EPA/530-SW-91-065E
PB92-12U809
Mining Sites on the National Priorities List
NPL Site Summary Reports
U.S. Environmental Protection Agency
Office of Solid Waste
June 21, 1991
FINAL DRAFT
Volume V
Prepared by :
Science Applications International Corporation
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
REPRODUCED BY
U.S. DEPARTMENT OF COMMERCE
NATIONAL TECHNICAL
INFORMATION SERVICE
SPRINGFIELD. VA 22161
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50272-101
REPORT DOCUMENTATION I 1. REPORT NO. 2.
PAGE j EPA/530-Sb-91-Oi5E
]
4. Title and Subtitle
PI1NIN6 SITES ON THE NATIONAL PRIORITIES LIST: SPL SITE SUMMARY REPORTS
(FINAL DRAFT) VOLUME V: TELEDYNE WAH CHANS TO WAYNE INTERIM STORAGE
FACILITY/W.R. BRACE
7. Author (s)
V. HQUSEMAN/OSW
9. Performing Organization Mane and Address
U.S. EPA
Office of Solid Waste
401 M. Street SW
Washinqton. DC 20460
12. Sponsoring Organization Name and Address
SAIC
ENVIRONMENTAL & HEALTH SCIENCES GROUP
7600-A LEESBURG PIKE
FALLS CHURCH, VA 22043
15. Supplementary Notes
3.
PB92-124809
5. Report Date
JlflE 21, 1991
6.
S. Performing Organization Rept. No
10. Project/Task/Work Unit No.
11. Contract (C) or Brant (6) No.
(C)
(6)
13. Type of Report & Period Covered
SITE SUMMARY REPORT
14.
16. Abstract (Limit: 200 woros)
Volume V of the Mining Sites on the National Priorities List contains the following WL site summary reports: Teledyne
Wan Chang, Tex-Tin Corp., Torch Lake, United Nuclear Corporation/Churchrock Site, U.S. Tatanium, Uravan Uraniusi Mill,
Whitewood Creek, and Wayne Interim Storage Facihtv/W.R. Grace.
17. Document Analysis a. Descriptors
b. Identifiers/Open-Ended Terms
c. COSATI Field/Group
13. Availability Statement
RELEASE UNLIMITED
(See ANSI-Z39.18)
19. Security Class (This Report)
UNCLASSIFIED
20. Security Class (This Page)
UNCLASSIFIED
OPTi
1 (For
21. No. of Pages
i/£
22. Price
0
ONAL FORM 272 (4-77)
•ffleriy NTIS-35)
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5SNT BY-.SRIC UlfiSTE REGS DEFT ; 2- 3-92 12:25PM ; 703S214775-» 321 6199:8 3
UNITED STATES ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON. O.C. 20460
SOLID WASTE AND EMERGENCY
Appendices of these reports include excerpted
pages from documents referenced in the text of
the reports, and as a result, page numbers in
the appendices are not necessarily consecutive.
In addition, since many of the references are
3rd or 4th generation copies, some pages may
not be legible, but are the best available.
Pnnted on Raeyeiad Ptptr
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Mining Waste NPL Site Summary Report
Teledyne Wah Chang
Albany, Oregon
U.S. Environmental Protection Agency
Office of Solid Waste
June 21, 1991
FINAL DRAFT
Prepared by:
Science Applications International Company
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
II,
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j V
DISCLAIMER AND ACKNOWLEDGEMENTS
The mention of company or product nam is not to be considered an
endorsement by the U.S. Government or by the U.S. Environmental
Protection Agency (EPA). This document was prepared by Science
Applications International Corporation (SAIC) in partial fulfillment of
EPA Contract Number 68-WO-0025, Work Assignment Number 20
A previous draft of this report was reviewed by Howard Orlean of
EPA Region X [ (206) 553-6903], the Remedial Project Manager for
the site, whose comments have been incorporated into the report.
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Mining Sites on the National Priorities List
-- NPL Site Summary Reports
TABLE OF CONTENTS
Volume V
Teledyne Wah Chang Albany, OR
Tex-Tin Corporation Texas City, TX
Torch Lake Houghton Co., MI
United Nuclear CorporationlChurchrock Site Gallup, NM
U.S. Titanium Nelson Co., VA
Uravan Uranium Mill Uravan, CO
Whitewood Creek Lawrence/Meade/Butte Co’s., SD
Wayne Intenm Storage Facility/W.R. Grace Wayne, NJ
V
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Mining Waste NPL Site Summary Report
TELE [ )YNE WAll CHANG
ALBANY, OREGON
INTRODUCTION
This Site Summary Report for the Teledyne Wah Chang site is one of a series of reports on mining
sites on the National Priorities List (NFL) The reports have been prepared to support EPA’s mining
program activities In general, these reports summarize types of environmental damages and
associated mining waste ni2nagement practices at sites on or proposed for the NFL as of February 11,
1991 (56 Federal Renister 5598). This summary report is based on information obtained from EPA
files and reports and on a review of the summary by the EPA Region X Remedial Project Manager
for the site, Howard Orlean.
SiTE OVERVIEW
Teledyne Wah Chang Albany (TWCA) is a Superfund Site located in Millersburg, Oregon, an
industrial suburb 3 miles north of Albany, Oregon (see Figure 1). The Superfund Site consists of two
areas, the 110-acre Plant Site property and a 115-acre area approximately .75 of a mile north of the
plant site known as the Farm Site. The Plant Site contains numerous buildings and facilities including
an extraction area, a fabrication area, a solids storage area, and a parking and recreation area. The
Farm Site contains four 2.5-acre solids storage ponds. The remainder of the Farm Site is used
primarily for agriculture (Reference 1, Chapter 2, page 1; Reference 2, page 1).
TWCA is an active facility that has been manufacturing primary and mill-product zirconium and
hafnium from zircon sand for approximately 30 years. The facility has also produced smaller
quantities of tantalum, niobium, and vanadium products. TWCA is a primary producer of zircomum
metal Zircon sand, the principal ore for the manufacturing process, is imported from Australia
(Reference 1, Chapter 4, page 1).
Most of the wastestreams from the plant’s operations are treated prior to discharge or disposal.
Treatment techniques include continuous chemical precipitation and sedimentation of aqueous wastes
in the wastewater treatment plant; segregation and disposal of solid wastes; and use of a variety of air
contaminant control systems to cleanse emissions. Solids produced in the wastewater treatment plant
have been managed over the years at several onsite areas, including the Lower River Solids Pond
(LRSP), Schmidt Lake, the Farm Ponds 1 through 4, and the V-2 Pond (Reference 1, Chapter 5,
pages 1, 5, and 6).
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Teledyne Wah Chang
F1GUCE
LOCA11ON MAP
MI .
FIGURE 1. LOCATION MAP
— — — 1 uI ‘U’
2
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Mining Waste NPL Site Summary Report
TWCA currently has a National Pollutant Discharge Elimination System (NPDES) permit to regulate
the discharge of process wastewater. The facility also has an Air Contaminant Discharge Permit that
regulates air emissions from the facility. Although the facility submitted a Resource Conservation and
Recovery Act (RCRA) Part B Application for the operation of hazardous waste management activities
at the site, EPA determined that a Part B RCRA Permit was not necessary. Radioactive wastes are
managed under the requirements of a Naturally Occurring Radioactive Materials (NORM) license
(Reference 1, Chapter 5, pages 5, 15, 16, and 19).
The TWCA facility has been cited for numerous violations of its NPDES permit, occurring in 1975,
1977, 1978, 1979, 1980, and 1989. The company was fined for illegal burning in 1983. In 1986,
TWCA was cited for several violations of the State’s hazardous waste management rules (Reference
7, page 10).
Onsite storage of the solid wastes has attracted the attention of regulatory agencies and the public for
many years, particularly with regard to the low-levels of radioactive materials found in these wastes
(first confirmed by the Oregon State Health Division in 1977). In 1978, TWCA was granted a
Radioactive Materials License to transfer, receive, possess, and use zircon sands and industrial
byproducts containing licensable concentrations of radioactive materials (Reference 2, page 4). The
company applied to the Energy Facility Siting Council (EFSC) in 1981 to obtain a site certificate to
close the LRSP sludge pond and to store approximately 120,000 cubic yards of lime solids from the
wastewater treatment process. After several years of deliberations, the EFSC ruled (in 1987) that the
sludge was not subject to their jurisdiction because the levels of radioactivity were too low. In
October 1983, during the EFSC deliberations, the TWCA site was placed on the NPL (Reference 2,
page 4).
On May 4, 1987, TWCA signed a Consent Order to conduct the Remedial InvestigationfFeasibiity
Study. As part of this order, EPA and TWCA agreed to address the LRSP, Schnudt lake, and Farm
Pond sludges in an expedited fashion prior to the completion of the Remedial Investigation/Feasibility
Study for the entire facility. This expedited action resulted from the public’s concern of the sludge
materials, the location of the sludges in the floodplain, and the potential of the sludges to contribute to
ground-water contamination at the site. The Farm Ponds were later dropped from the expedited
investigation and are being included as part of the overall site Remedial Investigation because they did
not lie within the floodplain, and they contained levels of radioactivity lower than the other locations
(Reference 2, page 4; Reference 1, Chapter 5, page 7; Reference 7, pages 1, 5, 10, and A-i).
In 1989, a Record of Decision (ROD) was finalized as an interim response for Operable Unit 1 (i.e.,
the sludge ponds unit consisting of the LRSP and Schmidt Lake) (Reference 7, page 1). The ROD
specified a remedial action consisting of excavation and treatment of the sludges with cement, and
3
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Teledyne Wah Chang
offsite disposal of the sludges in a spe ally constructed monocell. According to Region X, EPA
issued a Unilateral Administrative Ord oTW in February 1991 that called for the treatment,
excavation, and offsite disposal of the _iSP and Schmidt Lake sludges along with long-term
operation and maintenance of the offsite monocell.
TWCA is currently conducting the Remedial Investigation/Feasibility Study in response to the May
1987 EPA Order of Consent, Docket No. 1086-02-19-106 (Reference 1, Chapter 5, page 7 and
Chapter 7, page 2). The Remedial Investigation is designed to characterize the nature and extent of
contamination in various media (e.g., ground water, surface water, and sediments) throughout the site
as well as evaluate pathways by which contamination may be leaving the site. At the request of EPA,
TWCA has also initiated a baseline human Health Assessment that will consider the risks posed by the
site to human health and the environment (Reference 5, pages 1 and 2).
As the Remedial Investigation/Feasibility Study for the entire site is not yet complete or available to
the public, much of the information defining the problems at the TWCA site is preliminary.
Conclusions about the risks associated with the site have only been summarized for Operable Unit 1
and are reported in the ROD for that unit. This document presents information from the ROD for
Operable Unit 1 and describes the available preliminary information for other areas at the site.
OPERATING HISTORY
The TWCA site has been in operation since 1956, when the Wah (lang Corporation reopened the
U.S. Bureau of Mines’ zircomum metal sponge pilot plant. New facilities were constructed in 1957,
primarily for the production of zirconium and hafnium sponge. Tantalum and niobium pilot facilities
were also included. Melting and fabrication operations were added in 1959. Teledyne Wah Chang
Albany was established in 1967 after Teledyne Industries, Inc., purchased Wah (lang Corporation of
New York (Reference 1, Chapter 4, page 1) The facility is still operating today as a primary
manufacturer of zirconium metal. It is also capable of manufacturing hafnium, niobium, and
vanadium metals (Reference 1, Chapter 4, page 1).
Zircon sand, the principal ore for the manufacture of zirconium metal, is imported from Australia.
At TWCA, the sand undergoes a chlorination process from which zirconium tetrachloride is
produced. Silicon tetrachloride is also produced from this process; it is purified and sold as a
byproduct (Reference 1, Chapter 4, pages 1 through 3).
Following chlorination, the zirconium tetrachloride completes a separation process using the organic
solvent methyl isobutyl ketone (MTBK) to remove the hafnium portion of the zirconium (most
4
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Mining Waste NPL Site Summary Report
zirconium minerals contain 1 to 5 percent hafnium). The resulting zirconium and hafnium oxides
follow similar processes to final metal production, including a second chlorination step; a reduction
process using elemental magnesium (magnesium chloride is removed and sold as a by-product); and
the consolidation of zirconium sponge into ingots for eventual forming into numerous shapes and sizes
(Reference 1, Chapter 4, pages 3 through 6).
Some of the wastes produced from the zirconium and hafnium manufacturing process include sand
chlorinator residues (characterized as “radioactive”); MIBK still bottoms (characterized as
“ignitable”); magnesium chloride wastes (characterized as a fire hazard); and smokehouse residue
(characterized as “Extraction Procedure (EP) toxic waste code D008” according to the facility
owner/operator) (Reference 1, Chapter 5, page 13). Slag wastes containing niobium and iron metals
are produced from the niobium and vanadium manufacturing processes. Ancillary processes
associated with the manufacturing operations include metal forming, painting, maintenance activities,
and analytical laboratory Quality Assurance/Quality Control (QAIQC). These ancillary processes
produce wastes, including salts, metal fines, waste thinners, MIBK, and 1,1,1-trichioroethane
(Reference 1, Chapter 5, page 13)
Because so many processes are involved in the production of nonferrous metals and products, many
waste management programs are employed at TWCA, including process wastewater treatment, solid
waste management, hazardous waste management, radioactive-material control, Polychlorinated
Biphenyls (PCBs) equipment m2n2gement, and air-quality control (Reference 1, Chapter 5, page 1).
TWCA operates a wastewater treatment system for the handling of industrial wastewaters generated
from metals manufacturing operations. The wastewater treatment process, consisting of a continuous
chemical precipitation and sedimentation system, generates treated wastewater and sludges. The
treated wastewater is discharged to Truax Creek under the guidelines of a NPDES permit that was
first issued in March 1975. Sludges produced from TWCA’s chemical precipitation and
sedimentation processes are collected and placed in storage ponds for additional settling and
dewatering. These “ponds” include the LRSP, Schmidt Lake, and Arrowhead Lake (located onsite)
and Farm Ponds 1 through 4 (located north of the plant) (see Figure 1). A smaller pond, known as
the V-2 Pond, was also used for a short period of time for temporary solids storage and pretreatment
(Reference 1, Chapter 5, pages 1 through 6).
The solids produced from the various wastewater treatment processes were stored onsite in the LRSP,
Schmidt Lake, and Arrowhead Lake from 1967 to 1978. Arrowhead Lake was dewatered and
covered in the early 1980’s. The LRSP and Schmidt Lake have not been used to store solids since
1979. TWCA also obtained a solid waste permit to use the sludge as a soil amendment on the TWCA
5
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Teledyne Wah Chang
Farm Site in 1976. The sludge was applied at an average rate of 108 tons per acre; the use of the
sludge as a soil amendment was only done in 1976 (Reference 1, Chapter 5, pages 5 through 8).
In 1979, the Farm Ponds came into operation as solids storage ponds for sludge from the wastewater
treatment processes. The switch to sludge disposal in the Farm Ponds occurred after production
processes for zirconium and hafnium were modified in 1978. The process modification reduced
concentrations of radioactive materials in the sludges, and directed the radioactive materials to a
separate solid waste referred to as “chlorinator residue” that is managed as a radioactive waste and
shipped to Hanford, Washington, for disposal (Reference 1, Chapter 5, pages 5 through 8).
The V.2 Pond, built in 1960, was used for settling the lime solids from the lime-treated zirconium
sulfate wet cake filtrate wastewater stream from the zirconium and hafnium separations process
Some of the wastewaters from the niobium and tantalum process used before 1975 were also placed
into the V-2 pond. The V.2 pond was operational until the addition of storage tanks and a separations
spill treatment system between 1977 and 1980 eliminated any waste or waste-water influent into the
V.2 Pond. The contents of the pond, with the exception of approximately 5,400 cubic yards of
solids, were removed and transported to an EPA-approved landfill in 1987 (Reference 1, Chapter 5,
pages 9 and 10).
TWCA also has an extensive system of solid waste management. All solid wastes generated at the
TWCA facility are initially delivered to the Dumpmaster Area, where they are inspected and
separated into nonhazardous and hazardous components. According to a 1988 Current Situation
Summary for a Remedial Investigation/Feasibility Study prepared by CH2M Hill Northwest, TWCA
is disposing of nonhazardous waste materials at a public landfill. Hazardous wastes are temporarily
stored onsite until they can be transported offsite to a hazardous materials storage, treatment, or
disposal facility (Reference 1, Chapter 5, page 12). Whenever practical, TWCA recycles waste
materials.
TWCA has not always practiced offaite disposal for its solid waste process residues. Three onsite
areas of the plant have been used for disposal, including the chlorinator residue pile, the magnesium
resource recovery pile, and the Truax Creek landfill area. Beginning in 1972, chlorinator residue
from the sand chlorination process was stored in a pile north of Schmidt Lake. This disposal practice
was discontinued in 1978 and pile contents were transferred to the Hanford radioactive disposal site in
Washington (Reference 1, Chapter 5, page 17). Solid residues from the nonferrous metals
manufacturing process (primarily magnesium chloride wastes) were placed in the magnesium resource
recovery pile until May 1983. In October 1983, TWCA, with the approval of the Oregon
Department of Environments] Quality (ODEQ), began operations to recover and beneficially use the
contents of the pile (e.g., substituting a magnesium hydroxide slurry for lime in the operation of
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Mining Waste NFL Site Summary Report
TWCA’s wastewater treatment system) (Reference 1, Chapter 5, pages 17 and 18). From 1958 to
1973, a portion of the area north of Truax Creek (extending from the area opposite of the V-2 Pond
and east to Arrowhead Lake) was used as a landfill Arrowhead Lake was briefly used as a landfill in
1976 (Reference 1, Chapter 5, page 18).
Radioactive wastes are managed under the requirements of the facility’s NORM license issued by the
Oregon Health Division (Reference 1, Chapter 5, page 16). Currently, low-level radioactive residues
generated by the pure chlorination and sand chlorination processes are collected and transported in
special containers to an offsite radioactive waste disposal facility, such as the one located at the
Hanford site in Washington (Reference 1, Chapter 5, page 14).
Some of the solid waste disposal activities undertaken by TWCA involve transformers and capacitors
containing PCBs. While the majority of electrical transformers used at the TWCA site are owned and
maintained by Pacific Power and Light, a few transformers and most capacitors are owned and
maintained by TWCA. Some of this equipment holds oil containing PCBs. Spent equipment known
to contain PCBs is sent to an EPA-approved PCB facility for proper treatment and disposal
According to TWCA, there have been no known spills of PCBs into soils or waters
onsite (Reference 1, Chapter 5, page 15). However, PCBs have recently been detected in sediment
samples collected from Truax Creek (Reference 3, pages 2 and 3).
TWCA operates a range of air contaminant control systems to cleanse air emissions from their
transition metal refining operations. Some of the air emissions control systems that have been
implemented include water and caustic sprays, scrubbers, baghouses, demisters, and wet electrostatic
precipitators (Reference 1, Chapter 5, pages 19 and 20).
SITE CHARACTERIZATION
The TWCA site is located in the north-central part of Oregon’s Willaniette Valley in the community
of Millersburg, Oregon. The site is 3 miles north of Albany, approximately 65 miles south of
Portland, and 60 miles east of the Pacific Ocean. The Willamette River forms the western boundary
of the plant site. Ground surface in the vicinity of the site slopes westward towards the Willamette
River (see Figure 1) (Reference 1, Chapter 2, pages 1 through 4; Reference 4, page 9)
The immediate area surrounding the TWCA plant site is primarily industrial, with some land north
and west of the site used for agnculture Residential and commercial activities are located to the east
and south of the facility The population of Albany is approximately 27,000, and Millersburg has a
population of 600 (Reference 1, Chapter 2, pages 3 and 4).
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Teledyne Wah Chang
Ground Water
The alluvial deposits of the Willamette River and its tributaries make up the principal aquifer in the
Albany area (Reference 1, Chapter 3, page 3). Ground-water levels are generally shallow, with depth
to ground water ranging from 3 to 22 feet below ground surface in the LRSP area, and 5 to 9 feet
below the extraction and fabrication area (Reference 1, Chapter 3, page 17). The general direction of
ground-water flow beneath the site is to the northwest and west towards the Wilamette River, with
local drainage to Murder and Truax Creeks (Reference 1, Chapter 3, page 4). Approximately 250
domestic wells are located within 3 miles of the facility, all of which are upgradient of the site.
There are no known domestic, municipal, mdustrial, or irrigation wells located between the site and
the Wilamette River (Reference 1, Chapter 3, page 4; Reference 2, page 3).
Ground-water monitoring has occurred at the Farm Ponds Site and the Plant Site since the early
1980’s. At the request of the ODEQ, TWCA began a ground-water monitoring program at the Farm
Site in 1980, and it continued quarterly through 1988. In 1982 and 1983, samples were analyzed for
MIBK, Total Organic Carbon (FOC), and an array of inorganic parameters. Beginning in 1984,
analyses were limited to the indicator parameters of ammonia, nitrate, chloride, sulfate, Total
Dissolved Solids (TDS), and conductivity (Reference 1, Chapter 6, pages 2 and 3).
The Current Situation Summary for the site presented analytical data for ground-water samples
collected in the area of the Farm Ponds (see Figure 1). These data were presented as concentration
ranges reflecting all of the years of sampling data. A comparison of the maximum concentration
range for each parameter to the appropriate Federal Drinking Water Standard demonstrates that
concentrations of heavy metals (including cadmium, chromium, and lead) exceed the Federal Primary
Drinking Water Standards. The maximum concentrations for chloride, iron, manganese, sulfate, and
TDS exceeded Federal Secondary Drinking Water Standards (see Table 1) (Reference 1, Chapter 6,
page 3).
Volatile organic compounds (including 1,1, l-trichloroethane, 1, 1,2-trichloroethane, and 1,1-
dichioroethane) were also detected in some ground-water samples in the Farm Ponds area (Reference
1, Chapter 6, page 3). There are no Federal Drinking Water Standards for these constituents;
however, a comparison of maximum concentrations to Maximum Contaminant Levels (MCLs) for
ground water indicated that no MCL levels were exceeded.
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Mining Waste NPL Site Summary Report
TABLE 1. GROUND-WATER CONTAMINANTS THAT EXCEED DRINKING WATER
STANDARDS
Constituent
Farm Ponds
Area (Concentration
Range - mg/I)
Federal Drinking
Water Standards
(mg/I) (Reference 7)
(Primary)
Cadmium
<0.0003 - 0.092
0.01
Chromium
<0.01 - 0.09
0.05
Lead
<0.02-0.1
0.05
Nitrate (N)
<0.01-62
10
(Secondary)
Chloride
0-3,100
250
Iron
<0.01 - 7.5
0.3
Manganese
<0 05 - 21
0.05
Sulfate
0 - 880
250
TDS
0 - 13,400
500
Source: Reference 1, Chapter 6, page 3
A number of locations at the Plant Site are sampled, including quarterly sampling since 1982 at the
LRSP area (including Schmidt Lake, chlorinator residue handling area, and magnesium resource
recovery pile); the Arrowhead Lake area (old Truax Creek landfill area); and the ammonium
chloride/sulfate storage area. Quarterly sampling has occurred at the metals formmg sump area since
1986 (Reference 1, Chapter 6, page 4).
Analytical data for a variety of constituents from the Plant Site were summarized in the Current
Situation Summary for the site. These data were presented as concentration ranges reflecting all of
the sampling data. When the MCL for each parameter is compared to the Federal Drinking Water
Standards, several constituents, from various locations around the Plant Site, were indicated as
exceeding the appropriate Drinking Water Standard (see Table 2).
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TABLE 2. GROUND-WATER CONSTITUENTS DETECTED AT PLANT SITE ThAT EXCEED DRINKING WATER
STANDARDS
I
—
Constituent
LSRP Area
Arrowhead
Lake Area
Metals Forming
Sump Area
Ammonlum Chloride
Sulfate Storage
Area
Federal Drinking
Water Standards
(Reference 7)
(Primary)
Cadmium
--
0.003 - 0.018
--
<0.003 - 0.02
0.01
Chromium
<0.01 - 0.96
--
—
--
0.05
Lead
<0.02 -0.28
<0.02 -0.15
—
<0.02 -0.07
0.05
Nitrate (N)
--
<0.5 - 160
<1 - 240
<0 5 - 550
0.01
Fluoride
--
I - 6
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Mining Waste NPL Site Summary Report
Exceedances of the Primary Drmking Water Standard were noted for cadmium, chromium, lead,
nitrate, fluoride, selenium, radium 226, and radium 228. Exceedances of the Secondary Drinking
Water Standard were noted for chloride, iron, manganese, sulfate, TDS, and fluoride (Refarence 1,
Chapter 6, pages 5 through 8).
Although Drinking Water Standards were not available for all of the constituents detected in the
ground water, a comparison to MCLs for ground water indicated that three volatile organic
compounds (1, 1-dichioroethane, chloroform, and 1,1, 1-trichloroethane) detected in ground-water
samples at the plant site exceeded the appropriate MCLs (see Table 3) (Reference 1, Chapter 6, pages
1 through 8).
TABLE 3. UPPER CONCENTRATION RANGES OF GROUND-WATER CONTAMINANTS
AT THE PLANT SiTE THAT EXCEED FEDERAL STANDARDS
Constituent
LRSP
Area
Arrowhead
Lake Area
MetaLs
Forming
Sump
Ammonium
Chloride
Storage
MCL
(Refer-
ence 9)
chloroform
<5 - 230
—
—
—
100
trichloroethane
<5 - 330
—
—
7 - 400
5
1,1,1-
trichloroethane
—
310 - 7,561
10 - 18,000
—
200
Concentrations are m g/1
Source: Reference 1, Chapter 6, pages 5 through 8
Ground-water monitoring data from the metals forming suxnp area mdicated that no constituents
exceeded Federal standards. Additional ground-water monitoring data is being collected and analyzed
as part of the ongoing Remedial Investigation for the site.
Surface Water
The Willaniette River is the major regional drainage flowing north through the Willarnette Valley and
is used for recreational, fishing, agricultural, and industrial purposes. Currently, there are no known
communities or individuals downstream of the TWCA that use the Wilainette River as a source of
drinking water (Reference 1, Chapter 3, page 23).
