EPA-905/9-74-011-B
VOLUME 2 (APPENDICES)
US. BMRONMBirAL PROIKHON JIGMCY
REGION V BfORCHMDir DIVISION
GREAT IAKESIHTIAIIVE CONTRACT PROGRAM
OCTOBER, 1974
-------
WATER POLLUTION INVESTIGATION: CALUMET AREA
OF LAKE MICHIGAN
VOLUME 2
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-B
EPA Project Officer: Howard Zar
October 1974
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Table of Contents
Volume II
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
Volume I
1. INTRODUCTION, SUMMARY AND RECOMMENDATIONS
2. DESCRIPTION OF AREA AND WATERSHED
3. FLOW DATA OF TRIBUTARY STREAMS
4. INDUSTRIAL WASTE SOURCES, OUTFALLS AND EFFLUENT DATA
5. MUNICIPAL SOURCES AND COMBINED SEWER OVERFLOWS
6. WATER QUALITY DATA
7. SEDIMENT POLLUTION AND BENTHIC ORGANISMS
8. IMPACT OF POLLUTANTS ON QUALITY AND USE OF WATER
9. BIOLOGICAL INDICATORS OF WATER QUALITY
10. LAKE CURRENTS
11. IITRI FIELD SAMPLING PROGRAM AND DATA
12. DISPERSION OF EFFLUENTS FROM INDIANA HARBOR CANAL (IHC)
13. AMMONIA-NITROGEN
14. PHENOLS
15. OIL AND GREASE
16. BACTERIAL POLLUTION
17. PHOSPHORUS
18. CHLORIDE AND SULFATE
References
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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.
-------
BIBLIOGRAPHIC DATA
SHEET
1. Report No.
EPA-905/9-74-011-B
S.^Bc-cipient's Accession No.
. Title And Subtitle
Water Pollution Investigation: Calumet Area of Lake Michigan
/olume 2 (Appendices)
Report Date
October 1974
6.
. Author(s)
Richard H. Snow
8» Performing Organization Kept.
No.
. Performing Organization Name and Address
I IT Research Institute
0 West 35th Street
hicago, Illinois 60616
10. Pto)ect/Task/Work Unit No.
11. Contract/Grant No.
68-01-1576
2. Sponsoring Organization Name and Address
J.S. Environmental Protection Agency
Enforcement Division, Region V
230 S. Dearborn Street
hicago, Illinois 60604
13. Type of Report & Period
Coveredpinal Report
(Appendices)
u.
5. Supplementary Notes
EPA Project Officer: Howard Zar
6. Abstracts An investigation 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
hinlngiral impart nf pollutants nn thp r.alnmpt arpa nf lakp Mirhigan
17. Key Words and Document Analysis. 17a. Descriptors
Water Quality Aquatic Biology, Water Pollution
17b. Idemifiers/Open-Ended Terms
Calumet Area, Indiana Harbor Canal, Lake Michigan, Great Lakes,
Chemical Parameters, Biological Parameters
17c. COSATI Field/Group
gp
18. Availability Statement
19. Security Class (This
Report)
UNCLASSIFIEI)
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 14952-P72
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APPENDIX A
A REVIEW OF SELECTED RESEARCH
ON THE BIOLOGY AND SEDIMENTS
OF SOUTHERN LAKE MICHIGAN
WITH PARTICULAR REFERENCE TO THE CALUMET AREA
by
Richard P. Howmiller
Department of Biological Sciences
University of California
Santa Barbara, California 93106
A-l
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TABLE OF CONTENTS
Page
Introduction A- 3
Bacteria 5
Algae 11
Phytoplankton Abundance
Composition of the Plankton Flora 17
Macroscopic Algae 23
Sediments 25
Distribution of Sediment Types 25
Evidence of Human Contamination of Sediments 32
Benthic Macroinvertebrates 35
Abundance of Major Components of the Lake Michigan Fauna 35
The Value of Studies at the Species Level ^3
Benthic Studies in the Calumet Area 45
Effects of Benthos on Sediment-Water Exchange 61
Recommendations for Applied Research on the Benthos 63
on the Calumet Area
Species Distributional Patterns 63
Effects of Benthos on Chemical Parameters 65
Literature Cited 68
A-2
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INTRODUCTION
Effluents of municipalities and industries can have pronounced
ecological effects upon receiving waters. They may, because of some
toxic components, eliminate many or most forms of life. Large amounts
of oxygen-demanding organic matter may upset the oxygen regime, thus
greatly modifying the biological community. Even non-toxic inorganic
components can be biologically important by serving as plant nutrients,
thus accelerating the process of eutrophication.
The resulting biological changes may be of great importance because
of their economic impact. Excessive growths of algae and aquatic plants
may increase the cost of municipal and industrial water treatment, and
may interfere with usual recreational uses of water. Fish stocks usually
change in composition to less desirable, and economically less valuable,
species under the influence of pollution and eutrophication.
Because the biota of lakes and rivers changes gradually with in-
creasing 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 constant-
monitoring system for many years, viz; the community of plants and
animals living in the water.
This report is a review of literature on some components of the
biota of Lake Michigan. It is, admittedly, a rather uneven treatment,
giving greatest attention to the invertebrate bottom fauna. This is a
reflection of the particular interests and experience of the author.
Studies of the zooplanktpn are omitted entirely from this review, being
A-3
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the subject of a similar report by Gannon (1973).
The following pages place particular emphasis on knowledge of the
south-western corner of the lake. The author has attempted to point out
changes in the biota which may be related to pollution and/or eutrophica-
tion, especially that related to pollutants originating in the Calumet
area.
A-4
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BACTERIA
The natural bacterial flora of lakes remains relatively little
studied and information on the bacteria of Lake Michigan, other than
those of sewage origin, is limited.
Scarce (1965) and the Federal Water Pollution Control Administration
(FWPCA 1968b) reported results of a study of 4100 samples from city
harbors and 1200 samples from inshore area (within 10 miles of shore).
Three families were most common, Achromobacteriaceae, Pseudomonaceae,
and Eubacteriaceae. The Achromobacteriaceae were most prevalent,
accounting for 95 to 99 per cent of the colonies examined from plates
incubated at 20 and 35°C. Each family was represented by several genera.
It is questionable to what extent the study presents a true picture of
the lake's normal bacterial flora. Methods involving culturing are
selective for those species well adapted to grow on the media used and
under the oxygen and temperature conditions established during incubation
(Scarce 1965, Robohm and Graikowski 1966). It has also become obvious
that culture methods grossly underestimate density as established by
direct counts (Bell and Dutka 1972).
Considerable more effort has been devoted to studies of abundance
and distribution of bacteria of sewage origin. For the most part these
investigations have been concerned with "coliform bacteria", believed
largely to be represented by Escherichia coli, a species which is not
normally pathogenic itself but which is indicative of recent fecal con-
tamination of the water and, therefore, of the possible presence of
pathogens.
Damann (1960) reported upon counts of coliform bacteria from a
A-5
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Chicago water intake during the period 1926-1958. Methods used for
estimating numbers apparently remained unchanged over this period.
Highest annual average numbers were reported in 1940, 1941 and 1942 (Most
Probable Number (MPN) 180, 222, and 250 per 100 milliliters, respectively)
Damann saw fit to remark that it was during this period that, due to the
demands of World War II, industry in the region was undergoing great
expansion. Lowest annual average numbers occurred in 1950, 1952, and
1954 (MPN; 7, 7, and 8 per 100 ml). There was an apparent trend of
decreasing coliform numbers, with an annual average MPN for 1926-1942 of
70 per 100 milliliters but for the period 1943-1958 of only 23 per 100
milliliters. The trend proved not significant at the 0.01% level,
however (Fig. A-l).
Scarce (1965) discussed results of coliform counts on samples from
313 stations in the southern basin of Lake Michigan. Samples from off-
shore stations had little or (usually) no coliform content. Highest
coliform densities occurred with greatest frequency near centers of
urbanization along the western shore. For example, surface samples from
10 nearshore stations between the northern limit of Chicago and the
eastern end of Gary, Indiana contained the following coliform densities:
estimated coliform number of
density stations
(cells/100 ml) in range
<1 1
1-10 2
11-100 2
110-1000 4
1100-2000 1
z. = 10
A-6
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o
2300
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The average density here would obviously be much higher than what
one would expect from the data presented by Damann (1960) and the
discrepancy may reflect differences in methodology. Other recent reports
indicate that high coliform bacteria concentrations occur frequently at
several water intakes and most beaches along southwestern Lake Michigan
(Holleyman 1960, FWPCA 1968b) . For example, Rainbow Beach and Calumet
Park Beaches failed to meet the joint federal-state criteria for bacterial
levels approximately 66% of the time during 1966, 20% of the time during
1967, and 33% of the time during 1968. Some beaches had even worse
records (FWPCA 1968c). High coliform bacteria counts in this area occur
mostly under conditions of onshore winds following heavy precipitation
(Holleyman 1968).
Scarce and Peterson (1966) investigated the coliform abundance and
the incidence of selected pathogenic bacteria in several streams of the
Chicago and Calumet area. The waters studied are regularly or occasion-
ally tributary to Lake Michigan. Results reflected gross pollution of
sewage origin. Total coliform geometric mean densities ranged to almost
700,000 per 100 ml in the Sanitary and Ship Canal. Individual determin-
ations ran as high as 25,000,000 per 100 ml in this waterway. A station
on the Grand Calumet River had a geometric mean coliform density of
3,000,000 per 100 ml and fecal streptococcus concentrations as high as
260,000 per 100 ml. Salmonellae were present throughout the stream
systems investigated. These included 23 strains, all pathogenic.
Pathogenic enteroviruses were found in 27 per cent of the stream samples.
It is easy to understand why intolerable bacterial densities in the lake
follow heavy rains which accelerate flushing of these water courses.
A-8
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High numbers of coliforms and pathogens of fecal origin would not
persist for long in the lake if it were not for continuing inputs.
Hedrick, Meyer and Kossoy (1962) studied the survival of JE. coll.,
Salmonella typhosa, S_. paratyphi, S^. schottmue11er i, Shigella dysenteriae,
^5. paradysenteriae, and j^. sonnei using pure cultures and sterile-filtered
Lake Michigan water obtained at the South District Filtration Plant in
Chicago. All but the first of these are enteric parasites and pathogens.
With few exceptions, they found substantial mortality of these bacteria
within 24 hr. They attributed this to a toxic factor in the lake water
since corresponding studies employing well water resulted in smaller
decreases or increases in bacterial numbers. With the possible exception
of Salmonella schottmuelleri, the enteric pathogens were more sensitive
to the toxic factors in Lake Michigan water than was 15. coli. In general,
the Shigella strains, Salmonella typhosa and j^. paratyphi usually under-
went at least a 50% reduction of numbers within 24 hr, while S^.
schottmuelleri and IS. coli either grew or suffered less than a 50% loss
in 24 hr.
At the same time, Hedrick, Meyer and KossOy (1962) also studied the
survival of coliform bacteria present in untreated water from the South
District Plant. During the period July 1952 - Sept. 1953 they found
great reduction in numbers of coliforms during 24 hr. However, in the
winter and early spring of 1954 there was very little loss of coliforms
during their 24 hr experiments. Comparison of their data with that of
earlier studies (Noble and Gullans 1955) showed that the short survival
times are the usual case in Lake Michigan.
Results from winter and spring of 1954 are unusual but remain unex-
plained.
A-9
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Survival of JE. coli and EL schottmuelleri in the first-mentioned
series of experiments paralleled very closely the behavior of the
coliforms in the tests with untreated lake water. Thus it seems that the
"toxic factor" in Lake Michigan water is at times less effective at
reducing numbers of coliforms and S^. schottmue 11 eri but even on these
rare occasions, numbers of many important pathogens are quickly reduced.
A-10
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ALGAE
Phytoplankton Abundance
The FWPCA (1968a) reported that in 1962-63 deep-water (open lake)
areas supported low abundance of phytoplankton, generally in the range
100-300 organisms/ml. Nutrient rich inshore areas, on the other hand,
generally had abundances exceeding 500/ml. (Fig. A-2,3,4). Phytoplankton
were very abundant in the Chicago-Calumet area with densities reaching
1298/ml in 1962 and 2,143 in 1963.
Beeton (1969) reported that open lake plankton abundance has gener-
ally been about 1/3 that at the Chicago intake.
It is obvious from Figures A-2,3 and 4 that the southwestern corner
of the lake was, in 1962-63, unique in having high phytoplankton densities
in both spring and fall. Other inshore areas on the western side of the
southern basin had peak densities in fall while along the eastern and
northwestern shores the peak came in spring.
This may represent a regular difference in the annual cycle of
abundance in these areas. Damann (1966) pointed out that over a period
of many years phytoplankton sampled at Chicago has had two peaks of
abundance annually while abundance was unimodal at Milwaukee and in the
open lake. It is difficult to know what importance to ascribe to this
observation, other than that the Chicago area seems a unique area in
Lake Michigan. More recently, Holland (1969) has observed a bimodality in
diatom abundance in Green Bay, the most eutrophic area of Lake Michigan.
Beeton (1969) feels that a bimodal cycle of phytoplankton abundance may
be characteristic of more productive areas in the Great Lakes.
Data from the Chicago water intake show that phytoplankton abundance
A-ll
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NORTH
MILWAUKEE
ii:ii::ii:i:i- Racine
O-300/ml.
300-500/ml.
over 5OO/ml.
25
MILE
Figure A~2. Showing phytoplankton
abundance as numbers per milliliter
in Lake Michigan during Spring 1962.
Figure taken from FWPCA (1968a).
A-12
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ll!:!! s (r -::::::::::!!::i:i!:!ii!!"!:!"i:!"""lii
I I 0-30O/ml.
300-500/ml
ovw 500/ml.
Figure A-3. Showing phytoplankton
abundance as numbers per milliliter
in Lake Michigan during Summer 1962.
Figure taken from FWPCA (1968a).
A-13
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I 1 0-300/ml.
300-50O/ml.
over 5OO/ml.
O 25
l i i • • l
MILE
Figure A-4 . Showing phytoplankton
abundance as numbers per milliliter
in Lake Michigan during Fall 1962.
Figure taken from FWPCA (1968a).
A-14
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increased at an average of 13 organisms/ml per year during the period
1926 to 1958 (Fig. A-5, Damann 1960).
A-15
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z 17--
Ul
O.
S 15
cc
Q
3
X
.. TOTAL PLANKTON
13"
II --
9--
1926 28 30 32 34 36 38
-------
Composition of the Plankton Flora
In reviewing studies of the Lake Michigan phytoplankton, Davis (1966)
drew attention to the nearly unanimous agreement of investigators that
diatoms dominate the flora. For example, he cites Damann (1945) who
reported that diatoms constituted an average of 94% of the phytoplanktets
over the course of the year of his study and at no time accounted for
less than 89% of the total.
The dominant diatoms of open Lake Michigan are Fragilaria crotonensis,
Melosira islandica, Tabellaria flocculosa, Asterionella formosa, Cyclotella
stelligera and C^. michiganiana (Holland 1969). This is very clearly an
oligotrophic flora (Rawson 1956, Beeton 1965).
To some extent the extreme dominance of diatoms may represent an
artifact of the methods used by most of those who have studied the Lake
Michigan phytoplankton. Recent work done with special attention to other
elements of the flora indicates that diatoms are frequently not dominant,
at least in some inshore waters (Claflin and Beeton 1972). Algae other
than diatoms which Davis (1966) reported to be abundant at times include;
Dinobryon, Ceratium, Anacystis, Chrooccus and Oocystis.
It is becoming clear from recent studies that the flora of inshore
waters may differ greatly from that in the main body of the lake (Holland
and Beeton, 1972) . Stoermer (1968) reported on pronounced inshore (less
than 4 mi from shore)-offshore differences. He attributed these to a
horizontal thermal discontinuity ("thermal bar") which was present during
his two day study. Holland (1968, 1969) found several species of diatoms
(Diatoma tenue v. elongatum, Fragilaria crotonensis, Melosira ambigua,
Stephanodiscus tenuis, Tabellaria flocculosa) more abundant inshore than
offshore during the period April - November 1965. Furthermore, generation
A-17
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times were less inshore than offshore. Obviously, these inshore-offshore
differences are not exclusively short-term phenomena associated with
thermal bars. The differences in distribution, abundance, and generation
times of diatoms were related to inshore-offshore differences in nutrients.
More recent studies (Beeton 1970) continue to illuminate great differences.
These inshore-offshore differences are being emphasized because much of
our knowledge of Lake Michigan plankton has resulted from studies of
samples taken from municipal water intakes which are invariably located
within a mile or two from shore. It is important to realize that results
of such studies may not be validly extrapolated to the lake as a whole.
The results are nevertheless important, for it is the inshore waters
which serve most of our esthetic and recreational needs, from which we
draw water, and where much commercial fishing is done. In terms of our
interest in the Calumet area, knowledge of these pronounced inshore-
offshore differences indicates that the only studies having direct rele-
vance will be those done within a few miles of shore in the southern end
of the lake.
Stoermer and Yang (1970) examined over 900 Lake Michigan phytoplank-
ton samples collected between 1876 and 1967. They give a detailed account
of the distribution and relative abundance of the dominant planktonic
diatoms of the lake and have documented floristic changes during this 90
year period. They found that those 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 nearshore waters and
virtually all nearshore waters now have a flora radically different from
that indicated by the earliest samples. Collections from the Chicago
area in 1876-1881 contained most of the species which now are found
A-18
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exclusively in the open lake, although some of the species which are now
characteristic of inshore waters were also present. This pattern, of new
introductions to the flora appearing first in nearshore waters and later
spreading to the open lake, was taken by Stoemer and Yang C1970) as
evidence that the changes are caused by nutrient pollution and not natural
phenomena. They predicted further changes in the flora, with perennial
and oligotrophic species being replaced by seasonal species more favored
by mesotrophic or eutrophic conditions. It was estimated that within
10-20 years changes may have progressed to the point where offshore
diatom blooms would be considered esthetically objectionable. The authors
did point out, however, that this was a very tenuous estimate because of
the possibility that changing chemical conditions will result in a flora
dominated by algae other than diatoms.
Itecent experimental work by Schelske and Stoermer (1971, 1972) pro-
vides evidence that silica is sometimes limiting the growth of diatoms
in Lake Michigan. Phosphorus, presumably the usual limiting nutrient at
most times in the past, has been added to the lake in such quantities
that it has allowed diatoms to grow up to the level of available silica.
Relative to the needs of diatoms, phosphorus enters the lake in much
greater quantities than does silica. The ratios indicate that 10 to 20
times more phosphorus is being added to the lake than can be utilized
with present inputs of silica (Schelske and Callender 1970, Schelske and
Stoermer 1972). Thus it can be expected that the composition of the
planktonic flora will shift from near complete dominance of diatoms to
a greater proportion of the less desirable nonsiliceous green and blue-
green algae. Evidence indicates that this is happening (Schelske and
Stoermer 1972).
A-19
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Major changes can be expected to occur first in the southwestern
section of the lake. During the summer of 1969, the lowest concentrations
of silicon were found in surface samples taken at the southern end of the
lake (Schelske and Callender 1970). Powers and Ayers (1967) found the
lowest concentrations of silicon at Chicago in an analysis of records
kept for municipal water intakes. The Chicago records, as well as those
from other areas, show decreasing concentrations with time (Fig. A-6).
Abundant plankters of certain taxa have caused problems for water
supply arouni southern Lake Michigan. Dinobryon has been cited as the
cause of "fishy" odor in the Chicago water supply (Baylis 1951).
Tabellaria, and several other genera of diatoms, have caused problems of
filter-clogging (Baylis 1954, 1957, 1960). Two diatoms not previously
reported from Lake Michigan, Stephanodiscus hantzschii and S^. binderanus
(M. binderana?) have become abundant enough at the Chicago intake to
cause further filter clogging problems in recent years (Vaughn 1961).
Blooms and filter clogging by _S_. hantzschii, and perhaps also _§_.
binderanus, were correlated with periods when a fine turbidity occurred
in raw and finished (filtered) water. This turbidity was caused by small
cuboidal crystals of calcium carbonate and the conclusion reached was
that it was caused by the diatom blooms. It was surmized that the dense
blooms used up available free CCL and then used bicarbonate as a CO-
source* resulting in the precipitation of carbonate. This theory was
supported by observed changes in pH and alkalinity (Vaughn 1961).
Ayers, Stoermer aad McWilliam (1967) observed "milky water" in
several cruises on five cross-lake transects between Chicago and Frankfort,
Michigan. They found some evidence that this condition occurred period-
ically as far back as 1954 but suggested that it had become more pro-
A-20
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14-
E12-
gioH
8-
6-
4—
Q
& 6H
Q.
4
* 2H
8 —
E S
a ^
o-H
GRAND RAPIDS
MILWAUKEE
CHICAGO
I I I I I I I I I I I T I I pi I I I I
26 28 30 32 34 36 38 40 42 44 46 48 50 52 54 56 58 60 62 64
YEARS
Figure A-6. Silica concentration at water intakes of Grand Rapids,
Milwaukee, and Chicago plotted against time for the periods of
existing records. (Figure taken from Powers and Ayers 1967.)
A-21
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nounced in the period 1964-1966. "Milky water" was again observed at
stations off Chicago in the summer of 1969 (Schelske and Callender 1970).
Ayers, Stoermer and McWillians hypothesized that the cause of this tur-
bidity was fine particles of calcium carbonate formed when diatoms used
bicarbonate as a CCL source. The situation is thus possibly the same
as that observed by Vaughn (1961) and illustrates again that phenomena
observed in degraded inshore waters may be anticipated soon the open
lake if eutrophication continues at its present rate. We have, in the
southern end of the lake, a large-scale nutrient enrichment experiment
and to use the terms chosen by C. H. Mortimer (discussion to Schelske
and Stoermer 1972) the Chicago intake might be considered a useful "early
warning system".
Phytoplankton abundance in Lake Michigan, even in southern Lake
Michigan, is low compared to Lake Erie. There is no doubt that phyto-
plankton would increase in abundance with accelerated eutrophication and
that, consequently, problems of objectionable tastes and odors and filter-
clogging would become more frequent and more severe. This would be
particularly true if, as has been predicted, further inputs of phosphorus
result in depletion of silica by excessive diatom growths and the flora
shifts to one dominated by glue-green algae. Blue-greens are typical of
eutrophic situations and are notorious for creating taste and odor prob-
lems and the clogging of filters.
A-22
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Macroscopic Algae
According to the FWPCA (1968a),the Chicago Park District has, for
several years, experienced problems with fouling of beaches by algae
washed in from the lake. In 1961, the offending organism at Oak Street
and Montrose beaches was found to be Dichotomospiphon, a green filamentous
alga. In 1962 the green alga Cladophora glomerata was the principal
species involved but Qedogonium was also present (FWPCA 1968a). All of
these organisms require a firm substrate and thus do not grow on the
beach but are washed up there when luxuriant growths are broken loose
during heavy weather. The resulting windrows of algae become foul-
smelling after a few days in the summer heat. Flies and other insects
become very abundant in the decaying masses (FWPCA 1968a). The unesthetic
appearance of the decaying algae, as well as the resultant odor and
swarms of insects, obviously detract from the recreational value of the
beaches.
Cladophora has, since the 1950*s become an important algal nuisance
in lakes Erie and Ontario as well as in southern Lake Michigan. Herbst
(1969) reported Cladophora very abundant (problem conditions) near
Milwaukee, Racine, Kenosha, Chicago, Michigan City and Benton Harbor.
He found only sparse growths, small in extent, along northern shores of
Lake Michigan.
The distribution of Cladophora is correlated with nutrient-rich
water, it being rare in the upper lakes except near centers of population.
Herbst (1969) considered phosphorus to be the limiting nutrient in most
situations. Application of phosphorus to suitable locations in Lake
Huron, which were otherwise devoid of Cladophora, resulted in its estab-
lishment and subsequent growth (Neil and Owen 1964). Mechanical removal
A-23
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and the use of algicides have effected temporary control of Cladopbora
in local situations (McLarty 1961). Considering the magnitude of the
problem growths, however, and the possible side-effects of applications
of biocides, tertiary treatment of effluents for phosphorus removal seems
the only feasible control measure (Herbst 1969). We can expect continuing
problem growths of Cladophora in direct proportion to the input of
nutrients, especially phosphorus.
A-24
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SEDIMENTS
Distribution of sediment types
The surficial bottom sediments of Lake Michigan have been described
by Hough (1935), Ayers and Hough (1964), Ayers (1967), Powers and Robertson
(1967, 1968), Somers and Josephson (1968).Mozley and Alley (1973) and
other authors. Of interest in the present context are comments on the
distribution of sediment types in the southern end of the lake as this
may have some bearing on consideration of the distribution and sampling
of benthic invertebrates. Reports of contamination of sediments are, of
course, also of value. The following discussion will thus rely heavily
on those few papers which provide the greatest detail in describing the
sediments of the southern end of the lake.
Ayers (1967) reported on the distribution of sediment types as based
on a "Field description" at the time of collection. He recognized 12
categories of sediment, mostly on the basis of texture. Figure A-7,
taken from Ayers1 paper,shows that sediments of the southwestern corner
of the lake range from silty sand to till, with fine to coarse sands
covering most of the area.
Somers and Josephson (1968) published a paper based upon mechanical
analysis of the same samples described by Ayers (1967). They include a
map of sediment distribution patterns which is essentially identical to
Figure A-7 , except that they have lumped Ayers' several classes of sand,
silt and clay under these three simple headings. For the area of our
concern conclusions remain the same; bottom sediments are "hard" over
most of the area, consisting largely of sand with small areas of gravel
and till.
A--25
-------
Explanation of symbols used in Figure A-7
on facing page. From Ayers (1967).
No Sample (Hard Bottom?)
Till
V_/ Gravel (Granules to Boulders)
Coarse to Very Coarse Sand
• Medium Sand
LJ Very Fine to Fine Sand
Silty Sand
>J( Clayey Sand
Sandy Silt
Sandy Clay
Silty Clay
V Clayey Silt
^ "Clay"
A-26
-------
87*50" 87*40' 87*30' 87*20" 87*10'
4Z*
10'
42*
00"
40
LAKE MICHIGAN
SURFICIAU BOTTOM SEDtMf NTS
CONTOUR INTERVAL 60 FEET
OAR
_L
_L
_L
_!_
_L
87*50" 87*40" 87*30" 87*20" 87*10" 87*00" WSff 86*40
86*tO"
Figure A-7. Distribution of surficial sediment types in the southern end of Lake Michigan.
Symbols are explained on previous (facing) page. Figure taken from Ayers (1967).
-------
Somers and Josephson (1968) also plotted phi median diameter and
measures of deviation, and skewness of phi (Inman, 1952) against depth
for all transects. In the Chicago-Gary area, in contrast to many parts
of the lake, there was no consistent relationship between these measures
and depth of distance from shore.
Mozley and Alley (1973) present a map of the distribution of sedi-
ment types in the southern end of the lake which is based on Ayers (1967)
data as well as additional observations of their own (Fig. A-8). Their
map gives less detail and differs in some important respects from that
of Ayers (1967). For example, Mozley and Alley indicate that gravel is
the dominant sediment type in the inshore area north and west of Gary,
Indiana. Ayers' map shows a good deal of sand in this area. Perhaps
Mozley and Alley felt that the greater detail of Ayers map was unwarranted
since they found that the sediment type at many stations varied from
cruise to cruise. For example at one station about 30 km off Gary,
Indiana the recorded sediment type was gravel once, fine sand once, silty
sand five times, and sandy silt once. This observation may simply indi-
cate lack of precision in locating the station or may reflect periodic
movements of surficial sediments in the shallower waters of southern
Lake Michigan. The generally poor sorting observed by Somers and
Josephson (1968) and comments by these authors and Hough (1935) appear
to support the latter explanation. Certainly there are many important
sources of sediment along the southern shore of the lake, yet fine sedi-
ments are rarely found at shallower depths. Poor sorting and patchiness
of sediments in the southern basin may result from a seasonal cycle
involving large inputs of finer sediments with spring runoff and temporary
deposition of this sediment in shallow areas followed by resuspension and
A-28
-------
Waukegan
Benton Harbor
VO
South
Haven
SEDIMENT CODES
4
Kilometers
Gory
.
A
» • • • i
» » • • i
Figure A-8. Distribution of sediment types in the south end of Lake Michigan according to
Mozley and Alley (1973). Sediment codes: 1 = gravel, pebbles; 2 = coarse or medium sand;
3 = clean fine sand; 4 = silty sand; 5 = sandy silt; 6 = silt, clay. Figure taken from
Mozley and Alley (1973).
-------
transport to greater depths by storm currents in fall and winter.
The distribution of sediment types in the Calumet-Indiana Harbor
area (Fig. A-9 ) reflects substantial inputs of finer materials by the
streams. The silts and clays are found largely at or just off stream
mouths. Other areas have coarser sediments, presumably because of
removal of finer materials by lake currents.
A-30
-------
KEY:
Grovel
Coarse to Medium Sand
Fine Sand
Silt & Clay
Figure A~9. .Distribution of sediment types in the Calumet-Indiana
Harbor area; «'• Based on unpublished data obtained by the FWPCA in 1967.
A-31
-------
Evidence of Human Contamination of Sediments
Some of the bottom samples examined by Somers and Josephson (1968)
and Mozley and Alley (1973) had an oily odor. This may result from
dumping of petroleum products in the lake either directly or through the
open-lake disposal of dredging spoils from harbors. Other samples
examined by Somers and Josephson (1968) contained cinders, wood, ceramic
tile, rusty nails, and other evidence of recent dumping. These authors
did not give any further indication of the location or extent of affected
sediments.
Oil pollution in Lake Michigan occurs primarily at the southern end,
originating in the Calumet area. Indiana Harbor canal sediments have
been found (June 1967) to have oil and grease contents ranging from 3 to
17% (Johnson ^t al. 1968). The FWPCA (1968) reported that waste discharges
in harbors along the southern shore resulted in sediments which were
inhibitory to the establishment of benthic organism populations. They
referred specifically to oil, grease, and allied petroleum wastes as the
source of the problem.
Mozley and Alley (1973) reported that comparison of oily samples
and non-oily samples from the same Lake Michigan stations revealed no
strong or consistent effect on the benthos, though in a few such cases
oligochaetes made up a larger percentage of the fauna in the oily sample.
Gannon and Beeton (1969, 1971) pursued this problem through labora-
tory investigations, using sediments from nine Great Lakes harbors. In
selectivity tests Pontoporeia affinis avoided Indiana Harbor sediments
and displayed a lower preference for Calumet Harbor sediments when com-
pared to sediments from an unpolluted harbor and the open lake. In
viability tests, Calumet and Indiana harbors were among the five harbors
A-32
-------
whose sediments caused greatest mortality of £. affinis. Gannon and
Seeton (1969, 1971) concluded that sediments from these harbors were so
toxic that dredging spoils should not be dumped in the open lake. While
they did not attempt to identify the toxic substance(s) involved, the
Calumet and Indiana Harbor samples used in the tests were obviously
polluted with oil.
Shimp, Leland and White (1970) and Shimp e£ al. (1971) have studied
the vertical distribution of trace elements in cores taken in southern
Lake Michigan. In many cores, concentrations of bromine, chromium,
copper, lead and zinc, were much higher in the upper few centimeters than
at greater depths in the cores. Patterns of concentration with depth
suggest continuing increases in deposition of these trace elements. On
a geographical basis, highest concentrations in the most recent sediments
were generally off Grand Haven or Benton Harbor, Michigan. Except for
zinc, and chromium at a few stations, concentrations in the Calumet area
were not particularly high when compared to the southern basin as a whole.
Shimp and co-workers (1970, 1971) did not look for biological effects of
accumulation of these trace elements, and other research on the benthos
of the open lake has given no indications that any have built up to
harmful levels.
In the immediate area of Calumet and Indiana Harbors there are high
concentrations of many pollutants, several of which could have been
responsible for the toxicity observed by Gannon and Beeton (1969, 1971).
The distribution pattern strongly suggests that the pollutants enter in
the two tributary streams (Fig. A-10).
A-33
-------
-------
BENl'HIC MACROINVERTEBRATES
Abundance of Major Components of the Lakejlichigan Fauna
Numerous studies of the benthos of Lake Michigan have shown that the
fauna is dominated by amphipods (Pontoporeia affinis) and oligochaete
worms (most importantly Stylodrilus heringianus; Hiltunen 1967, Howmiller
1972). Sphaeriid clams are third in abundance (two genera; 23 spe-
cies). Other invertebrates; mysids, isopods, leeches, snails, flatworms,
roundwormsj and midge larvae occur in small numbers.
