EPA-440/5-78-012
IN-PLACE POLLUTANTS
IN TRAIL CREEK AND
MICHIGAN CITY HARBOR,
INDIANA
U.S. Environmental Protection Agency
Office of Water Planning and Standards
Washington, DC 2046U
February 1978
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CONTENTS
Section
I. INTRODUCTION
A. PURPOSE AND SCOPE
II. SUMMARY
III. CONCLUSIONS AND RECOMMENDATIONS 5
A. CONCLUSIONS 5
B. RECOMMENDATIONS 5
IV. MICHIGAN CITY HARBOR/TRAIL CREEK DESCRIPTION 7
A. USES OF THE WATER RESOURCE 7
1. Navigation 7
2. Cooling 11
3. Propagation of Fish and Wildlife 11
4. Wastewater Disposal; Drainage 12
B. PREVIOUS STUDIES OF THE AQUATIC ENVIRONMENT 13
V. FIELD AND LABORATORY STUDIES 19
A. FIELD SAMPLE COLLECTION 19
1. Sampling Methods and Materials 19
a. Sampling Methods Common to All Stations 19
b. Coring Methods Used with Each Vessel 22
B. ANALYSES OF CHEMICAL AND PHYSICAL PROPERTIES 22
1. Methods and Materials 22
a. Water Analyses 24
(1) Dissolved Oxygen 24
(2) Ammonia Nitrogen 24
(3) Heavy Metals 24
b. Bulk Sediment Analyses 28
(1) Percent Solids and Particle Size 29
(2) Organic Pollutants 29
(3) Oil and Grease 29
(4) PCB 29
(5) Arsenic 30
(6) Other Heavy Metals 30
c. Elutriate Tests 30
(1) Ammonia 30
(2) Heavy Metals 30
(3) PCB 31
(4) Aeration vs. Shaking 31
d. Summary of Physical and Chemical Analyses 31
iii
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CONTENTS (Cont.)
Section page
C. INVESTIGATION OF BENTHIC ASSEMBLAGES 32
1. Methods and Materials 32
2. Results and Discussion 34
D. SEDIMENT BIOASSAYS 38
1. Introduction 38
2. Overview of Methods 39
3. Results and Discussion 40
a. Sediment Preference Test 4o
b. Bioassays 42
VI. INTERPRETATION: CHARACTERIZATION OF ZONES WITHIN 47
THE CREEK AND HARBOR
A. RELATIONSHIPS AMONG BIOLOGICAL AND PHYSICAL- 47
CHEMICAL DATA
1. Macrobenthos Investigation 47
2. Bioassays 47
B. RANKING OF ZONES WITHIN THE HARBOR 55
1. Criteria 55
a. Biological 55
b. Chemical 56
2. Rankings 56
C. SOURCES OF IN-PLACE POLLUTANTS 56
VII. ASSESSMENT OF POTENTIAL CORRECTIVE ACTIONS 59
A. DREDGING 59
1. Present Plans for Dredging at Michigan City 60
2. Relationship of Dredging Plans to In-Place 63
Pollutants
a. Corps of Engineers Volume Estimates 66
b. Depth of Cut 66
c. Volume of In-Place Pollutants 66
B. COVERING 67
1. Practical Considerations 67
2. Possible Covering Methods 68
a. Cover Materials 68
(1) Inert Materials 68
(2) Chemically Active Materials 68
(3) Sorbents 68
(4) Sealing Agents 69
iv
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CONTENTS (Cont.)
Section Page
3. Assessment of Covering Concepts 69
C. SUMMARY OF POTENTIAL CORRECTIVE ACTIONS 70
REFERENCES 71
APPENDIX A 75
APPENDIX B 77
APPENDIX C 82
v
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FIGURES
Number
1 Trail Creek, Michigan City Harbor, Indiana ]8
2 Shoreline Activities and Other Features of the Study Area 9
3 Depths to be Provided by Maintenance Dredging 10
4 Stations Occupied by EPA Region V Sampling Efforts 18
5 Station Locations Used in this Study 20
6 Schematic of Gravity Sediment Corer 23
7 Apparent Effect of Lead Concentration on Toxicity of 49
Michigan City Sediments
8 Apparent Effect of Cadmium Concentration on Toxicity of 50
Michigan City Sediments
9 Apparent Effect of Volatile Solids on Toxicity of Michigan 51
City Sediments
10 Apparent Effect of Oil and Grease Concentration on 52
Toxicity of Michigan City Sediments
11 Apparent Effect of Percent Solids on Toxicity of 53
Michigan City Harbor Sediments
12 Relationship Between PCB Concentration and LC50 of 54
Michigan City Harbor Sediments
13 In-Place Pollutant Areas Outside Navigation Project 64
vi
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TABLES
Number Pag£
1 1975 Water Quality Data for Trail Creek 14
2 Bulk Sediment Analysis Results from EPA Region V 15
Sampling in 1970
3 Bulk Sediment Analysis Results from EPA Region V 16
Sampling in 1975
4 Samples Collected at Michigan City/Trail Creek at Each 21
Station: Purpose and Handling
5 Water Analyses (All Values in mg/£ Except pH, conductivity 25
and temperature)
6 Bulk Analyses of Bottom Sediment (all value mg/kg dry 26
weight unless otherwise noted)
7 Elutriate Test Results 27
8 Comparison of Aerated vs. Mechanically Shaken Elutriate 31
Tests for Two Stations
9 Rank-ordering of Stations by Concentration of Each 33
Parameter Measured
10 Macrobenthic organisms in Ponar grab samples collected at 35
stations in the Trail Creek Study Area, Michigan City,
Indiana in April, 1977
11 Percent composition and total taxa for macrobenthic 37
organisms in Ponar grab samples collected at stations in
the Trail Creek Study Area, Michigan City, Indiana in
April, 1977
12 Results of Sediment Preference Tests with Pontoporeia 41
13 Summarized Data for Sediment Bioassays with Pontoporeia 43
affinis
14 Summarized Data for Sediment Bioassays with Daphnia 44
galeata mendotae
15 Summarized Data for 48-hour Sediment Bioassays with 45
Cyclops bicuspidatus thomasi and Salmo gairdneri
16 EPA Region V Bulk Analysis Guidelines (14), Compared with 57
Michigan City Data
vii
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TABLES (Cont.)
Number
17 Summary of Areas and Volumes of In-Place Pollutants
Compared to Proposed Maintenance Dredging
viii
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ACKNOWLEDGEMENTS
The work reported here represents the efforts of a large number of
individuals. Dr. Thomas McComish and Mr. Greg Asbury of Ball State
University were essential to the project in ways that could not be foreseen
at the outset. Their tireless cooperation in the field, and their knowledge
of the study area, were of great benefit. Especially valuable was their
arranging the use of the facilities of the Indiana Department of Natural
Resources as a base of operations. Mr. Robert Koch of IDNR, in addition
to allowing our use of the facilities, was most helpful in sharing his
knowledge of the aquatic habitats of the Michigan City area.
Drs. John Ayers and Marlene Evans of the Great Lakes Research Center,
University of Michigan (Ann Arbor) and the crew of the R/V MYSIS were most
helpful during the field sampling.
Chemical analysis of sediments, waters, and elutriates were performed
by several laboratories in the Boston area. Arsenic and PCS analyses were
performed by Herbert V. Shuster, Inc. Ammonia, TKN, oil and grease, and heavy
metals analyses were performed by Interex Corp. All other analyses, as well
as elutriates and metal digests, were done at JBF, primarily by
Margolia Gilson.
The difficult task of conducting sediment bioassays was performed by
Dr. John Gannon and Mr. Daniel Mazur of the University of Michigan Biological
Station in Pellston. This effort produced useful data with techniques that
required some development because of the lack of standard methods for sediment
bioassays. Sediment bioassays remain a research topic, and these workers
encountered and overcame several obstacles to produce useful results.
Within JBF, much credit must go to Stephen Greene, without whose
crafty organization the field work on this project could not have been
completed in a successful and timely way. Jaret Johnson was Project
Manager.
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I. INTRODUCTION
Increasing attention in recent years has been given to the effects
that in-place pollutants in bottom sediments may exert on benthic communi-
ties and on aquatic systems in general. Systems of in-place pollutants
result from the fact that many pollutants such as heavy metals and pesti-
cides are sparingly soluble in water and are often sorbed onto suspended
particulates and hydrous iron oxides that sink to the bottom. One critical
question that must be addressed is whether the amelioration of pollutant
discharges may be counteracted by in-place pollutants remaining from
previous years. In other words, even "zero discharge" may not yield
healthy aquatic ecosystems unless in-place pollutants are removed or
inactivated.
Recognizing these important issues, Congress enacted Title I, Section
115, of the Federal Water Pollution Control Act of 1972, PL 92-500,
requiring the following action of the Environmental Protection Agency:
IN-PLACE TOXIC POLLUTANTS
Sec. 115. The Administrator is directed to identify
the location of in-place pollutants with emphasis on
toxic pollutants in harbors and navigable waterways
and is authorized, acting through the Secretary of
the Army, to make contracts for the removal and
appropriate disposal of such materials from criti-
cal port and harbor areas. There is authorized
to be appropriated $15,000,000 to carry out the
provisions of this section, which sum shall be
available until expended.
To identify the locations of in-place pollutants, the EPA let a contract
to JBF Scientific Corporation. The scope of that contract included collection
of existing data on in-place pollutants and the setting of priorities defining
critical waterways. The final report (1) did set those priorities while
pointing out that the locations on the priority list were tentative because
of the inadequacy of available data. To augment the data base, the EPA has
let two site-specific studies that included field and laboratory investiga-
tions. The first study (2), begun in the Spring of 1976, investigated
Baltimore Harbor, a large marine embayment with a good pre-existing data
base, intensive industrial activity, and very active port traffic. This
second site study has assessed Michigan City Harbor and Trail Creek,
Indiana. Michigan City offers an excellent contrast to Baltimore Harbor
with respect to Section 115 because the water is fresh, there were few
data on in-place pollutants, industrial activity and its wastewater dis-
charges are less extensive, and harbor traffic consists almost exclusively
of small recreational boats.
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A. PURPOSE AND SCOPE
The purpose of this study was to define and assess the in-place
pollutants in Trail Creek/Michigan City Harbor and, based on that defini-
tion and assessment, to evaluate potential corrective actions.
Michigan City Harbor and Trail Creek are likely to undergo maintenance
dredging in the near future for navigation enhancement. The navigation
channel to be dredged includes most of the study area, and a confined up-
land area is planned as a result of considerable study by the U.S. Army
Corps of Engineers' Chicago District. These facts have influenced the
scope of the investigation in the following ways:
1) Any recommendation from this study must take into account the
future maintenance dredging of the navigation channel. Even if
dredging did not prove to be the best option from the standpoint
of Section 115, dredging is a virtual certainty given the
shoaling of the waterway and its effect on recreational boating
and the local economy.
2) Areas outside the navigation channel have been investigated,
and have been considered for possible inclusion in the dredging
to be done. For these areas, all other corrective actions (e.g.
burial or chemical treatment) are active choices, as is the
choice of leaving the polluted sediments in-place.
The following two sections consist of a summary, and conclusions and
recommendations. The report then presents a description of the study area,
the procedures and results of the field work, interpretation of the results,
and assessment of corrective actions that might be taken.
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II. SUMMARY
Michigan City Harbor and its upstream extension, Trail Creek, are
important waters in many ways. They are stocked with, and provide
migratory runs for, salmonid species forming a vital sport fishery in the
Indiana waters of Lake Michigan. They are the base of a large recreational
boating community, and of an active commercial fishery.
Trail Creek flows slowly through the urban area of Michigan City,
and pollutants that have been discharged over the years have settled to
the bottom of these quiescent waters. This study was undertaken to
evaluate the effects of the resultant deposits of in-place pollutants,
and to determine what if any corrective action should be taken.
Field sampling of waters, sediments, and macrobenthos was conducted.
During the field work, waters and sediments were also collected for
laboratory bioassays. Other laboratory work included physical and chemical
analyses of the sediments, chemical analyses of site water, and detailed
assessment of the macrobenthos. These efforts showed that the sediments
of much of Trail Creek and Michigan City Harbor are toxic to several species
of desirable aquatic organisms, and conducive to extreme dominance of a
few species that are known to tolerate grossly polluted benthic environments.
Although the overlying waters also show some signs of pollution, the fact
that salmonid migrations are supported indicates that severely toxic dis-
charges have been abated and are now evidenced primarily by the in-place
pollutants that were deposited in past years.
It therefore appears that removal of these deposits would be a fruitful
and worthwhile operation. Before such action under Section 115, however,
the importance of a large landfill on the bank of Trail Creek as a potential
source of future pollutants should be assessed. If that landfill can be
proven unimportant, then hydraulic pipeline dredging followed by disposal in
a confined disposal facility (or several small facilities) is recommended.
The cost of such a program could exceed $4 million, but some fraction of this
could probably be provided from funds that the Corps of Engineers will spend
in any event to maintain depths for navigation in the study area.
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III. CONCLUSIONS AND RECOMMENDATIONS
A. CONCLUSIONS
1. The waters of Trail Creek show signs of continuing degradation
by heavy metals, oxygen demanding substances, and ammonia nitrogen. None-
theless, the stream supports salmonid migrations.
2. The sediments in Trail Creek and Michigan City Harbor contain
high levels of in-place pollutants from the entrance to the Yacht Basin
upstream to the local wastewater treatment plant.. The in-place pollutants
in this reach do not form localized "hot spots", but are relatively uni-
formly distributed. The deposits of in-place pollutants consist of oily
organic silt with high water content. Below the deposits is a hard, con-
solidated clay stratum. The pollutants of concern are organic (volatile)
solids, oil and grease, and heavy metals. PCB is present, but not in
unusually high concentrations.
3. The macrobenthos in Trail Creek and Michigan City Harbor typify
a severely degraded benthic habitat. Little difference in benthic animal
assemblages was observed among stations within the polluted reach. Stations
near the harbor exhibited slightly more benthic species diversity than
stations farther upstream. Increased diversity, however, was not related
to lower concentrations of in-place pollutants.
4. Bioassays with four selected sediments overlain by clean water
in aquaria showed a significant range of toxicity. Toxicities of sediment
samples did correlate with the concentration of several pollutants,
suggesting that the bioassays provided a finer distinction regarding the
degree of sediment pollution than was provided by studies of macrobenthos.
5. Sources of in-place pollutants cannot be distinguished between a
large landfill and a nearby wastewater treatment plant. An investigation
of leachate and runoff from the landfill would be required to make this
distinction. Direct industrial discharges to Trail Creek do not appear
to be a problem.
6. The maintenance dredging for navigation purposes planned by the
Corps of Engineers, Chicago District will affect approximately half of
the polluted area and will remove about one quarter of the volume of
in-place pollutants.
B. RECOMMENDATIONS
1. Although the data developed in this study provide some insight
regarding the sources of in-place pollutants, the role of a large landfill
could not be ascertained. Definition of the importance of this landfill
would require long-term studies of leachate and runoff. This definition
should be done before taking any action to remove in-place pollutants.
If the landfill is an important source, abatement of that source should
precede Section 115 action.
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2. Action to remove in-place pollutants from Trail Creek and Michigan
City Harbor is recommended, if the landfill is not an important source of
pollutants or if it can be abated as a source. The only other likely past
source of in-place pollutants, a wastewater treatment plant across Trail
Creek from the landfill, has upgraded its processes in recent years. There-
fore, Section 115 action should not be frustrated by accumulation of in-place
pollutants in the future.
3. Dredging, followed by confined disposal of the dredgings, is the
only proven reliable method for dealing with in-place pollutants. The
total cost of disposal facility construction, of hydraulic pipeline dredging,
\and of operation and maintenance of disposal facilities, would probably
exceed $4 million. In a joint program of navigational maintenance and
Section 115 action, some of this cost (perhaps 10 to 30%) may be recovered
from Department of the Army funds for navigation project maintenance
dredging.
4. If such a dredging program is undertaken, the thickness of the
in-place pollutant deposits between the Franklin St. Bridge and the waste-
water treatment plant should be more clearly defined. Because vessels of
sufficient size to take deep cores cannot navigate within this reach, a
means should be devised to take cores from each of the four bridges crossing
the waterway in the subject stream reach.
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IV. MICHIGAN CITY HARBOR/TRAIL CREEK DESCRIPTION
Trail Creek, with Michigan City at its mouth, is one of the few inlets
on the Indiana shore of Lake Michigan (Figure 1). Trail Creek in Michigan
City is narrow, with a width of approximately 150 meters near its mouth and
only four to five meters at the upstream end of the study area (Figure 2).
Within the downstream reaches used for recreational boating, currents are
generally slow (<0.3 m/sec), but the smaller channel upstream of the muni-
cipal wastewater treatment plant carries a consistently higher downstream
current. Water levels in southern Lake Michigan exert a strong seiche
effect on Trail Creek. The flow of the surface waters of Trail Creek often
is reversed in the study area. Such flow reversals were observed during
the field sampling phase of this study.
The most numerous shoreline developments on Trail Creek are facilities
supporting recreational boating. Other prominent facilities include the
Northern Indiana Public Service Company's (NIPSCO) Michigan City Generating
Station, public water supply and wastewater treatment plants, two manufac-
turing facilities, a. commercial fishing operation, and a U.S. Coast Guard
station.
A. USES OF THE WATER RESOURCE
The recommendations of this study must be realistic in view of present
and anticipated uses of the water resources of Trail Creek and Michigan
City Harbor.
1. Navigation
Recreational boating and commercial fishing based in Michigan City
are very important factors in the local economy. Much of the recreational
boating activity is stimulated by salmon and trout fishing in the Indiana
waters of Lake Michigan. Access is available through launching ramps as well
as through the many local marinas. Approximately 640 slips and nine
launching lanes are provided, as well as services such as marine fuel and
oil, ice, potable water, and boat hoists.
