfill, to
locate the IHC plume. We then continued south toward Gary, and
noted the location of a large plume from the U.S. Steel Gary
Works, that issues from an outfall near the American Bridge Works.
We sometimes flew along the shore as far east as Burns Ditch,
before returning to the airfield.
In general, we found that the IHC plume, which was a brownish
or reddish purple color, could best be seen with the sun behind
the observer. Oil slicks on the Lake could best be seen when
looking toward the sun. The Lake itself varied in shades from
blue to greyish green, depending on the amount of turbidity, and
the illumination. It tends to appear more grey on overcast days.
The prevailing illumination is indicated on the figures.
We found that the aerial observation provided an excellent
way of locating the plume from the IHC as well as other plumes.
In sketching the plume on the map, we related the dimensions of
the plume and its position to prominent landmarks, such as the
Inland Steel landfill revetment, and the Calumet Harbor break-
water. Subsequent comparison of the plume observations with the
115
-------
current meter records showed that in every case the plume was
going in the direction of the Lake current.
Several patterns of plume behavior were observed. On
November 12 and 13, November 17 and December 8, the Lake current
was upshore, while the wind was to the northeast. The plume
moved out into the Lake, met the upshore current, and was carried
northward as it mixed with Lake water. On November 16 and 19
the wind was to the south; also on November 29 and December 7
the wind had just changed from this direction. On these four
days the current was to the southeast, and the plume flowed down-
shore around the Inland landfill, in a similar manner to that
shown in the Skylab photo, Figure 13.2. On November 14, 18 and 30
the current was just changing direction. On November 14, this
situation resulted in flow of the plume directly out into the Lake;
on the other two days these conditions produced puddles of colored
water directly out in the Lake. The mechanisms of movement and
dispersion of the plume are discussed in Chapter 12.
11.5 Flow Measurements
Flow measurements were made in the IHC at two stations.
These measurements were made at Columbus Drive bridge on all
sampling days except November 5 and 12. They were made at the
mouth of IHC (CAL06) on boat sampling days, November 14 and 19,
and December 7, 1973.
At Columbus Drive, we gauged the IHC by measuring the depth
at each fencepost along the downstream side of the bridge. We
then computed the cross-sectional area to be 1160 sq ft. The
width of the bridge was 63 ft. To measure the flow we timed the
passage of a piece of debris under the bridge. We selected
debris that was just below the surface, rather than a floating
object, because wind influenced the motion of a floating object.
Since the depth was only about 10 ft, and the flow is turbulent,
we felt chat the velocity near the surface was representative of
the total. Two measurements were made on each day. The results
are given in Table 4.4 in Chapter 4.
116
-------
At the mouth of the IHC, the flow pattern is more complex,
because Lake water intrudes under the IHC water. For this measure-
ment, Argonne personnel lowered a Bendix Q15 current meter over
the side of the boat and measured the speed and direction of the
current at each meter of depth, and repeated the measurements as
the meter was pulled up. We then calculated the total outflow by
numerically integrating over the depth where the flow was outward,
multiplying by the cosine of the angle of the current vector with
the channel axis. We followed the same procedure to calculate
the Lake water inflow in the bottom portion of the channel. The
results of these flow measurements are given in Chapter 12,
Tables 12.1 and 12.2.
11.6 Lake Current Measurements
Currents were measured continuously at two stations in Lake
Michigan during the period from November 3 to December 8, 1973.
The measurements were made for us by Argonne National Laboratory
using three current meters. These meters were modified by
Argonne. The original meters, Braincon Model 381, were designed
for deep-x-;ater moorings. They had a rotor that is ornni-directional
and would not respond to rapid reversals due to wave action. To
make these meters suitable for use near the surface, where wave
action must be averaged out, the rotor assembly was replaced
with a wave-oriented, ducted impeller assembly. This impeller
operates equally well in both directions and therefore is able
to null out the oscillatory wave produced motions that are super-
imposed on the steady Lake currents.
The meters were calibrated in a tow tank facility at North-
western University. Steady-steady motion was used to obtain the
calibration curve shown in Figure 11.13 and to establish the
threshold of the impeller (^2 cm/sec). At speeds above 15 cm/sec,
oscillatory motions produced by a wave generated produced no
noticeable deviations from the steady-state calibration curve,
but at speeds below this value, small but significant deviations
117
-------
4.6
4.0
54 63
SPEED, cm/sec
Figure 11.13
STEADY-STATE CALIBRATION CURVE FOR MODIFIED METER
118
-------
did occur due to the dead band associated with the threshold of
the impeller. In addition to the speed calibration, the direc-
tional response of the meter to flows approaching from some angle
other than parallel to the duct was observed and found to approxi-
mate a cosine-law response. The sensitivity of the vane to low-
speed flow and the vane's distance constant were also observed.
The vane responded to speeds as low as 3 cm/sec, and the vane's
distance constant xvas 2.25 m. The accuracy should be about +2
cm/sec. The directional accuracy should be ±10 or 20°. The
spread in direction is an indication of the variability of direc-
tion during each 20-min interval of recording.
The current meter records agreed well with measurements
made with the Q15 meter from the boat at 68th St. crib on
November 14 and November 19, 1973, given in Table 10.1.
One current meter was installed adjacent to the 68th St.
crib, at a depth of 17 ft. The other two meters were installed
in the Lake off the Inland Steel landfill, at a position indicated
on Figure 11.2. The coordinates of the meter locations are given
in Table 11.1. The meters off Inland were at depths of 9 ft
and 19 ft. The rneter at 9 ft failed to record speed, but it did
record direction. The direction was almost the same as that
indicated by the meter at 19 ft.
The photographic records obtained from the'meters were
retrieved and processed by computer at Argonne. The results are
presented in Figures 11.14 and 11.15. They present a continuous
record of the Lake currents in these locations. Generally, the
direction of flow is similar at the two locations. The flow
generally follows the shore. The flow is related to the wind,
but it is not directly related. In general, a wind to any direc-
tion near the north results in a current toward the north along
the shore, but there may be a delay in change of current when the
wind changes direction. The flow was north along the shore about
half of the time. The flow was out toward the center of the Lake
only for brief periods, that were associated with current
119
-------
AA 8
veajOap esedujoa 'o» uo|i9«jip
Ol
Figure 11.14
OZ
CURRENT METER RECORDS AT 68TH ST. CRIB
SHOWING CURRENT DIRECTION, WIND DIRECTION
FROM NATIONAL WEATHER SERVICE,
TEMPERATURE OF WATER. AND CURRENT SPEED
120
-------
IZl
Current Speed, cm /«ec
1O
2O
Z CD
0
(0
vl
U
W '
«
('3UOO)
Current and Wind direction to. compass Degrees
-------
ZZl
Current Speed, cm sec
2O
Temp, *c
5 10
Current and Wind direction, compass degrees
IM E S w
Cu
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N E 8 W
Current end Wind direction to, compete degrees
-------
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Current and Wind direction to. compos. d«gra*«
N E S W N
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Current meter 1 mile off
Inland Steel Breakwater, Lake Michigan
Meter 19 ft. below surface
2O
22
23
24
25
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Nov 1973
-------
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Current meter 1 mile off
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Meter 19 ft. below surface
cr
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Dec 1973
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Dec 1973
-------
reversals. One of these periods occurred November 14, during a
boat sampling time.
The current speed shows a cyclical variation with time, and
dropped to zero or near zero between each cycle. These times of
zero current correspond to the times at which current changes
direction. This appears to be a shore effect. Further out in
the Lake the current can swing to any direction (FWPCA, Lake
Currents 1967) but the shore boundary limits the velocity component
normal to the shore. Long periods of zero current correspond to
calm weather periods. A small off-shore component is apparently
possible, as is indicated by the plume observations shown in
Figures 11.3 to 11.12. Although the two meters at 9 and 19 ft
indicated practically no difference, the current closer to the
surface than 9 ft could differ somewhat. Nevertheless, the
observed plume directions agree well with the current meter
records.
These results are discussed further in Chapter 12.
126
-------
12. DISPERSION OF EFFLUENTS FROM INDIANA HARBOR CANAL (IHC)
The objective of this part of our study was to determine
what mechanisms govern the behavior of effluents from the IHC and
other sources, to determine the extent of dispersion on the days
of our measurements, to estimate the fraction of time during
which the observed dispersion is typical, and also to estimate
cases that are likely to lead to extremes of effluent concentra-
tions. Such estimates are based on observations, measurements,
and mathematical models. A complete mathematical model of the
transport and mixing of the effluents in the coastal waters is
beyond present capabilities, unless a much larger study were
undertaken with more extensive measurements of currents and mixing
of tracers. Nevertheless, some conclusions can be drawn from the
results and estimates given here.
Eventually, pollutants introduced into the Lake may be dis-
persed, deposited in sediments, released to the atmosphere, or
flushed out the Straits of Mackinac, Whatever their eventual fate,
the highest concentrations and most severe problems occur before
the pollutants are dispersed. The extent of local pollution
near sources such as the IHC depends on the rate of mixing or
dispersion. It is the objective of this chapter to investigate
this rate, and to determine dilution ratios of pollutants, at
various distances from the source. It appears that several
mechanisms govern the rate of dispersion, and these are discussed
and analyzed. We also attempt to estimate the worst conditions
that can result, if the dispersion mechanisms fail to act for a
period of time. These conditions can lead to the most harmful
effects.
For example, Chapter 13 presents measurements from the IITRI
field sampling program of NH^-N concentrations in the Lake. Some
of the concentrations in the IHC plume exceed water quality stan-
dards for the Lake by at least ten-fold. Chapter 13 also presents
data from the Radial and South Shore Surveys (Chicago Water Dept.
127
-------
1967 to 1973) that show peaks of NH-j-N at stations 4J, 5J and 6J,
and these peaks lie in the path of the IHC plume. Examples for
other pollutants are given in Chapters 14 to 18.
The present study of the spread of pollutants in the Calumet
area is mainly concerned with the effluents from the IHC, since
this canal is the major source of effluents in the area; however,
data were also obtained on other sources that flow directly into
the Lake, particularly the municipal sewer outflows, the U.S.
Steel South Works effluents at Calumet Harbor, the outfalls of
American Maize and American Oil Co., the Burns Ditch effluents,
and the Lake Michigan outfalls of U.S. Steel Gary Works. Data
on these sources are given in Chapters 4 and 5.
12. 1 Behavior of IHC Plume
We found evidence that several mechanisms can act to disperse
the effluents from IHC, depending on conditions at the mouth of
the canal and in the Lake. These mechanisms will be described
and their impact on water quality assessed. The observations
land measurements which lead us to describe these mechanisms will
then be given. Then mathematical models will be given which
allow us to calculate the concentration and extent of polluted
zones for certain special cases.
Measurements to calibrate dispersion models are very impor-
tant, because the models are partly empirical, even if they are
based on an understanding of the actual mechanisms occurring.
For this purpose, it is fortunate that a number of the pollutants
in the IHC effluent are effective tracers. We make use of
measured parameters at various Lake stations to determine the
movement and dilution of the canal effluent, and to distinguish
it from other sources of polluted water.
Several mechanisms operate to dilute the effluents from the
IHC and to influence the spread of the plume and the location of
the polluted area. These mechanisms begin with shear and eddy
mixing within the canal; they include mechanisms of flow and
128
-------
spread of the canal plume; and they extend to mechanisms that mix
the effluents with waters of a wider coastal zone; and eventually
disperse them into the main part of the Lake. Although the pollu-
tants are eventually dispersed, what is needed is an estimate of
the concentrations that will exist while dispersion is taking
place.
The following are some of the mechanisms and an estimate of
their relative importance. The list is in order of when they
occur, beginning with those that act at the mouth of the IHC,
and extending to those that can act over a wider area.
1. Turbulent vertical mixing within the canal
with intruding colder Lake water (important)
2. Inertial jet flow near canal mouth (not
important)
3. Gravity spreading (important)
4. Vertical mixing of plume due to turbulent
eddies in Lake (important)
5. Floating plume being carried along by
natural Lake currents (important)
6. Mixing at edges of plume due to turbulent
eddies in Lake (important only over a
distance of two miles or more)
7. Shearing and dispersion of plume by Lake
currents varying direction with depth
(not important on the days of our
measurements)
8. Gradual build-up of pollutants in near-
shore area, with occasional return of
polluted water along the coast due to
current reversals, and periodic flushing
with clean Lake water due to upwelling
or downwelling (probably important).
There is evidence from aerial and satellite observations,
and from current and dilution measurements in the Lake, to
indicate that some of these mechanisms are operating on parti-
cular days. Calculations can be made to estimate the magnitude
of these mechanisms; they are discussed in the following sections.
129
-------
12.2 Estuary Mixing at Canal Mouth
The water of the IHC is almost always warmer and less dense
than the Lake water, and this gives rise to a typical estuary
effect at the mouth of the Canal. The IHC is dredged to a depth
of about 10 m; the warmer canal water flows out in the top 3-5 m
of this depth, and colder Lake water intrudes in the bottom por-
tion. This behavior is similar to that observed in a salt-water
estuary, and described by Ippen (1966) in Figure 12.1. The
density differences are much more pronounced in the salt water
estuary than in the IHC thermal estuary.
Well-mixed estuary
Pressure Salinity Velocity
downstream distrib. distrib.
Me
level
Pressure
upstream
K-r-j^-vv 'Wim?-' ^ss^s^'s^''-^'
Sta(/0)
Figure 12.1
SCHEMATIC REPRESENTATION OF SALINITY INTRUSIONS
IN ESTUARIES
Station i^ in the figure corresponds to station CAL06 at
the mouth of the IHC.
130
-------
The colder Lake water which intrudes under the canal water
mixes with the IHC water in the lower part of the canal. Mixing
is probably due to eddies caused by shear between the counter-
flowing layers, and eddies due to change of flow direction in the
Inland turning basin. As a result of this inflow and mixing, the
IHC water is already diluted 20 to 50% at the mouth of the canal
(Station CAL06). Flows measured with a current meter on three
boat sampling days are listed in Table 12.1, and detailed measure-
ments are given in Table 12.2.
Table 12.1
MEASURED FLOWS AT MOUTH OF IHC - IITRI DATA
Total outflow
Date
November 14, 1973
November 19, 1973
December 7, 1973
m3/sec
89
102
120
cfs
3150
3590
4226
Lake inflow*
m3/sec
44
(14)
(22)
cfs
1546
(495)
(778)
'^Values in parentheses are uncertain, either because of the
passage of a large eddy causing the flow to change direction
during the measurement, or because the measurement was not
made at the center of the channel. Nevertheless, there is
no doubt that inflow was present on all three days, because
the water was colder and less polluted near the bottom.
Inflow is produced because the warmer canal water flows out
of the harbor faster than it is supplied from upstream. The Lake
water is drawn in to make up the deficit, and to conserve mass.
This behavior is also described by Harleman and Stolzenbach
(1973, p. 21). The mechanism that governs the outflow appears
to be the gravity spreading mechanism discussed in the next
section.
131
-------
12.3 Gravity Spreading Mechanism
The heated canal water tends to spread on the colder Lake
water, just as oil spreads on water, because of the gravity
difference. It seeks to flow out and become thinner, decreasing
its gravitational potential. Such a wavefront is vertical and
sharply defined (Cederwall, 1970). This is not an oscillatory
wave like the usual waves that are seen on the water surface,
but a solitary wave. Although the wave front is moving with
respect to the bulk of the water, it may appear stationary if
the water has the same velocity in the opposite direction. Such
a wave occurring in an enclosed channel is a well-known effect,
and is called a control section (Csanady, personal communication,
1974), or a wedge (Parker and Krenkel 1969). Parker and Krenkel
(1969) describe the phenomenon in some detail and review mathe-
matical descriptions of it. Cederwall (1970) applied the
mechanism to estuaries.
The differential equations describing the movement of the
wave front were given by Abbot (1961), and Cederwall (1970) and
Parker and Krenkel (1969) give some useful relations. The wave
velocity is given by
UA =
where
p is density of water, consistent units
o
g is acceleration of gravity, 9.80 m/sec
H is depth of heated water, m
Measurements of temperature and depth of heated water were
taken at the mouth of IHC, Station CAL06, on three boat-sampling
days, and are given in Tables 12.2 and 12.3. From these data and
Equation 12.1 we can calculate the outflow velocity based on the
spreading mechanism. It is compared with the measured outflow
velocity in the last two columns of the table. The agreement is
BO good that this confirms the mechanism of outflow.
132
-------
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Table 12.3
GRAVITY FLOW AT IHC MOUTH (CAL06)
Date, outflowing layer Temperature, °C
1973 m Top
November 14
November 19
December 7
3.5
3.5
3.5
5*
15.9
15.0
13.5
Bottom
10.0
11.5
10.5
Outflow velocity,
Deiriitv drfirit- m/sec
g/m£ Calculated
0.00076 0.15
0.00045 0.12
0.00034 0.10
0.12
Measured
0.15
0.13
0.13
,_, *Depth of outflow was uncertain because a large eddy passed during one of two measurements.
u>
-------
We may ask what would happen if the temperature difference
were greater or less than on the days of our measurements. The
temperature differences we measured in November 1973 varied from
3 to 5.0°C. Examination of Storet data indicates that the IHC ii
usually 5°C warmer than the Lake, and this is due to the fact
that IHC water consists of Lake water that has been pumped through
industrial processes and used for cooling; however, there are
occasions in November when it is the same temperature as Lake
water, or occasionally even colder. Presumably this depends on
the weather conditions.
Equation 12.1 indicates that the flow velocity will be varied
by a factor of /AT. This assumes that density is proportional to
temperature, which is true for temperatures above 10°C, Thus an
increase in temperature difference will increase flow, and a
decrease in temperature difference will decrease flow for a given
H. At lower temperatures approaching the temperature of maximum
density, the density varies only slightly with temperature, and
the temperature effect will be less. There is another mechanism
that decreases the effect: an increase in outflow will cause a
greater intrusion of Lake water into the IHC, and as this Lake
water mixes with the water in the IHC it decreases the temperature
difference. Thus the net effect of a temperature difference on
flow will vary by a power less than 0.5.
A more important effect can occur if the Lake temperature is
close to 0 C. In this case the IHC water may be near 4°C, the
temperature of maximum density, and the plume will tend to sink.
Such a sinking plume was measured at the Point Beach power plant
on the Wisconsin shore of Lake Michigan by Hoglund and Spigarelli
(1972). A report by Industrial Biotest (1974) shows inverted
temperatures near the mouth of the IHC on January 28, 1974,
indicating a sinking plume. Pritchard (1972) discussed the effect
that sinking may have on the dispersion of a thermal plume, He
suggests that the plume may not actually sink if it mixes suffi-
ciently by the inertial jet mechanism, but the IHC plume has low
135
-------
inertia and apparently did sink on January 28, 1974. The mixing
coefficient generally decreases with depth, so mixing may be less
when the plume sinks. Furthermore the water intakes of municipal
water plants are located at some depth, and may receive higher
concentrations of pollutants under these conditions. Reed and
Pawlowski (1974) report more frequent taste and odor problems at
the Chicago south water crib in winter of 1973-74.
Sinking of toxic water only once a year could control the
absence or presence of those benthic organisms having a one-year
life cycle (Beeton 1974).
12.4 Behavior of Plume in Lake Just Outside IHC Mouth
The behavior of the plume just outside the IHC mouth appears
to depend on the interaction of gravity spreading with Lake
currents that usually run parallel to the shore, as will be
described. Since this region is heavily polluted, it is important
to be able to predict concentrations there under various conditions
A calculation shows that gravity spreading (sometimes called
buoyant spreading) is more important than inertial jet flow of
effluents out of the IHC mouth. The ratio of these two effects
is measured by the Froude number, F.
F = Ua (12.2)
where
Uo is centerline velocity of jet, m/sec
p is density of water, consistent units
g is 9.8 m/sec2
H is depth of plume, m.
At the mouth of IHC (CAL06) we measured U0 = 0.13 m/sec,
Ap/p = 0.00045, H = 3m, and from these we calculate F = 1.1.
A value of F < 2 means that the gravity effect is more important
136
-------
than the inertia of the jet (Cederwall 1970). (Some authors
define F as the reciprocal of Equation 12.2).
There is visual evidence that gravity spreading interacts
with Lake currents to determine plume behavior outside the mouth
of the IHC. As shown in Figure 12.2, the spreading plume usually
encounters a Lake current flowing parallel to the shore. In
Figure 12.2 the Lake current is to the southeast, around the
Inland landfill, across the direction of spreading of the plume.
This pattern is clearly shown by the Skylab photo, Figure 13.2.
This photo suggests that there was a fairly strong general current
in the main Lake water flowing from north to south, dragging the
plume around the landfill into a whorl centered on the East
Chicago water intake crib located just south of the landfill.
We observed this type of behavior on several days, including
November 16, 19, 29 and December 7, 1973.
Even when the plume is flowing around the landfill, it gives
the appearance of gravity-spreading behavior on the north boundary.
Typically it fills the region as far north as a line running
eastward from the Youngstown landfill breakwater, and the demar-
cation between clear Lake water and the plume is sharp. A gravity
plume is said to have a sharp, vertical wavefront (Cederwall 1970).
This would be the case if the rate of gravity spreading was about
equalled by the rate at which the Lake current pushes the water
southward around the Inland landfill. The Lake .current flows
under the plume, and the plume width is determined by a balance
between the spreading velocity and the Lake current. The effect
was described above (Section 12.4). The effect has been recog-
nized, but it is usually neglected in comparison with the jet
inertia effect. Power plant plumes usually have a higher velocity,
and the inertial effect exceeds the gravity spreading mechanism;
whereas the opposite is true in the case of the IHC. The width
of the plume as it passes around the Inland Steel landfill
(Figure 13.2) varies according to our observations from 100 m
to several km, presumably depending on the magnitude of the Lake
137
-------
Lake current
Youngstown
landfill
IHC
Spreading
of plume
Inland
landfill
N
Figure 12.2
CROSS-FLOW OF LAKE CURRENT AND GRAVITY
SPREADING OF PLUME
138
-------
than the inertia of the jet (Cederwall 1970). (Some authors
define F as the reciprocal of Equation 12.2).
There is visual evidence that gravity spreading interacts
with Lake currents to determine plume behavior outside the mouth
of the IHC. As shown in Figure 12.2, the spreading plume usually
encounters a Lake current flowing parallel to the shore. In
Figure 12.2 the Lake current is to the southeast, around the
Inland landfill, across the direction of spreading of the plume.
This pattern is clearly shown by the Skylab photo, Figure 13.2.
This photo suggests that there was a fairly strong general current
in the main Lake water flowing from north to south, dragging the
plume around the landfill into a whorl centered on the East
Chicago water intake crib located just south of the landfill.
We observed this type of behavior on several days, including
November 16, 19, 29 and December 7, 1973.
Even when the plume is flowing around the landfill, it gives
the appearance of gravity-spreading behavior on the north boundary.
Typically it fills the region as far north as a line running
eastward from the Youngstown landfill breakwater, and the demar-
cation between clear Lake water and the plume is sharp. A gravity
plume is said to have a sharp, vertical wavefront (Cederwall 1970).
This would be the case if the rate of gravity spreading was about
equalled by the rate at which the Lake current pushes the water
southward around the Inland landfill. The Lake .current flows
under the plume, and the plume width is determined by a balance
between the spreading velocity and the Lake current. The effect
was described above (Section 12.4). The effect has been recog-
nized, but it is usually neglected in comparison with the jet
inertia effect, Power plant plumes usually have a higher velocity,
and the irtertial effect exceeds the gravity spreading mechanism;
whereas the opposite is true in the case of the IHC. The width
of the plume as it passes around the Inland Steel landfill
(Figure 13.2) varies according to our observations from 100 m
to several km, presumably depending on the magnitude of the Lake
137
-------
Lake current
Youngstown
landfill
IHC
Spreading
of plume
Inland
landfill
Figure 12.2
CROSS-FLOW OF LAKE CURRENT AND GRAVITY
SPREADING OF PLUME
N
138
-------
current and the density difference. In one infrared color photo
taken by IITRI on November 29, 1973, there can be seen four super-
imposed boundaries of the plume curving around the landfill, as
if four successive advances of gravity waves were being carried
around, each having penetrated to a different depth and perhaps
a different dilution.