Many of the benthic studies done on the lake have focused on the
distribution and abundance of the dominant elements of the fauna. In an
extensive investigation, involving sampling in several months on five
cross-lake transects, Powers and Robertson (1965) estimated average numbers
of amphipods, and of oligochaetes, and the ratio of the two. Their data
indicate that the southern portion of the lake has somewhat lower densities
of amphipods, much larger numbers of oligochaetes (Fig. A-11),, and amphipod/
oligochaete ratios much lower (Fig. A-12)than in other regions of the
lake. Verber (1966) cites data of Cook (1965) which reflect similar
distributions and says that Cook has reported a significant change in the
amphipod/oligochaete ratio in the last 30 years. Robertson and Alley
(1966) compared the abundance of dominant benthic organisms in 1964 with
the data of Eggleton (1931, 1932). They found 1.5 times more Pontoporeia,
2.6 times more oligochaetes, and 4.3 times more sphaeriids in 1964. Thus
the amphipod/oligochaete abundance ratio decreased, on the average, to
1
Cook's report was not available to me, and is apparently unpublished.
A-35
-------
Wisconsin
Illinois
Michigan
Indiana
•gs
G I cfl
•H I -H
rH 'TJ
rH 0
Figure A-ll. Average numbers of oligochaete worms, 1000's/m , August -
November 1964, in the benthos of Lake Michigan south of Milwaukee-Grand
Haven. (After Powers and Robertson 1965).
A-36
-------
Wisconsin
Illinois
Michigan
Indiana
Figure A-12. Average distribution of the ratio of numbers of amphipods
to numbers of oligochaetes, August - November 1964, in the benthos of
Lake Michigan 'south of Milwaukee-Grand Haven (After Powers and Robertson
1965).
A-37
-------
about 0.6 of the value in 1931-32.
There seems to be an implication in the comments of Verber (1966)
that the amphipod/oligochaete ratio has significance as an indicator of
environmental quality, and that the reported change in this ratio reflects
some deterioration of the lake. This opinion is given support by the
results of Robertson and Alley, since a decrease in the value of the ratio
occurred concurrently with an increase in standing crop of benthos which
probably reflects increased productivity of the lake. This is rather
indirect reasoning, however, and we have no understanding of why the
dominant oligochaetes of the lake should increase relative to amphipods
as a result of eutrophication, especially when we consider the fact
that Stylodrilus is generally considered to be an indicator of oligotrophic
conditions in the Great Lakes.
A report by the Federal Water Pollution Control Administration (FWPCA
1968a) summarized studies done in 1962-1964. They found extensive areas
of high oligochaete ("sludgeworm") abundance off southern and southwestern
2
shores of the lake. They considered worm densities exceeding 1000/m to
be indicative of pollution (Wright 1955, Surber 1957) and, using this
criterion, identified a 2100 square mile area of polluted conditions in
southern Lake Michigan (Fig. A-13). Pollution of this large area was
attributed to inputs from the large metropolitan areas on the southern
and southwestern shore (FWPCA 1968a).
Shallow areas near the southern tip of the lake had lower numbers of
amphipods than comparable areas along eastern and western shores. The
area of low amphipod density coincided, at least partly, with areas which
held >2000 oligochaetes/m2 (Fig. A-14 ,FWPCA 1968a).
A-38
-------
I • "•' 1,-f ' '' I
Grand v ',
Haven (:; '
POLLUTED , 1000- 2000/m Z
VERY POLLUTED, OW 2000/tn Z
FIGURE I
GREAT LAKES - ILLINOIS j
RIVER BASINS PROJECT
SLUDGEWORM POPULATION
NUMBER PER SQUARE
METER
U.S DEPARTMENT OF THE INTERIOR
FEDERAL WATER POLLUTION CONTROL AOMIN
Great Lake* Region Chicago .llttrote
Figure A-13. Abundance of oligochaete worms in the benthos of southern
Lake Michigan, 1962 (From FWPCA 1968a).
South.: :..'•.•:!.••
Havcoj- -:. •!=' p.V
OVER 1500/m2
FIGURE 2
GREAT LAKES - ILLINOIS
RIVER BASINS PROJECT
SCUD POPULATIONS
NUMBERING GREATER THAN
1500 PER SQUARE METER
U S. DEPARTMENT OF THE INTERIOR
FEDERAL WATER POLLUTION CONTROL ADMIN
Grant Lakes Region Chicago .Illinois
Figure A-14. Abundance of amphipods in the benthos of southern Lake
Michigan, 1962 (From FWPCA 1968a).
A-39
-------
Mozley and Alley (1973) present a. more detailed picture of the
differences in numbers of these organisms in the central and southern
basins of the lake (Table A-1). Average abundance of amphipods was
greater in the central basin at all depths but the difference was greatest
at depths of 40 m or less. Oligochaetes were more abundant in the
southern basin at depths of 40 m or less. At greater depths (40 - 140 m)
there was no striking difference between the two regions of the lake
(Table A-l) .
Areas where Mozley and Alley (1973) found average abundances of
1000 or more oligochaetes per square meter were approximately the same
as those found by the FWPCA (Fig. A-13). They found, however, much larger
areas of high amphipod abundance and attribute the difference to the fact
that different samplers were used. The FWPCA used the Petersen grab
while Mozley and Alley used a Ponar. The Petersen, as built and sold
in the U.S., has solid surfaces in the tops of the jaws and thus a
hydraulic disturbance forms ahead of the grab as it is lowered. Such a
hydraulic disturbance ("shock wave") can serve as a directional signal
allowing very motile animals to escape and can even blow away fine
surficial sediments with their resident animals (Wrigley 1967). Since
amphipods live near the sediment water interface ("epifauna") and are
capable of swimming, they would understandably be more seriously affected
by a hydraulic disturbance than the slowly burrowing oligochaetes which
are more typically found deeper in the sediments ("infauna"). The
Ponar, having screened tops in the jaws, creates less of a hydraulic
disturbance and can thus provide a more realistic estimate of amphipod
abundance.
A-40
-------
TABLE A-l. Comparison of the abundances of Amphipoda and
Oligochaeta between the central and the southern regions of
Lake Michigan by depth zones, 1964-67. X « mean; S- = standard
error; N = number of observations (single grab samples) (From
Mozley and Alley, 1973).
Taxon
Amphipoda
Oligochaeta
Depth
Zone
0-20m
21-40m
4l-60m
61-140m
0-20m
21-40m
4l-60m
. 61-140m
Central Region
6
8
6
3
1
1
2
X
,380
,477
,876
,353
,389
,460
,509
520
Sx
828
286
294
86
727
83
307
29
N
12
199
116
286
10
196
91
227
Southern Region
-'
2,
4,
4.
3,
2,
3,
2,
^M
X
544
264
858
137
898
411
171
720
Sx
216
301
177
86
346
281
109
49
N
235
160
164
250
229
157
163
248
A-41 .
-------
While Mozley and Alley (1973) did find higher numbers of oligochaetes
in the southern basin than in the central basin (at depths < 40 m), they
2
failed to confirm the picture of generally extreme abundance (> 9000/m )
reported by Robertson and Alley (1965). Mozley and Alley (1973) analyzed
data from many more stations in the southern basin and we may take theirs
as the more representative of the two sets of data.
Mozley and Alley also found that, generally, benthic biomass at a
given depth declined south of the latitude of Benton Harbor. This indi-
cates that increase in oligochaetes did not equal the geographical
decrease in amphipods. They suggest that this is because of the prepon-
derance of coarse sediments in this area. Since oligochaetes prefer
fine sediments, the effect of the large areas of sand and gravel would
counteract the tendency for higher pollution levels to elevate oligochaete
abundance. Mozley and Alley (1973) suggest that interuption of the band
of high oligochaete abundance shown in the Chicago area by the FWPCA
(Fig. A-13) was due to the frequent occurrence of coarse sediments in
that area, rather than to lower levels of pollution. They conclude that,
because of the lack of permanent deposits of fine sediments and the dif-
ficulty of collecting grab samples from rocky bottoms, oligochaete
abundance cannot serve well as an indicator of pollution in the Chicago
agea.
In the discussion so far, we have made the point that the abundance
of the two major elements in the benthic fauna; amphipods and oligochaetes,
and the ratio of their abundances are considered to have some value as
indicators of environmental quality. There is evidence that abundance
of both these groups has increased, and the ratio amphipods/oligochaetes
has decreased in recent years; presumably indicating that eutrophication
A-42
-------
is proceeding at a perceptable rate.
We have seen, however, that attempts to estimate the abundance of
these organisms is affected by the selection of sampling gear, and that
physical features of the environment may modify the effect of a given
level of pollution or eutrophication upon abundance of benthos. Further-
more, whatever indicator value exists in estimates of amphipods, oligo-
chaetes, or their ratio, it will certainly not have the same significance
in nearshore waters, bays or harbors as in the open lake. This is
because, in bays and harbors, amphipods other than Pontoporeia are likely
to occur and oligochaetes will be represented largely or entirely by
tubificids, some of which are exceedingly tolerant of pollution. In the
open lake Pontoporeia is the only amphipod and Stylodrilus accounts for
most of the oligochaete fauna. In short, attempts to assess environmental
quality through numbers of organisms of major groups are limited in
sensitivity and in scope.
The Value of Studies at the Species Level
Analysis of the benthic fauna at the species level appears to offer
much more sensitivity for detecting and documenting environmental change
than the enumeration of individuals at higher taxoncmic levels. I am
not referring here to indicator species in the sense that simple presence
or absence has any significance. Rather it is the relative abundance of
species varying in pollution tolerance that offers greatest promise in
comparing environmental quality between locations or over time in a
particular area. To do this correctly requires identification of all
organisms to the fullest extent possible. Judgements may then be made
on the basis of the proportion of each species and what is known of its
A-43
-------
environmental requirements. It is not satisfactory to simply list
numbers of pollution tolerant and intolerant organisms. Without identi-
fication to the species level, reinterpretation of the data on the basis
of new knowledge of environmental requirements is not possible. Reports
with results expressed in this manner also leave the impression, probably
generally correct, that the organisms were, in fact, not really identified.
In practice, few studies have attempted complete identification of
all organisms found. This is because most studies are done by one or a
few people whose taxonomic competence is limited. Also, some groups are
less valuable than others for these purposes; because they lack ecological
differentiation in the Great Lakes or because we have, as yet, a very
incomplete knowledge of their environmental requirements.
As previously mentioned, there is general agreement that Pontoporeia
affinis is a clean water organism. It is also commonly considered to be
a cold stenotherm (Henson 1966), although it exists in Lake Michigan at
temperatures ranging from 1-19 C (Alley 1968). While high densities of
Pontoporeia may be considered good evidence of unpolluted conditions, low
densities do not necessarily reflect pollution but may be related to
other environmental factors (Alley 1968) or, as pointed out earlier, can
simply reflect a poor choice of sampling gear. Other species of amphipods
are very rare in the lake, but may occur in bays or harbors; e.g.
Howmiller and Beeton (1971) reported Hyalella azteca, Gannnarus fasciatus,
and Crangonyx sp. as well as P_. affinis from Green Bay.
Sphaeriid clams are an important group in the benthos of the lake.
At least 23 species are present (Henson and Herrington 1965, Robertson
1967) but little use has been made of them in environmental surveillance.
A-44
-------
Chironomidae larvae have long been employed in the classification
of aquatic habitats (cf. Brundin 1949, 1958) but have been little utilized
in this respect in Lake Michigan. This is probably because they are a
quantitatively unimportant element in the benthos of the lake; comprising
about 1% of the deep water benthos (Powers and Alley 1967) and little
more (4%; Mozley and Garcia 1972) of shallower benthic assemblages. In
bays and harbors, however, they constitute a larger proportion of the
fauna (26% in Green Bay; Howmiller and Beeton 1971) and may play a useful
role in environmental assessment in these situations (Howmiller and Maass
1973).
Oligochaete worms appear to offer particular promise for the bio-
assessment of environmental quality in Lake Michigan. They are found in
bottom samples from all parts of the lake, including bays and harbors,
and, except on very coarse substrates, are relatively abundant. Further-
more, more than forty species are known from the lake, and these have a
considerable range of environmental preferences. Recent studies (Hiltunen
1967, Brinkhurst, Hamilton and Herrington 1968, Howmiller and Beeton 1970)
of species distributions with respect to water quality have allowed a
classification of some species according to their indicator value (Table
A-2).
Benthic Studies in the Calumet Area
Against the background of some general knowledge of the Lake Michigan
bottom fauna, and of the differences in utility of studies at various
taxonomic levels, we can review the few studies done to date in the
Calumet area.
A-45
-------
Table A-2. Classification of some Lake Michigan oligochaetes according
to the degree of enrichment or pollution of the environment (from Mozley
and Howmiller 1973).
I. Largely restricted to unpolluted
oligotrophic situations
("saprophobes").
Stylodrilus heringianus
Pelvoseolex variegatus
P. superiorensis
Lirmodnlns pvofundioola
Tubifex kessl&rn.
Rhyacodrilus eooeineus
H. man tana
III. Species tolerating extreme
enrichment or organic pollution
(saprophiles and saproxenes,
see also IV).
Limnodrilus hoffmeisteri
L. udekemLanus
L. angustipenis
Tubifex tubifex
II. Species characteristic of
areas which are mesotrophic
or only slightly enriched.
Peloscolex ferox
P. freyi
Ilyodrilus templetoni
Potamothrix moldaviensis
P. vejdovskyi
Aulodrilus spp.
IV. Species restricted to areas
of gross organic pollution
(saprobionts).
Limnodrilus eervix
L. claparedeianus
L. maiffneensi-s
PelosGolex multisetosus
A-46
-------
The FWPCA (1968a) reported that sludgeworms and sphaeriid clams were
dominant in the benthos along the southern shore of the lake (Calumet
Harbor to Burns Ditch). They felt that the area was "extensively degraded
biologically in degrees ranging from severe near Indiana and Calumet
Harbors to less severe near Burns Ditch."
According to the FWPCA (1968a) the degradation of the benthic
community extended out as far as twenty miles and the total area affected
2
by wastes discharged from the Chicago-Calumet area covers 2100 mi . This
latter judgement is based on the high sludgeworm abundance in the area
shown in Fig.A^12. The relatively low population density of amphipods
in the southern tip of the lake was said to be caused by toxic wastes
discharged in the Calumet area. This, of course, is simply speculation.
As has already been indicated, the sampling gear used by the FWPCA will
almost certainly underestimate amphipod abundance, and the effectiveness
of their sampler (Petersen grab) varies greatly with depth and substrate
type (Beeton, Carr and Hiltunen 1965). The lower density of amphipods
is also possibly a reflection of the shallowness of this region of the
lake and the normal depth distribution of Pontoporeia (Alley 1968, Mozley
and Alley 1973). Lastly, the FWPCA (1968a) provides no evidence that
amphipods are being affected by any toxic agent nor that any waste addi-
tion from the Calumet area is present over such a large area at levels
toxic to any organism.
The FWPCA (1967) reported briefly on examination of a few bottom
samples taken in Calumet Harbor, Indiana Harbor, and tributary canals in
1965 and 1966. Results are not quantitative and organisms are identified
only to major groups (Table A-3). Nevertheless, they clearly convey the
impression that the harbors and immediate tributaries are severely
A-47
-------
TABLE A-3. Benthic invertebrates found at stations in Calumet Harbor,
Indiana Harbor and tributary canals in 1965 and 1966 (From FWPCA 1967).
Area
Grand Calumet River
ii ti it
Indiana Harbor Canal
ii 11 11
Indiana Harbor Canal
it ii n
Indiana Harbor
n n
Little Calumet River
n n n
Calumet Harbor
n 11
FWPCA
Station
Number
1
1
2
2
3
3
5
5
8
8
13
13
Date
1965
1966
1965
1966
1965
1966
1965
1966
1965
1966
1965
1966
Benthic Invertebrates
None
None
None
Sludgeworms
None
None
Sludgeworms
Sludgeworms
2
Sludgeworms , bloodworms ,
mayflies
Snails , bloodworms
3
Fingernail clams
Fingernail clams, sludgewon
1 23
tubificid oligochaetes, chironomid larvae, sphaeriids
A-48
-------
polluted. They do not, however, offer the possibility of detecting minor
improvement or degradation of the environments as would quantitative data
at the species level.
Gagler (1973) examined bottom sediments collected from the Little
Calumet River and Burns Ditch. He found no benthos in 12 of 13 samples
and only sludgeworms in the other. Chemical analyses indicated highly
polluted sediments in these waterways as one would be lead to believe
from general paucity of benthic organisms.
Howmiller examined bottom samples taken in shallow water at Bailly,
Indiana. Benthic invertebrates were absent, or present in only low abun-
dance, at many stations. This was attributed to the fact that most
stations were on hard sand bottoms which, in shallow water and under
periodically turbulent conditions, are a physically harsh environment.
At only one station out of eight did a sample from a sand bottom in water
less than 3 m depth contain benthic invertebrates. Where the bottom
contained some silt, animals were found even though the water was only
1.5 m deep. Animals occurred at nine of eleven stations with depths
exceeding 4 m.
Oligochaete worms of the family Tubificidae accounted for 52% of
the invertebrates found. These included seven recognizable taxa; Aulodrilus
pluriseta, Limnodrilus cervix, a form morphologically intermediate between
L_. cervix and L_. claparedeianus, L^. hoffmeisteri, Peloscolex multisetosus,
Potamothrix moldaviensis, and P_. vejdovskyi, and a large proportion of
unidentifiable sexually immature forms (Table B-4). The worm fauna is
Howmiller, R. P. 1970. A Report on Benthic Invertebrates from the
Bailly, Indiana Region of Lake Michigan. Unpubl. Kept, to Industrial
Biotest Laboratories, Inc.
A-49
-------
thus composed of a mixture of forms tolerant of enrichment or pollution
and some normally restricted to heavily polluted areas (Table A-3).
Sphaeriid clams were abundant at two stations and small numbers of
chironomid larvae (Chironomus cf. attenuatus, and Cryptochironomus cf.
digitatus) occurred at most stations. Leeches (Helobdella stagnalis)
and amphipods (Pontoporeia affinis) were present in low numbers at a few
stations.
It was concluded that the bottom fauna of this inshore region was
dominated by forms characteristic of eutrophic regions, but not of highly
polluted regions, of the Great Lakes.
2
Howmiller also studied the oligochaete fauna of the Calumet and
Indiana Harbor region. Specimens examined were from bottom samples taken
by personnel of the Metropolitan Sanitary District of Greater Chicago in
December 1967 (16 stations) and August 1968 (23 stations). The collections
included eleven species of oligochaetes.
Table A-4 compares the composition of the oligochaete fauna in the
Calumet-Indiana Harbor region with that in some other shallow areas of
Lake Michigan. The comparison suffers from the fact that the studies
differed in terms of the size of area, depth range, number of stations
and samples, and in the time of the year in which samples were taken.
Also, in each case, the areas studied are not homogeneous in sediment and
water quality and each includes considerable pattern in terms of worm
species distribution. Nevertheless, marked contrast in the composition
of these faunas is obvious and correlates well with what we otherwise
know of environmental quality in these areas.
2
Howmiller, R. P. 1969. The Oligochaeta of the Indiana Harbor-Calumet
Harbor Region of Lake Michigan. Unpubl. Rept. to Metropolitan Sanitary
District of Greater Chicago.
A-50
-------
TABLE A-4. Composition of the oligochaete fauna and relative abundance
(percent of total oligochaetes) of species in some shallow areas of Lake
Michigan.
3
Species Calumet-Indiana
Dec. '67 Aug. '68
Stylodrilus heringianus *
Dero digitata
Nais elinguis *
Slavina appendiculata
Uncinais uncinata
Aulodrilus americanus * *
A. pigueti
A. pluriseta 4.8 *
Ilyodrilus temple toni
Limnodrilus angustipenis
L. cervix-claparedeianus 1.1 1.4
L. hoffmeisteri2 23.3 12.8
L . prof undicola
L. udekemianus 2.8 *
Peloscolex ferox
P. freyi *
P. multisetosus 13.1 3.0
P . variegatus
Potamothrix moldaviensis *
P. vejdovskyi * *
Tubifex ignotus
T. tubifex
Undetermined immatures;
with hair chaetae 1.1 *
without hair chaetae 52.9 78.8
*
indicates that species was present but at
percent .
**
species was present but quantitative data
Waukegan Benton
Bailly4 Green Bay5 -Zion6 Harbor7
Sept. '70 May '67 1970-71 July '70
35.0 51.0
*
*
*
**
* ** *
*
* *
1.1 **
*
4.3 3.2 ** *
* 21.8 ** 21.8
** *
* **
*
2.6
* 8.1
** *
9.8 * ** 2.1
4.3 **
**
* **
6.1 4.6 ** 1.7
74.2 56.8 ** 18.5
relative abundance of less than one
are not available.
intergrades or morphological intermediates.
Includes counts of L_. spiralis, a species recognized by some Great Lakes
investigators but synonomized with JL. hoffmeisteri by Brinkhurst (1965).
A-51
-------
The Calumet-Indiana Harbor fauna is dominated by Limnodrilus
hoffmeisteri. Mature individuals of this species comprised 23.3% of the
December 1967 samples and 12.8% of the August 1968 samples. Like some
other tubificids, L_. hoffmeisteri cannot be positively identified in the
immature condition. Immature L^. hoffmeisteri are thus included among
the undetermined immatures without hair chaetae (52.9% in Dec., 78.8% in
Aug., Table A-4). Species in these collections which, as immatures,
appear similar to immature L_. hoffmeisteri are other Limnodrilus species,
Peloscolex freyi and Potamothrix moldaviensis. Since these are relatively
uncommon as mature specimens in the Calumet-Indiana Harbor collections,
we can safely assume that almost all the immatures without hairs are L_.
hoffmeisteri. Thus this species, which is tolerant of extreme pollution
(Table A-2), comprises approximately 75-90% of the worm fauna in the
Calumet-Indiana Harbor region. Second in relative abundance is Peloscolex
multisetosus, largely or entirely restricted to areas of gross organic
pollution in the Great Lakes (Table A-2). The composition of the worm
fauna in this region is obviously much like that in Lower Green Bay
(Table A-4), an area which vies with the Calumet area for the distinction
of being the most severely degraded portion of Lake Michigan (Howmiller
1971, Howmiller and Beeton 1970, 1971).
Footnotes to Table A-4 (cont.)
3
From data of Howmiller (1969); see footnote p. A-49 .
4
From data of Howmiller (1970); see footnote p. A-50-
5 From data of Howmiller (1971).
From data of Orenstein, Larson and Lamble (1971).
From data of Mozley and Garcia (1972).
A-52
-------
In contrast, the most common species in the samples from the Bailly
region is Potamothrix moldaviensis (9.8%; Table A-4). Doubtless many of
the numerous undetermined immatures without hairs also belong to this
"mesotrophic" species. The presence of £. vejdovskyi in substantial
numbers also indicates that this area is not grossly polluted. From the
relative abundance of Limnodrilus cervix-claparedianus we can surmize
that there is some patchiness within the area studied and that there are
places where sediments resemble those found in grossly polluted regions.
The high relative abundance of Stylodrilus heringianus (a saprophobe,
Table A-2) indicates much cleaner conditions in the Waukegan-Zion and
Benton Harbor study areas. Nevertheless, Limnodrilus hoffmeisteri
accounts for over 20% of the fauna at Benton Harbor. This, again can be
attributed to patchiness (commented upon by Mozley and Alley, 1973) and
the fact that an environmental gradient exists within the area studied.
Some of the regional variation in composition of the worm fauna
within the Calumet-Indiana Harbor area can be seen in Figs.A-15 through
A-20 which are taken from the report by Howmiller.
Figure A-15shows the relative abundance of worms of the genus
Limnodrilus, including immatures without hair chaetae, at stations sampled
in December 1967. Figure A- 16is a similar plot of data from the survey
of August 1968.
In this area, the genus includes only species tolerant of, or
restricted to, polluted conditions. The distributional pattern (Fig. A-15,
16) clearly reflects the importance of the Indiana Harbor as a source of
pollution in this part of the lake. It is difficult to know whether any
See footnote on p. A-50.
A-53
-------
Ul
Figure A-15 . Relative abundance of worms of the genus Limnodrilus
(percentage of all oligochaetes) at stations of December 1967 survey.
-------
Oi
Ui
Figure A-16. Relative abundance of worms of the genus Limnodrilus
(percentage of all oligochaetes) at stations of August 1968 survey.
-------
importance should be ascribed to the difference between the two years,
viz. the apparently larger area of very high relative abundance in August
1968. When comparisons are made between years, care should be taken to
replicate exact station locations, the season of sampling, and methodology
(Howmiller and Beeton 1971). At least the first two criteria are not met
in this case, and so the difference between years may be an artifact or
may be caused by normal seasonal variation in the numbers of some taxa.
In both 1967 (Fig. A-17 and 1968 ( Fig. A-18) the greatest relative
abundance of Peloscolex multisetosus was found at some distance from the
two polluting inflows and on sediments of "low" or "moderate pollution"
(cf Fig. A-10) . This is in agreement with studies elsewhere (Brinkhurst
1969, Howmiller and Beeton 1970) which have showed that, while P_.
multisetosus is favored by pollution, it is not as extremely tolerant as
Limnodrilus hoffmeisteri or L_. cervix-claparedeianus.
Worms of the genus Aulodrilus, characteristic of slightly enriched
areas in the Great Lakes, are here present at a low relative abundance
and are conspicously absent from stations near Indiana Harbor (Fig. A~19>
A- 20) .
Abatement of pollution in this area would be expected to be followed
by a decrease in the relative importance of Limnodrilus spp., expansion
of the areas occupied by P_. multisetosus and Aulodrilus, increase in
relative importance of these and some other taxa currently less numerous
(Table A-4), and invasion by other species not currently found in the
area. On the other hand, worsening of conditions would eliminate P_.
multisetosus and Aulodrilus completely and result in a fauna consisting
solely of L_. hoffmeisteri and L_. cervix-claparedeianus. Areas near the
Indiana Harbor outlet would probably become devoid of macrobenthos. It
A-56
-------
f
Ul
•J
Figure A-17 . Relative abundance of Peloscolex multisetosus (percentage
of all oligochaetes) at stations of December 1967.
-------
Oi
00
ooo
Figure A-18. Relative abundance of Peloscolex multisetosus (percentage
of all oligochaetes) at stations of August 1968.
-------
Aa - Aulodrilus americanus
Apl - A. pluriseta
Figure A 19. Relative abundance of worms of the genus Aulodrilus
(percentage of all oligochaetes) at stations of December 1967.
-------
I
cr«
o
Figure A-20. Relative abundance of worms of the genus Aulodrilus
(percentage of all oligochaetes) at stations of August 1968.
-------
can thus be seen that this study of the composition of the worn fauna
can serve as a valuable baseline from which to measure future changes in
environmental quality in this area. Analysis of the worm fauna at the
species level becomes particularly necessary when, with increasing levels
of pollution, other invertebrates are eliminated while worms become an
increasingly abundant part of the fauna (cf. Carr and Hiltunen 1965,
Howmiller and Beeton 1971).
Effects of Benthos on Sediment-Water Exchange
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 water. These effects may be
caused by mechanical overturn of sediments, chemical transformation of
sediment within the gut of the animal, or by irrigation of burrows with
consequent changes in the stratification of redox potential.
This area has been so little studied that we have no good estimate
of the importance of these processes under various natural conditions.
However, the studies which have been published give an indication that
the subject should not be ignored in programs concerned with pollution
abatement or eutrophication control. For example, concentrations of
pollutants or plant nutrients may not change in direct response to changes
in inputs if the new conditions alter the rate at which invertebrates
cause release of the substance(s) from the sediments.
Various authors have attempted to estimate the rate at which tubificid
oligochaetes overturn sediments. Results have been variable but indicate
2
that it may range to 6-12 kg/m /yr (Lundbeck 1926). Clearly, mixing of
this magnitude could have substantial effects on chemical processes.
A-61
-------
Tubificids (Zvetlova 1972) and chironomid larvae (Rossolimo 1939,
Edwards 1958) have been shown to increase the rate of oxygen consumption
by sediments.
Howmiller (unpublished) conducted an experiment in which Limnodrilus
2
hoffmeisteri, at densities equivalent to 10,000 and 50,000 /m , were
placed in Milwaukee Harbor mud and covered with filtered Lake Michigan
water. Three sets were run; at high and low oxygen concentrations and
under anaerobic conditions. In all cases the water increased more in
phosphate concentration than it did in comparable controls lacking worms.
Jernelov (1970) showed that tubificids, and also the clam Anodonta,
cause an increase in the depth from which mercury is released to the
overlying water. Yealy (1971) studied uptake of methyl-mercury and
effects on release to the water by three common Lake Michigan inverte-
brates; Stylodrilus heringianus, Pontoporeia affinis, and a sphaeriid
clam. Results suggested that the organisms enhanced the release of
mercury and Yealy believed that Stylodrilus played an especially import-
ant role in this respect. It had the highest uptake of methyl-mercury of
the three species studied.
Review of this subject has been cursory but an exhaustive treatment
would bring us to the same conclusion, viz? research has been insufficient
to provide generalizations but the subject seems an important one for
consideration of nutrient and pollutant pathways. This is especially
true in many parts of the Great Lakes, such as the Calumet area, where
the sediments contain high concentrations of nutrients and pollutants
(Fig. A-10).
A-62
-------
Recommendations for Applied Research
on the Benthos of the Calumet Area
Species Distributional Patterns
An earlier section was devoted to discussion of the use of species
distributional patterns, and the relative abundance of species with
indicator value, in documenting the state of the environment. Another
section reviewed, existing knowledge of this sort for the Calumet area.
The major short-coming of this study was that it covered only a restricted
area; an area obviously grossly polluted with inputs from Calumet and
Indiana Harbors.
There seems little point in duplicating this study in the near
future as we b,ave little reason to believe that environmental conditions
in the area have undergone substantial change. However, a survey is
needed whiph will extend the area investigated? to determine the areal
extend of degradation of the benthic environment in the Calumet area.
The only study which has attempted to provide this information (FWPCA
1968a) is woefully inadequate because it employed a sampling device
known to be very ineffective, because organisms were not identified to
species, and (while station locations are not given in the report) it
appears to have taken few samples in the Calumet area.
Following is a proposal for a sampling plan which would pro-
vide a far better picture of the benthic communities in the Calumet area.
Samples should be taken in triplicate on a (60°) diagonal grid (Fig. A-21)
a pattern which gives the most even coverage of the area and allows
calculation of indices of similarity between benthic assemblages over
uniform distance. The usefulness of an index of similarity between
A-63
-------
assemblages at adjacent stations is in providing a numerical value
representing quantitative and qualitative change in the benthos and thus
change in environmental conditions. The value used should take into
consideration both the number of species in common and differences in
equitability (evenness of distribution of individuals among species).
A measure of "overlap" based on information theory may be suitable for
the purpose (Horn 1966).
Needless to say, this will require species identification of all
organisms, and I hasten to recommend that quantitative species lists, as
well as exact locations, be presented in any report on the survey.
Altogether too often it is impossible to reproduce an earlier study, or
to analyze the data in light of new concepts, because the authors give
only their reduced data and we really have no idea of how much of what
was found where.
The Ponar grab is recommended as the sampler of choice for the
Calumet area. It is more effective than the Petersen on hard or soft
substrates (Powers and Robertson 1967), and while less effective than
the Ekman grab on mud (Howmiller 1972) it is at least better than the
Petersen (Powers and Robertson 1967). Since ^he Ponar is used for most
benthic investigations by the Great Lakes Research. Division (Univ.
Michigan) and the Center for Great Lakes Studies (Univ. Wisconsin-
Milwaukee) , the major research groups on the lake, it^s use in the Calumet
area will facilitate comparison of data with a maximum number of other
studies. Two samplers which may initially have great appeal, because
they will obtain a sample from most any kind of substrate, are the Shipek
and orange-peel. These should not be used as they have been shown to be
quantitatively ineffective for biological samples (Sly 1969, Flannagan 1970"
A-64
-------
Figure A-21, The above map was drawn from Lake Survey Chart No. 751.
f - Proposed sampling stations
Compass Headings for possible runs between stations
313 NW* and 133 SE* (along lettered transect line)
213 SW** and 43 NE** (along numbered line)
13 ME*, 193 SSW*, 73 ENE* and 253 WSW* (diagonal)
* On these runs distances between adjacent stations are exactly 2.0 mile
** On these runs distances between stations are ca 3.46 mile
A-66
-------
Benthic samples should be screened immediately using a U.S. Std. No.