Although Michigan City's waterborne commerce formerly included signifi-
cant tonnages of salt and grains, this traffic declined and ceased between
1965 and 1970. Fresh fish is the only commercial cargo presently handled
through Michigan City Harbor. Landings between 1965 and 1974 ranged from
51 to 371 tons, with the later years consistently showing landings above
100 tons.
Because neither the recreational fleet nor the commercial fishing
vessels require a deep draft channel, the Corps of Engineers does not intend
to maintain the authorized 18-foot depth near the mouth of Trail Creek.
However, shoaling of the inner reaches of Trail Creek has resulted in plans
by the Corps of Engineers, Chicago District, for maintenance dredging. If
funds are available for constructing a confined disposal facility on land
adjacent to Trail Creek, maintenance dredging will take place in 1978 or
1979. Figure 3 shows the project depths to be maintained.
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Figure 1. Trail Creek, Michigan City Harbor, Indiana
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LAKE MICHIGAN
OUTER
(YACHT)
BASIN
WATER
TREATMENT
NAVAL PLANT
ARMORY
RAILROAD BRIDGE
SECOND ST BRIDGE
FRANKLIN ST
BRIDGE
NORTHERN
INDIANA PUBLIC
SERVICE CO.
GENERATING MICHIGAN CITY
STATION
TURNING
BASIN NO. I
MARINA RAILROAD BRIDGE
TRAIL CREEK
TURNING
BASIN NO 2
MILLER ST
BRIDGE
T
MARINA
\
\WASTEWATER
TREATMENT
PLANT
E ST BRIDGE,
5CALE IN FEET
o too 400 too iioo i«oo
Figure 2. Shoreline Activities and Other Features of the Study Area
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LAKE MICHIGAN
TO BE MAINTAINED AT 12 FOOT DEPTH
(AUTHORIZED DEPTH 18 FEET)
JO BE MAINTAINED AT 10 FOOT DEPTH
(AUTHORIZED DEPTH 18 FEET)
TO BE MAINTAINED AT 6 FOOT DEPTH
(AUTHORIZED DEPTH 6 FEET)
UPSTREAM
LIMIT
SCALE IN FEET
0 ZOO 400 BOO 19.0O ISOO
Figure 3. Depths to be Provided by Maintenance Dredging
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2. Cooling
The NIPSCO Michigan City Generating Station's cooling water intake
structures are adjacent to Turning Basin No. 1, on the shoreline of the
power plant property. The volume of water pumped through the plant
typically ranges from 100 to 225 million gallons per day (mgd), based
on daily operating data from July to December 1976 (3). Cooling water
is discharged to Lake Michigan, west of Trail Creek, outside the area
under consideration in this report.
Physical and chemical water characteristics near the intake (Turning
Basin No. 1) are shown later in this report to be more characteristic of
Lake Michigan water than of Trail Creek water. This observation cannot
lead to a conclusion regarding the plant's effect on the movement of
Trail Creek water without further study. Two possibilities exist:
a. Turning Basin No. 1 at the cooling water intake is affected
by the intake in that Lake Michigan water is drawn "abnormally"
far upstream into Trail Creek, OR,
b. Turning Basin No. 1 contains a high proportion of Lake
Michigan water because of the hydrologic characteristics
of the site, and the cooling water intake has little effect.
Understanding of the generating station's hydrologic effects, as
well as its thermal effects resulting from the discharge of cooling
water to Lake Michigan, should be improved as a result of a program
nearing completion by the University of Notre Dame. That program,
sponsored by NIPSCO, will include "identification of boundaries of
individual water masses and movements of these water masses in the
vicinity of the generating station" (3). The final report from that
project should be released in the Fall of 1978.
3. Propagation of Fish and Wildlife
Trail Creek is the largest Indiana stream tributary to Lake Michigan,
and is very important to the fish stocking program of the Indiana Department
of Natural Resources (IDNR). A recently developed salmonid fish hatchery
near Michigan City provides stocks of coho and chinook salmon and lake,
steelhead, and brown trout. Many of the young from this hatchery are re-
leased into Trail Creek in the spring (several thousand were released
during the sampling work on this study). Salmonids migrate up Trail
Creek from Lake Michigan to spawn in the fall. Salmonids are the focus
of intense recreational fishing activity using boats berthed at or
launched from Michigan City. Much fishing is also done from waterside
structures such as breakwaters. Fish resources of Lake Michigan near
Michigan City have been reported by McComish (4). That study did not
include Michigan City Harbor/Trail Creek, and therefore is only of
indirect interest to this report.
11
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4. Wastewater Disposal; Drainage
The Michigan City Wastewater Treatment Plant effluent is discharged
to Trail Creek from the plant site, which is noted in Figure 2. Several
industries discharge to the municipal collection system. These industries
have been characterized by a sampling program that has resulted in a
series of "industrial users," "industrial surveillance," and "industrial
pre-treatment" reports that were made available to this study by the
Michigan City Sanitary District. Plating operations contribute small
amounts of cyanide and heavy metals to the sewerage system, but the
Michigan City Sanitary District monitors these discharges closely. Because
of dilution and pretreatment, little or no effect on the treatment plant
or Trail Creek is evident. Another industry's discharge is high in sus-
pended solids (primarily rubber), but the treatment plant has reported no
trouble in removing these materials from the wastewater.
Stormwater overflows have been a problem in the combined collection
system at Michigan City, but the Sanitary District has been constructing new
storm sewers in a separation program begun in 1962. This separation program
is alleviating the problem of raw sewage overflows during periods of high
rainfall. As in all urban areas, however, the separated stormwater can still
be expected to cause water quality problems in receiving waters (i.e. Trail
Creek). Prominent among these potential problems are biochemical oxygen
demand (BOD), suspended and settleable solids, bacteria, and oil and grease.
Four other direct discharges to Trail Creek have also been identified:
The Michigan City Water Works filter backwash enters Trail
Creek approximately 600 ft upstream of the Franklin Street
Bridge (Figure 2). A study found that the suspended solids
concentration of the backwash was a maximum of 87 mg/£.
Suspended solids concentrations in Trail Creek returned to
background levels within 30 minutes after backwash events (5).
Wastewater from air pollution control devices at a manu-
facturer of castings enters a storm sewer that discharges
to Trail Creek 500 yards upstream of the wastewater treatment
plant.
A small metal fabricator has its own treatment facilities,
and is planning to join the municipal collection system.
A plastics manufacturer has a large septic system near
Trail Creek, with possible entry of leachate into the
stream.
None of these discharges appears to be a significant source of in-place
pollutants.
12
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B. PREVIOUS STUDIES OF THE AQUATIC ENVIRONMENT
The following discussion is a brief background to the prior knowledge
about the aquatic environment of Trail Creek in Michigan City. Much of
this report's reference to earlier work appears in the next chapter on
field and laboratory studies, and is intended to lend perspective to the
data developed in this study.
Previous studies have included biological sampling, sediment sampling,
and water sampling. Biological studies have been conducted by the
University of Notre Dame to assess the effects of the NIPSCO Michigan City
Generating Station on fish (3,6,7). Reports received to date have contained
abundant data regarding fish and ichthyoplankton sampling, temperature,
conductivity, pH, dissolved oxygen, and residual chlorine. The final report,
containing interpretations of these data, is expected to be released in
mid-1978.
Other biological work has been conducted by Ball State University.
These studies (4,8,9) have emphasized zooplankton, macrobenthos, and fish
in the nearshore Indiana waters of Lake Michigan, but have not sampled the
area discussed in this report.
Water quality in Trail Creek at Michigan City is monitored monthly
by the State Board of Health, Division of Water Pollution Control. Some
of their data for 1975 (the most recent year for which data have been pub-
lished) are presented in Table 1, for two stations identified on Figure 2
(Franklin St. and E St. bridges). The data show undesirably high levels
of several constituents. For most parameters, water quality is slightly
better at the downstream station (Franklin Street Bridge), probably reflecting
the dilution of Trail Creek water by Lake Michigan water. One exception
is fecal coliforms, which were consistently higher at Franklin Street than
at E Street, which is within sight of the Wastewater Treatment Plant outfall.
This trend probably reflects the importance of combined sewer overflows and
of urban runoff in bacterial contamination of Trail Creek.
Sediments in Trail Creek were sampled and analyzed by Region V of
the U.S. Environmental Protection Agency in 1970 and 1975. Their data are
shown in Tables 2 and 3 for stations identified on Figure 4. At the
time of submittal of the initial report on Section 115 to EPA (1), the
1975 sampling had not been done. On the basis of the 1970 data (Table 2)
showing very high levels of several parameters including arsenic, Michigan
City was included in a group of six "Priority 1" waterways across the
United States most strongly needing further action under Section 115.
These data also were valuable in this study for identifying likely "hot-
spots" of in-place pollutants and for planning the field work accordingly.
For example, both sets of data indicated that the most serious apparent
problems with in-place pollutants were upstream of Turning Basis No. 1.
Sampling stations in this work were therefore more closely spaced upstream
of that location, and more widely spaced lakeward of that location.
13
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Table 1. 1975 Water Quality Data for Trail Creek
E Street Bridge
Minimum
Maximum
Average
BOD5
1.6
3.9
2.5
Suspended
Solids
3
51
19
Volatile
Suspended
Solids NH3
1 0.80
24 4.00
7 2.27
Phos-
phorous
0.09
0.52
0.21
Oil &
Grease
1.0
29.0
13.7
Fecal
Coliform
(MPN/100 m£)
10
1700
172
Specific
Conductance
(pmhos/cm)
450
600
527
Pb
0.020
0.050
0.032
Zn
0.040
0.170
0.092
Franklin Street Bridge
Minimum 1.4 1
Maximum 3.2 32
Average 2.3 12
1 0.20 0.03 1.0
12 2.50 0.41 29.0
4 1.22 0.12 11.9
10
4700
1216
250 0.020 0.030
580 0.030 0.230
413 0.024 0.070
Source: Indiana State Board of Health and Indiana Stream Pollution Control Board (10).
All units in mg/H unless otherwise noted
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Table 2. Bulk Sediment Analysis Results from
EPA Region V Sampling in 1970
Station:
Parameter
Oil and Grease
Ammonia-N
Nitrate-N
Organic-N
COD
Total Phosphorous
Total Iron
Lead
Zinc
Mercury
Total Solids (%)
Volatile Solids (%)
Specific Gravity
(no units)
Arsenic
70-2
391
None found
0.44
None found
3,975
56.8
2,182
13
16
0.06
67.7%
0.3%
1.6881
350
70-3
172
None found
0.13
81
4,420
95.1
2,572
21
20
0.02
78.3%
0.5%
1.9846
400
70-4
217
None found
0.13
68
3,285
126
3,111
11
17
0.06
76.0%
2.2%
2.0004
500
70-5
1,354
236
0.50
1,077
33,120
772
8,095
33
925
0.20
59.8%
3.9%
1.4883
2,200
70-6
16,870
845
0.79
4,823
316,380
8,695
31,937
244
10,897
1,8
25.4%
18.6%
1.1652
9,660
All units in mg/kg dry weight unless otherwise noted.
15
-------
Table 3. Bulk Sediment Analysis Results from EPA Region V Sampling in 1975
PARAMETER
Volatile Solids %
Chem. Oxy. Demand
T. Kjel. Nitrogen
Oil-Grease
Mercury
Lead
Zinc
MCTY 75-1
MCTY 75-2
MCTY 75-3
MCTY 75-4 MCTY 75-5 MCTY 75-6 MCTY 75-7
5.40
73,000
1800
2500
*
90
360
8.2
111,000
3100
4300
*
150
870
15.5
224,000
5200
11,000
*
270
2060
13.6
202,000
4300
7300
*
190
1430
19.9
309,000
7100
15,000
*
200
2050
17.4
274,000
4200
12,000
0.1
240
2000
15.8
254,000
5400
15,000
0.1
325
2340
T. Phosphorous
Ammonia Nitrogen
Manganese
Nickel
Arsenic
Barium
Cadmium
Chromium
Magnesium
Copper
Iron
23,
17,
720
93
510
55
6
70
63
56
000
56
000
1600
160
610
75
9
130
19
120
22,000
200
24,000
3600
360
790
0.0150
14
270
58
300
17,000
260
36,000
3300
270
620
105
13
200
36
200
13,000
190
26,000
6300
390
810
160
12
275
81
320
9800
180
25,000
3900
460
680
150
10
250
45
270
13,000
170
27,000
4700
380
690
140
8
280
61
290
9900
215
25,000
*Below detection limit (0.1 mg/kg)
All values in mg/kg dry weight unless otherwise noted,
-------
Table
3 (cont.) Bulk Sediment Analysis Results from EPA Region V Sampling in 1975
PARAMETER
Volatile Solids %
Chem. Oxy. Demand
T. Kjel. Nitrogen
Oil-Grease
Mercury
Lead
Zinc
MCTY 75-8
12.0
195,000
4200
11,000
*
360
7160
MCTY 75-9
16.4
265,000
5200
15,000
0.1
270
2470
MCTY 75-11
9.4
129,000
3200
7000
*
130
705
MCTY 75-12
16.6
250,000
4500
14,000
*
290
2710
T. Phosphorous
Ammonia Nitrogen
Manganese
Nickel
Arsenic
Barium
Cadmium
Chromium
Magnesium
Copper
Iron
3300
300
710
130
8
260
44
235
12,000
185
23,000
5700
210
710
170
10
325
78
360
11,000
215
29,000
2100
340
560
90
5
155
22
125
5800
90
19,000
5000
190
750
160
14
380
80
370
11,000
220
28,000
*Below detection limit (0.1 mg/kg)
All values in mg/kg dry weight unless otherwise noted
-------
N
LAKE MICHIGAN
,70-1 OBS ONLY
00
V75- 9,12
MICHIGAN CITY
O 70-2 1970 SAMPLING SITE
• MCTY 75-1 (975 SAMPLING SITE
\\ MCTY 75-10
\^£/ IfiAIL CREEK
%?\
SCALE IN FEET
0 too 4OO 900
1100 1100
Figure 4. Stations Occupied by EPA Region V Sampling Efforts
-------
V. FIELD AND LABORATORY STUDIES
A. FIELD SAMPLE COLLECTION
All samples for this project were collected between April 14 and 17,
1977. The field crew consisted of cooperating groups from JBF Scientific,
Ball State University, and the University of Michigan (Ann Arbor). Logistic
support was provided by the Indiana Department of Natural Resources (IDNR).
The station locations are shown in Figure 5.
1. Sampling Methods and Materials
The water depths in the area under study varied from a few cm up to
about 8 m. The approach to the field work was to use the best equipment
that could be brought to each sampling station. Accordingly, three plat-
forms were used. In deep water (>2 m), the Research Vessel MYSIS of the
University of Michigan was used. This platform offered the full complement
of sampling equipment and shipboard processing that was desired. For
intermediate depths (1 to 2 m) a 19-foot research vessel operated by Ball
State University was used. A small flat-bottom skiff made available by
the IDNR allowed access to very shallow upstream areas. The principal
difference among platforms was in the ability to take sediment cores and
in the physical difficulty of retrieving ponar grabs.
a. Sampling Methods Common to All Stations
Water samples were taken with Van Dorn samplers and were subdivided,
preserved, and stored for laboratory analysis of separate subsamples for
separate parameters. All samples were taken from 1 meter above the bottom
except for stations with less than 1 m water depth. Samples at those
stations were taken at mid-depth. The handling of these separate water
samples is described in Table 4. Field measurements were also made as
described in that table.
Samples of benthic organisms were collected with a ponar grab with
bite dimensions of 22 x 22 cm. A single grab was collected at each sample
station by lowering the sampler onto the substrate at an impact speed of
about 0.3 m per second and retrieving as quickly as possible to the boat.
In the flat-bottom skiff, retrieval was by hand because no winch could be
fitted. Immediately after removal of the sampler from the water it was
placed in a large tub lined with a polyethylene bag. The sampler was then
opened and contents were emptied and washed from the sampler into the bag
with site water. Each bag was then marked for station identification and
tightly tied.
All benthic biological samples were washed onboard the RV MYSIS (in-
cluding samples taken from the smaller boats) using an elutriation device
("Critter Catcher") and washing small debris and substrate materials
through nitex screen of 0.5 mm square mesh dimensions. Organisms and
large debris particles retained were collected in labeled jars and pre-
served in about 10 percent formalin.
19
-------
N
LAKE MICHIGAN
I3S
14
SCALE IN FEET
0 200 400 «oo Itoo taoo
Figure 5. Station Locations Used in this Study
-------
Table 4. Samples Collected at Michigan City/Trail Creek at Each Station: Purpose and Handling
Sample Description
WATER
(conductivity, temperature,
DO, pH in field)
SEDIMENT PONAR GRABS
(Immediate Oxygen Demand in
field on surficial sediments)
SEDIMENT CORES
sample top, middle, bottom
Type of Container and Preservation
1-quart glass - cap lined
with aluminum foil
1-quart glass (5 m£ H SO.)
1-pint polypropylene
(2.5 m£ H2S04)
1-pint polypropylene
Four 5-gallon polyethylene
containers from one central site
Three 5-gallon polyethylene
containers from one site near
mouth of Trail Creek
Mason jars
5-gallon polycarbonate bucket
shipped and stored at 4°C.