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Teledyne Wah Chang
Portions of the TWCA (namely the sludge pond units — LRSP and Schmidt Lake) are located in the
100-year and 500-year floodplains of the river. The Farm site is above the 500-year floodplain. The
ground surface at the TWCA site slopes westward toward the river at a gradient of approximately 11
feet per mile. Local creeks, drainage ditches, and lakes that receive drainage from the plant site feed
into the Willamette River. These waterbodies include four oxbow lakes (Second, Third, and Fourth
Lakes, and Conser Slough) and two creeks (Truax Creek and Murder Creek) (Reference 1, Chapter
3, pages 22 and 23; Reference 7, page 1).
The two creeks drain the plant site from east to west. They join northwest of the site and flow
northward through Third Lake, Fourth Lake, and Conser Slough, ultimately discharging to the
Wilamette River. Truax Creek receives discharges from the TWCA process wastewater treatment
system (under TWCA’s NPDES permit) and from parts of the site’s storm-water drainage system.
Murder Creek also receives discharges (mainly roof drainage) from the Plant Site storm-water
drainage system. The Farm Site is drained by two drainage ditches that enter the area from the east,
flowing westward and discharging to Conser Slough and the river (Reference 1, Chapter 3, pages 22
and 23).
Surface-water monitoring of an area drainage ditch north of the Farm Ponds designated as East
Boundary (upgradient), West Boundary (downgradient) and the Railroad Culvert (downgradienz)
occurred quarterly between June 1984 and March 1987. The parameters examined as part of this
sampling strategy included nitrate-nitrogen, TDS, conductivity, chloride, calcium, and sulfate. At the
plant site, Truax Creek is monitored weekly for ammonia, nitrate, and TOC, as required by the
NPDES permit (Reference 1, Chapter 6, pages 9 and 10).
Concentrations of constituents detected in surface water at the Farm Site and at the Plant Site are
presented in Tables 6-7 and 6-8 of Reference 1, respectively. These tables list the ranges of
constituent concentrations found throughout the monitoring program over the years (Reference 1,
Chapter 6, pages 9 and 10). Data for the Plant Site suggest that low levels of volatile and
semivolatile organic compounds are found in the surface waters on and around the site.
When the maximum concentrations from the Plant Site data are compared to the appropriate Ambient
Water Quality Criteria (AWQC), the following constituents are shown to exceed the criteria:
• Chloroform [ maximum concentration of 6 micrograms per liter (jLg/I) exceeds the surface
water AWQC for water and fish ingestion of 0.19 igfl
• 1,2-dichloroethane (maximum concentration of 7 g/l) exceeds the AWQC (also for water and
fish ingestion) of 0.94 gJl
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Mining Waste NPL Site Summary Report
Surface-water monitoring data for the Farm Site were conducted on a very limited number of
parameters, and could not be compared to the AWQC.
Additional surface-water monitoring data is being collected and analyzed as part of the ongoing
Remedial Investigation for the site. The Remedial Investigation was not complete or available to the
public at the time of this report’s preparation.
Sediments and Soils
Sediment sampling was conducted from September 19 through October 18, 1989, as part of the Phase
1 Remedial Investigation (Reference 6, pages 1 and 2). The results of these analyses will be provided
as part of the Remedial Investigation, which is not yet available for the public. The sediment samples
from this sampling episode were analyzed for volatile and setnivolatile organic compounds, total
metals, pesticides, PCBs, and radionuclides (Reference 3, Memo Page).
There were no analytical data available to characterize potential contamination of the soils at the
TWCA site. However, as described previously in this report, TWCA received a permit from ODEQ
to use the sludge from the wastewater treatment processes (stored in the Farm Site solids storage
ponds) as a soil amendment on the TWCA Farm Site. Although this practice was conducted for only
1 year (1976) the spreading of potentially radioactive material on the land raised many concerns in the
Site Investigation Report for the TWCA Site, including concerns about contamination of the food
chain and long-term contamination of the soil and land The Site Investigation recommended that
land use in the area be restricted (Reference 1 Chapter 5, page 8; Reference 4, pages 4, 5, and 6).
Air
TWCA has been monitoring the ambient air for radon emissions and radionuclide dispersion on and
around the site since 1967 under Air Contaminant Discharge Permits (Reference 1, Chapter 6, page
12). Extensive area and point source studies have also been conducted relative to radon emanation
and radionuclide dispersion near the LRSP, Schmidt Lake, and Farm Pond areas Measured radon
concentrations averaging 0.26 pico Curies per liter (pCill) have been similar to background levels
(0.21 pCi/I) in the vicinity of the site (Reference 1, Chapter 6, pages 13, 14, and 15). Airborne
particulate studies have indicted no detectable concentrations of alpha emitters; air emissions are
considered an ummportant pathway for radionuclide transport. Monitoring of gamma radiation levels
at the site boundaries and selected areas in the facility also indicate that levels are below the limits
specified by the Nuclear Regulatory Commission (NRC) (Reference 1, Chapter 6, pages 12 through
18).
13
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Teledyne Wah Chang
ENVIRONMENTAL DAMAGES AND RISKS
The ongoing Remedial Investigation/Feasibility Study, addressing contaminated ground water, surface
water, soils, and sediments associated with manufacturing and disposal activities at the TWCA site, is
currently being undertaken by TWCA and its consultant, CH2M Hill. Until an Endangerment
Assessment is completed, detailed information on environmental damages and risks for the whole site
is not available.
A general assessment of risks for the entire TWCA site were provided as part of the Site Investigation
report for the facility. Some of the risks identified in the Site Investigation included the following
(Reference 4, pages 4 through 7):
• The threat to workers by radon gas
• The potential that flooding could cause widespread contamination of radioactive wastes
• The contamination of the land by the application of radioactive materials
• The potential for ground-water and surface-water contamination.
A more detailed assessment of the environmental risks from the LRSP and Schmidt Lake was
provided in the ROD for those units.
Analytical data from the ROD (see Tables 4 and 5) indicated that the LRSP and Schmidt Lake sludge
contain metal compounds including zirconium, hafnium, chromium, mercury, nickel, uranium, and
radium. Cyanide was also found in the sludges. Several organic compounds were also identified;
hexachlorobenzene being the most prevalent (Reference 7, page 13).
Many of the constituents found in the sludge were identified as contaminants of concern in the ROD.
The following constituents were specifically identified as contaminants of concern and potential risks
to human health:
• Carcino2ens - Arsenic, beryllium, bis (ethyihexyl) phthalate, cadmium, chromium-VI,
hexachlorobenzene, methylene chloride, nickel, tetrachloroethene, trichloroethane, 1,1-
dichloroethane
14
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Mining Waste NPL Site Summary Report
TABLE 4. CONTAMINANTS IN LRSP SOLIDS
Ce t s s e nt Ma um f nmunn’ Average j Backgrixiiid 3
lnorgamcs
Arsenic
39
2
10
24
Barium
3,500
33
173
116
Beryllium
13
0.5
07
07
Chromium
220
65
tOO
20
Copper
77
29
48
12
Mercury
76
03
12
<02
Nickel
3,000
25
206
14
Lead
260
38
102
10
Antimony
24
5
11
<20
Selenium
16
I
3
3
Thorium
74(83)
11(12)
317(35)
35
Uranium
129(87 8)
127(6 4)
69 2 (46 5)
0 8
Zinc
87
24
40
39
Cyanide
1650
30
16
<2
Radium’ Activity Concentration
(222)
230x IG
(‘32)
3.32x10’
(13.2)
1 37x10 i
(1 0)
I 04x 10”
Zirconium 3
100
30
51
<10
Volatile Organics
Methylene chloride
22 000
0 006
0 084
—
1,1,1,-Tr ichlomethane
0860
0053
0155
.—
4-Methyle-2 .pcn tanone
1,1-Dichloroethane
1,400 000
0 040
3 929
—
0860
0053
0174
—
Tet r achloroethene
0 970
0 005
0 164
—
S re O thcs
Hexachlorobenzcne
64000
0740
6 600
—
b taC2-ethyl .hexyl)phtha late
1295
—
Note. All concentratiom in mg/kg of as received, wet solids
Concentrations in parentheses are in pCi/g
Only coontuienla that were detected in 10 percent or more of the samples arc shown
1 Mimir.um value detected above detection limit
2 Gcometric avenge Duplicates were averaged to obtain one value that was then included in the geometric average No values below
detection limits were
included in the avenge
‘From soil samples taken eaiyof the exiating Farm Ponds, October 1988 Sec Remedial Investigation report
‘As radsum-226
Zitconium is expressed ass percent (Reference 10. pages 6 and 8)
15
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Teledyne Wah Chang
TABLE 5. CONTAMINANTS IN SCHMIDT LAKE SOLIDS
Conetitn it I Aver ages
—__________
Ai,emc
36
8
16
24
Barium
72
36
39
116
Bciyliium
11
07
08
07
Cadmium
12
01
03
<01
Chromium
13
79
90
20
Copper
72
34
45
12
Mercury
14
0.2
0.6
<02
Nickel
4,300
1,700
2,600
14
Lead
150
70
103
10
Antimony
14
8
9
<20
Selenium
4
1
2
3
Thorium
593(75)
308(34)
463(51)
33
Uranium
237 7(1609)
1046(70 8)
1626(110 1)
0.8
Zinc
97
50
67
39
Cyanide
110
23
5.3
<2
Radium’ Activity Coricentiation
Zirconium’
288
39
74
<10
Volalile Organics
Methylene chloride
0 090
0031
0 046
—
1,1,1,-Trichloroethane
0320
0073
0168
—
4-Mcthyl-2-pen lanone
54000
24 000
32 708
1,1 -Dachlcroethane
3 900
0 170
1.054
—
Tetrachlocoethene
0073
0.073
0013
—
Sani,olatile Organics
Hexachlo roberizene
25.333
7300
14.087
—
bis(2-ethy l-bcxy l)pblhalate
N-Nitroseo.di-n -propy la m ine
0 190
0.048
—
Note All concentrations in mg/kg of as-received, wet solids
Concentrations in psrentheaes are in pCu/g
Only corlst ,wenls that were detected in 10 peri enI or more of the samples are shown
1 M,m ,n .rn , value detected above detection lung.
‘Geometric average. Duplicates were avenged to obtain one value that was then included in the geometric avenge No values below
detection limit were included in the avenge
‘From sod samples taken eaat of the Farm Ponds, October 1988. Sec Remedial lavealigation report
‘As radium-226
‘Zirconium is expressed as a percent (Reference 10, pages 7 and 9)
16
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Mining Waste NPL Site Summary Report
• Radionuclides - Uranium, thorium, radium
• Noncarcino ens - Antimony, barium, zirconium (Reference 7, pages 14 through 16).
The LRSP and Schmidt Lake are located on the floodplain of the Wilamette River; therefore,
contamination by flooding is a potential risk. The two units are also unlined surface impoundments
that could be a source of ground-water contamination. Another concern is contamination by airborne
dust from the ponds as they dry during the summer months or dust resulting from sludge removal and
potential treatment. The last major risk concern potentially resulting from the sludge from these units
is direct dermal contact by onsite workers or trespassers (Reference 7, page 13).
The ROD estimates that the risk of developing cancer from the LRSP and Schmidt Lake sludges
ranges from 1 in 1,000 to 1 in 3,000 for exposure over a lifetime for people who reside onsite The
greatest cancer risks are from nickel, chromium-VI, arsenic, and hexachlorobenzene. The risk of
death from cancer due to exposure from radionuclides if no clean-up action is taken range from 7 in 1
million to 1 in 1,000 (Reference 7, page 17).
REMEDIAL ACTION AND COSTS
According to EPA, the overall Remedial InvestigationlFeasibility Study for the TWCA site is not yet
completed and is not expected to be available until 1992 A ROD for Operable Unit 1 (i.e., the
LRSP and Schmidt Lake) was finalized in December 1989 as part of an expedited action to address
those sludge ponds. Seven clean-up alternatives were developed and analyzed in detail in the ROD.
Of these, an action involving the removal, solidification, and offtite disposal of approximately 85,000
cubic yards of material from the LRSP and Schmidt Lake was selected (Reference 7, pages 1, 3, and
4).
The specific remedy for the remediation of Operable Unit 1 begins with the excavation of sludge from
the LRSP and Schmidt Lake. Once excavated, the sludge will be mixed with a solidification agent,
such as Portland cement, to improve the handling and transportation of the material and to reduce the
mobility of the contaminants. The solidified sludge will be transported offsite to a permitted solid
waste disposal site. As part of the requirements for this disposal, the waste will be placed in a
separate, lined monocell and capped according to State and local requirements. The monocell is also
required to have a leachate control system (Reference 7, page 34).
The estimated cost for the remedy is $10.7 million, with the specific elements and costs of the action
defined below:
17
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Teledyne Wah Chang
• Sludge Removal and Haulina - $590,000
• Solidification Treatment Process - $1,586,000
• Offsite Disoosal - $6,000,000
• Engineering Design. Bids. Contingencies. etc . - 2,540,000 (Reference 10, page 35).
The long-term operation and maintenance costs (including monitoring) are included as part of the
offsite disposal cost.
CURRENT STATUS
According to EPA Region X, the Remedial Investigation/Feasibility Study is ongoing and expected to
be completed in 1992 (Reference 11). TWCA is preparing to remove the LRSP and Schmidt Lake
sludges under a February 1991 Unilateral Administrative Order. The monocell will be constructed at
the Findley Buttes landfill in Boardman, Oregon.
18
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Mining Waste NPL Site Summary Report
REFERENCES
1. Current Situation Summary for a Remedial Investigation/Feasibility Study for the Teledyne Wah
Chang Albany (Revision 4); CH2M Hill; October 1988.
2. Decision Summary, Interim Response Action, Operable Unit 1; EPA; 1989.
3. SAIC Report, Data Validation for Work Assignment C10005, Teledyne Wah Chang Albany,
DCN: TZ4-C10005-DV-02775; SAIC; 1990.
4. Potential Hazardous Waste Site, Site Inspection Report for Teledyne Wah Chang, Albany,
Oregon; EPA; 1982.
5. Review of CH2M Hill Work Plans for Baseline Risk Assessmenr Human Health Evaluation and
Environmental Evaluation, Remedial InvestigationlFeasibiity Study, Teledyne Wah Chang
Albany, DCN: TZ4-C10005-EP-H0773; Environmental Toxicology International Corporation;
1990.
6. Technical Memorandum Concerning Fall 1989 Sampling Activities, DCN: TZ4-C 10005-EP-
00568, From Thomas A. Tobin, SAIC, to Neil Thompson, EPA; Undated
7. Record of Decision, Decision Summary, and Responsiveness Summary for Interim Response
Action - Teledyne Wah Chang Albany Superfund Site Operable Unit 1 (Sludge Ponds Unit),
Albany, Oregon; EPA; December 1989.
19
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Teledyne Wah Chang
BIBLIOGRAPHY
CH2M Hill, Current Situation Summary for a Remedial Investigation/Feasibility Study for the
Teledyne Wah Chang Albany, (Revision 4) October 1988.
EPA. Decision Summary, Interim Response Action, Operable Unit 1989.
EPA. Potential Hazardous Waste Site, Site Inspection Report for Teledyne Wah Chang, Albany,
Oregon. 1982.
EPA. Record of Decision, Decision Summary, and Responsiveness Summary for Interim Response
Action - Teledyne Wah Chang Albany Superfund Site Operable Unit 1 (Sludge Ponds Unit),
Albany, Oregon. December 1989.
Environmental Toxicology International Corporation Review of CH2M Hill Work Plans for Baseline
Risk Assessment: Human Health Evaluation and Environmental Evaluation, Remedial
Investigation/Feasibility Study, Teledyne Wab Chang Albany, DCN: TZ4-C10005-EP-H0773.
1990.
SAIC. SAIC Report, Data Validation for Work Assignment C 10005, Teledyne Wah Chang Albany,
DCN: rZ4-C10005-DV-02775. 1990.
Tobin, Thomas A. (SAIC). Technical Memorandum Concerning Fall 1989 Sampling Activities,
DCN TZ4-C10005-EP-00568 to Neil Thompson, EPA. 1989.
20
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Teledyne Wab Chang Mining Waste NPL Site Summary Report
Reference 1
Excerpts From Current Situation Summary for a
Remedial Investigation/Feasibility Study for the
Teledyne Wah Chang Albany (Revision 4);
CH2M Hill; October 1988
-------
CURRENT SITUATION S1.ThQIARY
Revision 4
October 1988
CURRENT SITUATION SUNNARY -
FORA
RE DIAL INVESTIGATION/FEASI3 1LITY TUtY
TELEDYNE WAI! CBANG ALBANY
ALBANY . E ON
—
-
S
/s \ ‘‘
-F - :
--
Prepared for
Teledyne Wah Chang Albany
by
CH2M HILL NORTHWEST, INC.
Corvallis, Oregon
C22806 .WO
-------
CURRENT SITUATION SUt2tARY
Revision 4
October 1988
Chapter 2
PHYSICAL SETTING
TWCA is in M llersburg, Oregon, an industrially-based corn—
rnunity 3 miles north of Albany. The site is predominantly
in Sections 21, 28, 32, 33 of Township 10 South, Range 3
West, Willamette Meridian (WM), in the north—central part of
the Willa!nette Valley of western Orego Fig re -l). It is
roughly 20 miles south of Salem, 6 j.iles south f Portland,
and 60 miles east of the Pacific Ocea .
Plate 1 shows the site bo an Th TWCA site consists
of two manor areas: the plt’ si te area and the farm site
area. The 110—acre l .t zite CntaiflS an extraction area
south of Truax .C \a\fabr .icatiofl area north of Truax Creek,
a solids stora a ea vest of the Burlington Northern Rail-
road (Spokane—POrt d .Seattle Railroad), and a parking and
recreation area east of the Southern Pacific Railroad. The
farm site, approximately 115 acres, is 3/4 of a mile north
of the plant site and contains four 2—1/2—acre solids stor-
age ponds. The ponds are in the southern portion of the
site; the remainder of the site is used primarily for agri-
culture.
The iiwnediate area surrounding TWCA is primarily industrial
(see Plate 1). The industries closest to the sites are:
2—1
-------
“I ,
19 , •
- ‘‘,Mu*enburg /
• • F FARI SITE° 4/’
ii A 4/
29 \ - \__— r L
— 4 i ii .— -‘ -
‘, .‘ -• -•.-.
- I 2 4 /J//
- • - r
• t;- : - .v
f
--
- - A -
\
(‘ r.s:. . ‘
AY
32 I - ,‘ 3C
F1 • - • ç • ..i’JiI
tI1
q • - ‘:. 17 P l
-u Jr
L ___
- n ru ’ -
i
,, ,•‘ _ 4
&YA; 7 A _
‘ t ( .
• -• MAPLOCATION
Sossor USGS 124.000 Mbvy. Omgoii
— ,It,
SCALE Figure 2-1
LOCATiON MAP
1. idyn . WWi CP a a
-------
. c. — a.a oe 1
October 1988
o Wjllamette Industries’ Duraflake Division particle
board plant, at the northeast corner of the TWCA
plant site
o Willaznette Industries’ Western Kraft paper mill,
including settling and infiltration ponds, north
of the TWCA plant site and adjacent to the Willa—
mette River /
o Menasha Corporation’s wood flour proc ssing plant,
east of Willainette Industries Duraf1ake Division
‘: - - -i
o Georgia—Pacific orpo resin plant, also
east of Will iêttèJ . ,ndustrjes’ Duraflake Division
‘ =‘j==% .
o Siznps ’ Càx any’s plywood mill, about
1/2 i i l’ southwest of the TWCA plant site
o Truax Oil Company, Linn County Plywood Mill, and
SRC Incorporated, all between the TWCA plant and
farm sites on Arnold Lane
o Elstor Sales Corp. (formerly Sun Transformer),
about 1/4 mile south of the TWCA plant site
The land to the north of the TWCA plant site is used mainly
for industrial and agricultural purposes. The land east of
2—3
1 --
-------
CURRENT SITUATION SU? ARY
Rev2.sion 4
October 1988
1—5 and south of the plant site is used mainly for residen-
tial arid commercial purposes. The land west of the Willamette
R .ver, which forms the western boundary of the plant site,
is used for farming. The land surrounding the farm site
area .s agricultural. Albany, the urban area south of the
plant site, has a population of approximately 27,000; Mu—
lersburg has a population of about 560 peopl TWCA employs
more than 1,300 people from the area. /
/1
CVRi.53/037
V
‘ ii
2—4
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CURRENT SITUATION SU? 1ARY
Revision 4
October 1988
Chapter 3
ENVI RONMENTAL SETTING
The topographic and geologic, climatic, groundwater, and
surface water conditions of the TWCA site are described in
this chapter.
F
TOPOGRAPRY AND GEOLOGY
—
The broad and relatively flat i n .tti Valley was formed
by the Willainette River aa4t miándere back and forth be-
tween the Coast Range taifr o the west and the Cascades
to the east. the vicinit” of TWCA
slopes westward’t ward.s\thé ±iVer with a gradient of approx-
imately 11 feet per mile. Most of the hills within the Wil—
lamette Valley consã.s of relatively resistant volcanic rock.
The uppermost geologic unit in the Albany area is undiffer-
entiated younger and older alluvium deposited by the Wil-
lamette River. The upper portions of the alluvium include
about 5 to 15 feet of clayey silt mapped as Willamette Silt
by Allison (1953). Below the silt is a sandy gravel deposit
varying in thickness from a few feet to tens of feet and
mapped as Linn Gravel (Allison, 1953). This unit is wide-
spread in the mid—Willamette Valley but is exposed only
3 —1
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CURRENT SITUATION Stfl 4ARY
Revision 4
October 1988
where the silt has eroded. Frank (1974) differentiates the
gravel into younger and older alluvium. The younger depo-
sits are limited to the present flood plain of the
Willamette River; the gravels beneath the TWCA plant and
farm sites are mapped as older alluvium. Younger alluvium
may underlie the western half of the Lower River Solids
Area.
The alluvium is underlain by a fine-grafi ed ,itty clayey
sandstone (sometimes a sandy, claye £ilt tone or sandy,
silty shale). This rock unit is part of the Spencer Forma—
tion, which probably underlie t o the Albany area (Frank,
1974). In places it is deeply wéa therid and soft; in others,
it is moderately hard/. toc I’—eiOs on and redeposition as a
-
soft silty, clayey d ko.r siIt j clay may also explain some
of the unit’s i (ab ity.\.Because the Spencer was an ero-
sional surface i or to illuvial deposition, the thickness
of overlying alluv is variable. The Spencer is exposed
at the surface about 2 miles west of the site, across the
Willaxnette River.
CLIMATE ANtI TEOROLOGY
The climate in the Willamette Valley is influenced by moist
maritime air masses from the Pacific Ocean. Temperatures
are moderate, with maximums seldom reaching 1000? and minimums
3—2
tic’
-------
CURRENT SITUATION SU?* ARY
Revision 4
October 1988
rarely reaching 00? (NUS, 1983). Roughly 70 percent of the
40—inch annual precipitation falls during November through
March, while only 6 percent occurs during June, July, and
August. There are usually only 3 or 4 days per year with
measurable amounts of snow. The average annual potential
evapotranspiratiOn rate for the Albany area is about
27 inches. Therefore, there is an average anwial moisture
surplus of approximately 13 inches. }Iowever% there is a
substantial seasonal deficit during th dry umi r months,
resulting in the need to irrigate agricultural lands (NUS,
1983).
/ = \_\
2
The prevailing wind direct1Q 1 is’fzbm The south with an aver-
age wind speed of abotit 7 miIe6 per hour.
..., / ,
/= % • •
/
j\ REGIONAL GROUNDWA’I’ER
The alluvial deposits of the Willamette River and its tribu-
taries make up the principal aquifer in the Albany area
(Frank, 1974). The layers and lenticular bodies of coarse
sand and gravel in the alluvium locally yield large quanti-
ties of water to wells. The coarse deposits are interbedded
with finer deposits of sand and silt that produce consider-
ably smaller quantities of water. The underlying Spencer
3—3
-------
CURRZ T SITUATION SUZ’24ARY
Revision 4
October 1988
Formation has low permeability and yields only small quanti-
ties of water to wells. Water wells drilled into this for-
mation locally produce poor quality saline water (Frank 1974).
Direct precipitation during late fall and winter is the pri-
mary source of aquifer recharge in this area. Regional
groundwater flow is to the northwest and west-3lhere it dis-
charges to the Willamette River (Frank, 19 74L and locally to
Truax and Murder Creeks.
All known domestic wells in the TWCA ric. inity are upgradient
‘
of the site. There are no kn* do est3V. municipal, indus-
S..-
trial, or irrigation veils pcatéd’,bet een the site and the
Willamette River.F/) .\i
Si GROUNDWATER
S
The general hydrogeologic conditions beneath the plant and
farm sites have been identified based on specific hydrogeo-
logic data from previous investigations (see Figure 3-1). A
few other monitoring wells and numerous geotechnical founda-
tion borings provide additional information.
3—4
-------
3 mesw oo (1 9 lI)
Kno (19$4)
CH2M HILL (1987b)
4 EnvirOnmental G.ology and Ground
Waler (1660)
5 iwc* insatêe mon’tOflflg welts A
1910/1981
6 names and Moor, (1961b)
Figure 3-1
AREAS OF PREV%OUS
HYDROGEOLOGIC
INVESTiGATIONS
Teledyne Wsh Chang Albany
Albany. Oregon
LEGEND
— TWCA Boundafles
1 Science ApplIcadon. Inc. (1961)
Dames and t.$oore (1611$)
CH2M HILL (19$Z
2 CH2M HILL (1917$)
-------
CURRENT SITUATION StJ? 21ARY
Revision 4
October 1988
PLANT SITE
The conceptual model of the hydrogeologic system in the
plant site area is swnmarized in Figures 3—2 through 3—11.
These figures have been reproduced from CH2M HILL (1982 and
1987a)
The following generalizations can be made -ãbOut plant—site
groundwater conditions based on the CE2 1iILIa repOrtS and
other reports listed in “Reference (ChaP ter 8T:
o Fill material is pr se ’ Qc a1i .Y across the plant
site.
‘ /
o Aliuvial efl.tSrZflgiflg in thickness from 10 to
20 fe tf neath thi metals-forming area and up to
60 f et’beneath the Lower River Solids Pond (LRSP)
form the surficial geological unit at the site.
o The upper alluvium is composed of flood plain de-
posits consisting of fine—grained lenses of silt,
clay, and some sand (Willamette Silt). These de—
posits have relatively low permeability and pro-
duce little water. Permeabilities are typically
less than 1 foot per day (3.5x10 4 cm/sec).