30 Mesh (0.565 mm) as this is the mesh most commonly employed in Great
Lakes Studies (Mozley and Howmiller 1973). Residue from the screen should
be preserved immediately with buffered 10% formalin (4% formaldehyde).
Low power magnification should be used in separating organisms from the
screen residue and the most recent monographs used in their identification.
It is perhaps worth pointing out that safe, and efficient fieldwork
requires a seaworthy vessel fitted with a sonic depth finder and naviga-
tional radar. The vessel should have ample deck space, a (powered)
hydrographic winch, and water under pressure piped to the working deck.
The R/V Mysis (Great Lakes Research Division) and R/V Neeskay (Center for
Great Lakes Studies) are examples of suitable vessels for benthic sampling.
A tentative sampling plan, shown in Figure A-2} involves 15 stations
on a two mile diagonal grid. Under favorable weather conditions, and with
a suitable vessel, sampling could be accomplished in a day by experienced
personel.
The proposed plan is, of course, tentative. Preliminary sampling,
or analysis of water quality data, may indicate that some modification
would be desirable. For example, one might wish to expand the area of
investigation, especially in the direction of the usual path of water
originating in the Calumet-Indiana Harbor area.
Effects of Benthos on Chemical Parameters
Attempts at modeling expected changes in water quality should not
ignore the possible importance of benthic organisms in facilitating
chemical transport across the sediment-water interface. In the Calumet
area new effluent standards may result in lower concentrations of toxic
A-65
-------
substances and higher concentrations of oxygen in and near the harbor
areas. This cpuld conceivably allow a great increase in benthic popula-
tions since the sediments, in many places, have abundant organic matter
for them to exploit. Greatly increased populations of burrowing benthic
invertebrates could cause a large difference in the rate at which certain
substances are released from, or bound to, the sediments. This possibility
must be considered in attempts to predict future water quality.
This situation demands research to estimate current rates of sediment-
water exchange of important materials (oxygen, phosphorus, nitrogen com-
pounds, metals). It must also include predictions of effects of antici-
pated water quality changes upon the abundance of benthic invertebrates
and upon their effect on sediment-water interactions. This is a very
complex problem for which basic science has not yet provided the ground-
work. However, the current fiscal situation in basic science seems to
suggest that we have to wait a long time for answers to certain questions.
In such a case basic research must become "applied" in areas where real
or potential problems exist.
A-67
-------
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the depth distribution of macrobenthos in Lake Michigan. Univ.
Michigan Great Lakes Res. Div. Spec. Rept. 30: 112-125.
A-74
-------
Powers, C. F. and J. C. Ayers. 1967. Water quality and eutrophication
trends in southern Lake Michigan. Univ. Michigan Great Lakes Res.
Div. Spec. Kept. 30: 142-178.
Powers, C. F. and A. Robertson. 1967. Design and evaluation of an all-
purpose benthos sampler. Univ. Michigan Great Lakes Res. Div. Spec.
Rept. 30: 126-133.
1968. Subdivisions of the benthic
environment of the upper Great Lakes, with emphasis on Lake Michigan.
J. Fish. Res. Bd. Canada 25: 1181-1197.
Rawson, D. S. 1956. Algal indicators of trophic lake types. Limnol.
Oceanogr. 1: 18-25.
Robertson, A, 1967. A note on the Sphaeriidae of Lake Michigan. Univ.
Michigan Great Lakes Res. Div. Spec. Rept. 30: 132-135.
Robertson, A. and W. P. Alley. 1966. A comparative study of Lake
Michigan macrobenthos. Limnol. Oceanogr. 11: 576-583.
Robohm, R. A. and J. T. Graikowski. 1966. Variables affecting enumera-
tion of bacteria in Lake Michigan waters and sediments. Univ.
Michigan Great Lakes Res. Div. Publ. 15: 140-146.
Rossolimo, L. 1939. The role of Chironomus plumosus larvae in the ex-
change of substances between the deposits and the water in a lake.
Arb. Limnol. Sta. Kossino 22: 35.
Scarce, L. E. 1965. The distribution of bacterial densities in Lake
Michigan. Univ. Michigan Great Lakes Res. Div. Publ. 13: 182-196.
Scarce, L. E. and M. L. Peterson. 1966. Pathogens in streams tributary
to the Great Lakes. Univ. Michigan Great Lakes Res. Div. Publ. 15:
147-154.
A-75
-------
Schelske, C. L. and E. Callender. 1970. Survey of phytpplankton and
nutrients in Lake Michigan and Lake Superior. Proc. 13th Conf.
Great Lakes Res., p. 93-105.
Schelske, C. L. and E. F. Stoermer. 1971. Eutrophication, silica deple-
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1972. Phosphorus, silica, and
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Spec. Symp. Amer. Soc. Limnol. Oceanogr., p. 157-171.
Shimp, N. F., H. V. Leland and W. A. White. 1970. Distribution of major,
minor, and trace constituents in unconsolidated sediments from
southern Lake Michigan. Illinois State Geol. Surv., Environ. Geol.
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Shimp, N. F., J. A. Schleicher, R. R. Ruch, D. B. Heck and H. V. Leland.
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Somers, L. H. aid P. D. Josephson. 1968. Bottom sediments of south-
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A-76
-------
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A-77
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APPENDIX B
THE ECOLOGY OF LAKE MICHIGAN ZOOPLANKTON -
A Review with Special Emphasis on the Calumet Area
by
John E. Gannon
University of Michigan Biological Station
Pellston, Michigan 49769
B-l
-------
TABLE OP COFT^TTS
Page
I. Introduction B-3
II. A Brief Synopsis of Zooplankton Invest1" e.s +• innr. ' n
the Lake Michigan Basin B-5
Taxonomy B-5
Plankton Bionass B-7
Seasonal and Vertical D1 str-:but i^n B-9
Horizontal Distribution B-14
Zooplankton as Food for Fish B-18
Zooplankton in Green Bay B-20
III. Zooplankton Stiidies in the Calumet Ares .... B-23
IV. Identification of Data Gaps an^ Recommendstions for
Zooplankton Research in the C lumet Area .... B-47
V. References Cited B-51
B-2
-------
I. INTRODUCTION
The zooplankton community of Lake Michigan consists
primarily of a diverse assemblage of Rotifera and micro-
crustaceans (Cladocera and Copepoda). These organisms are
quantitatively abundant and significant in food chain
dynamics and energy flow characteristics of the Lake
Michigan ecosystem. They spend most of their life history
in the water column.
A few other organisms are predominately bottom-
dwellers but at times can be collected in the plankton.
Some non-photosynthetic Protozoa (e.g., Difflugia)
are normally benthic in habit but occasionally are found
in large numbers in the plankton. The opposum shrimp,
Mysis relicta, and the deepwater amphipod, Fontoporeia
affinis, typically are in \alce bottom sediments during
the day and migrate into the water column at night. Many
aquatic insects spend their larval stages in the benthos and
become planktonic only for a brief portion of their life
cycle when they move towards the lake surface in preparation
for emergence into the terrestrial environment as adults.
Many larval fishes spend a brief time in the plankton before
assuming predominately bottom-dwelling habits. In addition,
a variety of small invertebrates (Qstracoda, Hydracarina,
Nematoda, Annelida, and some Cladocera and Copepoda) are
characteristically foun^ on bottom or among rooted plants
and at times are temporarily swept into the plankton in
turbulent near-shore waters.
B-3
-------
Since the euplanktonic Rotifera, Oladocera, and
Copepoda comprise most of the total biomgss of lake
Michigan zooplankton, this review will be concerned only
with these organisms. The b'ology and ecology of rotifers
and micro-crustaceans in Lake Michigan are poorly under-
stood even though over 60 scientific papers have appeared on
the subject since the late 19th century (Gannon 19^9).
Most papers are descriptive, concentrating heavily upon
taxonomy and distribution in space and time. Pew papers
have been concerned specifically with the Calumet area of
southern Lake Michigan, and fewer still hqve dealt with
zooplankters in relation to water quality problems in that
region.
The earliest studies on Lake Michigan zooplankton
were strictly taxonotnic. They were prorpted by curiosity
about the kinds of organisms found in city wter supplies.
Later, concern about water pollution from municipal sewage
and industrial wastes initiated further studies. However,,
zooplankton received little attention since most of the
emphasis was placed upon chemical parameters, coliform
bacteria, and phytoplankton. Renewed interest in Lake
Michigan zooplankton has occurred during the past decade
due to concern about rapidly fluctuating fish stocks and the
recent predominance and abundance of planktivorous fish, such as
alewife, Al_osa pj3eudoharengus_. and smelt, 0smerua mordax. Additional
B-4
-------
impetus for zooplankton research has been prompted bj concern
about thermal and radioactive pollution effects on Lake
Michigan biota by waste water discharge from nuclear electric
power generating stations.
Thia report is a review of pertinent literature on
the ecology of zooplankton with particular emphasis on the
Calumet area of southern Lake Michigan (Figure B-l) . The
discussion must not be limited precisely to the Calumet
area alone. Zooplankters by no means are confined to
artificial boundaries created by man. The limnology of
Lake Michigan is characterized by complex and massive
hydrodynamics that undoubtedly sweep zooplankters in and
out of the Calumet region. Zooplankton research which has
been conducted elsewhere in the Lake Michigan basin but
containing data pertinent to the Calumet area will be
discussed.
II. A BRIEF SYJSOPSIS OP ZOOPLANKTOH IHVESTIQATIONS IS THE
LAKE MICHIGAN BASIN
This section includes a brief discussion of papers
dealing with zooplankton ecology throughout Lake Michigan.
The intent is to identify data sources of information on
various aspects of zooplankton ecology pertinent to future
work on zooplankton in the Calumet area.
U&XONOMT
Early investigations on Lake Michigan zooplankton
were strictly taxonomic. Birge (1882) briefly listed 9
B-5
-------
I
88'
87
86*
-46*
ESCANABA
MENOMINEE1'
45*
-44»
44'-
-42*
PORT
WASHINGTON-
MILWAUKEE
LAKE MICHIGAN
BATHYMETRY IN METERS
Compiled and'drown by: R. J. Ristlc
Dote; November 1970
43-
ZO 40 | 60 80 KILOMETERS
20 40 60 MILES
WAUKEGAN
Contour interval 20 meters,
except in northern end of
lake where contour interval
is 50 meters.
8ENTON HARBOR
42°-
tf>MlCHIGAN CITY
87* 86»
85*
Figure B-lo Morpheme trie map of Lake Michigan. The focus of this
report is on the Calumet area of extreme southwestern Lake
Michigan extending from the 68tH Street Chicago water intake c
to Burns Harbor near Gary, Indiana.
B-6
-------
species of Cladocera found in the City of Chicago water
supply. Forbes (1882) provided descriptions of some
zooplankton Crustacea collected near Chicago, Illinois;
off Racine, Wisconsin; and in Grand Traverse Bay. Marsh
(1895), Jennings (1896), and Kofoid (1896) gave taxonomic
accounts of Copepoda, Rotifera, and Protozoa, respectively,
collected in a biological survey of the Grand Traverse Bay
region (Ward I895;l896). Schact (1897; 1898) and Marsh
(1909; 1929) used specimens from Lake Michigan in taxonomic
treatments of North American Copepoda. Ahlstrom (1936),
in the first offshore investigation of plankton in Lake
Michigan, examined phytopiankton, Protozoa, and Rotifera
from net tows in the southern portion of Lake Michigan
during 1930 and 1931. None of his stations included the
Calumet area, but this work represents the most detailed
account available on rotifer species composition in the
offshore waters of Lake Michlg an. Many species encountered
in Ahlstrom1s study undoubtedly occur at times in the
Calumet region. The most recent taxonomic study using
specimens from Lake Michigan was by Deevey and Deevey (1971)
who revised a portion of the cladoceran family, Bosminidae.
PLANKTON BIOMASS
Several studies have examined total plankton biomass,
including zooplankton, at municipal water intakes at
Milwaukee, Wisconsin (Damann 1966) and at Chicago, Illinois
(Baylis and Gerstein 1929; Lackey 19144; Daraann 19U5, I960;
B-7
-------
Garnet and Rademacher I960; Gerstein 1965; Vaughn 1969;
Vaughn and Reed 1972). Total counts of plankton have been
routinely monitored where phytoplankton, mainly diatoms,
have caused clogging of filters and taste and odor problems
in city water supplies. Since phytoplankton and zooplankton
numbers were normally combined, and since zooplankters are
usually less than 0.1 percent of net phytoplankton counts
(Damann 19U^)> these data contain little information
concerning zooplankton. Identifications of zooplankton, if
attempted at all, were usually confined to the most
abundant genera. Total plankton count data have been useful
only in applied problems related to drinking water supplies
and in detecting a significant increase in phytoplankton
abundance in southern Lake Michigan during the past £0
years (see Howmiller 1973, p. A-l).
Further data from water intake stations in Lake
Michigan were obtained by Williams (1962; 1966) as part
of the National Water Quality Network program conducted by
the U.S. Public Health Service in 1957 through 1962. Two
Lake Mich^pn stations (Gary, Indiana and Milwaukee, Wisconsin)
were among 128 stations established in the Great Lakes and
on major rivers across the United States. Bnphasis in this
investigation was on phytoplankton but limited quantitative
data were obtained on rotifers, cladocerans, and copepods.
In comparison with stations elsewhere, Lake Michigan
exhibited a particularly rich rotifer fauna.
B-8
-------
Zooplankton biomass measurements, as dry weight and
particulate organic matter, were made by Robertson and
Powers (1965;1967) and Powers et al. (196?) in Lake Michigan
during 196U-66 and by Ayers and Huang (196?) during 196U
in Milwaukee Harbor. These data may be useful for compara-
tive purposes when similar tests are run in future years,
but presently contribute little to our knowledge of Lake
Michigan zooplankton ecology.
SEASONAL AND VERTICAL DISTRIBUTION
Eddy (1927) obtained the first data on seasonal
distribution of zooplankton in Lake Mich5.gan. He examined
plankton from near-shore surface tows taken in the extreme
southern end of the lake during 1887-88 and 1926-27. Most
of these data were treated qualitatively although some
semi-quantitative results were presented for a few dates
in 1926-27. Wells (I960) conducted the first truly
quantitative study at offshore stations 13 km (8 mi) west
of Grand Haven, Michigan in 195^ and 14..8 km (3 mi) west of
Frankfort, Michigan in 1955 using a Clarke-Burapus sampler.
Detailed data on seasonal and vertical distribution of
zooplankton Crustacea were obtained on 10 dates from June
through November. This work still stands as the most
thorough investigation of zooplankton ecology ever conducted
in the Lake Michigan basin.
Wells (1970) resampled his 195U station off Grand
Haven, Michigan in 1966 and 1968 at the same time of the
B-9
-------
year using identical methods. He noted dramatic changes in
zooplankton size and species composition between 195U
(pre-alewife abundance) and 1966 (maximum alewife abundance).
All species larger than 1.0 mm, except Diaptomus oregonenals,
sharply declined to one-fourth or less of their former
abundance while all smaller species, except Diaptomus
minutus, increased 1.2 to 72 times over their 1954 standing
crop (Table 1). Several species (Eubosmina coregoni,
Daphnia longiremis, Ceriodaphnia qiuadrangula, and Eurytemora
affinis) appeared in the community in 1966 that were not
reported in 195U- Size-selective predation by alewife was
strongly suspected as the causative factor. In 1968, following
the massive alewife die-off of 1967, there was some evidence
that the zooplankton community was shifting back to compo-
sition similar to pre-alewife abundance. Many of the larger
species increased in abundance from 1966 to 1968, although
Daphnia galeata-mendotae and Mesocyclops edax still
remained exceedingly rare (Table B-l).
Gannon (1972a) contributed information on
abundance and distribution of zooplankton Crustacea in
Lake Michigan off Milwaukee, Wisconsin in 1968-70. Seasonal
distribution was studied at two stations, an inshore station
in Milwaukee Harbor and an offshore station 18 km (10 mi)
east of Milwaukee. This investigation presented the only
detailed dste available on Lake Michigan zooplankton Crustacea
during the winter months. A parallel study was conducted
by Stemberger (1973) on the Rotifera of the Milwaukee Harbor
B-10
-------
Table B-1..' Abundance of zooplankton Crustacea in 1966 and 1968
relative to that in 1954. Calculated from Wells' (1970)
data for mid-July and early August in Lake Michigan
off Grand Haven, Michigan.
Mean
Length
Species (mm)
Cladocera
Leptodora kindtii
Daphnia galeata-mendotae
Daphnia retrocurva
Diaphanosoma leuchteribergianum
Polyphemus pediculus
Bosmina longirostrjs
Copepoda
Senecella calanoides
Limnocalanus macrurus
Epischura lacustris
Diaptomus sicilis
Mesocyclops edax
Diaptomus oregonensis
Cyclops bicuspidatus thorn as i
Diaptomus ashlandi
Diaptomus minutus
5t
1.1
1.1
0.9
0.7
0.5
2.9
2.5
1.7
1.3
1.2
1.1
0.9
0.8
0.8
Abundances relative to
1.00 in 1954
1966 1968
0.17
<0.01
0.03
0
72.08
4.63
0.25
0.23
0.09
0.25
0
1.22
2.85
1.16
0.72
0.65
<0.01
1.18
0
144.09
1.94
0.75
2.11
0.56
0.58
<0.01
0.90
2.17
0.21
4.93
B-ll
-------
region during 197;-. This study presents the only compre-
hensive analysis available on rotifer species composition
and abundance Tor the inshore waters of Lake Michigan.
Since the investigations of Gannon (1972s) and Gtemberger
(1973) were partially conducted in the enriched waters or
Milwaukee H&rbor and represent the most complete studies to
date on zooplankton spades composition and distribution in
Lake Michigan, they should be of interest to future workers
on zooplankton in the Calumet area of Lake Michigan.
Based upon the studies of Gannon (1972s) and Stemberger
(1973), Gannon (1972b) discussed the relative effects of
eutrophication and fish predation on recent changes in zooplsnkton
species composition in Lake Michigan. Both eutrophlcation
and size-selective predation can cause a decrease in the size
composition of zooplankton and such changes o^ten entail
shifts in species composition. Since eutrophication and
fish predation often result in similar changes in zooplankton
size and species composition, it is often difficult to
distinguish the effects of these two factors on the zooplankton
community. However, it was noted that oligotrophic offshore
waters of Lake Michigan contained high numbers of calanoid
copepods relative to cladocerans and rotifers and the
opposite was true for the more eutrophic inshore waters.
It was suggested that the relative proportions of
calanoid copepods to cladocerans and rotifers may be
useful in indicating the state of eutrophication of Great
Lakes waters (Gannon 1972b).
B-12
-------
A few additional studies have presented limited
data on seasonal distribution and abundance of Lake Michigan
zooplankton. Seasonal distribution of diaptomid copepods
in western Lake Michigan during spring through fall, 19614.
was reported by Robertson (1966). Manny and Hall (1969),
in an attempt to measure community metabolism by the diurnal
oxygen curve method, obtained limited data on zooplankton
abundance in the surface waters near Grand Haven, Michigan
in July, 1968.
Schelske and Roth (1973) obtained limited zoo-
plankton data from 6 stations in northern Lake Michigan
on 7 July 1970- Information on zooplankton (mostly Crustacea)
biomass by volume determinations and generic composition
was procured. These data offer little information on
Lake Michigan zooplankton alone. However, they are useful
in comparing zooplankton Crustacea community structure and
abxindance in Lake Michigan with other Great Lakes since
identical methods were employed on Lakes Superior, Huron,
and Erie.
In addition to the data of Wells (I960) on vertical
migration of zooplankton Crustacea in Lake Michigan,
McNaught (1966) and McNaught and Hasler (1966) obtained
more detailed information from a station off Saugatuck,
Michigan during summer, 196i| and another off Ludington,
B-13
-------
Michigan in spring, 1965. Correlations were made between
vertical migration patterns of several species, visual
sensitivity of those species to spectral composition of
light, and changes in light intensity. Lane and McNaught
(1970) reexamined data from August, 19614, using mathematical
analyses of niche specificity. Habitat selection through
vertical migration was considered the most significant
mechanism for separating niches among "omnivorous" and
"herbivorous" zooplankters.
HORIZONTAL DISTRIBUTION
Several investigations have examined horizontal
distribution of zooplankton in the offshore waters of
Lake Michigan. The Hardy continuous plankton recorder
has been utilized in two investigations in tte offshore
waters of the lake. Robertson (1968) presented limited
data for Lake Michigan in 1965 and 1966 while exploring
possibilities of adapting the Hardy recorder for use in
the Great Lakes. Swain, Olson, and Odlaug (1968;1970)
towed a continuous plankton recorder at a depth of 10 m along
the longitudinal axis of the lake during July and August,
1966 and July and October, 1967. Since only one depth was
sampled at all hours of the day and night, these data are
difficult to interpret due to unmeasured effects of vertical
migration on the samples obtained. In general, Daphnia and
Bosmina were more abundant at the southern end of the lake
than elsewhere. Cyclops was most abundant nearer the shorelines.
B-14
-------
Interest in the dispersal of pollutants in the near-
shore waters of Lake Michigan have spurred a number of
investigators to pursue studies on horizontal distribution
of zooplankton near harbors and other point sources of
potential pollutants. Several investigations have been
conducted in the vicinity of Milwaukee Harbor and a
considerable number of studies are currently underway in
the vicinity of nuclear electric power generating stations
mostly in the southern portion of the lake.
In the Milwaukee Harbor region, Torke (1971) studied
the distribution and abundance of Cladocera near the Milwaukee
Harbor in August and September, 1969. In general, no
significant differences in inshore-offshore species compo-
sition or abundance were detected. Only the higher abundance
of Daphnia retrocurva offshore (8-16 km) than inshore (O.lj.-
3.2 km) was statistically significant. Gannon (1972a)
investigated horizontal distribution of zooplankton Crustacea
by obtaining a series of samples from the cooling water
intake of a Chesapeake and Ohio railroad ferry as it steamed
across the lake along a northeast course from Milwaukee,
Wisconsin to Ludington, Michigan. The sampling program
was conducted overnight on six dates from March, 1969 through
January, 1970. Horizontal distribution of zooplankton was
notably uniform during spring, fall, and winter. However,
contrary to the results of Torke (1971), obvious inshore
and offshore differences in abundance were observed during
summer. Certain species (such as Bosmina longiroatris and
B-15
-------
Cyclops bicuspidatus thomasi) were dramatically more abundant
in the near-shore waters (0-l£ km) off Milwaukee in comparison
with stations farther offshore. Higher numbers off Milwaukee
reflect a response by the zooplankters to nutrient enrich-
ment of the near-shore waters by the discharge of municipal
sewage, industrial wastes, and storm water run-off from the
Milwaukee River watershed. Inshore and offshore differences
were evident but less distinct off the small town of
Ludington, Michigan.
Even more dramatic results of inshore and offshore
differences were noted in Stemberger's (1973) study of
rotifers in the Milwaukee Harbor region. Certain species,
most likely of lotic origin, were found only in the harbor
region. Lentic forms characteristic of the Lake Michigan
biota decreased dramatically in abundance at stations
further offshore. Rotifers near the harbor appear to be
responding to higher nutrient conditions with faster growth
rates enabling a large biomass to be accrued.
Our knowledge of zooplankton ecology in the coastal
zone of Lake Michigan has been augmented considerably by
investigations on the impact of heated water discharges
from electric generating stations on Latce Michigan biota.
Much of this research is currently underway and many reports
are unavailable for review at this date. Investigations on
B-16
-------
zooplankton have formed an integral part of many of these
studies. Most notable are the investigations of Roth and
Stewart (in press; also in Ayers and Seibel 1973) in the
vicinity of the Donald C. Cook Nuclear Power Plant near
St. Joseph, Michigan. Abundance and distribution of
zooplankton Crustacea were investigated at three stations
ranging from inshore (1.2 km from shore) to offshore (11.2 km
from shore) from April through November, 1972. A distinct
inshore fauna consisting predominately of Cladocera was
noted. Persistence of a distinct inshore fanna was attributed
to one or a combination of the following factors: thermal
stratification, high near-shore primary productivity, or
fish predation. Industrial Bio-test, Inc. (1972) has been
investigating thermal effects at two power plants in south-
western Lake Michigan since spring, 1971. Zooplankton
Crustacea species composition and abundance have been
investigated quantitatively in the coastal waters at a
functional fossil fuel plant near Waukegan, Illinois and
a nuclear plant currently under construction near Zion,
Illinois. Investigations on entrainment and condenser
passage by zooplankton have also been conducted at the
Waukegan plant. Mortality was low (average of 6 percent)
with mechanical abrasion indicated as a more important
cause of death than temperature stress. A more limited
study was also conducted by Industrial Bio-test Laboratories,
Inc. (1971) at the Bailey generating station near Gary,
Indiana prior to conversion of the plant from fossil to
nuclear fuel. Distribution of zooplankton Crustacea was
B-17
-------
determined inside and outside of the thermal plume area
during October, 1970. Cladocera (mainly Daphnia and Bosmina)
were significantly more abundant in the plume while copepods
(mostly Diaptomus) were more prevalent outside the plume,.
ZOOPLANKTON AS POOD FOR PISH
Interest in the adequacy of the plankton food supply
for commercially valuable fish in Lake Michigan prompted
several studies on zooplankton. Forbes (1882) wrote:
"One cannot go far in the study of organic
life which prevails in a stream or lake,
without being made aware of the important
part played therein by the neglected but
interesting group of the smaller crustaceans.
They occupy a central position not only in
the classification of aquatic animals, but
also in the complicated network of physiological
relations by which the living forms of a body
of water are held together as an organized
society. Feeding, themselves, upon the lowest
and smallest of plants and animals, they furnish
food in turn to a great variety of the higher
animals, and even to some plants.
"The fisherman who toils at his nets, the
sportsman in pursuit of health and recreation,
rarely reflect, even if they know, that their
amusements and their labors depend strictly
upon these humble creatures, of whose very
existence, indeed, many of them are unaware;
and yet there is ample evidence that, with few
and unimportant exceptions, all young fishes,
of our fresh waters at least, live for a time
almost wholly upon entomostraca."
Forbes (1883; 1888) ran a series of laboratory experiments
on the first food of larval whitefish, Coregonus clupeaformis,
using plankton from southern Lake Michigan. Cyclops and
Diaptomus were the most important food snrces following
absorbance of the yolk sac. Wells and Beeton (1963)
B-18
-------
examined stomach contents of l,lj.69 bloaters, Coregonus hoyi,
collected from various locations in Lake Michigan during
1951t through 1961. Bloaters under 18 cm (7 in) long fed
heavily upon zooplankton Crustacea. The most frequent
species in stomachs were Cyclops bicuspidatus thomasi,
Diaptomus spp., and Daphnia galeata-mendotae. Pish larger
than 18 cm fed predominately on Pontoporeia and Mysis.
The population explosion of alewife, Alosa
pseudoharengus, during the last decade prompted several
studies on the food habits of this species. Norden (1968)
examined the food of larval alewife (0.5-6.7 cm) in
Milwaukee Harbor during August, 1966 and August through
October, 1967. Positive selection for both cladocerans
and copepods was generally observed. Cyclops spp. and
Bosmina spp. were most prevalent in larval alewife stomachs.
Morsell and Norden (1968) examined food habits of juvenile
and adult alewife in Lake Michigan from May, 1966 through
July, 1967. Cladocera and Copepoda comprised most of the
alewife diet. Limnocalanus macrurus was most common in
profundal zone collections while Cyclops bicuspidatus and
Diaptomus spp. were most prevalent in littoral collections.
Bosmina long_irostris and Diaptomus spp. were prominent in
stomachs of alewife collected in summer,
A series of studies most pertinent to the Calumet
area have been conducted on interspecies relationships
of fish in the Indiana waters of Lake Michigan. The
investigations were conducted by graduate students from
B-19
-------
Ball State University under the leadership of T. S.
McComish. Three of the investigations have involved
zooplankton. Johnson (1972) conducted quantitative studies
on zooplankton species composition and abundance during
June through October 1970. Two parallel studies examined
food habits of the alewife in the same region (Rhodes
1971; Webb 1973). These
investigations represent the most thorough studies on
zooplankton ecology in the Calumet area of Lake Michigan
and will be discussed in detail in the next section.
ZOOPLANKTON IN GREEN BAY
All previously mentioned studies have been
conducted in the main portion of the Lake Michigan Basin.
Although Green Bay is geographically distant and morpho-
logically distinct from the Calumet area of Lake Michigan,
the two regions are similar in that they both receive
high volume waste water discharges from municipal and
industrial sources. Consequently, it may be of interest
to briefly mention the few studies that have been
conducted in the Green Bay region.
Balch, et al. (195&) collected zooplankton samples
in lower Green Bay during February, 1955 and in the Pox
River during April and July, 1955 using a plankton trap
of unknown dimensions. Data were expressed only as
numbers of Cladocera, Copepoda, and nauplii per unit volume.
B-20
-------
These data indicate that the Pox River supports high
numbers (8,000-lj.QQ»000 per m*) of zooplankton Crustacea
during summer. It was estimated from dry weight
measurements that 1.21). x l(r kg (136.U tons) of plankton
was flowing from Lake Winnebago and entering the lower
Pox River. Judging by plankton densities throughout
the river, a considerable biomass of plankton is suspected
to enter Green Bay by way of the river.
The open waters throughout Green Bay were sampled
with vertical tow nets in 1969-70 during all seasons by
Gannon (1972a). The zooplankton Crustacea of southern
Green Bay differs substantially from that of the northern
portion of the Bay and Lake Michigan proper. Due to
the shallow nature of southern Green Bay, the incidence of
littoral and benthic micro-crustaceans in the plankton was
higher in this region than elsewhere in the Lake Michigan
basin. The southern portion of the Bay is strongly
influenced by the inflow of the Pox River. Water from the
Pox River retains its identity from 3f? to $0 km north of
the river mouth along the eastern shore of the Bay. This
zone of Pox River water in southrn Green Bay exhibits
faunal characteristics most dissimilar to Lake Michigan.
Standing crop of zooplankton Crustacea was generally
higher in the zone of Pox River water than elsewhere .
The large biomass of zooplanktnn in snthern Green
Bay is due to constant inputs from the Pox River and is
probably enhanced by high recruitment and productivity
of zooplankton in the nutrient laden waters of the Pox
River water mass. Many species common in the plankton of
B-21
-------
Lake Winnebago were transported through the Pox River and
established populations in southern Green Bay. Many of
these species are rare or entirely absent elsewhere in the
Lake Michigan basin.
A brief study on zooplankton distribution in
southern Green Bay was conducted by Torke (1972). He
sampled 7 stations with a vertical two net on 12 July 1971.
He noted that Cyclops vernalis and Diaptomus siciloides
were important constituents of the micro-crustacean fauna.
The former species is rare in Lake Michigan while the
latter has not been reported elsewhere in Lake Michigan.
A few investigations have examined food habits of
planktivorous fishes in Green Bay. The previously
mentioned study of Norden and Morsell (1968) on alewife
food habits included collections in southern Green Bay.
Further studies on alewife were conducted by Gannon (1972a)
who examined stomach contents of alewife collected off
Pensaukee, Wisconsin on 10 July 1969. Large copepods
were found to be the predominant food source for alewife.
Hogman ( 1971 ) examined stomach contents of larval
whitefish collected in central Green Bay in May, 1968-1970.
Cyclops bicuspidatus was the most prevalent food source
followed by Diaptomus spp., Daphnia, and Bosmina.
In summary, our knowledge of Lake Michigan zooplankton
has barely advanced beyond basic descriptive natural history.
Very little is known concerning the ecology of planktonic
Protozoa and Rotifera. Most investigations have concentrated
B-22
-------
on the larger zooplankton Crustacea. Some knowledge has
been gained about their species composition, distribution
in space (vertical and horizontal) and time (seasonal),
and their importance as food for certain planktivorous
fish. Our knowledge of response of zooplankton to
specific pollutants and overall changes in water quality
is indeed depauperate.
III. ZOOPLANKTON STUDIES IN THE CALUMET AREA
The first samples of Lake Michigan zooplankton
made available to science were strained from the City of
Chicago water supply by a public works official, B. W.