2-quart polycarbonate wide mouth
Three 1-quart glass - wide
mouth cap lined with aluminum foil
Purpose
PCB and Arsenic
Oil and Grease
Ammonia-N
Metals
Elutriate Test Water
Site Water for Bioassays
Benthic Analysis
Bioassay
Particle Size and
Elutriate Test, Percent
Solids
Blend and Divide from each
in laboratory:
Sample Bottle - PCB and
Arsenic
1-pint glass wide mouth -
TKN, Oil and Grease
Remainder - Percent Solids,
Volatile Solids, Metals
Digestion
-------
b. Coring Methods Used with Each Vessel
Stations occupied with the MYSIS were represented by cores taken with
a gravity coring device as described schematically in Figure 6. A core
retainer was used to avoid loss of core material during retrieval. As each
core was brought on board, the following procedure was observed:
Remove core liner from pipe core-tube
Drill small hole immediately above sediment-water interface to
allow supernatant water to escape
Measure core length
Extrude core from core liner, subdividing into samples of
10 to 25-cm increments (3 samples maximum).
A clean core liner of acrylic material was used for oacb coring event.
Despite the use of 182 kg of lead and 300-cm core liners, the longest core
retrieved was 76 cm. Some cores terminated in a layer of hard clay, but
others were found to contain organic sediment to the base of the core.
Relationships between the length of the core sample and the length of in
situ sediment represented (always greater than the sample length) are dis-
cussed in Appendix A.
Cores were taken from the smaller boats with a coring device similar
in all respects to that used on the MYSIS except for size and weight. The
core liner was 61 cm long and 5 cm in diameter. The direct pushing force
of an oar was used to achieve penetration because the usable weights and
fall distances were inadequate.
B. ANALYSES OF CHEMICAL AND PHYSICAL PROPERTIES
1. Methods and Materials
The many types of analyses that were performed in the laboratory
involved several procedures that require detailed, specialized description.
Those descriptions, including procedures for quality control, appear in
Appendix B. Before proceeding to the discussion of results in tte text,
one procedure - the elutriate test - should be described briefly.
The elutriate test involves shaking a sample of sediment with added
water, followed by settling, filtering of the water, and analysis of the
filtrate. Instead of shaking, aeration may be used to provide mixing. Both
mixing methods were used in this study. The main reason for performing an
elutriate test is to simulate the interaction of a sediment with water at a
dredged material disposal site or with water in a hydraulic pipeline. The
latter situation was simulated in this project. Dredging at Michigan City
would most likely use a hydraulic pipeline dredge, and any release of
pollutants to the carrier water in the dredged slurry is of interest.
22
-------
Valve to Permit
Escape of Water
Cable
\
r
400 Ib.
Lead Weights
Core Liner
Core Retainer
Nose
Figure 6. Schematic of Gravity Sediment Corer
23
-------
Data from the chemical and physical laboratory investigations appear
in the accompanying tables: Table 5, Water Analyses; Table 6, Sediment
Analyses; Table 7, Elutriate Analyses. Selections of stations for bioassays
and for intensive benthos evaluations were based on these data. The
rationale behind those selections is discussed below.
a. Water Analyses
The water quality data shown in Table 5 were developed for several
purposes:
To assess the total aquatic system rather than only the sediments
To characterize waters used in bioassay and elutriate tests
To compare present water quality with past conditions as re-
vealed by earlier data and by the sediment characteristics.
This comparison is useful for inferences as to whether the
sources of in-place pollutants are still important.
(1) Dissolved Oxygen. Upstream of the wastewater treatment
plant and immediately downstream, D.O. levels were at or near saturation.
Between the E Street and Franklin Street Bridges, levels were as low as 50%
of saturation. D.O. concentrations were higher lakeward of the Franklin
Street Bridge, but because water temperatures were lower, the water remained
slightly undersaturated. Dissolved oxygen concentrations, while below
saturation, are not so low as to jeopardize biota or other uses of Trail
Creek. Without a mathematical model for dissolved oxygen in Trail Creek
it is difficult to separate the causes of the oxygen deficit and thedr
relative importances. However, it appears unlikely that the wastewater
treatment plant outfall is the sole cause of the deficit. Benthic oxygen
demands are also probably significant.
(2) Ammonia nitrogen. The species NHo + NH were observed
at quite high levels between the wastewater treatment plant^and Franklin
Street Bridge. These substances reflect the breakdovm of organic nitrogen,
and indicate organic pollution. EPA1s most recent water quality criteria
document (11) recorouiends a maximum of 0.02 mg/£ as un-ionized NH~; at the
pH and temperatures in Trail Creek, the observed values of NHo and NH>
(above 2 mg/£) indicate violation of this criterion.
(3) Heavy metals. Of the metals selected for water
analyses, nickel, lead and zinc appeared to be at levels worthy of concern.
EPA criteria (11) stipulate that these metals should be present in concen-
trations less than 0.01 times the 96-hour LC50 for the most sensitive local
organisms. Since most bioassays with salmonids have found 96-hour LCSO's
for these metals typically less than 10 mg/£, the values shown in Table 5 -
especially for lead - can be considered as violating tre Federal criteria.
The cadmium levels shown may also be of concern; although concentrations
are low, the hazard of even low levels cf cadmium is great.
24
-------
Table 5. Water Analyses
(All Values in mg/£ Except pH, conductivity, and temperature)
Dissolved
Station
1
2
3a
4a
5a
6
7
8a
8b
8c
8d
8e
9a
9b
10
11
12a
12b
13c
13d
14
15
£H
7.2
7.2
7.1
7.1
7.3
7.3
7.3
7.2
7.4
7.1
7.1
7.2
7.2
7.3
7.1
7.3
7.3
7.4
7.1
7.3
7.3
7.4
Oxygen
8.
8.
8.
8.
8.
8.
6.
6.
5.
5.
4.
4.
5.
6.
6.
6.
6.
6.
8.
10.
10.
10.
4
4
3
5
4
2
7
1
5
0
8
7
4
4
4
8
4
7
9
4
4
2
Conductivity
ymhos
200
250
260
205
210
260
340
410
430
450
450
430
720
405
400
405
410
410
385
410
405
400
Tempera- „„ XT
ture °C
10
16
12
11
12
13
15
15
17
17
17
17
15
15
15
15
15
15
16
17
17
17
3
0.
0.
0.
1.
2.
1.
0.
2.
3.
0.
; PCB
40 <0.01
31
33
33 <0.01
20
92
95
57
03 <0.01
17
Cd
0.002
0.02
0.03
0.02
0.01
0.04
0.04
0.04
0.02
0.002
Cu
0.02
0.01
0.03
0.02
0.03
0.02
0.02
0.04
0.02
0.01
Ni
0.15
0.18
0.10
0.15
0.09
0.19
0.16
0.12
0.23
0.18
Pb
0.88
0.71
0.50
0.63
0.79
0.97
0.74
0.64
0.85
2.80
Zn As
0.
0.
0.
0.
0.
0.
0.
0.
0.
0.
09 <0.
10
06 <0.
21 <0.
24
15 <0.
26 <0.
31
34 <0.
16
-------
Ni
ON
Table 6. Bulk Analyses of Bottom Sediment
(all values mg/kg dry weight unless otherwise noted)
Depth Range
Below Water/
Station Sediment
No.
1
2
3A
3B
3C
4A
4A
4A
5A
5B
5C
6
6
6
7
7
8A
8B
8C
8C
8D
8E
9A
9B
10
11
11
12A
12A
12B
13B
13C
13D
14
Interface
(cm)
0-10
0-15
0-11
0-13
0-18
0-20
20-40
40-60
0-13
0-25
0-23
0-25
25-50
50-74
0-18
36-53
0-10
0-10
0-22
22-43
0-18
0-15
0-23
0-10
0-10
0-10
10-20
0-13
13-25
0-13
0-8
0-8
0-8
0-8
Percent
Solids
68.8
45.6
67.3
51.0
39.5
41.7
44.1
46.3
29.7
31.3
31.5
25.4
30.4
31.0
24.8
22.6
37.9
31.1
42.9
47.3
32.0
25.0
60.1
41.9
34.2
27.8
37.5
54.2
72. 3
36.4
79.5
70.0
80.1
Percent
Volatile
Solids
0.8
5.6
1.9
5.1
10.4
8.9
9.2
17.0
14.9
15.3
18.7
17.8
17.8
18.7
2.1
15.0
16.5
13.0
10.1
15.7
18.2
1.9
10.5
12.3
18.4
13.2
5.7
4.3
13.3
1.3
3.6
0.5
Particle Si
Percent
Sand
92.8
17.2
66.4
8.5
3.0
2.0
0
0
10.3
88.0
13.0
13.8
2.0
26.8
15.7
91.1
43.0
54.0
22.0
24.3
10.0
97.5
1.0
96.2
Percent
Silt
5.6
62.6
26.6
70.5
78.8
80.2
87.3
86.0
76.9
5.7
72.3
75.4
83.0
71.0
73.3
7.2
53.4
37.3
74.5
6E.4
67.5
1.2
93.0
2.7
ze
Percent
Clay
1.6
20.2
7.0
21.0
18.2
17.8
12.7
14.0
12.8
6.3
14.7
10.8
15.0
2.2
11.0
1.7
3.6
8.7
3.5
7.3
22.5
1.3
6.0
1.1
Immed
Oxygen
(mg 0,,/gm
<0.
0.
0.
0.
0.
0.
1 .
1 .
1.
1.
0.
1.
0.
1.
1.
0.
0.
0.
0.
0.
0.
<-o.
0.
<0.
late
Demand
dry wt)
1
46
25
4
94
77
31
02
21
61
9
09
89
06
12
1
64
41
67
76
74
1
47
1
TKN
100
3500
1200
13400
4800
10800
670
860
27600
440
370
13700
5900
8400
10300
7200
6600
940
800
1100
1800
670
5600
13300
930
4200
1700
960
380
1600
370
Oil
and
Grease
1200
3500
2800
6000
4300
7700
9300
9800
12600
3800
1100
15300
14200
10600
17000
13500
7400
6600
5600
1200
1700
6200
13500
14400
8300
4100
1800
1900
1100
2100
370
PCB
<0.01
'0.01
0.14
0.12
0.35
1.10
0.45
<0.01
0.69
0.40
0.32
0.38
0.69
<0.01
0.53
0.33
<0.01
0.72
0.88
'0.01
0.04
0.32
<0.01
<0.01
<0.01
0.15
<0.01
Arsenic
< 0.1
10.9
5.4
1 .3
2.4
11.3
3.6
12.5
21.6
1.3
1.9
1.9
1.8
1 .3
10.5
21.7
16.7
15.8
10.7
11.6
1.8
2.1
0.8
3.8
0.8
8.8
17.3
1.4
4.2
2.1
0.7
3.7
2.4
2.3
Cadmium
1
7
5
,•
26
11
67
53
49
82
78
46
63
60
41
59
42
35
46
54
70
5
37
55
74
35
21
6
6
7
8
1
Copper
1
22
10
27
38
65
16
14
79
23
14
71
68
56
87
77
57
16
17
23
15
14
72
76
14
28
15
2
17
18
2
Nickel
9
55
30
86
84
219
105
136
255
153
93
179
230
178
167
135
93
142
120
193
47
116
119
133
152
114
34
16
31
50
17
Lead
21
170
180
250
280
410
360
280
430
340
390
430
360
510
470
540
370
410
580
440
130
230
450
590
210
140
83
9. 3
110
85
3.1
Zinc
29
1400
230
1900
600
2900
1600
1600
3350
2800
1800
3180
2800
2400
3500
3400
2700
1500
1200
3000
2100
1300
4700
4590
1300
1100
280
32
300
260
50
-------
Sample
1A
IS
2A
2S
3AA
4AA
5AA
5AS
7A
7S
8AA
8CA
11A
13CA
13DA
13DS
14A
8A
A = Aerated
S = Shake
3~ Cd
0.19
0.21
0.21
2.0
64
41
160
18
120
61
54
40
42
33
44
98
2.0
0.18
0.01
0.24
0.02
0.03
0.24
0.05
<0.01
0.02
0.04
0.01
<0.01
<0.01
0.02
<0.01
0.02
<0.01
0.01
0.01
Cu
0.01
0.01
0.01
<0.01
0.01
0.06
0.03
0.02
0.01
0.04
0.06
0.03
0.01
<0.01
0.04
0.03
0.01
0.02
lclt>J.<
All
Ni
0.13
0.06
0.02
0.11
0.15
0.04
0.14
0.11
0.48
0.06
0.11
0.16
0.27
0.09
0.05
0.20
0.02
0.05
i / . iij.utrj.ai.fc; leau r\.et>u.
Values in mg/Jl Except pH
Pb Zn PCB
<0.04
2.00
<0.04
<0.04
0.50
0.08
0.31
0.48
0.47
0.06
0.21
0.58
0.45
0.29
0.65
0.24
0.80
0.37
0.02
0.05
0.03
0.03
0.02
0.04
0.06
0.22
0.05
0.08
0.06
0.03
0.02
0.04
0.07
0.30
0.01
0.11
<0.01
—
<0.01
—
<0.01
<0.01
<0.01
—
<0.01
—
<0.01
<0.01
<0.01
<0.01
<0.01
—
<0.01
<0.01
LUS
As £
<0.1 7
~j
<0.1 7
— 7
<0.1 7
<0.1 6
<0.1 7
— 7
<0.1 6
— 6
<0.1 7
<0.1 7
<0.1 7
<0.1 7
<0.1 7
— 7
<0.1 8
<0.1 7
H
.8
.7
.1
.1
.1
.9
.5
.2
.9
.8
.1
.1
.9
.9
.7
.2
.1
.3
DO
8.1
8.0
0.8
2.8
6.8
0.6
1.7
0.4
0.6
3.0
2.6
1.0
5.2
9.4
1.8
0.4
9.2
—
Shake
_p_H DO
— —
— —
— —
— —
7.1 7.6
6.9 3.6
— —
— —
— —
— —
6.8 2.8
7.0 1.6
7.5 4.8
7.3 8.4
— —
— —
7.6 8.8
— —
(Site Water)
-------
In summary, the water analyses shewed organic and toxic pollutants to
be present in the water column, indicating a potential hazard to aquatic
biota and causing dissolved oxygen depletion.
b. Bulk Sediment Analyses
Considerable scientific debate has taken place in recent years over
the value of bulk sediment chemical analyses for assessing the probable
environmental impacts of dredging and dredged material disposal. It has
been argued and demonstrated (12,13) that bulk sediment analyses are a
poor predictive tool for evaluating release of pollutants to the water
during dredging or disposal. Elutriate tests are generally favored by
most investigators for such evaluations. However, a focus on short-tern
release to the water does not address the issue of in-place pollutants.
Bulk sediment chemistry is the most appropriate and convenient way to
describe sediment properties and to relate them to organisms present and
to sedimert bioassay data. The elutriate test in this context is a
useful but secondary method of sediment characterization.
The Great Lakes Surveillance Branch of Region V, EPA, hfs developed a
classification system for sediment quality based primarily on bulk analyses
(14). This system has been defended by Bowden on very appropriate grounds
(15):
"The bulk sediment approach has been widely criticized
as not being scientifically sound. We acknowledge that
there may be some merit to these criticisms, but we adhere
to the system for the following three reasons:
1. No suitable alternative system has been developed.
2. The fundamental assumption that adverse impact
on the environment is related to degree of
anthropogenic contamination has not been re-
futed and is probably sound.
3. The critics do not appear to understand how the
guidelines are applied. The criticism is based
on attempts to find correlations between indivi-
dual parameters and toxicity or releases to the
water column. In no case have we seen any author
evaluate bulk sediment data as an overall family
of data rather than as individual parameters.
Thus far, our overall classifications agree
remarkably well with bioassays using organisms
indigenous to the lakes..."
With this background, bulk sediment properties shown in Table 6 can
be discussed. The discussion begins in general terms to identify zones
of highest contamination then proceeds to a more specific description of
noteworthy stations.
28
-------
(1) Percent Solids and Particle Size. In general, higher
percent solids and larger proportions of sand relative to silt and clay
were observed at tue lakeward stations and at stations upstream of the
E Street Bridge. The intermediate stations between stations 5A and 12A
produced fine-grained sediments with high water content. The fine-grained
sediments tended to be more polluted, as the following discussions show.
(2) Organic Pollutants. Percent volatile solids, Immediate
Oxygen Demand, and TKN (Total Kjeldahl Nitrogen) are indicators of organic
matter in sediments. The Immediate Oxygen Demand (IOD) test (see Appendix
B for specification) is an indirect method of assessing organic deposition.
It is a simple yet effective measure of the oxygen consuming potential of a
sediment that is mixed with water. The reduced iron, manganese, and sulfide
species responsible for this oxygen consumption are associated with low Eh
(redox potential) caused by anaerobic decomposition of organic matter in the
sediments. All three of these parameters (volatile solids, TKN, and IOD)
were found to indicate the highest degree of organic pollution between
Turning Basin No. 1 and the E Street Bridge. Most of the stations within
this reach had values of these parameters many times higher than stations
farther upstream or downstream. Organic contamination such as this could
occur because of natural conditions (settling of detritus) or from the
historic discharges of wastewater and urban stormwater to Trail Creek.
Because detritus such as leaf litter was observed in very few sediment
samples, it is not likely that the organic sediment components are primarily
natural.
(3) Oil and Grease. At most stations between Turning Basin
No. 1 and the E Street Bridge, oil was clearly detectable in the sediments
by sight and smell. The act of taking sediment samples often caused an oily
sheen to appear on the water surface. These observations are corroborated
by the data in Table 6, showing elevated concentrations of oil and grease
between Stations 4A and 11.
The most severe oil and grease contamination was found at Stations
7, 8A, 8B, 8C, and 11. These stations all are near marinas, indicating
the effects of power boat activities. Engine maintenance at the marinas
may be a source of oily materials, possibly through accidental spills and
runoff of oily soil and storage yard debris during storms.