When the Lake current is upshore to the northwest, the plume
motion is different. From airplane observations in Chapter 11,
such as Figures 11.3, 11.6 and 11.12, it appears that the plume
drifts out into the Lake until it reaches the end of the Inland
landfill, and then it meets the cross-flowing Lake current. A
splotchy-looking plume results, that spreads out into the Lake
several km and is visible for 15 km (10 miles) or more to the
north.
On November 18, 1973, (Figure 11.7) the effluent did not
look like a normal plume, but looked like a round puddle centered
on the north corner of the Inland landfill. The puddle was about
3 km (2 mi) in diameter, and a second puddle of similar size lay
further out in the Lake. The current meter record showed that
the Lake current was zero at this time, due to the fact that it
was just changing direction. Again on November 30, 1973
(Figure 11.10) a larger puddle was seen in the Lake off the north
corner of the landfill, in addition to the curving plume; again
the current was just changing direction and was stagnant. Such
puddles could be caused by gravity spreading. Estimates of the
rate of gravity spreading given in Section 12.6 below indicate
that ten hours are required to form a puddle of 2300 rn (1.4 miles)
in diameter. When an upshore durrent again sets in, it could
carry such a puddle along and cause stronger than usual pollution
at water intakes along the shore.
12.5 Rate of Gravity Spreading in Lake
The rate of spreading of a buoyant plume was determined in
model experiments by Sharp (1969). In these experiments, water
was floated on dilute brine. The water was supplied at the center
139
-------
of the tank surface, and the spreading of the circular puddle
of water on the brine was measured as a function of time after
the start of flow. The data are plotted in Figures 12.3 and 12.4.
Sharp expressed the results in terms of three dimensionless
groups. They are
t s'3'5 R s';/5 and Q g'1/3
-I f CtllU. V )
Ql/5 Q2/5 v5/3
where
t is time, sec
g1 is g Ap/p = 9.8 Ap/p m/sec2
Q is flow from source, m3/sec
R is radius of puddle
v is kinematic viscosity of water, 1.3xlO~6 m2/sec
at 5°C.
Sharp's (1969) data are presented in Figure 12.3. For a
given flow 0 and constant conditions, the abscissa value is a
constant at various times. The figure can be used to calculate
the spread of warmer water over time by reading up from the
abscissa, and relating values of spread distance R to time t.
Note the curved portions of the graph to the left side. This
curvature arises because of the influence of viscous drag between
the spreading liquid and the substrate at long times or large
spread distances, especially for smaller flows. Larger flows
correspond to points to the right, on the horizontal portion of
the curves. It is safe to extrapolate to larger flows, since
viscous forces can then be neglected. In fact the horizontal
portions of the curves can be expressed in a single graph,
Figure 12.4. This graph is valid if ratio of
Q Rll/3 to R Sll/5
5/3 n2/5
Vs" A Q:
is at least (2xl03)/3. For values of the abscissa greater than
20, Figure 12.4 can be represented by the following straight line:
140
-------
TO
6-0
50
40
R(fr')
MfrT'
loP*
so
20
10
0
pe o
° % • g i- • r-
—o- f I—
O 2,IOb 4»10» b.W B.IO" 10,10* 12x10" 14.10" Ib.lO' IB.IO" 20.10' 21.10*
<3« O')'/!
Figure 12.3
SPREAD DIAGRAM
from Sharp (1969)
40
1-0
O 10 40 60 »0 100
Figure 12.4
NONVISCOUS SPREAD DIAGRAM
from Sharp (1969)
141
-------
I 1 / 5 J- „ t 3 / 5
= 1.6 + 0.44 i-S-, — (12.3)
,
Q25 Ql/5
Calculations were done for two cases.
November 19 at CAL06 (mouth of IHC)
Q = 102 n3/sec (Table 12.1)
Ap/p
=
1
10
1
4
0.00045
t
min
min
hr
hr
(Table 12.2)
R, m
37
106
487
1860
Q
This means that it would take about 1 hr for IHC effluents
to reach the north edge of the Youngs town landfill breakwater.
These values are within the range where viscous forces can be
neglected.
November 14 or December 7 at LI168
Ap/p
= 0.00008
t
10 min
1 hr
2 hr
10 hr
R, m
78
266
490
2300
Q = 89 m
(1.4 miles)
The normal width of the plume when it flows around the Inland
landfill is about 500 m, which means that 2 hr was required to
reach this width.
12. 6 Measured Dilutions
The dilution of the IHC plume was determined experimentally
on three boat sampling days. The experimental procedure was
142
-------
described in Chapter 11. The results are plotted in Figures 12.5
to 12.7.
We define the dilution factor as the ratio of concentration
of a substance measured at the mouth of the IHC, to that measured
at a point in the Lake, less the background concentration. The
background for each pollutant was chosen to be the lowest value
measured on that day at stations that appeared to be well outside
any plume. Generally these backgrounds were consistent with Lake
backgrounds discussed in Chapters 13 to 18.
Although there is some spread in the dilution curves for the
various parameters, the trends are similar. Coliform bacteria
is an exception, but its behavior is not unexpected. Howmiller
(Appendix A) reviews available data on the rate of decay of fecal
organisms. With few exceptions there is a substantial mortality
of such bacteria within 24 hr. This was attributed to an unknown
"toxic factor" in Lake water, since the mortality in well water
was slight. The apparently greater dilution for coliform given
in the Figures actually represents dilution plus decay. The
presence of coliform is still an indicator that the samples con-
tain IHC effluents, although the coliform data cannot be used to
measure dilution.
The curves for chlorophyll show an apparent decrease in
dilution. This is because the IHC effluents have a nutritive
effect causing growth of algae. This subject is discussed in
Chapter 17.
Some scatter in the data for the remaining parameters occurs.
The reason for this is not known, although it might be due to
fluctuations in the composition of IHC effluents with time.
12.7 Interpretation of Dilutions in Terms of Dispersion
Mechanisms
Two different situations are represented by Figure 12.5
(November 14) and by Figures 12.6 and 12.7 (November 19 and
December 7). On the first date the plume was flowing out into
143
-------
otal coliform
t mile
Distance from mouth of IHC
LM 68
LM 80
LM 102
Figure 12.5
DILUTION OF IHC EFFLUENT AT LAKE MICHIGAN STATIONS
BASED ON WATER QUALITY MEASUREMENTS BY IITRI
November 14, 1973
-------
Ol
1 mile
Distance from Mouth of IHC
68 6
Figure 12.6
DILUTION OF IHC EFFLUENT AT LAKE MICHIGAN STATIONS
BASED ON WATER QUALITY MEASUREMENTS BY IITRI
November 19, 1973
Chloride
.Coll
CAL1 15
-------
Fluoride
1 mile
Distance from Mouth of IHC
LM 68
6 J
Figure 12.7
NH3-N
Total Iron
Total Coli
DILUTION OF IHC EFFLUENT AT LAKE MICHIGAN STATIONS
BASED ON WATER QUALITY MEASUREMENTS BY IITRI
December 7, 1973
7 J
-------
the Lake. On the other dates it was flowing around the Inland
Steel landfill. The dilutions appear to exhibit several of the
mechanisms discussed in preceding sections. There is an initial
spreading in width of the plume over colder Lake x?ater. This is
followed by turbulent mixing of the surface plume with the under-
lying water, resulting in an initial dilution between the mouth
of the IHC and Station LM068, 2400 meters out along the Inland
landfill. Hydrolab measurements (Table 11.2) taken at Station
LM068 indicate substantial vertical mixing at this point, although
gentle gradients with depth persist for several miles beyond this
point. The dilution at LM068 was 2.5 on November 14 and December
7; and was 6 on November 19.
On November 19 there was little further dilution as the
plume flowed around the Inland landfill to Stations 6J and 7J.
This is probably due to the fact that as the plume hugs the land-
fill there can be no lateral mixing in the landfill side. Lateral
eddy mixing is normally slow, and when this mixing is limited to
the outside edge it should not affect the center of the plume for
some distance. On December 7 a similar effect occurs between
Stations 6J and 7J, but a sharp increase in mixing occurs betwen
Stations LM068 and 6J. On this day, the Hydrolab measurements
(Table 11.2) show that the plume was not vertically mixed at
Station LM068, but vertical mixing continued until Station 6J.
The dilutions for November 14 (Figure 12.5) show some simi-
larities and some differences. There is a relatively horizontal
portion of the dilution curve between Stations L11068 and LH080;
during part of this distance one side of the plume was partly
protected from lateral mixing by contact with the Inland landfill.
Except for this partial break in slope, the mixing continues
almost linear with distance. Extrapolating to greater distances
one would expect these dilutions curves to become flatter as the
width of the plume increases, since this is the usual behavior
of plumes.
147
-------
In general, the behavior of the dilution curves fits the
other observations and the mechanisms that are postulated to
determine its behavior.
148
-------
13. AMMONIA-NITROGEN
Our own studies, together with extensive data from other
agencies, indicate that violations of ammonia-nitrogen (NH3-N)
standards occur regularly in Lake Michigan as a result of efflu-
ents from the IHC, and that reduction of NH3-N levels in the IHC
will be needed to correct this condition. In the following, we
review the available data and recommend that NH3-N loadings from
the IHC be reduced by a factor of 7.7.
This will substantially improve water quality in the "inner
harbor." Further study is needed to determine whether reductions
of IHC loads or of other sources could allow water quality stan-
dards to be met outside of the inner harbor.
13.1 Water Quality Standards
The Indiana Standards (1973) for Lake Michigan are 0.02 mg/5,
NH3-N monthly average, and 0.05 single value. The Illinois Stan-
dard for Lake Michigan is 0.02 mg/&. The Indiana Standard for
the "inner harbor" including the water within a line from the
Calumet Harbor breakwater to the Inland Steel Company breakwater
is 0.05 monthly average and 0.12 for single value. The Indiana
Standard for IHC is 1.5 mg/&.
In the following we show that in or'der to meet Lake Michigan
standards, the effluents must be reduced below the IHC standard.
Ammonia is harmful to Lake waters because of its toxicity
to fish, its consumption of chlorine in water treatment plants,
and its nutritive effects promoting eutrophication of the near-
shore waters. The last two effects are described by Vaughn and
Reed (1972) and by Thomas, Hartwell and Miller (1972). The
National Academy of Sciences (1974) reviewed measurements showing
toxic effects in various fish including trout and perch at
un-ionized ammonia concentrations of 0.27 mg/£, and at 0.006 mg/£
with Chinook salmon fingerlings. Because the pH of Lake Michigan
water is relatively high, ranging from 8.0 to 8.7, the fraction
of ammonia that is un-ionized is high, reaching as much as 257o.
149
-------
Twenty-five percent of 0.025 is 0.006; therefore, an NH3-N con-
centration of 0.025 can result in 0.006 mg/Jl un-ionized ammonia,
Thus, the toxicity data provide some support for the existing
standards, although the problem of toxicity to fingerlings is
avoided by growing salmon in hatcheries.
150
-------
13.2 Background NH^-N Concentrations
Even if the NHo-N were completely eliminated from large
sources such as the IHC, there would still be some NH^-N in the
nearby Lake, due to background levels in the Lake. In this
section, we review available data on background levels.
We define background as a concentration that exists in the
main body of the Lake, uninfluenced by fluctuations due to local
effluents. Background levels can be reached in near-shore waters,
on occasions when these waters are flushed by movements of water
from the main body of the Lake. Therefore, background levels
can be determined from measurements at places in the Lake far
from polluted areas, or in near-shore areas on occasions when
they appear to be flushed by water from the main body of the Lake.
Few values of NHo-N have beep reported at places in the Lake
far from populated areas. Schelske and Roth (1973) reported 16
measurements in the summer of 1970 near Charlevoix in the north-
east corner of the Lake. Readings were taken at six stations and
four depths. The average was 0.018 + 0.006 mg/A. Variation with
depth was slight. These values are similar to the lowest non-zero
values reported by the Chicago Water Dept. at the 68th St. water
intake. The lowest value measured by IITRI in Nov-Dec 1973,
Table 11.2, was 0.02 mg/£. These readings were found at stations
that were in clear water, that apparently was not polluted by
local sources, such as station LM102 on Nov. 19, 1973 (Table 11.2).
It is difficult to decide what is the true background con-
centration of NHo-N because there is a large variation in reported
measurements, both at near-shore locations and in deep water
locations. Fluctuations in near-shore data (Illinois EPA 1972)
may be due to currents carrying polluted waters from sources along
the shore. If we assume that the lowest values reflect incursions
of relatively pure open-Lake water, as our visual observations
(Chapter 11) tend to suggest, then these low values should reflect
the background. On this basis, the lowest measurements in the
Calumet area would indicate a background of 0.02
151
-------
On the other hand, the deep-water measurements (FWPCA,
Physical and Chemical Water Quality 1968) also show fluctuations.
Values range from below the detection limit of 0.02 to 0.50,
while the average of 429 samples was 0.06. Values of 0.50 seem
too high to represent the background, and may be influenced by
local sources of pollution, but this cannot be determined retro-
spectively. Therefore some doubt exists as to the true background,
but the author favors a value of 0.02 mg/jfc.
13.3 Water Quality Data
The most extensive data are those obtained by the Chicago
Water Department. Not only has the Chicago Water Department
measured the quality of water at its own intake cribs, but since
about 1950 it has measured the water quality at Hammond and
several other municipal intakes in Indiana, and they have also
sent a boat to take Lake water samples for analysis. The samples
•were taken weekly and the Lake survey samples were taken about
6 to 8 times during each year.
Results of the South Shore Lake survey are plotted in
Figure 13.1. Station 5S, located one mile off the mouth of IHC,
shows high values of NHo-N. In order to meet the open-Lake
standards at 5S, a reduction of ten-fold in both average and
individual values would be needed from 1971-72 levels, or five-
fold from 1973 levels. Values at other stations that are not
usually in the plume are also in violation and would require
reductions of two- to three-fold.
The following additional data will show that IHC is the
main source of NHo-N, and that the situation is at least as bad
as the above figures show. Table 13.1 presents results of a
sampling program conducted by IITRI for the U.S. EPA in November
and December 1973. Figure 11.2 (Chapter 11) is a map showing
the location of sampling stations. They are all Lake Stations,
except for IHC-3S (IHC at Columbus Drive) and CAL06 (mouth of
IHC). Our observations of the plume of pollutants from IHC were
described in Chapter 11. These observations clearly showed that
152
-------
AMMONIA-NITROGEN
ANNUAL AVERAGE AND MAXIMUM, mg/i
Chicago Water Pept.
South Shore Lake Survey
153'
-------
Table 13.1
AMMONIA-NITROGEN IN LAKE MICHIGAN
IITRI measurements
mg/i
CAL17
Boat
M
Ul
-O
November 14, 1973 0.
November 19, 1973 0,
December 7, 1973 0,
.03
.02
.13
Crib
0.
0.
0.
07
03
06
CAL16
Boat
0
0
0
.05
.05
.14
CAL15
Crib B C
0
0
0
.02 0.05 0.04
.07 0.21 0.22
.07 0.17
LM047 CAL14 IHC CAL06
B C B C 3S B
2.03 0.03 - 0.05 4.5 2.7
0.04 0.11 0.02 5.7 2.8
0.16 0.09 0.11 0.05 6.3 1.5
CALll CAL13 LM68 LM70 LM80 LM102 4J 5J 6J 7J
B BBBBB BBBB
0.35 0.05 0.50 0.11 0.50 0.27 0.03 0.18 - 0.11
0.09 0.04 0.36 0.08 0.05 0.02 0.03 0.04 0.21 0.06
0.36 0.31 0.47 0.10 0.02 0.03 0.90 0.02 0.22 0.13
-------
on November 14, an off-shore wind was moving the plume out from
CAL06, past stations LM68, to LM70 and LM80, and finally to
LM102 (four miles out in Lake. Michigan). The concentration at
LM80 was 0.50 and at LM102 it was 0.27. These values are ten
and five times higher than the single value standards. Other
parameters measured at these stations (coliform bacteria, total
iron, chloride, conductivity, pH, fluoride, and temperature) gave
a signature of tracers to definitely identify the plume as coming
from IHC.
Measurements of NHo-N in the same area of the Lake were
conducted by Industrial Biotest Inc. (1973) on the same day as
these IITRI measurements, November 14. The agreement of their
data with IITRI data in Table 13.1 is excellent.
On the other two dates (November 19 and December 7) the
plume was observed to flow around the Inland Steel Company land-
fill breakwater and to mix with the waters south of this landfill,
in the region where the water intake for the city of East Chicago,
Indiana, is located. The flow on these dates was similar to that
shown in Figure 13.2, which is a photo taken by Skylab in Septem-
ber 1973. The Skylab photo clearly shows the iron-colored plume.
In Table 13.1 the pollutants can be traced from station CAL06
(mouth of IHC) to LM68 to 6J to 7J and CAL15 (East Chicago intake)
and even to CAL14 (Gary water intake). These values are five
times greater than the standards for individual Lake values for
NH3-N.
The Chicago Water Department has also made measurements in
the Lake at some of the stations used by IITRI. Figure 6.3 in
Chapter 6 is a map of stations in their SWFP Radial Survey.
Figures 13.3 to 13.5 show measurements at these stations during
1970 to 1972. High values are often observed at station 6J, as
would be expected when the plume is flowing around the Inland
landfill as in Figure 13.2. These 1970-1972 levels are ten
times higher than single-value standards.
155
-------
Figure 13.2
SKYLAB PHOTO SHOWING PLUMES FROM IHC AND CALUMET RIVER
September 13, 1973
156
-------
Cn
0.6 i-
0.5
0.4
01
bO
O
l-i
4J
t
cd
0.3
0.2
0.1
3F 2F IF
U 2J 3J
4J 5J
Location
Figure 13.3
6J
June 27
Indiana standard
Single value
Average
F I ~
7J 41 51 61 71
RADIAL SURVEY OF AMCHtA NUBOGEM CO8CEHTKAT1ON - 1971
Chicago South Water Filtration Plant
-------
u.or
0
3F 2F
U 2J
3J 4J
Location
Figure 13.4
5J
6J
Indiana standard
Single value
Oct 3
RADIAL SURVEY OF AMMONIA NITROGEN CONCENTRATION - 1972
Chicago South Water Filtration Plant
-------
0,6 i-
0.5 -
t
-0.4
0)
M
O
M
4J
•H
I-1 -rl
t_n c
vo g
0.3
0.2
0.1
3F 2F
IF
U 2J 3J
4J 5J
Location
Figure 13.5
Indiana standard
Single value
Average
14
RADIAL SURVEY OF AMMONIA NITROGEN CONCENTRATION - 1970
Chicago South Water Filtration Plant
-------
The Chicago Water Department has also recorded the highest
value of NHo-N at the 68th St. water intake each year since 1950.
Peaks of 0.60 were observed in the late 1950's, but since 1970
the peaks have reached only 0.20. Earlier peaks nay have been
due in part to effluents from U.S. Steel South Works, which
is close to the 68th St. intake. Improvements at the South Works
have lowered NHo-N effluents so that this is no longer a signi-
ficant source in comparison with the IHC (see effluent loads,
Tables 4.3 and 4.5).
13.4 Behavior of IHC Plume
The dilutions that we measured from the IHC mouth to
stations 6J, 7J, and CAL15 appear to be typical ones, based on
our current meter data. Current meters were installed for us by
Argonne National Laboratory in the Lake one mile off Inland Steel
landfill and also adjacent to the 68th St. Chicago water intake
crib, at depths of 19 and 17 ft, respectively. On November 19,
the current at Inland landfill averaged 9 cm/sec in the direction
E/SE, and on December 7 it was 10 cm/sec in the same direction.
A plot of .measured currents (Figure 11.14) shows that this speed
is about average for the whole period of measurement, November 8
to December 8. The current flowed in this same direction for
13 out of the 30 days measured. According to our understanding
of the dispersion mechanism of the plume, the dispersion depends
mainly on the magnitude of Lake currents in the area, and so
these dilution results on these two days are expected to be
typical of those to be found during the whole period. The only
other factor of importance is the buoyancy of the plume from the
IHC as a result of industrial heating of the IHC water. Storet
records show that the IHC is normally about 5°C warmer than Lake
water. On the days of our sampling, it varied from 3.5 to 5.9°C
warmer, and we therefore expect that the behavior of the plume
was normal with regard to its thermal buoyancy behavior. We can
conclude that the measured open-Lake NHo-N values quoted above
are typical ones, and correspond to typical plume spreading
behavior.
160
-------
13.5 IHC As an Ammonia Source
I
! We will now show that the IHC is actually the source of the
NHo-N peaks measured in the Lake studies quoted above. This can
be seen by examining the loadings in the IHC, and checking these
by means of measured concentrations and flows in the IHC.
IITRI measurements of flow and concentration of NH^-N at
CAL06 (mouth of IHC) indicated loadings totaling 45,900, 54,200,
and 34,200 Ib/day for the three sampling days (November 14, 19,
and December 7). The agreement is reasonable with loadings deter-
mined from permit and effluent data (Combinatorics 1974) shown
in Table 4.5. These quantities can certainly account for the
quantities measured in the Lake near the mouth of the IHC.
A summary of data obtained by the State of Indiana in early
November 1973, and summer 1973 are given in Table 13.2. Other
measurements of NHo-N in the IHC are those of the U.S. EPA, pre-
sented in the bottom three lines of Table 13.3. These values are
in reasonable agreement.
The most extensive data, however, are from the Chicago Water
Department at Dickey Rd, presented in Figure 13.6. This figure
indicates a significant increase from 1969 to the present. The
values in Figure 13.6 are likely to be most representative,
because they average one sample every week in the year, whereas
the EPA and Indiana data were taken only for brief periods in
recent years.
The dramatic increase in NHo-N at Dickey Rd can be explained
by diversion of Inland Steel and Youngstown Sheet and Tube
effluents from the IHC to the East Chicago STP. Dickey Rd is
upstream of Inland Steel and most of the Youngstown outfalls,
but downstream of the STP. This diversion also explains the
•very high NH^-N loading from East Chicago shown in Table 13.4,
'far in excess of the population equivalent of that city.
Table 13.5 gives a detailed list of the effluents of NH3-N
from each outfall on the IHC. The data are from permit applications
161
-------
Table 13.2
IN-STREAM WATER QUALITY, 1973
Combinatorics (1974)
Description
Water quality standard 1.5 mg/jg,
72 73 72-73
Monitoring stations Average Average Maximum
GCR 41 1.9 1.8 5.6
Grand Calumet River
Gary (U.S. 12)
GCR 37 2.3 2.35 5.70
Grand Calumet River
East Chicago (Kennedy Rd.)
GCR 36 44.8 86
Grand Calumet River
East Chicago (Indy. Blvd.)
GCR 34 - 15.0 36.0
Grand Calumet River
Hammond (U.S. 12).
IHC 3W 5.1 4.1 9.0
Indiana Harbor Canal
East Chicago (Indy. Blvd.)
IHC 3S 3.4 3.14 8.5
Indiana Harbor Canal
East Chicago (Columbus Drive)
IHC 1 4.7 3.3 8.5
Indiana Harbor Canal
East Chicago (Dickey Rd.)