3—6
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CURRENT SITUATION S 21ARY
Revision 4
October 1988
o The lower alluvium (Linn Gravels) consists of water-
bearing coarsegrained deposits of gravel and sand,
often with thin lenses of silt or clay (referred
to as shallow aquifer”). This unit is the upper-
most aquifer. Perineabi1it es are typically be-
tween 10 and 100 feet per day (3.5x10 3 to 3.5x10 2
cm/sec). -
o Bedrock consisting of a fine—qráined z.iltY clayey
sandstone, sandy clayey sfltsto1 a, orsandy silty
shale (the Spencer Formati n) underlies the lover
alluvium in most of the AThan area. Locally, the
unit appears to bQeither-deëplY weathered or
eroded and deposited as a soft silty clayey sand
. ¼
or a
ci
o Watet levels are generally shallow, ranging be—
tween ap rorimately 5 and 9 feet below ground sur-
face in the extraction/fabrication areas and be-
tween approximately 3 and 22 feet below ground
surface in the LRSP area.
o Groundwater in the shallow aquifer flows generally
westward beneath the plant site toward the Willa-
utette River, with local drainage to Murder and
Truax Creeks.
3—17
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CURRENT SITUATION SU 1ARY
Revision 4
October 1988
and sand often with thin lenses of silt or clay
(referred to as “shallow aquifer”). This unit,
which is 20 to 25 feet thick, is the uppermost
aquifer.
o A blue—gray clay (J.acustrine?) underlies the lower
alluvium in the farm site.
o Water levels are generally s 1lowj ge.nerally
ranging between approximately l to l0feet below
the natural ground surface -
o Groundwater inth sh] .Qwa uifer flows generally.
westward bet eath :th site towards the Willa-
mette
o Vertf gradiénts are downward through the upper
\,
alluvium tojthe shallow aquifer. The vertical
gradients are most prominent during the winter and
less so during the suer, indicating surficial
recharge of precipitation.
SURFACE WATER
Local creeks, ditches, and lakes in the vicinity of the TWCA
site are shown in Plate 1. The Willamette River is the uia:
3—21
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CURRENT SITUATION St.Th tARY
Revision 4
October 1988
regional drainage flowing north through the Wil].amette Val-
ley. The headwater of the Willamette River is in the Cas-
cade Mountains about 100 miles southeast of Albany. The
mouth of the river is in Portland, where it joins the Colun—
bia River. Swnmer and winter flows in the Willaxnette River
near TWCA are about 5,500 cubic and 110,000 feet per second,
respectively, according to USGS gaging record. . Portions of
the TWCA plant site are in the 100—year and 500—year flood
plains of the river (see Plate 1). Mo fthe TWCA plant
site east of the Burlington NortherIçt’ra k.s was above the
1964 flood elevation. The corridor &long Truax Creek, how-
/
ever, experienced significant I q q during this record
event. The Farm site isaboye e S0 year flood plain.
Local surface water_driinage i ipredominantlY westward to—
- - -
wards the Wil1ai i er Site surface water consists of
bodies that rec . e drainage from the plant site, including:
—
-
o Second, Third, and Fourth Lakes, and Conser Slough
(ox,bow lakes formed when the Wi].lainette River abart-
doned a former channel).
o Truax and Murder Creeks that drain the plant site
from east to west. The creeks join northwest of
the plant site and flow northward through Third
Lake, Fourth Lake, and Conser Slough, ultimately
discharging to the Willamette River.
3—22
I : ?
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CURRENT SITUATION SUMZIARY
Revision 4
October 1988
The Farm site is drained by two drainage ditches that enter
the area from the east and also flow westward, discharging
to Conser Slough and the river (see Plate 1).
The Willamette River is used for a variety of purposes, in-
cluding recreations fishing, agriculture, and industry. It
also serves as a water source for wildlife. No counities
or individual residences downstream of the’ TWCA plant site
are known to use the Willamette River as.a sourc of drink-
ing water at the present time. -
Truax Creek receives discharge f a e4 by NPDES permit)
from the TWCA process wasteiu ateZ treatment system and from
parts of the plant sip€Ato r age system. Murder Creek
receives discharge roof drains) from the plant site
storm drainage te ‘ BOt b/creek5 and Second Lake are also
local groundwa diSChaXge areas for shallow groundwater
w /
beneath the plant 9 3e.
AIR
Since 1967, air quality monitoring has been in effect and
TWCA has been operating under Air Contaminant Discharge Per-
mits. Area and point source studies have been conducted
relative to radon emanation and radionuclide disperson near
the LRSP, Schmidt Lake, and the farm site (Scientific Appli—
3—23
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CURRENT SITUATION SU? 1ARY
Revision 4
October 1988
Chapter 4
PLANT PROCESSES
The TWCA site has been operating continuously for approxi-
mately 30 years. Operations began in 1956 when, under con-
tract with the U.S. Atomic Energy Commission, Wah Chang Cor-
poration reopened the U.S. Bureau of Mines- Zirconium Metal
Sponge Pilot Plant. Construction of ne ir-faci.lities, at the
site of the existing plant, began .r l957 - The e facilities
were established primarily for the production of zirconium
and hafnium sponge. However, taat nài d niobium pilot
facilities were also included. e1rii and fabrication op-
erations were added in l959 — eIedyne Wah Chang Albany was
established in 1967af r Thle the Industries, Inc., pur-
chased Wah Chanq r&tib of New York.
-‘F
ZIRCONIUM AND HAFNIUM
TWCA is a primary producer of zirconium metal. (The zir-
conium manufacturing process is shown in Figure 4-1.)
Zircon sand, the principal ore, is imported from Australia.
This material is found in deposits that also contain several
other important raw materials, including rutile, ilmenite,
and monazite. Zircon (zirconium ortho silicate, ZrSiO 4 ) is
4—1
I ’
-------
‘3 ML I I *I
r9 ”1 f M
i1 ’* ‘I SIMII IS P SI SLIC S I IS MS ISS ZS
IF.*M ID VNII . ,
,— , - sS .S
I
I— -—
I
— — - • —-—.
, S,— .s5IIu 5oipIsig ,ft. , .c
—
- %L
—— - , _ I— . • — — — —•
• _•IS
—— I
,
•e
— —.-—--, -.-- —
s- - 4 j
ISUIS_
IS fl
-
— . ,c•. o
. -,—- —
IS
‘I
IIS
-
I,
IS
• I
S. I
S.
S. I SS I S I —
S.
— IS• S•
IS 5
FSgIMS 4 - I
ZMCOMUM
MANUFACTURING PROCESS
S
- •
IS RIOUCROW
-J
-------
CURRENT SITUATION SW2tARY
Revision 4
October 1988
concentrated in Australia by gravity, electrostatic, and
magnetic methods to remove all but a small amount of ixnpuri—
ties.
SAND CHLORINATION
The zircon concentrate is combined with petroleum coke, and
milled/mixed in a ball mill before feeding tO a chlorination
reactor. The chlorination reaction, coi d’uctèd’at a tempera-
ture of approximately 1,100°C (2,0l2°.F), is as follows:
ZrSiO 4 + 4C 4Cl 2 2rCL 4 ? -_1C.2 . 4 * 4CO
- - -
--
The silicon tetrachlori e (S1e1 4 Tiànd zirconium tetrachlo—
ride (ZrCl 4 ) are s 2 it d. by h’ictional condensation. Re-
maining of fgase ent tk r hber where caustic soda (NaOH)
removes chloriñ’ ài d chlorides. The SiCl 4 is purified and
sold as a byproduc .y
SE PARAT IONS
Most zirconium minerals contain 1 to 5 percent hafnium.
Hafnit is a sister element of zirconium; their chemical
properties are almost identical. The hafnium level in zir-
conium used in nuclear reactors must be extremely low. Zir-
conium has a low thermal—neutrOflCaPtUre cross section and
4—3
-------
CURRENT SITUATION SU Q4ARY
Revision 4
October 1988
will allow neutrons to pass through it without appreciable
absorption of energy. Hafnium, on the other hand, will ab-
sorb appreciable amoUnts of energy due to its high thermal-
neutron-capture cross section. The zirconium—hafnium sepa-
ration process involves dissolution of the Zr(Hf)C1 4 in water
with subsequent feed to a liquid—liquid extraction unit oper-
ation. The feed solution is mixed with an o qanic solvent,
methyl isobutyl ketone (MIBK), containing ãii oniumfl thiocyanate
(NE 4 cNS). Hafnium is more soluble in e organic (extract)
phase and thus is separated from th aquebus (r ffinate)
phase. Hafnium is removed from the t act phase by strip-
ping with sulfuric acid, and h .e&.i to a solid by
2
precipitation with an noni yd d .d fl B 4 OH) the preci-
pitate is isolated by itrat q a&id calciried to an oxide
(Rf0 2 ). Zirconium Lr InO ed from the raffinate phase by
precipitation wft1f fateN. ns (SOT). The precipitate is
isolated by fiI t tion) repulped with ai onium hydroxide,
and calcined to (Zr0 2 ). The MIBK and thiocyanate
materials are purified and recycled.
PURE CHLORINATION
Zirconium and hafnium oxides follow similar paths to metal
production. Zirconium oxide is mixed with petroleum coke
and fed to a chlorination reactor. The chlorination reac-
4—4
-------
CUF.RENT SITUATION StTh2 ARY
Revision 4
October 1988
tion, conducted at a temperature of about 1,100°C (2,012°F)
is as follows:
Zr0 2 + 2C + 2Cl 2 ZrCl 4 + 2C0
Reaction offgases are scrubbed with caustic soda to remove
chlorine and chlorides.
REDUCTION -
The final extraction operation invol zes the reaction of zir-
conium tetrachioride with ele zV . grTe iUm in a classical
Kroll” reduction reactiOfl4
—
ZrC1 4 + 2Mg • + 2MqCl 2
Magnesium chlor14 (MgC1 2 ) is physically removed from the
zirconium sponge ai 4 old as a byproduct. The zirconium
sponge is then heated in a vacuum (distillation) to remove
any residual magnesium chloride or elemental magnesium, which
is recycled or sold as byproduct.
CONSOLIDATION
Consolidation of the zirconium sponge into ingots involves
crushing to 3/4—inch minus, blending appropriate q uantities 1
4—5
-------
CURRENT SITUATION StTh 4ARY
Revision 4
October 1988
and pressing into briquettes. The briq,.iettes are then welded
together with an electron beam to form an electrode suitable
for consumable vacuum arc melting.
FORMING
Zirconium and zirconit m alloy ingots are processed into nu-
merous shapes and forms such as forgings, plate, sheet, foil,
tubing, rod, and wire. The forming op atiorts include forg-
ing, rolling, extrusion, drawing, t be reductioff and swag—
ing. Intermediate and final surface co ditioniflg can involve
caustic cleaning, degreasing & i tiichloroethane
(1, 1 , 1—TCA), and pickling- wk th fluoric (HP) —nitric
(HNO ) acid mixture. #C ist 1e- n& acid solutions are treated
3 -
prior to final dis arg .. j”rhe’q,l,l—TCA is sent to a recycler
for purificati4 etUrh /
NIOBIUM AND VANADIUM
TWCA can produce niobium metal from an ore, using sequential
processes of chlorination, hydrolysis, precipitation, calcin-
ation, and al.uminothermic reduction. The rate of operation
of these processes is variable due to changing demand for
the metal. Of fgas re scrubbed with caustic soda for re-
moval of chlorine a hlorides.
4—6
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CURRENT SITUATION StThCIARY
Revision 4
October 1988
Chapter 5
WASTE MANAGEMENT PROGRAMS
Waste management programs at TWCA include a wide range of
activities because of the many processes involved in produc-
tion of nonferrous metals and products. These activities
include process wastewater treatment, solid waste manage-
ment, hazardous, waste management, PCB4 t1pmènt’management,
radioactive—material control, wast miniaLzation through
beneficial use, and air quality control programs.
--
pc ,t as WASTZWATER
- ,
TWCA operates a ,rwac water tteatment system for management
of industrial wasetwater.s generated from the manufacturing
and forming of nonfetbus metals of zirconium, hafnium,
titanium, niobium, and refractory metals. Domestic waste—
water is collected separately and discharged into the sani-
tary sewage collection system for appropriate treatment by
the City of Albany.
The facility’s central wastewater treatment system consists
of a continuous chemical precipitation and sedimentation
5— 1
-------
CURRZNT SITUATION SU .1ARY
Revision 4
October 1988
system. Metals removal is accomplished by neutralization
with lime, magnesium hydroxide, or sulfuric acid and carbon
dioxide to pH 6 to 8 to form metal hydroxides and sulfates.
Fluorides are removed by the formation of calcium fluoride.
These compounds are removed in a clarifier by settling.
Solids generated from the operation of the clarifier,
referred to as “sludge, are placed in storage ponds for
additional settling and dewatering (see tbe discussion that
follows on wastewater treatment system 1ids).\
An emergency neutralization system f in place so that the
treated wastewater’S pH can be t_ w thin acceptable limits
should the central wastewater treatment system malfunction
before its discharge t67rruai-Cr k. Sodium hydroxide, sul-
N/ -
furic acid, or car dioxide thay be added by the emergency
- -
neutralization i Ste%.,\ \
\\ 1
Other systems used t?rWCA located on the upstream side of
the central wastewater treatment system include:
o Dechlorination to remove residual chlorine from
the blowdown of air pollution control devices
employed for the removal of chlorine and chloride
from gaseous emissions
5—2
-------
Revision 4
October 1988
o Spill collection and treatment to assist in meet-
ing limits for MIBK, ammonia, and thiocyanate from
the separations process
o Th ocyanate regeneration for control and recycle
of thiocyanate within the separations process
o Ammonia recovery /
o Oil separation 7 -
o MIBK steam strippin ft ntror and recovery of
MIBK within the epara foMs rocess
-
-
o Barium su at e..cdprec-ipitation for control of
-,= ‘ \
radium
. . .#
o Selecti uzinium precipitation and settling with
filtration for solids dewatering
o Boj].down for concentration of a dilute solution of
ainmonium sulfate for use as fertilizer or recycl-
ing in the zirconium/hafnium separations process
Figure 5—1 is a block diagram of the treatment systems and
process wastewater sources at TWCA.
5—3
-------
Figure 5-1
SCHEMATIC FLOW DIAGRAP
OF WASTEWATER SOURCES
AND TREATMENT SYSTEMS
Teledyiie Wab Cliaiig Albany
Alli my Oiegoii
ItRUUZ(R
R(CYQE
METALS MANUTACTURINC
(U(IT1NC. MAcHINING. AND
METAL RECOVERY PROCESS(S) I
STORM WATER . - IRUAX
STORM WAl ER
(I 0 TO 30 U CD)
-------
CURRENT SITUATION SU!’24ARY
Revision 4
October 1988
PERMIT STATUS
The process wastewater treatment facility was issued an
NPDES permit in March 1975 by the State of Oregon Department
of Environmental Quality (DEQ). Two addenda to the permit
were subsequently issued. The permit expired in June 1978
and was reissued in October 1978, with an expiration date of
July 1981. ApplicatiOn Forms 1 and 2C were submitted on
April 10, 1981. DEQ extended the expiration -date until a
new permit could be issued. Issuance oL& new permit was
delayed by DEQ until national efflue iimitations guide—
lines could be established (5O E L.3 76 %Jeptember 20, 1985
[ nonferrous metals manufacti ring pb 1 áseIIJ, 50 FR 34242,
August 23, 1985 [ nonf usmetals;forming) , and 49 FR 8742,
••\ \_/_ - -=, ,- _ -_ :-
March 8, 1984 [ non o s teta1 manufacturing Phase I)). A
new permit is e e t to’b&issued by the DEQ in 1988.
TWCA has been subm tt x g monthly monitoring reports to DEQ
since 1975.
WASTEWATER TRZAT NT SYST 4 SOLIDS
Solid residues generated from the operation of waste treat-
ment systems are most often referred to as sludges.
Sludges generated from the facility’s central wastewater
treatment system are presently stored in a number of surface
5—5
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CURRENT SITUATION SW’ 1ARY
Revision 4
October 1988
impoundments. Sludges generated prior to 1980 are contained
in the Lower River Solids Pond (LRSP), Schmidt Lake, and
Arrowhead Lake. Some of the sludge, generated prior to 1976,
was used as a beneficial soil amendment under permit on the
TWCA farm site located about 1 mile north of the TWCA plant
site. Sludge generated after 1980 is contained in one of
the four ponds located at the TWCA farm site and referred to
as Farm Ponds 1, 2, 3, and 4. Previous wastewater treatment
associated with the removal and recove.r -of ã nonia resulted
in the construction of an additionai. pond (V—2 Pond). This
pond was used for temporary storage ‘ánd- pretreatment with
lime prior to sending it to an Ma recovery steam strip-
ping system. The use of th&s pqn&was abandoned in 1979.
Solids remaining in tb pond’- oi st mostly of hydrous metal
precipitate and unte4 ime olids.
Lower River Sol Pond ,Schmidt Lake, and Arrowhead Lake
From 1967 until 1978, the solids produced from various waste-
water treatment processes were stored onsite in the LRSP,
Schmidt Lake, and Arrowhead Lake.
Arrowhead Lake was dewatered and covered in the early 1980s.
The LRSP and Schmidt Lake have not been used to store solids
generated since 1979. Supernatant water is returned to the
onsite wastewater treatment plant.
5—6
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CURRENT SITUATIO 4 SU 1ARY
Revision 4
October 1988
In the early 1980s, various agencies and environmental in-
terest groups focused on the solids stored in the LRSP and
Schmidt Lake because of their purported low-level radioactive
properties. TWCA submitted an application for a site certi-
ficate for the maintenance of a radioactive waste disposal
facility to the Oregon Energy Facility Siting Council (EFSC)
in 1982. A series of public hearings was held. The EFSC
ruled in March 1987 that the radioactive level of the LRSP
sludge was too low to meet the criteri t as a low—level radio-
active waste and, therefore, was no-t nder EFSC ’ s jurisdic-
tion. TWCA, on May 1, 1987, announc p.lans to relocate the
- . . . --
sludges approximatelY 1 mile to re aV&the D from the 500—
year flood plain. These pi sis erepl ced on hold after it.
\c_
was ruled that the riskjana Deifl 1atiOfl options for the
• =
sludges had to be rese4 as’ PTart of the CERCLA (Superfund)
, - - \ %. ‘
RI/FS process.,/
/
Farm Site Solids S cr ge Ponds
In 1978, TWCA modified the process for the production of
2irconium and hafnium metal that lowered the trace concen-
trations of radioactive compounds in the sludge. The
process modification directed the radioactive materials into
a separate solid waste referred to as chlorinator residue.
This residue is managed as a radioactive waste and shipped
to Hanford, Washington, for disposal.
5—7
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CUR.RZNT SITUATION StThffIARY
Revision 4
October 1988
Sludge generated since the implementation of this modifica-
tion has been stored in the four Farmsite ponds. These
ponds were placed into operation in October 1979, after ap-
proval by the DEQ as part of the NPDES Wastewater Discharge
Permit program. A groundwater monitoring program was imple-
mented as a permit condition.
Farm Site Soil Amendment Programs -
The use of sludge generated by the .cemtra wastèwater treat-
ment system as a beneficial soil ame rnent has been imple-
mented i.n the past by TWCA. were con-
ducted by the Depareflt SoiS çii eS of Oregon State
University under cont CA-before 1976. Additional
studies were conducted y SU 1979.
(
TWCA obtained h.s J .id Waste permit (No. 1079) from DEQ to
use the sludge as so il amendment on the TWCA farm site in
1976. The sludge was applied at an average rate of 108 tons/
acre on the 47.8 acres available for soil amendment. Further
use of the sludge as a soil amendment has not been imple-
mented since 1976.
V—2 Pond
The name V—2 Pond comes from the major wastewater stream
discharged into the pond, which was the lime—treated
5—8
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CURRENT SITUATION SUZ2IARY
Revision 4
October 1988
zirconium sulfate wet cake filtrate (V-2 filtrate) produced
by a rotary vacuum filter used i.n the zirconium and hafnium
separations process. The V—2 Pond was used to settle the
lime solids in the treated filtrate. Because processes for
the extraction and manufacture of niobium and tantalum were
located in the building used for the separations process,
some of the wastewaters from the niobium and -tantalum pro-
cess used before 1975 were also placed into the V—2 Pond.
The V—2 Pond was built in 1960 as one lar e pond . The ammo-
nia recovery treatment system consist .rig of a steam strip—
ping column, was installed in -1.!6& rëcoVer ammonia from
the treated V—2 filtrate prior to Lsc arging to TWCA ’s
central wastevater treerts s th.
\_ :=:
A dike constructe . ..crushe rock was installed in 1975,
making one lar . qnd and one small pond. The dike was
installed to reduc the level of sulfate ion in the V-2 Pond
by directing the discharge of separations process spillage
into the small pond and precipitating the sulfate with lime
before it entered into the large pond. The contents of the
large pond were directed to an ammonia recovery treatment
system.
A 200,000—gallon tank and a 400,000—gallon tank were built
in 1977 and 1978 to store the V—2 filtrate in a tank rather
than in the V—2 Pond. A separations spill treatment system
5—9
I ,
-------
CURRENT SITUATION SL 4ARY
Revision 4
October 1988
was installed in January 1978, and then modified with major
improvements by February 1980 to eliminate any waste or waste—
water influent into the V—2 Pond.
The contents of the small V—2 Pond were removed and trans-
ported to an EPA—approved landfill for disposal in 1987. It
is estimated that 5,400 cubic yards of solids . are presently
contained in the remaining large portion o f the pond.
SOLID WASTE \
- .-
CURRENT MANAGEMENT PROGRA I&
Solid waste manage tp.rograms ât TWCA have been developed
and iJ.h the requirements of RCRA,
TSCA, and CERCL ..\These programs include procedures for:
o Proper management and disposal of brand—name pro-
ducts and items used on the plant site
o Proper management and disposal of solid wastes
generated by different process operations
o Proper management of transformers and capacitors
containing PCB
5—10
-------
j. jATiON SU 1ARY
Revision 4
October 1988
All materials are initially delivered to the TWCA Duznpmaster
Area if they are intended for transportation to arid disposal
at a public landfill or at a hazardous waste treatment, stor-
age, or disposal facility. Nonhazardous material is inspec-
ted by the operator of this area to make sure it does not
contain any items prohibited from disposal in a public land-
fill by federal and state law or by more restrictive dis-
posal policies developed and inplementedb ’ WCA.
Hazardous wastes intended for disposal a r also nspected by
the operator of the Dumpmaster Area s they are transferred
from the generating process a - to-e D nnpinaster Area for
temporary storage. The wastes ar inspected to make sure
- r
they have been placed aprop çcontainer with correct
labeling.
Manaaement and ‘t i posa1 of Brand—Name Products
As part of its solid waste program, TWCA has reviewed all
items purchased to determine if they would be RC A hazardous
waste due to ignitability, corrosivity, reactivity, or toxi-
city; a fire hazard; or an environmental liability if im-
properly managed or disposed. All of these items have been
assigned a disposal code so the material will be disposed of
properly if it is no longer needed. This practice, as well
as instructions to implement a spill contingency plan in
5—11
-------
CURRENT SITUATION SU ARY
Revision 4
October 1988
case of an environmental incident, are formally documented
in a written procedure and used at the TWCA site.
Solid Process Wastes
Each process area has been evaluated to minimize the genera-
tion of waste and make sure it is properly managed. Table 5-1
lists process wastes presently generated on a routine basis
at TWCA. This listing describes each Waste’ characteriStiC
and the waste management option used for -r ecycle treatment,
or disposal.
Written procedures are inp inente& to make sure that hazard-
ous and radioactive w es,are Pr PerlY managed and packaged
- ;- —.-
on the TWCA site ransportatiOfl offsite for treat-
ment and disposai ( \
\ 1
- - .F
Containers of hazardoys waste are temporarily stored at the
Dumpmaster Area where they are inspected weekly until trans-
ported offsite. The Dumpmaster Area includes an asphalt
surface and collection sump so as to collect and direct any
contaminated rainfall and runoff to the Central Wastewater
Treatment System. All liquid wastes, such as solvents, that
are forbidden from entering the treatment system are placed
in separate steel trays so any spillage may be fully con-
tained and properly managed.
5—12
-------
Table 5—1
p c s WASTE AT TW .
_iJ .k 2Ci uA . t1 .flI A Z
Revision 4
October 1988
Sand chlorinator
Residues
Sand Chlorinator
Residues
MISK Still Bottous
Dranius R oval
Treatnest Systes
Solids
Pure lorinator
Residues
Pure Chlorination
Residues
Recycled Oxide
Chlorinator
Residue
MgCl 2 Wastes
(an.taal fat)
Fire Hazard
doue
Nonhazerdous
HP xic
CD 008)
Iqni table
Toxic (F 001)
Fire Hazard
Nonhasardous
Fire Hazard
Nonhazardous
IqnL table
Methyl lsobutyl Ignitable
Ketone
l,l,l—TricblOroethane Toxic (F 001)
Radioactive Waste Landfill
Onsite Corrosive Neutral-
ration Tank
Hazardous Waste Incinerator
Radioactive Waste Disposal
Site
,11
IwICVR1 S3/0il
Waste Characteristic
Generating Process
Zlrconiun and Mafnius
Manufacturing
Sand Chlorination
Separations
_________e
Radioactive
Nonbazardous
Ignitable
Radioactive
Pure Chlorination
Reduction
Nonhazardous 0nsita’ CorTOsive Neutraliza-
tion Tank
Radioactive Radioactive Waste L.andf ill
HP xic CD 009P Hazardous Waste Landfill
Fire Hazardf ..-8 eficial--85S of Mg as Nag-
- nesius ds xide Slurry
- Oxidation of Metal Fines in
okabousS Material azardou . Public Landfill
(Nonhazardous)
ok.bouse Material eeLc .008 !-HazazdOuS Waste Landfill
(Hazardous) -
Stainless Steel ) ue haMrdbu?