(4) PCB. Polychlorinated biphenyl distribution in Trail
Creek sediments is scattered; although the highest concentrations occur
in the same reach as the highest concentrations of other pollutants, some
stations in this reach (e.g. 8B and 8E) produced samples with PCB below
detection limits. Review of Table 6 and Figures 2 and 5 shows that most
of the higher values occurred between the railroad bridge and Turning
Basin No. 1. The presence of any PCB is undesirable, but the concentrations
found are not unusually high for an urban area (1).
29
-------
(5) Arsenic. The pollutant most influential in the
inclusion of Michigan City as a Priority 1 location in the first report
on Section 115 was arsenic. Data available at the time of that report
showed arsenic concentrations in the thousands of mg/kg dry weight. This
study found a maximum arsenic concentration of 21.7 mg/kg dry weight. It
is interesting to note that most stations for which more than one core
depth interval was analyzed for arsenic showed more arsenic in the deeper
sediment than on the surface (Table 6). This trend may indicate that
the source of arsenic is diminishing or has ceased. (One possibility is
aerially transported fly ash, reduced in recent years by air pollution
control equipment at the NIPSCO station). No other pollutants showed
kind of trend with depth intervals in the sediment cores.
(6) Other Heavy Metals. All the other heavy metals
investigated showed the same tendency toward relatively high concentra-
tions between Turning Basin No. 1 and the E Street Bridge. The
concentrations in this reach of Trail Creek are typical of heavily polluted
urban waterways in the U.S. The levels of cadmium and zinc in Table 6
are seen by a review of the data in the first Section 115 report to be
among the highest in the country (1).
A review of all stations for which more than one core depth interval
was analyzed (Stations 4A, 6, 7, 8C, 11, and 12A) does not indicate
consistent trends of heavy metals with depth. With the possible exception
of arsenic, pollutant concentrations did not vary consistently with depth
in the cores. Thus, throughout the history of deposition of polluted
sediments, little change appears to have taken place.
c. Elutriate Te_sts_
Laboratory tests were performed to assess the short-term availability
of in-place pollutants to the water when intimately mixed with the water
as would occur during hydraulic dredging, open-water disposal of dredged
materials, or other turbulent mixing event. Test methods are given in
Appendix B. Briefly, elutriate tests involve shaking sediments with clean
water, settling and filtering the water, and analysis of the filtrate. The
results, shown in Table 7, yield the following brief interpretations.
(1) Ammonia. The NH3 - NH4+ species were released to
the aquatic phase in large amounts by the sediments from the polluted
reach between Turning Basin No. 1 and the E Street Bridge. The greatest
releases were from Stations 5A and 7 (Table 7). These stations both
had high values of TKN in the bulk analyses (Table 6), so the release of
ammonia nitrogen from these samples in the elutriate test is not surprising.
(2) Heavy Metals. Release of heavy metals was inconsistent,
as a review of Table 7 shows. Often the elutriate contained lower metal
concentrations than site water (for example, Zn at most stations). This
type of behavior is often observed in the elutriate test, and is generally
attributed to adsorption of metal ions to clay particles.
30
-------
(3) PCB. Detectable levels of PCB were not released in
any elutriate tests.
(4) Aeration vs. Shaking. Agitation for the elutriate
tests was provided by two means for some stations, to determine whether
aeration rather than mechanical shaking produced consistently different
results. The two procedures used to suspend the sediments did not
reveal consistent trends with regard to any tendency for either proce-
dure to release more or less pollutant to the aquatic phase. For
example, Table 8 compares the two agitation methods for Stations 7 and
13D.
Table 8. Comparison of Aerated vs. Mechanically
Shaken Elutriate Tests for Two Stations
Station Agitation Method that Resulted in Higher Levels of Each Parameter
m3~® Cd Cu Ni Pb Zn £H Do
7 A (Aeration) AS A A S AS
13D S (Shake) A A S A S A A
As an earlier discussion noted, elutriate tests are not of primary
importance in assessing in-place pollutants, but do have potential use for
assessing dredging and disposal options. Because the focus here is on
in-place pollutants, the elutriate test results do not weigh heavily in
the following summary of sediment testing.
d. Summary of Physical and Chemical Analyses
The preceding discussion reveals general patterns of water and sedi-
ment characteristics. More specific trends will now be described, forming
the rationale for selection of stations to be investigated through bioassays
and benthos studies.
Themost important inference that can be gained from reviewing the
data is that Trail Creek and Michigan City Harbor are not characterized by
intense, localized "hot spots." Rather, the entire reach from Turning Basin
No. 1 to the wastewater treatment plant exhibits a fairly uniform bottom type
with regard to in-place pollutants. Upstream and lakeward of this reach are
areas much less affected by anthropogenic sediment contaminants.
Despite the absence of intense "hot spots", several stations within the
polluted reach of Trail Creek are anomalously low in one or more pollutants.
Stations 8B and 8E, for example, did not contain detectable quantities of
PCB. Similarly, some stations were low in arsenic relative to surrounding
stations. No correlations were apparent between these observations and sta-
tion location or other sediment parameters.
31
-------
Because the stations within the polluted reach were fairly uniform in
physical and chemical characteristics, it was not necessary to use any com-
plex indexing schemes for selecting priority stations for biological studies.
A simple rank-ordering was performed for the stations with highest concen-
trations of pollutants in surficial sediments. This rank-ordering (Table 9),
while providing a convenient summary of relative sediment pollution, was a
further indication that in-place pollutants are widespread rather than con-
fined to ':hot spots".
The following\ stations were selected for analysis of benthos:
Station 4A, with the highest PCB content but relatively
low values of other pollutants except arsenic and TKN.
Stations 6, 7, and 8B, representing the most contaminated
stations (most pollutants ranked in Table 9). Station
8B was of particular interest because of a PCB concentra-
tion below the detection limit.
Station 11, which showed high burdens of heavy metals and
oil and grease, in comparison with neighboring upstream
stations.
Station 13D, a relatively "clean" station downstream of
the wastewater treatment plant outfall and upstream of the
Federally authorized navigation channel.
The particularly interesting stations in the above group: 4A, 8E and
11, were selected for bioassays, together with Station 1, a relatively un-
contaminated area at the mouth of the harbor which served as a control.
C. INVESTIGATION OF BENTHIC ASSEMBLAGES
These investigations were conducted by Dr. Thomas McComish and his
students at the Department of Biology, Ball State University, Muncie,
Indiana.
1. Methods and Materials
In the laboratory, all macrobenthos were separated from debris in each
sample by hand. The procedure involved placing a small amount of the sample
in a 90 mm diameter gridded petri desh, adding water and slowly searching
through all debris. After sight recognition, each organism was removed
with a forceps, counted and sorted into an appropriate vial with about 10
percent formalin as a preservative.
The identification procedure varied according to the group involved.
Chironomids were first examined wet using a dissecting microscope at 12.5
to SOX. Then each head capsule was removed and mounted on a microscope
slide in polyvinyl lactophenol and a cover was added. Head capsules were
examined at 100 to 400X using a compound microscope. Chironomids were
32
-------
Table 9. Rank-ordering of Stations by Concentration of Each Parameter Measured
Parameter
Rank (e.g. 1 =
Blank =
Station
2
3c
4a
5a
5b
5c
6
7
8a
8b
8c
8d
8e
9a
9b
10
11
12a
12b
13b
Volatile
Solid
4
7
IT
IT
8
5
6
3
IOD
8
2
7
3
1
5
6
4
TKN
3
4
1
2
6
5
7
8
Oil &
Grease
8
7
5
2
6
1
3T
3T
PCB
8
1
4
6
7
5
3
2
As
5
4
1
7
2
3
6
8
Highest concentration of all stations.
Not among 8 stations most
in that pollutant)
Cd
3
8
1 2
4
5
7
2
6
Cu
8
6
1
5
7
1
3
4
Ni
2
7T
4
5
6
8
3
7
concentrated
Pb
4
7T
3
4
2
1
6
5
Zn
7
5
8
2
3
6
-------
identified only to genus with the aid of appropriate keys but primarily
Mason (16). Other arthropods, molluscs and leeches were identified from
wet mounts using the dissecting microscope noted above and suitable
taxonomic keys.
Oligochaetes were extremely numerous in samples necessitating sub-
sampling for specimens to identify. The procedure was to place all of the
worms from a sample onto a tray (25 x 40 cm) gridded into 1000 numbered
square centimeters. Care was taken to spread the specimens evenly over
the tray. Next a table of random numbers was used to select a specific
numbered square centimeter from the tray. All worms were removed from
the centimeter and enumerated. Additional square centimeters in the grid
were selected using this procedure until about 100 intact specimens were
accumulated for a sample. Then the worms for each subsample were mounted
in CMC-10 (Turtox), a non-resinous mounting medium with clearing agent
and a cover slip was added. Specimens were identified to species when
possible using suitable taxonomic keys, but mainly Hiltunen (17), and a
compound microscope at 100 to 1000X. Peloscolex multisetosus multisetosus.
P.. m. longidentus and Limnodrilus udekemiames were identified in all life
stages (mature and immature). The remaining species (see Table 10) were
only identifiable as adults. Immature tubificids which were not identi-
fiable were listed only as with or without capilliform chaetae.
2. Results and Discussion
Oligochaetes dominated the bottom fauna on a numerical (Table 10)
and percent composition (Table 11) basis. The number per ponar grab
ranged from over 10,000 at station 8b to about 400 at station 7 with a
mean for all stations of about 3,000. Large numbers of Oligochaetes
relative to other benthic organisms is clearly shown by percent composi-
tion which ranged from 96.9 at station 7 to 100.0 at station 8b.
The oligochaete fauna was dominated by Limnodrilus spiralis. L.
hoffmeisteri. and Tubifex tubifex at most stations. The population level
of 1. tubifex was particularly high (8,900 per grab, or an estimated
185,000 per mz) at station 8b and the average for all stations was over
1,800 per grab. J\ tubifex was, however, absent at station 13d. L_.
spiralis and L. hoffmeisteri population levels were generally lower" than
. tubifex. The maximum and average numbers for these two species respec-
tively were 1500 (estimated 31,000 per mz) and 640, and 400 (estimated
8,000 per m2) and 190.
A single species of carnivorous midge, Procladius sp_. dominated the
chironomid fauna (Table 10). It was present at all stations but in very
low numbers (1 to 11, mean of 6). The three genera of midges in samples
comprised only from 0.1 to 2.5 percent abundance at stations.
Other taxa represented included: a single mayfly specimen (Hexagenia
limbata) which was probably a transient carried by currents from elsewhere,
a single gammarid (Crangonyx gracilis). a single crayfish, individual
specimens of two leeches (Helobdella stagnalis. and Dina sp.), and sphaerid
clams (Pisidium sp.) in very low numbers (2 to 4 per grab).
34
-------
Table 10. Macrobenthic organisms in Ponar grab samples collected at stations in
the Trail Creek Study Area, Michigan City, Indiana in April, 1977
LO
Ul
Taxa
Annelida
Oligochaeta
Tubificidae
Ilyodrilus templetoni
Limnodrilus cervix
Limnodrilus claparedeianus
Limnodrilus hof fmeisteri
Limnodrilus spiralis
Limnodrilus udekemianus
Peloscolex multisetosus
longidentus
Peloscolex multisetosus
multisetosus
Tub if ex tub if ex
Unidentifiable immature
With capilliform chaetae
Without capilliform chaetae
Hirudinea
Glossiphoniidae
Helobdella stagnalis
Erpobdellidae
Dina sp.
Number per Grab at Station
4a
2142
2142
2142
45
156
89
381
66
135
111
446
713
334
379
—
—
__
—
6
2237
2237
2237
25
25
402
327
76
125
25
577
655
378
277
—
—
__
—
7
443
432
432
6
6
153
179
60
11
17
6
11
1
1
1
—
8b
10416
10415
10415
—
115
469
8904
927
698
229
1
—
1
1
11
5702
5702
5702
—
108
51
1290
108
376
1129
2640
1237
1403
—
—
—
—
13d
2737
2737
2737
—
57
1526
27
1070
85
985
—
—
—
—
-------
Table 10 (Continued)
U)
Taxa
Arthropoda
Crustacea
Amphipoda
Gammaridae
Crangonyx gracilis
Decapoda
Unidentifiable
Insecta
Ephemeroptera
Ephemeridae
Hexagenia limbata
Diptera
Chironomidae
Tanypodinae
Procladius sp.
Psectrotanypus sp.
Alabesmyia sp.
Unidentifiable
Chironominae
Chionomus sp.
Mollusca
Pelecypoda
Sphaeridae
Pisidium sp.
Number per Grab at Station
4a
1
—
—
—
—
—
1
—
—
—
1
1
1
1
—
—
—
—
__
4
4
4
4
6
7
—
—
—
—
—
7
—
—
__
7
7
7
7
—
—
—
—
....
2
2
2
2
7 8b 11
13 5 3
2
1
1
i _
_L ™-^
1
1
11 5 3
—
—
_
11 5 3
11 5 3
11 5 3
952
i _ _
JL "•
1
1
—
»— «_ ___
— — — „
—
— — —
— _.. __
13d
13
—
—
—
__
—
13
1
1
1
12
12
12
11
—
—
1
1
—
—
__
-------
Table 11. Percent composition and total taxa for macrobenthic
organisms in Ponar grab samples collected at stations in the Trail Creek
Study Area, Michigan City, Indiana in April, 1977
Taxa
^
Annelida
Oligochaeta
Hirudinea
Arthropoda
Crustacea
Insecta
Ephemeroptera
Diptera
Mollusca
Pelecypoda
Total Taxa**
Station
4a
99.8
99.8
—
T*
—
T
—
T
0.2
0.2
10
6
99.6
99.6
—
0.3
—
0.3
—
0.3
0.1
0.1
10
7
97.1
96.9
0.2
2.9
0.4
2.5
—
2.5
—
—
11
8b
100.0
100.0
T
T
—
T
—
T
—
—
5
11
99.9
99.9
—
0.1
—
0.1
— _
0.1
__
—
8
13d
99.5
99.5
__
0.5
__
0.5
T
0.5
__
—
7
*T = Trace; less than 0.1%
** Number of different taxa classified at least to genus,
37
-------
Diversity at all stations was very low. The total taxa, which
included organisms identified at least to genus, ranged from 5 to 11 (Table
11). Diversity of organisms was highest (10 to 11) at downstream stations
4a, 6, and 7 and lowest (5 to 8) at upstream stations 8b, 11, and 13d.
These data tend to show slightly improved environmental conditions at
downstream stations, probably because of the dilution effect of lake water
entering the creek during reverse flow. This dilution apparently outweighs
the fact that in-place pollutants were generally more concentrated at the
downstream stations. In general, however, the biota show severe limitation
in diversity at all stations.
The low diversity together with high numbers of oligochaetes and the
indicator species predominating indicate conditions of high organic enrich-
ment at all stations. Brinkhurst (18) presents data for European rivers
with "bad" organic pollution. Tubificids which were population dominants
for this degree of pollution Included T_. tubifex, L. hoffmeisteri and L.
udekemianus. These species, together or in part, were major components of
the oligochaete communities at stations sampled in Trail Creek. Brinkhurst
also points out that I_. tubifex and 11. hoffmeisteri "are the most resistant
(oligochaetes) to organic and inert mineral pollution in Britain".
Additional evidence for conditions of poor water quality and environ-
mental conditions (e.g. substrate components) is the few oligochaete species
at stations. Downstream stations 4a, 6, and 7 had from 6 to 8 oligochaete
species present while more upstream stations had only 3 to 6 oligochaete
species. Further, the only crustaceans (Crangonyx gracilus and an unidenti-
fiable crayfish) and molluscs (Pisidium sp.) sampled were at the downstream
stations. These data support the possibility of slightly improved down-
stream conditions probably because of dilution with cleaner Lake Michigan
water. Brinkhurst (18) points out that as environmental conditions im-
prove toward "normal", more oligochaete species are found. Such was the
case for Trail Creek downstream compared to upstream stations. It should
be emphasized, however, that all stations indicate "bad" to "gross" pollu-
tion as defined by Brinkhurst (18) for stream conditions.
Relationships between thes.e findings and the physical-chemical data
are investigated in the next section of the report (Section VI).
D. SEDIMENT BIOASSAYS
These studies were performed by the University of Michigan Biological
Station at Pellston. Because the description of methods and materials is
quite detailed, it appears in Appendix C.
1. Introduction
The purpose of this investigation was to design and conduct acute
static bioassays to determine the effects of Michigan City Harbor sediments
on biota. Although laboratory bioassay procedures for waterborne toxicants
are well-established (19,20) only a few sediment bioassays have been con-
ducted (21,22,23). Because of the dynamic nature of chemical equilibria
38
-------
at the sediment-water interface (24) , laboratory test conditions should be
maintained as closely as possible to those in the field.
Organisms indigenous to Lake Michigan which were readily adaptable
to laboratory conditions were selected for the tests. Four species were
included, representing different trophic levels and habitats: Pontoporeia
affinis Lindstrom, Cyclops bicuspidatus thomasi Forbes, Daphnia galeata
mendotae Birge, and Salmo gairdneri Richardson. The amphipod Pontoporeia
affinis was selected because it is a sensitive indicator of polluted con-
ditions and is an abundant species in the benthos of Lake Michigan offshore
waters (22). The co^epod Cyclops bicuspidatus thomasi was chosen because
it is the most abundant crustacean plankter in Lake Michigan (25) and is
often most prevalent near the sediment-water interface (25). The cladoceran
Daphnia galeata meruiotae was selected because Daphnia have frequently been
used as freshwater test organisms in laboratory bioassay and comparative
literature is readily available (19). This planktonic species is common
throughout Lake Michigan (26). Salmo gairdneri (rainbow trout) was chosen
as the fourth species because it is commonly stocked in nearshore waters
of Lake Michigan and is widely used in bioassay tests.
2. Overview of: Methods
Although detailed procedures are given in Appendix C, the general
methods are described here for the reader seeking a less thorough descrip-
tion.
