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Preliminary Investigation of the Extent of Sediment
Contamination in the Lower Grand River
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Table of Contents
This work was supported by Grant Number GL985555-01-0 between
the Environmental Protection Agency Great Lakes National Program Office (GLNPO) and Grand
Valley State University. Additional funding was provided by the Robert B. Annis Water
Resources Institute (WRI).
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Project
Team |
EPA Project Officer
Dr. Marc Tuchman USEPA GLNPO
Principal Scientists
Dr. Richard Rediske GVSU Sediment Chemistry
Dr. Min Qi GVSU PCB Congeners
Jeffery Cooper GVSU Sediment Toxicity
The Gas Chromatograph/Mass Spectrometer used by GVSU
for this project was partially funded by a National Science Foundation Grant
(DUE-9650183). |
Project technical
assistance was provided by the following individuals at GVSU:
Carissa Bertin, Jessica Blunt, Alexey Stiop, Mike Sweich,
Shana McCrumb, Kane OnwuzulikeShip support was provided by
the crews of the following Research Vessels:
R/V Mudpuppy (USEPA)
J. Bohnam and the
R/V D.J. Angus (GVSU)
B. Burns
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A preliminary investigation of the nature and extent of
sediment contamination in the lower Grand River was performed. Three areas in the lower
Grand River exceeded sediment quality guidelines for heavy metals and selected organic
chemicals. The locations and parameters of concern are listed below:
Harbor Island (G20). Exceeds sediment PEL values for
chromium, lead, nickel, and DDE in the top core section. Deeper core sections were
extensively contaminated with heavy metals.
Spring Lake (G6). Exceeds sediment PEL values for chromium,
lead, cadmium, nickel, and DDE.
Grand Haven (G12). Exceeds sediment PEL values for chromium
and nickel. The sediments at this location exhibited a statistically significant level of
toxicity to amphipods when compared to the control.
The extent of contaminated sediments in the vicinity of G12
(near the Grand Haven tannery) appears to be localized in a small area. Some additional
sampling of this area would be necessary to define the extent of the contaminated
sediments. The results for Spring Lake and Harbor Island show these areas to be
contaminated with heavy metals and selected organic compounds. Additional sampling and
analysis would be necessary to characterize the extent of sediment contamination in the
areas around Harbor Island and Spring Lake.
Meander core islands appear to play a significant role in the
lower Grand River with respect to the deposition of contaminated sediments. Pockets of
contaminated sediments were found at the downstream tip of Harbor Island (G20), and the
unnamed islands near G24 and G17. These areas serve as sediment deposition zones and
indicate the effects of historical discharges of metals and organic chemicals to the lower
Grand River. High water events however can transport contaminated sediments from these
deposits and increase the contaminant loading to Lake Michigan. Since metals and organic
chemicals are associated with the suspended sediment load, the role of the meander core
deposits in contaminant transport needs to be examined in detail. This investigation
examined three of the 12 meander core islands that are located in the lower Grand River.
The normalization of heavy metal data with aluminum was
examined for chromium and lead. Statistically significant correlations between these
elements were determined in background samples (r = 0.73 and 0.75 for Cr and Pb
respectively). Plots of the project data set demonstrate that anthropogenic enrichment of
lead and chromium has occurred in a majority of the top and middle core sections.
Statistically significant (alpha = 0.05) acute toxicity
effects were observed in the sediments of samples G6-P and G12-P on the amphipod,
H. azteca, by the Dunnett’s test. The PEL values for chromium and DDE were exceeded
at G12-P. PEL values for arsenic and DDE were exceeded at G6-P. Statistically significant
(alpha = 0.05) mortality was not seen on the midge, C. tentans in the Grand River
sediments.
The Grand River watershed contains the longest river in the
State of Michigan and comprises 13% of the entire Lake Michigan drainage basin (Sommers,
1977). A map of the Lower Grand River is provided in Figure 1.1.