Uners - /
Niobiux Manufacturing No Thezeitr’SUg - HP Haxlc CD 005)
FeNo The i Slaj nbNa4rdous
Vanadiua Manufacturing Thereite s g ’ onbazardous
Round Products Foraing Salr JIat ri k HP x.tc (D 005)
Ixtrusion Products c* Th b e
Foraing
-.If .inq So1 s
B1as n Grit
S uHber Solids
haido ua)
Scru_bb r So lids
(Ha züd )
Isaprogyl Alcohol
1,1 ,l—Tri loro.thane
Metal Grinding
Solids
Abrasive Saw Fines
Metal Fines
Buruback Material
Waste Thinners
Powder Metallurgy
Metal Forming
Metal Recycle Facility
Hazardous Waste Landfill
Public Landfill
Public Landfill
Hazardous Waste Landfill
Biological Treateent Lagoon
Hazardous Waste Landfill
Recycle or Public Landfill
Public Landfill
Hazardous Waste Landfill
Ignitable Waste Incinerator
Recycle at Hazardous Waste
Facility
Hazardous Waste Landfill
Public Landfill
Onsite Oxidation in Burnback
Syst
Public Landfill
Incineration
Recyci. Onsite
Paint Sbop and
Maintenanco Shop
Analytical lab
Recycle at Hazardous Waste
Facility
-------
CUR ENT SITTJATISN SU?24ARY
Revisi•n 4
•ct• er 1988
Low-level radioactive residues are generated by the pure
chlorination and sand chlorination processes. They are col-
lected and transported from the process area in specially
designed steel collection containers to the residue handling
facility. This facility is used to transfer the residues
from the special containers into containers for transporta-
tion and disposal. The facility includes an impermeable
surface sloped so as to collect any contaminated rain water
or washdown water for removal of radium ’-’in a -separate waste—
water treatment system. RadioactiVe-.te dues and solids
generated from the trea ent system e- transported to an
offsite radioactive waste dispoS._ 1.t .
- - i , —
Transformers and Capa itorscO t tfliflg PCB
There are consi erabT èletriCal power requirements for
operation of ñetaià manufacturing and forming processes
at TWCA. Therefor number of transformers and capacitors
are used throughout the plant site. Most transformers are
owned by Pacific Power and Light as part of the electrical
distribution system. A few transformers and most capacitors
are owned and operated by TWCA. Some of this equipment
holds oil that contains PCB (po].ychlorinated biphenyl),
which is regulated by the EPA and DEQ.
5—14
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CURRENT SITUATION SUt24ARY
Revision 4
October 1988
PCB—contaifliflg equipment that is owned and operated by TWCA
is managed and inspected as required by specific procedures
and training requirements developed by TWCA to ensure corn—
pliarice with regulatory requirements. Due to environmental
concern, any equipment containing PCB that is removed from
service is sent to an EPA—approved PCB facility for proper
treatment and disposal. As such, TWCA does nQt have a stor-
age site for PCB waste. Equipment or items containing PCB
and designated as waste are only temporYily St3 ed for less
than 90 days in drums in the Du master A ea un i trans-
ported to an EPA—approved facility. Wrior to construction
of the Dumpmaster Area, waste PCB. teas were temporarily
stored in a specially des.ig d iterage facility with a
bermed concrete floorF/ ‘
•\ / - ,-- ;
There are no knc fl il1s ,f PCB into soil or water. As
required by EPAX e ts? are completed annually that document
management of PCB ttears owned by TWCA.
PERMIT STATUS
TWCA has notified the EPA and DEQ that the only hazardous
waste activity included at the site is generation.
On February 3, 1984, TWCA submitted a complete RCRA Part B
Application for the operation of hazardous waste management
5—15
-------
CtJRRZNT SITUATION SW2tARY
Revision 4
October 1988
activities at the site, including thermal treatment of non-
ferrous metal fines in the Burnback Area. It also included
management of magnesium chloride wastes by the beneficial
use of magnesium within these wastes as magnesium hydroxide
slurry and thermal treatment of the remaining metal fines in
the smokehouse. This application was considered complete by
the EPA. However, the EPA concluded that these wastes man-
aged and treated at the facility did not meet the criteria
to be classified as an ignitable or re tive waste. There-
fore, a Part B RCRA Permit was not deemed neCeSSarY for
these activities.
--
Radioactive wastes are manaq d under the requirements of a
Naturally Occurring R ioactive . Materials NORM” license,
issued by the Stat ç reqOfl 1th Division. It was re-
newed in 1987. -- -/ \
PAST DISPOSAL PRAC ICZS
TWCA has not always practiced offsite disposal for all of
its waste process residues. Three major areas of the plant
site have been used in the past for this purpose: the
chlorinator residue pile, the magnesium resource recovery
pile, and the Truax Creek area landfill.
5—16
-------
CURRENT SITUATION SUMMARY
Revision 4
October 1988
Chlorinator Residue Pile
Beginning ifl 1972 with the startup of the sand chlorination
process chlorinator residues were placed in a separate pile
north of Schmidt Lake. This practice was discontinued in
1978, when the contents of the pile were transferred to the
Hanford radioactive waste disposal site in Washington. After
the contents of the pile were removed, the area was surveyed
with a R meter and visually inspected t ensure that no
contamination remained. Powdered baz.fum -sulfate’WaS applied
over the entire area.
The Chlorinator Residue Eam.dljngYa.Ciflty was constructed in
December 1978, on the tewbere’the pile was previously
located.
Magnesium Resot ce. Recovery Pile
-
Solid residues generated during the development and opera-
tion of nonferrous metals manufacturing processes at the
plant site were placed in a resource and recovery pile. Due
to improvements in process operations and modifications in
management of materials, no material has been placed in the
pile since May 1983.
Intentions were to later recover the metallic value from the
material placed in the pile. Because the major metal of
5—17
-------
CURRENT SITUATION SU! 21ARY
Revision 4
October 1988
value contained in the pile was magnesium, the pile was ap-
propriately named the Magnesium Resource Recovery Pile. The
major material placed in the pile was magnesium chloride
wastes generated by the zirconium/hafnium reduction process.
Other materials included stainless steel liners and thernu.te
slag containing small amounts of niobium.
In October 1983, TWCA notified the DEQ of ã proposal for a
process to recover and beneficially use the contents of the
pile. A small-scale process was appr.oved -and pI’aced into
operation. It was modified and enla qedin February 1984,
and again in October 1984, of the DEQ.
Since the initial startup ver 2Q ,OOOCUbiC yards of
material has been proc 9sed te.prcduCe a magnesium hydroxide
slurry used as a for operation of the TWCA
Central Wastewatex Tratmei System. In August 1986, a
sheetpile wall installed to eliminate mixing of the LRSP
solids with the be iç cial portions of the pile. The
recovery operation will be completed in June 1988.
Truax Creek Landfill
A portion of the area north of Truaic Creek extending from
the area opposite of the V—2 Pond and east to Arrowhead Lake
was used as a landfill beginning in 1958 until 1973. Arrow-
head Lake was used briefly as a landfill in 1976.
5—18
‘1
-------
CURRENT SITUATION StTh2tARY
Revision 4
October 1988
AIR
TWCA operates air coflta!Ttiflaflt control systems to cleanse
emissions from the transition metal refining operations under
Air Contaminant Discharge Permit No. 22—0547. Table 5-2
lists emission sources, control systems, and air contaminants.
Control system blowdowns are directed to the entral waste—
water treatment system.
-f -
,
CVR153/040
- --=
- -- - - .- - .-—. -
—
5—19
-------
CURBDiT SITUATION SUMMARY
Revision 4
October 1988
Table 5—2
AIR CONTAMINANT CONTROL SYSTEM SUMMARY
issi.on Sources Control System(s) Air Contaminant
Sand Chlorir ation Water Spray, Caustic Cl 2 , CL, particulate
Of fgas Packed Bed
Sand C ilorination Area Caustic Spray, Caustic Cl 2 , CL, particulate
Vent Packed Bed
Feed Makeup Of fgas High Pressure Venturi, Cl 2 , cL., particulate
Demister -
Feed Makeup Area Vent Low Pressure Venturi, C1 2 ,C , particulate
Dem.1.ster -
Separations Area Vent Acid Packed Bed - - - - 1H 3 , NH 4 +-
Zr0 2 /Hf0 2 Calciner Cyclone, Med. Pressure 502; SO3 particulate
Venturi. Demister, -
Caustic, Packed .Bed,
Wet Electrosta C . —
Precipitator
Siltet Purification High Pre sure Venturi Cl 2 , CL, particulate (mm)
Caust c.-Pucted Red
Pure Chlorination Ca st c Spr austic Cl 2 , cf, particulate
West Zr Reduction Pr%ss IXe Venturi CL , particulate
East Zr ReductmoD .t High ressüre Venturi CL, particulate (mm)
Magnesium Recovery \Wet . onmzer, High CL, particulate
P ess’ure Venturi,
Qemister
Crucible Handling High Pressure Venturi CL, particulate (mm)
2°5 Calciner High Pressure Venturi, Particulate (mmn)
Demmster
Boilers (3) None SON , NOR, particulate
Metal Pickling None F, NO
Operation
Crucible Burn Pots None Particulate
Raw Material Handling Scrubbers Particulate (mm)
Fabrications Scrubber
Baghouse s
Reference: DEQ Review Report, January 12, 1987.
CVR153/009
“4
-------
CURRENT SITUATION STJ?*IARY
Revision 4
October 1988
Chapter 6
ENVIRONMENTAL MONITORING PROGRAMS AND DATA
This c iapter su.uunarizes ongoing environmental monitoring
programs at TWCA. It briefly describes the sampling loca-
tions, periods, and frequencies. Sporadic or: one—time grab
sample analyses are not included. Summary tables show para-
meters analyzed and concentration ranges
This section is organized as follows .
o Groundwater Qua.1 t y Menftcring
—__ % _
\ _ _ f - - ,
- Fa t (
,.. \ -\:\
- •P( \‘ % -
- ia t s1te (LRSP, metals-forming sump area,
‘-=- \/__,-_
Arrówh ad Lake, and a.miuonium hydroxide and
sulfate storage area)
o Surface water quality monitoring
o Solids Characterization
- Farm site
— Plant site (LRSP and V-2)
6—1
-------
CURRENT SITUATION SU ARY
Revision 4
October 1988
o Air Quality Monitoring
o Treated Process Wastewater Quality Monitoring
GROUNDWATER QUALITY MONITORING
FARM SITE -
At the request of the Oregon Department o Environmental
Quality and Oregon Water Resources Department, TWCA imple-
rnented a groundwater monitoring pr P aXfl at the farm site.
Fourteen wells are routine—1 . sa 1ed (see Plate 3 for loca-
tions). /7
Sampling of most wii bega iin 1980 and has continued quar-
terly to date. Iñ 1982 and 1983, samples were usually
analyzed for MIBXk 9 ’ and the inorganic parameters sum-
marized in Table 6—1. From 1984 to date, analyses have been
limited to the indicator parameters of ammonia, nitrate,
chloride, sulfate, total dissolved solids, and conductivity,
with periodic additions of other parameters. The Knoll re-
port (2984) presents the initial monitoring program. The
CH2M HILL (i.987b) report documents the monitoring program
for the deep railroad (RRD) well. Table 6—1 summarizeS the
range of groundwater quality data from these sampling activi-
ties.
6—2
-------
ab1e 6-1
( 00ND AT QUALITY
FA SIT!
CURRE 4T SITUATION StThfl4ARY
RevisiOn 4
October 1988
Concentration
Ranne
P&r t r
Concentration
Range
Calcium
Magnesium
Potassium
Sodium
Aonaa (N)
Bicarbonate
Carbonate
Cb loride
Fluoride
Nitrate cm
o — 1,220 mg/i
6 — 330 eq/i
0.48 — 8.3 eq/i
7.8 - 360 mg/i
o - 10 ag/i
0.01 - 200 mg/i
0.001 - 160 ag/i
0 — 3.100 mg/i
<1 — <5 ag/i
‘0.01 — 62 eq/i
Copper
iron
Manganese
Nickel
Zinc
<.005 - 0.28 a g/i
<.01 — 7.5 ag/i
<.05 — 21 ag/i
<.01 - 0.19 ag/I
<.005 - 0.26 ag/i
0.2 — (1.0 ag/I
(1.0 ag/i
<.0003 — 0.092 ag/I
(.01 — 0.09 mg/I
<.02 - 0.1 ag/i
<.002 — .01 mg/i
<.003 — <.005 ag/i
.01 — <.02 ag/i
— <.7 pCi/i
(.1 — (i. 2 pCi/i
W L.belov thod detection limit
NOTE: S.. Table 6—2 for veil location n ers
- aicro
6—3
Sulfate
Thiocynate
Con ctivitY
pH
Total Dissolved Solids
Arsenic..
Bari -
Ca t
- ch i u m
L ad
0 - 880 eq/i erumzy
-------
CURRENT SITUATION S MMA
Revision 4
October 1988
PLANT SITE
Groundwater has been monitored at various areas of the plant
site since about 1980. The last area added to the plant
site monitoring wel]. network is the metals—forming sump area
in 1986. Table 6—2 suxmnarizes the areas monitored and cor-
responding wells. Plate 3 shows the location of the wells.
Tables 6-3 through 6—6 summarize groundwater-quality results
from each area. - — -
Tab -&--2
SUMMARY OF PLANT AND FARM ShE GROUNDWATER MONITORING
Approximate
Area : — . -Wells Frequency
.—.,
Aonium Chloride Quarterly
and Sulfate Storag , , , % PW3 Since 1982
Arrowhead Lake PW4 and PW5 Quarterly
Since 1982
Lower River Solids PonL - PW7 - PW9 Quarterly
WlO Since 1982
PWA - PWE
Metals Forming Sump PWIO - PW14 Quarterly
Since 1986
Farm Site RRD, RRS, WS, WD1 Quarterly
WD2, ND1, ND2, NS Since 1984
ND, ES, NW, SD & SS
a lncludes Schmidt Lake, chlorinator residue handling area,
and magnesium resource recovery pile.
6—4
-------
CURRENT SITUATION SU 1ARY
Revision 4
October 1988
Table 6—3
0VNDWA QUALITY
AJ* NIUM IDE A18 SOLPATE STORAGE ABZA
Su ) late
Thiocynate
Conductivity
Total Dissolved
Solids
Copper
Isen
Manganese
Nickel
Zinc
Arsenic
Bari
Ca iue
Chrosius
Lead
-------
CURRENT SITUATION SU 4ARY
Revisi.on 4
October 1988
Bicarbonate
Carbonate
Chloride
Fluoride
Nitrate (N)
Sui iate
Thiocynate
Conductivity
pH
Total Dissolved
Solids
Copper
Iron
Mangen e
Nickel
Zinc
A.rs ic
Barium
Ca .t
C hr ium
Lead
120 — 230 eq/i
0.005 - 0.09 eq/i
10 — 4,900 eq/i
1 — 6 eq/i
<.5 - 160 eq/i
<10 — 1,200 eq/i
<1 — 19 eq/i
1,160 — 10,200 uebos/
6.0 - 7.8
20 - 8,000 sq/i
<.1 — <1.2. pCi/i
<.34 pCi/i
(1 eq/i
5 — 140 sg/1
<5 — 14 .700 s q/i
310 — 7,561 ugh
31 — 480 ug/i
<100 ugh
<100 ugh
<50 — <100 uq/l
<50 - <100 ugh
<50 - 100
-------
CURRENT SITUATION SU *1ARY
Revls2.ofl 4
October 1988
Table 6—5
G VNDWAT QUALITY
L0W RIV SOLIDS AREA
Parameter
Calcium
Nagnes ium
Potassium
Sodium
Amoxu .a (N)
Bicarbonate
Carbonate
Cbloride
Fluoride
Nitrate (N)
Sulfate
Thiocynate
Co ictiVity
pH
Total Dissolved
Solids
Copper
Iron
Manganese
Nic e1
Zinc
Arsenic
Barium
Cadeiu2
Cbr ium
Lead
<3 — 1,200 ag/i 1,1,1 Tc toroethane
(1 — 165 mg/i 1,1 DicbI oetMane
170 - 113,000 umbos/em
4.5 - 10.0 Mety eO. b1Otide
Tet ach1 roet oe
1.1 - 89,500 mg/i 1
Tr s—1 ,2-Di 1erothene
<.005 - 0.23 mg/iF rt 1 oethe ne
<.05 - 570 m 1\.. 0ther Vo1atile Organics
<.03 - 230 mg/t%
<.01 - 2 .g*i
<.OV-44’ i/1
< .05 mqI
<.5 - iOsVi/
<.003 - 9mg/i
<.01 — .96 /1
<.02 — 0.28 mg/i
<.002
<.003
<.01
<.1
<.3
Concentration
Range
- <2 ng/1
- <0.01 /l
- <.05 ng/1
— 7.6 pCi/i
- 11 pCi/i
<.11 — ‘1.1 pCi/i
<.34 pCi/I
<1 — <50 sgIl
<3 — 200 mg/i
4 - 68,400 mg/i
<50 — <100 ugh
14 — 100 ugh
‘S — 230 ugh
<5 — <100 ugh
-------
Table 6-6
GRO0NDWAT QOALITY
ALS- Rl D G SW AW
CURRENT SITUATION SUZ 1ARY
Rev3.slon 4
October 1988
Paraseter
Concentration
Ranae
a
Concentrat.or.
RAnce
Calci.un
Mag esiua
Sodi
Aonia (N)
Sulfate
Thiocyanate
Conductivity
pH
Total Dissolved
Solids
Copper
Iron
! nganese
NicXel
Zinc
Ba.ri a
Chro .Lua
Lead
Radiu .-226
Radiu .—228
Thoriua
tiranlu .
Total Susp óed
Solids
Total Organic
Carbon
2 — 220 ag/i
1 — 89 ag/i
6 — 94 ag/i
(.5 — 29 ag/i
10 — 130 ag/i
<2 — 2 ag/I
140 - 1,940 u.bos/
5.2 — 7.2
38 — 1,500 ag/i
(Li pCi/i
(.34 pCi/i
(10 — l, ag/i
(3 — 26 .g/i
Cbloroaetbane
Bronoethane
Dicbiorodif luoroaethane
Vinyl Chloride
chioroethane
Trans-i ,3-Dicblorcpropene
Tricbleroethene
Broaof or.
1,1,2 ,2-Tetrachioroethane
Percbloroethy lene
cblorobeczene
1 ,3-Dicnlorobenzene
1 ,2-Dicblorobeazeae
l,4- i leroben2eae
(5 — 1.300 ugh
<1 — <100 ugh
(1 — 420 ugh
3 — 7600 ugh
<1 — <100 ugh
<1 — <100 ugh
<1 — 110 ugh
10 — 18,000 ugh
(1 — 100 ugh
<1 — <100 ugh
(1 — (100 ugh
<1 — (100 ugh
<1 — <100 3q11
<1 — (100 ugh
<1 — (100 ugh
(1 — <370 ugh
(i — <100 ugh
<1 — (100 ugh
<1 — (100 ugh
<1 — <100 ugh
<1 — <100 ugh
<1 — <100 ugh
<1 — <100 ugh
4— thy1—2
pentanone (flmfl
(1 eq/i
NOTE: WL below aethod detection Unit
u .icro
Thioride
(10 - 240
ag/i
Fluoride
<1 - 87
ag/i
Nitrate (N)
l — 240
ag/i
(1 —
<1 —
(1 —
(1 —
<1 —
<100 ugh
<100 ugh
<100 ugh
<100 ugh
540 ugh
Nethyleae ChLoride -
Trtch lorof luoroaethane
1,1—Dichioroethylene -
1,l-Dicb loieethane
Trans-i ,2-Dicb1orethea
Ch ioretore.,
1 ,2-Dict proetbane
1. l-Tri 1oraethane
as oñ!.tra oride
0.1 - 0.04 ag/i
<.05 — 2.5 ag/i -=- .
(.05 - 150 agI )i - . .— , .\ 1,2 Dicbloropropaae
<.02 - 0.22.gV -=-Cfs-L,3-Dicbloropropene
<.0 1 - 0.06 sq/r-- broeocb1oroaeth1fle
1,1 ,2-Tri ieroethane
<1
(.2 - 3 pC13’i
<4 pCi/i
6—8
-------
CURRENT SITUATION SUMMARY
Revision 4
October 1988
SURFACE WATER QUALITY MONITORING
FARM SITE
Monitoring of the drainage ditch north of the Farm Ponds,
designated as East Boundary (upgradient), West Boundary (dow—
ngradient) , and Railroad Culvert (downgradient) , was started
in June 1984, continued quarterly through March 1987, and
included the following parameters: n1trate—IT3 trOgen, total
dissolved solids, conductivity, chloride, calcium, and sul-
fate. Table 6—7 swnxnarizes Farm site-s zface water quality.
Table
SCRFA 2 CIT . Q &LITY
-
Cou iti etiO -
Concentration
Range
Paraneter
-- it- 950 eq/i SuUate
1O —2,200 egli Conductivity
Dissolved Solids
21 — 670 eq/i
236 - 2.900 uahos/c
140—4,500 eq/I
Calcit
Chloride
Nitrate (N)
<3- 6.8 eq/i total
— --
NOTE: u = ei o
PLANT SITE
Routine monitoring of Truax Creek is conducted weekly for
anonia, nitrate, and total organic carbon as required by
the NPDES permit. Monitoring locations include upgradient
and downgradient of the Pond 2 weir on Truax Creek and near
the confluence of Truax Creek with Murder Creek. Table 6-8
sununarizes surface water quality at the Plant site.
6—9
-------
Table 6-8
5 FAC! WAT QOALITY
PLANT srit
CURRENT s:TUAT:oN STTh! .ARY
Rev3.si.on 4
October 1988
Parameter
Ca1ci
Magnesium
Aon a (N)
Chloride
Nitrate (N)
Sulfate
miocyanate
Conductivity
pM
Total Dissolved
Solids
Copper .O
Iron .3
Manganese .b
Nicksi
Bari
Cadu.ti
Lead
Methyl Iso atyl
Retone
Total Organic
Carbon
Total Susp ided
Solids
13 — 680 mg/i
4 — 91 mg/i
<.5 — 9.8 mg/i
<10 — 1,300 mg/i
<1 — 16 mg/i
<10 - 450 mg/i
‘2 — 4 mg/i
190 - 3,930 bos/
6.6 7.2
86 — 2,900 eq/i
0.01 - 0.03 mg/i
<.05 — 0.5 eq/i
<.05 — 1.2 mg/i
<.02 e q/i -
<1mg/i -—
<.003 mg/i
<.02 mg/J. ._
<1. mg/ I :
< t4 ag/i
8 - %. eg/i
1,1,1 -Trithloroethane
1,1,2 ,2—Tetracbloroethane
1,1-Dichioroethane
1 ,2-Oicblorcbeflzefle
1 ,2—Dicbloroethane - -
1 ,l-Dichloroetheme -
1 ,2-Dichloroptop e
1 ,3—Dich1or enzene -
1, 4-DicniorebenZene
3roaodicorm, ne
Broeofom
thane
- aon ?etra oride
Ch1or nt
hIe cbenzene
Tricb loroethene
Trichierofluoromethane
<1 — 23 ugh
<2 — 3 ugh
<1 — 7 ugh
<1 ugh
<1 — 7 ugh
‘1 — 4 ug/1
1 ugh
(1 ugh
<1 ugh
<1—lug/i
<1 ugh
<1 ug/1
(1 ugh
(.02 ug/i
(1 ug/i
<1 — 4 ugh
‘1 — 6 ugh
<1 ug/1
‘1 ug/1
<3 ug/1
<2 ug/i
<1 — 4 ugh
<1 ug/l
11 — 140 ugh
<1 — 2.0 ugh
<1 — 3 ugh
<1 ugh
Cooeentrat Ofl
DaramoP or
Concentrat i
anoe
-=ethane
=
loromethane
CIS-1,3-DtchloroproPefle
Dthro.ocb loro methafle
DicblorodifluorOeethafle
fluoranthene
Methyleme loride
Naptha le ne
Tra -l ,2-Dicbioroethene
PETE: a micro
Truax and I irder Creeks
6—10
-------
FARM SITE
CURRENT SITUATION SCM.M.ARY
Revision 4
October 1988
SOLIDS CHARACTERI ZATION
The farm site contains four solids ponds denoted as Ponds 1,
2, 3, and 4. Sampling was conducted in 1980, 1983, 1985,
1986, and 1987. Samples were analyzed for total metals and
inorganic compounds, Extraction Procedure (toxic) for
metals, inorganics, and radiological compounds. A summary
showing ponds sampled and analyses performed for each year
is in the site chronology. Table 6—9 summarizes the chemical
quality of the farm site solids.
Table 6-9
SOLIDS cJwrT IZATI l
FA I SITE
a dry weigbt basis.
Parameter
ConcentratiOn
Rance
Calcium
Magnesium
Carbonate
chloride
Fluoride
Sulfate
A lumizni m
Ant i mony
Carbon
Copper
Iron
KtcXel
Silica
Titanium
Zinc
Concentration
Range
16 - 22%
0.24 - 0.59%
0.72 — 6.0%
1 - 2%
0.6 - 5.2%
5.4 • 11%
1.2 — 2.4%
550 - 540 ppm
5.05 - 5.26%
510 - 360 ppe
4.9 - 19%
80 — 450 ppm
6.9 — 11%
3.0 - 4.4%
96 - 220 ppm
Radium—226
Thorium
1.1 — 7.9 pCi/gm
14 - 91 ppm
Uranium
200 - 610 ppm
Zircon lumJHafniUm
14.6 - 36.4%
Arsenic
15 - 58 ppm
1 COO
BarIum
Ca .iu m
Chromium
200
§10 - § 0 ppm
73 — 610 ppm
Lead
63 — 180 ppm
flercury
5.3 — §1 ppm
Silver
§5 — §50 ppm
4ote: Concentratioom are on
6—11
-------
CURRENT SITUATION SU 2tARY
Revision 4
October 1988
PLAN 1’ SITE
Samples were collected arid analyzed from the LRSP during
April 1978, April 1979, April 1982, April 1985, January 1986,
April 1986, August 1986, and September 1986. Samples were
collected and analyzed from Schmidt Lake in March 1979,
April 1979, and February 1987. Table 6—10 summarizes the
chemical quality of the LRSP and Schmidt lake lime solids.
Samples from the V—2 pond were collected, and analyzed in
January 1987. Table 6—11 summarizes the chemical quality of
the V-2 pond solids.