Thomas (Ward l8?9). Thomas sent samples of organisms
to several experts of the day including E. A. Birge and
S. A. Forbes. Birge (1882) and Forbes (1882) both
published brief species lists of micro-crustaceans found
in the samples. Several of the species (Diaptomus sicilis,
Epischura lacustris, and Cyclops thomasi, now known as
C_. blcuspidatus thomas i) reported by Forbes (1882) were
new to science at that time. The species lists provided
in these two papers are undoubtedly incomplete and many
more species have been reported for the Calumet area.
Their importance today is primarily as historical documents.
The collection of plankton at the City of Chicago
water works, which was begun by B. W. Thomas nearly 100
years ago, has been continued by subsequent workers.
B-23
-------
Routine collections and quantitative enumeration of total
plankton have been regular procedures in water analysis
since 1926. As pointed out earlier, phytoplankton and
zooplankton counts are combined, thus rendering these
data of little use in analysis of zooplankton information.
If zooplankters are specifically mentioned at all, only
data for the most common genera of Rotifers, Copepoda, and
Cladocera are mentioned (Baylis and Gerstein 1929;
Lackey 19UU; Damann 19lj.5). Although these data have been
adequate for purposes of water filtration plant operation,
they are not adequate for detecting long-term changes in
zooplankton species composition and abundance commensurate
with changes in water quality. Identification of zooplankton
to the species level and separation of phytoplankton and
zooplankton counts would have been invaluable in augmenting
our limited knowledge of zooplankton ecology in the
Calumet region.
Williams (1962; 1966) presented quantitative data
on abundance and generic composition of predominant rotifers
from five water intakes around the Great Lakes including
one station at Gary, Indiana (Table B-2). The Gary station
exhibited a higher number of rotifer genera (15) than any
other station in the Great Lakes, but only the five most
abundant genera were identified. The Gary water intake
station had relatively high mean numbers of individuals per
unit volume and this was correlated with relatively high
phytoplankton counts. On the basis of results from 128
B-24
-------
Table B-2. Dominant planktonic rotifers from selected Great Lakes sampling stations
(Williams, 1966).
Rotifers in
semimonthly plankton samples,
counts/liter,
Lakes and stations
w
i
On
Lake Huron, Port Huron,
Michigan
Lake Michigan, Milwaukee,
Wisconsin
Lake Michigan, Gary,
Indiana
Lake Superior, Sault Ste.
Marie, Michigan
Lake Superior, Duluth,
Minnesota
CO H- €
At 1-4 l_|.
{JJ 3 r*
3 Q* ft
^3 h1" 3^
n> H* tn
QJ
O C O
Ht 01 h|
(— •
*>5T 3
oo o
•o n
CO ft) u)
01 H
3
•o
1— •
(D
CO
11
9
15
6
5
Z co
C 01
O* *T3
fD I—1
W O
O 0
M> M>
ua *>.
t) 00
3
0) CO
n o»
01 3
i—"
(D
CO
14
63
45
12
8
>
(D
0)
03
0)
3
C
tr
n
H*
M
.1 0
.7 1
.3 0
.0 0
.5 0
1961
and
1962
Five most abundant
network — averages
May to
w x
n n>
fli H
O 01
3* rt
(->• fl)
O 1-
3 j— •
C 01
CO
.7 33.1
.2 82.0
.9 38.6
.3 4.2
15.2
TJ
o
i—*
•^
01
H
rt
3*
n
0)
12.5
45.0
22.4
8.0
3.0
genera of
for 24
the
samples from
November
1
5
3
1
1
w
"^
3
n
3*
01
n
rt
0)
.3
.9
.4
.3
.2
2
1
1
0
H3
H
H-
O
3*
O
O
fD
H
o
0)
.5
.5
.9
.7
0.3
U.H
0
iQ ft
n> oi
3 M
H 0
01 M)
ft
ro
50.2
135.1
67.3
19.6
19.8
-------
stations on water courses throughout the United States,
Williams (1966) concluded that high numbers of rotifers
were consistently found in waters or high clarity and
high phytoplankton concentrations. Zooplankton Crustacea
were not identified in his study, but Copepoda averaged
three times more abundant tha n Cladocera in 214. samples
collected from July, I960 to July, 1961 at the Gary,
Indiana water intake (Williams 1962).
The investigation by Eddy (192?) was the first
attempt to analyze species composition, abundance, and
seasonal distribution in the Calumet area of Lake
Michigan. He obtained samples from Lake Michigan in
November through December, 188?; April through October,
1888; October, 1926; and May and July, 192?. This paper
contains the most complete species list of planktonic
Protozoa, Rotifera, Cladocera, and Copepoda available
for the Calumet area of Lake Michigan. He reported 9
species of non-photosynthetic protozoans, 16 species of
rotifers, 11 cladocerans, and 9 copepods. Most species
were typical of limnetic conditions, but some littoral and
benthic forms were also present because collections were
made so close to shore.
The list of species presented by Eddy (192?) is
difficult to interpret because of subsequent changes in
taxonomic nomenclature. For example, Eddy listed the
cladoceran, Bosmina longispina, in his collections.
B-26
-------
Wells (I960) only found Bosmina longirostris in his study
off the eastern coast of Lake Michigan in 195i|-55. Based
upon the results in these two studies, Beeton (1965)
suggested that B. longispina (=? B. coregoni) was replaced
by B. longirostris in Lake Michigan and used this alleged
species shift as an indicator of advancing eutrophication.
However, because of taxonomic problems in the genus Bosmina
(Deevey and Deevey 1971) and since Eddy's samples have
evidently been discarded long ago, the exact identity of
his Bosmina longispina remains unknown and this indication
of advancing eutrophication must be considered dubious.
Likewise, Brooks (1969) attempted to determine shifts
in abundance of various Lake Michigan zooplankters between
1927 and 195U by comparing data of Eddy (192?) and Wells
(I960). He suggested that there had been a shift toward
zooplankton that are larger and more efficient at filtering
phytoplankton between 1927 and 195U- He further suggested
that the larger zooplankters, due to their effectiveness
in cropping phytoplankton, may be ". . .a factor in the
preservation of the oligotrophic condition of that lake."
(Brooks 1969>. However, Eddy (1927) and Wells (I960) sampled
entirely different portions of Lake Michigan using widely
divergent methods of collection. Any conclusions drawn
B-27
-------
from these data on changes in zooplankton populations in
Lake Michigan should be viewed as extremely tenuous.
Airther difficulties in the interpretation of Eddy's
(1927) study also exist. The 1587-88 dats W9*e treated
only qualitatively while some quantitative information
was given for the 1926-27 collections. Any changes in
abundance or distribution between the two series of
collections are not readily detectable. Samples during
the important winter months were lacking so the information
on seasonal d! stribution of many species is incomplete.
Although this paper was a landmark in plankton investigations
of large lakes, its utility in interpretation of relations
between zooplankton population dynamics and water quality
changes in the Calumet area of Lake Michigan is limited.
A brief study was conducted in fall, 1?70 by
Industrial Bio-test Laboratories, Inc. (1971) on tne
effects of a thermal plume on zooplankton species composition
and distribution. The plume of hot water was from the Bailey
electric power generating station near Gar^y, Indians. The
thermal plume at this plant remained as a contiguous water
mass because the plume area was protected from prevailing
winds and current action by a large breakwater. Total
B-28
-------
numbers of zooplankton Crustacea were substantially higher
inside the plume than in an area beyond the plume's
influence. Cladocerans (mainly Daphnia retrocurva and
Bosmina longirostris) and the calanoid copepod, Burytemora
affinis, were noticeably more abundant inside the plume
than outside it. Further studies wouia be required to
disclose if this is a prominent and consistent feature of
heated water plumes in the Calumet area.
The investigation by Johnson (1972) contains
the most pertinent information on zooplankton species
composition, inshore distribution, and abundance available
for the Calumet area. Stations were aampled along three
transects off Gary, Burns Harbor, and Michigan City, Indiana
on seven dates from June through October, 1970 (Figure B-2).
A small Wisconsin plankton net with 76 MM mesh size was
used as the collecting device. The small diameter of the
net and the fine mesh size possibly biased these data since
larger species of zooplankton Crustacea are capable of net
avoidance. In addition, clogging of the fine mesh by
phytoplankton likely reduced the filtration efficiency of
the net. Consequently, calculations of zooplankton
abundance may be low by as much as 50 percent (Gannon 1972a),
B-29
-------
N
41°50'
LAKE MICHIGAN
18m
Michigan
City
h 41
Hammond, East
Chicago, Gary
Metropolitan Area
^ 10000
jittle Calumet R-i ga ea
Feet
10000 30000 50000
20000
5000
40000
15000
INOANA
0 . 10000
Statute Miles
357 9
11 13
.. BJJJH I
87°30'
87W20'
87°10'
024
87°00'
t
8
10 12
86°50'
i
Figure B-2. Indiana waters of Lake Michigan showing sampling stations along transects
from Gary (0), Burns Ditch (B), and Michigan City (M), Indiana at depths of
5, 10, 15, and 18 m. (Prom Johnson 1972)
-------
Johnson (1972) recorded 10 species of Copepoda and
!!<. species of Cladocera and Rotifers in the study area
(Table B"3)•Bosmina longirostris, Daphnia retrocurva, and
Cyclops bicuspidatus were the most abundant crustacean
zooplankters throughout the study period (Figures B-3, B-4 and
B~5 ). There were few consistent patterns in zooplankton
abundance and distribution between the three transects.
However, biomass of zooplankton Crustacea was generally
higher at Michigan City and Gary stations than at Burns
Harbor (Figures B-6, B-7, B-8). Although sampling methods
employed in this study may have underestimated population
numbers, the abundance of zooplantoon at all stations in
the Indiana waters were considerably higher than values
reported for elsewhere in Lake Michigan. Total numbers
of zooplankton Crustacea in the Indiana waters ranged from
o
about 225,000 to 375,000 individuals per m . These values
are approximately 10 times higher than biomass figures
reported for the offshore waters of Lake Michigan (Wells
I960; Gannon 1972a), and two to three times higher than
values reported by Eddy (1927) for a sample collected near
Chicago, Illinois on 10 July 1927. Comparable numbers have
been reported only in Milwaukee Harbor, at the mouth of
the Pox River in Green Bay (Gannon 1972a), and near the
southwestern shore of Lake Michigan (Roth and Stewart 1973),
The zooplankton Crustacea community in the Indiana
waters was characterized by low numbers of calanoid copepods
relative to cyclopoid copepods and cladocerans. Phenomenally
B-31
-------
Table B-3. List of zooplankton found in the Indiana waters
of Lake Michigan during 1970 (from Johnson 1972).
COPEPODA
CALANOIDA
Diaptomus ashlandi
Diaptomus minutus
Diaptomus oregor^ensis
Diaptomus sicilis
Eurytemora affinTs
>ischura lacustris
Lironocalanus ma crurus
CYCLOPOIDA
Cyclops bi cuspid a tus thomasi
Tropocyclops pra sinus
HARPACTICOIDA
Canthocamptus sp.
CLADOCERA
Bosmina longirostris
Bo am In a" coregonT
Chydorus gphae^ricus
Eury c er cus^l.amell a tus
AIona affinTs
Leptpdora
Polyphemus'^ed i culus
Diaphanosoma leuchtenbergianum
Ceriodaphnia sp.
Daphnla ret^rocurva
Daphnia' galeata-mendotae
Daphnia' longiremis
Daphnia pulex
B-32
-------
Table B-3. (Continued)
ROTIPERA
Polyarthra vulgaris
Keratella"'eochleari3
KeratelTa" quad rat a
%ellicott'i_a
Synchaeta sp.
Gastropus sp.
Trichocerca sp.
Asplanchna priodonta
Ploesoma truneaturn
Fompholyx sp.
Filinia longiseta
Brachionus angularis
Brachionus calyciflorus
Notholca sp.
B-33
-------
Cyclops bicuspidatus thomasi
100
90
80
70
Other cladocerans
Bosminn lonqirostris
60
c
o
W
a50
E
8
*
40
30
20
10
Other copepoda L~l
Daphnia retrocurva |['Q
JUN
JUL
AU6
\
SEP
OCT
Figure B-3. Percent species composition of adult crustacean
zooplankters as a mean 'of all stations on the Michigan
City transect in Indiana waters of Lake Michigan, 1970
(from Johnson 1972).
B-34
-------
Bosmina longirostris [23 Dnphnia retrocurva QJJ
Cyclops bicuspida Lus thomasi ^M^__^
Other clndocerans •• other cop«pod»I I
JUN
JUL
AUO
SEP
OCT
Figure B-4. Percent species composition of adult crustacean
zooplankters as a mean of all stations on the Burns
Ditch transect in Indiana waters of Lake Michigan, 1970
(from Johnson 1972).
B-35
-------
Bosmina longirostris fy7] Daphnia retrocurva
Cyclops bicuspidatus thomasi
100 "
other cladocerans
Other copepods ("""1
90 -
80 -
70 -
60 -
c
o
•rt
4J
•H
0)
&50 -
40 -
30 -
20 -
10 -
JUN
JUL
AUO
SEP
OCT
Figure B-5. Percent species composition of adult crustacean
zobplankters as a mean pf all stations on the Gary
. transect in Indiana waters of Lake Michigan, 1970
(from Johnson 1972).
B-36
-------
400
350
300
250
41
•H
200
150
100
50
Bosmina longiroatris T7\ Daphnia retrocurva
Cyclops bicuepidatug thomaai ffgg
Other cladocerans Other copepoda
-d2
I
JUN
I
JUL
1
BBSS
AUQ
\
SEP
OCT
Figure B-6. Abundance of adult crustacean zooplankters as a
mean of all stations on the Michigan City transect in
Indiana waters of Lake Michigan, 1970 (from Johnaou 1972)
B-37
-------
No ./liter
I
OJ
00
-------
400
Bosmina longirostriji
Cyclopa
Other
Daphnia retrocurva
350
300
250
M
-------
high numbers of a few species of cladocerans and cyclopdd
copopods coupled with low numbers of calanoid copepdods
may indicate a response by the zooplankton community to
nutrient enrichment of the Indiana waters of Lake Michigan
(Gannon 1972b). The dominance of smaller species and
individuals of zooplankton Crustacea in the Indiana waters
may be the result of heavy alewife predation. This conclusion
is augmented by the work of several investigators who found
Cladocera and Copepoda to be predominate food sources of
alewife in the Indiana waters of Lake Michigan (Rhodes 1971;
Webb 1973; Webb and McComish 1974; Rhodes and McComish 1975).
Johnson (1972) reported 12 genera of Rotifera in
the Indiana waters of Lake Michigan (Table B-3) Polyarthra
was most abundant followed by Keratella, Synchaeta,
Kellicottia, and Trichocerca (Table B-4). Mean numbers of
rotifers per sample were over 100,000 individuals per
m . These values were approximately 7 times higher than those
reported by Eddy (1927) for a July, 1927 sample off Chicago,
Illinois. The high numbers of rotifers recorded in 1970
in the Indiana waters of Lake Michigan may indicate a
response of the rotifer community to nutrient enrichment.
The only study tba t has examined the impact of
potential pollutants from the Calumet area on Lake Michigan
zooplankton was conducted by Gannon and Beeton (1969). They
studied the effects of sediments from nine Great Lakes
harbors, including Calumet and Indiana Harbors, on mortality
of crustacean zooplankters. The investigation was conducted
B-40
-------
Table B-4. Mean abundance of rotifers in numbers per liter on Michigan City, Burns
Ditch, and Gary transects in Indiana waters of Lake Michigan, 1970
(from Johnson 1972).
Cd
I
Transect
Michigan
City
Burns
Ditch
Gary
Mean no.
of rotifers
per sample
109
124
128
Mean of the five
genera per
Poly-
arthra
45
51
42
Kere-
tella
38
41
49
Synch-
aeta
8
13
21
roost common
sample
Kelli-
cottia
9
10
5
Tricho-
cerca
4
2
2
Total mean
of five most
common
genera per
sample
104
117
119
-------
in the laboratory using sediments collected from five
stations in Calumet Harbor (Figure B-9) and Indiana
.Harbor (Figure B-10) and from one to five samples in the
other Great Lakes harbors. Two sets of experiments were
run: one using a laboratory culture of Daphnia^ pulex
and the other using freshly collected Lake Michigan zoo-
plankton. In both tests, the zooplankters were placed in
125 ml bottles with different concentrations of suspended
sediments. After 1^8 hours, counts of live and dead
organisms were made.
Results of the Daphnia puleg and natural Lake
Michigan zooplankton tests were similar. In Calumet
Harbor, significant mortality occurred in the river
sediment samples but no significant mortality occurred in
the outer harbor (C-l) sample (Figures B-ll and B-12). The
sediment from the outer harbor of Calumet was one of the
least toxic sediments encountered in the study. This
harbor differed from others included in the investigation
since Lake Michigan water flows into the Calumet River.
Consequently, there is a continuous influx of relatively
high quality water into the outer harbor. In Indiana
Harbor, highest mortality of zooplankton was observed at
the innermost stations (Figures B-ll and B-12). Indiana Harbor
samples were among the most toxic to plankton and benthos
encountered during the study. No attempt was made in this
investigation to identify the toxic substances responsible
for the zooplankton mortalities. However, mortalities
were generally greatest in samples exhibiting an oily
texture and a high chemical oxygen demand (Gannon and Beeton
B-42
-------
-!>
LO
LA KE
CALUMET
Seal* of F««l
1000 0 I 2 5000
Figure B-9. Location of sampling points, 1968, Calumet river (from Gannon and Beeton 1969).
-------
V
A
»«
«b
v->
V
%
> ,A
A,
?/
%>
00 T331S (JNV1NI
-------
too
78
SO
o
3E
w
-p-
Ul
IOO-
87S
1
1 2,
0-
'
:
RH
i \
M 1 F
;
f*
': '. B ' , -
: e : : •
: ; : : . : ; :
':'.': ': '. : i •
; : = It ; ;
C-l C-2|c-3 C-4 C-5 I-
~[ \ f ^ ^ ^
IB
||
t"
l|l-2 1-3 1-4JI-5 GB-l|GB-2
GB-3JGB-<
^GB-5
Control 5ml lOml 25ml
Stdiment Dilutions
Figure B-ll,
Mortality of Daphnr pulex in vario.-s concentrations of harbor sediments
(B, C, CL, GB, I; M," R. RK, S, and T) .aid Fuller's Earth (F). Calumet
Harober (C) and Indiana Harbor (I) (from Gannon and Beaton 1969)
-------
100
—. 7B
-
£• so
0 25
25
" I
y
-
:
[
T
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i I
R-IJR-2
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.- |CL-2|CL-
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: ;
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'•
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-2 B-sJfl-
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hi
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f
:
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: r
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-l|
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C-2
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-
; :
C-3 C-
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~_
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:
•4]C
•
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j| :
:-5 I
5
; t
: \
-i i
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E
1
-2
• i
o :
fe • ;
J| : '
1-3 1-4 I
i
: •
: p :
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: : i
-5 GB- C
-IE
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5B-5
> C
111
; K
; f
;B--
5C
111
, E
§
3B-<
i
||
S3-5
I D I I
Control 5ml 10ml 25ml
Scdimtnt Dilutions
Figure B-12 .Mortality of zooplankton in various concentrations of harbor sediments (B, C,
T M R. RH. S. and T) and Fuller's Earth (F). (from Gannon
-------
IV. IDBHTIFICATIpy OP DATA GAPS AID RBCOMMEgDATIOyS FOR
ZOO PLANKTON RESEARCH TM J*Hli CALUMET AREA
It is readily apparent from the previous discussion
that our knowledge of zooplankton ecology in the Calumet
area of southern Lake Michigan is woefully incomplete.
Basic descriptive information on species composition,
spatial distribution, and seasonal distribution is
inadequate. Undoubtedly, many species of planktonic
Protozoa, Rotifera, and Crustacea occur in the Calumet
region that have not been previously reported. The
zooplankton community in a shallow, estuarine region such
as the Calumet area will consist of euliranetic Lake
Michigan species, littoral species, organisms that are
predominately benthic but occasionally are found in the
plankton, and other species most characteristic of rivers.
Stemberger (1973) and Gannon (1972a) have compiled species
lists for the Rotifera and Crustacea, respectively, of
the Milwaukee River estuary. It is most likely that many
zooplankters occurring in the Milwaukee Harbor region may
also exist in the Calumet area.
The work of Johnson (1972) has provided some
information on horizontal distribution of zooplankton in
the near-shore waters of the Calumet area. Seasonal
distribution data is available only for the spring, summer,
and fall months (Eddy 1927; Johnson 1972), Winter data
are needed in the Calumet area to complete our knowledge
B-47
-------
of this important aspect of zooplankton ecology. Distri-
bution studies on zooplankton ought not be limited to the
Lake Michigan portion of the Calumet area alone. Although
volumes have been written on pollution problems of the
rivers tributary to Lake Michigan in the Calumet area
(e.g , U.S. Department of Health, Education, and Welfare
1965), zooplankters have been ignored. The contribution
of zooplankton species composition and biomass to the
inshore waters of Lake Michigan from tributaries in the
Calumet region should be investigated. A background of
descriptive information on species composition and distri-
bution must be acquired before questions on the relations
between zooplankton community structure and water quality
can be tackled.
Studies on the impact of water quality degradation
on zooplankton in the Calumet area are practically non-
existent. Zooplankters are known to be sensitive to
toxic pollutarts (e.g., Anderson 19UUK The extreme reduction
or absence of zooplankters in a given area will be a good
indication of toxic pollution. On the other hand, certain
species of zooplankton respond to nutrient loading with
faster growth rates and build up phenomenally high
numbers of individuals in a short time. High numbers of
a few species in a certain region will be a good indication
of nutrient enrichment. For example, Johnson (1972) noted
that Bosmina longirostris was often the most abundant
crustacean zooplankter in the Indiana waters of Lake
B-48
-------
Michigan. Gannon (1972a) observed such high numbers of
this species only in the nutrient enriched waters at the
mouths of the Milwaukee and Pox Rivers. Consistently high
numbers of Boamina and other zooplankters in the Indiana
waters of Lake Michigan may indicate that nutrient loading
has a greater effect on the zooplankton population than
discharge of toxic wastes.
The following types of zpoplankton studies are
recommended for applied research in the Calumet area:
1) An examination of plankton records at the City of
Chicago Department of Water and Sewers wouti be desirable.
If it is possible to separate phytoplankton and zooplankton
counts, valuable information on changes in zooplankton
abundance with time may be discernable.
2) Field studies on the species composition and distri-
bution of zooplankton in the Calumet region. I'hese
investigations should include stations in the lower portions
of the Calumet River complex and Burns Ditch. The purpose
of such studies should be to identify areas where the
zooplankton community is responding to toxic wastes and/or
nutrient loading. Taxonomic identification to the species
level is imperative if worthwhile data are to be gained.
Protozoa and Rotifera may provide more valuable information
than Crustacea since the smaller organisms have a high
reproductive capacity and can respond quicker to environ-
mental changes than the larger Crustacea. Analysis of
B-49
-------
zooplankton community structure may be more valuable
than looking for single indicator species of water
quality. Gannon (1972b) suggested that the relative
proportion of calanoid copepods to cladocerans and rotifers
may be a useful ratio in indicating changes in water
quality of the Great Lakes. Schelske and Roth (1973)
successfully used this ratio to characterize zooplankton
response to water quality in Lakes Michigan, Superior,
Huron, and Erie.
3) Laboratory bioassay studies using zooplankton would
be most useful in identifying the reaponse or zooplankton
to specific pollutants in the Calumet area. Such studies
would be invaluable in setting effluent and water quality
standards in the southern Lake Michigan region.
B-50
-------
CITED
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Balch, R. P., K. M. Mackenthun, W. M. Van Horn, and T. P.
Wisniewski. 1956. Biological studies of the Fox River
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the lower Pox River and Green Bay made in 1955-1956.
Wisconsin Comm. on Water Poll., Bull. WP102, 7l+ pp.
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Beeton, A. n. 1?65- Eutrophication of the St. Lawrence
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Birge, S. A. 1882. Notes on Crustacea in Chicago water
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Chicago Med. J. & Exam.., U3 (l8Rl): 58U-590.
Brooks, J. L. 1969. Sutrophioaticn and changes in the
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Damann, K. E. 19U5. Plankton studies of Lake Michigan.
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Damann, K. E. I960. Plankton studies on Lake Michigan.
II. Thirty-three years of plankton uata collected at
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Damann, K. E. 1966. Plankton studies of Lake Michigan.
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Deevey, E. S., Jr. and G. B. Deevey. 1971. The American
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Eddy, S. 1927. The plankton of Lake Michigan. Bull. Illinois
State Div. Natur. Hist. Surv., 17(10 : 203-232.
Forbes, S. A. 1882. On some Entomostraca of Lake Michigan
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Forbes, S. A. 1883. The first food of the common white-
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Forbes, S. A. 1888. Notes on the first food of the
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Gannon, J. E. 1969. Great Lakes plankton investigations:
A bibliography. Univ. Wisconsin-Milwaukee, Center for
Great Lakes Studies, Spec. Rept. No. 7, 65 pp.
Gannon, J. E. 1972a. A contribution to the ecology of
zooplankton Crustacea of Lake Michigan and Green Bay.
Unpubl. Ph.D. Diss., Univ. Wisconsin, 257 pp.
Gannon, J. E. 1972b. Effects of eutrophication and fish
predation on recent changes in zooplankton Crustacea
species composition in Lake Michigan. Trans. Amer.
Microsc. Soc., 91: 82-81+.
Gannon, J. E. and A. M. Beeton. 1969. Studies on the effects of
dredged materials from selected Great Lakes harbors on plankton
and benthos. Univ. Wise on sin-Milwaukee, Center for Great Lakes
Studies, Spec. Rept. No. 8, 82 pp.
Hogman, W. J. 1971. The larvae of the lake whitefish
CCoregonus clupeaformis (Mitchell)] of Green Bay, Lake
Michigan. Unpubl. Ph.D. Diss., Univ. Wisconsin, 126 pp.
Howmiller, R. P. 1973. A review of selected research on
the biology and sediments of southern Lake Michigan with
particular reference to the Calumet area. Appendix A, this raport.
Industrial Bio-test Laboratories, Inc. 1971. Northern
Indiana Public Service Company, Bailey Generating Station,
Nuclear 1, Environmental Report.
Industrial Bio-test Laboratories, Inc. 1972. Evaluation
of thermal effects in southwestern Lake Michigan in the
vicinity of the Waukegan and Zion generating stations,
April 1971 through March 1972. Unpubl. report submitted
to Commonwealth Edison Co.
Jennings, H. S. 1896. Report on the Rotatoria - with
description of a new species, p. 85-93. In: Ward, H. B.,
A biological examination or Lake Michigan~Tn the Traverse
Bay region. Bull. Mich. Fish. Comm., No. 6, 99 pp.
B-52
-------
Johnson, D. L. 1972. Zooplankton population dynamics in
Indiana waters of Lake Michigan in 1970. TJnpubl. M,S.
Thesis, Ball State Univ., 129 pp.
Kofoid, C. A. 1896. A report upon the Protozoa observed
in Lake Michigan and the inland lakes in the neighbor-
hood of Gharlevoix, during the summer of l89U» P» 76-814..
In: Ward, H. B., A biological examination of Lake
Michigan in the Traverse Bay region. Bull. Michigan
Pish. Comm., Ho. 6, 99 pp.
Lackey, J. B. 19^. Quality and quantity of plankton in
the south end of Lake Michigan in 19^2. J. Amer. Water
Works Assoc., 36: 669-6714..
Lane, P. A. and D. C. McHaught. 1970. A mathematical
analysis of the niches of Lake Michigan zooplankton.
Proc. 13th Conf. Great Lakes Res., Internat. Assoc.
Great Lakes Res., p. V7-57.
Manny, B. A. and A. S. Hall. 1969. Diurnal changes in
stratification and dissolved oxygen in the surface waters
of Lake Michigan. Proc. 12th Conf. Great Lakes Res.,
Internat. Assoc. Great Lakes Res., p. 622-63U*
Marsh, C. D. 1895. On the Cyclopidae and Calanidae of
Ldke St. Clair, Lake Michigan, and certain of the inland
lakes of Michigan. Bull. Mich. Pish. Comm., 5, 214, pp.
Marsh, G. D. 1909. A revision of tha North American
species of Cyclops. Trans. Wis. Acad. Sci., Arts,
Lett., 16, Pt. 2 (3): 1067-113U.
Marsh, C. D. 1929. Distribution and key of the North
American copepods of the genus Diaptomus, with a descrip-
tion of a new species. Proc. U.S. Nat. Mus., 75? 1-27.
McNaught, D. C. 1966. Depth control by planktonic
cladocerans in Lake Michigan. Proc. 9th Conf. Great Lakes
Res., Univ. Michigan, Great Lakes Res. Div., Publ. No.
15: 98-108.
McNaught, D. C. and A. D. Hasler. 1966. Photoenvironments
of planktonic Crustacea in Lake Michigan. Verh. int.
Ver. Limnol., 16: 19U-203.
Morsell, J. W. and C. R. Norden. 1968. Pood habits of the
alewife, Alosa pseudoharengus (Wilson), in Lake Michigan.
Proc. llth Conf. Great Lakes Res., Int. Assoc. Great Lakes
Res., p. 96-102.
B-53
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Norden, C. R. 1968. Morphology and food habits of the
larval alewife, Aloaa pseudoharengus (Wilson), in Lake
Michigan. Proc. llth Conf. Great Lakes Res., Int.
Assoc. Great Lakes Res., p. 103-110.
Powers, C. P., A. Robertson, S. A. Czaika, and W. P.
Alley. 1967. Lake Michigan biological data, 196U-66,
p. 179-187. In; Ayers, J. C. and D. C. Chandler.
Studies on the eutrophication of Lake Michigan. Univ.
Michigan, Great Lakes Res. Div. , Spec. Rept. No. 30,
PP-
Rhodes, R. J. 1971. The food habits of the alewife in
Indiana waters of Lake Michigan. Unpubl. MS. Thesis,
Ball State Univ. , 82 pp.
Rhodes, R. J. and T. S. McComish. 1975. Observations on
the alewife 's food habits in Indiana's waters of Lake
Michigan in 1970. Ohio J. Sci., 75: in press.
Robertson, A. 1966. The distribution of calanoid copepoda
in the Great Lakes. Proc. 9th Conf. Great Lakes Res.,
Univ. Michigan, Great Lakes Res. Div., Publ. No. 15:
129-139.
Robertson, A. 1968. Abundance, distribution and biology
of plankton in Lake Michigan with the addition of a Research
Ships of Opportunity Project. Univ. Michigan, Great
Lakes Res. Div., Publ. No. 35, U2 pp.
Robertson, A. and C. P. Powers. 1965. Particulate organic
matter in Lake Michigan. Proc. 8th Conf. Great Lakes
Res., Univ. Michigan, Great Lakes Res. Div., Publ. No. 13:
175-181.
Robertson, A. and C. P. Powers. 1967. Comparison of the
distribution of organic matter in the five Great Lakes,
p. 1-18. In; Ayers, J. C. and D. C. Chandler, Studies
on the eutrophication of Lake Michigan. Univ. Michigan,
Great Lakes Res. Div., Spec. Rept. No. 30, Ul5 PP.
Roth, J. C. and J. A. Stewart. 1973. Nearshore zooplankton
of southeastern Lake Michigan, 1972. Proc. 10th Conf.
Great Lakes Res., Internat. Assoc. Great Lakes Res.,
p. 132-142.
Schacht, P. W. 1897. The North American species of Diaptomus .
Bull. Illinois State Lab. Natur. Hist., 5, Art. 3: 97-207.
Schacht, P. W. 1898. The North American Centropagidae
belonging to the genera Osphranticum, Limnoealanus,
and Epischura. Bull. Illinois State Lab. Natur. Hist.
5, Art. k: 225-270.
B-54
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Schelske, C. L. and J. C. Roth. 1973. LimnologJoal survey
of Lakes Michigan, Superior, Huron, and Erie. Univ.
Michigan, Great Lakes Res. Div., Publ. No. 17, 108 pp.
Stemberger, R. 1973. Temporal and spatial distributions
of rotifers in Milwaukee Harbor and adjacent Lake Michigan.
Unpubl. M.S. Thesis, Univ. Wisconsin-Milwaukee, 55 PP-
Swain, W. R., T. A. Olson, and T. 0. Odlaug. 1968.
Preliminary studies of zooplankton distribution with the
continuous plankton recorder. Water Resources Res.