Two thirds of this 3.6 million acre watershed is designated as agricultural with 22% of
the total pesticide usage in the Lake Michigan basin concentrated within its boundaries
(GAO, 1993; Hester, 1995). Approximately 300,000 lbs. of atrazine alone are applied within
the Grand River watershed on an annual basis (Hester, 1995). Since the Grand River
watershed includes two of the larger population and industrial centers in the State of
Michigan, there have been significant anthropogenic activities that have adversely
impacted the watershed. Historically, both the Grand Rapids and Lansing areas were known
for large-scale metal finishing and plating industries that contributed significant
amounts of heavy metals to the environment. A large tannery with a historic discharge to
the river is also located in the Grand Haven area. In addition, the lower region of the
Grand River supported a large number of wood processing facilities. High levels of the
wood preservative compound, pentachlorophenol, was recently found in sediments of Spring
Lake and in the navigation channel outside its confluence with the Grand River by the U.S.
Army Corps of Engineers (Bowman, 1995). A second sampling of the area was however unable
to confirm these results. Additional surveys of the sediments in the Grand River were
performed by USACE in 1996 (DLZ, 1996). Elevated levels of heavy metals and PAH compounds
were detected in these investigations. The USACE investigations focused on the evaluation
of the sediments for dredging and concentrated on samples collected from the navigation
channels. The sediments in areas outside of the navigation channel have not been
investigated.
Recent studies of the 12 major tributaries of Lake Michigan
have found the Grand River to be one of the most significant contributors of contaminant
loads to Lake Michigan (Shafer, et al., 1995; Hall and Behrendt, 1995; and Cowell, et al.,
1995, and Robertson 1997). For most contaminants, the loading from the Grand River is
comparable to that of the Fox River (WI), yet we know little about sites and sources of
contamination in the Grand as compared to the Fox. For example, preliminary results of the
Lake Michigan Mass Balance Study have found that the Grand River is the largest tributary
source to Lake Michigan for lead, DDT compounds and atrazine and the second largest source
for mercury (D. Armstrong, J. Hurley, and P. Hughes pers. comm.). There is, however, very
little data available concerning the location of contaminant source areas in the Grand
River watershed.
The geology of the Grand River Watershed was described in a previous report (U.S. Army
Corps of Engineers 1972). From its headwaters in northeastern Hillsdale County at
elevation 1040 feet, the Grand River flows northward to Lansing, Michigan, where it makes
an abrupt bend and meanders westerly to Grand Haven where it discharges into Lake
Michigan. The Grand River flows 260 miles through a basin 135 miles long and up to 70
miles in width. With a drainage area of 5572 square miles, the Grand River basin
encompasses all or part of nineteen counties. A map of the Grand River watershed is shown
in Figure 1.1. The topography of the basin is a result of
Pleistocene glaciating with moraines and outwash plains dissected by streams. Kettle holes
appear sporadically on out wash plains and usually are filled with water as swamps or
lakes. Till plains, moraines, kames, and esker systems of the Port Huron system are the
predominant surface feature with relief of 50 to 60 feet. Pasture and crop land comprise
approximately 63 percent of the basin and another 15 percent is comprised of forest. The
harbor at Grand Haven has a minimum draft of 21 feet, and a channel 100 feet wide and
eight feet deep extends 17 miles upstream. Above this point, the river is not suitable for
commercial navigation.
The Grand River Basin is underlain by two distinct groups of
rocks, the younger glacial tills, and the older bedrock. Glacial deposits are a mixture of
rock material from many different sources. This rock material was picked up, transported
and deposited by glaciers or by waters flowing from the glaciers. The principal glacial
deposits in the Grand River basin are till, moraines, outwash, and glacial lakebeds. The
bedrock, that underlies the glacial deposits, was deposited in large inland seas that
covered most of the area of the Great Lakes States. Bedrock formations are comprised
primarily of sandstone, limestone, dolomite and shale, but include thick beds of salt,
gypsum, and anhydrite. After deposition, the bedrock formations in the Great Lakes were
warped into geologic structures that resembles a gigantic set of shallow bowls. The Grand
River Basin overlies the south and southwestern part of this structure. The bedrock that
underlies this basin generally dips gently to the north and east toward the center of the
basin structure causing individual formations to be progressively deeper in a northerly
and easterly direction.