AIR tJLITY t4ONITORING
Since 1967, ai giia1ity monitoring has been in effect and
1. , -
Teledyne Wah Chang l any has been operating under Air Con-
taminant Discharge permits. Extensive area and point source
studies have been conducted relative to radon emanation and
radionuclide dispersion near the Lower River Solids Pond
(LRSP), Schmidt Lake (SL), and the Farm Pond Area (Scientific
Applications, Inc., 1980, and Battelle Pacific Northwest
Laboratories, 1985, 1986).
The Battelle report concludes that the average annual release
of radon and particulates from the lime solid wastes will
6—12
-------
CURRENT STUATION SUMMARY
Revision 4
October 1988
meet the air radioactive material pathway exemption criteria
of OAR, Section 345—50-035. Over a 10—month period, the
TWC.A site boundary at five locations had an average radon
concentration of 0.26 pCi/i. This value is close to the
Table 6—10
SOLIDS CHARACT IZATION
LRSP AND SO IDT LAKE
Concentrat o
Range
Calcium
Magnesium
Potassium
Sodium
Arsenic
B a.riua
Cadmium
Chromium
Lead
Mer y
Silver
Aluminum
Antimony
Copper
Iron
Manganese
Nickel
Niobium
Selenium
Silica
Tantalum
Titanium
Vanadium
Zinc
Zirconium amd
Hafnium (0)
5 — 15.9%
0.029 — 2%
0.02 — 0.58%
0.05 — 19,900 ppm
8 — 51 ppm
<200 - 400 ppm
<1 — 100 ppm
150 — 2,600 ppm
87 - 520 ppm
<.5 - 4 ppm
<.5 — <50 ppm
0.2 - 10%
<100 ppm
72 — 630 ppm
0.005 — 5%
0.015 — 0.58%
0.075 — 1,100 ppm
<.013 — 0.32%
<1 — <5 ppm
1.5 — 22.3%
<.01 — 0.7%
<100 — 250 ppm
400 - 700 ppm
54 - 270 ppm
S - 27.0%
Chloride
fluoride
Sulfate
Carbon
Nitroqen
Radium—226
Thorium
Uranium
1,1, 1-Trinbioroethane
1, l—Dtchloroethane
2—Hexanone
2-Methy lnapbtha lene
Acenapthene
Acetone
Hexacblorobenzene
Hexachiorobutadiene
Hexacmioroethane
Methylene Chloride
Phenanthrene
Cb lorobenzene
Chloroform
Dichioroethene
Tetrachioroethene
Other Volatile &
Senivolati le Organics
0.17 — 8.3%
0.099 - 13%
0.66 — 10.2%
0.35 — 15.3%
5,500 - 23,000 ppm
1.25 — 89 pC fge
0.006 - 0.029%
0.018 - 0.49%
(1 - 18 pb
<1 - 15 ppb
<10 - 250 pph
ND — <30 ;;b
<30 ppb
(10 - 17 ppb
4,500 - 5,000 ;pb
<30 ppb
<30 ppb
S - 39 ppb
<30 ppb
4.5 — 14.4 ;pb
(1 — 6 ;pb
(1 ppb
<1 - 4 p
ND
Note: ND = Not Detected
Concentrations are on a dry weight basis.
P r& t r
Concentration
Range
P.raflPar
6—13
-------
CURRENT SITUATION SUMMARY
Revision 4
October 1988
Table 6-11
SOLIDS C RACT IZATION
V-2 ND
Concentrat .on Concentration
? arameter Range Parameter
Ant nony <1.0 ppm C lordane <10 ppb
Copper 0.03 - 0.06 ppm C loroform ND—20 ppb
J cke1 0.39 - 4.43 ppm
Seleni <.05 ppm Di-t4-Sutyl Phthalate 376—962 ppb
Zinc 0.095 - 0.623 ppm Dicasba <100 ppm
Arsenic <0.05 ppm Die ldrin <.5 ppb
Barium <.05 - 0.132 ppm !ndosufan 1 <.5 ppb
Cad m.i um <.002 - 0.033 ppm Endosulfan II <.5 ;pb
Chromium <.005 - 0.009 ppm Endonilfan Sulfate <.5 ppb
Lead 0.018 - 0.06 ppm
Silver <.005 - 0.007 ppm Endrmn <.5 ppb
Rad.tu m—226 1.2 - 120 pCi/gm Endrin aldebyde <.5 ppb
Thor . u m 2 - 619 ppm Fluoranthene ND-499 ppb
Uranium 55 — 3,509 ppm Heptachior <.5 ppb
Tba llum <1 ppm Heptachior Epoxide <.5 ppb
2,4,5—TP <100 ppm
2,4—0 <100 ppm Mexach loroben:ene ND- 12.426 ppb
4,4-DOD <.5 ppb Lindane <.5 ppb
4,4-DOT <.5 ppb (ethoxyc 1or <1 ppb
Methyl Isobutyl Ketone 25 — 143 ppm ethy1ene Chloride 28 — 66 ppb
<10 ppb
Acetone 549 — 2,020 ppb
Aidrin <.5 ppb Pyrene ND-505 pph
B—BHC <.5 ppb Toluene ND-B ppb
a-BNC <.5 ppb loxaphene <50 ppb
d-BMC <.5 ppb Tri 1oroetbene ND—4 ppb
Benzo (K) Fluoranthene ND - 439 ppb Vinyl Acetate ND—213 ppb
Bis-2-(ethylbexy 1) Xylenes (0&II) ND—20 ppb
Phthalate 633 — 1,598 p
Carbon Disulfide 181 — 802 ppb
NOTE: ND = not detected
Concentrations are on a dry veight basis.
6—14
-------
RevisiOn 4
October 1988
radon concentration measured at eight background locations
(0.21 pCi/I). The data show that radon released from the
LRSP and SL is diluted to background levels at the site
boundary, and is only slightly elevated above background
levels on the banks of the LRSP. A MILDOS computer program,
developed for the U.S. Nuclear Regulatory Commission, was
selected to calculate maximum airborne particulate activity
adjacent to the LRSP and SL. Results are..shown in Table 6-12.
Table 6-12
cU.CUIJ .T UPP LINIT A TTI
C PAP WITH 0 P )1S 3QO35 V 0
—
Rad1o uc1ide 238 234 239 r 2.22 210 p 210 j 210 p
Concentration. -
2 3.3x10 2 4 200 7
LRSP 5x10 3 31 3x10 3 6x10 3 6x10 3 6 l0
Se idt Lake 4 10 4i -,2x1O i ô 3 8z10 5z10 SxL0 5x10 3
z== .
\
Airborne-partic 1a studies by Scientific Applications,
Inc., indicated tht.-r detectable concentration of alpha
emitters existed, and that the air pathway is considered
unimportant as a means of radionuclide transport. TWCA estab-
lished a monitoring program in July 1978 to quantify gaxmna
levels at the site boundaries and selected areas within the
facility. The data are shown in Tables 6—13 and 6—14. All
levels are below the limits specified by the U.S. Nuclear
Regulatory Commission.
6—15
-------
CURRENT SITUATION SU! 21ARY
Revis .on 4
October 1988
Table 6—13
PLANT PERIMETER MONITORINC--QUARTERLY BASIS
PENETRATINC/NONPENTRATING
7/01/87— 4/01/87— 1/01/87— 7/01/78— 10/01/78—
________ 9/30/87 6/30/87 3/31/87 9/30/78 12/31/78
1. rn/rn rn/rn rn/rn rn/rn 10/rn
2 rn/rn rn/rn rn/rn rn/rn rn/rn
4 rn/rn rn/rn ——- rn/rn rn/rn
6 rn/rn rn/rn rn/rn rnlrn rn/rn
7 rn/rn rn/rn rn/rn rn/rn rn/rn
8 rn/rn rn/rn rn/rn a/rn 31/rn
13 rn/rn rn/rn rn/rn - - rn/rn rn/rn
15 rn/rn rn/rn rn/rn - - : rn/&- rn/rn
16 19/rn rn/rn rn/rn.. - rn/rn rn/rn
17 rn/rn rn/rn rn/rn rn/rn 13/rn
18 rn/rn rn/rn rn, - - rn/rn rn/rn
19 rn/rn rn/rn - rn/rn rn/rn rn/rn
23 rn/rn rn/rn rn/rn rn/rn rn/rn
24 rn/rn rn/rn - Jth — - - rn/rn 10/rn
31 rn/rn rn/rn - rn4 1 rn/rn rn/rn
33 rn/rn rn/ r n - -rn/,rn - rn/rn 12/rn
34 rn/rn frn .- - — rn/rn rn/rn 18/rn
aS tes located throughout rnLfrp1ant’— Pte.
Notes: 1. Accepta 1 9 .AmitS5peCified by the U.S. Nuclear Regulatory
CornLs .on. -
Whole : h11250 rn.Llllrern.
-
2. rn—below asurable detect .on
3. date expressed as rn .ll .rern units.
6—16
k
-------
CURRENT SITUATION StTh2tARY
Revision 4
October 1988
The Farm Ponds contain lime solids generated after a mayor
process change that lowered the radionuclide levels vis—a—v].s
the material, in LRSP and Schmidt Lake. The radium content
is approximately 5 pCi/g, compared to a median value of about
40 pCilg for Schmidt Lake and the LRSP. The lower radium
content equates to a marked reduction in radon emanation.
Consecuently, the Farm Pond solids should pose no risk or
threat to the public health and welfare, or to the environ-
ment. -
Current monitoring programs conducte&puSUant to Air Contami-
nant Discharge Permit No. 22-O54i4 ave generated a significant
body of information on p].an .site -eUtiSSiOflS such as metals,
ammonia, chlorides, sulate—flUDrideS, sulfur dioxide,
carbon monoxide, n xou o ides r and particulates.
AREA AND POINT SO RCE STUDIES
Chlorides, Chlorine, and Ammonia
Ambient air measurements, which were supplied to the Oregon
Depar ent of Environmental Quality (DEQ), are typical of
the plant site and are presented in Tables 6—15 and 6—16.
6—18
I ’
-------
CURRENT SITUATION SU!2IARY
Revislorl 4
October 1988
Ta 1e 6—15
Anhient kir easureeents
January 1986
Period Nort La ss Sour
( ug/: ) ug/s ) ( ug/e )
Cl Cl Cl Cl N Cl Cl N !
___ 2 3 ____ 2 3 ___ 2 3
Jan. 2—9 <0.036 (0.014 0.002 <0.059 <0.024 0.017 <0.023 <0.009 ‘0.014
Jan. 9—16 <0.040 <0.016 <0.017 <0.066 <0.026 (0.015 <0.025 <0.010 <0.011
Jan. 16—23 <0.034 (0.014 (0.024 <0.042 <0.017 0.01.5 (0.036 (0.014 <0.010
Jan. 23—30 <0.041 <0.020 0.021 <0.050 ‘0.025 0.016 O.027 (0.013
aM l periods are in 1986. -
Notes: MeasureeefltS m e at the three sonitoring stations; eaSUree tS shown here a
average for the tine designated. - -- —
TLV—SAX, N. Irving, 3 4th Edition 1975
Chlorine: 3 ug/m
A onia: 18 ug/a - -
U = aicro -
b1e 6-1
Mbi 13z Neasigeeents
- Juar l987
Perioda Nort .__ Eas Sou h
( uq/ J • - (ug/ ) ( ;igie 3
Cl . C1 %C1 Cl 2 NH Cl 12 3
Jan. 2—7 (0.104
-------
Revision 4
October 1988
GENERAL
Event
Wah Chang Corporation began operation.
Plant site flooded to elevation of
approximately 209 feet above MSL.
Teledyne, Inc., purchased the plant from
Wah Chang Corporation.
Termination of zirconium carbide
production process. - - -
Installation and startup of sand chlorin-
ation process. -
TWCA placed on National Priorities List.
EPA (C. Fjfld R 1Ofl . X) made a Sec-
tion 104 CER LA egu St for environmental
data and=çadiat*Ofl studies conducted since
July 19
TWC a d EPA sgn Order on Consent Docket
r 02- t9- 106.
- — TW 3ub %.itted draft Work Plan for RIIFS.
!rWCA submitted revision No. 1 to draft
Wo .tk Plan for RI/FS.
Date
1957
Dec. 1964
May 1967
1969
1972
Dec. 1982
March 3, 1986
May 1987
Aug. 1987
Feb. 1988
7—2
-------
-------
Teledyne Wab Chang Mining Waste NPL Site Summary Report
Reference 2
Excerpts From Decision Summary, Interim Response Action,
Operable Unit 1; EPA; 1989
-------
I . ’
-------
DECISION SU1? ARY ____
TZ4-C1O uc 4 4 .
INTERIM RESPONSE ACTION / ‘ I
OPERABLE UNIT #1
j
SITE NAME
:-,.uc T s
Teledyne Wah Chang Albany (TWCA), Albany. Oregon
LOCATION AND DESCRIPTION
The Teledyne Wah Chang Albany facility is located in Millersburg. Oregon
(about three miles north of Albany) in the Willamette Valley (see Figure 1)
The Superfund site includes the 110 acre plant site property and the 115 acre
facility known as the “farm site”, which has the plant’s wastewater treatment
ponds (“Farm Ponds’) and is located approximately .A e mile north of the plant
site. Operable Unit #1. the unit addressed by this Interim Action, includes
the solids in the Lower River Solids Pond and Schmidt Lake.
f .l
Of the two major site areas, the plant site contains numerous buildings
and facilities including an extraction area south of Truax Creek. a
fabrication area north of Truax Creek. a solids storage area west of the
Burlington Northern Railroad. and a parking and recreation area east of the
Southern Pacific Railroad The farm site is 3/4 of a mile north of the plant
site and contains five 2—1/2 acre solids storage ponds The remainder of the
site is used primarily for agriculture Over 1300 people are employed at the
TWCA plant, making it the largest employer in the Albany area
The Lower River Solids Pond (LRSP) and Schmidt Lake are the two sludge
ponds addressed by this Record of Decision They lie in the western portion
-------
The immediate area surrounding TWCA is primarily industrial, with some
land to the north being used for agriculture The land east of Interstate S
and south of the plant site is used mainly for residential and commercial
purposes. while land west of the Willamette River, which borders the plant
site, is used for farming Albany. the urban area to the south of the site,
has a population of approximately 27.000: Millersburg has a population of
about 560
There are about 250 known private drinking water wells within three miles
of the facility, all of these wells are upgradient of the site There are no
known domestic, municipal, industrial, or irrigation wells located between the
site and the Willamette River The Willamette River is not used as a drinking
water source in this area
SITE HISTORY AND ENFORCEMENT ACTIVITIES
Site History
Operations at the TWCA site began in 1956 when, under contract with the
U S Atomic Energy Commission, Wah Chang Corporation reopened the U S Bureau
of riines : 3 irconium Metal Sponge Pilot Plant. Construction of new facilities
at the site of the existing plant began in 1957. These facilities were buiLt
primarily for the production of zirconium and hafnium sponge However.
tantalum and niobium pilot facilities were also included. Melting and
fabrication operations were added in 1959 Teledyne Wah Chang Albany was
established in 1967 after Teledyne Industries, Inc , purchased Wah Chang
Corporation of New York. In 1971 the plant became a separate corporati
Teledyne Wah Chang Albany
-------
Because of the many processes involved in production of nonferrous metals
and products, waste management programs at TWCA consist of a wide range of
activities, including Process wastewater treatment, solid waste management
hazardous waste management, PCB equipment management, radioactive material
control, waste minimization through beneficial use, and air quality control
programs Discharge of process wastewater is regulated by an NPOES permit
An Air Contaminant Discharge Permit regulates emissions at the facility
Teledyne is currently classified as a hazardous waste generator under the
Resource Conservation and Recovery Act (RCRA) program
The LRSP was constructed and placed into operation in 1967 to receive
lime solids (sludge) from TWCA’s onsite wastewater treatment plant, Schmidt
Lake was constructed for the same purpose in 1974 Sludge was pumped into the
two ponds until October 1979 when the farm ponds to the north of the facility
were put into operation The farm ponds were originally part of this operable
unit, but because they are outside the flood plain and are not considered an
immediate threat, they are now being investigated as part of the overall site
RI The sludge in both the LRSP and Schmidt Lake contains metals, a few
organic compounds, and trace levels of some radionuclides, Tables - L4
present a su nary of the contaminants found in the sludge.
In 1978, ThCA modified the process for the production of zirconium and
hafnium metal. The process modification directed the radioactive materials
into a .ieparate solid waste referred to as chlorinator residue This residue
3
.
-------
is managed as a low specific activity radioactive waste and shipped to
Hanford. Washington. for disposal Sludge generated since the implementation
of this modification has been stored in the farm ponds
Enforcement History
The sludge ponds have attracted the attention of regulatory agencies and
the public for many years. particularly because of the presence of radioactive
materials, which was first confirmed by the Oregon State Health Division in
1977 In March 1978, TWCA was granted a Radioactive Materials License to
transfer, receive, possess, and use zircon sands and industrial byproducts
containing licensable concentrations of radioactive materials TWCA took
samples from the ponds on sev’ral occasions in 1979 and 1980 In 1981. the
company applied to the Energy Facility Siting Council (EFSC) for a site
certificate to close LRSP. the next year. they made another application to
store approximately 120,000 cubic yards of lime solids The site was listed
on the National Priorities List (NPL) in October 1983 After several years of
hearings, court actions, and further sampling, EFSC ruled in 1987 that the
sludge was not subject to their jurisdiction, the levels of radioactivity
being too low. TWCA then submitted a closure plan to the Oregon State Health
Division, but EPA arid other agencies recommended that closure not take place
until after the conclusion of the RI Meanwhile, the site had been listed on -
the National Priorities List in 1983, and on May 4, 1987, TWCA had signed a
Consent Order agreeing to conduct the RI/FS.
The TWCA facility hu d p ’rrnits for water arid air emissions It was
found in violation of discharge permits in 1975, 1977, and 1978,
subsequent process chantje rt’dui d the toxicity of the facilitys wastewater
discharges TWCA was s s’ss d fines for other water quality permit violations
in 1979, 1980 and 1989 The company was fined for illegal open burning in
-------
Teledyne Wah Chang Mining Waste NPL Site Summary Report
Reference 3
Excerpts From SAIC Report, Data Validation for Work Assignment C10005,
Teledyne Wah Chang Albany, DCN: TZ4-C1000S-DV-02775;
SAIC; 1990
C ,’
-------
INTER-OFHCE MEMO
TZ4—C10005—DV—02 775
r r’ ‘;1
€ S ice Thtemah iaIC po’atice I- ’ — V
MAR 0 990
DATE March 1, 1990
-, Nic
TO Tom Tobin FROM Paul Mills
a-
SUBJECT: SAIC Report, Data Validation Work Assignment C10005, Teledyne Wah Cheng
Attached is a suary of the data validation performed on the data from EPA’s
Case 1 /12741. Metals, volatiles and base—neutral/acid organics by CC/MS. and
organochlorine pesticides and PCBs by CC were reviewed, using the EPA’s CLP
data validation guidelines (1988) to evaluate the completeness and compliance
with contract requirements.
The original data you provided us was copied and distributed to specialists
in the SAIC Environmental Chemistry Laboratory Division. Ray Martrano, CC/MS
Section Manager; Steve Glover, CC Section Manager; and Leta Thomsen, Metals
Section QC Specialist, performed the validations of their portions of the
data. I have enclosed their suaries as attachments behind my own. Additional
suoporting data for GC/MS, such as checklists, etc. is also included. We
will mail back the original data to you under separate cover. We will
maintain our copies in case there questions, until you have authorized us to
either dispose of them or send the copies back to you.
The hours charged by the reviewers are as follows:
Ray Martrano = 18 hours
Steve Clover = 14 hours
Leta Thomsen = 25.5 hours
57.5
There will probably some secretary time thrown in for typing Ray’s report.
I’ll charge my time to TES QA numbers, for oversight/auditing of lab work here,
since I think this is appropriate.
If you have any questions, please call me, (619)—535—7493
At ta c hnien t s
-------
soil matrix, and the standard should be analyzed under the same conditions as
samples. It is possible that the reported values for these samples are somewhat
high; “hot purge standards may have produced a larger response, against which
the samples’ responses would not have generated as high concentrations
Due to surrogate recoveries and spiking errors, several samples required re-
extraction for BNAs. These were re-extracted beyond the specified holding time
for extractions; since surrogate and matrix spike recoveries on the re-extracts
were acceptable, no significant data impact is noted. Where insufficient sample
volumes remained for re-extraction with full volumes of samples, 500 ml aliquots
were used, which would require an increase in reported detection limits by a
factor of 2, since usually 1000 ml are used.
Several non-criteria compounds showed a high RSD in calibration runs Jhile
contractually compliant, the data user is advised to note that samples containing
“hits” of these compounds may be considered estimated concentrations See the
tables attached to the CC/MS review section for details concerning which samples,
calibrations, and compounds are affected.
Several spectra of hits in these samples were judged by the SAIC reviewer to be
poor fits, i.e., not meeting the CLP-specified criteria for matches. These are
mostly very low-level (lower than contract required reporting limits) compounds
which the lab has self-reported as estimated, using the “J” data qualifier. See
the associated table in Section IX of the GC/MS review for details. If these
compounds from these samples are of concern, it is recommended that alternate
methods by used to identify and quantitate them (e.g.. GCs for volatile analysis
can more accurately measure low levels)
ORGANOCHLORINE PESTICIDES / PCBs
Several samples exceeded the extraction holding time when they were re-extracted
Re-extraction was required due to incorrect surrogate spike amounts. Original
results of initial extractions of these samples show the presence of PCB5 and
it is unlikely PCBs degraded in the few days after holding times expired The
data for the re-extracted samples should be qualified as “estimated” JFOG9RE,
JFO69MSRE. JFO69MSDRE.
JFO76MS and JFO76MSD aqueous spiked samples were extracted beyond the holding
time; since no compounds were found above reporting limits in the original sample
which met holding times, there is no significant impact on data quality
Although contract-required confirmation criteria were not met, the second-column
confirmation runs did show the PCB patterns which in the chemist’s judgment
confirmed the presence of PCBs
A method blank showed below-reporting limit levels of PCB-1260. no associated
samples showed this PCB at any detectable level It was judged a laboratory
contaminant, and no qualification of data from samples was noted.
Soil sample matrix spike/matrix duplicate recoveries on the re-extracted samples
exceeded the advisory control limits, probably due to the interferences from PCB5
in the native sample. There is not significant impact on data quality.
2
-------
SAIC’S data reviewer believes that the pattern(s) reported by the original CC
chemist as PCB-1248 and pcB-12 54 are all pCB-1248. Since identification is made
using several peaks common to both Aroclors, there could be some later -eluting
peaks of 1248 which may be interpreted to represent PCB-125 4 . The quantitatiOfl
of PCB-1248 uses ljer elUting peaks than PCB-1254 does, so the actual values
reported would not be changed much (perhaps 25 percent) if the Aroclors present
are considered all 1248 instead of a mixture. If total PCBs are of concern,
rather than amounts of specific isomers, there should be no impact from this
differing interpretation PCBs were detected in CC/MS runs of these samples,
but SAIC’s CC/MS data reviewer was unable to determine whether PCB-1248 and PCB-
1254 were both present
3
-------
Teledyne Wah Chang Mining Waste NPL Site Summary Report
Reference 4
Excerpts From Potential Hazardous Waste Site,
Site Inspection Report for Teledyne Wah Chang, Albany, Oregon;
EPA; 1982
-------
Vfl ST RELAT O INFORMATION (ce ”t. ’ .ed)
25 e (3pecI’) ( me.s ) of .sle b) Category fltark X to ,ndici le .ch •65 1e5 are present
SLUOCE
S OIL
C SOLVCWTS
4 CNCMICALS
• SOLIDS
I 07(O
0UNT
a—Ou,r
a—O
UN,
£
—OuST
). OUST
1106,000
uNIT QC C SUS( j T or sc.suo(
.,r .T Of ( 5 ,.,°C
UNIT OC —CASUR(
SIT 0 ’ CAS ,JNC
or ..C 5_,6c —
ubic yards
,,“.“
O i.’ r I.OC(sT(O
O — (.P.c.1y)
21 OTCP’6POCIIY)
. ,. .cos
121 £30702
ISP CAUSTiCS 1)1
i PC 5 ? IC IDES
J2I 05 0 ,TL
I3IRAOIOACTl7(
31 OT
S
JI.I IJ•: ’C ID AL
: ‘o 7 Cmsp.cUy)
SPOT ( 5/i 5 5 -
(SI
J 15101 CR(.PACII,)
61 C TANOC -
IS) OT...Cm(.peeIty)
171 0 CNOLI
Iii N.t.OGC66S
I’ PCB
IICIMCT&LS
1111 OT sCA(SR.C II F)
O LIST SUBSTANCES or GREATEST CONCE
RN WHICS ARE ON YNE SITE (pI.c lit d..e.nd.nI O,4.r OS h.a.,d)
2. FORM
( ..h X )
I SUBSTANCE
1.10 1.0. 0N
3 TOXICITY
(o..rk X)
4 cAS WUMB(R
S AMOUNT 6 WIlT
6.
— .0..
b
UCO
L0
— ——
• Ol.I
Radium chloride
X
X
None
Radon gas
X
X
None
Uranium
X
X
X
None
Thorium
X
X
None
VIU. HAZARD DESCRIPTION
UIJM&N NEALYM MAZAROS -
Radon gas is a serious threat to workers
In the event of a small flood these would be widespread contamination by radioactive
wastes
Land use must be restricted for thousands of years due to radioactive waste
A.
B.
C.
FIELD EVALUATION PIAZARO DESCRIPTION Place an a the boa to uid,caie that the lisied hazard ezisis Describe the
hazard in the space presided. - __________________________________
-------
I VIU HAZARD OESCRIPT ON
r wO ...Cpv u
Unknown
c INJURY/EXPOSURE
Several citations have been issued.
A. Fatality: anhydrous armnonia exploded, blasted and burned worker.
B March 17, 1976, Citation. HCI exposure
C. Sept., 1975. Citation. Rupture and explosion of titanium tetrachioride and
inhalation, 2nd degree burns.
0. C0MTAMIN*T,O OF WAT R SUPPlY
Possible. Many domestic wells in the area in the aquifer of concern. Need to
sample these wells.
C. CONTAMINATtOw or FOOD CHAIN
Food chain crops grown on land spread with radioactive wastes.
F CONTA I .ATION Or GROUND WATER
Wells sampled show 10 of 13 wells had elevated levels of radium chloride and
3 wells exceeded legal levels. Radium chloride levels at 6 p iCu found in
40 feet test well.