Two types of tests were performed: a sediment preference test with
Pontoporeia, and toxicity tests with all four organisms. The sediment
preference test involved the following major steps:
Place sediments from 27 stations in small containers, onen
at top
Place containers on the bottom of a large aquarium filled
with clean water
Scatter 100 organisms evenly over the water surface
Tabulate live and dead individuals in each container after
48 hours.
Because Pontoporeia prefers clean sediments, the number of individuals
selecting a sediment in this type of test provides some insight regarding
the relative suitability of each station to support "desirable" benthic
life.
Static bioassays were conducted in apparatus containing sediment from
a sampling station, with clean lake water over the sediment. Very little
work has been reported in the literature on solid phase bioassays of this
type. A manual discussing bioassays of dredged materials has recently
been published by EPA and the Corps of Engineers (27), and the solid phase
39
-------
bioassays described there have no variance of water .-sediment ratios.
The criterion for assessing the dredged material is a comparison of per-
cent mortalities observed with dredged material to mortalities observed
with a clean control sediment. Prater and Anderson (23) used a similar
approach.
Such a selection of a single water:sediment ratio provides little
opportunity for quantitative assessments (e.g. LC50 computations). There-
fore, a range of water:sediment ratios was used in this work for each
station and for each organism tested. In accordance with standard prac-
tice, the same size aquaria were used for all sediment bioassays with each
species. Therefore, sediment area was constant and equal to the plan
area of the aquarium used for each species. "Concentration" was varied
by varying the volume of water over the sediment. The controlled variable
in these tests was therefore not the suspected toxicant, but the diluent
water. Therefore, the ratio
volume of water
surface area of sediment
is used to derive inferences regarding the toxicity of each sediment.
No literature has been found on such sediment bioassays with variable
"concentration." The use of the above ratio therefore has no precedent;
it was used simply to be consistent with standard bioassay practice wherein
the controlled variable (normally an added toxicant, but in this case
the dilution water) is the numerator in the expression for "concentration."
As a result of the use of this type of ratio, and in contrast to conven-
tional bioassays, higher LC50 values indicate higher toxicity.
3. Results and Discussion
a. Sediment Preference Test
Duplicate tests were run, referred to here as Trial One and Trial
Two. Upon termination of Trial One, 67 individuals had selected sedi-
ments, with 42% found in the open-lake sediments from Station 1, and the
remainder scattered in 9 of the Harbor sediments. Upon termination of
Trial Two, 79 individuals were present in the sediments, with 54% occur-
ring in the open-lake sediments and the remainder found in 15 of the Harbor
sediments (Table 12).
The sediment preference test can be useful in determining whether
land or water disposal is more suitable for harbor dredgings because altera-
tion of the substrate and introduction of toxic substances at the disposal
site are probably the primary factors which cause adverse effects on the
benthos. The test is of less direct use to this study of in-place pollutants,
because the physical character of sediments is important in the preference of
mobile organisms. That is, even unpolluted harbor sediments may be avoided
by Pontoporeia simply because they are too fine-grained. The primary appli-
cations of the test to this study are two:
40
-------
Table 12. Results of Sediment Preference Tests with Pontoporeia
Station No.
1
1
1
1
1
1
Totals
2
3a
3b
3c*
4a
4b
4c
5a
5b*
5c
6
7
8a*
8b*
8c
8d
8e
9 *
9b*
10
11 *
12a*
12b
13b
13c
13d*
Totals
Trial
Live
7
8
1
0
6
2
24
3
7
0
0
4
2
0
0
0
1
0
3
0
0
0
1
4
0
0
0
0
0
0
11
0
0
36
One
Dead
0
1
1
0
1
1
4
0
0
0
0
1
1
0
0
0
0
0
0
0
0
0
0
1
0
0
0
0
0
0
0
0
0
3
Trial
Live
2
7
5
3
7
15
39
3
4
0
0
0
1
4
1
0
1
4
2
0
0
1
0
0
0
0
1
0
0
1
2
5
0
30
Two
Dead
0
2
1
0
0
0
3
0
1
1
0
1
0
0
1
0
0
0
1
0
0
0
0
0
o
0
0
0
0
0
0
2
0
7
*Sediments which did not contain any Pontoporeia after either trial.
41
-------
As a simple estimator for overall substrate suitability
As a quick and approximate guide to toxicity of a large
number of sediment samples.
Tests with Michigan City Harbor sediments indicated that Pontoporeia
displayed greatest preference for open-lake sediments. Those Harbor
sediments selected by Pontoporeia did not appear to adversely affect
this species, since mortality was low or absent in the preference tests.
Gannon and Beeton (22) conducted similar sediment preference tests
on sediments from harbors of Lakes Michigan, Erie, and Ontario and observed
that Pontoporeia preferred those sediments with the highest proportion of
sand, lowest chemical oxygen demand, and lowest amounts of volatile solids,
phosphate-phosphorus, and ammonia-nitrogen. They suggested that Pontoporeia
may be especially sensitive to petroleum hydrocarbons since dead amphipods
were usually covered with oil. However, other potential toxicants such as
heavy metals, chlorinated hydrocarbons, or pesticides may be causative
factors. These potential relationships are explored in Section VI, where
bioassay data are related to sediment analyses.
b. Bioassays
The three test sediments displayed the same increasing order of
toxicity (4a-ll-8b) in all bioassays (Tables 13-15). Extending the
duration of assays with Pontoporeia and Daphnia from 48 to 96 hours resulted
in a slight increase in mortality although the slope function remained
nearly the same. Mortality at maximum test concentrations employed averaged
25.7% for Station 4a sediments, 53.3% for Station 11, and 97.2% for Station
8b (Tables 13-15).
Mortality was sufficiently high in Station 8b sediments to calculate
LC 50 values with all test organisms. Based on LC 50 values, Salmo were
most sensitive to 8b sediments, followed by Daphnia, Pontoporeia, and
Cyclops.
Sediments from Station 11 were less toxic than 8b sediments. Mortality
was sufficiently high in the 96-hour assays with Daphnia and both 48 and
96-hour assays with Pontoporeia to calculate LC50 values. In remaining
tests with this sediment, LC 50 values were estimated by extrapolation.
Salmo was most sensitive to Station 11 sediments, followed by Pontoporeia,
Daphnia and Cyclops.
Sediments from Station 4a were least toxic. The LC 50 values were
estimated by extrapolation for all test organisms. Salmo was least sensitive
to sediments from Station 4a, with no mortality occurring in any of the test
concentrations. Cyclops were most sensitive, followed by Pontoporeia and
Daphnia.
Behavior of the organisms under test conditions frequently indicated
physiological stress. Pontoporeia tended to burrow immediately when
42
-------
Table 13. Summarized Data for Sediment Bioassays with Pontoporeia affinis
Station
Maximum
Percent
Mortality
LC50
(liters/in2)
Slope
Function
48-hour Bioassay
4a
8b
11
96-hour Bioassay
4a
8b
11
31
100
72
37
100
96
6.2* (8.5-4.5)+
20.5 (23.0-18.2)
17.0§ (17.2-16.1)
8.6* (11.5-6.4)
23.5 (27.0-20.4)
96.0§ (20.1-18.0)
0.46
0.71
0.37
0.71
*Extrapolated value from concentrations less than the LC 50
+Lower and upper 95% confidence limits.
§Estimated LC50 determined by the moving average-angle method of Harris (28)
43
-------
Table 14. Summarized Data for Sediment Bioassays
with Daphnia galeata mendotae
Station
Maximum
Percent
Mortality
LC50
(liters/m2)
Slope
Function
48-hour Bioassays
4a
8b
11
96-hour Bioassays
4a
8b
11
28
100
35
40
100
69
2.7* (5.6-1.3)+
30.3§ (35.2-25.4)
8.6* (13.6-5.4)
6.6* (11.0-4.0)
41.2§ (45.2-37.2)
13.3§ (15.1-12.0)
0.13
0.40
0.17
*Extrapolated value from concentrations less than the LC 50.
+Lower and upper 95% confidence limits.
§Estimated LC50 determined by the moving average-angle method of Harris (28)
44
-------
Table 15. Summarized Data for 48-hour Sediment
Bioassays with Cyclops bicuspidatus thomasi and Salmo gairdneri
Station
Maximum
Percent
Mortality
Cyclops bicuspidatus thomasi
4a
8b
11
Salmo gairdneri
4a
8b
11
18
100
18
0
83
30
LC50
(Iiters/m2)
6.7* (8.6-5.2)+
17.5 (20.3-15.1)
8.1* (11.6-5.7)
94.5 (111.2-80.3)
44.5* (58.6-33.8)
Slope
Function
0.61
0.59
0.49
0.64
0.58
*Extrapolated value from concentrations less than the LC 50
+Lower and upper 95% confidence limits.
45
-------
introduced into the test vessels but generally left the sediments when
physiologically stressed. Dead individuals were found lying on the sedi-
ment surface. Daphnia rarely experienced entrapment in the surface film
at the air-water interface while in culture or during test conditions
with open-lake sediments, but entrapment occurred frequently under toxic
test conditions. This apparently resulted from erratic swimming behavior
elicited by physiological stress. Behavioral indications of stress in
Cvcl°Ps could not be observed because of their very small size and burrow-
ing nature. Active movements of Salmo kept the sediments agitated This
sediment disruption resulted in such a high turbidity level with sediments
8b and 11 that individuals could be observed only when near the surface
ll ?^t0< !at^ s'ressed individuals were present near the surface, whereas
healthy individuals were primarily near bottom.
It is quite likely that suspended sediments were a significant factor
u f°r Salmo' especially in view of the fact that Station 4a
which did not have high turbidity in the Salmo tests, produced no mortali-
ties. Tests with Stations 1 and 4a for Salmo. and for all stations with
the other three organisms, were characterized by consistently clear water.
Sediments 4a and 11 were considerably less toxic than 8b sediments.
The relatively low mortalities do not appear to be artifacts resulting
from experimental design. Bioassays could not be run at any higher concen
trations than were actually employed, since this would have resulted in
water volumes being inadequate for maintenance of organisms.
The results of the physical, chemical and biological investigations
are interrelated in Section VI.
46
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VI: INTERPRETATION: CHARACTERIZATION OF
ZONES WITHIN THE CREEK AND HARBOR
Having described in an objective and quantitative way the charac-
teristics and effects of Trail Creek sediments, this report must interpret
those findings. This interpretation is needed to define areas or zones
with certain sets of characteristics so that priorities can be assigned
for any recommended action.
A. RELATIONSHIPS AMONG BIOLOGICAL AND PHYSICAL-CHEMICAL DATA
1. Macrobenthos Investigation
The results of the detailed studies of macrobenthos, presented in
Section V, showed that even at stations that were relatively "clean" from
a chemical standpoint, the benthic assemblages indicated severe organic
pollution. Annelida comprised more than 97% of the organisms at all six
stations selected for detailed study (Table 10), and the total taxa ranged
from 5 to 11. Little difference was noted between stations, although
conditions at the downstream stations appeared to show slightly improved
conditions relative to the upstream stations.
Chemically, there is no apparent corresponding evidence that the
three downstream stations (4A, 6, and 7) were any lower in in-place
pollutants than the three upstream stations (8B, 11, and 13D). Two
possible interpretations may be made:
a) Benthic environments in the entire reach between
stations 4A and 13D are so polluted that none of the
benthic assemblages is significantly "healthier" than
any other. OR,
b) The downstream benthic assemblages are, in fact,
slightly less improverished than those upstream.
The dilution by lake water, enhanced by the seiche
effect, permits a slightly more diverse benthic
community to exist.
Formal resolution of this question is not possible with the data
available, and it is probably not a worthwhile goal. It is clear that
the entire reach from Station 4A to Station 13D (at least) is charac-
terized by a poor benthic habitat, and fine gradations within this
reach have little significance. A clearer distinction among stations
was provided by the bioassay data.
2. Bioassays
The approach used to interpret bioassay data in view of sediment
quality has been simply to plot LC50 vs. concentration of in-place pollu-
tants. From this effort, some possible relationships between sediment
47
-------
toxicity and pollutant concentrations have appeared. Several sediment
contaminants, however, have not been shown by this effort to exert toxicity.
The most likely reason for not demonstrating the toxicity of known pollu-
tants in the sediment is that the concentrations of such substances were
not sufficient to exert independent, discernible toxic effects in the
presence of more dangerous concentrations of other substances. Another
possibility is that antagonistic effects among sediment contaminants were
exerted in some samples. That is, the presence of one pollutant may have
decreased the toxicity of another. Such effects sometimes occur with
combinations of heavy metals, although synergistic effects are also pos-
sible among other combinations.
Some of the correlations between LC50 and pollutant concentration
are shown in Figures 7 (lead), 8 (cadmium), 9 (percent volatile solids)
and 10 (oil and grease). For these parameters, concentrations and
toxicities both increase monotonically in the station sequence 1, 4A,
11, 8B. (In viewing the graphs, it is important to note that LC50 is
expressed in l/mz, as explained in Section V. Therefore, in contrast
to conventional bioassays, higher LC50 values indicate higher toxicity.)
No one of the plots of Figures 7 through 10 should be taken as proof
of a particular substance's exertion of toxicity in these tests. Many of
the parameters are highly intercorrelated in Michigan City and in other
waterways. Therefore, only one or two of the parameters might be important,
with the others implicated only circumstantially because of their correla-
tion with the causative toxicants.
One illustration of this possibility is in Figure 11, showing an
"effect" of percent solids similar to the trends of known pollutants
shown in Figures 7 through 10. Lower percent solids would appear to
exert higher "toxicity" if this Figure were taken out of context. In
fact, low-solids-content sediments in urban areas tend to consist of
large concentrations of recently settled fines, organics, and ferrous
iron and manganese oxides, all of which are likely to have high concen-
trations of sorbed toxic pollutants. On the other hand, it can be
argued that low solids content could exert its own effects through
the ease by which solids can be resuspended from such fluffy sediments.
Such may have been the case in some Salmo tests, but with the other
organisms the water remained clear.
Despite the cited uncertainties, it can be stated with some con-
fidence that one or more of the parameters represented by Figures 7
through 11 were responsible for the observed toxicity, at least in part.
This statement cannot be made for other investigated pollutants. For
example, the station with highest PCB concentration (4A) produced rela-
tively little toxicity while a station with undetectable PCB (8B) was
the most toxic of those tested (Figure 12). Similarly inconsistent
effects were noted for zinc, arsenic, TKN, immediate oxygen demand, and
percent clay.
48
-------
100
90
80
70
60
50
40
30
20
10
Percent
Mortality = 0
O
to
u
I-J
S = Salmo
D = Daphnia
C = Cyclops
p = Pontoporela
100 150 200 250 300 350
Lead Concentration (mg/kg)
400
450 500
475
Figure 7. Apparent Effect of Lead Concentration on Toxicity
of Michigan City Sediments
49
-------
O
u">
O
95
90
80
70
60
50
40
30
20
10
Percent
Mortality = 0
s Salmo
•= Average LC50 for Cyclops
Daphnia, and Pontoporeia
0 " 10 20 " 30 40 50 60
Cadmium Concentration (mg/kg)
Figure 8. Apparent Effect of Cadmium Concentration on Toxicity
of Michigan City Sediments
50
-------
100
90
80
70
60
50
40
30
20
10
Percent
Mortality = Ol_^
0
i I
S= Salmo
= Average LC50 for Cyclops,
Daphnia, and Pontoporeia
6 8 " 10 12
Percent Volatile Solids
14 16 17
Figure 9. Apparent Effect of Volatile Solids on Toxicity of
Michigan City Sediments
51
-------
CM
90
80
70
60
50
40
30
20
10 _
Percent
Mortality = 0
S = Salmo
•= Average LC50 for Cyclops,
Daphnia, and Pontoporeia
0 S?20"0"0~
6° 8 10 12"
Oil and Grease (mg/kg)
14 15 16 17 1
Figure 10. Apparent Effect of Oil and Grease Concentration on
Toxicity of Michigan City Sediments
52
-------
CM
o
u-1
CJ
95
90
80
70
60
50
40
30
20
10
S= Salmo
»z Average LC50 for
Cyclops, Daphnia,
and Pontoporeia
70 60 50 40
Percent Solids
30
Figure 11. Apparent Effect of Percent Solids on Toxicity of
Michigan City Harbor Sediments
53
-------
10 -
Percent
Mortality = 0
5=: Salmo
= Average LC50 for
Cyclops , Daphnia,
and Pontoporela
072
074 (J. 6 0.8
PCB (mg/kg)
2
Figure 12. Relationship Between PCB Concentration and
LC50 of Michigan City Harbor Sediments
54
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B. RANKING OF ZONES WITHIN THE HARBOR
1. Criteria
a. Biological
To rank the zones in Trail Creek/Michigan City Harbor on an environ-
mental basis, one must relate the laboratory investigations conducted in
this study to each other and to the real conditions in the area. Investi-
gation of the benthic organisms present appears to be the most direct
method of assessment. However, recent and continuing mitigations of
pollutant discharges to Trail Creek may be improving the aquatic system
faster than the benthic communities can adjust, thereby slightly
lessening the validity of macrobenthic studies. Bioassays seem to be a
more direct test of the present effects of the sediments, but have some
degree of deviation from the real world in that:
Some trout tests involved unrealistically high levels
of suspended solids because of resuspension by fish
activity.
Some organisms tested, while being appropriate for
bioassays in their sensitivity to pollution, may be
too sensitive for any urban waterway. In other words,
other organisms could perhaps form a very desirable
aquatic community in Trail Creek but would not yield
a significant number of mortalities in bioassays of
the type used in this study.