Cntr., Univ. Minnesota, Bull. No. 7, 21 pp.
Swain, W. R., T. A. Olson, and T. 0. Odlaug. 1970. The
ecology of the second trophic level in Lakes Superior,
Michigan, and Huron. Univ. Minnesota, Water Resources
Res. Cntr., Bull. No. 26, 151 pp.
Torke, B. G. 1971. Cladocera of Lake Michigan: Inshore-
offshore differences in the Milwaukee area. Unpubl. M.S.
Thesis, Univ. Wisconsin-Milwaukee, 21* pp.
Torke, B. G. 1972. The distribution of planktonic Crustacea
in southern Green Bay on 12 July 1971, p. U5-55. 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-III July 1971, Univ. Wi scon sin-Mi Iwaukee, Center for
Great Studies, Spec. Rept. No. 13, 71 pp.
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Conference in the matter of pollution of the interstate
waters of the Grand Calumet River, Little Crlumet River,
Calumet River, Wolf Lake, Lake Michigan and their
tributaries, Proceedings, Vol. 1, March 2-9, 1965.
Ward, H. B. 1895- The food supply of the Great Lakes;
and some experiments on its amount and distribution.
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Ward, H. B. 1896. A biological examination of Lake Michigan
in the Traverse Bay region. Bull. Mich. Pish. Comm.,
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Wells, L. and A. M. Beeton. 1963. Pood of the bloater,
Coregonus hoyi, in Lake Michigan. Trans. Amer. Pish. Soc.,
92: 2U5'25FT~
B-55
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Wells, L. 1970. Effects of alewife predation on zooplankton
populations. Limnol. Oceanogr., 15: 556-565-
Williams, L. G. 1962. Plankton population dynamics.
Nat. Water Qual. Netwk., U.S. Publ. Health Serv., Publ.
No. 663, Suppl. 2, 90 pp.
Williams, L. G. 1966. Dominant planktonic rotifers of
major waterways of the United States. Liranol. Oceanogr.,
11: 83-91.
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habits of the alewife in Indiana waters of Lake Michigan
near Michigan City, Indiana, in 1971 and 1972. Proc.
Indiana Acad. Sci. 83: in press.
B-56
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APPENDIX C
DESCRIPTION OF INDUSTRIAL EFFLUENT SOURCES
AND COMPARISON OF EFFLUENT DATA
Ci
-------
TABLE OF CONTENTS
P
1. INTRODUCTION 1
2. AMERICAN MAIZE COMPANY 3
2.1 Introduction 3
2.2 Data Evaluation 3
3. AMERICAN OIL COMPANY b
3.1 Introduction 5
3.2 Data Evaluation 5
3.3 Waste Treatment 8
4. UNION CARBIDE 9
4.1 Introduction 9
4.2 Chemicals and Plastics Division - Whiting .... 9
4.2.1 Wastewater Discharge 9
4.2.2 Wastewater Treatment 10
4.3 Linde Air Products Division, East Chicago .... 10
4.3.1 Wastewater Discharge 10
4.3.2 Wastewater Treatment 12
4.3.3 T-1200 Plant - Gary 12
5. ATLANTIC RICHFIELD COMPANY 13
5.1 Introduction 13
5.2 Data Evaluation 13
5.3 Waste Treatment 16
6. E. I. DU PONT IS
6.1 Introduction 18
6.2 Discharges 18
6.3 Proposed Effluent Loads 18
6.4 Waste Treatment 18
7. BETHLEHEM STEEL 23
7.1 Introduction 23
7.2 Data Evaluation 23
7.3 Waste Treatment 23
Cii
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TABLE OF CONTENTS (cent.)
Page
8. MIDWEST STEEL - PORTAGE 25
8.1 Introduction 25
8.2 Data Evaluation 25
8.3 Waste Treatment 27
9. INLAND STEEL COMPANY 28
9.1 Introduction 28
9.2 Data Evaluation 28
9.3 Waste Treatment 34
10. YOUNGSTOWH SHEET AND TUBE CO., EAST CHICAGO 36
10.1 General Description 36
10.2 Data Evaluation 36
10.3 Waste Treatment 38
10.4 Unreported Discharges 43
11. U.S. STEEL - GARY 44
11.1 Introduction 44
11.2 General Description - Water Discharges 44
11.3 Parameter Evaluation . , , . 48
11.4 Waste Treatment Facilities 50
11.5 Alternate Waste Lines 55
11.6 American Bridge and Universal Atlas Cement
Divisions 56
12. U.S. STEEL SOUTH WORKS 58
12.1 Introduction 58
12.2 Outfall Descriptions 58
12.3 Evaluation 58
REFERENCES 64
Ciii
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LIST OF TABLES
Table
1 American Maize Discharges 4
2 American Oil Company Outfall 002 Data Comparison . 7
3 Union Carbide, Chemical & Plastics Division
Effluent Data Comparison of NPDES Data, Operating
Reports and Effluent Survey 11
4 Atlantic-Richfield NPDES Data Comparison Parameters
Showing Increase 15
5 E. I. DuPont Effluent Loads 21
6 Midwest Steel Effluent Data, Comparison of NPDES
with Monthly Operating Reports to ISPCB and
U.S. EPA Survey 26
7 Inland Steel Company Outfall Summary 30
8 Inland Steel Company Effluent Concentrations ... 31
9 Inland Steel Effluent Concentrations, Comparison
of NPDES and ISPCB 24-hr Samples, July 11, 1973 . 32
10 Inland Steel Monthly Operating Report Data .... 33
11 Youngstown Sheet & Tube Company, NPDES and ISPCB
Outfall Identification and Flows 37
12 Youngstown Sheet and Tube Company Effluent
Concentrations 39
13 Youngstown Sheet and Tube Effluent Data, Compari-
son of NPDES, Monthly Operating Reports and
Effluent Surveys 40
14 U.S. Steel Gary Works Outfall Summary 47
15 U.S. Steel Effluent Concentrations 49
16 U.S. Steel Gary Works Effluents, Comparison of
EPA Analysis with Permit Application 51
17 U.S. Steel Gary Works Effluent Concentrations,
Comparison of NPDES, Monthly Operating Reports
and Effluent Surveys 52
18 U.S. Steel South Works Interim Effluent Concen-
trations at Outfall 006 62
Civ
-------
LIST OF FIGURES
Figure Pag(
1 Detail Map Showing Outfalls from American Oil
Co. and Union Carbide 6
2 Detail Map of Indiana Harbor Canal Discharges ... 14
3 Atlantic-Richfield Waste Treatment Flowsheet ... 17
4 Detail Map of Grand Calumet River Discharges ... 19
5 E. I. DuPont Outfalls Prior to December 1973 ... 20
6 Detail Map of Burns Ditch Discharges 24
7 Detail Map Showing Outfalls from Inland and
Youngstown Steel Cos 29
8 Inland Steel Company Terminal Waste Treatment ... 35
9 Detail Map Showing Outfalls of Gary Works U.S.
Steel Corp 45
10 Detail Map of Buffington Harbor Discharges .... 57
11 Outfall Locations 59
12 Existing Proposed Water Use and Wastewater System . 61
Cv
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DESCRIPTION OF INDUSTRIAL EFFLUENT SOURCES
AND COMPARISON OF EFFLUENT DATA
1. INTRODUCTION
This appendix was prepared under a subcontract by Citizens
for a Better Environment. It provides more detailed information
than was given in Chapter 4 (Vol. I of this report). It contains
tables showing the effluent flows and conpositions for the major
industrial facilities, and compares effluent data from NPDES
permit applications with industry monthly operating reports, and
24-hr effluent sampling done by Indiana and U.S. EPA. In the
case of two industries, it presents the effluent performance that
is being implemented as a result of court-enforced agreements.
Table 4.1 and Figure 4.1 in Chapter 4 locate the industries
and effluent sources in the Calumet area. Chapter 4 contains
summary tables giving the loads of major pollutants from all
outfalls to Lake Michigan , as well as summary tables of loads
from all outfalls entering Lake Michigan via the IHC. More
detailed tables of loads from outfalls on the IHC are presented
in the Combinatorics (1974) report, and some of these tables have
been included in Chapters 13 to 18. This appendix contains
further detailed data on large industrial facilities discharging
to the IHC. In general there is reasonable agreement with
Combinatorics (1974).
Information on the various effluent sources was gathered
primarily from U.S. EPA files, NPDES permit applications, Indiana
Stream Pollution Control Board files and in some instances from
the industries concerned. Although this appendix represents an
extensive compilation of data, it by no means contains all the
relevant data available.
Wide discrepancies have been noted in the amount of data
available on each effluent source. Generally, the more serious
the pollution, the more available is source data. For many minor
industrial discharges, often the only data available are in the
NPDES permit application.
C-l
-------
Of the various data sources utilized, perhaps the NPDES
permit application data when used in conjunction with the U.S.
EPA file is the most valuable. The NPDES application includes
detailed information relating to the effluent discharge including
flow, parameter concentrations and treatment methods. Additional
information from the U.S. EPA file can be used to update the
NPDES and offer more detailed information relating to waste
treatment facilities and the industry's litigation record. EPA
surveillance reports are also available in these files and can
be used as a cross-check on NPDES data. The NPDES applications
were originally submitted in mid-1971, based on measurements
made in late 1970.
The files of the Indiana Stream Pollution Control Board are
useful primarily for ISPCB effluent surveillance reports. These
reports are filed approximately once a year and can be used to
cross-check NPDES data and observe more recent changes in effluent
quality. Also in ISPCB files are monthly operating reports filed
by the industries, These data can be used as a cross-check, but
often very few outfalls and parameters are reported. In the
tables in this appendix we used only the most recent monthly
operating reports (April and May 1973) for comparison with NPDES
data, since these reports should reflect the most up-to-date
effluent conditions.
Information from industries was valuable and often provided
further clarification.
C-2
-------
2. AMERICAN MAIZE COMPANY
2.1 Introduction
American Maize Company located in Hanniond, Indiana, produces
cornstarch and corn syrup from shelled corn (NPDES application).
2.2 Data Evaluation
The company has six discharges, one into Lake Michigan and
five others into the Wolf River Channel which flows into the Wolf
Lake. Table C-l indicates discharge location, flow and usage.
Outfall 001 discharges into Lake Michigan with treated pro-
cess waste water. The plant effluent is typically high in BOD,
but after biological treatment, installed in 1969, BOD is reduced
to an average of 13 tng/fc as reported in the July 1973 ISPCB
Monthly Operating Report. Ammonia-nitrogen and total phosphorus
values reported in the NPDES Application are 1.57 mg/£ and 0.51
mg/£, respectively. These, however, are not included in monthly
operating reports to the ISPCB, therefore, no accurate data are
available concerning their present discharge concentration.
Effluent data for discharge 001 are included in Table 4.2,
Chapter 4.
Discharges 002-005 are indicated in the NPDES application
to be noncontact cooling water. Consequently, American Maize has
not submitted parameter data other than flow, pH, temperature,
and chlorine as OC1~. Waste treatment at this plant consists of
two primary settling tanks, an aerated lagoon used as an activated
sludge unit, a clarifier and two additional aerated lagoons from
which the final effluent flows to Lake Michigan. The monthly
operating reports submitted to the ISPCB indicate that batch
processes may cause peak effluent concentrations to occur once
or twice a month. These reports show peak COD and BOD concen-
trations of several times the average. This may explain a light-
colored plume from American Maize seen in Lake Michigan during
the IITRI aerial surveillance.
C-3
-------
Table C-l
AiMERICAN MAIZE DISCHARGES
Discharge
001
002
003
004
005
Unnumbered
Flow MGD
9.7
0.216
0.057
0.288
0.086
0.242
Location
Water Usage
Lake Michigan Process
Wolf River Channel Cooling Water
Wolf Lake
excess intake
C-4
-------
3. AMERICAN OIL COMPANY
3.1 Introduction
The American Oil Company (AMOCO) facility in Whiting, Indiana,
is a "Class DM oil refinery which performs lube oil processing,
topping and cracking/reforming operations. Crude oil is processed
into various products at an established capacity of 330,000
barrels/day. Processes utilized include distillation, catalytic
reforming, hydrodesulfurization, catalytic cracking, alkylation,
treating, extraction, dewaxing, grease and lube oil production,
coking, asphalt production and sulfur recovery (EPA permit appli-
cation file 1973).
3.2 Data Evaluation
Water use within the facility is for both process and non-
contact cooling water amounting to a combined discharge of 128
mgd. Outfalls are shown in Figure C-l. Outfe11 001 is the
treated process waste stream with a flow rate of 29.17 mgd.
NPDES BOD values average 20.0 mg/£; NK3-N 5.43 mg/&; oil and
grease 4.8 mg/£ and phenols, 0.249 mg/&. Additional parameters
are included in Table 4.2. These values substantially agree
with ISPCB monthly operation reports for the later half of 1973.
Nitrogen values, however, are consistently 2-3 mg/£ lower than
reported on the NPDES (see Table C-2).
Outfall 002 is noncontact cooling water with a flow of 99
mgd. Continuous monitoring is conducted to insure stream con-
tinuity. NPDES average effluent concentrations for various
parameters are BOD, 4 mg/s,; NHn-N 0.06 tng/&; total organic carbon,
20 nig/2,; oil and grease, 0.9 mg/£ and phenols, 0.031 mg/S- (see
Table C-2). ISPCB monthly operating reports (in Table C-2)
indicate values somewhat lower for each parameter than those
listed on the NPDES.
C-5
-------
o
i
Figure C-l
DETAIL MAP SHOWING OUTFALLS
FROM AMERICAN OIL CO. AND UNION CARBIDE
-------
Table C-2
AMERICAN OIL COMPANY OUTFALL 002 DATA COMPARISON
Parameters, mg/l,
PHENOL
OIL
APPLICATION
.0
U.OG
0.03
0.9
IKPCll MONTHLY
OPHRATTMO REPORT
APRIL, 1973
ISPCT3 MOIITHLY
O^r,RA.TIMO HEPORT
f/IAY,
1.0
2.1
0.015
0.01
0.06
0.03
0.6
0.71
C-7
-------
3.3 Waste Treatment
In-plant changes to reduce the pollution load include recycle
of decoking water, the sale of spent caustic and acids, stream
stripping of sour water and reuse of phenolic water bottoms. The
process waste water treatment area includes 20-24 API separators
of a two-stage type with a detention time of approximately 120
min. Process effluent from the separator goes to a gravity
settling lagoon where it flows into an aerated lagoon consisting
of four compartments in series. The aerated lagoon effluent is
coagulated with alum, flocculated using polyelectrolytes as
flocculating aids, followed by air flotation before release to
Lake Michigan. Sludges from primary and secondary treatment, and
skimmings from tertiary treatment are burned in a fluidized bed
incinerator along with tank cleaning sludges and other hydrocarbon
wastes, including selective noxious refinery waste streams such
as spent caustics. The fluidized bed incinerator was designed
and built to also dispose of the oily sludge (sulfonate soap).
Once-through cooling water is completely segregated with its own
collection system, gravity separator, and outfall (EPA application
file 1973).
C-8
-------
4. UNION CARBIDE
4.1 Introduction
There are three facilities operated by Union Carbide within
the Calumet Study Area, the Chemicals and Plastics Division in
Whiting, the Linde Air Products Division in East Chicago and the
Lakeside T-1200 Plant in Gary. The chemicals and plastics
division has two outfalls, one to Lake Michigan and the other to
the IHC, both of which are cooling water only. Process waste
water is pretreated and then sent to the East Chicago Sewage
Treatment Plant. Linde Air Products Division has oaly one out-
fall to the IHC, consisting of noncontact cooling water and pro-
cess waste water. The T-1200 plant has one outfall which has a
discharge to Lake Michigan similar in composition to the Linde
Division outfall (NPDES Applications).
4.2 Chemicals and Plastics Division - Whiting
At the Union Carbide facility in Whiting, refinery gases are
processed into various organic compounds. At present, plant
processes include power production, an olefin unit, a low-density
polyethylene unit and isopropanol manufacturing. Water use is
for cooling purposes with a small volume being diverted for
process use. All process waste water is diverted to the East
Chicago STP.
4.2.1 Wastewater Discharge
A flow of 40-50 nillion gallons/day is discharged to Lake
Michigan through outfall 001 shown in Figure C-l. Table 4.2 in
Chapter 4 indicates effluent parameter concentrations and loadings.
Comparisons between ISPCB monthly operating reports and
NPDES data indicate reasonable agreement. For the month of
April 1973, however, several process line leaks were encountered
which increased the effluent concentrations to relatively high
levels. Also, data from a ISPCB 24-hr survey conducted June 15
and 16, 1972, indicate much higher levels than those reported
C-9
-------
by Union Carbide. Table C-3 for that sampling date BOD is
14 tng/8,, COD is 26 mg/£ and oil, 4.4 mg/Ji.
Outfall 002 represents cooling water used in the polyethylene
unit with a flow of 216,000 gallons/day to the IHC. NPDES data
(Table 4.2) indicate BOD and COD loadings in excess of those
measured for 001. Comparisons in Table C-3 show recent ISPCB
reports with parameter values considerably lower than the earlier
NPDES data.
4.2.2 Wastewater Treatment
Outfall 001 consists entirely of noncontact cooling water and
receives no treatment. The waste stream is monitored continuously
by a total carbon analyzer to detect possible process leakage.
Flow to outfall 002 is treated for oil removal and retained in a
holding tank before discharge. Daily samples for BOD, COD, oil,
suspended solids and pH are collected and analyzed.
4.3 Linde Air ProductsDivision, East Chicago
This facility extracts oxygen, nitrogen and argon from air
by means of low temperature fractionating. Power required for
the extraction is, in part, supplied by an on-site generating
station. Water use at this facility is primarily confined to
noncontact cooling for compressors and condensers (NPDES appli-
cations) .
4.3.1 Wastewater Discharge
There is one outfall discharging to the IHC. Flow is
150,750 gallons/day. Effluent data are given in Table 4.2. A
May 1973 ISPCB report agrees with values for suspended solids
but not with chromates and oil. Chromates on NPDES are listed
as 0.27 mg/£ while ISPCB reports indicate a constant 7,7 mg/£
value. Oils arc nearly three times greater on ISPCB reports at
14 mg/£ average as opposed to 5 mg/£ in the NPDES application.
Stream loading is 13 Ib/day suspended solidg, 5 Ib/day chromate s
and 8 Ib/day oil.
010
-------
Table C-3
UNION CARBIDE, CHEMICAL & PLASTICS DIVISION EFFLUENT DATA
COMPARISON OF NPDES DATA, OPERATING REPORTS AND EFFLUENT SURVEY
Concentrations,
OUTFALL 001
BOD COD SS OIL
OUTFALL 002
COD SS OIL
NPDES DATA
6.8 13.2 2.4 1.7
14.5 54
11.5 0.9
O
ISI>CB REPORT 3
APRIL, 1973
11
19 0
ISPC3 RFPORT 3
MAY, 1973
U.S. EPA 24-hr 14
SURVEY
26
2.1 4.4
ALL DATA IN nci/1
-------
4.3.2 Wastewater Treatment
Oil receives the major emphasis in the treatment process.
There are a series of four ponds connected by subsurface dikes.
These allow oil to collect on the surface and suspended solids
to settle out. Floating oil is removed by punp ing and solids
are dredged. A rag filter is also employed between the third
and fourth ponds. Union Carbide plans to construct an enlarged
settling basin which will allow total recycle (EPA application
file 1973). Completion dates are unknown at present. At that
time, the IHC outfall will handle only storm water runoff from
roof drains.
4.3.3 T-1200 Plant - Gary
This facility is similar to the Linde plant in processes and
water use. There is ona outfall to Lake Michigan with a discharge
of noncontact cooling water of 100 mgd. This waste stream
receives no treatment other than continuous chlorination to
inhibit algae growth. Residual chlorine is reported to be 0.08
mg/£ (EPA application file 1973).
C-12
-------
5. ATLANTIC RICHFIELD COMPANY
5.1 Introduction
The Atlantic-Richfield Company owns and operates a "Class B"
crude oil refinery in East Chicago, Indiana, previously owned by
Sinclair, Inc. Crude oil is received by pipeline and is processed
into numerous organic compounds. Processes utilized include
fractionating, reforming, catalytic cracking, alkylation and
polymerization. There is one submerged discharge into tha Lake
George Branch of the Indiana Harbor Canal with a flow of 4.75 mgd,
shown in Figure C-2.
Water usage at the facility is for power generation and steam
production. Steam is used in many process lines and becomes
contaminated with oil and ammonia products. Noncontact cooling
water from various lines is combined with process water and treated
at the Industrial Waste Treatment Plant. Concentrated ammonia
and sanitary wastes are sent to the East Chicago Sewage Treatment
Plant (EPA application file 1973).
5.2 Pata Eva1uation
Data submitted for NPDES evaluation in 1971 was updated in
July of 1973. Effluent parameter concentrations are listed in
Table 4.2. Values reported for ammonia-nitrogen, Kjeldahl-
nitrogen, C.O.C., cyanide, iron, and phenols are relatively high.
A report prepared by the U.S. EPA in September 1971 (EPA appli-
cation file) compares data obtained in a 24-hr effluent survey
with the then applicable effluent guidelines. Several parameters
exceeded the guidelines including chlorides, sulfates, nitrates,
total phosphorus, iron, phenol, cyanide and total dissolved
solids. Furthermore, the NPDES application was updated as shown
in Table C-4. This table indicates that several of these param-
eters have increased 1971 to 1973. The 1971 EPA report mentions
the projected addition of a coker, fluid catalytic cracker,
hydro-cracker and a crude still. Arco is the only industry in
the Calumet area whose effluent has not improved but rather has
degraded in quality.
C-13
-------
o
/? TL ft A/ r / r
/*', - u ,-rft £
OOI
001-
OOl-
003-
09*'-
Figure C-2
DETAIL MAP OF INDIANA HARBOR CANAL DISCHARGES
-------
Table C-4
ATIANTIC-RICHFIELD NPDES DATA COMPARISON
PARAMETERS SHOWING INCREASE
Concentrations, tag/A
PARAMETER NPDES 6/25/71 NPDES 7/16/73
BOD 10 14.3
COD 125 1C7
TS 965 978
TSS 15 20.6
NII3-N 10 14.3
Cr 0.15 0.24
C-15.
-------
5.3 Waste Treatment
The total refinery effluent passes through oil separators
where oil is skimmed and sent back through the refinery for
processing (Figure C-3). This waste oil is stored in two tanks.
Sludge from oil separation, tank bottoms, etc. are stored in
tanks before going to a sludge disposal area. After process
water passes through the oil separators, it goes to an activated
sludge treatment plant. Two activated sludge complete mix tanks,
having a capacity of 4,059,000 gallons, provide treatment before
final clarification. These tanks provide 34 hr detention at
2,000 gpm, 27 hr at 2,500 gpm, or 19.4 hr at 3,500 gpm. Effluent
from the aeration tanks is sent to final clarifiers. Sludge from
the final tanks is sent back to the activated sludge mix tanks
and excess sludge goes to an aerobic sludge digestion tank, then
to a sludge thickener. The thickened sludge is sent to a sludge
disposal contractor and the supernatant is recycled through the
system. Effluent from the final clarifiers is sent to a manhole,
then to a submerged outfall for discharge into the Lake George
Branch of the Indiana Harbor Canal (Figure C-2). The total
refinery effluent is monitored (by a Beckman 9500 automatic
monitor) for flow, temperature, dissolved oxygen and total
organic carbon (EPA application file 1973).
016
-------
3 -s M 6 i>
1
OIL.
o
Ot
7s* A460
r/c ~ ;e/
-------
'6. E. I. DU PONT
6.1 Introduction
The E. I. DuPont de Nemours facility is located on the Grand
Calumet River near its junction with the Indiana Harbor Canal in
East Chicago. See Figure C-4. The facility produces inorganic
industrial chemicals and operates continuously with process waste
water and noncontact cooling water discharged to the Grand
Calumet River. At present, the plant is in the process of com-
plying with a consent decree issued November 14, 1972, resulting
from litigation initiated by the U.S. government.
6.2 Discharges
There are ten reported discharges in the NPDES application
of March 17, 1972 (Figure C-5). Outfall 006 has been closed
leaving nine outfalls. This number is expected to change as
compliance with the Consent Decree is achieved. DuPont is
expected to have only three outfalls by December 18, 1973.
Effluent parameters are given in Table 4.2, even though
these will not be representative after December 18, 1973. Since
these data will no longer be valid, no attempt is made to cross
check the NPDES data with ISPCB monthly operating reports.
6.3 Proposed Effluent Loads
Of the three outfalls remaining after December 18, 1973,
001 will discharge noncontact cooling water with 002 and 003
discharging treated process waste. See Table C-5.
6.4 Waste Treatment
Outfall 002 will contain waste water from the Freon manu-
facturing area, sulfuric acid manufacturing area, sulfamic manu-
facturing area and the agricultural manufacturing area, Treatment
for this waste stream will consist of various collecting tanks,
a neutralization tank, a 46,000 gallon settling tank, and three
cartridge filters. Continuous monitoring for various parameters
C-18
-------
Figure C-4
DETAIL MAP OF GRAND CALUMET RIVER DISCHARGES
-------
ppron AREA
o
I
to
o
CI:LOT»TDT:G
Figure C-5
E. I. DU PONT OUTFALLS PRIOR TO DECEMBER 1973
-------
Table C-5
E. I. DU PONT EFFLUENT LOADS
Beginning January 15, 1974 through October 15, 1974, the
effluent loads will be:
Parameter
Zn
P
Suspended solids
Chlorides
Loading, Ib/day
8
4
600
2500
Monthly average
12
6
900
4800
After October 15, 1974, the loads will be:
Sulfates
Dissolved solids
39,000
74,000
58,500
102,000
C-21
-------
;will be included along with a final pH and adjustment unit. A
flow of 1400 gpm is expected.
Outfall 003 will discharge wastes from the chloride and
silicate products manufacturing area. Treatment will consist of
two 300,000 gallon equalization tanks, a rapid agitation coagu-
lator, a flocculator and thickener followed by two diatomaceous
earth coated rotary filters. This flow will then combine with
another waste stream from the Ludox area. Combined, the waste
flow of 600 gpm will go through two 16-ft high pressure sand
filters and receive final pH adjustment before being discharged.
022
-------
7. BETHLEHEM STEEL
7.1 Introduction
This facility, located at the Burns Waterway Harbor, is the
newest in the study area and consequently one of the best in
pollution control. The plant was built during the 1960's and
$33 million has been expended on air and water pollution abate-
ment equipment with the results being apparent in the effluent
concentrations reported in the NPDES application.
7.2 Data Evaluation
The Burns Harbor plant has 163 coke ovens, one blast furnace
and two basic oxygen furnaces (300 tons each). Water usage is
258.0 million gallons/day and there are two outfalls, one to the
Little Calumet River and the other to the Burns Waterway Harbor.
Effluent parameter concentrations are listed in Table 4.2 with
outfall location shown in Figure C-6.
The correlation between ISPCB monthly operating reports and
the NPDES application for BOD and suspended solids is very good.
Data for all other information contained on the NPDES cannot be
confirmed since they are not included in the ISPCB monthly reports,
7.3 Waste Treatment
For the coke plant, blast furnace and EOF shop, waste water
is given physical-chemical treatment, cooled and then recirculated.
Finishing mill waste goes to the main treatment plant where
primary treatment removes oil and large particulates. Secondary
treatment is physical-chemical with a flocculator and clarifier
to remove additional wastes. The effluent from the clarifier
passes to a finishing lagoon which is aerated (NPDES Application
File).
C-23
-------
o
i
Ctfftf
Figure C-6
DETAIL MAP OF BURNS DITCH DISCHARGES
-------
8. MIDWEST STEEL - PORTAGE
8.1 Introduction
Midwest Steel is a division of National Steel Co., which is
the fourth largest steel producer in the nation. The Midwest
facility in Portage, Indiana, is a finishing mill only and does
not conduct coke, blast furnace or basic oxygen operations. Cold
reduction, sheet tempering, annealing and plating operations are
performed.
There are six outfalls from Midwest into Burns Ditch. See
Figure C-6. For five of these, NPDES applications have been
submitted. Outfall 006 is a discharge from a privately owned
sewage treatment plant and has no NPDES application.
8.2 Data Evaluation
Outfalls 001, 002, 003, 005 are all noncontact cooling water
from air compressors and oil coolers. Storm water run-off from
roof drains is also included in these outfalls. Effluent flows,
concentrations and loads are given in Table 4.2.
Outfall 004 represents the discharge from the Industrial
Waste Water Treatment Plant. Wastes from the continuous pickle
line, cold reduction mill, cleaning line, sheet tempering,
annealing, plating preparation, electroplating, hot dip zinc
coating lines and boiler blow-down lines are channeled into the
industrial treatment plant where physical-chemical treatment
occurs.
Comparisons given in Table C-5 between NPDES and ISPCB data
indicate close correlation for those parameters listed.
Data for outfall 006 are available only from ISPCB monthly
operating reports and EPA 24-hr surveys (Table C-6). Average
flow is approximately 10,000 gpd with BOD and suspended solids
values very low at 2 and 7 mg/& , respectively. Discharge is to
Burns Ditch. No NHo-N values were given for this outfall.
C-25
-------
Table C-6
MIDWEST STEEL EFFLUENT DATA
COMPARISON OF NPDES WITH MONTHLY OPERATING REPORTS TO ISPCB
AND U.S. EPA SURVEY
Concentrations, m^/£ except for turbidity, JTD
OUTFALL
14PDES
IGPCB REPORT
APRIL, 1973
Flow 9.06 mgd
BOD TUKIilDTTY
3.1 2J
3.7 25
CIJLFATr
375
434
CYA'Jini:
0.05
0.10
CJIP.OMIUN
0.03
0.02
IRON OIL
0.5 2.0
0.3 3.0
o
N3
IS PC P. REPORT
MAY, lb)73
3.2
o.n
0.04
0.5
1.9
OUTFALL 006
TLO17 700 CPD
Concentrations, mg/jfc
!;OD FUSPENDTD SOLIDS
PJ^P. CHLORIME
U.S. EPA 24hr
SURVEY
20
ISPCB REPOR1
APRIL, 1973
1.2
0.17
ISPCB DEPORT
MAY, 1973
7.7
0.14
-------
8.3 Waste Treatment
Midwest's facility, being constructed in the 1960's, was
able to incorporate some of the latest technology available for
pollution control.
C-27
-------
9. INLAND STEEL COMPANY
9.1 Introduction
The Inland Steel facility in East Chicago, Indiana, is one
of the largest steel mills in the country producing 5.3% of the
nation's total steel output. There are 523 coke ovens, 19 open
hearth furnaces (12 of which are due to close), 2 basic oxygen and
2 electric furnaces. Water use is 1,008 mgd, discharged through
15 outfalls shown in Figure C-7. Processes utilizing water
include coke quenching, coke processing, ironmaking, steelmaking,
sintering and hot and cold rolling (Council on Economic Priori-
ties 1973).
9.2 Data Evaluation
Of the 18 outfalls included in the NPDES application, three
008, 009, and 010, have been discontinued. See Table C-7. The
remaining outfalls and their effluent parameter concentrations
are listed in Tables 4.2 and C-8. The concentrations reported
in 1971 reflect the completion of an extensive waste water treat-
ment program at Inland. Since late 1970, no major additional
treatment has been placed on line.
A comparison between NPDES data and a recent 24-hr survey
conducted by the Indiana Stream Pollution Control Board is given
in Table C-9. Data obtained during the survey agrees closely
with that submitted in the NPDES application. The only exceptions
are the values for total iron. These values fluctuate
widely, being either substantially more or less than NPDES
values.
Comparison with ISPCB monthly operating reports in Table C-10
again show fluctuations in iron values with relatively stable
values for other parameters. The ISPCB monthly operating reports
for April and May of 1973 (Table C-10) indicate a high degree of
dependence upon intake water loading conditions in determining
the total effluent quality.
C-28
-------
.5
Ml CL
O
I
hO
/*!(.<-
.»«•>*
Oi o O
olo o
t t
•n V V,
§ § 8
COKC
/>/?n t
'"•6 ] 009 y
c
1ST" fUKtJAt.es
Oil _»
-
>
/"^
./
jr
0/2.
y^T
V *
o o
of>£u uterus.