G CONTAMINATION OF SURFACE WATER
Sampling at Truax Creek shows higher radionuclide concentrations attributable
to TWCA plant.
PA r.. 2 ii:
ACZ O IC
-------
UI AZARP O SCRIPTlON (Continued )
O AG( OcLORA/FAUHA
Unknown
I
FISi KILL
Unknown
.1
COMTA IWATIOH OF AIR
Radon gas emission from sludge lagoons.
NOTIC A9LE ODORS
None
L
COPdTAMI IATIOH OF SOIL
Landspreading of radioactive wastes.
M
PROP RTY OA AGE
Land use greatly restricted
-------
c—’” a F,o,, Pare 6
_______________________________ / 111 I . &ZARO OESCRIPTIOP (cont,n. e )
[ j N. ruR OR EXPLOSION
Several explosions due to magnesium and zirconium.
0 SPILI / * ,,4 CONTAINER5/RUNOrF/STAW OINQ LIQUID
Chlorinator residues. Ordered to clean up in 1977. No other spills or
hot spots the Health Department is aware of.
P. SEWER STORM DRAIN PROBLEMS
Discharged radioactive materials to sewer but nothing detected in excess of
State standards.
0 EROSION PROBLEMS
Water leaching through dikes in past. Not felt to exist at present. Dikes
made of rip-rap, not lined.
Lx i R INADEQUATE SECURITY
Not fenced on river. Rest of site is fenced. Ponds not under constant guard.
Guard at gate.
5. INCOMPATIØ [ ASTES
A. Magnesium and zirconium
B. Radioactive substances
EPA Fe —.— 1:: —) (‘:—c
-------
vrn I.4AZARD DESCRIPTION ‘ron n.., d)
E P* Fo. T2070-3 o-7c)
0
PAGE 6 O O
ColIs,n ,e O, P. e 9
? MIDNIGI T OUNPING
None known
U OTHER (.p.cIl )
IX. POPULAT OW DIRECTLY AFFECTED BY SITE
A LCCATIOH Or POPuLATION
B APPROX NO.
OF PEOPlE AIFECT(O
C.*PPROX NO OF PEOPLE
AFFECTED wITHIN
us.? AREA
APOROX NO.
OF BUILDINGS
AFFECTED
£ DISTANCE
TO SITE
.p.c.S
“s.DY’A Rc 1
20,000
3 miles
‘ 5000
3 miles
ONHU3T I AL.. C A1
3,000
1 miles
‘ 1000
3 miles
0 ubL’Ct.t
AREAS
> 10,000
2 miles
> 1000
3 miles
U S C -
. .,
6 sbhools
1 n rk
2 mi ies
.
mi es
X WATER AND NYDROLOGICAL DATA
A DEPTH TO GROUNORATERI.p.cSI, II) B. DIRECTION oc ,Lo. C G OU DA E u IN VICINITY
WNW omestic 5 industrial
SU PLY
PQT N7IA YIELD OF AQUIFER E DISTANCE TO OPI ING .A(R SIJDPI..Y F DIRECTION TO DRIWNING
“ ‘ < 1 mi le all around site
C TYPE OF DRINKING A TEa SUPPLY
S IION.COWWuNITY 2 CO UNITY (P’ ’ ‘ ‘ Al banv, from the Santanium River
>ISCONWCCTIOWS (private domestic wells)
3 SURrACE ATER 4
-------
Conr,.n,e P,oi, PaOe I
X. WATER AP4D HYDROLOGICAL. DATA (cent ,n..ed)
H 1. 1ST ALL °IRI4G ATEO CLLS ITMIN A I/ I NIL S RADIUS O 5IT 5
CLL 2 OCDTH
(Cp.c.Iy (P’o..W 10 000..1 1r00./bNIIdIngl)
—
(See files and maps)
70
“
55’
1
-———
“
I Htç LIVnC. WA EN
S 3EWC05 ( J 3 STNCAI 0INCN3
Willamette and
Truax Creek LANC3lm(SC O ,., D
5 CC USC AHO C ASSIrICA y.0 O r NEC LIvING —. T(RS
Willamette is Class I water
X I. SOIL AND VEGITATION DATA
LOCATION OF SITE IS IN
A I NOWN FAULT ZONE 0 e KARET ZONE C. 100 YEAR FLOOD PLAIN 0 WETLAND
E. A REGULA1ED FLOODWAY 0 F. CRITICAL HABITAT RC I4ARGE zouc OR SOLE SOURCE AQUIFER
)CI. TYPE OF GEOLOGICAL MATERIAL OBSERVED
Mark X to snd ,c.te the type(s) of geo øgtc.1 stertai observed and speczty rtie,e necessary, the component parts.
t1 j. T .
A LVERBURDEN —1 9. BEDROCk (.p.c.l - b.Io—) C OTHER (.p.clly bale.)
I SArO J
X 2 CLAY
X 3 GWAVC
X I I I SOIL PERMEABILITY -
A UN’NCNW 0 S. VERY W10. (100.000.0 4000 cW/..C.) 0 C HICN(1000 1020 Cl. ./..c.)
0 ‘ODER*TE (40 to S c/..c.J C. LOS I to 001 0 F. VERY LOW (.001 •0 00001 e,/..c
C RECHARGE AREA
. YES 2. NO 3 COMMENTS.
DISCHARGE AREA
I YES 2 NO 3 CO (WTS Discharoe to nearby surgpce water bodies.
SLOPE
• £STIA YE CC SI.Q0( S SNCCIV • O’CC “C .. Of 3 1.00 5 CQ..OIT .Oto Or $LODC (YC.
0 02% SloDe is west towards Wiligmette River
I OT .4ER GEOLOGICAL DATA
Settina in an alluvial flood pla’n with lakes in abandoned meanders.
EPA F e. — 7C72 —3 (,C .’F)
PAGE 9 OF 10
Continue C— r..”ae
&
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C r u .! - — = -ont
X IV PERMIT INFORMATION
st all .pphcsble permits held by the site arid provide the ,elated inlorm .Uon.
A P 5QMI? TYP(
‘. a RCRA 5’. ..i%POES.. .a.)
B ISSuING
AGENCY
C P(PMIT
NUN BER
0 OATE
ISSUED
( n .e .day.Ayr)
C EXPINATSON
DATE
( 0- ).aF’•)
(n,s .h X)
r’cs
.?
:.. :N
RCRA
EPA
3-16—82
x
NPDES OR DEQ
0R10001112
1-4-78
7-31-81
X
SD
EPA
220547
x
XV PAST
REGULATORY OR ENFORCEMENT ACTIONS
NONE YES q.ira..r.a. in Shi• apse.)
1972 — 1979
Numerous failures to comply with NPDES permit requirements for one or more
pollutants.
Several citation from Oregon Accident Prevention Division.
NOTE Based on the information in Sections III through XV. fill out the Tentative Disposition (Section 1!) information
on the fi st page cf this forni.
EPA F..— I ? 7C .-3 ( 1049 )
PAGE IOOF to
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Teledyne Wab Chang Mining Waste NPL Site Summary Report
Reference 5
Excerpts From Review of CH2M Hill Work Plaits for Baseline Risk Assessment:
Human Health Evaluation and Environmental Evaluation,
Remedial InvestigationfFeasibility Study, Teledyne Wah Chang Albany,
DCN: rZ4-C10005-EP-H0773; Environmental Toxicology International Corporation; 1990
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10 EP Envfronmental
RECEIVED Toxicology
International. Inc
MEMORANDUM MAY?51990
To:
Pat Cirone, U.S. EPA
1
From:
Jeanne M. Funsdh, Eli
Date:
16 May 1990
Subject
Comments on the Teledyne Wah Chan
Plans
g Superfund Site Draft Work
This memo presents the comments on the Teledyne Wall Chang Superfund Site
Draft Work Plans for the Baseline Risk Assessment that were discussed by
Jeanne Funsdh (Eli). Bruce Duncan (EPA). and Pat Cirone (EPA) on 15 May
1990. The comments on the Environmental Evaluation are presented first,
followed by comments on the Htim n Health Evaluation.
nvlxoumental Evaluation
1) Using a h rd Index approach (Le., comparing estimated wildlife
exposures to water quality criteria or reference values from the scientific
literature) may not be a sufficiently-complete assesqmpiit of the potential
affects to the ecosystems present at the Teledyne site. This approach Is
useful for screening purposes, however. The results of this screening
may warrant ecarninatlon of certain cont rnIn ntq and/or exposure
pathways in more detail (e.g.. bloassays). A discussion of how the
screening would be Interpreted and used should be Included In the Work
Plan, Including the rationale for either eliminating contaminants from
further study or progressing to a more detailed analyses.
2) There Is a lack of basic site-specific Information In the Work Plan. A
conceptual site model Is needed that Includes a representation of critical
habitats and exposure pathways. Information on the species and habitat
types present on site Is also needed before any assessment strategies are
formulated.
flt,mai Health Evaluation
1) New EPA Region X guidance Is expected in appro dmately one month.
However, the guidance presented by Region X In January of 1991 Is more
Plaza 600 Bui1d g
Sigh and Stewart Suite 700
Seattie WA 98101 USA
Telephone (206) 441-6142
Facsimile (206) 443-1812
Tel 4947618 Ffl U1
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current than the guidance used in writing the Human Health Evaluation
Work Plan and therefore should be consulted at this time.
2) Information regarding the exposure scenarios (I.e.. residential, industrial,
etc.) and the exposure parameters to be used In the risk assessment
should have been submitted prior to the Work Plan (as Is outlined In the
Region X guidance Included as Attachment A of the Work Plan). Current
and future scenarios for both residential and Industrial qosures are
required by Region X guidance. Also, the separation of the site Into two
source areas should be addressed relative to the exposure scenarios.
3) A more Illustrative conceptual site model would complement a discussion
of exposure scenarios (I.e.. Instead of a flow chart). The geographic areas
of concern should be emphasized In this modeL For example. a depiction
that supports the elimination of exposure to soil as a pathway of concern
and the areas where workers are currently active would both be
appropriate.
4) AddItional risk estimates currently required under Region X guidance to
be Included In a Baseline Risk Assessment are risk reduction for each of
the remedial alternatives selected for detailed review and estimates of
risks that may occur during remedial actions. Remedial action goals
should also be discussed In the Baseline Risk Assessment (I.e., will
cleanup levels be based on established criteria or risk-based
concentrations). None of these topics Is currently addressed in the Work
Plan. These Issues were apparently not addressed In the guidance
included as Attachment A to the Work Plan. Parts B and C of the Risk
Asseqqrnerit Guidance for Superfund under development by the EPA will
discuss these topics in more detail. Until these documents are finalized.
EPA Region X should be consulted.
5) RIsk-based detection limits should be used In the P.1/FS process.
6) The Uncertainty Section was missing In the Baseline Risk Assessment
Process outlined In the Work Plan on page 1-6. ThIs section Is discussed
later In the document (page 5-1). but should also Include discussions of
the following: uncertainty In the sampling and analysis procedures.
differences In the absorption of contrnnffi rits, the degradation of
contaminants to more or less to c compounds. dermal exposure
uncertainties, and the chemical form of the contaminants that Is
expected on site (I.e.. trivalent or hexavalent chromium).
7) Including the results of Phase I sampling In the Work Plan would be
appropriate, particularly If only these data will be used In the risk
assessment
8) Plates 2 and 3 are missing from the Work Plans.
cc: John Kane (SA1C)
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Teledyne Wah Chang Mining Waste NPL Site Summary Report
Reference 6
Excerpts From Technical Memorandum Concerning Fall 1989 Sampling Activities,
DCN: TZ4-C1000S-EP-00568; From Thomas A. Tobin, SAIC, to
Neil Thomp6on, EPA; Undated
-------
DCN : TZ4 - EP-C 10005 -00568
TECHNICAL MEMORANDUM
EPA Contract No. 68-W9-0008, WA No. C10005
Teledyne Wah Chang Albany RI/FS Oversight
September/October 1989
1.0 Introduction
From September 19 through October 18. 1989 SAIC provided technical oversight
for the Phase I Remedial Investigat .on (RI) sediment, surface water, and
ground water sampling effort at the Teledyne Wah Chang (TWCA) facility near
Albany, Oregon. The RI, conducted by TWCA’s consultant CH2M Hill of
Corvallis, Oregon, will assess the presence and extent of chemical
contaminants in ground water, sediment, and surface water in and around the
TWCA facility. From September 19 through September 29 SAIC provided oversight
jointly with the TES-4 contractor, Tetra Tech, Inc.
Tetra Tech provided primary oversight of TWCA’s RI sampling activities during
the first week of sampling with SAIC in a support role. Conversely, SAIC
provided primary oversight during the second week with Tetra Tech in a support
role. SAIC alone provided oversight during the remaining three weeks. SAIC
provided one field engineer during the initial week of sampling to makeup the
two person team. During the second and subsequent weeks of oversight, SAIC
provided two field personnel to provide full time oversight of TWCA’s sampling
procedures.
SAIC documented CH2M Hill’s sampling activities and collected duplicate
sediment, surface water, and ground water samples concurrently with CH211 Hill
as described in SAIC’s Sampling and Analysis Plan (SAIC SAP, 1989) and Quality
Assurance Project Plan (SAIC QAPjP, 1989). SAIC directly observed the
sampling of approximately 80 percent of the ground water monitoring wells and
obtained duplicated samples from approximately 10 percent of CH2M Hill’s
sampling sites. Table 1 summarizes all duplicate samples collected by SAIC
and their corresponding traffic report numbers. Table 2 summarizes SAIC’s
sampling oversight activities and provides additional information applicable
to each sample station. Appendix A contains annotated photographs and
associated documentation of sampling activities.
Duplicate samples collected by SAIC are currently being analyzed by process
laboratories under contract to EPA using EPA Contract Laboratory Program (CLP)
protocols. When available, validated results will be submitted under separate
cover.
2.0 Weekly Activities and Observed Deviations
Following is a week-by-week description of SAIC’s sampling and oversight
activities. Deviations to CH2M Hill’s Field Sampling Plan (CR214 Hill FSP,
1988) or SAIC’s SAP, and subsequent consequences, are provided. Except where
noted, CH2M Hill. followed sampling procedures outlined in their Field Sampling
Plan.
1
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Se; -‘ber 19-21. 1989
Week 1 Activities
Robert Brockhaus (SAIC) and Kurt Schineirer (Tetra Tech) oversaw Week I
surface water and sediment sampling activities. SAIC collected duplicate
samples at Truax Creek sampling stations TC-5, TC-6 and at the Murder Creek
sampling station, MTC-l. SAIC also prepared two Quality Control (QC) samples
-- a field replicate sample (designated TC-9) collected at sample station TC-
5 and a transfer blank sample (designated TB-i) collected at sample station
MTC-]. (Table 1).
Week I Work Plan Deviations and Consequences
1 SAIC proposed collecting a sediment sample at station MTC-l. Only surface
water was collected at sample station MTC-l, however because SAIC did
not at the time have a sufficient number of sediment sample containers.
This inadequacy was caused solely because some of the sediment sample
containers had broken in transit from the glassware supplier. Able to
obtain CLP-clean sediment sample containers from CR211 Hill, SAIC instead
collected a sediment sample at station TC-6.
Consequences : Since all CLP glassware follows a stringent cleaning
protocol, the use of cR211 Hill’s glassware is not expected to affect
QA review of sediment sampling results. There is no consequential
change to the level of QA review by substituting one sediment station
for another where both samples are subject to comparable analytical
tests.
2. SAIC proposed including volatile organic compounds (VOC) trip blanks
composed of organic-free water with each set of VOC field samples
collected and shipped to the analytical laboratories. SAIC personnel did
not include VOC trip blanks with Week 1 VOC field samples because the VOC
blanks obtained from the laboratory contained air bubbles.
Consequences : Sample trip blanks are used to assess possible sample
container contamination by volatile organic compounds (SAIC QAPjP,
1989). Upon receipt of the unacceptable blanks, SAIC immediately
requested, and received within 48 hours, new “bubble-free” VOC trip
blanks from the laboratory. Trip blanks were included with sample
shipments during all succeeding weeks. The impact of not sending trip
blanks with the first week’s samples is expected to be minimal to the
overall quality of the oversight program as all sample bottles were
taped closed and enclosed in a sealed ice chest.
3. CR211 Hill relocated sediment sample station TC-6 from that originally
proposed in their FSP because cobbles and gravel in the stream bed made
sediment sample collection difficult. As a result, the sediment sample
from station TC-6 was collected approximately 50 feet upstream of surface
water sample station TC-6. In addition, the sediment sample from TC-6 was
2
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Teledyne Wah Chang Mining Waste NPL Site Summary Report
Reference 7
Excerpts From Record of Decision, Decision Summary, and R nsiveness Summary
for Interim Response Action - Teledyne Wah Chang Albany Superfund Site
Operable Unit 1 (Sludge Ponds Unit), Albany, Oregon; EPA; December 1989
-------
RECORD OF DECISION,
DECISION SUMMARY, AND
RESPONSIVENESS SUMMARY
FOR
INIERIN RESPONSE ACTION
IELEUYNE WA C ANG ALBANY SUPERFUNU SITE
OPERABLE UNIT #1 (SLUUGE PUNOS UNII)
ALBANY, ORECON
DECEMBER 1989
UNITED STATES ENVIRONMENTAL PROTECTION ICENCY
REGION 10
1200 SIXTH AVENUE
SEATTLE, WASHINGTON 98101
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iJj: ECiSi3’ 1
INtERIM ACIIUN SELECtION (SLU E PONUS UNII)
1ELE YNE WAR C AN ALBANY
ALBANY, OREGON
Statement of Basis and Purpose
This decision document presents the selected remedial action for the
sludge pond unit at the Teledyne Wah Chang Albany (TWCA) site in Millersburg,
Oregon, Just north of Albany, developed in accordance with CERCLA (32 U S C
§9601). as amended by SARA and, to the extent practicable, t re Natio’-ai
Contingency Pie’,
This decision is based on the administrative record for this site. A
copy of the administrative record index is attached as Appendix C.
The state of Oregon has concurred in the selected remedy A copy of the
state’s letter is attached as Appendix B.
Assessment of the Site
Actual or threatened releases of hazardous substances fro n this site, f
not addressed by implementing the response action selected in this ROD. may
present an imminent and substantial endangerment to public health, welfare, or
the environment.
Description of the Selected Remedy
The sludge unit addressed by this ROD is the first ooerable unit to be
addressed at the TWCA site The Remedial Investigation/Feasibility Study
(RI/FS) for the unit did not include certain components of a normal RI/ES,
such as a complete baseline risk assessment, because these will be Dart of an
overall site RI/ES (currently in the RI stage with the ES scheduled for
completion in 1991). The sludge pond unit is being dealt with separately due
to the procerty owners’, and the public’s, wish for an expeditious cleanup f
the sludges, which may be contributing to groundwa:er contamination at tne
51 te
The remedy consists of’
0 Digging up and removing the sludge
0 Partially solidifying the sludge with a solidification a eit 5.Cb es
portland cement, to improve handi ing and reduce the gross mobi lit,
of the solids A treatment piant gill be built for this puroo:e
0 Transporting the sludge mixture to a solid waste landfill and
disposing of it offsite
The wastes being acd”essed in thi interim Action are not hàZ3 Qu
wastes as defined by the Resource Conservation end Recovery Act (RCR.A)
therefore, the RCRA Lana Disposal Restrictions co not apply
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7: : :
, 1 .iL iI, i.i.
Teledyne Wah Chang Albany (TWCA) , Albany, Oregon
LOCATION ANU UESCRIPIION
The TWCA facility is located in Millersburg, Oregon (about three miles
north of Albany) in the Willamette Valley (see Figure 1). The Superfund site
includes the 110 acre plant site property and the 115 acre facility known as
the fariie site’, which has the plant’s active wastewater treatment sludge
ponds ( farm ponds”) and is located approximately 3/4 mile north of the plant
site Operable Unit #1. the unit addressed by this Interim Action, •ncludes
the solids in the Lower River Solids Pond (LRSP) and Schmidt Lake, which are
located on the plant site near the Willainette River and have riot been used
since 1979.
Of the two major site areas, the plant site contal s n mero is bui1dirigs
and facilities Including an extraction area south of Truax Creek, a
fabrication area north of Trua Creek, a solids storage area west of the
Burlington Northern Railroad, and a parking and recreation area east of the
Southern Pacific Railroid The farm site contains four 2—I/a acre solids
storage ponds The remainder of the site is used primarily For agriculture
The plant is currently operating and employs over 1300 people, making it the
largest employer in the Albany area.
The LRSP and Schi idt Lake ,,lie in the western portion of the plant Site,
next to the east bank of the Hillamette River, between Murder Creek to the
north and Truax Creek to the south (see Figure 2). The LRSP covers just over
3 acres and holds approximately 75,000 cubic yards of sludge: Schmidt Lake
covers roughly 0 6 acre and contains approximately 10.000 cubic yards of
material. The sludge in both ponds averaqei 40 percent sohdr Both pcrds
are diked to contain the sludge, which also allows rainwater to collect on the
top of the sludge: the rainwater is collected and pumped back to the plant
wastewater treatment facility for treatment The top few feet of the sludge
in both ponds have deep cracks that remain year—round Most of the surface of
the LRSP stays wet throughout tne year. out the surface of Schmiat Lake d- as
to dust during the summer
Portions of the TWCA site, including the sludge ponds, are in tne
100—year and 500—year flood plans of the Wi llamette River The ground
surface in the vicinity of TI4CA slopes westward towards the river with a
gradient of approximately 11 feet per mile
Willarnette Valley temperatures are rncdeiate, •,ith ma 1mums seldom
reaching 1000 F and minimums rarely reaching 00 F Roughly 70 oercent of t e
40—inch annual precipitation fails during November through March, hi1e or !j
6 percent occurs during June, July, and August, fall and winter preclpita:ion
is the primary source of aquifer recharge in the area There are usually on “
3 or 4 days per year with measurable amounts of snow
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—. — : ..—
tD :N D Z be ; sec ; :uit e a e :z of :- e
iri south f the plant site is use r a nly or residential a d ccmmercia
purposes, wnhie land west of the i’lillamette River, which borders the plant
site, is used for farming. Albany, the urban area to the south of the site,
has a population of approximately 27,000, Millersburg has a population of
about 560
There are approximately
three miles of the facility:
There are no known domestic,
located between the site and
not used as a drinking water
250 known private drinking water iells within
all of these wells are upgradient of the site.
municipal, industrial, or irrigation wells
the Willamette River. The Willamette R ver is
source in this area
4
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IiE diSTC J A i E iF’JRCEi i ci:; ;i
Site History
Operations at the INCA site began in 1956 when, under contract with the
U.S Atomic Energy Commission, Nah Chang Corporation began operation of the
U S. Bureau of Mines, Zirconium Metal Sponge Pilot Plant. Construction of new
facilities at the existing plant began in 1957. These facilities were built
primarily for the production of zirconium and hafnium sponge. However,
tantalum and niobium pilot facilities were later included. Melting and
fabrication operations were added starting In 1959. TWCA was estabhsned in
1967 after Teledyne Industries, Inc., purchased Wah Chang Corporation of New
York.
Because of the many processes involied in the production of non er.ci.s
metals and products, waste management programs at INCA consist of a wide range
of activities, including: process wastewater treatmen*, solid waste
management; hazardous waste management: PC8 equipment menaqemevst; radioactive
material contro1 waste m ni.tzat1oe throuqh beneficial use: aVTd a;r quality
control programs. Discharge of process wastewater is regulated by a National
Pollutant Discharge Elimination System (NPDES) permit An Air Contaminant
Discharge Permit regulates air emissions at the facility. Teledyne is
currently classified as a hazardous waste generatos under the Resource
Conservation and Recovery Act (RCRA) program
The LRSP was constructed and placed into o eretion in 1967 to receive
lime solids (sludge) from TWCA’s onsite wastewatar treatment plant. Schmidt
Lake was constructed for the same purpose in 1974 SlUdge was pun ed into the
two ponds until October 1q79, when the far. ponds to the north of tne facil;ty
were put into operation. The farm ponds wece ori q na .11y pert of this operable
unit, but because they are outside the flood plain and conkein lower levels of
radioectivitr. they are not considered an immediate threat and are now being
investigated as part of the overall site RewedLa.I Investigation (RI) The
sludge in both the LRSP and Schmidt Lake contains heavy metals, a few organic
compounds, and trace levels of some radionuclides. Tables 1—4 summarize the
contaminants found in the sludge
In 1978, INCA modified the process for the production of zirconium and
nafnium metal such tnat radioactive materials were directed into a separate
solid waste re a ed. t. -cfticrinator residue This residue is managed as a
low specific activity radioactive waste and shipped to HeirfOrd, llashington,
for disposal. Sludge generated since the imp ementation of this modification
has been stored in the farm ponds.
Enforcement Histor’i
The Slud9a- ad4 have attracted trie attention of regulatory agencies ard
the public for many years. particularly because of the pres rica o
radioactive materials w ch wes fir t conf1rme t Oreqon State Nealzh
Divl 1on In 1977 In March 1978. INCA was granted a Radioactive Materials
License to tri sfe . re ai e, po%.e.&s- and use arid industi ial
byproducts containing licensable concentrations of radioact je materials
INCA took samples from the ponds n eal occasions in 1979 and l80
5
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-
INORGANIC CONTAMINANTS :N L3S? sc:: s
Detects!
Sa p1es Max .mi M fl U a Averages Background°
Arsenic 40/40 39 2 10
Barium 39/40 3,500 33 173
Beryllium 20/40 1.3 0.3 0.7
Chromium 39/40 220 65 :oo 20
Copper 40/40 77
.ercury 36/40 7.6 0.3 1.2 <0.2
N ickel 40/40 3,000 25 206 14
Lead 40/40 260 38 102 10
Ant .mony 29/40 24 5 12. (20
Seleru.um 35/40 16 1 3 3
Thorium 40/40 74 (8.3) 11 .2) 31.7 (3.5) 3.1
tran ium 40/40 129 (87.8) 12.7 5.4) 69.2 (46.3) 0.5
Zinc 40/40 87 24 40 35
Cyanice 28/40 165.0 3.0 .6 <2
Radl.umd
Activity 40/40 (22.2) - (3.2) - (13.2) - . 3)
Concentration 2.30x0° 3.32x10° 1.3 10 ._2
Z ircrniume ‘0/40 10.0 3.0 5.1 < -.3
Note: All concentrations in ng/Kg of as-receivec, wet solics.