: IHC 0 - 2.3 4.2
Indiana Harbor Canal
East Chicago (Youngstown Steel)
162
-------
Table 13.3
AMMONIA-NITROGEN, mg/4
Averages
Storet Data, U.S. EPA
Year
CAL17
CAL16
CAL15
CAL14
CAL13
CAL06
CAL02
CAL03
Station
Chicago SWFP
Hammond WFP
East Chicago WFP
Gary WFP
Calumet Harbor
IHC Mouth
IHC 151 St.
IHC Dickey Rd.
1971
0.048
0.115
0.122
0.192
1.69
3.3
4.7
1972
5.19
3.25
2.9
1973
2.0
4.1
4.7
1965-1971
0.05
0.12
0.12
0.06
0.19
1.7
3.3
3.6
163
-------
s.o
E
Q.
o.
I
LJ
§
a:
to
I
bJ
O
<
ffi
<
z
<
4.0
3.0
2.O
1.0
- 7
Indiana Harbor Ship Canal
Dickey Rd. Bridge
IHC Standard
Calumet River -
92nd St. Bridge
Lake Michigan Standard
liissl
I I b«l
YEAR
-i — i — i
i
Figure 13.6
ANNUAL AVERAGE AMMONIA NITROGEN
WEEKLY SANITARY SURVEYS
Chicago Water Department
164
-------
Table 13.4
SUMMARY OF EXISTING AMMONIA EFFLUENT LOADS TO IHC
Source: Combinatorics (1974)
NH3-N,
Ib/day
Discharger
U.S. Steel Corp.
Gary
E. I. duPont de Nemours
U.S.S. Lead
East Chicago
Hammond
Union Carbide
ARCO
American Steel Foundry
Youngstown
Inland
Total
Existing average
5,056.80
4,080.00
1,243.87
0.30
10,700.00
2,480.00
41.00
601.00
0.08
4,535.40
4,573.51
33,309.00
165
-------
Table 13.5
INVENTORY OF NH3-N DISCHARGES TO IHC
Source: Combinatorics (1974)
NH.
Water Quality Standard 1.5 mg/1
Discharges
U. S. Steel
GW-1
GW-2
GW-2A
GW-3
GW-3A
GW-4
GW-5
GW-6
GW-7
GW-7A
GW-9
GW-10A
GW-11A
GW-1 3
ST-14
ST-17
GSTP
E.I. duPont
001
002-004
005
006-010
U . S . S . Lead
HSTP
ECSTP
Union Carbid
ARCO
Amer. St.
Foundries
Min.
Flow
(MGD)
19.9
10.9
1.4
2.7
0.4
Avg.
Flow
(MGD)
28.9
16.4
2.2
3.8
1.7
0.5 0.7
82.4
23.4
5.8
93.3
24.7
26.3
81.3
1.8
0.8
20.1
44.0
0.5
7.24
0.07
0.89
35.0
10.0
3 0.05
0.09
1
87.7
29.5
10.6
120.1
34.7
34.6
94.7
2.9
1.8
30.0
52.7
•
1.8
10.31
0.08
2.24
0.36
40.7
!
14.0
0.07
5.04
0.15
Max.
Flow
(MGD)
40.7
23.0
3.9
4.5
3.7
0.9
95.3
39.4
16.9
146.0
39.7
47.2
115.6
4.8
3.3
39.3
62.0
2.4
11.66
0.12
2.98
44.0
20.0
0.11
6.77
0.27
Avg.
Load
(Ib/day)
482.0
274.0
86.0
38.0
-------
Water Quality Standard 1.5 ng/1
Discharges
Youngstown
001 YS-20
002 YS-2
003 YS-4
004 YS-8
005 YS-11
006 YS-12
007 YS-13
008 YS-22
009 YS-14
010 YS-15
Oil
YS-18A
Inland
001 IE-2
002 4E-1
003 5E-1
004 5E-2
005 5E-3
006 6E-1
P07 7E-1
008 10E-1
Oil 13G-1
012 13H-1
013
14H-TT
014
15H-TT
015 16H-1
016 16H-2
017 16H-3
018 16F-1
Min.
Flow
(M6D)
8.46
1.50
0.53
1.03
1.19
3.30
6.30
3.00
34.00
36.60
107.80
8.60
Unknov
126.96
67.68
85.52
85.52
17.28
7.20
115.28
119.76
Avg.
Plow
(MGD)
13.70
3.62
0.98
1.40
1.60
5.70
14.00
5.00
48.70
58.00
121.60
.14
190.00
7.20
0.86
8.60
0.65
21.60
n 6 Hi<
158.70
50.80
106.90
106.90
21.60
9.00
144.10
149.70
Max.
Flow
(MGD)
23.60
7.50
1.40
1.75
3.00
8.40
18.90
11.70
60.00
67.00
138.70
.29
228.00
8.60
1.04
10.40
1.30
25.90
[hly Vai
190.44
70.00
128.28
128.28
25.92
10.80
172.92
179.64
Avg.
Load
(Ib/day)
114.0
30.2
8.2
12.0
40*0
536.0
234.0
166.0
406.0
969.0
2,020.0
.23
1,000.0
12.0
1.4
108.0
1.1
35.9
•iable
238.0
1,450.0
641.9
651.73
23.42
18.26
204.30
187.27
Max.
Load
1.0
1.0
1.0
1.0
2.0
11.7
2.0
4.0
1.0
2.0
2.0
.2
.63
.2
.23
1.5
.2
.2
.18
3.42
.72
.73
.13
.23
.17
.15
Max.
COBC.
Mo/l}
1.5
1.5
1.5
1.5
3.0
13.0
53.0
35.0
1.5
3.0
3.0
.4
6.44
.4
.4
2.0
.4
.4
.21
13.70
3.05
2.59
.20
.30
.20
.40
Comments
1,7
-------
and industry monthly operating reports to Indiana, and were
compiled by Combinatorics (1974).
13. 6 Other Ammonia Sources
Table 4.2 in Chapter 4 lists the sources in the Calumet
area other than those entering the Lake via the IHC . A signi-
ficant source in the Calumet area is Amoco Chemicals, 1300 Ib/day
net. Amoco Chemicals is close enough to influence the Lake
values quoted above, but it is small compared to the effluents
from IHC. Also, in the Whiting area are two combined sewer out-
falls discussed in Chapters 5 and 16. These outfalls and the
Amoco outfall could be responsible for some of the high NtU-N
values at the Whiting and Hammond water intakes, but their total
loads are too small to compare with the impact of IHC effluents
on the Calumet area. Prior to 1973 the U.S. Steel South Works
was a significant local source, as may be seen from Figure 13.6
but at present the load from this source is not significant.
Although the IHC is responsible for the peaks of NHo-N
measured in the Calumet area of Lake Michigan, high NHo-N concen-
trations are regularly measured in all of the near-shore waters
of the southern basin. Winters (1974) points out that stations
sampled by Indiana show high NtU-N values that cannot be attributed
to the IHC plume. For example, at Michigan City, Indiana, less
than one-third of the samples have values less than 0.10 mg/£ .
(See Figure 6.2 for Indiana sampling locations.) The maximum
value at Michigan City is 0.5 and the average is 0.23. Winters
(1974) also compares the concentrations and loads of the two
tributaries near Michigan City with the IHC as follows :
NHo-N concentration,
Load,
Tributaries Minimum Maximum Average Ib/day
IHC Dickey Rd. 1.8 5.9 3.6 57,709
Burns Ditch Mouth 0,3 0.8 0.48 1,807
Trail Creek 0.2 3.4 1.4 861
168
-------
In addition, the Illinois data (Illinois EPA 19/0, 1971>
1972) also show appreciable NH3-N concentrations all along the
Illinois shore. In 1972, 12 Lake county stations averaged
0.26 mg/£; 19 Cook county stations averaged 0.07 mg/&, and 13
Chicago stations averaged 0,07 rog/£. There are known to be sewage
and steel mill effluents to Lake Michigan in Lake County, Illinois,
In 1971, the average of all stations was 0.06. The average of
1751 samples of in-shore water measured in 1962-1963 was reported
by FWPCA (Physical and Chemical Quality Conditions 1968) to be
0.13 mg/ &. We agree with Winters (1974) that the NH3-N standards
for open water are very seldom met, and also with a statement by
Moore (1974) to Indiana SPCB that "there are other sources of
ammonia-nitrogen from Burns Ditch, Trail Creek, Illinois, Michi-
gan, rainfall, agricultural and urban sources, and algal decompp*
sition. Because lake Michigan is very cold, maximum of 77°J,
nitrification is a very slow process and distant sources must be
considered. "
On the other hand, Palmer (1974) measured the residence
of pollutants in the waters near a city in Lake Superior to be
40 days. If the residence time of NH3-II in the Calumet waters is
of this magnitude, then the IHC effluents could account for both
the total amount and the wide extent of NH3-N measured in the Lake.
Further study is needed to resolve this question. We agree with
Moore (1974) that "Additional studies to identify sources of
ammonia-nitrogen are necessary as well as the study of Lake
currents, quantification of the nitrification rate in the Lake,
and identification of ammonia concentrations with variable lake
depths." This is similar to the conclusion we reached with
regard to phosphorus in Chapter 17.
In conclusion, on the basis of the loads, and on the basis
of tracing of the motion of the plume from IHC, we can conclude
that IHC is the main local source of IJH3-N, but there are also
other sources of unknown magnitude. Reduction of NH3-N from the
IHC is the most important step to be taken, but it may not elimin-
ate WH3-W standards violations in the open waters of the Calumet
area. In the following section we recommend reductions in
169
-------
effluent loads from the IHC. These recommendations are based on
standards for the inner harbor rather than the open water, because
of the possible effect of other sources on the open water.
13.7 Required Reductions in IJH3-N from IHC
An average value of IIH3-H at the mouth of the IHC for 1973
is about 2.5 (from Section 13.5), and values of 4 are not uncommon.
Our measurements in the IHC indicate that dilutions by a factor
of 5 are usual by the time the effluent reaches LM068 and 6J;
dilutions of 10 are usual at LM102 and CAL15, In accordance with
the discussion in the previous section, we will calculate only
the reduction in IHC loadings needed to reach water quality stan-
dards at the inner harbor locations.
The concentration of NH3-N at a Lake station is the mean
value determined by mixing one part of IHC effluent water with an
amount of Lake water containing the background amount of NH3-N.
A mixing equation based on this concept is
d/R + (D - l)Cb = D-Cgtd (13.1)
where
Ci is concentration at mouth of IHC
R is required reduction ratio of effluent loads
D is expected dilution ratio in -Lake of IHC
water, so that one volume of IHC water
mixes with D-l volumes of Lake water
C, is background concentration of NHs-W in Lake
C , is water quality standard concentration in Lake.
We will consider station LM068 to represent IHC plume conditions
in the inner harbor (although it is actually just outside the
original boundary of the inner harbor) . For station L11068 we
showed in Chapter 12 that a typical dilution ratio is five-fold
(D = 5.). In Section 13.2 we showed that the background C, = 0.02.
This assumes that other nearby sources are also reduced to achieve
a Lake-wide background.
170
-------
If Ci is 4 mg/£ at the mouth of IHC, then Equation 13.1 can
be solved for R
4/R + (5 - 1)0.02 = 5-0.12
R = 7.7.
An even greater reduction is needed to reach the average
standard of 0.05, but this does not appear possible since higher
values than 0.05 are reported outside the IHC plume. We there-
fore recommend a reduction of 7.7 in the effluent loads from IHC.
In making this calculation we have been concerned only with
the effects of the effluents that can be identified with the IHC
plume. If it could be shown that the IHC effluents are responsible
for the observed NHa-H water quality violations over a wider area
than we have done, then further reductions in IJH3-N loads could
be required.
As indicated in Section 13.5, present 1TH3-N loadings to Lake
Michigan from the IHC range from 34,000 to 54,000 Ib/day. In
order to achieve water quality standards in the inner harbor, the
recommended reduction of a factor of 7.7 would lower these to
4400 to 7000 Ib/day.
13.8 Pvecommended Implementation of Reductions
The way in which the reductions are achieved is important.
Ammonia removal is a difficult task for municipal sewage treat-
ment plantP, because the available processes are somewhat uncer-
tain, especially when the wastes contain varying amounts of toxic
industrial effluents. It is usually easier and more cost-effective
tq take out ammonia at the source, where concentrations are greater,
Evidence presented in a current court case (People of the
State of Illinois vs. Inland Steel Co.) indicates that peak values
of industrial effluents to the East Chicago STP are higher than
was indicated in the Combinatorics report (1974); and that these
peaks are disrupting the performance of the STP. As a result,
NH3-W effluents from the STP are showing higher peaks of NH3-j.I
of 130 mg/&, rather than 92 as indicated by Combinatorics (1974).
171
-------
A recent EPA report (EPA 1974) states that steam stripping
is the best practicable method of removing UK 3 from steel wastes.
Coke plant operating records (People of the State of Illinois vs,
Inland Steel Co. 1974) show the effluent from an ammonia stripper
to have low values of 14 mg/Jt, buc these are interspersed by
effluents of 1300 mg/£ to the STP on single days about a week
apart. Furthermore, the effluents are sometimes overloaded with
lime. (Lime is used to raise the pH and convert the ammonia ion
to UR3 thai; can be stripped out.) The uncontrolled lime can
upset the activated sludge sewage treatment process. These fluc-
tuating industrial inputs not only provide more IW3 than the Zast
Chicago ST? can handle; they also result in intermittent poor
sewage treatment. Furthermore, the high ammonia concentrations
in the East Chicago STP effluent prevent effective chlorination
at a reasonable chlorine cost. This is the reason bacteria
counts in the IHC are so high, representative of a stream with
raw sewage.
The municipal sewage treatment plants in the area must be
protected from upsets due to dumping of toxic wastes into them
from industry. We recommend that the municipalities be required
to limit the amount of JH3, lime, toxic metal, oil and other
unmanageable inputs from industry, and that the industries be
required to install equipment chat will provide back-up protection
against upsetting peak emissions. Alternatively, the municipal
treatment plants could be expanded to handle ~>eak loads of all
pollutants from industry, appropriately cnar;;iii ; the industries
for this service. A separate study of che economics of this
approach would be needed to show thit it is feasible and cost-
effective. We f-'rr/ier recommend that these steos be supplemented
by lowered municipal loadings if neces.sar/ co achieve the
recommended total loading reductions.
The ammonia reductions must be accomplished without releasing
the ammonia to the atmosphere. Moore (1974) has expressed this
as follows: "A part of the requirement for reduction of ammonia-
172
-------
nitrogen must be control of the contribution from the steel mill
coke plant operations. Youngstown and Inland presently discharge
to the East Chicago sewer system, and U.S. Steel Corporation
discharges a portion to the Gary sewer system and the bulk to be
quenched on coke. Only Inland practices any recovery of ammonia.
Ammonia emitted to the atmosphere from quenching may eventually
fall back to the watershed with rainfall; therefore, this prac-
tice is not recommended. All three companies should recover
both free and fixed ammonia and discharge the residual to the
municipal sewer system for removal in the biological nitrifica-
tion systems to be installed."
173
-------
3
o
CAL03
IHC and Dickey Rd.
EPA data •
ON
ON
Figure 13.7
STORET WATER QUALITY PLOT
ctf
jj
o
H
co
O
«^ CO
IHC 1
IHC and Dickey Rd.
Indiana data
0)
00 O
O es +
J-l
o
r-l
O
O O
r*» 00 ON O iH
vo vo \o T^^ r*^
ON ON ON ON ON
iH rH r-< rH r-l
es co st
r«- r- i«*
ON ON ON
i-H r-l ?H
Figure 13.8
STORET WATER QUALITY PLOT
-------
Ul
BJ
CAL02
IHC and 151st St,
Figure 13.9
STORET WATER QUALITY PLOT
IHC 3S
£ EPA data
a
i •
g
; ;
o •
*>* <"> J-
---.
|f '
8 ^ ;
60 O i i : i
0 CNJ t i i i • 1 \ f
Vi ''I':,.!
i-l • ' • i ' ! •
55 i I1'-!;
1 T i i ; ; 1
5 ! ; i
1-1 ( ! , t i .
c o ' 1 ! ' • ! '
< I i 1 ' ' :
| y : i ! ' || ! '
s r^W^^l* -i i i -s| ;
o L ,
O O " " "" ' " "
I^-OOON Oi-iojrovt
vovovo r*. r* r^ r«« R*
r-l iH r-l r-4 i-4 rH r-< iH '
S
ss
1
§
«*
'M
8
c
0)
t>0
o
4J
•r4
y^
t
1
§
•<
O
0
o
AA*^ *»»•»•• ^**^ ^^^^^^ ^«» ^ ™ ^f
Indiana data
l.^ '..t;: ^r; 1 .-. ^
1 1
i'|!.l
O i 1. . , •
**"> 1 : , ;
! ' I
: ' 1
i
1 i ' '
O i . i ;
j • i I ' •
liit;
+ i i
i . ; i
i * ' i >
* i ; i i i i
i ! ; i^J j ]
L_ . ._[l_jL _.^ :_
r^ oo ON o r-i c>
vO vO vO f^o f*** Is-
O^ OH O^ O^ O^ O
1
i-"*—%
i
i
<
;
: i
i*.
*
< a
i . i.
\
i *
i
i |
i
i «
i t-
_LJ
' «*> ^
. r^ Pt
N ON tf»
Figure 13.10
STORET WATER QUALITY PLOT
-------
CAL17
Chicago SWFP Intake
EPA data
- 4-
3T
O
o
, i
:1ti'' f
1967
1968
1969 1970
Time, years
Figure 13.11
STORET WATER QUALITY PLOT
1971
1972
-------
CAU3
Calumet Harbor
EPA data
o '
^ L...
1967
4-
1968
J.
1969 1970
Time, JWU4
Figure 13.12
SHSET UAIE31 QBKLITY
tm.
-4-
-------
CAL16
Hammond Water Plant Intake
EPA data
•*: 4-
~l
oo
o
o
1967
1968
1969 1970
Time, years
Figure 13.13
STORET WATER QUALITY PLOT
-M-
-I— ' 1--
1971
1972
-------
VO
Whiting Water Plant Intake
Indiana data
1
l>
i\
\
r~-
X
o I
1967
1968
,r.f t
i ' ' 1
;+; ; H :!
' ii Uku
i i
1969 1970
lime, years
Figure 13.14
STORET WATER QUALITY PLOT
1971
1972
-------
00
o
CAL15
East Chicago Water Plant Intake
EPA data
X
1967
1968
1969 1970
Time, years
Figure 13.15
STORET WATER QUALITY PLOT
t - T __(
1971 1972
-------
CAU4
Gary Water Plant Intake
EPA data
has:
•—-4-**
•^ J
-I-
~
D
O
I
1967
Time,
f'it
:.&..
'STORET ^JATER QUALITY 3PLOT
1911
isra
-------
oo
LM G
Gary West.Water Plant Intake
Indiana data
C3
1967
1968
I t t
: f ; t t f ;l
l i
+ ..I ••: ': t
\ ': , , , , . '!
-!- -H--H-H+ -H-li+4+1-
i .._, —> -L- --^
1969 1970
Time, years
Figure 13.17
STORE! WATER QUALITY PLOT
1971
1972
-------
14. PHENOLS
Measurements of phenols at Dickey Rd on the IHC show steady
decreases in the last few years, reaching a level which falls
within the Indiana standard for the IHC; however, additional
phenols are discharged into the IHC below Dickey Rd. by Inland
and Youngstown Steel Companies. In 1973, the average values in
the Lake just met water quality standards; previous years showed
water quality violations. On the other hand, the Chicago Water
Dept. experienced a series of taste and odor periods in December
1973 which, because they were combined with high NH^-N values,
were attributed to the IHC effluents. Periods of high emissions
of phenols are still possible, but the average values are improved
sufficiently so that average water quality standards are not
exceeded. The load allocations should be reduced to reflect the
present observed performance, to prevent degradation of phenol
levels back to earlier conditions.
14.1 Water Quality Standards
The Indiana (1973) water quality standards for phenol-like
substances are 1 ug/£ monthly average for Lake Michigan, and
3 ug/£ single value. For the "inner harbor" they are 2 and 5,
respectively. For the IHC the standard is 10 p.g/4 . The Illinois
standard for water intakes is 1 ug/4.
Very low limits of phenols are permissible in drinking water
primarily because of their offensive tastes. Chlorine reacts
with phenols to produce even worse-tasting compounds; because of
the high phenol levels in the Lake near Whiting, the Whiting
water treatment plant uses ozone instead of chlorine for dis-
infecting its water supply.
14.2 Phenol Sources
There has been a marked improvement in the amounts of phenols
emitted from the IHC in the last ten years. Figure 14.1 shows
183
-------
(l) Indiana Harbor Ship Canal sampling at Canal St.
Bridge and Dickey Rd. Bridge
(7) Calumet River sampling at 92nd St. Bridge
0.25 r
Indiana Harbor Ship Canal (1
OOO
1950
250
200
oo
a
150
100
1973
YEAR
Figure 14.1
ANNUAL AVERAGE PHENOL
WEEKLY SANITARY SURVEYS
Chicago Water Department
184
-------
the annual averages of weekly samples taken by the Chicago Water
Dept. at Dickey Rd. on the 1HC. The concentrations have dropped
from a high of 200 ug/£ in 1963 to 3 in 1973. In 1973, the
highest individual value was 13, which just exceeds the IHC
standard of 10.
Of course, the Dickey Rd. station does not measure the
influence of Youngstown and Inland Steel Companies, which have
most of their outfalls downstream of this point.
EPA data shown in Table 14.1 indicates somewhat higher
values at Dickey Rd., including a value of 21 in 1973. Values
are also given at Station CAL06, at the mouth of IHC, and these
are lower because of dilution there. Table 14.2 gives some
values measured by the State of Indiana at IHC stations. The
1973 average at Dickey Rd. was 4, in agreement with Chicago
Water Dept.
14.3 Water Quality Data
Figure 14.2 shows results of phenol measurements at stations
in Lake Michigan by the Chicago Water Dept. There were vio-
lations at most of the stations in 1972, but no violations of
average values in 1973. A few individual readings of 3 were
measured, which just meet the Indiana individual value standard
for the Lake.
Figure 14.3 from the Chicago Water Dept. Radial Survey shows
a few peaks in 1972 which could be attributed to the IHC. The
data for 1973 show no peaks.
Historical records of phenol peaks at water intakes in the
Lake are shown in Storet plots, Figures 14.4 to 14.9.
These records also indicate recent improvements in phenol con-
centrations.
An unpublished report from the Chicago Water Dept. indicates
a severe taste and odor problem at the end of 1973. This suggests
185
-------
Table 14.1
PHENOL, ug/£
Annual Averages
Storet Data, U.S. EPA
CAL17
CAL16
CAL15
CAL14
GAL 13
CAL06
CAL02
CAL03
Station
Chicago SWFP
Hammond WFP
East Chicago WFP
Gary WFP
Calumet Harbor
IHC Mouth
IHC 151 St.
IHC Dickey Rd.
1971
0.062
1.4
1.1
1.0
1.6
8.58
49.7
58.
Year
1972 1973 1965-1971
1.1
2.2
2.0
1.4
1.8
8.17 6.0 21.8
16.0 57.0 163.
6.5 21. 67.
186
-------
Table 14.2
IN-STREAM WATER QUALITY
from Indiana State files
Combinatorics (1974)
Description
Water quality standard
Monitoring stations
GCR 41
72
Average
_
Phenols
0.10 TDK/ I
73
Average
0.031
72-73
Maximum
0.066
Grand Calumet River
Gary (U.S. 12)
GCR 37
Grand Calumet River
East Chicago (Kennedy Rd.)
GCR 36
Grand Calumet River
East Chicago (Indy. Blvd.)
GCR 34
Grand Calumet River
Hammond (U.S. 12)
IHC 3W
Indiana Harbor Canal
East Chicago (Indy. Blvd.)
IHC 3S
Indiana Harbor Canal
East Chicago (Dickey Rd.)