Figure C-7
DETAIL MAP SHOWING OUTFALLS FROM INLAND AND YOUNGSTOWN STEEL COS
-------
Table C-7
INLAND STEEL COMPANY OUTFALL SUMMARY
Source: NPDES APPLICATION
n
i
Outfall number
NPDES
001
002
003
004
005
006
007
008
009
010
Oil
012
013
014
015
016
017
018
New proposed
outfalls
ISPCB
01E-2
4E-1
5E-1
5E-2
5E-3
6E-1
7E-1
13F-1
13F-2
13G-1
13H-1
14H-1
15H-1
16H-1
16H-2
16H-3
16F-1
24K-1
24N-1
Flow,
mgd
0.144
190
7.225
0.864
8.64
0.648
21.6
-
-
-
158.7
84.6
106.9
106.9
21.6
12.9
144
149.7
0.14
50.4
Average pH
8.2
7.9
7.9
8.0
8.1
8.3
7.5
-
-
-
8.0
8.0
8.0
8.0
8.2
Average temperature
Winter
34
45
45
46
59
46
55
-
-
-
48
56
45
45
54
Summer
68
80
77
80
93
80
89
-
-
-
82
90
79
79
88
-------
Inland Steel
IS 070 0X3
Table C-8
INLAND STEEL COMPANY EFFLUENT CCHCENTBATIONS
Application Date: June 22, 1971
Dg/t, except * - uf/4
O
I
003
005
014
014>
106 2 11
110 14 »
107 9 24
111 2 12
« a B 8 a 3 ii | ., 1 a
227 207 23 13 .19 83 16 .01 15 7 146
173 145 25 34 0.23 0.58 0.25 0.02 20 14 148
188 175 19 15 1 . 23 3. 44 . 3* . 01 36 19 149
200 187 19 30 .23 . 45 1 . 1£ . 11 9 10 145
1
25
26
30
25
3 SUICIDE
* CHLORIDE
0.0 41
0.1 11
0.1 25
.1 14
0 11
HIM
0 .13 - 0 4
0 0-06
.12 .08 - 0 9
0 14 0 2
0 .16 - O 3
1 1 | « .m
0 - 0 25 24S9
0 - 1 47 2175
0 - 1 12 3800
0 - 0 18 190
0 43.6 4 15 1800
*
I
20
86
IB
0
65
1 >. - 1
| | 1 | | fi .JJ
O 1O 2.1O 16 O 2O
- O 14 l.S 5 0 35
- 0 2O 2.0 6 O 29
0 5 2.2 9 0 14
S
1
o
9
18
5
4
§
1
O
O
13
0
-------
OUTFALL!
SOURCE
BOD
TR
MII-:I
TOT. P
TOT. To
OIL
PHFHOL*
BOD
TS
.<::.-:,
TOT . P
TOT Fe
OIL
I'IT;:I.OL*
OUTFALL i-
sourer.
P.OD
TS
NH3-:i
TOT. P
TOT . FG
OIL
PHENOL*
INLAND STEEL MrVLUQU CONCENTRATIONS
COMPARISON OF NPDES AND ISPCB 24-HR SAMPLES JULY 11, 1973
Parameters in mg/jt except * • ug/jt
001 002 003 004 005
NPDES ISPCB NPDES ISPCB NPDES ISPCB NPDES ISPCB NPDES IS»
3.0 3.3 2.0 1.0 . 2.U 1.8 2.0 1.5 14.0 1.8
308 32C 158 180 227 270 176 2BO 173 220
.12 .3 .59 .3 .19 .1 .17 .1 .23 .13
.3 1.2 .03 .04 .1 .1 .01 .04 .02 .06
1.2 1.0 .23 .4 2.5 1.1 1.8 6.5 2.2 0.8
7 -2 -9 - 9 - 18 -
0 -8 -o-O-O-
007 Oil 012 013 014
1.0 1.0 2.0 1.0 2.0 1.6 9.0 2.3 9.0 1.8
150 11,0 159 190 253 330 224 210 188 210
.17 .3 .18 .2 3.42 .4 1.41 .2 1.23 .2
.01 .03 .01 .06 .01 .03 .01 .03 .01 .03
.7 .6 ,2 .5 .3 .3 4.0 2.6 3.8 2.2
3-2 -2-5- 5 -
33-8 - 100 - 192 - 191
815 016 017 018
;]rors ISPCH IIPDEG inncn NPDKS ispcn NPDES ISPCB
2.0 2.1 2.0 2.2 4.0 3,5 2.0 1.9
175 231) 200 190 189 200 214 210
.14 .1 .23 ,2 .17 .1 ,15 .2
.05 .15 .11 ,30 .01 .03 .03 .05
.2 .3 .2 .5 .7 .3 1,8 .8
7- 4 - 4 - ' 2
0-0-0-0
C-32
-------
Table C-10
INLAND STEEL HONTHLY OPERATING REPORT DATA
APRIL, 1973 MAY, 1973
Concentrations in mg/z except * = ug/i
0
w
u>
OUTFALL 001
MONTH APR MAY
BOD
COD
PHENOL* 15 9
CYANIDE
OIL 3 3
SS 25 15
SULFATE
NH3-N
TOT. Fe
CHLORIDE
002 003 004 005 OOr, Ou7
APR MAY APR MAY APR MAY APR "AY B^P, MAY APS MV
2 3 9 5 12 5 18 17 11
27 11 29 10 30 21 34 la 30 11
33 27
.78 .58
16 16 57 11
I'll 012 Oil
APR -!AY APR ".AY APR
7 '
20
42
.04
1 ] 2 2 3
30 1-1 25 17 35
11
.81
1.7
17
"AY
6
20
3G
.03
4
2f,
?7
.G5
4.1
]Q
01"
APR
8
22
56
.04
4
27
32
.-il
2.5
19
016*
MAY APR 'IAY
6
18
34
.03
4 1 '
17 12
28
.03
2.G
IB
017 018
APR '1AY APR !*AY
35 11
28 21 21 15
-------
9.3 Waste Treatment
The last major program for wastewater treatment ended in
1970 with the completion of a $10 million "terminal treatment
plant" which consolidated the flow from six outfalls. This
treatment facility receives effluents from numerous finishing
operations, the sinter plant and the open hearth shop. Treatment
consists of primary settling basins, oil skimmers and a 1000-ft
terminal settling basin (Figure C-8).
Other waste streams receiving treatment as part of this
most recent phase include the 80-in. cold strip mill, blast
furnace waste, electric furnace and biller caster shops. Waste
from the basic oxygen furnace and the 12-in. merchant bar mill
are treated and recirculated. Acid pickle liquor is now being
discharged into a deep well (4300 ft) at a rate of 164,000 gpd.
Prior to 1965, many additional plant processes received
treatment systems. What remains now are fifteen active dis-
charges with total net parameter loads shown in Figure 4.2.
Although individual effluent streams may not contain excessive
amounts of pollutants, the total volume of water discharged
daily (1008.9 mgd) indicates a large pound loading of pollutants
reaching Lake Michigan. Phenols average 440 Ib/day and NHo-N
average 5536 Ib/day.
A citizen complaint against Inland filed before the Stream
Pollution Control Board has resulted in an eight-point program
of pollution control. Plans include additional treatment for
outfalls 003, 004 and 005, plant #2 and #3 blast furnace wastes,
and acid pickle liquor line improvements. Further action and
approval by the Indiana Stream Pollution Control Board is
expected. In addition, an Illinois lawsuit (People of the State
of Illinois vs Inland Steel Co. 1974) has resulted in a finding
that Inland Steel Co. is polluting Illinois waters of Lake
Michigan, and the parties havfe been ordered to negotiate
corrective action.
C-34
-------
Figure C-8
INLAND STEEL COMPANY TERMINAL WASTE TREATMENT
Process
water
i
OJ
Ln
Process
water
SCALP IIIG
TAJIK
OIL CONG.
SCALPING
TAIIK
OIL CCT7C.
TAIIK
1,000' TEPJ1INAL SETTLING
BASIN
1,000' TERMINAL SETTLING
BASIN
OUTFALL 013
-*- OUTFALL 014
-------
10. YOUNGSTOWN SHEET AND TUBE C'O., EAST CHICAGO
10.1 General Description
The Youngstown Sheet and Tube Co. Indiana Harbor Works is
an integrated steel producing facility located adjacent to the
Indiana Harbor Canal and Lake Michigan in East Chicago, Indiana.
This facility includes coke ovens, blast furnaces, open hearth
and EOF processes, primary and secondary mills for the production
of sheet, galvanized tin, bar, plate and tube products. In 1971,
7906 tons of steel were produced daily. Water discharges from
cooling and process lines total 291 mgd from 11 outfalls
(Council on Economic Priorities 1973).
10.2 Data Evaluation
There are 11 outfalls which discharge directly to the IHC.
The discharges are shown in Figure C-7. Flow from these outfalls
averaged 291.67 mgd at the time of filing the NPDES permit in
June 1971. Present flow and process line information is pro-
vided in Table C-ll. Most existing treatment facilities were
completed by late 1970. Permit data in Tables 4.2 and C-12
should therefore be an accurate portrayal of existing conditions.
Data comparisons between NPDES, ISPCB 24-hr surveys and
monthly operating reports are of limited value since all param-
eters for all outfalls are not given. Available data are com-
pared in Table C-13.
The most dramatic differences occur between reported values
on the NPDES and those values obtained in a 24-hr composite
sampling conducted by the Indiana Stream Pollution Control Board
on June 13 and 14, 1972. These data indicate values in excess
of those reported in the NPDES for suspended solids, iron, and
phosphorus. Iron content was exceptionally high for outfalls
004 and 005 with values of 90 and 45 mg/H, respectively.
C-36
-------
Table C-ll
YOUNGSTOWN SHEET & TUBE COMPANY
NPDES AND ISPCB OUTFALL IDENTIFICATION AND FLOWS
JULY 1973
NPDES
001
002
003
004
005
006
007
008
009
010
OUTFALLS
ISPCB
20
2
4
8
11
12
13
22
14
15
FLOW-MGD
15.2
2.0
.07S
1.233
2.24
6.2G
14.6
9.53
50.9
Oil
ISA
65.0
PROCESS LINE
Central Waste
Treatment Plant
Cold Reduced
Sheet Mill
irl Tin Hill
#1 Tin Mill
#1 Tin Mill
Coke Plant
Coke Plant
Coke Plant
Sinter Plant
Blast Furnace
Cooling Uater
Sinter Plant
C-37
-------
Monthly operating reports submitted by the company have
little information for some outfalls and none for others. An
accurate and reliable picture of present effluent discharges is
difficult to assess for the parameters of suspended solids, iron,
and phosphorus. Ammonia nitrogen, phenols and oil values appear
to be consistent between NPDES and monthly operating reports data.
10.3 Waste Treatment
Process water from the cold reduced sheet and tin mills is
routed through the Central Waste Treatment Plant (CWTP) consisting
of primary mixing tanks, scalping tanks, secondary mixing tanks,
final clarifiers and sludge thickeners. The primary purpose is
to remove oil and solids in the waste stream. At present there
is an emergency by-pass around the CWTP which would discharge
untreated wastes into the IHC. After treatment the values (in
Table C-13) for iron, oil and suspended solids are still high.
They are 5, 8 and 40 tng/Jl, respectively. Youngs town monitors
this effluent daily but does not analyze for phenols, iron, and
ammonia nitrogen. After treatment, the effluent is combined
with noncontact cooling water from the temper mill of the No. 2
tin mill, and discharged through outfall 001.
Flow of 3.62 mgd of once-through noncontact cooling waters
from the No. 2 cold reduced sheet mill is discharged without
treatment through outfall 002. Outfalls 003, 004, and 005 are
all storm water and noncontact cooling water from electrolytic
cooling, forming and pickling line discharges and receive no
treatment. Again, these are not monitored.
C-38
-------
Youngstown Steel and Tube Company
IN 070 0X3 2 720319
Table C-12
YOUNGSTOWN SHEET AND TUBE COMPANY
Application Date: July 1, 1971
EFFLUENT CONCENTRATIONS
mg/i except * = g/i
OUTFALL*
§
1
I
U)
V0
001 93 5.5 82 614 596
002 112 1.5 8 199 194
003 114 1.8 12 200 193
004 110 5.4 8 219 205
005 62 2.6 4 282 244
006 132 10.4 85 228 213
007 108 3.1 36 217 202
008 110 27.8 53 218 198
009 106 3.4 12 216 200
010 J.10 3.5 24 227 199 107
0X1 132 1-6 8 310 283
40
19
17
22
26
19
20
22
22
.07
22
8
3
4
6
11
4
12
10
5
9
7
2
2
2
2
3
31
2
4
2
2
3
2
4
3
3
3
7
3
3
4
3
3
.24
.24
.24
.23
.34
.24
.24
.23
.26
.25
.19
. 009 65
.016
.024
. 022 88
.006 125
.048
.028
.031 45
.052
.041
.028 22
-
5
9
13
39
4
6
6
5
7
17
235 620
167 16.4
290
170 37
30
14
13.7
235 21.8
.01 .76 5000
28 .58
5750
9700
112 28.8
37 .04
29
21 .17 .75 8550
19
3.75
10.50
2.5
13
22
8
12
113
10
11
14
8
14
6.4
13 10
2090
303
290
11
-------
Table C-13
YOUNGSTOWN SHEET & TUBE EFFLUENT DATA, mg/4
COMPARISON OF NPDES, MONTHLY OPERATING REPORTS AND EFFLUENT SURVEYS
o
I
Monthly
ISPCB operating
Parameter,
mq/t
Chloride
Sulfate
Ammonia-Nitrogen
Phosphorus
Iron
Oil and grease
Phenols
Suspended solids
Chloride .
Sulfate
Ammonia-Nitrogen
Phosphorus
Iron
Oil and grease
Phenols
Suspended solids
Chloride
Sulfate
Ammonia-Nitrogen
Phosphorus
Iron
Oil and grease
Phenols
Suspended solids
NPDES
_
62.0
2.0
0.009
5.0
8.0
_
40.0
28.0 .
16.4
2.0
0.024
_
1.13.0
_
17.0
_
37.0
3.0
0.006
9.70
11.0
26.0
24-hr survey
report
6/13/72 March 1973
Outfall
_
_
1.0
0.3
2.1
4.0
0.01
15.0
Outfall
_
_
-
-
_
-
_
—
Outfall
2.6
0.4
45.0
6.9
0.004
13.0
001
_
_
-
_
-
5.0
_
12.0
003
_
_
-
-
-
-
-
—
005
-
-
Monthly
operating
report
April 1973 NPDE5
_ _.
_
2.0
0.016
-
4.0 12.0
- -
11.0 19.0
_ _
290.0
2.0
0.022
5.750
10.0
— -
22.0
112.0
30.0
31.0
0.048
14.0
2.09
19.0
Monthly
IS?CB operating
24-hr survey
report
6/13/72 March 1973
Outfall
_
-
0.8
0.6
1.3
3.1
0.001
97.0
Outfall
_
-
1.1
0.4
90.0
4.8
0.001
270.00
Outfall
-
9.0
0.4
1Q
.a
3.6
1.72
100.0
002
_
-
-
-
-
-
-
—
004
_
-
-
-
-
-
-
"
006
-
15.0
12.0
1.63
42.0
Monthly
operating
report
Aoril 1973
-
-
-
-
-
—
—
_
-
-
—
-
-
—
-
5.0
5.0
1.10
4.0
-------
Table C-13 (cont.)
O
I
Parameter,
mq/l
UPOES
Monthly
ISPCB operating
24-hr survey report
6/13/73 March 1973
Oatfall 007
Chloride
Sulfate
Ammonia-Nitrogen
Phosphorus
Iron
Oil and grease
Phenols
Suspended solids
Chloride
Sulfate
Ammonia-Nitrogen
Phosphorus
Iron
Oil and grease
Phenols
Suspended solids
Chloride
Sulfate
Ammonia-Nitrogen
Phosphorus
Iron
Oil and grease
Phenols
Suspended solids
37.0
14.0
2.0
0.028
_
8.0
0.303
20.0
_
_
2.0 .
0.052
—
-
_
22.0
21.0
21.8
3.0
0.028
8.550
10.0
11.0
22.0
_
-
-
-
_
3.4
_
3.0
Outfall
_
_
-
-
-
2.8
0.003
72.0
Outfall
_
-
2.2
0.2
2.8
2.4
0.072
13.0
_
-
-
-
_
-
_
-
009
_
_
-
-
-
-
_
5.0
Oil
_
-
-
-
-
-
-
-
Monthly
operating
report
Apjril 1973 NPDES
29.0
13.7
4.0
0.031
_ _
14.0
0.29
22.0
_. _
_ _
2.0
0.041
- -
6.4
_ _
0 107.0
_
-
-
-
-
-
-
-
Monthly Monthly
ISPCB operating operating
24-hr survey report report
6/13/73 March 1973 April 1973
Outfall 008
_
_
_ _
— _ _
_ _ _
14.0 6.0
.: _
15.0 0
Outfall 010
_
_ • _ _
_ _ _
_ _
_ _ _
4.5
0.017
85.0 17.0 13.0
-------
Outfalls 003, 004 and 005 convey untreated cooling water
and storm water from the No. 1 tin mill including the electro-
lytic cooling, forming and pickling lines. Process wastes from
these lines are diverted to the CWTP. Although this stream is
designated as noncontact cooling water, reported effluent values
are very high for iron, phenols and oil (see Table C-12) indi-
cating some contamination. Outfalls 006, 007, and 008 are
represented as once-through noncontact cooling waters from the
ammonia processing and light oil areas of the coke plant;
however, outfall 006 has 31 mg/£ of NH3-N, 14 mg/jt of oil
and grease, and 2.09 mg/£ of phenols. Outfalls 007 and 008 have
values of 8 and 14 mg/l of oil and grease. Monthly reporting
for 006 includes NHo-N phenols and oil, while no reporting is
done for 007. Outfall 008 receives only oil and grease and
suspended solids monitoring.
Condenser cooling water from the on-site power station is
discharged without treatment through outfall 009. There is an
emergency connection between 009 and 010 which Youngstown reports
as normally closed. Flow is normally 64.46 mgd.
Outfall 010 discharges once-through noncontajt cooling water
from No. 1-4 blast furnaces and heated waste waters from the
No. 2 continuous buttweld mill. Also on this line is the emer-
gency overflow /"from the blast furnace gas cleaning plant.
Effluent from the No. 2 continuous buttweld mill is treated in a
scale pit to remove oil and solids. Table C-12 for 010 indicates
very high suspended solids, 107 mg/jK and relatively high oil,
6.4 mg/j£. Monthly operating reports include only one parameter,
suspended solids, which are based on one 24-hr composite sample/
month.
C-42
-------
Outfall 001 receives treated effluent from various mills at
Youngstown including the No. 1 continuous buttweld mill, billet
mill, No. 1 and 2 blooming mills, seamless mill, and the 10-in.
and 18-in. merchant mills. All waste lines receive individual
treatment from scale pit for oil and solids removal. The flow
from six scale pits is then channelled to the Main Scale Pit for
further oil recovery. Here noncontact cooling water from the
No. 2 open hearth, EOF mill water, primary treated wastes from
the seamless mill and boiler house are added to the flow. After
treatment at the main scale pit, the effluent then passes to the
terminal lagoon for final oil and sludge removal. This treated
effluent then is mixed with 6700 gpm untreated mold cooling water
from the EOF. An emergency overflow line exists which will
by-pass the No. 2 open hearth gas cleaning treatment system
directly to the Main Scale Pit. Reported values for oil, phenols
and iron indicate inadequate treatment (Table C-12).
In all cases, except for 001, monthly reports are based on
one 24-hr composite sample. Source of much flow, treatment,
outfall data is Youngstown Sheet & Tube Co. Drawing No. 569849
5/11/72 (U.S. EPA Application file).
10.4 Unreported Discharges
There are four discharges to a lagoon within the breakwater
for which no NPDES application for permit is on file. These
four discharge 118 mgd into a lagoon which is open to Lake
Michigan by a 200-ft opening in the breakwater (U.S. EPA NPDES
application file). Youngstown alleges that intake from the
lagoon exceeds the 118 mgd and, therefore, that flow is always
from the lake, in effect, causing recirculation.
Pickle liquor is stored in a lagoon onsite and removed by
an outside contractor for disposal.
C-43
-------
1-1. U.S. STEEL - GARY
11.1 Introduction
U.S. Steel's Gary Works is one of the largest steel mills
in the country. There are 829 coke ovens, 12 blast furnaces,
5 sinter plants, and 6 basic oxygen furnaces (3 are under con-
struction). It is a completely integrated mill with all aspects
of steel manufacturing represented.
At the Gary works, there are ancillary divisions for specific
product manufacturing. These are National Tube Works, American
Bridge Division and Universal Atlas Cement Division (NPDES appli-
cation file).
11.2 General Description - Water Discharges
There are 39 individual outfalls at the Gary Works for which
NPDES permits have been requested. These are shown in Figure C-9
and listed in Table C-14. Five of these ourfalls discharge to
Lake Michigan and the remaining 34 discharge to the Grand Calumet
River, which drains into the Indiana Harbor Canal and therefore
to Lake Michigan. Total discharge flow from the Gary Works is
804 mgd. Of this, 552.5 mgd is discharged to the Grand Calumet
River through 34 outfalls and 251.5 mgd to Lake Michigan through
5 outfalls. These 34 outfalls from U.S. Steel constitute nearly
the entire flow of the Grand Calumet River at 552.5 mgd or
913.4 cfm.
The NPDES application, revised in 1972, indicates 15 Grand
Calumet outfalls for which no flow and parameter data is given.
Of these 15, two, 005 and 014, have been permanently discon-
tinued. Outfalls 013, 024 and 025 are storm water overflow
sewers. A recent U.S. Steel flow drawing GW-202752 (NPDES
application) indicates that two outfalls which previously had no
flows now are operational. These two are Oil and 038 with flows
of 3.5 mgd and 10.4 mgd, respectively.
C-44
-------
LAKE M/CM/6 AM
o
*>
Ol
Figure C-9
DETAIL MAP SHOWING OUTFALLS OF GARY WORKS, U.S. STEEL CORP.
Legend is on following page
-------
Figure C-9
U.S. STEEL - GARY WORKS
NPDES
002
007
009
010
Oil
015
017
013
019
020
021
022
020
029
030
031
032
033
034
035'
03G
037
osa
039
OUTFALL
inrcB
GW-l
GW-2
GW-2A
GW-1
CW-3A
GW-4
GW-S
GU-G
Gw-7
TI-77>
ry T_O
GVJ-10
GU-10A
GIT- 11
H'-llA
G'.;-12
GW-l 3
ST-l*
ST-17
GU-L1
CW-LlA
ST-L5
ST-L2
ST-1,6
LEGEND
FLOW MOD
27.3
16.4
5.7
4.7
3.5
1.3
G4.5
31.C
5.7
109.7
25.2
no FLOW
42.3
::o FLOH
71. G
NO FLO!.'
7.7
3.1
26. 8
7G.3
23.2
7.0
10.4
71.3
TTEATf'IFNT *
P W/T
P-1TT
P W/T
P-NT
P VJ/T
P-NT
P W/T
H-C
:i-c
TJ-C
P-NT
P W/T
P t-7/T
'I-C
P-IIT
P V7/T
N-C
N-C
N-C
1J-C
P W/T
* p = process waste
W/T = waste treatment
NT - no treatment
N-C = noncontapt cooling water
C-46
-------
OUOTALL *
001
002
003
004
OOS
006
007
008
009
010
Oil
012
013
014
015
016
017
018
019
020
021
022
P23
024
025
026
027
028
029
030
031
032
03)
034
035
036
037
038
039
T»ble OH
U.S. STEEL GARY WORKS OUTFALL SUMMARY
Source: NPDES Application
FLOW(HOD)
1.8
.32
.01
42.3
71.3
AVERAGE PH
7.9
7.7
7.7
7.9
7.6
7.2
AVERAGE TEMPERATURE
WINTER - SUMMER
27.3
.005
.029
.004
16.4
5.7
4.7'
7.7
7.7
8.0
7.9
7.9
'•2
7.6
61
48
-
49
61
57
59
82
68
77
70
86
79
95
81
64.5
31,8
5.7
109.7
25.2
7.1
7.5
7.9
7.4
7.1
63
50
59
54
_
88
75
75
93
75
7.7
3.1
26.8
76,8
28.2
7.0
7.2
6.7
7.5
7.6
7.8
7.7
57
61
59
54
55
54
68
73
75
75
84
72
C-47
-------
There are three categories of active outfalls at the Gary
Works, noncontact cooling water, process water without treatment
and process water with treatment. The first, noncontact cooling
accounts for 264.1 mgd of flow. Outfalls in this category are
018, 019, 032 and 039 which discharge to the Grand Calumet River.
Outfalls 35-38 also are noncontact cooling but discharge to Lake
Michigan (NPDES application).
Process water which receives no treatment totals 88 mgd, all
of which enters the Grand Calumet River. These outfalls include
007, 010, 015, 020, 021, and 033. Wastes from the coke plant,
the basic oxygen furnaces, continuous casting line, open hearth
furnaces, the No. 3 sinter plant and the atmospheric gas plant
are discharged from these lines.
The remaining outfalls 002, 009, Oil, 017, 028, 030, 034, and
039 discharge 298.6 mgd of treated waste waters. Wastes from
the Gary Tube Works amounting to 27.3 mgd are discharged through
outfall 002. Blast furnace waste water amounting to 70.2 mgd
are treated and discharged through outfalls 009, Oil and 017.
Wastes from the bar, slab, blooming and 160/210 plate mills
are treated and discharged through outfalls 028 and 030. These
discharges average 103 mgd.
Wastes from operations conducted at the 80-in. and 84-in.
hot strip mills are treated at the terminal treatment plant and
discharged through outfall 034 with a flow of 26.8 mgd. Separate
waste and treatment lines exist for specific operations of the
80-in. and 84-in. hot strip mills. Wastes averaging
71.3 mgd receive treatment and are discharged from outfall 039.
11.3 Parameter Evaluation
Table C-15 gives the effluent parameter data for all 39
outfalls. These data were originally submitted July 1, 1971.
Since then, U.S. Steel has updated their information twice.
The values in Table C-15 should therefore indicate present
C-48
-------
U. I. lt««l
tt» 372 - 0608
0*ry
TabU C-15
U.S. STEEL EFFUJEWT CONCENTRATIONS
Application Data: July 1, 1971
Conctntwtloni, mg/i axeapt x - ug/l
001*
002
003
004
005*
006
007
008 *
009
010
Oil *
012*
013*
014*
015
016*
017
oia
019
020
021
022*
023
024*
025-
026*
027
026
029*
105 «.' 29 233 221 12 111 0.2 .9 .16 * 4 3 20.S 148 28 .3 10
94 1.1 12 159 111 2 46 .7 .9 - 07 3 1 1.7 122 21 .2 12
96 11.4 200 790 61 218 197 1.2 2.0 .5 .1 54 S 12 131 47 .2 15
103 .9 53 218 1M 34 71 .2 .4 .2 .03 5 1 3 123 24
10l 5.8 22 l&l 172 9 87 .7 2.6 .58 .01 5 2 14.5 76 31
1900 2.5 3.8 20 770 3
300 8 2 160 2
800 6 1.8 80 11
800 4.0 1.6 - 50 5 -
1300 9 1.9 - 590 1 32
4.9 18 326 291 35 44 5.6 6.6 0.4 06 9 20 - 174 40 .4 26 .IS 1.5 20° 280° 18'4
25° 3 2°
40 4 239 202 37 127 2.0 2.7.38 Ol
6 36 158 36 .3 14
3300 2.8 7.5 20 100 - 18'
12.6 29 182 174 8
8.3 137 25
1100 2.3 3.5
154 8.9 33 257 231 26
2)3 7.0 J6 184 178 €
226 6.8 4 182 175 7
187 10 36 190 179 11
215 2.5 50 224 214 10
7,9 ,47 .03
.3 1.0 .05
.3 .3 .02
.8 .2 .03
.7 .1 .03
55 10
5
6.5
4.0
2.3
163 38
138 27
138 29
2.0 137
2.2
24
8800 14.8 5.7
200 4.8 3.2
200 3.5 8.8
1300 2.2 3.8
1500
120 1.1
151 .3
175 174
223 204
2.9 141
1.5 151
100 1.9 2.8
5800 4.5 2.8
031*
032
033
034
035
036
037
038*
039
2700 3.1 2.2
104 0.4 12 200 19S 5 60
103 1,3 20 364 368 1& 67
78 6.2 43 474 458 16 165
115 0,7 *9 156 l53 3 32
115 2,8 H 16a l58 10 28
11C 0,7 19 165 l59 6 33
97 7 23 226 205 21 59
.6
0.3
.02
.02
4 1.0 596
53 3.0 592
9 7.5 572
596
I - 580
135 .3
139 .4
400 1.9 3.4
2600 3.5 9.1
900 8.0 18.2
2.1 3.0
100 1.9 3.4
1100 3.7 2.7
C-49
-------
conditions at each outfall, as reported by U.S. Steel. Effluent
loads from Combinatorics (1974) are given in Chapters 13 through
18.
Inconsistencies are apparent when the NPDES application data
are compared with data from other sources. U.S. EPA and Indiana
Stream Pollution Control Board 24-hr analyses were used in the
comparison and selected data are given in Table C-16. Most
importantly, two outfalls Oil and 038, listed by U.S. Steel as
inactive, are now operational. This is confirmed by both EPA
and ISPCB analyses and U.S. Steel drawing No. GW-202752 previously
referred to above. No data have been submitted to EPA for these
outfalls.
Effluent parameter data comparisons given in Table C-17
indicate some other inconsistencies with reported values. Outfall
002 has substantially higher NHo-N values in recent surveys than
in the NPDES application. Outfall 007 has one sample with param-
eter concentrations several times greater than reported for NPDES.
Outfall 009 is substantially higher for phenols and oil while
outfall 010 shows a general reduction for most values. Outfalls
015 and 018 are consistent but NHo-N for 017 is much higher along
with phenols and oil. Consistent values occur for 019, 020, 021,
028, 030, 032, 035, 036, 037, and 039. U.S. EPA and ISPCB 24-hr
analyses show increases in some parameters for 033 and 034.
11.4 Waste Treatment Facilities
Wastes from the Gary Tube Works are given primary treatment
in a scale pit and then combined with untreated coke plant wastes
for direct discharge through outfall 002 into the Grand Calumet
River. Average flow per day is 27.3 mgd.
Blast furnace gas wash waste water is collected in scalper
clarifiers. Overflow from the scalper pits is diverted directly
to outfalls 009 and Oil. Undiverted wastes continue from the
scalpers to two settling basins. After treatment, wastes are
channeled to five flue dust pits and from there to outfall 017.
Flow from these lines averages 94.4 mgd.
C-50
-------
PARAMETER
Table C-16
U.S. STEEL GARY WORKS EFFLUENTS
COMPARISON OF EPA ANALYSIS WITH PERMIT APPLICATION, mg/£
Source: NFIC Analysis 6/22/71 from EPA application
NPDES Application July 1971
OUTFALL 002 OUTFALL 007 OUTFALL 009 OUTFALL 010 OUTFALL Oil OUTFALL 015
EPA Applicat. EPA Applicat. EPA Applicat. EPA Applicat. EPA Applicat. EPA Applicat.
AMMONIA
PHENOL
CYANIDE
SUSP. SOLIDS
AMMONIA
PHENOL
CYANIDE
SUSP. SOLIDS
AMMONIA
PHENOL
CYANIDE
SUSP. SOLIDS
AMMONIA
PHENOL
CYANIDE
SUSP. SOLIDS
0.12 0.2
0.046 N.D.
0.02 N.D.
26 12
OUTFALL 017
EPA Applicat
6.3 0.1
0.693 0.288
4.27 4.37
35 26
OUTFALL 030
EPA Applicat.
0.15 N.D.
0.009 N.D.
0.0 N.D.
29 11
OUTFALL 037
EPA Applicat.
0.1 0.2
N.D.
0.0 N.D.
21 6
2.1 0.7
0.085 0.032
0.06 N.D.
53 9
OUTFALL 018
. EPA Applicat .
0.39 N.D.
0.008 0.004
0.07 0.01
23 6
OUTFALL 031
EPA Applicat.
0.12 N.D.
0.15 N.D.
0.02 N.D.
29 5
OUTFALL 038
. EPA Applicat.
0.11 No Flow
0.0
0.0
25
6.7
0.483
1.37
15.05
5.6
0.02
0.15
35
OUTFALL 019
EPA Applicat.
0.22
0.0
0.01
34
N.D.
0.002
N.D.