Concentrations in are’ tneSe5 are in C /g.
Only constituents : a: were detected in 10 percent or ore of t e
s D1es are shown.
value detectec aoc ’e cetection Limit.
0 Geometric average. up__ca:eS 4ere averaged to cota n one va e : .a:
as tner. includec i . : gecnetr c average. No values e1o tezect_cr
L its were included : e a rage.
c r soil sam 1es :i e a z :ne ex st ng Fa ?cr.cs, Oczo er _?55.
See RI report.
d. radium-226.
e
1.rconiLm is expressec as a perrent.
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able 2
IN0 ANIC CowrAMI . rs IN SC*tIDT L.?.K! SOLIDS
Detects/
Sa 1es M i Mi.nie Averaqeb
Azse ic 10/10 36 8 16 24
Bartue 10/10 72 36 39 116
2eryllium 10/10 1.1 0.7 0.8 0.7
Ca iue 7/10 1.2 0.1 0.3 (O.k
cbron.tue 10/10 13 79 90 20
Copper 10/10 72 34 45
Mercury 4/10 1.4 0.2 0.6 (Q.
Nickel 10/10 4.300 1,700 2.600 .4
Lead 10/10 150 70 103 10
10/10 14 8 9 <20
Se1e ..tua 7/10 4 1 2 3
Tbortuz 10/10 59.3 (7.5) 30.8 (3.4) 46.3 (5.1) 3.5
Ora.niue 10/10 227.7 (160.9) 104.6 (70.8) 162.6 (110.1) 0.3
Zinc 10/10 97 50 67 39
Cyanide 4/10 110 2.5 5.3 <2
Radiumd
Activity 10/10 (26.4)_i (14.9) _ (19.2)_s (1.0)_.
Concentration 2.54x10 1.44x 0 1.85x10 9.64x10
Zir niuee 10/10 28.8 3.9 7.4 (1.0
Note: All concentrations in ng/kg o as-recei ved, wet solLds.
Concentrations in arentbeses are in Ci/q.
Only ast tuents that were detected ..n .0 ;ercent or more o the sa pies are
sbovn.
5 Miniaum value detected above detect on i .zj .t.
b oietric average. ip11cates were averaged to obtaJ.n one ia1 .ie that aser .:.ide
in the g t.rLc average. 4o la.ues e ow detecti on .ere .icluded in the average.
CFron soil sa p1es taken ea.st o the Fa ?ond.s, October 1988. See RI report.
dAs radlue -226.
eZj o ue .s expressed as a pertent.
CVR126/051—2
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Tacle 3
ORG 1 NIC CONTAMINA TS IN LRSP SOLIDS
Detects/
Volati. les Samples Ma.x im inim .mta Ave rageb
Methylene chloride 36/40 22.000 0.006 0.084
1,1,1,—Tr ichloroethane 7/40 0.860 0.053
4-Methyl—2-pentanorLe 23/40 1,400.000 0.040 3.929
1,1—Di.ch loroethane 12/40 0.860 0.053 0.174
Tetracnloroethene 19/40 0.970 0.005 0. ô4
Semivolatiles
Hexachlorcben:ene 39/40 64.000 0.740 6.600
bis ( 2—ethyl—hexyl)
phthalate 5/40 1.700 1.000 1.295
Note: All concentrations in mgRg dry weight.
Only compounds that were detected in 10 percent or more of the
samples are shown.
aM value detected a. ove detection l .mit.
bGeomet.ric average. Duplicates were averaged to obtain one value that
was then included in the geometric average. No values below detection
limit were included n the average.
4 3
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Ta. 1e 4
ORGANIC CCNTAMINANTS IN SC *tIDT LA ! SOLIDS
Detects!
Volatiles Samples Mx imi. Mj.nj.m Averageb
Methylefle chloride 10/10 0.090 0.031. 0.046
l,1,1,—Tr ichloroethane 4/10 0.320 0.073
4—Methy l—2—pefltaflOfle 3/10 54.000 24.000 32.733
1,1—D ichloroethane 5/10 3.900 0.170 1.054
Tetrachioroethefle /.O 0.073 0.073 0.073
Semivolatiles
He cachlorobenzene 10/10 25.333 7.300 14.087
bi.s(2—ethyl-hexyl)
phthalate 1/10 1.000 1.000 1.000
N—Nitroso—d i-n-
propylam.u e 2/10 0.590 0.1.90 0.048
Note: All concentrations n ng/ g dry weight.
Only compounds tnat dere detected in 10 percent or more of the
samples are snown.
a 4 value detected above detection limit.
b cmetric average. Duplicates were averaged to octain one value tha:
was then included in the geometric average. No values below detection
limit were included in the average.
9
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I .’
\\
: t’e c:—ic / : -
Siting Council (EFSC) for a site eitificate : cose LRS? a i t stoic
approximately 120,000 cubic jaras of lime sol :s The TNC facil it 1 as
listed on the National Priorities List (NPL) in October 1983 After several
years of hearings, court actions, and further sampling, EFSC ruled in 1987
that the sludge was not subject to their jurisdiction, the levels of
radioactivity being too low. TWCA then submitted a closure plan to the Oregon
State Health Division, but EPA and other agencies recommended that closuie not
taKe place until after the conclusion of the RI On May 4, 1987, TIICA signed
a Consent Order agreeing to conduct the Remedial Investigation/Feasibility
Study (RI/ES)
The TWCA facility holds permits For watei and air emissions. It as
found in violation of wastewater discharge permits in 1975. 1977, and 1978,
subsequent process changes reduced the toxicity of the facilitys wastewater
discharges TWCA ‘ as assessed fines For other ater quality permit ‘,io1 ::ri;
in 1979. 1980. and 1989 Tne company was fined f i ii legal open bur ing
1983. In 1986, TWCA was cited for several violations of the states hazardou3
. aste management rules
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S
1 5 — — I — I
UI lr lr i ic I I I _ i j I
Contaminants Present
The s1udg in the LRSP and Schmidt Lake was sampled and contairi s metal
compounds produced by the various onsite processing units, including
zirconium, hafnium, chromium, mercury, nickel, uranium, and radium, cyanide
has also been feund. Of organic compounds detected, the most prevalent one is
hexachlorobenzene, which is probably a byproduct of plant operations (Tables
1—4).
TWCAS wastewater treatment system consists of a continuous cnemical
precipitation and sedimentation system. Metals are treated by neutralization
with lime, magnesium hydroxide, or sulfuric acid and carbon diox de t a
range between 6 and 8 to form metal hydroxides aria sulfates ,ncn .
precipitate Fluorides are removed by the formation of calcium fluoride.
These compounds are removed in a clarifier by settling. Lime solids, referred
to as “sludge”, generated from the operation of the clarifier are placed in
sludge ponds for additional settling, dewatering and storage.
Potential Routes of Migration
The LRSP and Schmidt Lake are unlined Impoundments constructed on native
soils in the Willamette River flood plain; thus, flooding is one potential
cause of contaminant migration. Because the ponds are unlined, they could
also be a source of groundwater contamination. Another possible route is
dermal contact with the sludge by onsite workers or trespassers. A fourth
potential route, dust, is a ina or concern because the dried sludge mate’-ial
can be spread by wind Some dust is created when the surface of Schmidt La t ce
dries during the summer, and more could be created by sludge treatment or
removal activities Fortunately, most of the sludge contains a high
percentage of water, which limits its migration as a dust
13
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ur
The foUow ng assessment is based on the data-generated and presented in
the TWCA Operable Unit Remedial Investigation (CURl) report and deals only
with the potential hazards associated with exposure to the sludges in the
ponds. Any potential hazards associated with contaminated soils beneath o-
surrounding the sludges or with groundwater associated with the pond; vii be
evaluated as part of the overall site RI/FS A baseline risk assessment is a
part of the overall RI/FS
Identification of Contaminants of Concern
During the OURI, sludges in the LRSP and Schmidt Lake were found to
contain inorganic eiements, organic compounds, and rad lonuciides Ii
estimating average concentrations, a value of one-half the iiethoa aetectiori
limit (MDL) was assumed for cases where no detectable contaminant quantities
were found. Of all the chemicals measured in the sludges, the inorga.riic
elements, part. cularly zirconium. yere found In the highest concentrations.
Thirty—four chemical substances were detected and positively identified
in the LRSP arid ScP intidt Lake sludges during the RI. In addition, several
tentatively identified compounds were also detected Of the 34 positively
identified chemicals, 25 are chenica s of concern nd potential contributors
to public health risk
For carcinogens, since there is no safe dose, an estimate of the
likelihood of developing cancer is derived from the average daily dose over a
lifetime multiplied by the potency factor f r that particular chemical T e
potency factor is the plausible upper bound estimate of the probability of a
response per unit intake of a chemical over a lifetime. EPA has developed a
classification system (A—E) for chemicals which have been evaluated a;
potential carcinogens The system is based on a weight of evidence scheme,
witn those chemicals being known human carcinogens considered as carcinogens
and those for which there is no evidence of carcinogenicity in the E category
For non—carcinogens, the average daily dose over the period of exposure
is comoared to a reference dose or other toxicity constant A reference ic;e
is an est mate (with a safety factor of 10 to 1000) oF a dail, e pos re l ’ e’
for the human population that could occur without prodLcing harmful neatn
effects. Non—carcinogenic effects include behavior changes. nervous ;,steci
disorders, birth defects, and damage to kidneys, blood. li’ier and lungs
Carcinogens
Tw v chemicals found in the pond sludges ma cause
cancei chroritum. and aLare kncwn to na’e the
potential for causing cancer :; human ; when Thaie na1ye iC e t ) C
were for total cnromiurn. with tne type unspecified, in ode’ to be moe
protective of public healtn. this i isk assessment is based on chromium ‘/1 ( tre
most toxic form). Eight chemicals are probable human carcinogen; througn
either ingestion or inhalation (Giouc B) and one is a possible human
car c r’cgen (CrDeo C) Poteric, est nate EPA clas ;iF caticn for :-e:e
chemicals are ro ided in Tabe 5
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TABLE 5 TELEDYNE WAN CHANG
OPERABLE UNIT NUMBER ONE
HUMAN HEALTH RISK ASSESSMENT
CANCER POTENCY
CONTAMINANT ORAL INHALATION
(mg/kg/d)A( l) (mg/kg/d)A(_l) EPA
CLASSIFICATION
Arsenic l.50E+OO l.50E+Ol A
Beryllium 4.80E+OO 8.403+00 B2
Bisethylhexylphthalate l.40E—02 82
Cadmium 6.103+00 B].
Chromium VI 4.1OE+00 A
Hexach].orobenzene 1.673+00 B2
Methylene chloride 7.50E-03 l.40E-02 32
Nickel 8.40E—0l A
Tetrachloroethene 5. 1OE—02 3.30E-03 32
Trichloroetherte l. 1OE-02 l.30E-02 B2
1,1 Dichieroethane 9.103—02 C
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V
G )fluC. ‘aes
The presence of uranium, thorium, and radium isotopes in the sludges f.-:n’
Schmidt Lake and the LRSP presents the potential for radlatton Induced
cane r. In the Teledyne Wah Chang Endangerment Assessment (part of the
Operable Unit Feasibility Study), the comitted dose equivalent was Converted
into an estimate of cancer risk using conversion factors from the “Effects on
Populations of Exposure to Low—Levels of Ionizing Radiation’ NAS, (1980),
ranging from 67 to 227 cancer deaths per million—man—rem These factors
suggest that if one million individuals were each to receive one rem, then 57
to 227 excess cancer deaths would be observed These conversion factors iney
be translated into estimates of individual cancer risk The ind vidual c nce ’-
death risk is 6 7xl0 4 per rein. Recent information indicates tnat tne
maximum number of cancer deaths per million—man—rem should be 400 instead of
227 The new number of 400 cancer deaths per million—man—rem was used in tne
suoolerneritary assessment to est’mate maninurn cancer deaths from rac’ :tc.
exposure. Radiation induced cancer is assumed to be fatal anc chemca •,
induced cancer may or may not be fatal.
Non—Carcinogens
For the non—carcinogens, antimony is likely to produce the most severe
effect from the ingestion exposure route, barium from the inhalation route
Zirconium, which occurs at the highest concentration, is not acutely toxic,
but accumulates in the body and may produce chronic effects
Exposure Assessment
Under current and future operating conditions, if no cleanup actions are
undertaken at the site, tne most likely exposures are for workers and
trespassers coming into direct contact with the chemicals in the sludge In
addition, if land use patterns change and the sludge site is opened to
residential development, onsite residents may be exposed to contaminated
sludges
In order to estimate potential health risks from contact with the sludge,
four exposure scenarios were evaluated in the risk assessment Two scenarios
were used to describe operations continuing at the facility with no corrective
action Under these two scenarios workers were assumed to come into direct
contact with pond sludges for an average of 10 years and a maximum period of
40 years For future risks, if trie sludge site should become residential, it
.ias assumed that the average esident wculd live on the site for 35 years anc
would be in direct contact with the slucges for 22 to 365 days per year For
tne highest residential exposure, it is assumed that an individual would ce in
direct contact with the pond sludges for his or her entire lifetime (75 year-fl
for 66 to 365 days per year
Exposure estimates (total dose over a lifetime for carcinogens and o”e
the exposure period for non—carcincgens) for ingestion of contaminated sl’id s;
and ;k’n absorption of chemicals Iere based on aierage and .na ’ linum
concentrations of chemicals measured in pond sludges If the ponds div. -
sludges could be dispersed into the atmosphere by the wind or mans actions
In order to complete the assessment for inhalation of chemicals, maximum
part culate concentrations ‘ier-e assumed to be egui’ialent to tIne fe’ e’
par: culate standard of 50 ug/cubic nieter (National mo ent Air Quai i:
16
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3: LC s , CF 3:. C :C nactei ass cnar o” a _a ::
2’ ricur average) pai’ticulate :onceritraticn of 53 ug/cu i: ez
as an average exposure condition In addition, contaminant concentrazcr:
were assumed to be the same in the airborne particulates as they are in the
sludges, with particles being 100 percent respirable.
Risk Characterization
A summary of risk estimates for exposure to contaminated sludges is giien
in Table 6. As this is only a preliminary assessment for a portion of the
TWCA facility, the summary risk estimates should not be viewed as a statemeit
about health risks to residents in the vicHi lty of the site. The risk
estimates presented in this report are representative of long term exposures
to chemicals in the ponds (from 10 to 75 years) for average and maximum worst
case scenarios Future residential development on the sludge site without
cleanup of the contaminants iii the ponds is clearly the maximum worst case
scenario The purpose of evaluating this unlikely event is to provide EP- Cr’:
tne public with sufficient information to make a decision regarding the
necessity for cleanup of toxic materials in the “nment.
Another scenario which is viewed as a Pot / - the
movement of contaminants into the Willamette P / R.t
due to flooding. The probability of a flood c
estimated at a one in 500 year event. Due to J:(.’(— L . :
likelihood, and difficulty in predicting how ;7, ‘ - Jvv 41.,,
such an event should occur, risk estimates w’
exposure pathway However, one can assume t __
provides a measure of what health effects wc 0 ? (Q
contaminants should occur over a long perio LI C
flooding should not exceed those which are
Cancer Risk Estimates ff21 JO.i j /
The risk of developing cance’ ranges (
million to greater than one chance in OflE d
length of exposure For onsite workers, L . -
cancer is under maximum exposure conditions (40 yeds
chromium ‘11. arsenic, and hexachlorobenzene are the major co’. e
increased cancer risk The potential risk of developing cancer for p . ,. iho
may reside ons t in the future if no action is taken. rar s from an
additione i-n one thou aii to tlw-e in one thousand for
exposure ove1Ea11reti h1e!’ Nickel, chromium VI, arsenic and hexachlorobenzene
are also the major chemicals contriouting to the cancer risk for this scena-’o
The ri r 4eat , ,frorn cancer due to exposure oradionuclides if no
cleanup act ion equivalent to those from other chemicals, rarigi g
from seven in one million to one in one thousand The greatest risk ‘s for
residents under maximum exposure conditions (75 years direct contact wr h ccn:
sludges)
Non—cancer Risk Estimates
Under current or future ooerating conditions, risks of health effect:
other than cancer aie only etpecte’i for the highest ior er exposure (4C
17
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—• rrr “
c L’ kur
Based upon consideration for the requirements of CERCLA. the detailed
analysis of the alternatives, and public comments, both the EPA and the state
of Oregon have determined that Alteraative 7 (removal, solidification, ar d
offsite disposal) is the most appropriate remedy for Operable Unit l at the
TWCA site It has been selected because it consistently ranked among the best
choices under all the ranking criteria except cost It effectively reduces
the likelihood of contact with the sludges and ensures that contaminants are
not transported into groundwater, surface water or air Human health and
environmental risks associated with the identified routes of exposure will be
eliminated or controlled by this remedial action
Approximately 85.000 cubic yards of sludge will be excavated from tne
LRSP and Schnndt Lake The sludge wrfl be -wed wikP a s&i&ification agent
such as Portland cement This will improve handling characteristics, reduce
mobility of contaminants, and increase the structural strength for landfill;rig
and capping. The mixture will then be transported to an offsite permitted
solid waste disposal site The mixture would be olace in a separate monocell
(adequately protected from coming into contact with other wastes) and capped
in accordance with state and local disposal requirements, applicable permit
conditions, and EPA approval The sludge mixture can be taken to a solid
waste landfill because it is not a RCRA hazardous waste. The inonocell must
have a liner and a leacriate control system this Interim Action, including
the removal and relocation of the sludges, is scheduled to be completed withi.-i
three years of the signing of the Consent Decree
The sludge relocation removes all of the sludge materials from Schmidt
Lake and the LRSP, both areas wnich could be impacted by a one in 500 year
flood. The sludge material must go to a permitted solid waste disposal
facility which by definition cannot be in a floodplain No location or
facility is specified by this ROD, but two facilities were identified in the
ES whicn meet the state requirements for a disposal facility There are al;o
out of state permitted landfill disposal facilities available
The disposal facility must not comingle the TWCA waste sludge materials
with any other waste; i e. , it must be a monofill This is to facilitate
comoliance with any monitoring requirements that may differ from those for
other wastes A suitable cap must oe placed Nhicn prevents sludge exposure to
peoole or the environment outside of the disposal unit The cap must aso
protect people from the release of radon contained or created from
contaminants in the sludge
A tre t step is part of this remedy Prior to relocation in the
perrnit:e.d. - d’ges will undergo partial treatment by using a
solidificatio a sA.t4ik ,,—Portland cement Iheobjectof this partial
solidification treatment process s to recuce the free water content o the
sludges, make the slucges easier :o handle :ing conventional eQuipment s:
reduce the mobility of contaminants by chem cal and physical processes
Although this treatment process will not make the sludges into rigid 5QT ids
it will improve the final handling characterist ics and provide a level of
treatment to the siudge mater rals ES ;:entified cnsite treatment
of tne recommended alternative Jffsite treatment (e g at the disposal
facli l y may be considered during the Je:i;n phase. E A :an ce assjre’j -
will be performed in accor Jance i tn CER A and meet ARS
34
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me ii ia uct n °! 5 Ct’ ; s:i :e: -=
cance:-s in a population of l•J3) .i t out any future cortrol actions (as m -
an extreme residential use scenario of tne actual sludge pond area) to
acceptable risk levels of less than 1 excess cancer in a population of
I million by permanently removing the routes of exposure. Additional
environmental risk assessment data is being developed during the overall site
investigation. Because the existing sludge ponds are unlined, there is a
future risk of contaminated groundwater being exposed to the environment
Relocation of the sludges reduces this risk.
Long term monitoring of the solidified wastes Is required and may be t ie
responsibility of the permitted landfill facility. Monitoriig and managemeit
of the facility are specified in the applicable permit and state laws EPA
must approve the use of any disposal site prior to its accepting the TWCA
sludge material.
The estimated cost of the remedy is $10 7 million The major cost
elements as presented in the FS are listed below.
Sludge removal and hauling $ 590.000
Solidification treatment process 1,586,000
Offsite disposal 6,000,000
Engineering design, bids, contingencies, etc. 2,540.000
Total Costs 10,716.000
The long—term Q&M costs, including monitoring, are included as part of
the offsite disposal cost. O&M and monitoring are the responsibility of the
disposal facility. The cost estimates may change based on final engineering,
design, disposal costs, etc. This decision does not specify the treatment
process, disposal site or engineering designs These activities are part of
the design phase of this action which occurs during the ROD implementation
process.
Performance standards for the ROD include the ARARs for excavation,
treatment, transportation, and disposal processes. Partial treatment of the
sludge material is required to reduce the water content, to improve handling
characteristics, and to reduce contaminant mobility The degree of
solidification will be determined during the design phase Special landfill
cap requirements to prevent radiation release are necessary (4’ of cover
material plus 1’ of clay) Long—term monitoring of any disposal site selected
must be consistent with the state of Oregon’s minimum requirements
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- . -,—. -
RESPONSIVENESS SUMNARY
TELEDYNE WAH C AN6 ALBANY
OPERABLE UNIT #1 INTERIM ACTION
Overview
The Teledyne l4ah Chang Albany (INCA) facility is located in t4Hler -soir -g,
Oregon (about 3 miles north of Albany) in the Willamette Valley of western
Oregon The INCA Superfund site includes a 110 acre plant site property and
the 115 acre facility known as the “farm site” The entire facility was
placed on the Environmental Protection Ageucy’s (EPA) National Pr’oritas L ::
(NPL) in 1983 A Remedial Investigation and Feasibil ty Study (RI/FS is
underway for the entire facility This responsiveness summary addresses
public comments made regarding a proposed Interim Action at the facility
This Interim Action addresses cleanup of the Lower River Solids Pona
(LRSP) and Schmidt Lake which are unlined surface impoundments that previously
received process wastewater from the various operations at the site.
The facility has been operating since 1956 when the Nab Chang Corporat o-i
began operation of the U.S. 8ureau of Mines Zirconium Metal Sponge Pilot
Plant. New facilities have been added at the Site which now include the
production of zirconium and hafnium—sponge from zircon sands, melting and
fabrication operations and facilities for the production of other specialit’,
metals Solids generated from the process wastewater treatment system rave
been stored in a number of surface impoundments, including the jand Schmidt
Lake prior to 1980. -
Since 1980 wastewater sludges have been stored in the farm ponds hich
were originally part of this Interim Action, but will be addressed under the
investigation of the entire facility The INCA sludges have been the subject
of several ballot initiatives, regulatory control processes, and environmental
group attention since the early 1980’s primarily because of the small amounts
of radioactive materials and the location of two of the ponds iii the
floodplain of the Nillamette River In 1979, INCA modified their productioi
process to significantly reduce the concentration of radioactive compounds n
their wastewater sludges.
In May 1987 INCA signed an agreement (Consent Order) with EPA to
investigate the nature and extent of the contamination problems at the
facility and develop alternatives fDr cleanup where necessary This jor’
called a Remedial Investigation and Feasibility Study arid is currently
underway. As part of this Order. EPA and I hCA agreed to address the LRSP.
Schmidt Lake, and Farm Pond sludges prior to completion of the RI/FS for tha
entire facility This action was due to concern over the sludges potential
contribution to groundwater contamination, public concern over the materials,
and their location in the floodplain
A-i
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Mining Waste NPL Site Summary Report
Tex Tin Corporation
Texas City, Texas
U.S. Environmental Protection Agency
Office of Solid Waste
June 21, 1991
FINAL DRAFT
Prepared by:
Science Applications International Corporation
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
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I
DISCLAIMER AND ACKNOWLEDGEMENT
The mention of company or product names is not to be considered an
endorsement by the U.S. Government or by the U.S. Environmental
Protection Agency (EPA). This document was prepared by Science
Applications International Corporation (SAIC) in partial fulfillment of
EPA Contract Number 68-W0-0025, Work Assignment Number 20
A previous draft of this report was reviewed by Ruth Lzraeli of EPA
Region VI [ (214) 655-6735], the Remedial Project Manager for the
site, whose comments have been incorporated into the report.
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Mining Waste NPL Site Summary Report
TEX TIN CORPORATION
TEXAS CITY, TEXAS
INTRODUCTION
This Site Summary Report for Tex Tin Corporation is one of a series of reports on mining sites on
the National Priorities List (NPL). The reports have been prepared to support EPA’s mining program
activities. In general, these reports summarize types of environmental damages and associated mining
waste management practices at sites on (or proposed for) NFL as of February 11, 1991(56 Federal
Register 5598). This summary report is based on inlbrmation obtained from EPA files and reports
and on a review by the EPA Region VI Remedial Project Manager for the site, Ruth Izraeli.
SITE OVERVIEW
Tex Tin Corporation is an active secondary copper smelting facility that was originally operated by
the U.S. Government during World War II as its primary tin smelting operation. It was subsequently
sold to private investors (Reference 3, page 2). Formerly known as Gulf Chemical and Metallurgical
Company (GC&M), the Tex Tin site was added to the NFL in August 1990 (Reference 10). The site
is included on the NFL due to the presence of heavy metals such as arsenic, tin, lead, and nickel
found in onsite surface water and ground water, and in ambient air sampled on and off the site
(Reference 3).
The Tex Tin facility is situated on approximately 175 acres located in an area of mixed land use.
Commercial businesses, residential areas, and petrochemical complexes are all located within .25 mile
of the site (see Figures 1 and 2) Swan Lake, a saline lake, is located approximately 2 miles from the
site. This lake is used primarily for recreational fishing and crabbing. A principal concern is the
potential environmental contamination of surface waters through the transport of heavy metals into the
Chicot Aquifer, and drainage of contaminated water into Galveston Bay (Reference 3, pages 6 and 7)
The Tex Tin site has been inspected on many occasions by representatives of the Texas Department of
Water Resources (TDWR) and EPA, arid was placed under an Enforcement Order in 1976 by TDWR
for unauthorized water-discharge violations. The Order was referred to the Texas Attorney General’s
Office in 1978 (Reference 2). Some remedial activities have been undertaken at the facility, including
deep-well injection of the contents of an acid pond (Reference 3, page 2).