IHC 1
Indiana Harbor Canal
East Chicago (Dickey Rd.)
IHC 0
Indiana Harbor Canal
East Chicago (Youngstown Steel)
0.021
0.029
0.018
0.501
0.011
0.005
0.019
0.004
0.008
0.053
4.800
0.096
0.013
0.066
0.170
0.017
187
-------
,'S
-1968-1
1969
1971
1972
1973
8S
1968
1969
1970
1971
1972
1071
frva
t3
1
,\\\\
1
t-
H
Figure 14.2
PHENOL
ANNUAL AVERAGE AND MAXIMUM, i_g/;
Chicago Water Dept.
South Shore Lake Survey
188
-------
0.012 P-
0.010 -
0.008 -
o
c
«J
•u
o
H
0.006 -
0.004 -
OQ
0.002 -
3F 2F IF
U
2J 3J 4J
Location
5J
6J
Indiana standard
Single value
May 4
October 3
41 51 61 71
Figure 14.3
RADIAL SURVEY OF PHENOL CONCENTRATION - 1972
Chicago Water Dept.
-------
that peak values of phenol or other chemical substances may
periodically issue from the IHC. The tastes were associated
with ammonia, which as we have seen comes mainly from the IHC.
14.4 Effluent Loads
Table 14.3 lists the discharges of phenol into the IHC.
The quantities given would result in much greater concentrations
than were actually measured at Dickey Rd or at the mouth of the
IHC. It appears that phenol effluents have been reduced below
the amounts given in this table. The table reflects permit
application data.
14.5 Conclusions and Recommendations
Phenol levels have been reduced to the point where they are
not usually a significant problem, but peak values may still
cause taste and odor problems. The load allocations should be
decreased to reflect this current situation, so that they are
not more permissive than current performance.
190
-------
Table 14.3
DISCHJMCES OF PHENOL INTO THE IHC
Source: Conabinatorics (1974)
Phenols
Water Quality Standard .01 mg/1
Discharges
U. S. Steel
GW-1
GW-2
GW-2A
GW-3
GW-3A
GW-4
GW-5
GW-6
GW-7
GW-7A
GW-9
GW-10A
GW-11A
GW-1 3
ST-14
ST-17
GSTP
E.I. duPont
001
002-004
005
006-010
U.S.S. Lead
HSTP
ECSTP
Union Carbid
ARCO
Amer. St.
Foundries
Mm.
Flow
(MGD)
19.9
10.9
1.4
2.7
0.4
0.5
82.4
23.4
5.8
93.3
24.7
26.3
81.3
1.8
0.8
20.1
44.0
0.5
7.24
0.07
0.89
35.0
10.0
3 0.05
0.09
Avg.
Flow
(MGD)
28.9
16.4
2.2
3.8
1.7
0.7
87.7
29.5
10.6
120.1
34.7
34.6
94.7
2.9
1.8
30.0
52.7
1.8
10.31
0.08
2.24
0.36
40.7
14.0
0.07
5.04
0.15
Max.
Flow
(MGD)
40.7
23.0
3.9
4.5
3.7
0.9
95.3
39.4
16.9
146.0
39.7
47.2
115.6
4.8
3.3
39.3
62.0
2.4
11.66
0.12
2.98
44.0
20.0
0.11
6.77
0.27
Avg.
Load
(Ib/day)
4.82
17.80
1.84
2.30
.42
.01
234.50
1.47
.44
35.10
.58
1.13
1.58
.24
.01
22.45
1.76
.01
.10
-
.01
-
1.47
18.58
-
2.90
.02
i r\ i
Max.
Load
(Ib/day)
10.18
30.30
15.30
2.66
5.61
.01
302.00
2.63
2.68
51.18
2.64
3.94
2.89
.48
.01
47.85
5.16
.01
.12
-
.01
-
3.67
432.00
-
8.06
:n
Avg.
Cone.
(mg/1)
.020
.130
.100
.064
.030
.001
.320
.006
.005
.035
.002
.004
.002
.010
.001
.090
.004
.001
.001
.001
.001
-
.004
.159
.001
.070
.003
Max.
Cone.
(mg/1)
.030
.158
.470
.071
.182
.001
.380
.008
.019
.042
.008
.010
.003
.012
.001
.146
.010
.001
.001
.001
.001
-
.010
2.590
.001
.143
.005
Comments
-------
Table 14.3 (cont.)
Phenols — water Quality Standard .01 mq/1
Discharges
Youngstown
001 YS-20
002 YS~2
003 YS-4
004 YS-8
005 YS-11
006 YS-12
007 YS-13
008 YS-22
009 YS-14
010 YS-15
Oil
YS-18A
Inland
001 IE-2
002 4E-1
003 5E-1
004 5E-2
005 5E-3
006 6E-1
007 7E-1
008 1QE-1
Oil 13G-1
012 13H-1
013
14H-TT
014
15H-TT
015 16H-1
016 16H-2
017 16H-3
018 16F-1
Min.
Flow
(MGD)
8.46
1.50
0.53
1.03
1.19
3.30
6.30
3.00
34.00
36.60
107.80
8.60
Unknov
126.96
67.68
85.52
85.52
17.28
7.20
115.28
119.76
Avg.
Flow
(MGD)
13.70
3.62
0.98
1.40
1.60
5.70
14.00
5.00
48.70
58.00
121.60
.14
190.00
7.20
0.86
8.60
0.65
21.60
n & Hi<
158.70
50.80
106.90
106.90
21.60
9.00
144.10
149.70
Max.
.Flow
(MGD)
23.60
7.50
1.40
1.75
3.00
8.40
18.90
11.70
60.00
67,00
138.70
.29
228.00
8.60
1.04
10.40
1.30
25.90
fhly Va:
190.44
70.00
128.28
128.28
25,92
10.80
172.92
179.64
Avg.
Load
(Ib/day)
1.14
.03
.01
.01
.01
69.30
303.00
14.10
.41
8.23
11.20
-
17.40
.06
.01
.07
.01
6.32
•iable
10.00
29.60
51.60
57.00
.18
.07
1.20
1.25
Max.
Load
(Ib/day)
3.06
.06
.01
.01
.02
114.00
3040.00
606.00
.51
12.77
17.20
-
179.00
- .07
.01
.09
.01
8.21
16.00
432.01
532.93
748.90
.22
.09
1.44
1.50
Avg.
Cone .
(mg/1)
.010
.001
.001
.001
.001
1.520
2.590
.290
.001
.017
.011
.001
.011
.001
.001
.001
.001
.035
.008
.070
.058
.064
.001
.001
.001
.001
Max.
Cone .
(mg/1)
.015
.001
.001
.001
.001
2.480
26.000
12.500
.001
.023
.017
.001
.094
.001
.001
.001
.001
.038
.012
.740
.500
.700
.001
.001
.001
.001
Comments
192
-------
D
O
ro
r-
f\!
rn
CAL17
Chicago SWFP Intake
EPA data
1967
1968
-1969
1970
Time,
•Figure 14 i-4
STORE! WATER QUALITY PLOT
J1I
—+IU
1971
1972
-------
CAL13
Calumet Harbor
EPA data
0,
r\j
en
M
1967
1 ti
1968
A
j |
1969 1970
Time, years
Figure 14.5
STORET WATER QUALITY PLOT
LLJZU- .
I [II
__^_ ———"Tinr
1971 1972
-------
VO
Ul
m
CM
m
CAL16
Hammond Water Plant Intake
EPA data
1967
1968
1969
1970
Time, years
Figure 14.6
STORET WATER QUALITY PLOT
uc*
1971
1972
-------
LM W
Whiting Water Plant Intake
Indiana data
(T,
J
CD
Z
UJ
O
on
OJ
rn
o
o
o
oo
o
o
1967
1968
J
1971
1972
Figure 14.7
STORET WATER QUALITY PLOT
-------
CAL15
East Chicago Water Plant Intake
EPA data
V£>
en
UJ
i:
Q_
O
on
r-
PJ
1967
1968
1969
1970
1971
1972
Time, years
Figure 14.8
STORE! WATER QBALITY PLOT
-------
CAL14
Gary Water Plant Intake
EPA data
vo
00
L'J
CO
_J
D
Q_
O
m
r-
OJ
ro
1967
1968
1969 1970
Time, years
Figure 14.9
STORET WATER QUALITY PLOT
1971
1972
-------
15. OIL MID GREASE
Available data on oil and grease in Calumet area waters is
obtained fron Storet and presented in Table 15.1. The values in
IHC generally fall within the Indiana Standard of 5 mg/£; however,
there are daily oil spills and emissions into the IHC, which we
documented by aerial photos during our sampling program. Oil
slicks are practically always observable in the Lake coming from
IHC, and they are blown by the wind many miles.
Oil can also be carried into the bottom sediments with solid
particles, and the oozy bottom of IHC and the inner harbor have
been observed to contain a large fraction of oil (see Table 7.1.)
Visual observations of oil on the surface and bottom of the IHC
and along its banks constitutes a violation of the practical
standards of Indiana for the IHC.
The Corps of Engineers (1968, Appendix V) report summarizes
the following harmful effects of oil pollution: "Oil pollution
is a deterrent to industrial and domestic use of water as well as
being detrimental to the marine environment. Oil films inter-
fere with gas exchange, exert a toxic action on some organisms,
and interfere with the natural marine life cycle by coating both
plankton and bottom. If oils become adsorbed on sediments they
then are available for later release with agitation. Oils impart
a disagreeable taste and odor to domestic water supplies and are
detrimental in industrial food and beverage preparation.
The Technical Committee (1970, Table 3) estimated total
effluents of oil to the IHC at 100,000 Ib/day, with an additional
20,000 Ib/day going direct to Lake Michigan outfalls. The Corps
of Engineers study (1968, p. 103) estimated that oil and grease
removed from the IHC in dredging spoils in 1967 amounted to
1750 tons (3,500,000 Ib, or the equivalent of 175 days accumula-
tion) . Combinatorics (1974) did not report the industrial load
of oil and grease, but the loads can be estimated from outfall
flows and permit effluent data given in Appendix C, at least for
the three major steel companies. The loads in Table 15.2 total
199
-------
48,000 Ib/day to the IHC. The BOD5 loadings from steel mills
and ARCO in Table 15.2 agree very well with the oil and grease
loadings; this checks the estimates since oil and grease should
comprise most of the organic effluents from these industries.
Appendix C does not contain sufficient data to calculate the
loads from the petroleum refineries on the IHC, but the Technical
Committee (1970, Table 3) indicated that the Mobil and Sinclair
(now ARCO) refineries contributed 500 and 1700 Ib/day of oil
respectively in 1968. Thus the total load has been reduced from
100,000 to 50,000 Ib/day since 1968, according to the permit data,
Loads direct to Lake Michigan are computed from permit data
as follows: American Oil 1870 Ib/day; Union Carbide 1125 Ib/day;
U.S. Steel Gary 3700 Ib/day, for a total of 6700 Ib/day.
Although there may have been an improvement in oil loads,
harmful effects of oil pollution are still evident in the IHC and
the Lake. We recommend that either the oil or the BOD5 alloca-
tions be reduced as a means to require the steel mills to dras-
tically reduce the amount of oil they discharge into the IHC.
Until this is done the IHC will remain an inhospitable place for
aquatic life, and the impact on aquatic life of the Lake will
continue to be substantial (Howmiller, Appendix A).
200
-------
Table 15.1
OIL AND GREASE, mg/£
Annual Averages
Storet Data, U.S. EPA
CAL17
CAL16
CAL15
CAL14
CAL13
CAL06
CAL02
CAL03
Year
Station 1971 1972
Chicago SWFP 4.8
Hammond WFP 5.57
East Chicago WFP 4.9
Gary WFP 5.3
Calumet Harbor 5.6
IHC mouth 6.1 5.0
IHC 151 St. 5.9 5.0
IHC Dickey Rd. 8.8 5.0
Table 15.2
SUMMARY OF EFFLUENT LOADS, IHC
Ib/day, existing averages
Discharger Oila
U.S. Steel 10,200
Gary
E. I. duPont de Nemours
U.S. Lead
East Chicago S.D.
Hammond S.D.
Union Carbide
ARCO
American Steel Foundry
Youngs town 9,970
Inland 27,500
1965-1971
1.7
1.8
1.7
1.7
2.3
3.5
4.76
21.5
BODsb
10,488
12,100
100
5
11,100
7,800
1
400
1
9,233
27,620
a D
Appendix C Combinatorics (1974)
201
-------
CAL02
IHC and 151st St.
EPA data
CAL06
IHC mouth
EPA data
N>
O
•P
O
H O
hJ CO
X
c/i
__ I '*' IUM — LJ.;-- -i-oi- -- -|-J»
(1)
CO
CO
(1)
o
m
o
o o
r-1 r-t
Figure 15.1
STORET WATER QUALITY PLOT
Figure 15.2
STORET WATER QUALITY PLOT
-------
CALll
Calumet River mouth
EPA data
CAL13
Calumet Harbor
EPA data
X)
o
tO
4J
O
H
X
en
-------
S3
O
CAL16
Hammond Water Plant Intake
EPA data
CO
O
H
H O
i-J c"">
X
CO
0)
CO
CO
0)
M
O
i
1-1
•r-l
O
§
O
CN
ON
Figure 15.5
STORET WATER QUALITY PLOT
CAL17
Chicago SWFP Intake
EPA data
4-1
O
H
H 0 ,
£
t?
0)
CO
CO
-------
16, BACTERIAL POLLUTION
16.1 Introduction and Summary
Human uses of the Calumet area of Lake Michigan have been
severely restricted by bacteriological contamination of the near-
shore waters. These restrictions have included greater water
treatment costs to achieve potable quality water and a restric-
tion on bathing at beaches in this area of the Lake (Technical
Committee 1970).
Bacteriological contamination measured in the form of total
coliform, fecal coliform and fecal streptococci comes into this
area of the Lake from many sources. Municipal sources such as
combined sewer overflows discharge directly to the Lake as well
as to tributary streams. Incompletely treated effluents from
municipal treatment plants are the other major contributors.
Substantial investments of capital and effort have been applied
to eliminate the combined sewer overflow problem. The Hammond
Robertsdale outfall and the Whiting Front St. outfall are now
supposed to be inoperative, but our observations suggest that
this is not yet the case. (See Section 16.5.) The three major
sewage treatment plants (Hammond, East Chicago, and Gary) have
been upgraded. Although improved, they are still the major
sources of coliform bacteria discharged into this area of the
Lake. Industrial discharge of coliform material appears to be
only a minor contributor to the coliform pollution, based on
permit application data.
Data presented in the following sections show that there
has been little improvement in coliform pollution in this part
of the Lake in the past five years, in spite of attempts to
upgrade the sewage treatment plants. The reasons for this are
discussed and steps to bring about improvement are recommended.
16.2 Water Quality Standards
Different standards apply to different areas of southern
Lake Michigan and its influent streams. The Indiana and Illinois
205
-------
standards for fecal coliform and their area of application are
given in Table 16.1. Illinois standards apply only to the open
Lake while Indiana has standards for the open Lake, Harbor areas,
the beaches and Indiana Harbor Canal.
The U.S. EPA (1973) has proposed fecal coliform standards
of 10,000/100 mi for fresh water used as a source of public water
supply. No applicable standards have been promulgated for total
coliform or fecal streptococci by Illinois or Indiana. The U.S.
EPA (1973) has proposed standards for total coliform of 2,000/
100 m£ for wildlife water uses and 10,000/100 m£ for fresh water
public water supply uses. The International Joint Commission
(1972) established the specific objective of 1,000 total coliforms
per 100 m£ and 200 fecal coliforms per 100 ml for the boundary
waters area of the Great Lakes. Of course, this does not include
Lake Michigan.
16.3 Water Quality and Violation of Standards in Lake
Michigan"
Howmiller (Appendix A) reviews published data on the bac-
terial flora of Lake Michigan. Most of the measurements have
been made at water intakes and beaches, and have concentrated on
bacteria of sewage origin. The trends of beach pollution in the
past decade are reviewed, and it appears that problems at the
Calumet area beaches are not new. Coliform densities in the IHC
were even higher a decade ago than now; values as high as
25,000,000 per 100 m£ were recorded. Twenty-three pathogenic
strains of salmonellae were found regularly in the Grand Calumet
River.
The most extensive data on water quality are those obtained
from Lake Surveys conducted by the Chicago Water Department.
Data on fecal coliform from the South Shore Survey are summarized
for the years 1968-1972 in Figure 16.1. These show that while
there is extensive violation of the open Lake water quality
standards of 20/100 mC, only sample station 5S, located immediately
206
-------
fO
o
Table 16.1
WATER QUALITY STANDARDS
FECAL COLIFORM (MPN or MF/lOO me)
Agency
ISPCB
ISPCB
111. EPA
U.S. EPA
IJC
Regulation Open water
SPC 4-R 20
SPC 7R-2
Chap. 3, Part 2 20
Paragraph 206
Proposed
Annex 1, 1. (a) 200
Lake Michigan
Inner harbor
1,000
(2,000)*
-
-
2,000
(secondary contact)
-
IP»I
'"-*
Beaches I$C,
200
(400)*
1,000
(2,000)*
-
200
-
''"maximum not to be exceeded in more than 107o of the samples.
Proposed criteria for water quality, October 1973, U.S. EPA. (As required by
Section 304(a) of the 1972 Water Quality Act Amendments.
-------
HAMMOND INTAKE (00 Mop)
O5,OOOFt.FromShor«
ORI-UZO
ORI-660
LAKE: MICHtGA N
OR2-I320
OR2-660
Robertsdole Outfall
WPB-Wti,tingPork B«acr
(NJ-No/lh
(Si— Souto
O— Sampling Station
111
\\l
OP 5 f'11
' „ - RS-.Ov.
- ' ,. • --Xjl'- '—x," '-ii;!
<^"'\\ /'f-.^r-v WP9
-------
north of the entrance to the Indiana Harbor Canal violated (1969)
the inner harbor water quality standards of 1,000/100 m£ . The
fecal coliform count at the near-shore stations of 3S, 4S, and
5S frequently exceeded the Indiana beach standard of 200/100 m£ .
During the past five years, the fecal coliform concentration
in the Calumet area has not shown any significant change, as
indicated by Chicago Water Department Surveys in Figure 16.1.
Analysis of the intake water quality data for the Whiting
and Hammond public water supply plants for the years 1967-1972
show frequent instances of 20,000 to 180,000 total coliforms/
100 me (Chicago Water Dept, Calumet Area Surveys 1967-1970).
During the period June 13 to July 20, 1972, the Illinois
District Office of U.S. EPA conducted bacterial analyses at
eight near-shore locations (Figure 16.2) from the Hammond Beach
to the American Oil Company at Whiting. Their results in
Table 16.2 show that on certain dates various sample stations
had very high total and fecal coliform and fecal streptococci
counts; while on other dates the counts were close to the back-
ground level for this area of the Lake. These incidents of local
high bacterial counts were suspected to be due to combined storm
and sanitary sewer overflows from the Robertsdale and Front St.
outfalls shown in Figure 16.2.
Table 11.3 indicates that bacterial pollution from the IHC
was measured by IITRI at station LM102, five miles out in the
Lake on November 14, 1973. The total coliform count was 1,000/
100 m£ . This indicates that sewage effluents from the IHC can
exceed sanitary standards over a large region of the Lake.
16.4 Sources of Bacterial Pollution
In this section it will be shown that the main source of
bacterial pollution in the Calumet area is the IHC, and that
the main bacterial discharge sources on the IHC are the three
municipal sewage treatment plants and the combined sewer outfalls.
The other important sources on the Lake are three combined sewer
209
-------
Indiana Water Quality Standard
Geometric Mean
Fecal Coliform 0.20/100 ml
Figure 16.1
FECAL COLIFORM
ANNUAL AVERAGE AND MAXIMUM, No. 7100 me
Chicago Water Dept.
South Shore Lake Survey
208
-------
Table 16.2
BACTERIA COUNTS AT HAMMOND AND WHITING BEACHES IN 1972
Data from U.S. EPA unpublished survey
Selected dates showing high counts
Date
June 01, 1972
June 29, 1972
July 03, 1972
July 14, 1972
July 18, 1972
July 24, 1972
j f
S ta t i on
Rl-1320
Rl-660
Rl-100
R2-1320
R2-660
R2-100
R3-1320
R3-660
R3-100
WPB(N)
WPB(S)
R2-1320
R2-660
R2-100
R2-1320
R2-660
R2-100
R3-1320
R3-660
R3-100
WPB (N)
WPB(S)
R2-1320
R2-660
R2-100
R3-1320
R3-660
R3-100
WPB(N)
WPB(S)
R2-1320
R2-660
R2-100
Total
coliform
>3,000
>3,000
11,000
200
70,000
96,000
2,000
130,000
260,000
370,000
310,000
150,000
390,000
1,200,000
110,000
210,000
230,000
260,000
270,000
300,000
280,000
330,000
540,000
3,300,000
3,300,000
2,700,000
1,700,000
1,000,000
1,000
18,000
13,000
Bacteria
Fecal
coliform
770
670
2,100
2
60
86
4
110
240
230
250
130
8,500
2,300
180
1,200
2,200
460
110
360
720
930
640
4,800
4,200
3,700
1,900
1,200
<10
20
200
Fecal
Streptococci
<2
550
270
24
550
230
1,300
1,100
860
22,000
9,400
380
740
1,500
380
940
1,700
590
700
1,000
11,000
10,000
8,000
5,600
3,500
20
190
700
211
-------
outfalls from Hammond and Whiting. The Calumet River also con-
tributes some bacterial pollution, but it is much less than the
IHC (we estimate it amounts to 1% of the IHC).
During IITRI's sampling program in November-December 1973,
the total coliform bacteria count in the IHC at Columbus Drive
(station IHC3S) averaged 200,000/100 m£ , and the maximum was
360,000. At the mouth of the IHC (CAL06) total coliform averaged
20,000. The Chicago Water Department's weekly Calumet Area
survey samples at Dickey Rd. bridge on the IHC show total coliform
counts of 500,000 to 5,000,000/100 me (Figure 16.3). The current
values are less than the highest values encountered more than
five years ago.
The sources of bacterial pollution on the IHC are the three
municipal sewage treatment plants, and combined sewer outfalls.
The average discharge flows from these plants are known, but the
plants do not measure their bacterial contents. On the average,
the Hammond, East Chicago and Gary STP's discharge 94.5 mgd to
the Grand Calumet River, and this usually flows to the Lake via
the IHC. (Table 5.1, Chapter 5). The flow rate of combined
sewer overflows is known only for Hammond; it amounts to 17 mgd,
or approximately 50% of the 36 mgd flow from the Hammond STP.
Seventy-four percent of the Hammond combined sewer overflow goes
to the Lake via the IHC (Table 5.6). Table 5.5 is an estimate
of all the combined sewer overflows.
In 1972 and 1973, the State of Indiana measured the fecal
coliform concentration in the east and west branches of the Grand
Calumet River and the Indiana Harbor Canal. Average values for
these two years are shown in Table 16.3. The location of the
monitoring stations may be obtained by reference to Figure 6.2.
Data in Table 16.3 show that the most consistently high fecal
coliform counts were obtained from the west branch of the Grand
Calumet River at stations on either side of the Hammond STP
(stations GCR 34 and GCR 36).
212
-------
O
O
o:
UJ
8 2
LU
cr
UJ
1950'
Indiana Harbor Ship Canal
Dickey Rd. Bridge
92nd St. Bridge
' '
YEAR
'I9TO
Figure 16.3
ANNUAL AVERAGE COLIFORM ORGANISMS PER 100 ML
WEEKLY SANITARY SURVEYS
. Chicago Water Department
213
-------
Table 16.3
IN-STREAM WATER QUALITY - FECAL COLIFORM, 1973
from State of Indiana Files
CoiAoinatoricG (1974)
Description
Water quality standard
Monitoring stations
GCR 41
Grand Calumet River
Gary (U.S. 12)
GCR 37
Grand Calumet River
East Chicago (Kennedy Rd.)