Therefore, to summarize the biological investigations in terms of
criteria, the following observations are made:
The environment for macrobenthos appears undesirable
at least from Station 4A to Station 13D. No criteria
significantly differentiating "desirable" from "un-
desirable" can arise from these data.
Toxicity to a variety of organisms ranges from nil
at control Station 1 to a maximum at Station 8B, with
4A and 11 (in that order) as intermediates. Several
criteria could arise from these data:
A threshold value could be selected for LC50,
above which all sediments would be considered
"polluted".
All sediments except Station 1 could be con-
sidered "polluted" because some toxicity was
observed at those stations.
The entire study area could be considered
acceptable, implying that the toxicities
observed were not significant.
55
-------
In the absence of a generally accepted method for assessing these
types of biological data, it appears that the logical criterion should be
that only zero toxicity should be accepted. Given the uniformly poor
quality of the macrobenthic community, the bioassay data seem to provide
a level of differentiation that is not significant.
b. Chemical
Prater and Anderson (23), in their paper on sediment bioassays,
cited bulk analysis criteria developed in EPA Region V for Great Lakes
Harbors (14). Some of the pollutants listed in those criteria are
shown in Table 16, with the ranges of conditions observed at Michigan
City. The last column in Table 16, giving stations located with the
aid of Figure 5, shows most of Trail Creek between the Yacht Basin and
the Wastewater Treatment Plant to be "heavily polluted."
2. Rankings
By two sets of criteria — the Region V chemical criteria and the
macrobenthic evaluations — the entire reach from the wastewater treat-
ment plant downstream to the Yacht Basin is well described as heavily
polluted with respect to bottom sediments. The bioassay data show some
differences in toxicity within this reach. Those differences, while
statistically significant (there is very little overlap of the 95%
confidence limits on LC50 from station to station), do not appear im-
portant in the overall context of this study. That is, while Station
4A's toxicity was low in relation to Stations 8B and 11, the sediments
at Station 4A must be considered poor habitat by any rational criteria.
Therefore, no rankings of isolated "hot spots" have emerged from
this study. The surface sediments of Trail Creek and Michigan City
Harbor from the wastewater treatment plant to the Yacht Basin should be
considered a single deposit of several in-place pollutants. Trail
Creek upstream of the wastewater treatment plant is relatively uncon-
taminated, as is the mouth of the Harbor lakeward of the Yacht Basin
entrance. The Yacht Basin itself (Station 2) appears to be a unique
zone chemically. It has several in-place pollutants above the Region
V "Heavily polluted" level, but appears less contaminated relative to
the upstream areas. Except for TKN, oil and grease, PCB, and cadmium,
these sediments are similar to those at Station 4A and therefore should
be grouped with the polluted reach.
C. SOURCES OF IN-PLACE POLLUTANTS
Trail Creek has a clean, sandy benthic habitat upstream of a large
landfill and the municipal wastewater treatment plant, which are in
close proximity to each other. Downstream of these two obvious sources
of pollutants, there lies a large, relatively uniform deposit of in-place
pollutants. Because of the absence of any severe "hot spots" within the
polluted area, it can be inferred that no important point sources such
as present or historic industrial outfalls are causing problems.
56
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Table 16. EPA Region V Bulk Analysis
Guidelines (14), Compared with Michigan City Data
Parameter
Volatile solids
COD
Total Kjeldahl
Nitrogen
Oil and Grease
Lead
Zinc
Mercury
Ammonia
Cyanide
Phosphorus
Iron
Nickel
Manganese
Arsenic
Cadmium
Chromium
Barium
Copper
Nonpolluted
<5%
<40 000
<1 000
<1 000
<40
<90
<1.0
<75
<0.10
<420
<17 000
<20
<300
<3
<25
<20
<25
Moderately
polluted
5%-8%
40 000-80 000
1 000-2 000
1 000-2 000
40-60
90-200
N.A.
75-200
0.10-0.25
420-650
17 000-25 000
20-50
300-500
3-8
25-75
20-60
25-50
Heavily
polluted
>8%
>80 000
>2 000
>2 000
>60
>200
>1.0
>200
>0.25
>650
>25 000
>50
>500
>8
>6
>75
>60
>50
Reach (Station to Sta-
tion) in Study Area tha
is "Heavily Polluted"
by these Guidelines*
3C -
4A -
2 -
2 -
2 -
2 -
13B
12A
13D
13C
13C
12A
Scattered stations
2 -
13D
Scattered stations
*Some stations within the indicated stream reaches may be below the "Heavily
polluted" guideline for one or more pollutants, but these few exceptions do
not seriously reduce the uniformly polluted stream reaches indicated.
57
-------
Detailed investigations of the wastewater treatment plant and of
the landfill are beyond the scope of this study. Techniques for identi-
fying sources are limited to inferences based on the location of in-place
pollutants in relation to likely sources. Because the landfill and the
wastewater treatment plant are in the same area upstream of the in-place
pollutants, their relative impact cannot be determined. It can be
stated with some confidence that no single source other than these two
is very important, because there is little change in the character of
in-place pollutants throughout the polluted reach. Pollutants entering
Trail Creek in the landfill/treatment plant area appear to flocculate
and settle to the bottom over a long reach of Trail Creek and Michigan
City Harbor.
The determination of probable future deposition of in-place
pollutants is contingent on ascertaining the relative effects of the
landfill and the wastewater treatment plant. Some informed observations
can be made, however. The wastewater treatment plant has upgraded its
processes and has intensified its surveillance of industrial sewer users
in recent years. The process upgrading has featured chemical precipi-
tation using alum for phosphate removal, and was installed in 1973.
Before installation of chemical treatment, effluent phosphate concentra-
tions averaged 10 mg/Jl. Now, effluent phosphate averages less than
0.5 mg/A (29). The more toxic pollutants described in this project
are not monitored at the treatment plant, but an efficient system of
this type should enhance removal of a variety of substances, especially
those occurring in suspended or colloidal form and likely to settle out in
the receiving water. Therefore, the present in-place pollutant deposits
represent a historical discharge that is now improved. Any landfill
leachate entering Trail Creek probably contains only dissolved pollutants
because particulate matter should be removed by the soil's effect in
filtering leachate. Many of these substances may become sorbed to
natural stream particulates and possibly suspended solids released by
the nearby treatment plant, so these substances are likely to settle to
the bottom upon reaching the more quiescent downstream areas. Another
potential means of contamination by the landfill is direct erosion from
rainfall and runoff. If the landfill should be found by further inves-
tigation to be a major source of in-place pollutants in Trail Creek,
pollution abatement would pose a major problem. No action to ameliorate
the in-place pollutants should be undertaken before this question of
sources is resolved.
58
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VII. ASSESSMENT OF POTENTIAL CORRECTIVE ACTIONS
The previous section showed that the in-place pollutants in the
sediments of Trail Creek/Michigan City Harbor exert adverse effects on
the aquatic system. Several options are available for responding to the
conditions of polluted sediments in Michigan City Harbor/Trail Creek.
These options can be generally categorized as:
No action
Dredging
Covering
Each option has costs and benefits (except for "no action"). The follow-
ing assessments attempt to evaluate these factors in a manner that is
realistic considering the present and potential uses of the water resource
under study.
Of utmost importance is the plan by the U.S. Army Corps of Engineers'
Chicago District to perform maintenance dredging in the near future, with
upland disposal and filtration of the return water from the diked disposal
area. With knowledge of that plan, this study has sought to accomplish
the following tasks in arriving at recommendations:
Evaluate the Corps' plans in the context of
Section 115 of PL92-500.
Evaluate modification to the Corps' plans. For
example, consider dredging a greater or lesser
area to a greater or lesser depth.
Evaluate options that do not include any dredging.
A. DREDGING
It is useful to describe the dredging procedures commonly used in
the United States in a brief and general way before discussing the site-
specific aspects of the dredging option.
Dredges can be classified as mechanical or hydraulic. Mechanical
dredges operate much like land-based excavation equipment, simply
digging sediment from the bottom and transferring it to a hold. The
hold is normally in a barge, which transports the material to a disposal
site. The most commonly used mechanical dredge is the clamshell. A
clamshell dredge consists of a crane-pulley-cable system mounted on a
barge. The cables support and control a set of iron jaws that are
dropped, open, into the sediment where they are closed, enveloping a
sediment mass that is then brought to the surface and dumped into a
barge.
59
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Hydraulic dredges operate by dislodging sediments and pumping them,
slurried with ambient water, through a pipe. Although there are many
variants, the most commonly used dredges of this type are the cutterhead
and the hopper dredge. A hopper dredge is an independent vessel and
normally pumps sediments into its hold ("hoppers") for transport to the
disposal site. A cutterhead dredge has a spinning array of iron teeth
that mechanically dislodge sediments adjacent to the suction pipe inlet.
The slurried sediment is pumped through a discharge pipeline to the
disposal area, either in water outside the channel or in a diked area.
1. Present Plans for Dredging at Michigan City
The Corps of Engineers plans to maintain the navigation project at
Michigan City with a cutterhead dredge, discharging to a confined upland
disposal site. There are few data available regarding the water quality
effects of the various dredge plants because most aquatic investigations
have emphasized open-water disposal. The available data do indicate,
however, that the planned dredging and disposal methods are the least
disruptive of the generally available options involving dredging and
disposal.
The scope of planned maintenance dredging is best explained by
excerpts from the Corps' Draft Environmental Impact Statement (30):
"Project features to be maintained will consist of:
An entrance channel starting at the detached breakwater
and continuing to the second turning basin at Blocksom & Co.
This channel will be maintained at a 12-foot depth lakeward
of the entrance to the small-boat outer basin, and at a 10-
foot depth from the entrance to the outer boat basin upstream
to the second turning basin at Blocksom & Co.
A channel in Trail Creek 6 feet deep from turning basin
No. 2 to the E Street bridge.
Turning basin No. 1 at Cargill Grain Co., which will be
maintained at a 10-foot depth.
Turning basin No. 2 at Blocksom & Co., which will also be
maintained at a 10-foot depth.
After the navigation channels have been surveyed, dredging
activities are conducted to remove channel shoals that have
decreased channel depths to levels that are less than desired
depths. Based on past experience at Michigan City Harbor, it
is anticipated that the portion of the harbor channel from
the entrance to the small-boat outer basin upstream to the
limit of the project in Trail Creek will require the removal
of approximately 5,000 cubic yards of sediment per year to
60
-------
maintain safe navigation depths. In order to remove accumu-
lated sediments in the most economical manner, this portion
of the channel will not be dredged annually, but only once
every five years with each dredging operation requiring the
removal of approximately 25,000 cubic yards of sediment.
Dredging in this portion of the navigation project is expec-
ted to be performed by a contract hydraulic dredge. The
frequency of dredging operations in the channel from the
entrance to the small-boat outer basin lakeward to the de-
tached breakwater to maintain the desired 12 foot depth is
unknown due to past experience being confined to maintenance
of an 18-foot channel. This area will be dredged as the
need arises to maintain the 12 foot depth and to provide
for safe navigation. This area will be dredged by the Corps
of Engineers or by a contractor using a clamshell or dipper
dredge and scows to transport the dredged material.
During 1968, 1969, and 1970, the harbor entrance channel
was dredged by a dipper dredge and the dredged material was
deposited in an open-lake disposal area in the amount of
25,000 to 48,000 cubic yards per year. In 1971 and 1972,
the entrance channel was maintained by a dipper dredge with
the dredged materials being deposited near the shoreline
west of the harbor area in the amount of 24,900 cubic yards
in 197L and 5,800 cubic yards in 1972. No maintenance
dredging has been performed since 1972, when it became
apparent that deep-draft commerce needing the 18-foot project
depth would not return.
Disposal of Dredged Material Unsuitable for Unrestricted
Disposal
Material to be removed from the portion of the channel
from the entrance to the small-boat outer basin upstream
to the E Street bridge has been classified by the
Administrator of the USEPA as unsuitable for unrestricted
or open-lake disposal. Under Section 123 of the River
and Harbor Act of 1970 (PL 91-611), the Corps of Engineers
is required to confine polluted dredged materials in a
diked disposal facility to eliminate any further degradation
of water quality by open-lake disposal. A contained dis-
posal facility will therefore be built on a site that has
been approved by all local, state and Federal regulatory
agencies. Section 123 provides that the capacity of the
site will be sufficient to contain a 10-year period of
dredged material. Engineering analysis and past experi-
ence at Michigan City have shown that approximately 5,000
61
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cubic yards of sediments must be dredged annually to main-
tain desired depths in the channels. Therefore, the
contained disposal facility has been designed with a
50,000 cubic yard capacity to accommodate two dredging
operations of 25,000 cubic yards each.
During dredging operations, the hydraulic dredge
will discharge directly into the contained disposal
facility through a pipeline extending between the
hydraulic dredge and the contained disposal facility.
This pipeline will float directly to the disposal site.
The pipeline will carry a slurry of approximately 90
percent water and 10 percent sediment. When the slurry
is pumped into the contained disposal facility, the
water will exit the site through the sand filter
leaving behind the drying sediments. Water quality
monitoring of the contained disposal facility will be
made before, during, and after disposal operations
to monitor the effectiveness of the sand filter and
dike. This water quality monitoring program will
include sampling of physical, chemical, and biologi-
cal parameters in coordination with the USEPA, State
of Indiana Department of Natural Resources (DNR), and
the Indiana Stream Pollution Control Board. Immediate
remedial action will be taken should the monitoring
reveal any water quality problems.
Disposal of Dredged Material Suitable for Unrestricted
Disposal
Dredged material to be removed from the harbor
entrance channel extending from the entrance to the
small-boat outer basin lakeward to the detached
breakwater has been classified by the Administrator
of the USEPA as suitable for unrestricted or open-lake
disposal. The Chicago District's experience in main-
taining the authorized 18-foot channel at Michigan
City Harbor indicates that this entrance channel may
not need to be dredged frequently to maintain the
proposed 12-foot depth. However, some dredging at
irregular periods will be needed. Disposal of the
sediments from the entrance channel, consisting of
clean sand deposited by lake currents and storms as
littoral drift, will be disposed of in an open-lake
disposal area which has been approved by the Indiana
DNR."
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2. Relationship of Dredging Plans to In-Place Pollutants
Figure 13 shows the areal extent of in-place pollutant deposits
that are not included in the planned maintenance dredging. The approxi-
mate areas of these deposits are: Yacht basin, 55,000 sq m; area to
the west of the navigation channel opposite the city wharf (near Turning
Basin No. 1), 25,000 sq. m; E Street Bridge to wastewater treatment
plant, 17,000 sq m; Total 97,000 sq. m. The area to be dredged is
approximately 106,000 sq m, practically equal to the polluted area out-
side the proposed maintenance project.
At least as important as area is the depth of cut planned for the
dredging project and that which would be required to remove in-place
pollutants. These depths are needed to compute the volumes (in situ) of
material to be dredged either under present plans for the navigation
channel or under any proposed plans for dredging to remove in-place
pollutants.
To calculate the thickness of material to be removed, the following
procedures have been used:
a. The study area was divided into six parts, based on
such factors as water depth and location in or out of
the authorized channel.
b. For dredging to maintain desired depths, the actual
average water depth in each area was subtracted from
the desired depth.
c. For dredging to remove in-place pollutants, the thick-
ness of the deposit was estimated from actual field
data where possible. Where the coring device struck
hard clay, its progress was halted. The length of
soft core material retrieved, multiplied by 2 (see
Appendix A), was taken as the deposit thickness. In
the polluted area lakeward from Franklin Street Bridge,
this thickness was fairly constant, averaging approxi-
mately 1.3 meters. From Franklin Street Bridge upstream,
the small craft that could be used and the limited depth
of fall of the corer prevented the corer from
penetrating the entire thickness of in-place pollutant
deposits. In these areas, the deposit thickness was
assumed at 1.5 meters, an estimate based on the thick-
ness observed lakeward of Franklin Street Bridge.
The results of these computations are summarized in Table 17.
The estimates of material to be dredged shown in Table 17 permit
the following observations.
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LAKE MICHIGAN
CITY
POLLUTED AREAS NOT WITHIN
NAVIGATION PROJECT :
SCALE IN FEET
0 200 4OO 100 IZOO ICOO
Figure 13. In-Place Pollutant Areas Outside Navigation Project
-------
Table 17. Summary of Areas and Volumes of In-Place
Pollutants Compared to Proposed Maintenance Dredging
Location
Area
(sq m)
Yacht Basin 55,000
Yacht Basin to Franklin
St. Bridge, in channel 46,000
Yacht Basin to Franklin St.
Bridge, outside Channel 25,000
Franklin St. Bridge to
Turning Basin No. 2 38,000
Turning Basin No. 2 to
E Street Bridge 22,000
E St. Bridge to Waste-
water Treatment Plant 17,000
Total to maintain desired navigation
Total to maintain navigation and remc
Sediment
Maintain
Navigation
Only
Thickness (m)
Remove
Pollutants
0 0.7
0 1.3
0 1.3
1.4 1.5*
0.8 1.5*
0 1.5*
depths only
>ve in-place pollutants
Volume (cu m)
Maintain
Navigation Remove
Only Pollutants
0 39,000
0 60,000
0 33,000
53,000 57,000
18,000 33,000
0 26,000
71,000
248,000
*Estimates based on other parts of the study area.
-------
a. Corps of Engineers Volume Estimates
The estimates quoted earlier in this section used historical infor-
mation. Experience has shown a deposition rate of approximately 5,000
cubic yards per year, and PL 91-611 requires a capacity for a 10-year
period of dredged material. Therefore, the planned 50,000 cubic yard
capacity (38,000 cu m) seems to be in accordance with the statute.