The Grand River Basin evolved during the retreat of the last
of the great continental glaciers. Most of the present surface features of the basin
resulted from deposition of the rock materials from glaciers and subsequent erosion. The
basin is underlain by sediments deposited from glacial lobes that advanced over the basin
from the Saginaw Bay and from Lake Michigan. The two lobes coalesced along a north-south
line near the center of Kent County. The area of coalescence is one of rolling topography.
The lower part of the Grand River Basin is formed on the sediments of former glacial Lake
Chicago.
The major portion of the basin is rather flat and
featureless. The maximum local relief in the areas upstream from Maple Rapids, Portland,
and Hastings generally ranges from 50 to 75 feet. The areas of minimal relief contain very
poorly drained soil. Swamps and marshes make up a significant part of the Maple, Looking
Glass, and Cedar River basins. The upper reaches of the Flat and Rogue River basins
include extensive and numerous swamps, marshes, and many lakes, as does the middle part of
the Thornapple River basin and the upper part of the Grand River Basin. The upper part of
the Maple River includes flatlands formed on the sediments of ancient glacial lakes. The
total relief between Lake Michigan, which has an altitude of about 580 feet, and the
highest point in the basin, which are at altitudes of about 1170 feet in southern Jackson
County, is about 700 feet. The maximum local relief within the basin ranges from 200 to
275 feet between the banks of the Grand River and the adjacent highlands. Areas with 200
or more feet of local relief, most of which are along the Grand River, constitute much
less than 5 percent of the total basing area.
The objective of this investigation was to conduct a Phase I
assessment of heavy metal and pesticide contamination in the lower Grand River. Selected
samples were analyzed for chlorinated phenols, PAH compounds, and PCB congeners in areas
where industrial releases may have occurred. In addition, a preliminary assessment of
sediment depositional patterns and sediment toxicity were performed to assist in the
analysis of the ecological effects and in the evaluation of remediation alternatives.
Specific objectives and task elements are summarized below:
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Determine the nature and extent of
sediment contamination in the lower Grand River.
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A Phase I
investigation was conducted to expand the sediment core sampling previously performed by
the U.S. Army Corps of Engineers. The investigation included additional spatial coverage
in the lower river section and targeted areas of suspected contamination from industrial
and agricultural sources. Twenty-three core samples were collected in this investigation.
Arsenic, barium, cadmium, chromium, copper, lead, nickel, zinc, aluminum, selenium, iron,
calcium, magnesium, manganese, mercury, TOC, DDT compounds, PCB congeners, and grain size
were analyzed on the sediments in all core samples. Aluminum, iron, magnesium, and calcium
were used to normalize the metals data (Loring, 1991). In addition, a subgroup of core
samples taken from the Spring Lake and areas adjacent to CERCLA and RCRA sites were
analyzed for chlorinated phenols and PAH compounds. Eleven cores were analyzed for these
semivolatile organic compounds.
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Surface sediments
were collected in the lower Grand River area with a Ponar dredge to provide heavy metal
concentration information for the toxicity evaluations. Four sites were selected for
toxicity evaluations based on the results of the core sample analyses.
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Critical
measurements were the concentration of arsenic, barium, cadmium, chromium, copper, lead,
nickel, zinc, aluminum, selenium, iron, calcium, magnesium, manganese, mercury,
chlorinated phenols, DDT compounds, PCB congeners and PAH compounds in sediment samples.
Non-critical measurements were total organic carbon, and grain size.
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Evaluate the toxicity of sediments
from sites in the lower Grand River area.
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Sediment toxicity
evaluations were performed with Hyalella azteca and Chironomus tentans
on
four sediment samples.
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Toxicity
measurements in Grand River sediments were evaluated and compared to the control location.
These measurements determined the presence and degree of toxicity associated with
sediments from the Grand River.
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Critical
measurements were the determination of lethality during the toxicity tests and the
monitoring of water quality indicators during exposure (ammonia, dissolved oxygen,
temperature, conductivity, pH, and alkalinity).