GCR 36
Grand Calumet River
East Chicago (Ipdy. Blvd.)
GCR 34
Grand Calumet River
Hammond (U.S. 12)
IHC 3W
Indiana Harbor Canal
East Chicago (Indy. Blvd.)
IHC 3S
Indiana Harbor Canal
East Chicago (Columbus Drive)
IHC 1
Indiana Harbor Canal
East Chicago (Dickey Rd.)
IHC 0
Fecal coliform
Geometric mean
1000/100 ml except
during storm runoff
72 73 72-73
Average Average Maximum
6,733 1,861 39,000
3,919 1,340 33,000
306,171 64,665 1,300,000
619,242 43,189 3,300,000
2,952 1,138 16,000
4,050 4,160 30,000
26,858 1,293 63,000
971 2,300
Indiana Harbor Canal
East Chicago (Youngstown Steel)
214
-------
IITRI conducted sampling in the Grand Calumet R.iver on
November 29, 1973, in an attempt to locate the major bacterial
sources. This was necessary because the STP only measures the
residual chlorine in their effluent and not the bacterial concen-
tration. We used the stations defined by Combinatorics (1974) as
follows:
HSTP2B downstream from Hammond STP
ECST-1 upstream from East Chicago STP
ECST-2 downstream from East Chicago STP
USL-1A downstream from Gary STP, near
junction with IHC.
Our data are given in Table 16.4. These show that the East
Chicago STP was the largest source of total coliform count at
that time. Chapter 5 indicates that Hammond STP increased the
amount of its chlorination in 1973, reducing the bacterial pollu-
tion in the adjoining part of the Grand Calumet River.
The appearance of the Grand Calumet River near the Hammond
STP outlet is that of an open sewer, with floating sewage debris,
fungal growths, and anaerobic bottom conditions. Some self-
purification is evident downstream towards the East Chicago STP,
but the appearance again deteriorates below the East Chicago STP.
On the east branch of the Grand Calumet River the flow is much
larger, and the influence of the Gary STP is less evident,
although the bacterial count is substantial.
The BOD removals of the three STP's are (from Chapter 5):
Sewage treatment plant %
Hammond 80% (1972)
East Chicago 63% (1973)
Gary 77% (1973)
215
-------
Table 16.4
WATER QUALITY MEASUREMENTS NEAR MUNICIPAL SEWAGE TREATMENT PLANTS
IITRI data, November 30, 1973
Parameter
Temperature
Conductivity
pH
Turbidity
Dissolved oxygen
Chloride
Fluoride
Ammonia -nitrogen
Total phosphorus
Total coliform
Total organic carbon
Total solids
Nonfilterable residue
(suspended solids)
Chlorophyll
Volatile solids
Iron (total)
Iron (dissolved)
Storet
No.
00010
00095
00400
00075
00300
00940
00950
00610
00665
35501
00680
00530
-
00505
00680
00681
Units of
measurement
°C
[amho/cm
pH units
Jackson
mg/£
mg/£
mg/1
mg/4
mg/£
MFIM ENDO
100 ml
mg/£
mg/i
mg/£
mg/£
mg/ji
mg/£
HSTP
2B
16.5
910
8.2
16.0
103
0.45
4.5
1.66
200
31.
665
26.1
-
22.9
0.66
0.11
ECSIP
15.0
820
7.4
9.1
120
0.54
7.6
1.83
18,000
27.
507
16.9
-
12.6
0.53
0.10
ECSIP
-2
14.0
1,010
7.0
9.0
170
0.82
21.0
1.26
520,000
36.
757
11.1
-
10.1
0.55
0.11
USL
1A
18.0
350
7.6
14.0
40
0.93
2.6
0.48
25,000
10.
216
19.2
-
6.0
0.67
0.09
-------
iThe Technical Committee (1970) recommended that the quality of
i
!effluent from the East Chicago STP must be improved. Little
improvement is evident. (See Appendix D ). The reason for its
poor performance is discussed in Chapters 5 and 13, and is
primarily due to upsets in the biological treatment process due
to inputs of industrial effluents from Youngstown Sheet and Tube
and Inland steel Mills. Excess lime from ammonia stripping,
large amounts of ammonia, and probably other toxic materials
impair the biological oxidation process at this STP.
The ammonia alone is a sufficient explanation for the high
effluent bacteria concentrations, since excess ammonia prevents
effective chlorination of the effluent. Improvement of per-
formance of this plant will require more effective pretreatment
by the steel industries. (See Chapters 5 and 13 where this is
discussed.)
16.5 Combined Sewer Overflows
There are 31 combined sewer overflows which can contribute
to the pollution of the Calumet area (Figure 5.2, Chapter 5).
The sources are:
Hammond Sanitary District 15
Metropolitan Sanitary District
of Greater Chicago 1
Gary Sanitary District 8
Whiting Sanitary District 2
East Chicago Sanitary District 5
There are additional overflows for storm water only. The Roberts-
dale outfall of the Hammond Sanitary District was supposed to be
discharging only chlorinated storm water as of May 1973; however,
, on November 30, 1973, we observed a large area containing a black
colored discharge that came directly from the Robertsdale outfall.
This indicates that improper discharges may still be entering
this "storm water only" system. The city of Whiting is responsible
217
-------
for two combined sewer outfalls to Lake Michigan. These three
lake-side outfalls, shown in Figure 16.2, are most probably
primarily responsible for the near-shore and beach bacterial
pollution referred to in Section 16.3.
The raw water samples at the Whiting water plant (LM047A)
typically show total coliform counts of 500 to 1000 (Table 11.3)
and on November 14, 1973, the count was 40,000. The currents
were not in the proper direction to attribute these high coli
values to discharge from the IHC. The Amoco refinery seems an
unlikely source for coli. The high counts suggest continuing
discharges from the three outfalls shown in Figure 16.2. The
problem from Whiting outfalls may be solved by present construc-
tion of a larger sewer, to carry Whiting sewage to the Hammond
system. In the past, the size of this connection has been said
to limit the flow, resulting in overflow to the Lake whenever it
rained.
16.6 Conclusions
The main conclusions that can be drawn from this study of
the bacterial pollution of the southern end of Lake Michigan are:
• There continues to be frequent violation of
the Indiana Water Quality Standards for the
Harbor, Beach and Open Water areas of this
part of the Lake.
• The main source of coliforms is the Indiana
Harbor Canal. Discharge from the Calumet
River is of much less significant, although
it is badly contaminated.
i • Effluent from the East Chicago STP appears
', to be the main coliform source to the IHC.
• The relative contributions from the Hammond
; STP and Gary STP are less. The reasons why
j the East Chicago STP does not function
| effectively were discussed in Chapters 5
i and 13.
: • Until flow meters are installed on the Gary
: and East Chicago combined sewer overflows,
their contribution to the total bacterial
218
-------
contamination will not be assessible. The
volume .of the Hammond Sanitary District
combined sewer overflow averages about half
of the treatment plant discharge. Infor-
mation on the strength of its bacterial
contamination is not available.
We were able to detect total coliforms,
traceable as originating in IHC discharge,
five miles out into the Lake on November 14,
1973, at station LM102.
High levels of bacterial contamination along
the Hammond and Whiting beaches appear to
be caused by combined sewers discharging to
the Lake at Robertsdale and Front St. The
Robertsdale outfall is supposed to be only
chlorinated storm water.
219
-------
X
o
o
D
O
O
LT)
m
CAL16
Hammond Water Plant Intake
EPA data
= i
r -.
O
o ..
o
1967
1968
--f
1969 1970
Time, years
Figure 16.4
STORE! WATER QUALITY PLOT
:-- --^H-U
4
1971
1972
-------
X
I
O
LO
rn
O
O
in
c j
o
o
LM W
Whiting Water Plant intake
Indiana data
1967
Lusa,,
19711
1968
1969 1970
Time, years
Figure 16.5
STORED WA^ER QUALITY PLOT
-------
I
f
* 17. PHOSPHORUS
1701 Introduction
Phosphorus represents one of the most serious pollution
problems in the Calumet area of Lake Michigan. Phosphorus con-
centrations are relatively high in the near-shore waters of the
Calumet area. The consensus of biologists is that these high
levels are responsible at least in part for the observed eutro-
phication of near-shore waters (Phosphorus Technical Committee
1972; Thomas, Hartwell and Miller 1972; and Schelske and Roth
1973). Control of phosphorus would limit eutrophication (Schindler
1974).
Phosphorus is one of the most important pollutants in Lake
Michigan because its concentration controls one of the most
evident effects of pollution, namely the growth of algae. The
harmful effects of various kinds of algae in clogging of water
intakes, forming unpleasant deposits on beaches and detracting
from the enjoyment of the water are discussed in Chapter 8 and
in Appendix A. Although Lake Michigan is not yet affected to the
extent of Lake Erie, the deterioration of near-shore conditions
in Lake Michigan in the last 15 years is alarming. As discussed
below, we do not have sufficient knowledge about the phosphorus
cycle in the Lake to predict reliably the length of time needed
for the Lake to recover after phosphorus inputs are reduced.
For these reasons the information in this chapter is important,
as well as the recommendations for further phosphorus control.
Our analysis of available data shows that the long-range
trend of phosphorus in the Calumet area has increased in the
past 15 years.
Control methods by the State of Indiana have lowered phos-
phorus from the IHC since 1970, and this may be responsible for
a slight decrease that is noted in near-shore concentrations.
We recommend further inspections to insure that controls are
properly carried out, so that phosphorus effluents can be further
222
-------
reduced to the. levels recommended by the Phosphorus Technical
Committee (1972). Further control efforts, should also be carried
out by Michigan, Illinois and Wisconsin to achieve the recommended
reductions.
17.2 Effluent and Water Quality Standards
The Phosphorus Technical Committee (1972) of the Lake Michigan
Enforcement Conference stated that a phosphorus reduction of more
than 8070 was needed. It was decided that this could best be
achieved by setting a limitation of phosphorus concentration in
municipal and industrial effluents of 1 mg/£, and this has nox7
been embodied in Indiana standards.
Water quality standards also exist for various waters, and
they are given in Table 17.1.
The Illinois limit is substantially lower than the Indiana
standards. The International Joint Commission (1973) (for other
Great Lakes) recommends that phosphorus levels be limited to
values that will prevent nuisance growths of algae, weeds and
slimes, but does not give a numerical value. The Phosphorus
Technical Committee (1972) quotes Vollenweider (1968) who speci-
fies a value of 0.01 mg/£ dissolved phosphorus to prevent nuisance
algal blooms. The Committee considers 0.02 to 0.03 total P to
be an equivalent goal for Lake Michigan.
17.3 Water Quality and Violations of Standards in
Lake Michigan
The most extensive data on water quality are those obtained
from Lake surveys conducted by the Chicago Water Department.
Data from the Shore surveys are summarized in Figure 17.1. Most
of the values exceed the Illinois standard and the recommendation
of the Phosphorus Technical Committee, and some exceed the
Indiana standards.
A striking increase is noted in 1973, but we do not believe
it represents a trend. The difference from previous years is due
223
-------
to one sampling run done in May 1973 when very high values were
found at all stations. Knight, Schmeelk and Lue-Hing (1972)
reported a similar high sampling run in May 1970, 1000 ft off
Worth Avenue, Chicago, and 5000 ft off Zion, Illinois. These
individual high values appear to be unusual or sporadic events,
and we cannot conclude from them that there is an upward trend
in 1973. Excluding the May run, the 1973 values would average
about 0.02 mg/£.
224
-------
Table 17.1
WATER QUALITY STANDARDS
PHOSPHORUS, TOTAL, mg/£ AS P
Lake Michigan
Open water Inner harbor
Agency
Indiana
Illinois
Phosphorus Technical
Committee
Ul
Regulation Average
SPC 4R 0.03
206
Single Single
value Average value
0.04 0.03 0.05
0.007
Indiana Harbor Canal
Single
Regulation value
SPC 7R-2 0.10
0.02
(recommendation)
-.
-------
.11
Figure 17.1
PHOSPHORUS
ANNUAL AVERAGE AND MAXIMUM, PPM
Chicago Water Dept.
South Shore Lake Survey
-------
The data in Figure 17.1 from the South Shore survey show
little correlation with position in the Lake, indicating that the
general phosphorus level in near-shore waters cannot be directly
traced to a local source; however, on three dates the Radial
Surveys of the Chicago Water Department plotted in Figures 17.2
to 17.4 clearly show peaks of phosphorus concentration at
stations 5J to 6J in the usual path of the plume from IHC. This
indicates that the contribution from the IHC is detectable and
significant, although it does not account for the main phosphorus
level throughout this part of the Lake. Other phosphorus data
from the U.S. EPA and from the State of Indiana are plotted in
Figures 17.7 to 17.12 (Storet data). An IITRI measurement
indicating a nutrient effect from the IHC plume is described in
Section 17.5.
Long-term trends of phosphorus are indicated by the data
for the Chicago South Water Filtration plant intake, plotted in
Figure 17.5. Although there are cyclical variations, there is
a general upward trend. Since 1971 there is a slight downward
trend. This will be discussed below.
The increasing concentrations of phosphorus and perhaps also
of nitrogen are believed to be the cause of increasing growths
of algae. A study by Thomas, Hartwell and Miller (1972) used
the nutrient algal assay method to determine that Lake Michigan
algal growth is primarily limited by phosphorus and secondarily
by nitrogen. Increased fouling of beaches by cladophera and of
water intakes by various algae are discussed in Chapter 8. These
biological growths tend to reflect average nutrient levels. The
increasing growths confirm that the increasing measured nutrient
concentrations are real, and are not due to sampling variations.
17.4 Background Phosphorus Values
Background values of phosphorus in Lake waters far from any
sources of pollution have been reported. Scheiske and
227
-------
N>
CO
Q.15
0.13
Figure 17.2
RADIAL SURVEY OF TOTAL PHOSPHORUS CONCENTRATION - 1970
KA Chicago South Water Filtration Plant
71
-------
O.lSr-
tsJ
3F 2F
I
41
3une 15
51
61
Figure 17.3
RADIAL SURVEY OF TOTAL PHOSPHORUS CONCENTRATION - 1971
Chicago South Water Filtration Plant
-------
U>
O
0.06
0.05 -
„- 0-04
D
a
en
o
•u
O
H
0.03
0.02 .
0.01 L
3F 2F
U 2J 3J
6J
4J 5J
Location
Figure 17.4
RADIAL SURVEY OF TOTAL PHOSPHORUS CONCENTRATION - 1972
Chicago South Water Filtration Plant
May 4
October 3
June 27
7J 41 51 61 71
-------
0,07
0.06
0.05
VI
3
; 0.04
« 0.03
4-»
O
0.02
0.01
Note: Prior to 1966, data
points represent single
samples analyzed once
every 3-4 months. After
1966, the points are
averages of
daily samples.
i I
I
1957 1959
1961 1963 1965 1967 1969
Time, years
Figure 17.5
1971
1973
TOTAL PHOSPHORUS CONCENTRATION - 1956-1973
Chicago South Water Filtration Plant
-------
Roth (1973) analyzed 16 samples of water fron six locations and
five depths in the northeast corner of the Lake, near Charlevoix,
Michigan. The samples were taken in July 1970. The mean value
of soluble phosphorus was 0.0017 + 0.0012 mg/£ P. The smallest
value was 0.0013 at 40 m depth. A greater amount of phosphorus
was contained in suspended particulate matter; this form of phos-
phorus averaged 0.0060 + 0.0077 mg/£ P. The smallest value was
0.0028 at the surface and the largest was 0.018 at 40 m depth, due
to settling of particulates. Adding these two forms, the total
phosphorus averages 0=008 mg/£. These values compare with an
average of 0.020 for the Chicago Water Department South Shore
surveys. The concentrations in the Calumet area are well above
those in the Charlevoix area,
Risley and Fuller (1965) reported results of surveys across
the Lake at several latitudes. One survey at the latitude of
Sheboygan, Wisconsin, gave phosphorus values of 0.02 mg/£ near
shore and 0.01 in the center of the Lake. At the latitude of
Calumet Harbor the values were 0.04 to 0.10, with the highest
values on the Michigan side. These measurements were made in
1962-1963. There may have been interferences in the analysis of
samples near shore (Fuller 1974).
Powers and Ayers (1967) summarize total phosphorus measure-
ments in mid-Lake waters. In the northern half of the Lake the
average is 0.006 mg/£ P, in agreement with the results of Risley
and Fuller (1965). Risley and Fuller's averages at Chicago
latitude are 0.013 mg/£, and at the Whiting latitude they average
0.020 mg/S,.
Holland and Beeton (1972) measured water parameters at five
locations on a transect from Milwaukee to Ludington from May
1970 to January 1971. The average value of total phosphorus was
0.0085 mg/£ at all stations except near Milwaukee, where the shore
water had higher values. The sampling was continued to October
1971 (Rousar 1973). Again the average value of total phosphorus
in the open Lake was 0.0085 mg/£.
232
-------
1 From all of the above data, we can conclude that a repre-
sentative background concentration of total phosphorus in open
Lake waters is 0.008 to 0.009 mg/£. Concentrations in near-shore
waters are generally higher, at least near sources of pollution.
17.5 Sources of Phosphorus
Table 17.2 (Phosphorus Technical Committee 1972) lists the
phosphorus inputs of various rivers to Lake Michigan. The Fox
River at Green Bay is the largest source, followed by the Grand
and St. Joseph at the southeastern end of the Lake. The IHC
contributes about 7% of the total. In addition to the rivers
there are other inputs to the Lake. Table 17.3 lists other point
sources, mostly municipal treatment plant outfalls. Those in
northeastern Illinois and southern Wisconsin contribute another
3,500,000 Ib/yr.
Shore currents might carry phosphorus effluents to the
Calumet area from the St. Joseph and Grand Rivers in Michigan,
as well as from sewage treatment plants on the north shore of
Illinois and Wisconsin. Such shore currents are known from
general circulation patterns (FWPCA 1967) and are also indicated
by recent ERTS satellite photos (Photo No. E-1394-16035 401)
which show sediment being carried down the eastern shore to the
Calumet area. Furthermore, algal damage to eastern Lake beaches
has been documented (FWPCA 1968) indicating that phosphorus
nutrient effects are observed at other points along the path of
travel of pollutants. Examination of the measured total phos-
phorus values for Calumet waters sho\m in Figures 17.2 to 17.4
indicates that there are some peaks due to the IHC plume, but
there is also a general high phosphorus level in the area. How
much of this high level is due to the IHC and how much to the
more remote sources cannot be determined from the data, partly
because we do not know the residence time of phosphorus in the
Calumet area. The larger inputs from the remote sources, and
the known currents that can carry phosphorus from remote sources
233
-------
Table 17.2
TOTAL PHOSPHORUS LOADING TO LAKE MICHIGAN
TRIBUTARY CONTRIBUTIONS
Source: Phosphorus Technical Committee (1972)
Tributary
Total
Drainage
Area
Average
Discharge
Tributary
Phosphorus
Discharge
To Lake
so. mi.
cfs
1000#/yr.
Root
Mi Iwaukee
Sheboygan
Manitowoc
West Twin
East Twin
Kewaunee
Fox
Pensaukee
Oconto
Peshtigo
Menonrfnee
B1g Cedar
Ford
Escanaba
Whitefish
Manistlque
Boardman
P1ne (Charlevoix)
Manistee
Pere Marquette
Pentwater
White
Muskegon
Grand
Black (Holland)
Kalantzoo
Black (S. Haven)
St. Joseph
Burns Ditch
Ind. Harbor
196
845
440
442
166
140
146
6,443
160
933
1,155
4,150
387
468
920
315
1,450
347
370
2,010
772
172
480
2,780
5,534
176 .
2,069
83
4,311
330
SsTTW
184
470
232
195
85
71
80
6,130
144
825
1,010
3,427
309
435
1,104
386
2,327
331
396
2,418
846
182
496
2,990
4,431
133
2,535
359
5,635
327
2.7DO
41,193
191
379
168
142
36
30
40
2,654
25
162
99
809
30
25
108
30
274
123
31
238
166
21
48
529
2,180
44-
648
84
2.107
199
850*
12,470
Unoonltored tributary non-point source contribution 1s taken to be 725,000
pounds per year (100 pounds of Phosphorus per square mile).
Total contribution from tributaries is thus estimated at 13.2 million pounds
*Indiaro Harbor figuremay include Phosphorus originally taken from lake by
Industrial coolfnf water use.
23A
-------
Table 17.3
ESTIMATED PHOSPHORUS SOURCES FOR 1AKE MICHIGAN
Source
Direct waste water sources
Indirect waste water sources
Total waste water sources
Load (million Ib/yr)
3.9
9.3
13.2
Erosion and other diffuse sources
1 to 7
Generalized total load excluding
precipitation and dustfall
14 to 20
1969 total load (estimated and measured)
excluding precipitation and dustfall
Combined sewer overflow
17.1
0.8
Precipitation and dustfall on surface
of Lake Michigan **
1.1
"Source: Phosphorus Technical Committee to the Lake Michigan
Conference (1972).
**Source: Lee (1972).
Murphy (1973) estimates that the phosphorus from rainfall amounts
to 4 million Ib/yr based on analysis of rainfall samples; the
source of this phosphorus has not been determined.
235
-------
could contribute. Correction of the Calumet eutrophication
problem may require controlling these other, more distant sources,
as well as the IHC.
IITRI measurements in Table 11.3 of chlorophyll in Lake
samples show that the IHC effluents have a nutritive effect, and
it will be shown that this can be taken as evidence that the IHC
is a significant source of phosphorus as well as ammonia. For
example, on November 14, 1973, the chlorophyll increased from
3 yg/fc at the mouth of the IHC (CAL06) to 5.4 at L11080 to 11.9 at
LM102, five miles out in the Lake but still in the plume of the
IHC. Locations not in the plume showed values from 1.5 to 2.0
chlorophyll on November 14. NH3-N concentrations were also
measured at these stations and are given in Table 11.2, but P
concentrations were not determined. The P concentrations at
CAL06 were 0.060 on November 19 and 0.070 on December 7, and these
are typical IHC values according to other sources of data. Data
from Industrial Biotest (1973) on November 14, 1973, indicate a
phosphorus value at CAL06 of 0.044, at LM068 of 0.014, and at
stations outside the plume of 0.001 mg/£.
On the other two IITRI boat sampling days, the chlorophyll
increases were not pronounced. November 19 was a cloudy day, and
the chlorophyll values in the plume reached only 2.7 at CAL15,
which value is above the values outside the plume. On December 7
the chlorophyll values were high ever^rwhere, perhaps because
phosphorus was high due to wave action stirring the Lake bottom,
as described in the next section.
Chlorophyll values in the IHC itself are lower than in the
Lake, and so high chlorophyll values in the plume are not due to
algae flowing into the Lake from the IHC. These low values in
the IHC may be due to a toxic effect, as was suggested in a
similar case by Fruh, Armstrong, and Copeland (1972).
The main conclusion from these chlorophyll studies is that
the IHC nutrients, when mixed with the Lake water, promote the
growth of algae in near-shore waters.
236
-------
The long-term trend of phosphorus input from IHC is measured
by the Chicago Water Dept. at Dickey Rd, Annual averages of
weekly samples are plotted in Figure 17.6. Included on the graph
is one point for the average of 12 days sampled by IITRI during
November-December 1973. This was done at Columbus Drive rather
than at Dickey Rd., but the results of phosphorus should be the
same at the two points. Additional values from the State of
Indiana summer 1973 sampling taken from Table 17.4 are indicated
on the graph. All these values show that phosphorus inputs from
IHC have decreased in recent years. These decreases are attributed
partly to phosphorus precipitation tertiary treatments installed
in 1972 by two of the sewage treatment plants in the area, and
parly to limitations on phosphorus content of detergents required
by recent Indiana law. But from the above discussion, a further
decrease is needed to prevent eutrophication of near-shore Lake
waters. Also, improvement will be needed in other states border-
ing on the Lake.