7
OUTFALL 033
EPA Applicat.
0.33
0.0
0.02
34
N.D.
N.D.
0.02
16
0.93 2 6.6 No Flow 0.07 0.1
0.069 0.18 0.539 " 0.0
0.0 N.D. 2.2 " - N.D.
14 37 36 " 27 8
OUTFALL 020 OUTFALL 021 OUTFALL 028
EPA Applicat. EPA Applicat. EPA Applicat
0.47 0.4 0.13 0.7 0.28 N.D.
0.053 0.018 - 0.011 0.022 N.D.
0.18 N.D. " 0.09 0.04 N.D.
25 11 S3 10 16 19
OUTFALL 034 OUTFALL 035 OUTFALL 036
EPA Applicat. EPA Applicat. EPA Applicat.
0.27 0.2 0.09 0.3 0.08 N.D.
0.129 0.03 - N.D. - 0.002
0.84 N.D. 0.01 N.D. 0.0 N.D.
38 16 31 3 25 10
OUTFALL 039
EPA Applicat.
0.13
0.009
0.0
25
0.3
N.D.
N.D.
21
C-51
-------
Table C-17
U.S. STEEL GARY WORKS EFFLUENT CONCENTRATIONS ma/i
COMPARISON OF NPDES, MONTHLY OPERATING REPORTS AND EFFLUENT SURVEYS
Study by:
Study date:
Outfall 002
SS
Fe
NK3-N
Phenol
Oil
Outfall 007
US
Fe
NH3-N
Phenol
Oil
Outfall 009
SS
Fe
1JH3-N
Phenol
Oil
Outfall 010
SS
Fe
NH3-N
Phenol
Oil
Outfall Oil
SS
Fe
NH -N
Phenol
Oil
Outfall 015
SS
Fe
NHj-M
Phenol
Oil
Outfall 017
SS
Fe
NH3-N
Phenol
Oil
NPDES
7/1771
12
1.9
0.2
-
3.0
9.0
1.3
0.7
0.032
1.0
35
2.8
5.6
0.02
3.0
37
3.3
2.0
0.18
~
-
-
-
-
-
8.0
1.1
0.1
-
3.0
26
B.8
0.1
0.288
-
Survey
6722771
26
2.92
0.72
0.046
NT
53
NT
2.1
0.085
-
15
6.1
6.7
0.483
NT
14
1.32
0.93
0.069
NT
36
9.9
6.6
0.539
NT
-
-
-
-
-
35
10.3
6.3
0.693
-
Analysis
5777T5
10
1.1
O.i
0.029
5.6
76
4.1
2.4
0.029
6.0
77
0.41
4.9
0.47
7.8
3.0
1.1
0.9
0.071
6.0
16
5.5
4.6
0.182
2.1
8.0
0.3
0.1
0.001
7.0
44
14
4.9
0.38
7.0
Analysis
6/9/73
9.0
0.8
2.0
0.015
-
5.0
0.9
2.0
0.122
-
15
2.3
4.7
0.077
-
6.0
0.5
1.2
0.064
7.8
-
-
-
-
-
10
0.7
C.I
0.001
-
11
4.0
4.3
0.19
-
U.S. steel
June 1973
21
'-
-
-
3.0
31
-
2.3
0.056
2.0
44
4.5
-
-
2.0
8.0
0.5
-
-
2.0
20
2.0
-
-
1.0
11
0.1
-
-
2.0
29
2.3
-
-
2.0
C-52
-------
I«bl« C-17 (oont.)
o\i«»ll Die in ISPCD iBfcn
itud)> byi HPDM »urv»v ^nlyiU m«iyiii U.S. it
SB
Po
Phenol
Oil
Outfall 019
Phenol
Oil
Outfall 020
Phenol
Oil
Phenol
Oil
NU3-N
Phenol
Oil
Outfall 030
Phenol
Oil
Outfall 032
NH3-N
Phenol
Oil
Outfall 033
SS
Fe
NH3-N
Phenol
Oil
run t
C.O
o.J
-
0.004
3.0
1.0
0,20
-
0.002
4.0
11
1.3
0.4
0.018
4.0
10
1.5
0.7
0.011
3.0
19
5.8
-
-
2.0
11
2.7
-
-
3.0
5.0
0.4
-
-
3.0
16
2.6
-
-
4.0
713771 VV?) Wl 1
23 10 3.0
1.51 0.3 1.1
0.39 - 0.1
0,008 0.008 0.001
4.5
34 9.0 6.0
1.32 0.4 0.4
0.22 0.2
NF 0.019 0.001
NT 5.7
25 5
1.98 0.2
0.47 0.2
0.053 0.001
NT 0.1
53 8.0 7.0
3.8 0.4 0.2
0.13 0.1 0.1
NT 0.01 0.04
"
16 24
6.3 8.0
0.28 0.2
0.022 0.010
8.7
29 13
6.8 5.1
0.15 0.2
9.0 0.003
7.4
29 25 7.0
4.2 11.0 0.5
0.12 0.2 0.1
0.015 0.001 0.012
7.3 4.1
34 55 30
16.4 25 14
0.33 0.4 0.3
NF 0.0001 0.0001
5.7 4.4
uno 191
17
9.3
-
-
1.0
15
0.1
-
-
1.0
75
2.9
-
-
-
9.0
0.2
-
-
1.0
24
1.2
-
-
3.0
14
0.9
-
-
2.0
3.0
0.5
-
-
1.0
23
7.7
-
-
1.0
C-53
-------
T«bl« C-17 (cont.)
Outfall 034
Study byi
Study Datei
SB
Fa
HH3-H
Phenol
Oil
Outfall 035
SS
Fo
N)I3-H
Phenol
Oil
Outfall 036
SS
Fe
HHj-H
Phenol
Oil
Outfall 037
SS
Fe
IIH3-N
Phenol
Oil
Outfall 038
SS
Fe
NH3-fl
Phenol
Oil
Outfall 039
ES
Fe
NH3-N
Phenol
Oil
EPA ISPCD ISPCn
NPDES Survey Analysis Analysis U.S. Steel
7/1/71 S/SS/71 J/S/73 S/19/73 Junn 1973
16 38 18 - 27
0.9 4.10 4.10 - 5.0
0.2 0.27 0.2
0.030 0.129 0.146
S.O - 7.9 - 7.0
3.0 31 4.0 - 5.Q
NT 0.2 - 0.1
0.3 0.09 0.1
NT 0.001
2.0 - 5.1 - 1.0
10 25 4.0 - 8.0
0.1 0.95 0.3 - 0.1
0.08 -
0.002 NT 0.001 -
2.0 - 3.7 - 1.0
6.0 21 3.0 6.0 12
1.1 4.5 2.9 1.2 .1.8
0.2 0.1 - 0.1
NT 0.001 0.001
3.0 - 5.5 - 1.0
25 6.0 13
107 - 0.4 0.3
0.11 - 0.1
NF 0.001
- 2.0
21 25 14 8 6
1.3 5.4 1.9 0.5 0.3
0.3 0.13 0.2 0.1
0.009 0.016 0.001
? - 4.5 - 2
C-54
-------
Wastes from bar, slab, blooming and the 160-210 plate mills
are diverted to three lagoons where oil is skimmed and collected.,
Wastes then pass through a scale pit for additional oil and sludge
removal. The treated effluent is discharged through outfalls
028 and 030 with a combined average flow of 141.8 mgd.
The terminal treatment plant receives wastes from the 80-in.
and 84-in. hot strip mills. Treatment includes four primary
separators, two settling tanks, flocculation clarifiers and a
centrifugal oil separator. Discharge is through outfall 034 at
26.8 mgd.
The last major treatment system is the 84-in. hot strip mill
filtration plant which receives wastes from both the 80-in. and
83-in. HSM's. There are through-primary scale pits, through-
secondary scale pits, one finishing pit, 12 sand filters, a
thickener and vacuum filters. Flow of 71.3 mgd from this facility
is discharged to Lake Michigan through outfall 039.
11.5 A11erna te Wa s t e Line s
Wastewater recirculation at the Gary Works accounts for
22.4 mgd. The 80-in. H.S.M., the 18-in. bar mill, the 160/210
plate mill and basic oxygen shops utilize recirculation for some
process lines. Future construction at the 84-in. H.S.M. will
add an additional 14.4 mgd to recycle systems.
A deep well disposal system is operational at Gary and
receives pickle liquor from the Gary Tube Works and the U.S.
Steel - Waukegan facility. The depth of the well is 4303 ft and
.wastes are injected at 210 gpm at 200 psi. Waste pickle liquor
consists of sulfuric acid 8-37%, ferric sulfate 18-251, ferric
chloride 15-20% and chromic acid 2-6%.
Coke plant wastes from the ammonia concentration operation
'are diverted to the Gary Municipal Sewage Treatment Plant.
C-55
-------
I 11.6 American Bridge and Universal Atlas Cement Divisions
These ancillary divisions of U.S. Steel do not have NPDES
applications on file for any discharges even though other sources,
as follow, do indicate the possibility of such discharges. A map
of discharges (Figure C-9) from U.S. Steel prepared by personnel
from the Indiana Stream Pollution Control Board on 8/23/73 (in
ISPCB files) indicates four unreported discharges; two from the
American Bridge Division and two from Universal Atlas Cement.
The American Bridge outfalls designated AB-15 and AB-16 are
located on the Grand Calumet River at Bridge St. Those outfalls
from Universat Atlas Cement are designated UA-L-3 and UA-L-4
on Figure C-10. They are located on Lake Michigan. Furthermore,
the existence of UA-L-4 is confirmed by U.S. Steel since they
include this outfall in monthly operating reports to the ISPCB.
Only data for oil, suspended solids and iron are given. Flow
is not reported.
C-56
-------
Uft-L-3
UA
n
i
Cn
Figure C-10
DETAIL MA? OF BTIFFINGTOH HARBOP. DISCHARGERS
-------
J12. U.S. STEEL SOUTH WORKS
I
12.1 Introduction
The U.S. Steel South Works is an integrated steel mill pro-
ducing 22,592 tons of steel per day (Attorney General Report,
page 4). Coke, however, is produced at the U.S. Steel facility
in Gary, Indiana and shipped to the South Works. Production
facilities which produce waste water discharges are the blast
furnaces, electric furnaces, basic oxygen process, sintering
plant, casting plants and bar mills.
The facility is located at the junction of the Calumet River
with Lake Michigan. There are two slips, the north and south
slips, which contain two outfalls shown in Figure C-ll. The
North Slip is separated from Lake Michigan by an air curtain to
retain any oil spills. At the origin of the North Slip is the
main plant water intake. Net flow through the North Slip is
reported by U.S. Steel as toward the intake, never to the lake
(Personal communication with plant officials).
12.2 Outfall Descriptions
The company has reported six outfalls in their NPDES appli-
cation. Outfalls 001, 002 and 003 discharge to Lake Michigan.
Outfalls 004 and 005 discharge to the Calumet River and outfall
006 discharges to the South Slip (see Figure C-ll). As reported
June 18, 1971, in the NPDES application, there is only one
process water discharge, i.e., outfall 006. Noncontact cooling
water is discharged through outfalls 001, 002, 003 and 005.
Outfall 004 is reported as inactive except for storm runoff.
12.3 Evaluation
NPDES application data from 1971 can not be considered
valid to the present discharge. On January 18, 1971, U.S. Steel,
the Illinois Attorney General and the Metropolitan Sanitary
,District of Greater Chicago (MSD) entered into a stipulated
C-58
-------
6S-0
fp A\ '<—t^u.'i^«____
§ /&• V%^% S^l
^^-' ~*~-'"
! ' /<•/«•. »\ f1/,// f>^ '
i r(. M^l^^//^'^
™W ft/fp^^^W/// w f!
^>-^>;oV*-:'.;-,< • fj; •
f ^^.^N//^-'-V-..<-,'' £ ; \r.
-------
(agreement leading to the complete recycle of process waste water
[with a blowdown entering the sewers of the MSB. The Order
!(#69CH3334 and 67CH5772) was the culmination of a legal battle
lasting three years.
Specifically, the Order provides that:
• A recycle system for process water from the
"South blast furnaces shall be completed by
October 31, 1972.
• A recycle system for process water from mill
operations shall be constructed according to
the following schedule.
• Recycle for the "South" side mills
shall be completed not later than
October 31, 1974
• The blow-down from the mill recycle
system shall be no greater than
3700 gpm and discharged to the MSD.
U.S. Steel South Works is presently in the process of
complying with this stipulated agreement. The treatment system
is shown in Figure C-12.
A report prepared for the Illinois Attorney General (Data
Graphics, Inc. 1970) proposed effluent concentrations which
correspond to interim levels achieved by the on-going construc-
tion of recycle systems, as given in Table C-18. These effluent
reductions will result in the following loads, based on flow at
17.4 mgd:
INTERIM EFFLUENT CONCENTRATIONS AT OUTFALL 006*
Parameter Load, Ib/day Concentration, mg/l
Suspended solids 15,025 10.3
Oil 1,586 10.9
C-60
-------
-------
Table C-18
U.S. STEEL SOUTH WORKS
INTERIM EFFLUENT CONCENTRATIONS AT OUTFALL 006
Parameter
Suspended solids
Oil
Phenol
Cyanides
Fluorides
Ammonia
Acid equivalents
Load,
Ib/day
48,080
3,172
114
145
238
114
5,083
*Data from Datagraphics Report,
Proposed effluent
mg/4
Average
41.3
2.73
0.097
0.124
0.204
0.097
4.37
concentration, *
Maximum**
80.4
5.3
5.19
0.24
0.39
0.19
8.50
July, 1970, Wastewater Treatment,
Reuse, and Disposal at South Works, U.S. Steel Corp., Chicago,
111.
**Based on 71.7 mgd flow.
C-62
-------
It is unclear at what stage U.S. Steel is presently at in
its construction schedule; however, total recycle should take
place by October 31, 1974.
Discharges of cooling water with flows are indicated in
Figure C-12.
063
-------
REFERENCES
Combinatorics, Inc., 1974
Load allocation study of the Grand Calumet River and Indiana
Harbor Ship Canal, Report to State of Indiana, Stream Pollution
Control Board.
Council on Economic Priorities, 1973
Environmental Steel, Washington, B.C.
Datamatics, 1970
Wastewater treatment, reuse, and disposal, Report at South Works,
U.S. Steel Corp., Chicago, 111, July 1970.
People of the State of Illinois and the Metropolitan Sanitary
District of Greater Chicago vs Inland Steel Co., 1974
Circuit court of Cook County, Illinois.
C-64
-------
APPENDIX D
MUNICIPAL SOURCES AND COMBINED SEWER OVERFLOWS
Di
-------
MUNICIPAL SOURCES AND COMBINED SEWER OVERFLOWS
This Appendix describes the status (on January 1, 1974) of
the sewage treatment plants and the combined sewer outfalls and
presents available data on the flows and loads of pollutants. In
general it will be seen that the indicators of municipal wastes
in this area have not improved recently, and may even have deter-
iorated in spite of improvements in some facilities. This is
caused partly by delays in construction and partly by diversion
of steel mill and other industrial wastes to certain facilities.
A list of plants is given in Table D-l, and maps in Figures D-l
and 4.1 (Chapter 4, Vol. I of this report).
1. EAST CHICAGO SANITARY DISTRICT FACILITIES
The East Chicago Sanitary District (ECSD) was formed in 1929
and includes the corporate boundary of the city of East Chicago.
The total population served is about 52,000, for which the sewage
treatment plant is adequate; however, about 12 major industries
also discharge to the ECSD sewers, and this creates problems dis-
cussed below. The district has a predominantly combined sewer
system. This description is from information provided to
Mr. Sweeney (1973) by personnel of the ECSD.
1.1 The District Wastewater Treatment Plant
The District wastewater treatment plant (WTP) is located on
the west branch of the Grand Calumet River in East Chicago (see
"B" on map, Figure 4.1, Chapter 4, Vol. I of this report). The
plant was put into operation in 1942 and has a 20-mgd activated
sludge type secondary treatment capacity.
Average discharge flow is about 12-13 mgd, but flows approach-
ing the 20-mgd plant design capacity are common. Some flow data
and effluent loads are given in Table D-2.
A 140-150 million gallon detention basin has been constructed
on the plant property, and its surface aerators provide additional
oxidation capability.
D-l
-------
o
I
ho
Table Dl
SUMMARY OF MUNICIPAL WTP DISCHARGES IN CALUMET AREA
Map
Ref.
No.
1.
System
Public Systems
Hammond S. D.
Hammond
Munster
Whiting
Griffith
Highland
Type of
sewer
c,s
c(s
c
c,s
c,s
Secondary
treatment
capacity,
mgd
36.0
Inflow
Average Receiving Point to
flow, mgd waterwav Lake Michigan
36.0 Grand Calumet R. I.H.C.*
Comment
Under construction
for expansion to
48.0 MGD capacity.
Contract area.
Contract area
Contract Area
East Chicago S.D.
East Chicago
Gary S.D.
20.0
12.5
Grand Calumet R. I.H.C.
4.
5.
6.
7.
8.
Gary
E . Gary
Merrillville
Portage
Chesterton
Chesterton
Porter
Valparaiso
Hobart
Crown Point
c.
c,
c.
S
c,
C,
S
c.
s
s
s
s
s
5
60.
3.
1.
6.
2.
0
0
5
0
1
1.8
46
1
1
3
2
1
.0
.2
.2
.5
.5
.7
Grand
Burns
Little
Calumet R.
Ditch
Calumet R.
Salt Creek
Deep River
Beaver
Dam Creek
I.H.C,
Burns
Burns
Burns
Burns
Burns
Ditch
Ditch
Ditch
Ditch
Ditch
Much Industrial
wastewater.
Newly expanded
Plant overloaded
to Turkey Creek
*Flow often is west to Illinois.
c is combined; s is separated.
-------
Table Dl (cont.)
REF.
No.
9.
10.
11.
12.
13.
? 14.
LO
15.
16.
17.
18.
19.
20.
System Type
of Sewerl
Semi -Public &
Private Systems
Bon Air Subd.
Brookview
Terrace Subd.
Knob Hill Subd.
Lake George Subd.
Lincolns Gardens
Rolling Hills
Est. Subd.
Schererville Hts.
Triple A. Util.
Ideal Dev. Inc.
Neighborhood Util.
South Haven Subd.
• Pleasant Valley
S
S
S
S
S
S
S
S
S
S
S
Secondary Trt
Cap. (MGD)
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
1.
36
10
10
10
20
035
06
05
10
10
4
Avg. Receiving
Flow (MGD) Waterway
Turkey Creek
Turkey Creek
Deep River
Deep River
0.16 Turkey Creek
Turkey Creek
0.05 Turkey Creek
Deep River
Salt Creek
Salt Creek
0.5** Salt Creek
Inflow Pt. Comment
to Lake Mich.
Burns
Burns
Burns
Burns
Burns
Burns
Burns
Burns
Burns
Burns
Burns
Ditch
Ditch
Ditch
Ditch
Ditch
Ditch
Ditch
Ditch
Ditch
Ditch • Expansion to
2.0 MGD
Ditch
Mobile Home Park
0.08
0.013** Squirrel Creek Burns Ditch
** Estimated.
-------
Table Dl (cont.)
REF. System Type Secondary Trt Avg.
No. of Sewer1 Cap. (MGD) Flow (MGD)
Receiving
Inflow Pt.
to Lake Mich.
Connaert
Semi-Public &
Private Systems
21. Robbinswood
Subd.
22. Oak Tree Park
Mobile Home Park
23. Elmwood
Mobile Home Park
24. Sands Mobile
Home Park
25. Porter County
Home
0.078
0.063
0.048
0.015
0.026 Salt Creek Burns Ditch
0.017 Salt Creek Burns Ditch
Damon Run to
0.04 salt Creek Burns Ditch
Damon Run to
0.01** salt Creek Burns Ditch
Septic Tank 0.003 Salt Creek Burns Ditch
**Estimated.
-------
a
i
Ul
Wastewater treatment facility
(The number beside each
refers to the Ref. No. on the
summary table.
Basin Boundary Line
Figure D-l
MAP OF LAKE-PORTER REGION WASTEWATER TREATMENT FACILITIES
-------
Table D-2
YEARLY EFFLUENT AVERAGES OF THE THREE MAJOR SANITARY DISTRICTS
Municipality
Hammond
East Chicago
(through 9/73)
Gary
J
Year
1966
1967
1968
1969
1970
1971
1972
1966
1967
1968
1969
1970
1971
1972
1973
1966
1967
1968
1969
1970
1971
1972
WTP design
capacity, Flow,
mgd mgd
36.00 35.1
32.1
33.0
35.
38
36
38
20.00 11.3
11.8
11.5
11.9
11.0
12.1
16.1
14.4
60.00 42.1
46.1
48,5
44.06
45.5
40.1
46.5
Raw,
mg/l
182
156
223
196
151
187
172
91
154
150
142
128
147
131
153
142
89
101
123
119
123
135
BOD
Final,
mg/£
22
21
39
24.4
22.6
20.9
36.2
9
16
28
32
43
48
54
56
10
16
11
12
16
22
29
Suspended solids
Load,
Ib/day
6,446
5,628
10,725
7,203
7,190
6,431
11,532
846
1,568
2,688
3,175
3,944
4,843
7,250
6,725
3,510
6,144
4,444
4,409
6,071
7,357
11,246
Raw,
mg/l
264
252
407
369
234
361
229
103
110
111
124
127
113
147
197
«.
239
200
202
224
230
225
Final,
mg/£
23
27
37
31
35
29
46
12
18
27
28
34
30
50
39
43
43
21
24
34
43
51
Load.
Ib/day
6,739
7,236
10,175
9,270
11,199
8,924
14,750
1,128
1,764
2.592
2,778
3,119
3,027
6,713
4,683
15,093
16,512
8,484
8,819
12,901
14,380
19,778
Source: Hammond S.D. WTP Monthly Operating Reports,
East Chicago WTP Monthly Operating Report.
Annual Report Gary Sanitary District.
-------
Interim phosphorus removal facilities were put into operation
in June 1972, and permanent facilities were operational by Septem-
ber 1973. The 80% P removal recommendations of the 1968 Lake
Michigan Enforcement Conference is being met according to District
personnel. Effluent concentration data in Table D-3 indicate that
the 1 mg/£ P concentration limit recommended as an objective by
the 1972 Lake Michigan Enforcement Conference is not always being
met. Other parameters are less well controlled, as will be
discussed below.
Chlorination of effluent discharged to the Grand Calumet
River is provided, but this is not effective in killing bacteria.
The reasons for this are discussed in the following.
1.2 Planned Plant Improvements
The Four-State Lake Michigan Enforcement Conference Technical
Committee (1968) put a July 1, 1977, deadline on completion of
advanced waste water treatment (AWT) by the ECSD, and the District
anticipates meeting this deadline. AWT plans were approved by
the Indiana Stream Pollution Control Board (ISPCB) and the U.S.
EPA, but the District is now reconsidering the methods involved
and finds them too costly. Possibly, new AWT plans will be sub-
mitted, and it is probable that feasibility planning of WTP
expansion to increase the design capacity from its existing 20-mgd
to a 26-30 mgd capacity may take place.
The ECSD is planning on a Fiscal 1974 infiltration study
which is expected to cost $200,000 and will help determine whether
sewer repair, WTP expansion, or both is necessary to handle the
problem of the increased flows to the WTP.
Problems of influent loads from industries are recognized
by ECSD.
A program of industrial influent analysis will be undertaken
in 1974, and it is estimated by the District that an additional
$150,000 for laboratory equipment will be spent to monitor
influents. Influent regulations so far have been limited to
informal agreements with industry.
D-7
-------
Table D-3
EAST CHICAGO SANITARY DISTRICT WASTEWATER TREATMENT PLANT REPORT*
1973
BOD
Mg/1
JAN.
FEB.
MAR.
APR.
7 MAY
00
JUN.
JUL.
AUG.
MGD
18.6
18.5
12.0
12.6
12.6
11.2
10.9
18.1
Raw
84
125
95
130
155
163
180
195
Fin.
26
36
48
45
63
66
70
75
SS
Mg/1
Raw
182
225
-
332
160
146
201
215
Fin.
38
35
42
78
33
31
29
38
NH3
Mg/1
Raw
76
79
93
76
94
100
117
100
Fin.
75
88
98
76
92
96
121
111
Cn~
Phenol
Mg/1 JUg/1
Raw
.40
1.2
1.12
1.30
1.34
1.04
0.85
0.88
Fin.
.33
.23
.49
1.16
0.18
0.63
0.43
0.53
Raw
5.6
1.18
1.40
2.3
1.25
2.16
1.39
4.3
Fin.
.34
.015
.02
.264
.02
.23
.06
1.24
Fe P04~
mg/1
Raw
3.7
3.1
-
3.3
3.6
2.9
2.6
3.4
Fin.
1.2
1.0
1.6
1.4
1.3
1.5
0.9
1.3
Mg/1
Raw
1.3
1.3
-
1.0
1.0
1.1
1.3
1.2
Fin.
0.2
0.2
0.3
0.3
0.4
0.3
0.3
0.2
N03~
Mg/1
Raw
6.2
5.8
5.8
4.6
4.6
4.3
3.2
3.6
Fin.
3.1
2.9
1.7
1.70
2.3
1.7
1.9
1.7
% Purif.
BOD
69
71
66
65
59
59
61
62
SS
79
85
78
78
79
78
85
87
•Source: East Chicago S.D. WTP Monthly Operating Reports
-------
1.3 Plant Performance and Effluents
Analysis of effluents from the WTP are shown in Table D-3.
The most striking deficiency is in NHo-N levels in the effluent.
This plant is an important source of NHo> and is causing viola-
tions of NH^-N values in the Lake, as described in Chapter 13.
The load is 10,000 Ib/day NH-j-N with a maximum of 30,000 Ib/day
(Combinatorics 1974). That the effluent has deteriorated can be
seen by comparing Table D-3 with Table D-4.
Excessive NH^-N has another harmful effect, in that it makes
effective chlorination impossible. Chlorine is known (Palin 1973)
to react with NHo> and residual chlorine is needed to sterilize
the effluents. Table D-3 does not report the bacterial counts-in
the plant effluents, but we believe that they are very high. On
November 30, 1973, IITRI sampled the Grand Calumet River upstream
and downstream of the plant outfall, and found high total coli-
form concentrations downstream (Table 16.4, Chapter 16, Vol. I
of this report). Effluents from EC WTP appear to be the largest
source of coliform bacteria measured in the IH.C as reported in
Chapter 16.
Table D-4*
EAST CHICAGO STP
SPECIAL EFFLUENT ANALYSIS, mg/jfc
Year
1966
1967
1968
NH3
18.9
23.6
48.5
Nitrate
-
-
0.71
Phenol
0.009
0.010
0.232
Iron Phosphorus
3.6
2.8
1.6 3.8
Cyanide
0.18
0.19
0.28
*(Technical Committee on Water Quality 1970)
D-9
-------
The amount of NH-, is far in .excess of what would be expected
in a plant serving a population the size of East Chicago. The
source of NH~ is the waste water from steel mills, primarily from
Inland Steel and Youngs town Sheet and Tube. This is shown in
testimony presented in a lawsuit (People of the State of Illinois
vs Inland Steel Co. 1974). The NHo comes from ammonia stills used
in coke oven operations. In addition to NHo, there are also
problems with other wastes. One of these is excess lime, which
is needed to raise the pH so that the NH^ can be distilled off.
Mechanical problems with the lime slaker sometimes result in
excesses of lime being sent to the sewer. When it reaches the
WTP, this lime can suddenly raise the pH, killing the bacteria
that function in the activated sludge process. The result is an
upset and a period of very poor sewage treatment. Other wastes
can be related to industrial sources as well. These include the
relatively high levels of cyanide and phenol shown in Table D-4.
Data are not given on oil, but its presence might be expected,
as well as heavy metals.
1.4 Pretreatment Guidelines
U.S. EPA guidelines (1973) for municipal treatment plants
receiving federal grants state that (p. 13) it is important that
no discharge from any source to the publicly owned treatment
works interfere with treatment processes or result in a violation
of effluent limitations. There must therefore be a legal basis
for regulating and controlling all discharges to the publicly
owned treatment works, such as a municipal ordinance. It may
be necessary to establish a local system which will allocate
waste loads to industrial users so that biological treatment
processes are not inhibited and to ensure that effluent limita-
tions are met.
The guidelines generally do not set limits on the concen-
trations of various pollutants discharged to the sewers, except
that they specify a 50 mg/£ limit for oil from refineries. The
guidelines specify several pretreatment processes that may be
D-10
-------
used by petroleum refiners, steel mills, and starch syrup plants,
but these do not appear to consider all of the problems to which
the East Chicago plant is exposed due to ammonia discharges.
Pretreatment guidelines for the steel industry are also given
in the EPA Iron and Steel Guidelines (1974). These guidelines
recommend that sufficient pretreatment be given so that after
further treatment by the municipal plant, the effluents will meet
the standards for new sources. The various processes that can
be used for removal of ammonia and other pollutants are listed.
Some municipalities have imposed limits on discharges of certain
pollutants to sewers, with rather high charges for industries
that exceed these limits. We recommend that such a course be
undertaken by East Chicago.
1.5 Storm and Combined Sewer Overflows
The three major Calumet area sanitary districts are also
required to treat or control combined sewer overflows. The out-
falls from these combined sewer overflows are shown on the map
of Figure D-2.
The ECSD is responsible for two combined sewer overflow
discharges to the Grand Calumet River (GCR), one to the IHC and
one storm water discharge to the IHC. These are shown in Figure
D-2 and Table D-5. There is no flow monitoring at this time,
but Table D-5 includes peak flow estimates.
The District constructed a 140-150 million gallon detention
lagoon in 1971 to hold the diverted flow from several combined
sewer overflows for treatment. The completion of the project
requires increases in the pumping capacity of the system, which
has been delayed due to bond sale problems. The lagoon is thus
D-ll
-------
.017
LEGEND:
-+• STORM AND COMBINED SEWER OVERFLOWS
» - storm
c = combined
H HAMMOND SANITARY DISTRICT
EC EAST CHICAGO SANITARY DISTRICT
G GARY SANITARY DISTRICT
O WATER QUALITY SAMPLING STATIONS
» SEWAGE TREATMENT PLANT
U i c h i g a a
\->
to
EAST GARY
MUNSTER
| HIGHLAND j
GRIFFITH
Figure D-2
SEWER OUTFALLS IN CALUMET AREA
-------
Table D-5
MAJOR COMBINED SEWER OUTFALLS TO IHC
Source: Combinatorics (1974)
o
M
Co
Municipality
Gary
Gary
Gary
Gary
Hammond
East Chicago
East Chicago
River Mile
Location
8.34, 8.26
7.10, 7.04
6.00, 5.77
3.46
1.90
(West Branch)
2.4
.7
(West Branch)
Combined Sewer
Description
Outfalls
.006 and .007
Outfalls
.008 and .009
Outfalls
.010 and .011
Outfall .012
Treatment plant
bypass
Cline Ave. Outfal
Alder St. pumping
station (storm w
and combined
Treatment plant
bypass
Peak Flow [cfs]
1 yr. storm
215.6
593.4
310.7
189.6
70.0
301.4
iter
128.0
5 yr. storm
327.4
892.4
466.7
286.5
100.0
455.2
192.7
Average Flow [cfs]
1 yr. storm
116.1
305.8
159.4
99.7
35.0
158.2
66.2
5 yr. storn
173.0
455.2
176.7
148.3
50.0
235.5
98.6
-------
not yet receiving any diverted flow and the possible need for a
i
re-bid by the contractor may delay completion until the end of
*1974. The two combined sewer overflow points to the GCR are
located 400 yd and 1000 yd, respectively, west of the Cline Avenue
bridge. These wet weather discharges will be diverted to the
detention lagoon at the WTP as soon as the new interceptor sewer
and the pumping station expansion projects are completed.
No interim chlorination is being provided, since the Dis-
trict has been too uncertain about the time delay to justify it
economically (Sweeney 1973). There are no data available to
judge the effects of these sources on water quality.
The storm water discharge from the Canal St. pumping station
to the IHC is a result of sewer separation of the area bounded
by the IHC on the east and Indianapolis Blvd. on the west. The
Canal St. pumping station has discharged unchlorinated storm
vater to the IHC beginning about October 1971.
On the east side of the IHC, opposite of the Canal Street
pumping station discharge point, is the Michigan Avenue pumping
station combined sewer overflow discharge point. This discharge
is tentatively being considered for treatment by microstraining
and chlorination as opposed to the alternatives of sewer separa-
tion, expansion of sewer capacity or detention basin methods of
controlling this problem.