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This investigation was designed to examine specific sites of
possible contamination as well as provide an overall assessment of the nature and extent
of sediment contamination in the lower region of the Grand River. This bifurcated approach
allowed the investigation to focus on specific sites based on historical information in
addition to examining the broad-scale distribution of contamination. To address
contamination at specific sites, 16 core samples were collected from locations likely to
have been impacted by significant anthropogenic activity. The locations were selected to
target current and historical point sources and downstream sites from known industrial and
municipal discharges. These sites were determined by the analysis of historical data and
industrial site locations. Analysis of river flow patterns and depositional areas were
then used to select seven locations that would reflect the general distribution of
contaminants.
Sediment samples were collected using the U.S. EPA
Research Vessel Mudpuppy
and the GVSU Research Vessel
D.J. Angus. The sediment cores were collected with a VibraCore device with core
lengths ranging from 6-8 ft. The core samples were then sectioned in three equal lengths
for chemical analysis. For each core, the analytical parameters included a general series
of inorganic and organic constituents as well as specific chemicals related to a
particular source or area. The general chemical series for each core included the
following heavy metals; arsenic, cadmium, chromium, copper, lead, mercury, nickel, zinc.
In addition, DDT, DDE, DDD, and PCB Congeners were analyzed on all cores. A subset of the
11 core samples were analyzed for PAH compounds and chlorinated phenols. Basic sediment
chemistry parameters (organic carbon, aluminum, calcium, iron, manganese, magnesium, and
grain size) were also analyzed on each core. Aluminum and other sediment chemistry
parameters were used to normalize sediment metal data for the differentiation of
background levels and anthropogenic sources (Loring 1991, Helmke, et al 1977). The
location of the sampling stations are illustrated in Figure 1.2.
Analytical methods were performed according to the protocols described in SW-846 3rd
edition (EPA 1994a).
Chemistry data were then supplemented by laboratory toxicity
studies that utilize standardized exposure regimes to evaluate the effects of contaminated
sediment on test organisms. Six Ponar samples were collected in areas that had elevated
levels of contaminants in the top core sections. Standard EPA methods (1994b) using
Chironomus tentans and Hyalella azteca were used to determine the acute toxicity
of sediments from the Ponar samples.
Bowman, D. W. 1995. Grand River at Grand Haven Michigan:
U.S. Army Corps of Engineers Tier II Evaluation. June, 1995.
Cowell, S. E., Hurley, J. P., Schafer, M. M. and P. E.
Hurley. 1995. Mercury partitioning and transport in Lake Michigan Tributaries. Presented
at 38th Conference. International Association of Great Lakes Research.
DLZ, 1996. Grand Haven Sediment Sampling and Analysis.
Delivery Order #0014. Prepared for the U.S. Army Corps of Engineers. Detroit District.
EPA, 1994a. Test Methods for Evaluating Solid Waste
Physical/Chemical Methods. U.S. Environmental Protection Agency. SW-846, 3rd Edition.
EPA, 1994b. Methods for Measuring the Toxicity and
Bioaccumulation of Sediment-Associated Contaminants with Freshwater Invertebrates.
U.S. Environmental Protection Agency. EPA/600/R-94/024.
GAO. 1993. Issues Concerning Pesticide Usage in the Great
Lakes Watershed. GAO-RCED-93-128. 39pp.
Hall, D. W. and T. E. Behrendt. 1995. Polychlorinated
byphenyls and pesticides in Lake Michigan tributaries, 1993-95. Presented at 38th
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Loring, D. H. 1991. Normalization of heavy-metal data from
estuarine and coastal sediments. ICES J. Mar. Sci. 48:101-115.
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sediment and phosphorus to Lakes Michigan and Superior-High flow and long –term
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Schropp, S. J., Windom, H. L., Ed. 1988. A Guide to the
Interpretation of Metal Concentrations in Estuarine Sediments. Florida Department of
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P. and P. E. Hughes. 1995. Levels, partitioning, and fluxes of six trace elements in Lake
Michigan tributaries. Presented at 38th Conference. International Association of Great
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Sommers, L. 1977. Atlas of Michigan. Michigan State
University Press. East Lansing. 241pp.
U.S. Army Corps of Engineers, 1972. Comprehensive Water
Resources Study. The Grand River Basin. Part II. Detroit District. Appendix C.
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