Table 17.5 gives details of phosphorus loads from various
outfalls going to the IHC, and indicates which sources are the
most important. A comparison of the Combinatorics load estimates
with measurements made in the IHC by IITRI indicate that the
actual loads are much higher than the estimates. The comparison
is given in Table 4.5, Chapter 4. This comparison suggests that
the treatment plants are not performing according to their design,
and is one basis for our recommendation that closer inspection
should be done. See Chapter 5.and Appendix D.
17.6 Effect of Bottom Stirring on Phosphorus Concentrations
Table 17.6 shows daily phosphorus concentrations at the
Chicago South Water Filtration plant intake during November-
December 1973. There are occasional periods of high concentra-
tions, and these seem to be correlated with high turbidity. We
noted that the turbidity of the near-shore waters is associated
with high waves and current during and after storms. Wind and
237
-------
0.4.1-
0.3 -
cc
•§
00
CO
00
0.2 -
IITRI Data,
Nov-Dec 1973
Columbus Drive
Indiana State Data,
Summer 1973
Dickey Road
0.1 -
Indiana standard, open Lake
1968
1969
1970 1971
Time, years
1972
1973
Figure 17.6
ANNUAL AVERAGE PHOSPHORUS CONCENTRATION IN INDIANA HARBOR CANAL AT DICKEY ROAD
Data Sources: Calumet Industrial Area Pollution Survey,
Chicago Dept. of Water and Sewers, weekly samples
-------
Table 17.4
IN-STREAM WATER QUALITY, 1973
Combinatorics (1974)
Description
Water quality standard
Monitoring stations
GCR 41
Grand Calumet River
Gary (U.S. 12)
GCR 37
Grand Calumet River
East Chicago (Kennedy Rd.)
GCR 36
Grand Calumet River
East Chicago (Indy. Blvd.)
GCR 34
Grand Calumet River
Hammond (U.S. 12)
IHC 3W
Indiana Harbor Canal
East Chicago (Indy. Blvd.)
IHC 3S
Indiana Harbor Canal
East Chicago (Columbus Drive)
IHC 1
Indiana Harbor Canal
East Chicago (Dickey Rd.)
IHC 0
Indiana Harbor Canal
East Chicago (Youngstown Steel)
Total phosphorus
0.10 ing/A
72 73 72-73
Average Average Maximum
1.4 0.10 6.6
1.1
4.5
8.5
1.2
1.1
1.0
0.23
0.85
1.84
0.19
0.23
0.13
0.10
2.7
9.9
9.9
3.3
2.5
1.6
0.16
239
-------
Table 17.5
PHOSPHORUS DISCHARGES TO IHC
Source: Combinatorics (1974)
Water Quality Standard . 1 r.g/1
Discharges
U. S. Steel
GW-1
GW-2
GW-2A
GW-3
GW-3A
' GW-4
GW-5
GW-6
GW-7
GW-7A
GW-9
GW-10A
GW-11A
GW-1 3
ST-14
ST-17
GSTP
E.I. duPont
001
002-004
005
006-010
U.S.S. Lead
HSTP
P:CSTP
Union Ccirbid
ARCO
Ar.er. DL.
Found j; i>. o
Mm .
I'low
(MGD)
19.9
10.9
1.4
2.7
0.4
0.5
82.4
23.4
5.8
93.3
24.7
26.3
81.3
1.8
0.8
20.1
44.0
0.5
7.24
0.07
0.89
35.0
10.0
: 0.05
0.09
Avg.
Flow
(MGD)
28.9
16.4
2.2
3.8
1.7
C.7
87.7
29.5
10.6
120.1
34.7
34.6
94.7
2.9
1.8
30.0
52.7
1.8
10.31
0.03
2.24
0.36
40.7
14.0
0.07
5.01
0.15
Max .
Flow
(MGD)
40.7
23.0
3.9
4.5
3.7
0.9
95.3
39.4
16.9
146.0
39.7
47.2
115.6
4.8
3.3
39.3
62.0
2.4
11.66
0.12
2.98
4-1 .0
20.0
0.11
6.77
0.27
Avg .
Load
(Ib/day)
17.00
5.50
.74
.95
.57
.23
65.80
12.30
8.84
50.50
8.69
11.53
31.60
1.20
3'.05
20.00
232.50
7.00
13.00
-
-
-
115.30
35.00
.27
180.30
.18
flax .
Load
( Ib/day)
23.78
9.58
1.60
1.90
1.50
.40
87.40
23.03
21.15
97.40
13.24
19.70
48.40
3.20
7.42
32.80
878.00
35.00
25.00
-
-
-
550.00
162.80
486.00
Avg.
Cone.
(mg/1)
.05
.04
.04
.03
.04
.04
.09
.05
.10
.05
.03
.04
.04
.05
.20
.08
.53
.56
.15
-
-
-
.34
.30
.46
4.30
.14
Max.
Cone.
(mg/1!
.07
.05
.05
.05
.05
.05
.11
.07
.15
.08
.04
.05
.05
.08
.27
.10
1.70
1.75
.26
-
-
-
1.50
.10
8.60
Comments
Net value
Net value
No net additioi
i
240
-------
Table 17.5 (cont.)
Phosphorus water Quality Standard .1 mg/1
Discharges
Youngstown
001 YS-20
002 YS-2
003 YS-4
004 YS-8
005 YS-11
006 YS-12
007 YS-13
008 YS-22
009 YS-14
010 YS-15
Oil
YS-18A
Inland
001 IE-2
002 4E-1
003 5E-1
004 5E-2
005 5E-3
006 6E-1
007 7E-1
008 10E-1
Oil 13G-1
012 13H-1
013
14H-TT
014
15H-TT
015 16H-1
016 16H-2
017 16H-3
018 16F-1
Min.
Flow
(MGD)
8.46
1.50
0.53
1.03
1.19
3.30
6.30
- 3.00
34.00
36.60
107.80
8.60
Unknov
126.96
67.68
85.52
85.52
17.28
7.20
115.28
119,76
Avg.
Flow
(MGD)
13.70
3.62
0.98
1.40
1.60
5.70
14.00
5.00
48.70
58.00
121.60.
.14
190.00
7.20
0.86
8.60
0.65
21.60
n & Hi<
158.70
50.80
106.90
106.90
21.60
9.00
144.10
149.70
Max.
Flow
(MGD)
23.60
7.50
1.40
1.75
3.00
8.40
18.90
11.70
60.00
67.00
138.70
.29
228.00
8.60
1.04
10.40
1.30
25.90
ihly Va:
190.44
70.00
128.28
128.28
25.92
10.80
172.92
179.64
Avg.
Load
(Ib/day)
9.41
2.49
.98
.70
1.33
3.33
9.62
4.17
24.37
48.37
60.70
1.40
63.38
6.00
.29
4.30
.43
5.40
iable
26.00
12.71
9.00
9.00
9.00
8.00.
12.00
37.00
Max.
Load
(Ib/day)
79.41
35.03
32.09
32.09
32.42
27.02
43.26
62.00
Avg.
Cone.
(mg/1)
.08
.08
.12
.06
.10
.07
.08
.10
.06
.10
.06
1.20
.04
.10
.04
.06
.08
.03
.02
.03
.01
.01
.05
.11
.01
.03
Max.
Cone.
(mg/1)
"
.05
.06
.03
.03
.15
.30
.03
.05
Comments
Intake ave .06
Intake ave .06
Intake ave .06
Intake ave .06
Intake ave .06
Intake ave .06
Intake ave .06
Intake ave .06
Intake ave . 06
Intake ave .06
Intake ave .06
Maximum
24 br. sample
Maximum
24 hr. sample
Maximum
24 hr. sample
Maximum
24 hr. sample
Maximum
24 hr. sample
241
-------
Table 17.6
PHOSPHORUS CONCENTRATIONS
CHICAGO SOUTH WATER FILTRATION PLANT,
NOVEMBER - DECEMBER, 1973
AND PARAMETERS INDICATING CORRELATION WITH BOTTOM STIRRING
Date
November 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
P04
mg/jt
0.06
0.03
0.03
0.03
0.04
0.04
0.03
0.02
0.03
0.02
0.02
0.02
0.03
0.03
0.04
0.04
0.03
0.04
0.05
0.04
0.03
0.03
0.03
0.03
0.02
0.02
0.03
0.06
0.06
0.06
Winds
Turbidity,
JTU
5.3
4.6
5.2
5.9
8.3
8.9
7.8
6.5
8.5
7.6
5.3
3.5
3.1
2.8
7.4
11
14
6.9
6.6
8.2
6.3
3.0
2.5
2.4
3.5
4.6
4.1
13
14
10
Direction
SW
NE
N
N
W
W
S
W
NW
SW
SW
SW
SW
. SW
NW
NW
S
S
NE
SE
SW
S
NE
SW
N
E
SW
W
SW
N
Speed,
mph
15
14
13
17
17
13
10
14
14
9
16
18
17
14
18
13
18
17
13
20
24
11
9
15
13
15
6
25
16
17
242
-------
Table 17.6 (cont.)
Date
December 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
P04
mg/£
0.06
0.05
0.04
0.07
0.05
0.04
0.04
0.04
0.03
0.03
0.04
0.04
0.11
0.09
0.08
0.09
0.08
0.09
0.08
0.11
0.07
0.03
0.03
0.03
0.03
0.04
0.09
0.09
0.05
0.04
0.04
Turbidity,
JTU
14.0
9.6
5.6
7.7
8.1
5.8
8.3
6.1
3.6
5.3
6.9
5.9
30.0
40
30.0
31.0
32.0
28.0
23.0
28.0
21.0
16.0
15.0
18.0
16.0
13.0
14.0
12.0
9.7
10.0
9.4
Winds
Direction
E
S
sw
S
sw
sw
S
sw
sw
w
sw
E
NE
NE
NE
NE
SW
SE
NE
N
SW
SW
E
E
SW
NE
W
SW
W
W
N
Speed,
mph
19
23
16
22
19
15
11
14
13
17
13
12
33
15
18
18
9
12
21
21
8
16
16
21
19
11
15
17
15
11
14
243
-------
wave observations are also recorded in Table 17.6, and the
correlation coefficient is 0.85. This correlation suggests that
the observed phosphorus concentrations in the near-shore waters
are determined largely by stirring up of bottom sediments, which
Schleicher and Kuhn (1970) have shown to contain phosphorus.
244
-------
Phosphorus is abstracted from the water and deposited in sedi-
ments in the detritus of organisms that die and settle, and may
be subsequently stirred up. Wildung and Schmidt (1973) have
reported elevated sediment phosphorus levels during late summer
and early fall in lake locations having increased organic carbon
and nitrogen concentrations.
Robertson and Powers (1965) measured particulate organic
matter in Lake Michigan and found higher concentrations near the
Chicago area than elsewhere.
The exchange of phosphorus between sediments and the water
is beyond the scope of this report, but the data in Table 17.6
indicate that such relationships are important factors in deter-
mining the phosphorus levels in this part of Lake Michigan, and
deserve further study.
17.7 Recent Phosphorus Trends and Models
Lee (1972) has analyzed the phosphorus sources discussed
above, and assessed their probable impact on Lake Michigan. He
points out that a conservative model for the build-up of P in
Lake Michigan is not valid, because the rate-determining step
is the deposition of P in sediments. He estimates that the
apparent residence time of P in the Lake is six years. This is
based on the 1971 P input rate of I8.1xl06 Ib/yr (8.2xl012 mg/yr)
and the Lake volume of 5x10 liters, together with the estimate
(Phosphorus Technical Committee 1972) that the mean P concen-
tration in the Lake is now 0.01 mg/£. This is a very crude
estimate, because the concentration of P in the Lake may not yet
have responded to increased P inputs due to increased population
and urbanization of recent years; however, it is more likely
to be correct than estimates of 30 to 100 years that are based
on the assumption that P is conserved in the Lake. Based on
this estimate, Lee (1972) quotes a model of Sonzogni and Lee
(1972) which estimates that the Lake will recover to 95% of its
245
-------
steady-state P concentration in 18 years after P inputs are
reduced; and that a significant improvement will be seen within
a few years after reductions are made in P inputs. This is
based on the idea that most of the P which is deposited in sedi-
ments is permanently lost. This, of course, has not been proven.
The problems of eutrophication discussed in Chapter 8 are
much more noticeable in near-shore waters than any effects in
the main part of the Lake. The response of the near-shore waters
to changes in P inputs should be almost immediate, except for the
contribution due to the background P concentration and from
sediments. The data for the Chicago water intake (Figure 17.5)
show a 20% decrease in the last two years. The decrease might
not be statistically significant by itself, but taken as a
possible result of the 4070 decrease in P from the IHC (shown in
Figure 17.6) it is an encouraging sign. It indicates that P
control efforts are probably having a beneficial effect in the
near-shore waters, and that these efforts should be continued.
17.8 Conclusions and Recommendations
The long-range trend of phosphorus has been increasing in
the Calumet area over the past 15 years. The long-range trend
in the whole Lake is not so sure, because applicable data are
limited. The inputs of phosphorus are large, but phosphorus is
deposited in sediments, and may also be released from sediments
(Wildung and Schmidt 1973). How much of the loss to sediments
is permanent is not known. Although increases of phosphorus at
mid-Lake locations are not certain, increases in the Calumet
area are very real.
Phosphorus levels in the Lake in the whole Calumet area
average at the Indiana standards (0.03 mg/4 P) and practically
always Exceed the Illinois standard of 0.007 mg/£ P. Further-
more, the phosphorus level is believed to be the main nutrient
limiting the growths of algae that have contributed serious
eutrophication in the near-shore waters in the years since 1966.
246
-------
However, the trend of phosphorus loads from the. IHC has been
decreasing since 1970 due to improved municipal sewage treatment,
including the installation of phosphorus precipitation processes
in 1972. Regulation by the State of Indiana of phosphorus content
in detergents is another reason for the improvement in IHC
loadings. These efforts by the State of Indiana are sufficient
to bring recent concentrations in the Lake outside IHC down to the
Indiana standards, but they are not sufficient to achieve phos-
phorus standards in the IHC itself.
IITRI chlorophyll measurements on November 14 and November 19,
1973, showed a pronounced nutritive effect of IHC effluents mixing
with Lake waters, causing algae to grow in the plume. This could
be due to phosphorus, nitrogen, or both. These data indicate that
IHC effluents are still contributing to algal fouling of water
intakes and beaches.
The 80% reduction in phosphorus effluents recommended by the
Lake Michigan Enforcement Conference and adopted by the states has
not yet been achieved, although a reduction of 40% has been
achieved in the IHC by the end of 1973. The Phophorus Technical
Committee (1972) recommended that phosphorus be further controlled
by setting an effluent limitation of 1 mg/2, total P for municipal
and industrial sources. The permit application data in Table 17.5
indicate that the effluent limitation of 1 rag/£ is being met for
most dischargers, but the measurements in the IHC (Figure 17.6)
indicate that the loadings are still too high. We recommend that
the control efforts be continued to further lower phosphorus
entering the Lake via the IHC. This may require closer inspection
and control of the operation of sewage treatment plants in the
area, rather than any new methods of control. It may also require
monitoring of combined sewer overflows, for which data are
presently lacking.
The IHC sources comprise 7% of the total phosphorus inputs
to the Lake. This figure is based on Combinatorics (1974) data
247
-------
from permit applications for IHC sources, and on Phosphorus
Technical Committee (1972) estimates of other Lake sources. The
main Lake sources are the Fox, Grand, and St. Joseph rivers,
located in other parts of the Lake, as well as sewage plant
effluents north of Chicago and in Wisconsin.
In conclusion it is recommended that renewed efforts be made
to control the phosphorus inputs in all parts of Lake Michigan,
to reverse the serious eutrophication trend that is evident in
near-shore waters.
248
-------
K>
CAL02
IHC and 151st St.
EPA data
4J
O
H
(X.
Figure 17.7
STORET WATER QUALITY PLOT
u
O
H
a
09
o
o
to
8
o
IHC 3S
IHC and Columbus Drive
Indiana data
O i
VD t
CM
00 ON
vo so
i-l tH
CM en
H-' .
Figure 17.8
STORET WATER QUALITY PLOT
-------
Ul
O
CAL03
IHC and Dickey Rd.
EPA data .
•*». l~.u
H»
CM CO
Figure 17.9
STORET WATER QUALITY PLOT
IHC 1
IHC and Dickey Rd.
Indiana data
O
H
xl- O
O vo
-
3
a
CO
O
•fi 0
PM CM
o
tn
vo
o
o
r» oo a\
vo vo vo
. 'i J—JLtJ._
-------
S3
Ul
LM H
Hammond Water Plant Intake
Indiana data
^- i
g
< +.*
t
1967
1968
1969 1970
Time, years
Figure 17.11
T"T' TTA'TT'O /^TTA T TTV TXT OT
1971
1972
-------
LM W
Whiting Water Plant Intake
Indiana data
N>
Ui
N?
rr
o
Q_
o
o
.o r
Q_
O
LD
co
o
o
o
d'
o
1967
1968
1969
Time, years
Figure 17.12
STORET WATER QUALITY PLOT
f W- '+ V +H-
t.
1970
1971
1972
-------
18. CHLORIDE AND SULFATE
18.1 Introduction
Chloride and sulfate concentrations in the Calumet area of
Lake Michigan seldom exceed open-Lake standards; however,
extensive data indicate long-term build-up of these parameters.
A mixing model of the Lake shows that because of the long reten-
tion time of water in the Lake, the average concentration will
rise in 20 years to exceed the standards for chloride, and
probably also for sulfate. The IHC comprises 7% of the total
chloride input to the Lake, and about 15% of the total industrial
input. The chloride effluents from IHC are still increasing,
but the sulfate levels are decreasing. Sulfate levels at water
intakes in the Calumet area appear to be also decreasing, but
the general Lake trend for the past three years is not known.
Control of increases of chloride would require Lake-wide
control of industrial chloride effluents and of road salting.
18.2 Water Quality Standards
For chloride,. the Indiana state standards for open water of
Lake Michigan are 10 mg/4 average, and 15 single value. The
Illinois state standard for Lake Michigan is not to exceed
12 mg/£. Indiana standards for the inner harbor are 20 mg/£
average and 30 single value. Indiana standards for the IHC are
35 mg/£ .
For sulfate, the Indiana standards for open water of the Lake
are 26 mg/£ and 50 single value. Illinois standard is not to
exceed 24 mg/£. Indiana standards for the inner harbor are 39
average and 75 single value. For the IHC the standard is 75.
Michigan has standards for total dissolved solids, which
includes chloride and sulfate as well as a substantial level of
bicarbonate.
253
-------
18.3 Water Quality Data
18.3.1 Chloride
The long-range trends of chloride and sulfate concentrations
at the Chicago South Water Filtration Plant intake are the most
complete long-term records for any Lake point, and they are
presented in Figure 18.1. A rapid increase in both of these
parameters has taken place since 1950. Chloride is still
increasing, although it appears that sulfate has peaked and is
either constant or decreasing.
The values of these parameters at Chicago and other Calumet
area stations is higher than in remote parts of the Lake, but
the general upward trend is a Lake-wide phenomenon. Weiler and
Chawla (1969) and Beeton (1971), as quoted by Schelske and Roth
(1973) observe this upward trend, and attribute it to human
activities.
Powers and Ayers (1967) compared chloride concentrations in
mid-Lake waters with data from water intakes near the shore.
The data were from their own 1962-63 measurements and those of
Risley and Fuller. They concluded that the average chloride
concentration in the Lake was 5 to 7 mg/£ in 1962. Values in
the southern end of the Lake and at near-shore locations were
several mg/£ higher. Risley and Fuller (1965) reported this
north/south trend; a mean value at the latitude of Sheboygan,
Wisconsin, was 6.6 with a range of 5.4 to 10 mg/£ across the
Lake in 1962-63; at the latitude of Calumet Harbor the mean was
8 with a range of 4.2 to 22. An increased mid-Lake value was
reported by Schelske and Roth (1973) who found an average of
7.22 + 0.32 mg/4 for 16 samples near Charlevoix in the northeast
part of the Lake.
Beeton (1965) summarized data from many sources and plotted
background values of chloride and sulfate in open-Lake waters.
These plots are shown in Figure 18.2. In general, they agree
with the early trend of Chicago water data, Figure 18.1, but they
do not extend to the time of most recent increases.
254
-------
N3
Ul
Ul
30
25
20
Q. 15
Q.
.10
0
I860
• ISOLATED SAMPLE
- YEARLY AVERAGE
I
Range of monthly averages
in a year
CHLORIDE
_L
!870 1880 !890
• ::ill
« . • .
• •«-•_*
. -- • ••
.
•• .».*-
. _- *v-^ •—
'.. J
J_
1
I.
!940 1950 I960 I9P7O
900 !9!0 i^EO 193O
Figure 18.1
100 YEAR RECORD OF CHLORIDE AND SULFATE INCREASE AT DUNNE CRIB - 68TH 8t
-------
Total Dissolved Solids
1870 I88O I89O I9OO I9IO 1920 1930 1940 I95O I960 I9W
YEAR
40
35 -
SO
z
O 25
2 20
CC
Ul
a. is
a: 10
2
Calcium
J L.
18*0 I9OO 1910 I9ZO I93O 1940 I95O I960 I97O
1810 1900 1910 It20 I9SO 1940 1950 I960 1970
YEAR
Figure 18.2
CHANGES IN CONCENTRATIONS OF DISSOLVED CHLORIDE SULFATE,
CALCIUM AND TDS IN LAKE MICHIGAN
Source: Beeton (in NSF, 1969)
Circled points represent open-Lake data;
crosses are from Chicago water intake;
other points are from Milwaukee water intake.
256
-------
13.3.2 Sulfate
Powers and Ayers (1967) compared sulfate concentrations in
mid-Lake waters with data from water intakes near the shore. The
data were from their own 1962-63 measurements and those of Risley
and Fuller (1965). They concluded that the average sulfate level
for the open Lake was nearly 16 mg/£. The average value at the
Chicago intake at that time was 18.2 mg/£. Risley (1965) reported
at the latitude of Sheboygan a mean of 21 ing/£ with a range of
10 to 49; at the latitude of Calumet Harbor the mean was 22 with
a range of 15 to 57, showing little variation in north/south
direction. Sulfate concentrations are higher near shore.
The data from Chicago Water Department (Figure 18.1) are a
little higher than in remote regions of the Lake, but the trend
of increase with years is valid for the whole Lake, at least
until the last few years; however, Schelske and R.oth (1973)
reported a mean for 16 sulfate measurements near Charlevoix of
15.5 + 3 mg/£ in 1970.
Figure 18.1 shows that the chloride values are continuing to
rise, but the sulfate'values are becoming constant, or perhaps
decreasing from a peak of 22 in 1967. Ho definite trend line can
be established. The data in Figure 18.1 represent daily measure-
ments .
Storet plots of chloride data for several Lake water intake
stations are given in Figures 18.9 to 18.18. Similar plots for
sulfate are given in Figures 18.19 to 18.29. Both the chlorides
and sulfates show similar patterns at several stations, with a
significant decrease since 1967; however, there are periods of
higher levels since that date. There are few indications of
257
-------
water quality violations. The greatest concern is not whether
there are presently violations, but whether the levels will
increase at the previous alarming rate.
18.4 Effluents from IHC
The Technical Committee (1970, p. 55) noted a decrease
in sulfate concentration at the mouth of the IHC, at station
CAL06, from a mean of 64 mg/4 in 1965 to a mean of 32 in 1969.