It should be recognized that computations based on our soundings (which
agree with 1976 soundings by the Corps' Chicago District) indicate that
substantially more volume than this must be dredged to restore the
planned depths. While the planned capacity of the confined disposal
area may equal 10 years' sedimentation at Michigan City, it is less
than the present deposit in the navigation channel. The only maintenance
within the last 10 years has been in the entrance channels.
b. Depth of Cut
With the possible exception of the reach between Franklin Street
and E Street, maintenance dredging will not reach the bottom of in-place
pollutant deposits.
c. Volume of In-Place Pollutants
Although many alternatives to the proposed disposal area were con-
sidered by the Corps (31), none was capable of handling such a large
volume as 248,000 cubic meters (324,000 cu yd). It is unlikely that a
site can be found near the study area that could accommodate a confined
disposal area of this size. If dredging is to be the means for removal
of in-place pollutants, the disposal site choice will be between:
A large area, distant from Trail Creek, involving one
long and difficult transport route, or
Several smaller areas, closer to Trail Creek, involving
several transport routes and shifting from one to
another as each facility is filled.
Cost estimates for facilities to hold 50,000 cu yd were performed
by the Corps of Engineers (29). Construction costs, based on February
1976 price levels, ranged from $264,000 to $1,308,000. The high figure
represents an offshore diked facility; disposal areas on land were
estimated to cost less than $300,000. Operation and maintenance costs,
including hydraulic pipeline dredging, ranged from $4.60 to $6.90 per
cu yd. The higher figure reflects higher transport costs for an offshore
diked disposal area. Only a few acceptable sites were located, even with
the 50,000 cu yd volume criterion. Many sites proposed were unacceptable
because of wetland protection or anticipated difficulties in procurement
from private landowners. If sites could be located for confined disposal
of all polluted materials, construction costs would probably be above
-------
$2 million ( 30>000 x $300,000) and operating costs would be of a
similar magnitude (324,000 x $5 to $6 per cu yard). The total construc-
tion cost plus operating cost would thus be approximately $4 million.
With these difficulties and high costs, it is logical to inquire
about the availability of processes that could be used to detoxify the
dredged material so that it might be acceptable for disposal in Lake
Michigan. Moore and Newbry (32) investigated this possibility for
dredged materials in general:
Biological treatment was found ineffective because the BOD
of the dredged materials examined represented only a small
fraction of the oxygen demand. Variability of the material
in its physical and chemical characteristics was also found
to be a detriment to biological treatment.
Chemical treatment was found useful, but only for the liquid
fraction after separation into solid and liquid fractions.
Such treatment would therefore be in addition to, rather than
a substitute for, diked disposal.
Physical treatment by vacuum filtration or sedimentation often
can be used, but would offer little or no benefit in comparison
to the diked disposal option at Michigan City.
These findings offer no attractive alternatives to diked disposal for
Michigan City's in-place pollutants.
B. COVERING
Covering refers to the operation of leaving in-place pollutants where
they are, and covering them with a substance that prevents or retards
upward migration of pollutants. The covering material may itself provide
desirable benthic habitat (e.g. clean sand), or it may only be intended
to seal the bottom sediments (e.g. polymer film overlay).
A large number of covering options exists, including combinations
of materials and emplacement methods. Before investigating detailed
options, however, it is useful to investigate the specific environment
of Trail Creek/Michigan City Harbor as to the practicality of covering
the bottom.
1. Practical Considerations
The immediate impression received by a visitor to the study area is
that the entire waterway upstream to the E Street Bridge is devoted to
boat traffic. There is no reason to expect this use of the waterway to
decline. This navigational use requires certain channel depths.
Experience has shown that shoals form in Trail Creek within Michigan
67
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City, necessitating periodic dredging operations. It can therefore be
expected that periodic maintenance dredging will occur for the fore-
seeable future.
This situation leaves only one option that could include covering
of the bottom in the navigation channel: dredging of present sediments
below authorized depth, followed by covering, with future maintenance
dredging limited to the recently deposited sediments above the cover.
Outside the navigation channel, a wider range of options exists; however,
a piecemeal approach to different harbor zones is likely to be costly in
comparison to a more unified approach to ameliorating in-place pollutants.
2. Possible Covering Methods
If covering is seriously considered, either after dredging in the
navigation channel or independently outside the navigation channel,
several methods may be applicable.
a. Cover Materials
Four categories of burial materials can be considered: inert
materials, chemically active materials, sorbents, and sealing agents.
(1) Inert Materials. Included in this category are
coarse materials such as sand, gravel, crushed stone, and crushed glass.
Fine-grained materials that may be useful include commercially and
naturally available clays and diatomaceous earth. Fine-grained materials
should be effective in retarding leaching of the spilled material.
Recommended cover thicknesses vary with both the material (clays being
much less permeable than sands and gravels, for example) and the benthic
life of the area. Potential benthic activity has been suggested as an
important factor in determining covering depths because some species
can enhance leaching by their burrowing activity in the cover material.
Approximately 10 to 20 cm is the minimum effective cover if such organisms
are likely to colonize the cover material.
(2) Chemically Active Materials. One covering strategy
that could be considered is the placement of a chemical compound over
the in-place pollutants. This compound would be "active" with respect
to the in-place pollutants; i.e. it would react with those pollutants
to form less toxic products. This approach has some promise in areas
with a specific in-place pollutant, such as the site of a hazardous
material spill. At Michigan City, however, the in-place pollutants of
concern are a diverse mixture of substances. It is very improbable
that a mixture of chemically active covering compounds could be developed
that would be effective against all the observed in-place pollutants.
(3) Sorbents. Sorption processes have long been consi-
dered among the most promising treatment methods for spills of hazardous
68
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materials in water. Activated carbon and several ion exchangers have
been evaluated for response to hazardous chemical spills (33, 34). These
substances have the same problems as those noted above for the chemically
active materials, however.
Sealing Agents. Grouts, cements, soil sealants,
polymer covers, and gels have been investigated for this report. These
substances are advantageous because they seal off the entire mass of in-
place pollutants and are not specific in acting toward any one substance
or class of substances. They are expensive, however. Grouting and
cementing can be applied over in-place pollutants using materials ranging
from modified Portland cement to simple mixtures of pozzolanics such as
lime, fly ash, and diatomaceous earth. Techniques could range from hand
application to pressurized grouting systems such as are used in the off-
shore oil industry. Such techniques produce a solid cover. Soil sealants
might be used in the covering of in-place pollutants. These are expanding
Bentonite clays, and would be difficult to put in place and keep in place.
Mixing of clays with coarser-grained materials such as gravel might inhibit
erosion. The material could be pressure injected onto the bottom or
dispersed on the surface according to supplier's instructions. Expense
and tendencies for erosion limit the potential of soil sealants.
A barge-mounted concept of roller deployment for performed polymer
films has been proposed (35, 36, 37). Costs would be three to four cents
per square foot (based on 1972 prices, certainly higher today).
Application of gelling agents to seal off polluted sediments has
not been made, though work on land and surface spills provides hope that
such materials could be developed (34, 38). The key problem with such a
concept would be to find a gelling agent with sufficient specific gravity
to remain on the bottom. It is likely that highly portable application
devices could be developed.
3. Assessment of Covering Concepts
None of the covering methods described above has ever been used on
a large scale. Some small-scale attempts have been made to cover mercury-
laden sediments in Sweden, but these have met with limited success. With
this lack of field success, it is difficult to justify a recommendation
to attempt covering the in-place pollutants at Michigan City. There are
several conceptual difficulties in predicting success of the covering option:
Emplacement techniques and equipment presently available
cannot assure complete coverage.
The available materials that are sufficiently impermeable
to retard leaching (clays, cements, grouts) are either
susceptible to erosion or are so permanent that they
foreclose on future options for use of the waterway.
69
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The available materials that would stay in place (sands,
gravels) are too permeable to retard leaching.
Because of the absence of field experience, costs cannot
be estimated with any confidence.
Accordingly, covering cannot be recommended for actual implementation
at Michigan City unless and until field demonstrations have been conducted.
The intent of Section 115 is action, while the technology of covering is
still in the research stage.
C. SUMMARY OF POTENTIAL CORRECTIVE ACTIONS
This section has shown that the state-of-the-art for covering and for
treatment of dredged materials is not sufficiently well advanced to
warrant action in a field situation such as at Michigan City. It has
also pointed out that maintenance dredging for navigation purposes can
be expected to continue periodically. Accordingly,"dredging followed by
confined disposal of In-place pollutants should be coordinated with
channel maintenance for effective implementation of Section 115 action
at Michigan City.
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REFERENCES
1. Johanson, E.E. and Johnson, J.C., "Identifying and Prioritizing
Locations for the Removal of In-Place Pollutants," final
Report on Contract No. 68-01-2920, U.S. Environmental
Protection Agency, Washington DC, May 1976.
2. Trident Engineering Associates, Inc., "Evaluation of the Problem
Posed by In-place Pollutants in Baltimore Harbor and Recom-
mendation of Corrective Action," Report No. EPA-440/5-77-015B,
September 1977.
3. Morgan, D.W., "A Study of the Effect of the NIPSCO Michigan City
Generating Station on Salmonid Migrations in Trail Creek,"
Third Biannual Report to Northern Indiana Public Service
17 January 1977.
4. McComish, T.S., "Interspecies Relationships of Fish in Indiana
Waters of Lake Michigan," Ball State Univ., Muncie, IN, 1975
5. Environmental Instrument Systems, Inc., "Report on the Effects of
Michigan City Water Works Filter Backwash on Trail Creek,"
Michigan City Department of Water Works, November 24, 1976.
6. Morgan, D.W., "A Study of the Effect of the NIPSCO Michigan City
Power Station on Salmonid Migrations in Trail Creek," First
Semi-Annual Report to Northern Indiana Public Serice Co.,
Hammond, IN, January 1976.
7. Morgan, D.W., "A Study of the Effect of the NIPSCO Michigan City,
Generation Station on Salmonid Migrations in Trail Creek,"
Second Biannual Report to Northern Indiana Public Service Co.,
Hammond, IN, 16 July 1976.
8. Johnson, D.L., "Zooplankton Population Dynamics in Indiana Waters
of Lake Michigan in 1970," Unpublished M.S. Thesis, Ball State
Univ., Muncie, IN, 1972.
9. Rains, J.H,, "Macrobenthos Population Dynamics in Indiana Waters
of Lake Michigan in 1970," unpublished M.S. Thesis, Ball State
Univ., Muncie, IN, 1971.
10. Indiana State Board of Health and Indiana Stream Pollution Control
Board, "Indiana Water Quality-Monitor Station Records, Rivers
and Streams, 1975."
11. U.S. Environmental Protection Agency, "Quality Criteria for Water,"
Report No. EPA/440/9-76/023, July 1976.
71
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12. Lee, G.F. and Plumb, R.H., "Literature Review on Research Study
for the Development of Dredged Material Disposal Criteria."
Contract Report D-74-1, U.S. Array Engineers Waterways
Experiment Station, Vicksburg, MS, June 1974.
13. Lee, G.F., ert al, "Research Study for the Development of Dredged
Material Disposal Criteria," Contract Report D-75-4,
U.S. Army Engineer Waterways Experiment Station, Vicksburg,
MS, 1975.
14. U.S. Environmental Protection Agency, "Guidelines for the
Pollutional Classification of Great Lakes Harbor Sediments,"
EPA Region V, Chicago, IL, April, 1977.
15. Bowden, R.J., EPA Region V, Chicago, personal communication
(letter), August 26, 1977.
16. Mason, W.T., Jr., "An Introduction to the Identification of
Chironomid Larvae, Analytical Quality Control Laboratory,"
U.S. Environmental Protection Agency, Cincinnati, Ohio, 1973.
17. Hiltunen, J.K., "Keys to the Tubificid and Naidid Oligochaeta
of the Great Lakes Region," Unpublished (mimeograph), 1973.
18. Brinkhurst, R.O., "The Biology of the Tubificidae with Special
Reference to Pollution," Proc. 3rd Seminar Biological
Problems in Water Pollution, Cincinnati, Ohio, 1965.
19. Martin, D.M., "Freshwater Laboratory Bioassays - A Tool in
Environmental Decisions," Phila. Acad. Nat. Sci., Contrib.
Dept. Limnol. No. 3, 1973.
20. American Public Health Association, Standard Methods for the
Examination of Water and Wastewater, 14th ed., 1976.
21. Gannon, J.E. and Beeton, A.M., "Studies on the Effects of
Dredged Materials for Selected Great Lakes Harbors on
Plankton and Benthos," Center for Great Lakes Studies,
Univ. Wisconsin, Milwaukee, Special Report No. 8, 1969.
22. Gannon, J.E. and Beeton, A.M., "Procedures for Determining
the Effects of Dredged Sediments on Biota - Benthos
Viability and Sediment Selectivity Tests," J. Water Poll.
Cont. Fed., _4J3, 3, March 1971.
23. Prater, B.L. and Anderson, M.A., "A 96-hour Bioassay of
Otter Creek, Ohio," J. Water Poll. Cont. Fed., _4j),
10, Oct. 1977.
72
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24. Lee, G.F. and Plumb, R.H., "Literature Review on Research
Study for the Development of Dredged Material Disposal
Criteria," Contract Report D-74-1, U.S. Army Engineer
Waterways Experiment Station, Vicksburg, MS, June 1974.
25. Heberger, R., Great Lakes Fishery Laboratory, U.S. Fish and
Wildlife Service, Ann Arbor, MI, personal communication.
26. Gannon, J.E., "The Ecology of Lake Michigan Zooplankton - A
Review with Special Emphasis on the Calumet Area,"
Appendix B in; Snow, R.H., "Water Pollution Investigation
Calumet Area of Lake Michigan," Report No. EPA-905/9-74-011-B,
Vol. 2 (Appendices), 1974.
27. Environmental Protection Agency/Corps of Engineers Technical
Committee on Criteria for Dredged and Fill Material,
"Ecological Evaluation of Proposed Discharge of Dredged
Material into Ocean Waters," U.S. Army Engineer Waterways
Experiment Station, Vicksburg, MS, 1977.
28. Harris, E.K., "Confidence Limits for the LD50 Using the
Moving Average - Angle Method," Biometrics, 15: 424-432
1959.
29. Unpublished data, Indiana State Board of Health.
30. Chicago District, Corps of Engineers, "Draft Environmental
Impact Statement Relating to Operation and Maintenance
Activities at Michigan City Harbor, Indiana," August 1977.
31. Chicago District, Corps of Engineers, "Letter report on
Confined Disposal Area for Michigan City Harbor, Indiana,"
May 1976.
32. Moore, T.K and Newbry, B.W., "Treatability of Dredged Material
(Laboratory Study)," Technical Report D-76-2, U.S. Army
Engineer Waterways Experiment Station, Vicksburg, MS, 1976.
33. Bauer, W. , jejt a.1, "Agents, Methods and Devices for Amelioration
of Discharges of Hazardous Chemicals on Water," Report
number CG-D-38-76, Department of Transportation, United
States Coast Guard, Office of Research and Development,
Washington, DC, August 1975.
34. Pilie, R.J., eit_ a.L, "Methods to Treat, Control, and Monitor
Spilled Hazardous Materials," report EPA-670/2-75-042,
National Environmental Research Center, Office of Research
and Development, U.S. Environmental Protection Agency,
Cincinnati, OH, June 1975.
73
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35. Widman, M. and Epstein, M., "Polymer Film Overlay System for
Mercury Contaminated Sludge - Phase I," U.S. Environmental
Protection Agency Water Pollution Control Research Series
No. 16080HTZ 05/72, May 1972.
36. Epstein, M. and Widman, M., "Coatings for Ocean Bottom
Stabilization," paper presented at 158th Meeting, American
Chemical Society, New York, NY, 1969.
37. Roe, T., £t al, "Chemical Overlays for Seafloor Sediments,"
paper no. OTC 1170 presented at the Second Offshore
Technology Conference, Houston, TX, May 1970.
38. Ziegler, R. and LaFornara, J., "In-Situ Treatment Methods for
Hazardous Materials Spills," paper presented at 1972
Hazardous Materials Conference, March 21-23, 1972,
Houston, Texas.
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APPENDIX A
RELATIONSHIP BETWEEN CORE LENGTH AND DEPTH OF SEDIMENT SAMPLED
In a classic piece of work reported in 1941, K.O. Emery and R.S.
Dietz (A-l) developed a gravity coring device very similar to that used
in this study from the RV MYSIS. The cited paper includes very detailed
observations on the mechanics of sediment coring. These observations
are germane to this report because of the need to interpret core sample
lengths with respect to the in situ depth of sediment represented. Some
of Emery and Dietz1s discussions are summarized here and applied to the
Michigan City Harbor/Trail Creek coring effort. Reference to the original
paper is highly recommended for more detailed discussion.
Before investigating the factors that Emery and Dietz found impor-
tant, it is necessary to note some factors that they found were not
important. The fact that cores are shorter than the depth sampled is
not primarily caused by:
Loss of sediment from the core-tube. This investigation
used a core retainer, preventing the escape of sediment
during retrieval.
Compaction/escape of water. Emery and Dietz could explain
only a 3% length reduction from this mechanism. This study
found core samples to have water contents similar to ponar
grabs, which should approximate in situ water content.
"Slumping" within the core-tube. The inner diameter of the
core nose is smaller than that of the core liner. Therefore,
the sediment cylinder that enters the core liner can "slump"
or shorten as it expands laterally to fill the core liner.
Emery and Dietz found that this mechanism could account for
only about half of the observed shortening of cores.
Collection of only the top layers of sediment. When a
coring device is retrieved with 100 cm of mud on the out-
side but only 50 cm of core, one potential explanation is
that after 50 cm, the corer kept penetrating but no more
sediment entered. Emery and Dietz showed by theoretical
arguments and experimental evidence that this does not
happen.