2. THE HAMMOND SANITARY DISTRICT
The Hammond Sanitary District (HSD) was formed in 1938 and
includes the corporate boundaries of the cities of Hammond and
Munster. The HSD also services the cities of Whiting, Griffith
and Highland by contracted agreement. The total population
served by the District is about 175,000. There are also several
industries discharging to the HSD, including American Maize and
Lever Brothers.
D-14
-------
2.1 The District Wastewater Treatment Plant
The following description of plant status is from HSD
personnel (Sweeney 1973).
The HSD wastewater treatment plant is located on the west
branch of the Grand Calumet River. See plant "A" on map, Figure
4.1. The plant was put in operation in 1942 and incorporates an
activated sludge secondary treatment process with a 36-mgd
capacity. The plant is often overloaded, since flows through
the plant vary from 36-42 mgd. The plant is presently under
construction to expand the secondary treatment capacity to 48 mgd
by 1974 as recommended by the Four State Lake Michigan Enforcement
Conference in 1968, and in a follow-up 180-day notice issued by the
U.S. EPA, Enforcement Division on October 12, 1971. Although the
ordered date of completion was December 7, 1973, delays in equip-
ment delivery will cause completion to be delayed until March
1974.
The appearance of the receiving stream was very bad during
IITRI sampling on November 30, 1973, with unsightly growths,
anaerobic conditions, and floating sewage; however, chlorination
of effluents is apparently effective, since the bacterial count
is not high (Table 16.4 , Chapter 16).
The plant effluent discharged to the Grand Calumet River
has deteriorated somewhat during the last year because of the
construction. Preconstruction averages are found in Table D-2.
Even these do not meet 1968 Lake Michigan Enforcement recommenda-
tions of 5 mg/4 BOD and suspended solids.
Shock loadings of organics from the American Maize and
Lever Brothers' plants have tended to impair plant efficiency
at times, as each plant discharges effluent of extremely high
BOD and suspended solids to the sewers at inconsistent intervals
(Sweeney 1973). This problem is mentioned in the U.S. EPA
pretreatment guidelines (1973). The Swift Chemical plant which
is now closed but which is soon to be operated by Ashland
D-15
-------
Chemical Company, was responsible for the discharge of oil
emulsions which broke down into oil globules when within the
sewers and caused serious pump-screen clogging, impairment of
plant processes, and additional disposal problems. Pretreatment
should be required, with effective enforcement of pretreatment
regulations.
Because the direction of the flow in the Grand Calumet River
at the point where the District WTP discharges is variable, a
barrier dam to be placed immediately to the east of the plant
in the Grand Calumet River was proposed by several agencies to
serve as a control structure (Combinatorics 1974). The barrier
dam is still being considered by the HSD since this method of
preventing the high phosphorus levels in the plant discharge from
reaching Lake Michigan might be less costly than the installation
and operation of permanent in-plant phosphorus reduction facili-
ties. The dam is being considered by Indiana SPCB, although
diversion of sewage effluents to Illinois waters might not be
approved.
The cities served by the HSD have predominantly combined
sewer systems, and force mains are necessary to maintain flow
because of the level topography. The sewage from the city of
Hammond accounts for about 7570 of the total flow to the plant,
with about 0.5 mgd being contributed from both American Maize
and Lever Brothers. Whiting, with domestic sewage from a popu-
lation of 7,000, contributes 2.5 mgd average flow. The munici-
palities of Griffith and Highland contribute average flows of
about 2 mgd and 3 mgd, respectively.
The City of Whiting has recently held discussions with the
U.S. EPA and Indiana SPCB concerning the construction of its own
wastewater treatment plant; but with the trend in wastewater
treatment toward regionalization, Whiting was urged to continue
its contract with the HSD. Whiting is presently doing sewer
improvement work to try to decrease a problem of infiltration
of water into its sewers.
D-16
-------
2.2 Planned Plant Improvements
As previously stated, the HSD treatment plant capacity will
be expanded to 48 mgd by the spring of 1974 according to HSD
personnel (Sweeney 1973). This expansion will also increase
digester capacity and provide nitrification tanks. Phosphorus
removal facilities are not planned because of uncertainty about
building a dam. The 8070 P removal requirement is not being met.
Plans for AWT for the HSD plant were submitted to the state for
approval on October 15, 1973, and call for a system of multi-
media filters (gravity sand filtration) which are expected to meet
the 1968 Lake Michigan Enforcement Conference requirement of BOD
and suspended solids effluent levels of less than 5 mg/4. This
is to be completed by February 15, 1975 according to agreement
with U.S. EPA. The HSD is scheduled to obtain 1974 funding for
AWT.
2.3 Combined Sewer Overflows
The HSD has subdivided its District into 17 distinguishable
drainage basins, and it does a commendable job of reporting the
discharges. The combined sewer overflow discharge points from
these areas and monthly volumes discharged are listed in Table
D-6. The locations are also shown in Figure D-2.
HSD has been pursuing a program of constructing relief
sewers over the last ten years to intercept combined sewer over-
flows. These were designed and located so as to provide the
trunk phase for eventual sewer operation. In completing this
separation, the District is planning construction of lateral
sewer connections to relief trunk sewers and the elimination of
surface drainage inlets. The District expects the remaining
planning and construction for separation and chlorination of
storm discharges to cost nearly $30 million in the next five
years.
D-17
-------
Table
o
I
COMBINED SEWER OVERFLOW - HAMMOND SANITARY DISTRICT*
Million gallons per month
Overflow Discharge
Location
GRAND CALUMET RIVER
Sohl Ave .
Johnson Ave.
Kennedy Ave.
Kennedy Ave. (New Bldg.)
Columbia Ave.
Sub-Totals (MG)
LITTLE CALUMET RIVER
Walnut Ave.
Kennedy Ave. Ejector
Baring Ave.
Tapper Ave.
173d - Homan Ave.
Hohman - Munster
Van Buren Ave.
Jackson Ave.
Indianapolis Blvd.
Sub-Totals (MG)
WOLF LAKE (Storm water
Roby
Forsythe Park
Sheffield Ave.
AUG
26.
25.
32.
30.
188.
304.
2.
1.
0.
13.
18.
1.
1.
9.
1.
48.
only)
10.
5.
3.
9
2
9
9
1
0
0
1,
4
2
9
1
6
0
7
9
0
7
1
SEP
43.7
9.2
40.0
38.3
224.5
355.7
1.3
14.0
7.1
14.6
5.6
1.1
2.0
39.2
4.3
89.2
10.9
56.7
3.7
1972
OCT
5.
2.
14.
25.
193.
240.
6.
1.
5.
5.
~1
0.
0.
3.
4.
31.
10.
4.
0.
4
5
2
1
4
6
7
3
5
9
5
6
7
5
4
1
2
3
9
NOV
5.7
4.6
32. J
39.9
355.3
437.6
17.9
10.0
38.4
21.2
9.8
2.1
2.8
17.2
8.1
127.5
2.7
19.9
4.5
one
16.1
9.4
34.0
41.3
283.9
384.7
19.8
12.6
43.8
19.2
10.6
1.5
3.8
44. 8
19.2
175.3
11.1
28.8
1.9
JAN
7.
3.
14,
38.
323.
386.
9.
1.
16.
7.
1.
9.
5.
51.
24.
127.
12.
45.
3.
.0
.8
.5
.3
.2
.8
.6
8
.8
9
8
.1
1
1
0
2
3
1
3
FEB
0
0.2
3.0
19.2
209.0
229.4
0.2
0.0
10.6
0.1
0.02
0.01
2.0
0.0
0.0
12.9
8.0
17.4
1.5
MAR
7.1
5.6
37.9
46.4
389.1
486.1
21.1
4.5
35.2
21.4
13.4
2.1
4.5
13.1
17.8
133.1
12.3
10.4
2.6
1973
APR MAY
7.
6.
40.
48.
530.
633.
40.
5.
32.
22.
1.
3.
0.
2.
33.
142.
0.
38.
2.
7
5
2
8
3
5
1
3
5
6
8
7
3
5
5
3
5
9
8
28.
16.
28.
43.
430.
548.
12.
9.
4.
6.
9.
1.
2.
1.
25.
72.
12.
47.
4.
9
5
6
7
4
1
1
8
6
8
6
3
1
2
1
6
5
0
8
JUN
12.
5.
18.
32.
313.
381.
8.
3.
8.
12.
5.
0.
1.
0.
6.
47.
11.
45.
2.
1
6
1
3
0
1
5
6
6
5
1
8
1
~i
8
7
4
3
5
JUL
9.4
51.5
11.3
10.8
37.6
120.6
2.2
1.3
6.5
4.0
1.0
0.3
0.2
0.0
3.5
19.0
.2
.2
.1
AUG
7.7
.2
7.1
9.1
36.9
60.9
.4
.2
3.4
1.0
.1
.1
.6
0.0
1.6
7.4
5.1
4.9
.8
Sub-Totals (MG)
LAKE MICHIGAN
Robertsdale
71.3 15.4
27.1
41.8 60.7 26.9 25.3 42.2 64.3 59.2
.5
(Chlorinated storm water
as of May, 1973).
GRAND TOTALS (MG) 412.6 556.5 328.2 652.2 635.3 587.0 281.5 696.9 910.4 770.0 548.3 171.6
10.8
40.9 40.3 41.1 60.0 33.5 30.3 12.3 52.4 92.4 85.0 60.3 31.5 12,3
91.4
*Source: HSD Monthly Combined Sewer Overflow Reports.
-------
Already completed in this large-scale plan is the complete
separation of the combined sewer overflow in the Robertsdale
area. The Robertsdale pumping station overflow discharge to
Lake Michigan (Atchison Avenue extended) was the subject of
federal enforcement action in the form of a 180-day notice by
the Enforcement Division of U.S. EPA issued on October 12, 1971.
As of May 1973 the Robertsdale discharge to Lake Michigan consists
only of chlorinated storm water, according to HSD personnel
(Sweeney 1973). This individual action by the HSD has cost
about $4 million in its entirety.
The contract areas of the District have also been subject
to enforcement action in regard to combined sewer overflow dis-
charges. The City of Whiting was issued a consent decree by the
District Court on September 6, 1973, which ordered its two com-
bined sewer discharges to Lake Michigan to be diverted by
November 15, 1974. Whiting is planning a 30 million gallon
detention basin to meet this requirement at an estimated cost of
$3 million. A construction grant was approved by U.S. EPA in 1973.
The Indiana SPCB ordered the town of Griffith to cease from
discharging of combined sewer overflow by December 31, 1976.
See Figure D-2. Griffith is therefore proposing to build a
34-mgd WTP to treat its combined sewer overflow.
Highland has submitted plans to the Indiana SPCB and is
awaiting funding to complete its sewer separation in the north-
east part of town. This would eliminate combined sewage over-
flow from its two overflow discharges.
3. THE GARY SANITARY DISTRICT
The Gary Sanitary District (GSD) serves over 200,000 people
and various industries in Gary, East Gary, and Merrillville.
The GSD was formed in 1938, and the District plant was put in
operation in 1940. It is located on a 52-acre site on the east
branch of the Grand Calumet River. (See Figure D-l.) Improve-
ments in facilities have been made, mostly through a $6 million
D-19
-------
expenditure for expansion in 1962.
The Merrillville Conservancy District negotiated a con-
tractual agreement with the GSD to treat its sewer flows subse-
quent to 1969. As of the end of 1972, the flow from Merrillville
to the Gary District plant was averaging 2 mgd.
The Miller Treatment Plant in East Gary was shut down in
July of 1971, and all East Gary sewage is now diverted to the
District plant (a flow averaging about 1.5 mgd). Gary has
predominantly a combined sewer system, while East Gary and
Merrillville have separate sewer systems.
3.1 The District Plant
The GSD WTP has a primary design capacity of 80 mgd and
activated sludge type secondary treatment capacity of 60 mgd.
Chlorination is now provided for disinfection of the effluent
discharged to the Grand Calumet River, which flows into the
Indiana Harbor Canal and hence, Lake Michigan. The yearly
average flow in 1972 was 46.5 mgd, and the 1972 average effluent
BOD and suspended solids levels were 29 mg/je, and 51 mg/£,
respectively. The 1973 monthly averages of sonv effluent
parameters are listed in Table D-7. The flow has increased,
with no improvement in BOD or solids removal.
3.2 Planned Treatment Plant Improvements
As a result of a court decree initiated by Indiana SPCB,
and a U.S. EPA 180-day notice, the GSD is being forced
to improve its District plant effluent through implementation of
phosphorus removal facilities and AWT facilities. Combined
sewer overflows have also been the subject of these actions,
and plans for their chlorination and eventual elimination are to
be drawn up. The original suit and notice required these actions
to be completed by December 31, 1972. This deadline was not met.
The goals were as follows :
D-20
-------
Table D-7
GARY SANITARY DISTRICT TREATMENT PLANT*
PERFORMANCE DATA 1973
OVERALL
AVG. FLOW BOD(p.p.m.)
MGD RAW FINAL
G
to
h-1
JANUARY
FEBRUARY
MARCH
APRIL
MAY
JUNE
JULY
AUGUST
55.9
49.6
55.0
61.6
57.7
58.0
50.43
51.0
128
125
126
102
93
104
151
238
28
31
42
32
15
22
26
29
SS(p.
RAW
219
220
294
207
187
214
266
449
.p.m. )
FINAL
55
82
74
70
25
45
38
40
AMMONIA i'p.p.m.)
RAW FINAL
6.4
9
-
8
9
10
8
13
5.2
8
-
4
5
5
3
10
P04(p.p.m.) PERCENT PURIFICATICM
RAW FINAL BOD SS
6.9
7
-
11
16
20
22
22
4.3
5
-
5
11
13
13
13
78
75
67
68
84
79
83
88
75
63
75
66
86
79
86
91
*Source: Gary S.D. WTP Monthly Operating Reports.
-------
• Phase A consists of phosphorus removal to a
concentration 1 mg/£ as P or 80% over-all
removal, and improvements to preliminary and
primary parts of the treatment system.
• Phases B and C consist of Secondary Treatment
improvement, sludge handling improvements,
and construction of AWT to attain the 5 mg/£
BOD and suspended solids ordered, and to
provide a high degree of nitrification.
• Permanent phosphorus reduction facilities
are to be capable of 80% removal.
• Interim chlorination of storm and combined
sewer overflows, and in-plant regulator
control facilities is planned.
On January 24, 1973, the GSD received a federal grant of
$3,996,150 for Phase A construction, but because of an injunction
brought by a citizen against the bond sales by the GSD, con-
struction was delayed.
3.3 Storm and Combined Sewer Overflows
The GSD is responsible for seven combined sewer overflow
discharges and a separate storm sewer system discharge to the
Grand Calumet River. The seven combined sewer overflows are
located at Rhone, Island Street, Alley 9E, Polk Street, Pierce
Street, Bridge Street, Chase Street, and Colfax Street. See
Figure D-2 for locations. Disinfection or control of these
discharges is being implemented by the end of 1973. Phase A
improvements are to provide for the control of the operation of
the combined sewage regulators on sewer interceptors at the
wastewater treatment plant, and for some improvements in pumping
station and interceptor flow capacity.
D-22
-------
4. CHESTERTON
The Chesterton, Indiana, wastewater treatment plant serves
the town of Chesterton and the town of Porter, which have a com-
bined population of about 10,000. The plant uses an activated
sludge type secondary process and has a 1.5 mgd capacity. The
effluent is discharged to Beaver Dam Ditch, which flows into the
Little Calumet River and thence to Burns Ditch and Lake Michigan.
The 1973 effluent parameter levels are listed in Table D-8.
The Indiana SPCB held a hearing on January 6, 1972, to
determine the need for Chesterton WTP to install phosphorus
reduction facilities capable of 80% P removal. An order was
issued which called for December 31, 1972, completion of such
facilities. Chesterton contested this order, but has since
agreed to install the required facilities. These facilities
plan to use pickling acid for P removal rather than the
customary ferric chloride. The facilities were expected to be
operational by the end of October 1973.
Chesterton has also submitted plans for approval to the
state for storm water separation of the present combined sewer
system.
5. PORTAGE WTP
The Portage WTP serves its 20,000 plus population through
a separated sewer system and its 3.0-mgd activated sludge type
secondary treatment facilities. Phosphorus removal facilities
have been operational since February 1973, and the chlorinated
effluent is discharged to Burns Ditch. Monthly effluent levels
for 1973 are reported in Table D-9.
6. HOB ART WTP
The Hobart WTP serves a population of about 21,000, by a
combination of combined and separated sewers. The 2.1-mgd design
capacity at the WTP is often overloaded due to sewer infiltration
problems. Performance data are given in Table D-10. The
D-23
-------
Table D-8
CHESTERTON WASTEWATER TREATMENT PLANT REPORTS*
1973
Daily Avg. Flow BOD (mg/1)
(MGD) Raw Final
Jan- 1-2 87.8 5.8
D
i
N3
4>
Feb.
Mar.
Apr.
May
Jun.
Jul.
Aug.
Sep.
1
1
1
1
1
1
.3
.2
.3
.2
.5
.2
.92
.83
77
87
79
106
142
101
97
99
7
9
4
7.4
7.6
5
4.4
10.3
Susp. Solids (mg/1)
Raw Final
69 6
79
69
83
73
51
71
98
118
9
6
. 6
6
6
6
5.5
4
BOD
93
90
90
94
93
94
95
94
89
Percent Purif.
SS
91
89
91
92
92
88
91
95
96
*Source: Chesterton WTP Monthly Operating Reports
-------
Table D-9
TOWN OF PORTAGE WASTEWATER TREATMENT PIANT REPORT*
1973
o
1
Ul
Jan.
Feb.
Mar.
Apr.
May
Jun.
Jul.
Aug.
Sep.
Daily Avg.
Flow (MGD)
1.14
.734
1.16
1.49
1.30
1.39
1.06
1.04
1.10
BOD (mg/1)
Raw Final
159 7.7
214
192
185
186
178
319
321
333
7
9
24
11
5
7
7
7
.0
.8
.3
.5
.9
.4
.0
.3
Susp. Solids (mg/1) Percent Purification Phosphorus
Raw Final BOD SS Raw Fina1
47 6.9 98.1 95.8 8.3 4.0
109
111
72
102
157
180
175
178
7.
7.
18
6.
€.
5.
6.
9.
6
5
4
3
5
0
7
96.7
94.8
86.8
93.8
96.6
97.6
97.8
93.0
93.
95.
75.
93.
95.
96.
96.
94.
0 6.0 1.65
2 5.6 1.3
0 4.16 1.1
7 3.0 .5
4 3.7 1.0
9 4.36 .67
5 6.9 .3
5 -
Percent
51.1
72.7
76.7
65.8
83.9
69.5
84.9
79.3
-
*Source: Portage WTP Monthly Operating Reports.
-------
Table D-10
HOBART V¥?TFWATER TREATMENT PLANT
1973 OPERATING REPORTS*
Month
Jan
Feb
Mar
Aor
May
? Jun
NJ
^ Jul
Aug
Sep
Oct
llov
Avy . Flov.7
2.9H
2.7G
2.75
2.93
2.73
2.99
2.45
2.23
2.11
1.99 -
2.01
bOD
Raw Final
66
75
70
77
107
IOC
140
125
1C 3
161
145
4.3
4.2
4.2
4.5
3.1
5.9
6.1
9.4
11.5
13.5
10.0
Suspend
Raw
56
G2
CO
61
GO
03
99
102
122
116
106
ed Solids
Final
4.4
4.G
4.7
4.4
4.4
4.4
4.9
6.8
11.3
10.0
7.7
% Removal
BOD SS
93.5
9^.4
94.0
94.0
94.0
94.0
95.C
94.4
92. C
91.6
93.0
90.4
91.0
93.1
93.0 .
94.5
93.0
95.0
98.5
90.7
91.0
92.7 '
* Hobart VJTP Monthly Operatinq Reports
-------
chlorinated effluent is discharged to Deep River. Plans for
expansion to a 5-6 mgd design capacity and for AWT implementation
are awaiting federal funding. Hobart expects this to be done
by the end of 1975.
The Hobart WTP is presently experimenting with adding
increased polymer concentrations to upgrade the existing plant
efficiency. There is a serious problem with the method of using
pickling liquor (acid) for phosphorus removal. The liquor
crystallizes within the piping system and has caused blockage of
piping. The facilities have thus been inoperable since September
1973.
7. CROWN POINT WTP
Crown Point has a population of about 13,000, and the town
is served by a combined sewer system. The WTP has an existing
design capacity of 1.8 mgd, but is awaiting federal funds for
planned expansion to a 5-mgd design capacity and implementation
of AWT in the form of polishing lagoons.
The WTP has been achieving the required 8070 phosphorus
reduction, as these facilities have been operable since January
of 1973. Effluent is chlorinated and the discharge is to Beaver
Dam Creek, a tributary of Deep River. Performance data are
given in Table D-ll.
The combined sewers are routed to the WTP, but in times of
extremely wet weather the increased flow rates often cause over-
flow to Beaver Dam Creek of untreated combined sewer waste water.
Sewer separation is presently underway, and storm waters will be
routed away from the plant.
8. SALT CREEK BASIN
There are eight wastewater treatment plants in the Salt
Creek Basin. The plants are listed in Table D-12. The largest
of these is the city of Valparaiso's plant. The location of these
plants is shown on Figure D-l.
D-27
-------
Table D-ll
TOWN OF CROWN POINT WASTEWATER TREATMENT PLANT REPORTS*
1973
Daily Avg. Flow BOD (mg/1)
O
l
to
00
Jan.
Feb.
Mar.
Apr.
May
Jun.
Jul.
Aug.
(MGD)
1.47
1.51
1.74
1.65
1.60
1.67
1.88
1.92
Raw
78
64
53
44
88
55
80
88
Final
14
15
14
10
19
11
22
18
Susp. Sol ids (mg/1)
Raw
56
70
46
63
17
85
105
109
Final
10
18
16
17
10
10
11
11
Percent Overall
BOD
82
76
73
77
78
80
72
78
Percent Purif.
SS
82
74
82
73
72
88
89
83
*Source: Crown Point WTP Monthly Operating Reports.
-------
Table D-12
SALT CREEK BASIN WASTEWATER TREATMENT PLANT REPORTS1
WTP
Valparaiso
South Haven Subd.
Pleasant Valley Mobile
Home Park
Robbinswood Subd.
Oak Tree Park
Design Cap.
(MGD)
6
1.4
0.080
0.078
0.063
Avg. Flow
(MGD)
3.1
0.5*
0.013*
0.026
0.017
Avg. Effluent Loadings
BOD(mg/l)
20
61
2.2
10
38
(Jan-June 1973)
NH3(mg/l)
20
20
-~
0.8
2.5
0.5
0.1
-
2.0
23.0
Mobile Home Park
O
NS
Elmwood Mobile Home
Park
0.048
0.04*
7.3
1.7
2.3
Sands Mobile Home
Park
0.015
0.01*
14
1.2
5.0
Porter County Home
Septic Tank 0.003
77
14
*Estimated.
•'•From: Report of Survey - Salt Creek Watershed, Porter County, In., July 1973, Div. Water Pol. Control, IBOH.
-------
8.1 Valparaiso WTP
The Valparaiso WTP serves in excess of 20,000 people with an
activated sludge type secondary treatment process. Construction
completed in May 19/3, at a cost of $2.2 million, has provided
for an expanded plant design capacity of 6 mgd. The plant is
also providing treatment for phosphorus removal and chlorination
of its effluent to Salt Creek. Performance data are given in
Table D-13.
Advanced wastewater treatment facilities are being planned,
and are expected to be operational by 1977.
The system of combined sewers in the Valparaiso plant's
service area has serious infiltration problems, causing increasing
flow rates to the plant.
8.2 South Haven Subdivision WTP
The South Haven Subdivision WTP has an existing 0.70 mgd
capacity but construction is being completed to give the plant a
1.4 mgd activated sludge secondary capacity with advanced waste
treatment and chlorination facilities. The plant will serve about
2400 lots in the South Haven and St. Michaels Subdivisions, about
165 mobile home units at Meadow View Mobile Home Park, and 560
camp sites at Camp Butternut Springs.
8.3 Sands and Elmwood Mobile Home Park WTP
The Sands and Elmwood Mobile Home Parks' treatment plants
discharge into Damon Run which is tributary to Salt Creek. The
Elmwood Park WTP is an extended aeration type treatment process
with chlorination facilities. Capacity is 48,000 gpd. The Sands
Mobile Home Park's WTP capacity is about 15,000 gpd and of a
similar extended aeration type. Effluent chlorination is provided
and a terminal lagoon is used.
8.4 Pleasant Valley Mobile Home Park
The Pleasant Valley Mobile Home Park has an 80,000 gpd
D-30
-------
Table D-13
VALPARAISO WASTEWATER TREATMENT PLANT REPORT**
1973
Daily
Avg. Flow
(MGD)
Jan.
Feb.
Mar.
Apr.
May
O
i
^ Jun.
Jul.
Aug.
4.
2.
2.
3.
3.
3.
2.
2.
0*
24
64
69
18
35
61
59
Raw
98.
110.
75.
78.
100.
76.
90.
85.
BOD (mg/1)
Final
8
3
9
1
3
9
6
2
7.
11.
9.
8.
100.
16.
13.
8.
8
8
0
3
2
5
3
8
Susp. Solids (mg/1)
Raw
173
163
102
180
145
125
146
124
Final
10
6
9
8
13
11
13
7
BOD
92
99
88
89
85
82
85
89
Percent Purif.
.2
.1
.3
.4
.8
.2
.2
.7
SS
94
96
91
95
91
92
79
94
.3
.3
.0
.4
.0
.0
.4
.4
*Estimate
**Source: Valparaiso WTP Monthly Operating Reports.
-------
extended aeration WTP which discharges to the Squirrel Creek
tributary of Salt Creek. This plant also provides nutrient
removal, chlorinetion and a terminal lagoon.
8.5 Neighborhood Utilities. Inc. WTP
Neighborhood Utilities, Inc., has a 78,000-gpd extended
aeration WTP on the southeast side of Portage. It now has
phosphorus removal facilities installed for its discharge to
Salt Creek.
8.6 Oak Tree Mobile Home Park WTP
The Oak Tree Mobile Home Park is in the northern part of
Porter County and has a 63,000 gpd extended aeration WTP. The
plant effluent is chlorinated, and a terminal lagoon is provided
with final discharge to Salt Creek.
8.7 Porter County Home Septic Disposal
The Porter County Home is served by a septic tank disposal
system which discharges to Salt Creek. The discharge averages
about 3000 gpd. It is the farthest upstream discharge known in
s
Salt Creek.
8.8 Other Minor WTP and Proposed Systems
Several other minor systems exist. These include the
Liberty School WTP, 0.05 mgd design capacity and Liberty Farms
Mobile Home Park WTP, 0.036 mgd design capacity. Plans for a
Lake Louise Subdivision WTP and Timber Lake Subdivision WTP with
respective 0.092 mgd and 0.150 mgd design capacities have
received preliminary approval from the Indiana Board of Health.
The planned Burns Harbor Estates WTP, 0.064 mgd, and a housing
complex at R. 36, R6W, Section 16; 0.045 mgd WTP's have not yet
been approved.
9. THE METROPOLITAN SANITARY DISTRICT OF GREATER CHICAGO
The MSD has no sewage treatment plant facilities whose
discharge is tributary to Lake Michigan. There is a combined
D-32
-------
sewer overflow which diverts heavy run-off flows from the 95th
St. pumping station to the Calumet River via the Howard slip.
As reported by the MSB, diversion occurred a total of 4 hr and
32 min in 1972. This discharge is chlorinated. During discharge
its flow in the Calumet River is assumed to be towards the Lake,
since flow to the Illinois waterway through the 0'Brian Lock is
limited. The Chicago Water Department's Surveillance Crew has
reported that during 51 weekly Calumet Industrial Area Surveys
in 1970 the Calumet River flowed toward the Lake on 31 or 61%
of the observations at the nearby 92nd St. bridge.
10. CONCLUSIONS AND RECOMMENDATIONS
Both the treated municipal effluents and the combined sewer
overflows which discharge to the south Lake Michigan basin, have
a definite, detrimental effect on the quality of these waters.
Lake Michigan is directly affected by the two combined sewer
overflows at Whiting, by the extreme pollutional loadings from
the IHC, and to a lesser extent by the pollutional loadings from
Burns Ditch.
The water quality of the Grand Calumet River is quite
degraded as a result of the high BOD, suspended solids, ammonia-
nitrogen, phosphorus, and bacterial effluents from the Hammond,
East Chicago, and Gary Sanitary District wastewater treatment
plants. To correct the immediate problems, pretreatment of the
industrial discharges to these plants should be required, including
back-up facilities to prevent peak loadings that can upset the
municipal treatment plants, monitoring of sources, and penalties
for excessive peak loads from industries. If the industries
presently discharging to municipal sewers wish to discharge to
the Lake instead, then highly effective treatment should be
required of them.
The planned advanced wastewater treatment facilities and
expansion project should be expedited to help upgrade the quality
of effluents flowing to the Lake via IHC. More rapid funding is
D-33
-------
needed for this to be achieved. Hammond SD should proceed with
a phosphorus removal process, since diversion of their effluent
to Illinois waters is unlikely to be approved.
The high NH-j-N and bacteria concentrations in East Chicago
treatment plant effluents cannot be remedied by the existing
plant without control of ammonia and other materials coming from
steel mills. The high level of NH3-N in the plant effluents
prevents effective chlorination with any reasonable chlorine
dosage. High bacterial loadings in the IHC will continue until
this problem is solved. High bacterial counts are an indication
that other pathogens may be present, and constitute a threat to
public health.
The planned implementation of AWT and the present work
towards achieving 80% phosphorus removal in treatment plant waste
water discharges should provide for a general improvement in
water quality of the receiving waters. Further effort is needed
(mainly by completing construction programs and monitoring
performance) to achieve phosphorus effluent requirements of 1 mg/4
gee Chapter 17 for effect of the phosphorus reductions on the
Lake. The control or elimination of combined sewer overflows is
also needed to provide a very definite improvement in water
quality. Monitoring should be continuous throughout this
period of implementation of such improvements so as to document
their value and serve as an example to other areas.
The Hammond SD should be commended for its monitoring of
its combined sewer overflows. Other districts should be urged
to follow similar practices.
The Gary SD should be forced to initiate a program to
eliminate its combined sewer overflows to the Grand Calumet
River, and uo provide interim chlorination and monitoring. The
combined sewer overflow elimination project in Whiting is being
slowed by litigation opposed to the planned detention lagoon.
This issue should be settled promptly and the project completed
at the
D-34
-------
earliest possible time, since pollution from Whiting overflows
is evident in the Whiting area. (See Chapter 16 in Vol. I of
this report).
The water quality of the Little Calumet River is degraded
because of the uncontrolled combined sewer overflows from the
Hammond Sanitary District and the Highland and Griffith contract
areas. Further planning and funding should be expedited
to allow this situation to be remedied more quickly than it is
presently scheduled to be done.
Deep River and its primary tributary Turkey Creek flow to
the Little Calumet River and contribute above average phosphorus,
BOD and suspended solids and coliform to Burns Ditch. In wet
weather, high coliform counts and increases in BOD and suspended
solids levels result from treatment plant by-pass. Those munici-
palities contributing flows should be required to do sewer infil-
tration studies and to correct the problem.
D-35
-------
REFERENCES
Combinatorics, Inc. 1974
Load allocation study of the Grand Calumet River and Indiana
Harbor Ship Canal, Report to State of Indiana, Stream Pollution
Control Board.
People of the State of Illinois and the Metropolitan Sanitary
District of Greater Chicago vs Inland Steel Co. 1974.
Testimony of Henry Bramer, and Coke Plant operating records intro-
duced as evidence. Circuit Court of Cook County, Illinois,
Judge Nathan Cohen.
Phosphorus Technical Committee, 1972
Report to Lake Michigan Enforcement Conference, U.S. EPA.
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.
U.S. Environmental Protection Agency, 1973
Pretreatment of pollutants introduced into publicly owned treat-
ment works, Office of water program operations, Washington, D.C.
U.S. Environmental Protection Agency, 1974
Iron and Steel Point Source Category, Proposed effluent limita-
tions guidelines and standards, Federal Register 39 (34), Part III,
6486-6487.
NT RESEARCH INSTITUTE
D-36
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