This could be responsible for the decrease in Storet Lake station
plots mentioned above. They attributed this improvement to con-
version by the steel mills from sulfuric to hydrochloric acid
pickling, and to deep well acid disposal systems.
The most complete data on concentrations in the IHC are the
weekly measurements by the Chicago Water Department at Dickey
Road. The annual averages of these measurements are shown in
Figures 18.3 and 18.4. A decrease in sulfate concentration is
noted since 1970, but the decrease is not as large as reported
by the EPA. Chloride (Figure 18.4) has continued to increase.
Chloride concentrations are often in violation of Indiana stan-
dards for the IHC.
Measurements by Indiana during the summer of 1973 are given
in Table 18.1. The Indiana measurements fall within the stan-
dards for IHC. Recent measurements by IITRI at Columbus Drive
on IHC all exceed the Indiana standard of 35 mg/4 for chloride.
Date Chloride, mg/1
Nov. 12, 1973 55
13 65
14 59
15 54
16 65
17 84
18 46
19 72
20 45
29 70
30 60
Dec. 07, 1973 - 71
258
-------
80
Indiana standard for IHC
60
Of,
Ul
QJ
00
40
20
Indiana standard for open Lake
(to indicate dilution needed
to meet Lake standards)
1968 1969197019711972fg73
Time, years
Figure 18.3
ANNUAL AVERAGE SULFATE CONCENTRATION IN INDIANA HARBOR CANAL AT DICKEY ROAD
Data source: Calumet Industrial Area Pollution Survey,
Chicago Dept. of Water and Sewers
-------
50_
Indiana standard for IHC
Indiana standard for open Lake
(to indicate dilution needed
to meet Lake standards)
L968
1969
1970 1971
Time, years
1972
1973
Figure 18.4
ANNUAL AVfKAf:: CHLORLD ' CONCEN'IRAI Ku-J IN INDIANA HARBOR CANAL AT DICKEY ROAI
Data source: Calutns, Industrial Area Pollution Survey
Chicago Deot. of Water and Sewers
-------
Table 18.1
WATER QUALITY IN IHC AND GRAND CALUMET RIVER
Data of State of Indiana, Summer 1973
Combinatorics (1974)
Ni
Description
Water quality standard
Monitoring stations
OCR 41
Grand Calumet River
Gary (U.S. 12)
GCR 37
Grand Calumet River
East Chicago (Kennedy Rd.)
GCR 36
Grand Calumet River
East Chicago (Indy. Blvd.)
GCR 34
Grand Calumet River
Hammond (U.S. 12)
IHC 3W
Indiana Harbor Canal
East Chicago (Indy. Blvd.)
IHC 3S
Indiana Harbor Canal
East Chicago (Columbus Drive)
IHC 1
Indiana Harbor Canal
East Chicago (Dickey Rd.)
IHC 0
Indiana Harbor Canal
East Chicago (Youngstown Steel)
72
Average
55.1
Sulfates
75 mq/ji
73
Average
44.0
53.1
50.3
59.7
43.6
72-73
Maximum
'60.0
115.0
187.8 410.0
147.3 139.9 223.0
86.7 123.0
70.0
80.0
70.0
Chlorides
35 mgA
except river flow
to Illinois = 125 mg/1
72
Average
27
31
281
155
59
40
40
73
Average
22
30.6
260.2
129.9
59.7
33.9
34.3
25.6
72-73
Maximum
44
97
620
550
115
125
125
37
-------
These IITRI measurements indicate either a recent increase in
effluents, or they reflect a seasonal fluctuation in chloride
effluents. Season fluctuations are apparent in plots of Storet
data shown in Figures 18.9 to 18.18. The reason for seasonal
fluctuations might be the use of salt on roads in winter in the
Calumet area; however, the timing is not right; for instance,
there was no snow during the period of IITRI's sampling. No
other reason is known.
18.5 Water Quality Violations
It appears that there are violations of chloride standards
in IHC due to increases in the last few years. At some times of
the year, the concentrations are just below the standards.
Violations occur in the Grand Calumet River due to its lower
flow rate.
There is no evidence of sulfate violations in IHC.
Violations of chloride standards in Lake Michigan are quite
rare. None were observed during IITRI's sampling near the mouth
of IHC during Nov-Dec 1973. The Storet data in Figures 18.9
to 18.18 indicate occasional violations, and so do measurements
of Chicago's 68th St. water intake crib. The main reason for
concern is not the occational violations at present, but the
persistent increase over time shown in Figure 18.1. Future
increases are predicted by model calculations below.
18.6 Sources of Effluents
Table 4.5 shows that the sum of reported chloride effluents
into the IHC totals 393,537 Ib/day, as determined by Combina-
torics Inc. (1974) from permit data. IITRI measurements at the
mouth of the IHC are higher than this, by a factor of 1.5 to 2.
A further check is given by comparing the effluents with the
loads measured by IITRI at Columbus Drive on the IHC; this
comparison is given in Table 4.4 . Again the IITRI measurements
are higher than the Combinatorics totals of reported effluents.
These higher values reflect the higher concentrations of chlorides
262
-------
by IITKI, and these were compared above vith data from
sources. We can conclude that the loads are at least as
high as reported by Combinatorics, and are perhaps higher some-
times.
Table 18.2 from Combinatorics (1974) lists the outfalls and
their loads of chlorides. Table 18.3 is a similar list for
sulfates. The major sources are the three steel companies in the
Calumet area, (U.S. Steel Gary Works, Inland Steel, and Youngs-
town Sheet and Tube), and the municipal sewage treatment plants
at Gary, East Chicago, and Hammond,
Plots of radial survey data from the Chicago Water Depart-
ment in Figures 18.5 to 18.7 show some peaks at stations 5J and
6J near the mouth of the IHC, indicating that this source is
strong enough to have measurable effect on local chloride con-
tent of the Lake waters, even though the background chloride
concentration is relatively high compared to the ratio for other
pollutants.
There are some additional sources that discharge directly
into the Lake, and they are listed in Table 4.2. The values
given in the table include the amount of chloride in the intake
waters, so these are not net figures. Only those sources whose
effluent concentrations are signficantly above Lake background
chloride levels provide significant net chloride inputs. Two
sources with significant net inputs of chloride are Bethlehem
Steel at Burns Ditch, and Amoco at Whiting. The loads from these
sources amount to 30,000 and 15,000 lb/day. These are not very
large in themselves, but if chloride effluents on IHC are con-
trolled, then these sources should also be controlled.
263
-------
Table 18.2
*
INVENTORY OF CHLORIDE DISCHARGES ON IHC AND TRIBUTARIES
Source: Combinatorics (1974)
Chloride:.
Wc.ter ^ua^itv St2r.dr.rd 33 r.c'l
^'.LTi . AV.j. ' XC.5C. ' AV'J. IMc.X. 'AVC.
Discharges 'Flow < Flow rlov/ Load 1 Load 'Ccr.c.
! ^GD) ' (MGC; ;XGD) ' (Ib/day) (lb/day; (r.o/1) '
U. S. Steel
GW-1
GW-2
GW-2A
GI7-3
GW-3A
GW-4
GW-5
GW-6
GW-7
GW-7A
GW-9
GW-10A
GW-11A
GW-1 3
ST-14
ST-17
GSTP
E.I. duPont
001
002-004
005
006-010
U.S.S. Lead
HSTP
ECSTP
Union Carbid
AKCO
Amer. St.
Foundries
19.9
10.9
1.4
2.7
0.4
28.9
ic.4
2.2
3.S
40.7
23.0
3.9
4.5
2,660
1,913
366
5,030
3,260
876
444 939
'
1.7 3.7 312
0.5 0.7 0.9
82.4
87.7
23.4 j 29.5
5.8
93.3
24.7
26.3
81.3
1.3
10.6
120.1
34.7
34.6
94.7
2.9
0.8 j 1.8
20.1
44.0
0.5
7.24
0.07
0.89
35.0
10.0
3 O.C5
0 . 09
30. 0
52.7
1.8
10.31
0.03
2.24
0.35
40.7
14.0
0.07
5 . 04
0,15
58
t
95,3
39.4
16.9
146.0
39.7
47.2
115.6
4.8
3.3
39.3
62.0
2.4
11 .66
0.12
2.98
44.0
20.0
0.11
6.77
. 15,380'
2,460
2,210
12,010
4,930
4,910
11,870
290
710
21,200
29,500
4,100
0
600
300
86
40,700
41,600
5
12,600
i
j
0.27
1,350
895
114
23,100
4,940
4,510
19,450
8,280
10,610
19,270
6S5
6,500
39,300
51,600
8,700
0
2,000
1,000
273
73,400
102,300
14
25,400
3,380
i
11
14
20
14
Ccr.c. i Corrsr.ant.3
15
17
27
25
1
22 29
10
21
10
25
12
17
17
15
12
50
85
67
280
_
910
}61
15
29
15
32
16
25
27
20
17
236
120
100
2,230
*-
3,330
403
28. 5J 91
120
356
10
200
675
15
300 450
1,030
1,500
i
I
.264
-------
Table 18J (cent.)
Chlorides Water Ou4iltv stanc
Dischdzyua
Youngstown
001 YS-20
002 YS-2
003 YS-4
004 YS-S
005 YS-11
006 YS-12
007 YS-13
008 YS-22
009 YS-14
010 YS-15
Oil
YS-18A
Inland
001 IE-2
002 4E-1
003 5E--1
004 5E-2
005 5E-3
006 6E-1
007 7E-1
008 10E-1
Oil 13G-1
012 13H-1
013
14H-TT
014
15H-TT
015 1CH-1
016 16H-2
017 16H-3 I
018 16F-1
Min .
i Flow
(MGD)
8.45
1.50
0.53
1.03
1.19
3.30
6.30
3.00
34.00
36.60
107.80
8.60
Unknov
126.96
67.68
65.52
85.52
17.23
1
7.20 j
115.28
119.70
Avg.
now
(MGD)
13.70
3.62
0.98
1.40
1.60
5.70
14.00
5.00
48.70
58.00
121.60'
.14
190.00
7.20
0.86
8.60
0.65
21.60
n & Hi<
158.70
50.80
106.90
106.90
21.60
y.ax.
rlow
(.•1GD)
23.60
7,50
1.40
1.75
3.00
8.40
18.90
11.70
60.00
67.00
133.70
.29
228.00
8.60
1.04
10.40
1.30
25.90
hly Va:
190.44
70.00
128.28
128.28
25.92
9.00 10.80
144.10J172.92
149.70
1
179.64
Avg. viax.
Load Load
(Ib/dav) (Ib/dav)
2,284
452
317
140
294
2,420
4,326
1,405
6,090
12,080
21,291
30
25,340
2,380
86
788
135
2,160
iable
17,200
16,099.54
16,000
16,000
2,520
1,050
14,400
13,730
265
5,900
1,560
475
278
750
7,210
26,638
72,440
10,000
16,740
32,444
249
57,000
3,730
156
1,560
282
3,240
19,800
39,698.4
32,095.6
36,375.0
2,700
1,500
18,000
23, 971 ..1
Avg.
Cone.
(nw/1 )
20
15
28
12
22
51
37
29
15
25
21
26
16
39
12
11
25
12
13
38
18
18
14
14
12
11
M«Jt.
ConC .
(ma/1)
30
25
42
19
30
103
169
L,495
20
30
32
103
30
52
18
18
26
15
15
68
30
34
15
20
15
16
lard 35 ?f/A
Comiwitt
Monthly report
data
P. data high
of 67
High recorded
in Jan.
-------
Table 18.3
INVENTORY OF SULFATE DISCHARGES ON IHC AND TRIBUTARIES
Source: Combinatorics (1974)
Salfates
Water Oualitv Standard 75 r~'l
.Iir.. .Vg. i Mix. i Avg.
Discharges ) /Isu < Flow | Flow i Load
i (MGD) i (MGD;: {.:GD! j (ic/day)
U. S. Steel
GW-1
GK-2
GW-2A
GW-3
GW-3A
GK-4
GW-5
GW-6
GW-7
GW-7A
GW-9
GW-10A
GW-11A
GW-13
ST-14
ST-17
GSTP
E.I. du?cnt
001
002-004
005
006-010
U.S. 3. Lead
HSTP
ECSTP
Union Carbid
ARCO
Foundries
19.9
10.9
1.4
2.7
0.4
0.5
82.4
23.4
5.8
S3. 3
24.7
26.3
81.3
1.8
0.8
20.1
44.0
0.5
7.24
0.07
0.89
35.0
10.0
2 0.05
0.09
28.9
16.4
2.2
3.3
1.7
0.7
87.7
29.5
10.6
120.1
34.7
34.6
94.7
2.9
1.8
30.0
52.7
1.8
10.31
0.08
2.24
0.36
40.7
14.0
0.07
5.04
0.15
40.7
23.0
3.9
4.5
3.7
0.9
95.3
39.4
16.9
146.0
39.7
47.2
115.6
4.8
3.3
39.3
62.0
2.4
11.66
0.12
2.98
44.0
20.0
0.11
6.77
0.27
8,450
4,240
459
1,140
355
146
18,300
8,610
3,360
35,350
11,500
8,660
23,670
1,450
4,620
48,750
28,600
7,670
15,225
300
31,000
665
40,700
11,100
9
16,300
48
~o£ £
Max . Aver . ! Max .
Load iConc. Cone.
(Ib/day) (rg/1) i fcg/1)
15,270
7,670
1,140
1,613
926
225
23,350
14,940
7,050
54,700
14,900
15,730
38,500
4,000
9,640
75,300
25,200
64,200
2,700
50,300
2,740
18
28,200
113
35
' 31
25
36
25 •
25
25
35
38
35
35
30
30
- 60
308
195
65
511
177
450
1,663
221.4
120
95
15
400
38
45
40
35
43
30
30
30
45
50
45
45
40
40
100
350
230
1,258
660
2,693
2,042
912.
20
500
50
Comments
Grab sample
5
Grab sample
Grab sample
-------
Table 18.3 (cont.)
5ulfs.-oes
Water Cualitv Standard 75 -a
Discharges
Youngstown
001 YS-20
002 YS-2
003 YS-4
004 YS-8
005 YS-11
006 YS-12
007 YS-13
008 YS-22
009 YS-14
010 YS-15
Oil
YS-18A
Inland
001 IE-2
002 4S-1
003 5E-1
Flew
8.46
1.50
C.53
1.03
1.19
3.30
6.30
Flow
! (MGZJ)
13.70
3.62
0.98
1.40
Max .
Flow
(M3D)
23.60
7.50
1.40
1.75
l.CO 3.00
Avg.
Load
(Ib/dav)
17,200
1,810
123
292
49*4
5.70 8.40 1,430
14.00 18.90 1,638
3.00 5.00 11.70 584.
34.00
36.50
107.80
004 5S-2 8.60
005 5S-3
006 6E-1
007 7E-1
008 10E-1
Oil 13G-1
012 13K-1
Ur.kr.o^
48.70
58.00
121.60
.14
190.00
7.20
0.86
8.60
0.65
21.60
60.00
67.00
133.70
.29
223.00
3.60
1.04
10.40
1.30
25.90
6,100
7,260
55,800
55,800
88
31,600
1,800
165
2,150
136
5,400
.-i s Hicrhly Variable
126. S6 158.70 ISO. 4-1 33,000
67 . 63
50. £0 70.0011,015.47
013
14H-TT S5.52 |106.90;i28.28
014 1
•*- .4 — — ^ .-_••—' I W «_ i '*"""" ^ " *" ^
015 16K-1 17.23
21.60 25.92
25,800
25, SCO
4,323.46
016 1S1I-2 7 ?: 9.00 10.30 1,375
017 ioH-3 HJf .2d 144.10 '172.92
28,820
"ax. Avg.
Load Cone .
(lb/dav)l (rac/1)
39,300
5,640
292
1,750
3,510
9,110
3,300
2,450
10,000
11,130
75,200
75,200
180
57,000
3,5SO
261
4,340
433
10,800
46,300
21,600.6
53,492.7'
-'5,65-: . CM
150
60
15
25
37
30
14
14
15
15
55
55
75
20
Max.
Cone .
(ng/1)
200
90
25
120
140
130
21
21
20
20
65
65
90
30
30 50
23
30
25
30
25
26
29
29
11,379.5 24
3,152.52 25
:3, 26-1. 53 24
018 167-1 |119. 75 J149.70;179. 6-1 36,120 74, 809. Si' 29
I
j
1
i 1
267
30
50
40
50
35
37
50
41
55
35
30
50
Comrner.cs
-------
121-
10
August 19
N> _i
ON
-------
13 r
N3
cy>
VO
11
O
T-l
.C
-------
20 i-
15
bO
6
0)
T3
•H
5-4
O
•u
o
H
10
0
3F
2F IF
2J 3J
4J 5J
Location
6J
7J
I
41
51
61 71
Figure 18.7
RADIAL SURVEY OF TOTAL CHLORIDE - 1972
Chicago South Water Filtration Plant
-------
13.7 Lake Michigan Water and Chloride Model
For a conservative parameter like chloride, the Lake as a
whole can be modelled by thinking of it as a well-stirred tank.
The build-up of concentration is the input of chloride less the
outflow (quantities are defined in Figure 18.8)
dC W
= v -
This can be rearranged for integration
C? jr. ft
dC f V dt (18.2)
U/Q - C
Ci
This is solved for the concentration C2(t), given the initial
concentration C^:
C2 = H[l - exp[- §fj + C^exp - ^]j. (18.3)
271
-------
Water
o
Q km /yr
Chloride
W kg/yr
Lake
concentration
C(t) kg/km3 or 10~Vg/£
volume V km3
Outflow Q
concentration C(t)
Figure 18.8
LAKE MICHIGAN MODELLED AS A STIRRED TANK
TO DETERMINE CHLORIDE BUILD-UP
The values of the flow parameters are from a Lake Michigan water
balance (Chandler 1964; Schelske & Roth 1973):
Inputs - Runoff from land
Precipitation
Outputs - Evaporation
Diversion
Outflow
Volume
Detention time, years
Hence, V = 4871 km3, Q = 49 km3/yr.
Q
km /yr
35
45
32
2.7
49
4871 km3
99
1000 cfs
39
51.5
35
3.1
55
1170 mi3
272
-------
O'Connor and Miller (1970) surveyed the available data on
sources of chloride to Lake Michigan as a whole. They estimated
the following inputs
Ib/day Metric ton/year
Road salt as chloride 1,400,000 233,000
Industrial effluents 2,600,000 433,000
Municipal effluents 300,000 50,000
Other sources 1,310,000 218,000
Total (to fit model) 5,600,000 943,000
The industrial effluents comprise the largest type of source.
This industrial effluent figure agrees well with a summation of
industrial effluents compiled by Businessmen in the Public
Interest (1972) from Rapp permit applications. The largest
industrial effluents were from salt-processing industries in
Manistee and Luddington, Michigan. Robbins, Lanstrom and
Wahlgren (1972) also list large inputs from rivers in Michigan.
The total chloride figure given above represents the amount
needed for the model to fit the observed build-up in Lake concen-
tration. The item "Other Sources" is the difference needed to
make up this total. The known sources in the list comprise 7770
of the total; this 7770 accounting very strongly supports the
model estimates. It is therefore reasonable to use the total
figure to estimate the further rate of chloride increase from
1970.
The effluents from sources on the IHC comprise 66,000 metric
ton/yr (400,000 Ib/day). This is 15% of the industrial input.
Because the area drained by the IHC is small, road salt is
expected to be a small fraction of this. Therefore, the IHC
contributes a significant portion of the industrial chloride
input to the Lake. The biggest sources, however, are the salt-
related industries in Michigan.
273
-------
From these estimates, the values of the parameters in the
Lake model are
W = chloride input rate = 943,000 metric ton/yr
W/Q = 943,000x10* mg/vr = ^
49x1012 £/yr
T//n - 4871 km3 nn
V/Q - = 99 years
49 km3/yr
The mean Lake concentration of chloride in 1970 is taken to be
7 mg/&. Of this, 3 mg/£ represents the natural background level
due to leaching of the earth, and 4 represents the accumulation
from human activities to date. Thus d in Equation 18.3 is
4 mg/£. A constant amount of 3 mg/£ is to be added to the
equation to equal natural background. The result is in Table 18.4,
The results indicate that only modest increases are expected,
provided that the chloride inputs do not increase.
Another question is the actual flow, Q, used in the model.
There are indications that there may be some exchange of water at
the straits of Mackinac (Ayers 1959, p. 7), so that the flow Q
may effectively be larger. In this case, O'Connor and Miller's
estimate of the input W may be low, by less than a factor of 2.
Our extrapolation from 1973 will not be affected, but use of the
model to calculate other water quality parameters would be
questionable.
We can conclude from Table 18.4 that as the general Lake
chloride concentration increases, the frequency of violations at
points in the Lake will increase. In addition, the average back-
ground level will exceed the Indiana state standard of 10 mg/£
in 1993.
A survey of the sulfate inputs to Lake Michigan has appar-
ently not been done; however, the curve for sulfate growth in the
Lake in Figure 18.1 parallels the chloride curve, with an increase
about three times the chloride increase. The time scale for the
274
-------
N3
Table 18.4
CHLORIDE MODEL FOR LAKE MICHIGAN
Concentrations, mg/f :,;
Year after
1973
1
10
20
50
100
200
Accumulation of
annual input,
|(l - exp(- $ t)J
0.189
1.89
3.5
8.1
12.0
15.5
Decay of previous
human input,
C1 exp(- $ t)
4.0
3.6
3.3
2.3
1.4
0.5
Natural
background
3
3
3
3
3
3
Predicted
total
7.2
8.5
9.8
13.4
16.4
19.0
-------
two curves will be the same, and the violations of sulfate stan-
dards will occur at about the same tine as chloride, if "inputs
are not reduced. The data presented below indicate that inputs
have been decreased, but from these Calumet area data, we cannot
extrapolate to the whole Lake.
276
-------
K5
CAL02
IHC and 151st St.
EPA data
O
vO
« r^
O\ OX
Figure 18.10
STORET WATER QUALITY PLOT
-------
CAL03
IHC and Dickey Rd.
EPA data
00
o
v£>
a!
o
>*
0)
•X3
O O
i-l CM
i
V
O
O O
ON ON ON ON ON ON
Figure 18.11
STORET WATER QUALITY PLOT
IHC 1
IHC and Dickey Rd.
Indiana data
o
v£>
(1)
.fi
O
ON
O
O O
f^- CO O\ O i-H CM CO
-------
CAL17
Chicago SWFP Intake
EPA data
1
to
0
X
L )
0
tt
f-t
f
'
:t
a
«.',
O j
o i
L._
1967
1968
1969 1970
Time, years
Figure 18.13
STORET WATER QUALITY PLOT
1971
1972
-------
CAL13
Calumet Harbor
EPA data
4-
i
i
NJ
00
O
cc
o
_J
X
LJ
O
CD
O
D
D
O
o
O --
4i +
^
gl i! -
-• + \ ft-
-T Ui f
'
-HK
4t'
1-
--^ -+ r-
1967
1968
1969 1970
Time, years
Figure 18.14
STORET WATER QUALITY PLOT
1971
1972
-------
CAL16
Hammond Water Plant Intake
EPA data
j?;
i.
'
co
I
i _)
0
c-'
O
. t
' t +
t
- t-
i ,
H !l'i
4 '44
1 -
A
7
1967
-.-^-4.
1968
— IT
A
7
1969 1970
Time, years
Figure 18.15
STORET WATER QUALITY PLOT
1
It
1971
IfW
------- An error occurred while trying to OCR this image.