The mechanics of coring that are important in deciding how much
depth a core or core increment represents are briefly described as
follows: As the coring device proceeds through the sediment, the sedi-
ment layers are downwarped and thrust aside. In addition, the core
inside the core liner develops frictional resistance, as does the sedi-
ment outside the corer-tube.
75
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Near the surface of the sediment, there is relatively low resistance
to penetration (low percent solids) and low friction (short lengths of
sediment-corer contact). At depth, where the sediment becomes denser
(higher percent solids), both the resistance to penetration and the fric-
tional resistance to core entry into the tube increases. That is, it is
more difficult for sediment to enter it. Emery and Dietz found that in
most recently sedimented deposits, these factors increase in approximate
equivalence with depth such that the incremental core length per incremen-
tal depth penetrated is approximately constant throughout the length of a
core. That is, if the top 6 cm of core represent 11 cm of sediment, then
the bottom 6 cm of core also represents 11 cm of sediment.
Another finding of Emery and Dietz was that hundred of cores ranged
from 40% to 70% in the ratio
core length
depth penetrated
The average was 50%.
In this study, where a corer similar to that of Emery and Dietz was
used, it has been assumed that all increments of any one core represent
consistent penetration increments, and that the ratio of core length to
depth penetration for those increments and for each core as a whole is 50%.
Reference
Al. Emery, K.O. and Dietz, R.S., "Gravity Coring Instrument and Mechanics
of Sediment Coring," Bulletin of the Geological Society of America,
Vol. 52, pp 1685-1714, Oct. 1, 1941.
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APPENDIX B
ANALYTIC METHODS FOR WATER AND SEDIMENT
Analysis of water and sediment samples was performed by JBF and several
other laboratories in the Boston area. Selection of each laboratory was
based on its specific capability to perform each analysis that was assigned.
Each laboratory had its own internal quality control procedures. In
addition, JBF provided blind replicates to confirm that the expected precision
of each method was being achieved, and blind spiked samples to confirm the
expected accuracies.
Arsenic in Water
These analysis were performed by Herbert V. Shuster, Inc., Boston, Mass.
The gaseous hydride method was used, with sodium borohydride to produce arsine,
which was analyzed by atomic absorption spectrophotometry. The method is
described in Ref. (Bl).
Arsenic in Sediment
Digestions of sediments were performed by JBF (see "Heavy Metals in
Sediment - a. Digestion", below). Digests were analyzed by H. V. Shuster, Inc.
with the method for water described above.
Ammonia in Water
These analyses were performed by Interex Corporation of Natick, Mass.
The Nesslerization method (direct, following distillation) was used (B2).
Heavy Metals in Sediment and Water
a. Digestion
All samples for metals were digested in accordance with Ref. (B3) by
JBF. The procedure ("Metals", Section 4.1.3 in the reference) features
nitric acid digestion followed by solution in warm hydrochloric acid.
b. Analysis
All digests for metals were analyzed by atomic absorption spectro-
photometry. With the exception of arsenic, all analyses were performed by
direct aspiration of the digest in accordance with Ref. (B3).
Immediate Oxygen Demand in Sediment
This test was performed in the field by JBF, with a procedure described
in Ref. (B4). Because the method is not described in standard analytic
references, it is described below.
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Sample Collection and Handling
Care must be taken to avoid oxidation of the sample before test. The
sample for testing, therefore, should be extracted from the mass of the
sediment in the sampling device with minimal air contact. A disposable
plastic syringe (10 or 20 cc) is inserted into the interior of the sediment
mass for handling the sediment and delivering it to the test container.
When the sediment is reasonably compacted, the bottom of the syringe is cut
off and the cylinder is used to bore a sample. If the sediment has a larger
water content, a smaller hole is bored through the bottom of the cylinder
and the sediment drawn into the syringe. Even a diluted hydraulic dredge
slurry can be accommodated in a properly prepared syringe. Once the sample
is in the syringe, it can be weighed without undue exposure to the air, and
the sample can be discharged directly into the test container. This is
done below the water surface to avoid contact with air.
Dilution Medium for Sediment
Large variations in water quality are possible at potential dredging
sites and disposal areas. Therefore, it seems appropriate to use one or
two standard types of dilution water for the IOD test. It is not necessary
to use nutrient-enriched media as in the BOD methods because the oxygen-
demanding phenomena in the IOD test are largely nonbiogenic. No matter
what dilution water is used, it should be close to saturation with respect
to air at the test temperature. It should also be free of oxygen-demanding
substances. Tap water (source: Lake Michigan) was used in this project.
In all the previous IOD tests, a single dilution was made with a
recommended quantity of sediment. This practice ignores the fact that the
concentration of DO can be measured more accurately at higher oxygen concen-
trations. A typical DO meter response is 90 percent in 10 sec at a constant
(30°C) temperature. However, at low DO values the 90 percent reading takes
30 sec to reach. Because the accuracy of the DO reading may be + 0.3 mg/£,
a small oxygen depletion should be avoided. These problems can Fe avoided
by conducting the laboratory IOD test on at least two, preferably three,
different dilutions. The results from dilutions showing 40 to 70 percent
depletion are the most reliable and should be the only results considered
acceptable.
Time
Fifteen minutes has been arbitrarily selected as the IOD test time.
This time can be maintained as the standard if the oxygen-depletion criteria
stated above are adhered to by making the proper sediment dilutions. Using
a longer time interval makes the test more cumbersome from an analytical
viewpoint. Under some special circumstances it may be instructive to
follow the DO concentration past the 15-min limit. However, this time
interval is suitable for the purposes of a standardized IOD test.
78
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Mixing
Mixing at the membrane surface of the DO probe is necessary to obtain
an accurate reading. A BOD mixing accessory is available from many DO
meter vendors which would Induce a current in the vicinity of the probe
membrane. This current would not, however, maintain the bulk of the
sediments in suspension. A magnetic stirrer can be used for this purpose.
However, it must be used with the proper precautions. Because magnetic
stirrers tend to give off heat, they can raise the water temperature in the
container within the 15-min testing period. Suitable insulation can be
used to reduce this effect. Proper correction on the instrument for the
temperature changes that do take place is necessary for accurate DO measure-
ments. When using the magnetic stirrer to induce a current across the
membrane surface, it must be remembered that the water in the center of the
BOD bottle is swirling at a slower rate than at the perimeter. A sufficient
stirring rate can be obtained by placing the probe in the dilution water
and finding a stirrer setting that does not cause any appreciable change in
the meter readings when the setting is increased or decreased slightly.
Calculation
For the IOD on a sediment dry weight basis, the calculation is as
follows:
•mn m»/ir« . mg/kg IOD (wet basis
IOD mg/kg - % golids (declmal fraction)
(DO. , - - DO... .) x 0.3
where: mg/kg IOD (wet basis) - - initial — final -
«'"* v ' grams of sediment in aliquot
The 0.3 term (300 m ) is the volume of a standard BOD bottle.
Oil and Grease in Sediment
Interex Corporation performed these analyses using Freon as the
solvent in the Soxhlet extraction procedure (B2).
PCS in Water and Sediment
Herbert V. Shuster, Inc. performed these analyses in accordance with
Ref. (B5). The method was modified by use of acetonitrile/petroleum ether
instead of DMF/hexane and liquid/solid chromatographic cleanup with
Floresil PR in place of alumina.
TKN in Sediment
These tests were done by Interex Corporation using the standard
Kjeldahl method with Nessler finish (B2) .
79
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Particle Size Distribution in Sediment
JBF performed these tests using ASTM Method D422-63 (Reapproved 1972)
Percent Solids and Percent Volatile Solids in Sediment
JBF performed these tests using Standard Methods (B2).
80
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REFERENCES - APPENDIX B
Bl. Fernandez, F.J. "Atomic Absorption Determination of Gaseous
Hydrides Utilizing Sodium Borohydride Reduction,"
Atomic Absorption Newsletter, 12, 4, July-Aug. 1973.
B2. American Public Health Association, Standard Methods for the
Examination of Water and Wastewater, 14th ed., Washington D.C., 1975.
B3. "Methods for Chemical Analysis of Water and Wastes", Report
No. EPA-625-/6-74003, U.S. Environmental Protection Agency,
Washington, B.C., 1974.
B4. Neal, R.W., Pojasek, R.B., and Johnson, J.C., "Oxygenation of
Dredged Material by Direct Injection of Oxygen and Air During
Open-Water Pipeline Disposal," Report No. D-77-15, U.S. Army
Engineer Waterways Experiment Station, Vicksburg, MS, Oct. 1977.
B5. "Analysis of Environmental Materials for Polychlorinated Biphenyls,"
Monsanto Chemical Co. Laboratory Analytical Chemistry Method 71-35
as revised November 1970.
81
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APPENDIX C
BIOASSAY METHODS
Stock Cultures
Cyclops bicuspidatus thomasi, Daphnia galeata mendotae and
Pontoporeia affinis were collected from Northern Lake Michigan with a
0.5-m diameter No. 6 mesh (239 ym) net. Cyclops and Daphnia were obtained
by towing the net vertically through the epilimnion. Pontoporeia were
collected at night by towing the net horizontally near bottom. This method
is most effective, since Pontoporeia migrate from the sediments into the
water column at night (Cl). All net tows were made at slow speeds
(0.5 m/sec) to minimize damage to the organisms.
Collections were immediately transported to the Biological Station's
Lakeside Laboratory and specimens were isolated for monoculture. Daphnia
were removed from the plankton samples with a glass pipette (Pasteur type)
and transferred to 475-ml glass jars. Cyclops were segregated by concen-
trating 4,000 to 8,000 organisms in a 1-liter bottle and adding 3 to 6 ml
of an aqueous food suspension (described below). The container was sealed
and held for 12 hours. This technique decreased the dissolved oxygen
level, resulting in the death of all organisms except Cyclops and
Holopedium. Holopedium were removed and the Cyclops were transferred to
3.8 liter glass jars. Both Cyclops and Daphnia were maintained in fil-
tered (25 urn) Lake Michigan water (from Little Traverse Bay). Pontoporeia
were separated from the smaller crustaceans by passing the tow sample
through a No. 30 (600 urn) sieve. Pontoporeia were then transferred to
20.8-liter aquaria containing Lake Michigan water and sediments (from
Little Traverse Bay).
The culture vessels containing these organisms were kept in a refri-
gerated incubator (Forma Scientific Model 23) with controlled temperatures
of 6-9°C for Pontoporeia and 12-15°C for Cyclops and Daphnia. Aeration
of the culture water was provided prior to transfer of Daphnia. to minimize
their entrapment in the surface film. Continual aeration was provided for
Cyclops (2-4 ml/min.) and Pontoporeia (80-120 ml/min.). Water was changed
daily for Daphnia, twice weekly for Cyclops, and biweekly for Pontoporeia.
Pontoporeia and Cyclops were fed a ground mixture of Glencoe fish
pellets and Cerophyl (20 to 1 by weight) which was freshly prepared each
week and kept under refrigeration. Pontoporeia were fed by sprinkling the
mixture over the water surface three to four times per week (^0,5 g/100
individuals). For Cyclops, the mixture was prepared as an aqueous suspen-
sion (4 g of this mixture in 100 ml deionized water) which was then filtered
through a 54-um mesh screen. Cyclops were fed the filtrate three times
weekly (1 ml/3.8 liters culture medium).
Daphnia were more difficult to maintain in the laboratory. Cultures
would die off within approximately 7 to 14 days when being fed the Glencoe
fish pellet-Cerophyl suspension and mixed algae cultures. Daphnia cultures
82
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were maintained successfully with the following technique supplied by
J. Marshall^: Daphnia were fed Chlamydomonas reinhardtii^ daily (^2 X lu
cells/vessel). The success of this method lies principally in maintaining
the food supply in continuous suspension. The mobility of Chlamydomonas
reinhardtii in the culture medium permits efficient ingestion of this
small flagellate by the filter-feeding Daphnia. This provided adequate
populations of 90-160 organisms/vessel.
Salmo gairdneri were obtained from the Michigan Department of Natural
Resources Oden Fish Hatchery as fingerlings (7 to 10 cm) and rapidly trans-
ported (<30 min.) to the Biological Station laboratory. The fish were
promptly transferred to 19-liter glass containers placed in a continuously
running cold water bath (11 to 12°C) in the aquarium room. Acclimation to
the Douglas Lake water supply came in two steps. The fish were initially
placed in a 1 to 1 ratio of Douglas Lake and Fish Hatchery water for 24
hours, then transferred to 100% Douglas Lake water. Water temperature in
the laboratory was maintained within 0.5°C of the Fish Hatchery water.
The water supply was aerated (80-170 ml/min.) to ensure adequate oxygen
levels (saturated conditions). The high feeding levels at the Fish
Hatchery caused high metabolic waste accumulation requiring daily water
renewal.
Salmo were fed 3/32-inch (0.24 cm) Glencoe fish pellets (0.3-5 g
fish"1 day"1). They were allowed to acclimate for one week before testing.
Laboratory physiocochemical conditions for the test organisms were
maintained as closely as possible to those observed in the field. Temp-
erature, dissolved oxygen and pH were regularly monitored. Temperature
and dissolved oxygen were measured with a YSI model 51B oxygen meter and
pH was determined with a Beckman model H-5 pH meter. Temperature was
maintained within a range of 1.0°C, dissolved oxygen within 2 mg/liter
(near saturation), and pH within 0.5 units. Organisms were not fed
during laboratory experiments.
Test Materials and Equipment
All test chambers were glass. Only tygon or glass tubing (for
aeration) entered the test vessels. Sediments were handled only with
stainless steel and polyethylene instruments.
Sediments and site water were collected by a JBF Scientific Corpora-
tion field crew on 14-17 April 1977. They were stored and transported in
a refrigerated condition. They were received at the Biological Station
on 18 April 1977 and promptly stored in a walk-in cooler with temperature
regulated between 0 and 4°C.
J. Marshall, Argonne National Laboratory, Argonne, IL.
2
From the Culture Collection of Algae, Department of Botany, University
of Texas, Austin, TX.
83
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Water collected at the control station site was used for assays with
Cyclops, Daphnia and Pontoporeia. Filtered (64 ym) Douglas Lake Water was
used for experiments with Salmo. Chemical characteristics of the various
water supplies used for cultures are listed in Table C-l.
84
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Table C-l. Chemical Characteristics of Water Supplies Used
in Maintenance and Culture of the Test Organisms
Chemical
Variable
PH
Alkalinity*
(as CaCO3)
§
Conductivity
Total - p**
NO 3 - N**
NH3 - N**
Ca*
Mg*
K*
Na*
Cl*
Si02
Lake Michigan ( '
* 8.5
109
261
—
129
15
37.4
—
—
—
7.2
0.3
\ (rv
Douglas Lakev '
8.5
115.3
249.5
18.7
53.4
33.9
31.2
11.0
0.7
2.3
5.4
1.0
1 Fish Hatchery (
8.1
164
300
20
600
20
42
14
0.7
—
2
8
*mg/liter
§jjmhos/cm @25°C
**yg/liter
(C4)
85
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REFERENCES - APPENDIX C
Cl. Marzolf, G.R., "Vertical Migration of Pontoporeia affinis (Amphipoda)
in Lake Michigan," Proc. 8th Conf. Great Lakes Research,
Univ. of Michigan, Great Lakes Res. Div., Pub. No. 13, 1965.
C2. Schelske, C.L. and J.C. Roth, "Limnological Survey of Lakes Michigan,
Superior, Huron and Erie," Univ. of Michigan, Great Lakes Res.
Div., Publ. No. 17, 108 p., 1973.
C3. Gannon, J.E., Univ. of Michigan Biological Station, unpublished data.
C4. Newton, M.E. and M. Wuerthele, "Analysis of Selected Michigan Fish
Hatchery Water Supply and Discharge Samples, Water Resour. Comm.
Michigan Dept. Nat. Resour., Lansing, 1970.
86
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-440/5-78-012
3. RECIPIENT'S ACCESSION NO.
4. TITLE AND SUBTITLE
IN-PLACE POLLUTANTS IN TRAIL CREEK AND MICHIGAN CITY
HARBOR, INDIANA
5. REPORT DATE
August 1978
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
JBF Scientific Corporation
2 Jewel Drive
Wilmington, Massachusetts 01887
10. PROGRAM ELEMENT NO.
2BH 413
11. CONTRACT/GRANT NO.
68-01-4336
12. SPONSORING AGENCY NAME AND ADDRESS
Office of Water Planning Standards
U.S. Environmental Protection Agency
401 M Street, S.W.
Washington, D.C. 20460
13. TYPE OF REPORT AND PERIOD COVERED
Final
14. SPONSORING AGENCY CODE
EPA 700/01
15. SUPPLEMENTARY NOTES
16. ABSTRACT
The sediments of much of Trail Creek and Michigan City Harbor are toxic to
several species of desirable aquatic organisms and condusive to extreme dominance
by a few species that are known to tolerate grossly polluted benthic environments,
Although the overlying waters also show some signs of pollution, salmonid migra-
tions do pass through the area. This indicates that severely toxic discharges
have been abated and are now evidenced by the in-place pollutants that were
deposited in past years. It appears that removal of these deposits would be a
fruitful and worthwhile operation. However, before such action is taken, the
importance of a large landfill as a potential source of future pollutants should
be assessed. If the landfill is shown to be unimportant, dredging with disposal
in a land-based, confined disposal area is recommended. The cost of such a
program could exceed $4 million, but cost sharing with the Corps of Engineers in
their navigation maintenance program in the Creek and Harbor would significantly
reduce the section 115 funds required
17.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
Environmental Research
Sediments
Water Quality
Bioassay (Sediment)
b.IDENTIFIERS/OPEN ENDED TERMS c. COSATI Field/Group
Trail Creek
Michigan City Harbor
Pollution
Dredging
13 B
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Release to Public
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SUS GOVERNMENT TOUTING OFFICE 1979 -281-147/31
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