-------
CAL15
East Chicago Water Plant Intake
EPA data
s *- 1f
^ ! ,'J r
i ^k^ ^
i
-r
.^ , i
IT
v l;
cr
o
o
in
L- \
-ii- W ! 4r
V
At
'
1967
1968
1969 ' 1970
Time, years
Figure 18.17
STORET WATER QUALITY PLOT
1971
1972
-------
o
Cj
CAL14
Gary Water Plant Intake
EFA data
o
o
iT>
>~J
00
O
rr1
CD
O
O
_ -t-
2 i
u~ t
1967
V
+—I-
1968
1969 1970
Time, years
Figure 18.18
STORET WATER QUALITY PLOT
'£
-Ht-
1971
1972^
-------
CAL02
IHC and 151st St.
EPA data
N>
00
O
o j.
CO
o
cn
o i
o ;
CM >
a)
«4-l O
r-l O
m
ON
O
O O
!i
r-l r-l
Figure 18.19
STORET WATER QUALITY PLOT
IHC 3S
IHC and Columbus Drive
Indiana data
O
o
en
•-*.- 4-.J-.
1
I i
o
o
CM
CO
«W O
r-l O
3 rH
ON
o
vo
00
so
OS
CTi
so
O
Is-
CM cn
r-. r-.
l-l T-l
Figure 18.20
STORET WATER QUALITY PLOT
-------
CAL03
IHC and Dickey Rd,
EPA data
o
o
CO
C/l
00
0)
•U
3 r-<
ON
O
o
ON
O"i ON ON
Figure 18.21
STORET WATER QUALITY PLOT
IHC 1
IHC and Dickey Rd.
Indiana data
o
o
c?
o
O i
CM
ON ON ON ON ON
CM CO ^f
ON ON ON
t*™» ^™i i 'i
Figure 18.22
STORET WATER QUALITY PLOT
-------
00
CAL06
IHC mouth
EPA data
CO
o
o
|_» ._
4J
> CO
vo vo
^ CTN
O r^ CM CO
Figure 18.23
STORET WATER QUALITY PLOT
GAL11
Calumat
EPA data
8
o
to
o
o
| 8 t
CO i
Figure 18.24
STORET WATER QUALITY PLOT
-------
CAL17
Chicago SWFP Intake
EPA data
00
00
rr
o
CO
UJ
^—
cc
u_
_J
Z)
in
in
=r
O)
o
o
o
o
r-
o
o
o
o
CJ
o
o
o
o
r\j
a
o
D
D
1967
1968
1969 1970
Time, years
Figure 18.25
STORE! WATER QUALITY PLOT
1971
1972
-------
CAL13
Calumet Harbor
EPA data
NJ
00
vo
cr
in
LT>
j*
O)
o
o
1967
1968
1969 1970
Time, years
Figure 18.26
STORE! WATER QUALITY PLOT
------- An error occurred while trying to OCR this image.
-------
S3
VO
LU
I—
cr
CAL15
East Chicago Water Plant Intake
EPA data
1967
PK
LP
rr
m
0
o
^ 1
j
o
o
o
1
1
1968
1969 1970
Time, years
Figure 18.28
STORE! WATER QUALITY PLOT
1971
-------
CAL14
Gary Water Plant Intake
EPA data
vo
CD
t—
I
EJ
CO
t—
-------
REFERENCES
Abbot, 11. B., 1961
On the spreading of one fluid over another, LaHouille Blanche
16 (6) 327-846.
Atomic Energy Commission, 1973
Environmental Statement related to construction of Bailly
Generating Station Nuclear-1, U.S. Atomic Energy Commission,
Directorate of Licensing, Docket No. 50-367.
Alley, W. P. and Powers, C. F., 1970
Dry weight of the macrobenthos as an indicator of eutrophication
of the Great Lakes, Proc. 13th Conf. on Great Lakes Res., Part II.
Asbury, J. G. and Frigo, A. A., 1971
A phenomenological relationship for predicting the surface areas
of thermal plumes in lakes, Argonne National Laboratory, ANL/ES-5,
Ayers, J. C., 1959
The currents of Lakes Michigan and Huron, Great Lakes Research
Institute, University of Michigan, Ann Arbor.
Ayers, J. C., Chandler, D. C., Lauff, G. Hf, Powers, C. F., and
Henson, E. B., 1958
Currents and water masses of Lake Michigan, Great Lakes Research
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169 pp.
Beeton, A. M., 1965
Eutrophication of the St. Lawrence Great Lakes, Limnology and
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Beeton, A. 11. , 1969
Changes in the environment and biota of the Great Lakes, in
Eutrophication: Causes, consequences, corrections, National
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2.93
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Beeton, A. 11. , 1974
Personal communication, Center for Great Lakes Studies, Univ.
of Wisconsin-Milwaukee.
Beeton, A. 11. and Edmondson, 1972
The eutrophication problem, J. Fisheries Res. Bd. of Canada, June.
Bellaire, F. R., 1963
Relation of winds, water levels and water temperatures to currents
in lower Lake Michigan, Proc. 6th Great Lakes Research Conf.,
219-230.
Bellaire, F. R., 1964
A comparison of methods of current determinations, Publ. Ho. 11,
Great Lakes P^esearch Div. , University of Michigan, Proc. 7th
Great Lakes Research Conf., 171-8.
Birchfield, G. E., 1967
A case study of coastal currents in Lake Michigan, Proc. 10th
Great Lakes Research Conf., 264-273.
Bowden, Robert, 1974
Personal communication, U.S. EPA, Region V, Chicago,
Businessmen for the Public Interest, 1972
Lake Michigan major industrial polluter inventory, prepared for
Lake Michigan Enforcement Conference, September 1972, 14 pp.
Cederwall, Klas, 1970
Dispersion phenomena in coastal environments, J. Boston Soc.
Civil Engrs. 51_ (1) 34-70.
Chandler, DC., 1964
The St. Laurence Great Lakes, Great Lakes Research Div., Univer-
sity of Michigan, collected reprints, Vol. 1, 280-298.
- 294
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City of Chicago, 1972
Report on Lake Michigan Uater Quality Surveys, Division of Water
Purification (1973).
Combinatorics, Inc., 1974
Load allocation study of the Grand Calumet River and Indiana
Harbor Ship Canal, R.eport to State of Indiana, Stream Pollution
Control Board.
Copeland, R. A. and Ayers, J. C., 1972
Trace element distributions in water, sediment, phytoplankton,
and benthos of Lake Michigan, E. R. G. , Inc., Ann Arbor, Michigan.
Corps of Engineers, 1968
Dredging water quality problems in the Great Lakes, Vol. 4,
Appendix A 25, Preliminary report on effects of spoil disposal
at Indiana Harbor, Indiana.
Corps of Engineers, 1969
Dredging and water quality problems in the Great Lakes, Summary
report, U.S. Army, Buffalo District, Corps of Engineers.
Corps of Engineers, 1973
Environmental impact statement on proposed dredging of Indiana
Harbor Ship Canal channel, U.S. Army Corps of Engineers, Chicago
Engineer District.
Csanady, G. 1. , 1974
Personal communication, Woods Hole Oceanographic Inst., Woods
Hole, Mass. 02543.
Environmental Protection Agency, 1974
Proposed effluent limitations guidelines and standards, Iron and
steel point source category, Fed. Register 22 (34) 6487, Feb. 19,
1974.
Fish and Wildlife Service, U.S. Dept. of Interior, 1966
Fish and wildlife as related to water quality of the Lake Michigan
Basin.
295
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Frigo, A. A. and Frye, D. E., 1972
Physical measurements of thermal discharges into Lake Michigan
in 1971, Argonne National Laboratory Report, AIIL/ES-16.
Fruh, E. G., Armstrong, N. E. and Copeland, B. J., 1972
Water quality for estuarine ecological stability, in "Conflicts
in water resources planning," E. F. Gloyna and W. S„ Butcher,
Eds., Center for Research in Water Resources.
Fuller, R. D., 1974
Personal communication, EPA Region V laboratory.
FWPCA, 1967
Lake currents, a technical report, 364 pp.
FWPCA, 1968a
Physical and chemical quality conditions, Lake Michigan Basin,
31 pp.
FWPCA, 1963b
Water pollution problems of Lake Michigan and tributaries.
FWPCA, 1968c
Water quality investigations, Lake Michigan Basin, Biology, 41 pp,
Great Lakes Basin Commission, 1971
Great Lakes Basin Framework Study, Appendix 18, Erosion and
Sedimentation.
Harleman, D.R.G. and Stolzenbach, K. D., 1973
Fluid mechanics of heat disposal from power generation, Ann. Rev.
of Fluid Mechanics 7_, 7-32.
Harrington, M. W., 1895
Currents of the Great Lakes, U.S. Dept. of Agriculture, Weather
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296
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Harris, R. H. and Brecher, E. M., 1974
Is the water safe to drink, Consumer Reports 3£ (6) 436-442.
Hiltunen, J. K., 1967
Some oligochaetes from Lake Michigan, Trans. Am. Microsc. Soc.
86, 433-454.
Hoglund, B. and Spigarelli, S. A., 1972
Studies of the sinking plume phenomenon, 15th Great Lakes Research
Conf., 614-624.
Holland, R. E. and Beeton, A. M., 1972
Significance to eutrophication of spatial differences in nutrients
and diatoms in Lake Michigan, Limnology and Oceanography, 17 (1)
83-96.
Howmiller, R. P. and Beeton, A. 11., 1970
The oligochaete fauna of Green Bay, Lake Michigan, Proc. 13th
Conf. Great Lakes Res., p. 15-46.
Howmiller, R. P., 1972
The oligochaete fauna of central Lake Michigan, p. 58-62 in
R. P. Howmiller and A. M. Beeton, Report on a cruise of the R/V
Neeskay in central Lake Michigan and Green Bay, 8-14 July 1971,
Uriiv. Wisconsin-Milwaukee, Center for Great Lakes Studies, Special
Report 13, 62+10 pp.
Howmiller, R. P., 1973
Review of biology and sediments of southern Lake Michigan, included
as appendix to this final Report.
Illinois EPA, 1970
Lake Michigan open water and Lake bed survey, 87 pp.
Illinois EPA, 1971
Lake Michigan open water and Lake bed survey, 84 pp.
297
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Illinois EPA, 1972
Lake Michigan shore and open water report, 107 pp.
Indiana Stream Pollution Control Board, 1970
Lake Michigan Enforcement Conf, Proc. 2_ (May) 494.
Indiana Stream Pollution Control Board, 1973
Water quality standards, regulations SPC 4R (Lake Michigan and
contiguous harbor areas) and regulation SPC 7R-2 (Grand Calumet
River and Indiana Harbor Ship Canal), reaffirmed Sept. 11, 1973.
International Joint Commission, 1972
Great Lakes water quality, agreement between the U.S. and Canada,
U.S. Govt. Printing Office, Washington, B.C. 20402.
Ippen, A. T., 1966
Estuary and coastline hydrodynamics, McGraw-Hill, New York.
Johnson, J. H., 1960
Surface currents in Lake Michigan, 1954 and 1955, U.S. Fish and
Wildlife Service, Dept. of Interior, Special Scientific R.eport
No. 338, 120 pp.
Keup, L. A., 1968
Phosphorus in flowing waters, Water Research 2, 373-386.
Knight, E. W. , Schrneelk, W. G. , and Lue-King, Cecil, 1972
Water quality trends in in-shore waters of southwestern Lake
Michigan, manuscript of a talk, Metropolitan Sanitary District
of Greater Chicago.
Lake Porter County Regional Transportation and Planning Commis-
sion, 1972
Water and waste water, a component of the regional plan, Dec.
LaVeille, W. C., 1972
Discussion before Phosphorus Committee, July 27, 1972.
298
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Lee, G. F., 1972
Phosphorus, water quality and eutrophication of Lake Michigan,
31 pp., paper presented and included in transcripts of Lake
Michigan Enforcement Conference, Sept. 1972. Proceedings of this
conference have not been published, but are on file at U.S. EPA,
Chicago, Illinois.
Merna, J. W., 1960
A benthological investigation of Lake Michigan, Unpublished M.S.
Thesis, Michigan State University, 74 p.
Moore, S. L., 1974
Summary of waste load allocations GCR and IHC, memorandum of staff
to Indiana SPCB, May 19, 1974,
Mortimer, C. H., 1968
Internal waves and associated currents observed in Lake Michigan
during the summer of 1963, Special Report Ho. 1, Center for Great
Lakes Studies, University of Wisconsin-Milwaukee.
Mortimer, C. H., 1970
A pictorial account of oscillatory responses to wind stresses in
large lakes, with particular reference to long waves in Lake
Michigan, manuscript, University of Wisconsin-Milwaukee.
Mortimer, C. H., 1971a
Chemical exchanges between sediments and water in the Great Lakes
— speculations on probable regulatory mechanisms, Limnology and
Oceanography 16 (2) 387-404.
Mortimer, C. H., 1971b
Large-scale oscillatory motions and seasonal temperature changes
in Lake Michigan and Lake Ontario, Special Report Ho. 12, U.S.
Army Engineers Contract No. DACW-35-68-C-0072, University of
Wisconsin-Milwaukee, Parts I & II.
Mozley, S. C. and Garcia, L. C., 1972
Benthic macrofauna in the coastal zone of Lake Michigan, Proc.
15th Conf. Great Lakes Res., pp. 102-116.
299
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llurphy, T. J., 1973
Phosphorus inputs from the atmosphere — their importance to
oligotrophic lakes, 16th Great Lakes Research Conf.
National Academy of Sciences, 1969
Eutrophication: causes, consequences, correctives, Proc. of
International Symposium on Eutrophication.
National Academy of Sciences, 1974
Water quality criteria, Pveport to U.S. EPA, to be published by
U.S. Government Printing Office.
Noble, V. E., Huang, J. C. and Saylor, J. H., 1960
Vertical current structure in the Great Lakes, Special Report
No. 37 of the Great Lakes Research Division, University of
Michigan.
O'Connor, D. J. and Miller, J. A., 1970
A water quality model of chlorides in Great Lakes, J. Sanitary
Engr. Div. ASCE, 96_ (4) 955-975.
Palin, A.. T. , 1973
Chemistry and control of modern chlorination, LaMotte Chemical
Products Co., Chestertown, Maryland 21620.
Palmer, M. D., 1974
Coastal region residence time estimates from concentration
gradients, 17th Great Lakes Research Conference.
Parker, F. L. , arid Krenkel, P. A., 1969
Thermal pollution: status of the art, Report No. 3 prepared for
FWPCA, Vanderbilt University, Nashville, Tenn.
Parsons, T. R. and Strickland, J.D.H., 1963
Discussion of spectrophotometric determination of marine-plant
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300
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People of the State of Illinois and the Metropolitan Sanitary
District of Greater Chicago vslnland Steel Co., 1974
Circuit court of Cook County, Illinois.
Phosphorus Technical Committee, 1972
Report to Lake Michigan Enforcement Conference, U.S. Environmental
Protection Agency.
Powers, C. F. and Robertson, A., 1965
Some quantitative aspects of the macrobenthos of Lake Michigan,
University of Michigan Great Lakes Research Division, Publication
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Powers, C. F. and Ayers, J. C., 1967
Water quality and eutrophication trends in southern Lake Michigan
in Studies on the environment and eutrophication of Lake Michi-
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Pritchard, D. W., 1972
Testimony at Lake Michigan Enforcement Conference, Sept. 21,
1972, Vol. 3, Part 3, p. 789-883. (Unpublished, available from
U.S. Environmental Protection Region V library.)
Reed, Philip and Pawlowski, C., 1974
Taste and odor incidents at 68th St. water intake, unpublished
report, Chicago Water Dept.
Risley, Clifford and Fuller, R. D., 1965
Chemical characteristics of Lake Michigan, Proc. 8th Great Lakes
Research Conf., 166-174.
Risley, Clifford and Fuller, R. D., 1966
Chemical findings from pollution studies in the Calumet area of
Indiana and Illinois and the adjacent waters of Lake Michigan,
Proc. 9th Great Lakes Research Conf., 423-9.
Robbins, J. A., Landstrom, Edward and Wahlgren, Morris, 1972
Tributary inputs of soluble trace metals to Lake Michigan, Proc.
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301
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Robertson, A. R. and Alley, W. P., 1966
A comparative study of Lake Michigan macrobenthos, Limnology and
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Robertson, A. and Powers, C. F., 1965
Particulate organic matter in Lake Michigan, 8th Great Lakes
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Robertson, A. R., and Powers, C. F., 1967
Comparison of the distribution of organic matter in the five
Great Lakes, in Studies on the environment and eutrophication of
Lake Michigan, University of Michigan Great Lakes Research Div.,
Special Report No. 30.
Robertson, A., Powers, C. F. and Rose, Jeanne, 1971
Distribution of chlorophyll and its relation to particulate
organic matter in the off-shore waters of Lake Michigan, 14th
Great Lakes Research Conf., 90-101.
Rousar, D. C., 1973
Seasonal and spatial changes in primary production and nutrients
in Lake Michigan, Water Air and Soil Pollution, 2_, 497-514.
Sager, P. E. and Wiersma, J. H., 1972
Nutrient discharges to Green Bay, Lake Michigan from the lower
Fox River, Proc. 15th Conf. on Great Lakes Research.
Santina, William and Bochantin, Bernard, 1974
Personal communication, U.S. Army Corps of Engineers, Chicago
Engineer District.
Saylor, J. H., 1968
Lake Michigan harbor currents (Calumet area), Army Corps of
Engineers, Subproject GLR-111.
Schelske, C. L. and Roth, J. C., 1973
Limnological survey of Lakes Michigan, Superior, Huron and Erie,
Publ. No. 17, Great Lakes Research Div., University of Michigan,
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302
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Schelske, C. L. and Stoermer, E. F., 1971
Eutrophication, silica depletion and predicted changes in algal
quality in Lake Michigan, Science 173, 434-4.
Schindler, D. W., 1974
Eutrophication and recovery in experimental lakes: implications
for lake management, Science 184 (June 7), 897-9.
Schleicher, J. A. and Kuhn, J. K., 1970
Phosphorus content in unconsolidated sediments from southern
Lake Michigan, Illinois State Geological Survey, Environmental
Geology Note No. 39.
Sharp, J. J., 1969
Spread of buoyant jets at the free surface, J. Hydraulics Div.
ASCE 95. (HY3) 811-825.
Shimp, et al., 1970a
Distribution of arsenic in unconsolidated sediments from souther
Lake Michigan, Illinois Geological Survey, Environmental Geology
Note Series, EGN 37.
Shimp, et al., 1970b
Distribution of major, minor, and trace constituents in uncon-
solidated sediments from southern Lake Michigan, Illinois
Geological Survey, Environmental Geology Notes Series, EGN 32.
Shimp, et al., 1970c
Phosphorus content in unconsolidated sediments from southern
Lake Michigan, Illinois Geological Survey, Environmental Geology
Notes Series, EGN 39.
Shimp, et al., 1970d
Preliminary stratigraphy of unconsolidated sediments from the
southwestern part of Lake Michigan, Illinois Geological Survey,
Environmental Geology Notes Series, EGN 30.
303
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Shimp, et al., 1970e
Stratigraphy of unconsolidated sediments in the southern part of
Lake Michigan, Illinois Geological Survey, Environmental Geology
Notes Series, EGN 35.
Shimp, et al., 1971a
Distribution of mercury in unconsolidated sediments from southern
Lake Michigan, Illinois Geological Survey, Environmental Geology
Notes Series, EGN 44.
Shimp, et al., 1971b
High-resolution seismic profiles and gravity cores of sediments
in southern Lake Michigan, Illinois Geological Survey, Environ-
mental Geology Notes Series, EGN 47.
Shimp, et al., 1971c
Trace elements and organic carbon accumulation in the most recent
sediments of southern Lake Michigan, Illinois Geological Survey,
Environmental Geology Notes Series, EGN 41.
Shimp, et al., 1972a
Dep. patterns and trace element accumulation in the southern
end of Lake Michigan, Illinois Geological Survey, Environmental
Geology Notes Series, EGN 58.
Shimp, et al., 1972b
Geologic cross-sections derived from seismic profiles and sedi-
ment cores from southern Lake Michigan, Illinois Geological
Survey, Environmental Geology Notes Series, EGN 54.
Shimp, et al., 1973
Major, minor, and trace elements in sediments of Lake Michigan,
Illinois Geological Survey, Environmental Geology Notes Series,
EGN 60.
Somers, L. H. and Josephson, P. D., 1968
Bottom sediments of southwestern Lake Michigan, Proc. Great Lakes
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304
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Sonsogni, W. and Lee, G. F., 1972
Recovery of the Madison Lakes after nutrient diversion, AIChE
meeting, Minneapolis, Minnesota, August 1972.
Stoermer, E. F., 1969
Plankton diatom assemblages in Lake Michigan, FWQA Report, Program
No. 18050 DKC.
Sweeney, Dan, 1973
Citizens for a Better Environment as subcontractor to IITRI,
Information obtained by site visits and interviews with personnel
of East Chicago Sanitary District, September to December 1973.
Technical Committee on Water Quality, 1970
Water quality in the Calumet area, Conf. on Pollution of Lower
Lake Michigan and Calumet Area, Issued separately by U.S. Environ-
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Thomas, N. A., Hartwell, K. and Miller, W., 1972
Technical working report No. 3, Grosse lie laboratory, U.S.
Environmental Protection Agency.
U.S. Bureau of Outdoor Recreation, 1965
Water-oriented outdoor recreation in Lake Michigan basin, report
to FWPCA.
U.S. Environmental Protection Agency, 1973a
Comparison of NTAC, NAS and Proposed EPA Numerical criteria for
water quality.
U.S. Environmental Protection Agency, 1973b
Pretreatment of pollutants introduced into publicly owned treat-
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U.S. Public Health Service, Dept. of HEW, 1963a
Currents at fixed stations near Chicago, Special Report No. 11,
Great Lakes-Illinois River Basins Project.
305
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U.S. Public Health Service, Dept. of HEW, 1963b
Currents in the southern basin, Special Report No. LM 12, Great
Lakes-Illinois River Basin Project.
U.S. Public Health Service, Dept. of HEW, 1963c
Lake currents at a single station, Special Report No. LM 9, Great
Lakes-Illinois River Basins Project.
U.S. Public Health Service, Dept. of HEW, 1963d.
Drogue surveys of Lake currents near Chicago, Special Report No.
10, Great Lakes-Illinois River Basins Project.
Van Oosten, John, 1963.
Surface currents of Lake Michigan, 1931 and 1932, U.S. Fish &
Wildlife Service, Dept. of Interior, Special Scientific Report
No. 413, 51 pp.
Vaughn, J. C., 1969
A current report on e ffect of water quality deterioration on the
operation of Chicago's south water filtration plant, Presented
at FWPCA Conference, City of Chicago, Dept. of Water and Sewers.
Vaughn, J. C. and Reed, P. A., 1972
Progress report on water quality of Lake Michigan near Chicago,
Presented at four-state pollution conference at Chicago, Illinois,
City of Chicago, Dept. of Water & Sewers Report.
Verber, J. L., 1964
The detection of rotary currents and internal waves in Lake
Michigan, Proc. 9th Great Lakes Research Conf., 299-306.
Vollenweider, R. A., 1968
Scientific fundamentals of the eutrophication of lakes and flowing
waters, with particular reference to nitrogen and phosphorus as
factors in eutrophication. Report to the Organization for
Economic Co-operation and Development, Directorate for Scientific
Affairs.
Wilding, R. E. and Schmidt, R. L., 1973
Phosphorus release from Lake sediments, Report EPA-R3-73-024,
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306
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Winters, J. L., 1973
Personal communication, Indiana State Board of Health.
Winters, J. L., 1974
Ammonia loading to Lake Michigan from IHC, unpublished office
memorandum, Indiana State Board of Health, May 9, 1974.
Wnek, W. J. and Fochtman, E. G., 1972
Mathematical model for fate of pollutants in near-shore waters,
Environ. Sci. & Tech. 6_ (4) 331-7.
307
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