1
‘I
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Tex Tin Corporation
—
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VIRCIN!A PCIN Q AC ANCLZ
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FIGURE 1. VIRGINIA POINT QUADRANGLE
VIRCINIA POINT. TEX
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-
2
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Mining Waste NPL Site Summary Report
FIGURE 2. GULF CHEMICAL AND METALLURGICAL COMPANY, TEXAS CITY
PLANT
I
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‘sac
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• ‘.ocL vail. v u.
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GULF CHEMICAL & METALLURGiCAL
TEXAS crrr PLANT
Sac.. •,
3..
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Tex Tin Corporation
OPERATING HISTORY
The facility was initially operated by the U.S. Government as a tin smelter during World War II
(Reference 1, Cover Sheet). It was subsequently acquired by the Associated Metals and Minerals
Corporation from the Wah Chang Corporation in 1970, and became known as GC&M (Reference 2).
Since 1985, the company has been known as the Tex Tin Corporation. At one time, the facility was
operated as an iron recovery facility (iron recovery from ferric chloride). It is currently engaged in
the secondary smelting of copper (Reference 3, page 2).
In 1977, Tex Tin was described as having three metals reclamation circuits: nickel sulfate, ferric
chloride, and tin. The nickel circuit was described as “nickel sludge is stored in drums in the north
end of the smelter building. After smelting, ‘waste sludge’ is sold for other metal recovery. A small
quantity removed during vessel cleaning is dumped with the slag from the tin process.” The ferric
chloride circuit was described as “GAF sells the company iron sludge contaminated with the herbicide
Amiben. The material is stored in the two areas (not clearly designated in the references). Runoff
would supposedly flow through the plant to the pond system. A small quantity removed from the
settling-tank is disposed of in acid pond B.” Finally, the tin ingots circuit was described as: “product
is received in the following forms: ore sacks from Bolivia stored on pallets by Ponds A and B, tin
residues in 55-gallon drums stored in ore storage building, and tin ore piled along Highway 519.
After primary smelting, rich slag is stored onsite. End slag is produced after the electrolyte process
GC&M is planning to install a new rotary furnace for tin smelting. This new process will further
remove tin from the end slag” (Reference 4, pages 1 and 2).
In 1979, it was reported that the nickel circuit had been “torn down” and that nickel sludges were no
longer generated. Ferric chloride production had also decreased due to the loss of the principal
buyer; causing GC&M to cease buying Amiben-contaminated iron sludge for use in this circuit. In
addition, GC&M stopped disposing of the settling-tank sludge in the acid pond. It was also noted that
a rotary furnace had been added to the tin circuit. As a result, “end slag now generated has an
obsidian-like appearance. The material is dumped north of the acid pond. The company has hopes of
reclaiming additional tin from the slag in the future” (Reference 5, pages 1 and 2).
Tex Tin is situated on approximately 175 ares that contain various active and inactive structures
reflective of its past and present industrial activities. Waste areas identified at the site have included
wastewater treatment ponds, a gypsum slurry pond, an acid pond once containing ferric chloride and
hydrochloric acid, several drained acid ponds, slag, sludge, and ore piles. One of the slag piles is
contaminated with the herbicide Amiben (Reference 6, page 1). The facility also stored
approximately 4,000 drums containing radioactive material (Reference 3, page 2). At one time, the
facility stored piles of spent catalyst in the anticipation of building a plant to extract metals such as
4-
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Mining Waste NPL Site Summary Report
tungsten (Reference 7, page 3, Item 2). An inactive, licensed, low-level radioactive landfill,
containing uraniumiantimony slag, is also located onsite. The slag is from a pilot study on the
extraction of bismuth from a bismuth-uranium catalyst (Reference 7, page 3, Item 2).
SITE CHARACTERIZATION
Ground water, surface water, and soil sampling has detected various metals such as antimony,
arsenic, barium, cadrmum, chromium, copper, lead, manganese, mercury, nickel, silver, tin, and
zinc. In addition, ambient-air samples collected offsite have detected concentrations of arsenic,
cadmium, chromium, lead, nickel, and tin. The remnant acid ponds are considered a potential source
of ground-water and surface-water contamination. The pond is documented as being poorly
constructed and maintained (Reference 1, page 2a). Contamination has also been attributed to the
onsite slag piles that are uncovered and have no containment or diversion systems (Reference 1, page
4).
“One other area of possible contamination, an abandoned oil-processing facility, has been identified
on the Tex Tin property. The Morchem Resources facility was located on the northwestern portion of
the site (then owned by GC&M) from 1982 to 1983. Morchem processed Luwa bottoms (high
boiling-point glycols with 1% molybdenum) and waste oil from chemical and refining companies.
The facility was abandoned in 1984” (Reference 3, page 3). No other information is known about
this facility.
Ground Water
The Aquifer of concern underlying the site is the Chicot Aquifer. The Aquifer extends from 60 feet
to approximately 1,000 feet below the land surface. The flow of the Aquifer is generally in a
southeasterly direction towards Galveston Bay. The Chicot Aquifer is underlain by the Evangeline
Aquifer (Reference 1, page 2b).
Tex Tin monitored ground water in the vicinity of the acid pond from 1975 to 1980 (Reference 3,
page 5) The monitoring wells were screened at 37 to 47 feet below the ground surface (Reference 1,
page 2a) The contaminant concentrations detected were significantly higher in the samples taken
from the two downgradient wells as compared to the samples taken from the upgradient well. A
Preliminary Health Assessment prepared by the Texas Department of Health in 1989 concluded that
the concentrations of 12 metals exceeded drinking-water standards and long-term health advisories
5
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Tex Tin Corporation
(Reference 3, page 5). The metals of concern detected in the ground-water samples
concentration ranges are described in Table 1 (Reference 3, Table 1, page 4).
TABLE 1. CONTAMINANTS IN GROUND WATER
and the
Contaminant
Range of Concentrations
(in ppm)
Arsenic
<0.02 - 0.198
Barium
1.9-6.5
Cadmium
0.01 -7
Chromium
0.03 - 0.25
Copper
0.08 - 390
Lead
0.25-200
Manganese
6.3 - 357
Mercury
<0.0002 - 0.011
Nickel
002-7
Silver
0.07 - 1.02
Tin
0.018 - 100
Zinc
0.11-140
Surface Water
Tex Tin obtained a National Pollutant Discharge Elimination System permit in March 1976 for the
discharge of wastewater from the facility. However, it was believed by an EPA inspector (during a
Preliminary Site Investigation in February 1980) that the facility had been noncompliant with the
issued permit (Reference 6, Section XIV, page 10) Inspections by the Texas Water Quality Board
concluded that dikes d igned to prevent discharges from two old outfalls and the acid pond were
seeping, allowing cont2nainated water to enter Wab Chang Ditch (Reference 4, page 1). The Wah
Chang Ditch is currently pumped into the Texas City Industrial Channel, which enters Galveston Bay
Twelve surface-water samples were collected from various locations at the facility between 1975 to
1988. Constituents of concern and the concentration ranges are detailed in Table 2 (Reference 3,
Table 1, page 4).
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Mining Waste NPL Site Summary Report
TABLE 2. CONTAMINANTS IN SURFACE WATER
Contaminant
Range of Concentrations (in ppm)
Arsenic
0.05 - 0.94
Chromium
<002-81
Copper
0 03 - 60
Mercury
000024-0.02
Nickel
0.083 - 535
Zinc
0 175 - 42.7
QII
Possible soil contamination is not well characterized In 1980, EPA conducted a Potential Hazardous
Waste Site Inspection. At this time, it was the opinion of the investigator that it was ‘inevitable” that
soil contamination was occurring after viewing the site. Piles of tin slag, iron ore, and crushed empty
barrels were noted to be in abundance at the rear of the plant. A reddish material ossibly iron) was
noted in a drainage ditch located close the area of the material piles (Reference 8, Section Vifi, page
6-L).
A single soil sample was collected by the Texas Department of Health’s Bureau of Radiation Control
near the low-level radioactive landfill in December 1984. Four metals were detected at significantly
elevated concentrations; they are detailed in Table 3 (Reference 3, Table I, page 4).
TABLE 3. CONTAMINANTS IN SOIL
Antimony
Arsenic
Copper
Lead
2,590
720
130
980
‘ ci
Contaminant Concentration (in ppm)
7
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Tex Tin Corporation
Accorduig to the reference, the level of copper in the soil was not sufficiently elevated to represent a
health concern. The reference further indicated that the concentrations of antimony, arsenic, and lead
did constitute a health concern.
Ambient Air
In January 1986, the Texas Water Commission contracted with the Texas Air Control Board to
conduct air-quality momtoring of the Tex Tin site. The samples were obtained along the site
perimeter using high-volume particulate samplers. The conclusion reached after the sampling was
that heavy metals and arsenic were being carried offsite by the wind (Reference 6, page 7). The
maximum values of the detected contaminants are provided in Table 4 (Reference 3, Table 2, page 5).
TABLE 4. CONTAMINANTS IN AMBIENT AIR
Contaminants
Maximum Value Detected (in iig/m 3 )
Arsenic
2.34
Cadmium
0.64
Chromium
0.40
Lead
4.42
Nickel
0.21
Tin
103.6
Radioactivity
Low levels of radioactivity have been detected onsite in association with the tin, copper, and antimony
slags and with the company roads that have been graded with tin slag. According to the Bureau of
Radiation Control, the radiation levels are well below Federal occupational exposure limits, but are
approaching the upper limits of the range of levels generally considered safe for the general public
(Reference 3, page 8).
8-
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Mining Waste NPL Site Summary Report
ENVIRONMENTAL DAMAGES AND RISKS
In general, drinking water is supplied to the communities within the 3-mile radius of the site by the
Galveston County Municipal System rather than by private wells. However, a drinking water-well
survey conducted in 1985 identified a small beach house community, located approximately 1 mile
southwest of the Tex Tin facility, that uses private water wells. The community, consisting of
approximately 60 homes, is supplied by 25 wells. While most of the wells are more than 200 feet
deep, at least three of the wells are less than 105 feet deep and are in the aquifer of concern
(Reference 9, page 2).
In early 1989, the Texas Department of Health undertook a Preliminary Health Assessment of the Tex
Tin Corporation Site for the Agency for Toxic Substances and Disease Registry. The Department of
Health found numerous physical hazards at the site, particularly due to the lack of adequate security,
enclosure of the site, and inadequate containment of industrial materials and treatment ponds
(Reference 3, page 5).
The report concluded that potential environmental exposure pathways include ground water, surface
water, soil, and air contaminated with a variety of metals including antimony, arsenic, barium,
cadmium, chromium, copper, lead, manganese, mercury, nickel, silver, tin, and zi ic. Possible
human routes of exposure were noted as ingestion, inhalation, and dermal contact with the
contaminated media. Inhalation and incidental ingestion of airborne particles of Tex Tin emissions or
entrained dust also were cited as potential pathways of concern. However, more sampling is needed
to assess the potential risks (Reference 3, page 12).
REMEDIAL ACTIONS AND COSTS
Due to the failure of Tex Tin to achieve compliance with recommendations made by the Texas Water
Quality Board regarding ground-4.water and surface-water violations, the case was referred to the
Texas Attorney General in 1978 for legal action A suit was filed on June 1, 1982, by the State of
Texas (Reference 2), but was dismissed for want of prosecution on December 12, 1984 (Reference
10, page 1).
The Tex Tin corporation has made several attempts at remediation including the construction of a
deep well for injection of the contents of the acid pond, a major contributor of contamination at the
facility (Reference 7, Item 1, pages 1 and 2). According to the Preliminary Health Assessment, the
contents of the acid pond were disposed of in the well over a 2-year period beginning in 1985
(Reference 3, page 2). Also, the 4,000 drums containing radioactive material were removed from the
site (Reference 3, page 2).
9
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Tex Tin Corporation
CURRENT & ATUS
According to EPA, a Remedial Investigation/Feasibility Study was initiated in the last week of
November 1990. At this tune, no Record of Decision has been issued, nor are estimated costs for
remediation available.
10
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Mining Waste NPL Site Summary Report
REFERENCES
1. Tex Tin Hazard Ranking System Package; EPA; March 6, 1987.
2. Facility Management Plan; EPA, Undated.
3. Preluninary Health Assessment, Tex Tin Corporation; Texas Department of Health; Undated.
4. Internal Memo Concerning Tex Tin Corporation; From K. Macko, District 7 Representative, to
George Green, TDWR; September 26, 1977.
5. Internal Memo Concerning Tex Tin Corporation; From K. Macko, District 7 Representative, to
Steve Cook, TDWR; March 26, 1979.
6. Air Quality Monitoring at Tex Tin Corporation, Final Report; Texas Air Control Board;
February 12, 1987.
7. Letter Concerning Tex Tin Corporation; From H.L. Newman, Tex Tin Corporation, to Martha
McKee, EPA Region VI; January 25, 1985.
8. Potential Hazardous Waste Site Inspection Report, Gulf Chemical and Metallurgical Company,
EPA; February 21, 1980.
9 Drinking-water Well Survey at Tex Tin Corporation; Ecology and Environment; October 4,
1985
10. Letter Concerning Tex Tin Corporation; From Robin Morse, Esq., Baker and Botis, to Bob
Hannesschlager, EPA Region VI; July 15, 1985.
11
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Tex Tin Corporation
BIBLIOGRAPHY
Ecology and Environment Drinking Water Well Survey at Tex Tin Corporation. October 4, 1985.
EPA. Facility Management Plan. Undated.
EPA. Tex Tin Hazard Ranking System Package. March 6, 1987.
Morse, Robin, Esq. (Baker and Botts). Letter Concerning Tex Tin Corporation to Bob
Hannesschlager, EPA. July 15, 1985.
Newman, H.L (rex Tin Corporation). Letter Concerning Tex Tin Corporation to Martha McKee,
EPA. January 25, 1985.
Prepared for EPA by Gulf Chemical and Metallurgical Company. Potential Hazardous Waste Site
Inspection Report. February 21, 1980.
Prepared for EPA by TDWR. Potential Hazardous Waste Site Inspection Report. July 9, 1984.
Stevens, Mary (SAIC). Personal Communication Concerning Tex Tin Corporation to Ruth Izraeli,
EPA. June 13, 1990.
TDWR. Internal Memo. September 26, 1977.
TDWR. Internal Memo. March 26, 1979.
TDWR. Internal Memo. March 7, 1985.
Texas Air Control Board. Air Quality Monitonng at Tex Tin Corporation, Final Report. February
12, 1987.
Texas Department of Health. Preliminary Health Assessment, Tex Tin Corporation. Undated.
Texas Water Quality Board. Solid Waste Disposal Compliance Survey. September 21, 1977.
Texas Water Quality Board. Solid Waste Disposal Compliance Survey. March 5, 1979.
12
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¼
Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 1
Excerpts From Tex Tin Hazard Ranking System Package;
EPA; March 6, 1987
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--____
-_
Facility Name: Te .Tin Co p _ 3r3t1 ,.i
LOC. ti r . Texas C’ty —
EPA e 1on: V I ___ —— — —
Person(s) ii Charge of the FaclHty: Mr. larold ‘4 wai
P.O. Box 2130
—
i .e xas TX
pa — —______
- LL! __ 2f I 9 )
- a—
(4. ______
Name of Reviewer: R. Roblin — Date: _ j( /87 ______
General Description of the facility:
(For example landfill, surface impoundment, pile, container; types or
hazardous Substances; location of the facility; contamination route of
major concern; types of information needed for rating; agency action, et
.! _ e site is an ac _ tive tin smelting operation that was orlginafly ooe e
p1 _ the U.S. Government during W.W.U. It was then sold to private lnves
ors. The site Ic Situated on aooroximate ly 128 acres with waste handHi
. 5Clllties
that include five wastewater treatment ponds, Gypsum S 1 u’y
Ponds, OPen
and closed acid pond three Inactive Impoundments, slag o l
! d
inactive and permitted landfill containing radioactive was:es.
The
groun a route is the migra j pathway of primary Conceri.
$Jec’ficafly, three OflSite monitoring wells that are associated with the
Closed
acid_pond are valuated and scored. !norg n1 contaminat o. has
been documented
and Is characterlzad by elevated levels of lead, rnang ’-
ese
Scores: 38.43 (S 9 30.61 5 Sw 5 a 58.8!
5 FE N/A
N/A C
, ‘
FIGURE 1
MRS COVER SHEET
I
C.
C
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c hrie ‘ i tA
Gc iwate . Ra ior le
I igh levels of cooper and tin have been detected in
samples taken from On-site monitoring wells which are screened at an
interval of 37-47 ft. below the ground surface. (Ref 12. Ref 13)
The concentrations detected are significantly higher ifl the samples taken
from the down-gradient wells (MW.2, MW.4) as compared to the samples ta e
from the up-gradient well (M .1) (Ref. 10, Ref. 05). The monitoring eil
locations are Shown in Ref. ii. The contaminants can be directly dttrib :a
to remnant acid ponds that have been documented as being poorly cor.str c:e:
and mainrained by facility operators (Ref. 04). Although the facility
is still active, the company is exempt from RCRA regulati n due to t e
ore and mineral Processing exclusion set forth in 40 CFR Part 261 4(c)7.
(Ref. 14).
“—C.
\
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\
esc”::’cn C’ u ’e’ o’ Coice’r ,
-e c szcn Oistrict consists of all of Harris, Wailer, ar Fart
Bend Co .. n ies and parts o Galveston, Montgomery, Brazoria, Chambers.
aria Liberty Cot. nties. Within the district, groundwater is rimarily
drawn from geolocic formations composed of sedimentary deposits of
gravel, sand, silt and clay. The hydrologic units are the Catahoula
Sandstone and Fleming Formation of Miocene age; the Goliad Sand of
P iocene age; the Willis Sand, Bentley and Montgomery Formations, and
Beaumont Clay of Pleistocene age; and alluvium of Quaternary age. (Ref 21)
Because of their origin and method of deposition, the sand and clay beds
grade into each other both laterally and vertically within short distances;
consequently, differentiation of geologic formations based on drilers
or electric logs is almost imoossible (Ref. 22).
In the area of tne site, water is predominantly drawn from the
Chicot aquifer. The CPncot aquifer is composed of the Willis Sand, Bentley
formation, Montgomery formation, Beaumont Clay, and any overlying Ouarternary
alluvium. This aquifer includes all overlying Quarternary alluvium. This
aquifer includes all deposits from the land surface to the top of the
Evangeline aquifer. In the area of the site, the aquifer can be separated
into an upoer and lower unit. Where the upper unit of the Chicot aquifer
is undifferentiated, the areal extent of the upper unit roughly correspcnds
to the areal extent of the Beaumont Clay. (Ref. 21). The Chicot ma,ntains
a thickness of aporox. 1000 to 1100 ft in the area of the site, while tne
Evangeline has about 3900 to 4000 ft. of thickness (Ref. 16).
Throughout most of Galveston County and southeast Harris County. the
base of the Chicot aouifer is formed by a massive sand section with high
hydraLlic conductivity. This sand unit is known locally as the Alta Loma
Sand. The city of Galveston has an established well field drawing from
the Alta Loma Sand. The Chicot aquifer is underlain by the Evangehne
aquifer everywhere except where salt domes pierce it. The Evangeline
aquifer is underlain by the Burkeville confining layer. (Ref. 22)
Water levels in Chicot wells have risen 10 to 20 feet from 1975 until
1980 Corresponding subsidence has been 4 to 5 feet from 1943 until 1978
and 0.25 to 0.5 feet from 1973 until 1978 centered in surface subsidence
through near the site. No significant surface faulting occurs within
20 miles of the site. (Ref. 4).
For the purposes of this MRS package, the aquifer of concern will
be considered to be the upper unit of the Chicot Aquifer. In the area
of the s1te, this aquifer extends from the surface to a depth of approx.
100 ft.
G ’
-------
3 C3N AI\” S ’
C:a:-:e
t waits or l.achac. con:a . eva1. a ,d:
WA
Method with Pughe score:
N/A
4 VAS e URACT!*2ST1cs
To icjty s d Pers stenee
Co ound(g) evaluated:
Copper 18
Lead 18
Mercury - 18
Ref. S
Co peund w th h gh.st score:
me above contaminants were detected in samples taken from the acid pond
on June 1, 198A. (Ref. 01, Ref. 05)
hRS Value 1E
Mizardoui Vast, Qsncitv
Total qua tLcy of hazardo,.&, substantes at the facility, excluding those
with a congainasat score of 0 (Civi a reasonable •sci ace evem f
qi.iancicy is •bovs g ):
An estimated 19 million gallon surface impoundment that has no liner and has
visible seeoage from dikes. Monitor wells have documented a release of
contaminants, to the shallow aquifer below the site. (Ref. 10). In aCdition.
three slag piles are located within the site boundaries with a total
estimated waste volume of 13,636.74 cubic yards. These piles have no cover
or containment/dlversjon system. (Ref. 19, Ref. 20) HRS Value sS(Ref 1)
Basis of escisacing and/or ce pu:&ng waste quantity:
‘See Attachment C’
‘S.
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Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 2
Excerpts From Facility Management Plan;
EPA; Undated
-------
\
uLf Cherr:ca]. arid Metallurgical
TX 23 4
Iitrcducti n
On April 20, l9 4, M 5 • aren riebus, Texas Departnent f Water lesources
(T iR) District 7 off ice, -tade art inspection of the Gulf Chertical art 1
Metallurgical (CCI) facility in Texas City. Also present at the irsoect:o’
was Ms. Pat Fotertot, iR District 7, and Mr.Haroj.d Ne an with SCM. The
inspection consisted of an interview with Mr. Newman, file review, site
surveillance, and sartpling activities.
Sackgrourtd
The site consists of 128 acres, which was originally started as a tin
smelter by the U. S. goverr ent during World War II. CC I bought the
facility in 1970 from the Watt Chang Corporation. Waste handling facilities
include five wastewater trea ent ponds, gypsi.m slurry ponds, acid pond,
closed acid ponds, three inactive impoun&lents, niben contaminated iron
sludge, slag piles, 20, 300 druns of spent catalyst, and a landfill contain-
ing radioactive waste. On August 10, 1978, the T referred 0CM to the
Texas Attorney General’s office for surface and ground water pollution
offenses. On June 1, 1982, a petition and application for tenporary
injunction were filed against CCI for violations relating to their waste—
water permit. The T! l has doc .mented ground ter contamination fron the
acid pond. Leaks in the acid pond have also been doctmtented by sa’ p1ing
liquid coming from the pond’s dikes. Contaminated runoff from the slag
piles; closed i untt ertts and dri storage area have also been docunent& .
Drum in the drt. storage area are badly corroded and leaking.
Rec mertdation
Though CC I considers their waste piles and drt storage area to contain
potential. raw material, the ?laterial is presenting an unknown threat to t e
envirorm int.. Further, the acid pond is contaminating ground ter as we1
as surface runoff. Th. dikes of the acid pond are unstable and In poor
condition. For these reasons, a high level of seriousness is assigned t
this site. A ranking package will be developed to determine if this site
cart be included on the National Priorities List for remedial action under
Superfund.
-------
Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 3
Excerpts From Preliminary Health Assessment,
Tex Tin Corporation; Texas Department of Health; Undated
-------
p UMINAR’i HEALTM ASSESSKUIT
Tex Ttt CorporattO
CERCLIS No. TXD062U 3329
Texas CitY. Texas
?reparsd by rh. Texas D.p .X Sflt of Health
PrsparSd for:
DtViIiOt of Health A 5ISSI t aM Consultat 0n
Tb. AgSUCY for Toxic Subats c aM DLse’sS R.gistry
u.s. Public Hu]th S.rvtCS
-------
SU 0(ARY
The Tex Tin Corporation facility. formerly Gulf Chemical and MecaLLrg .ca .
corporation. is a proposed National Priorities List site Located in Texas
city, Galveston County, Texas. Tex Tin previously operated as a primary
tin sm.lter. but currently operates as a copper smelter. Significant
concentrations of metals (antimony, arsenic, barium, cadmium, chromium,
copper, lead, manganese. mercury, nickel, silver, tin, and zinc) have been
detected on-site in surface water, groundwater, and soil. Significant
concentrations of metals (arsenic, cadmium, chromium, lead, nickel, and
tin) hav, also been detected in ambient air sampl.ss collected off-site.
Some remadiation activities have occurred on-sit, including the closure of
a 19-million-gallon ferric chloride pond and the removal of approxtmatei.y
4,000 drums containing radioactive material. The Tex Tin sit . poses a
potential public health concsmn for on-itt. workers, residents Living in
nearby neig borhooda, and possibly for a Limited n b.r of residents on
private wells located within approximately one mil. of th. sit..
8ACKGR OUND
The Tex Tin Corporation, formerly the Gulf emLcal and Metallurgical
Corporation, was proposed for inclusion on the National Priorities List .n
June 1988. The 128-acre site is located at the tnt.rsection of State
Highway 146 and Farm to Market Road 519 in Texas City, Galveston County,
Texas. Tex Tin previously operated as a tin s.sltst, but currently
operates as a copper smelter. The materials managed at th. sits are
primarily inorganic and mineral in nature and also includ. by-level
radioactive material.
Industrial waste erase that have ben identified on-sit. include five
wasrevacer trea snt ponds, slag and ore piles, and several inactive acLd
pond... An inactive, Licensed, low-level radioactive landfill, which
contains uranium/antimony slag, is located on th. southwest portion of the
sits. Previous sits inspections had identified three primary areas of
concern: a 19 million gallon ferric chloride pond. a storage area which
held approximstsly 4,000 dz s containing radioactive material • and the
slag and ore piles. The original contents of the acid pond were disposed
of in a permitted waste disposal well located onsite over a two-year
period b.gix2nin$ in 1985 (1). The drums that contained radioactive
material have also been removed from th. site (2). Th. slag and ore
piles, which have me cover or contairment/diVSrsiQfl system, remain
onsite. On. of the slag piles is contami”-ated with the herbicide Am .ben
Numerous metals, including antimony. arsenic, barium, cadmium, chromium.
copper, lead, manganese, mercury, nickel, silver, tin, and zinc have been
detected at elevated levels on.site in groundwater, surface water, and so.l
samples. Ambient air sampling has detected stgaiftcant concentrations 3
arsenic, cadmium, chromium, lead, nickel, and tin offsite.
-------
One other area of possLble contamination, an abandoned oil.processing
facility, has been identified on the Tex Tin property. The Morchem
Resources facility was located on the northwestern portion of the site
(then owned by Gulf Chetical and Metallurgical) fron 1982 to 1983.
Morchem processed Luva bottoms (high boiling-point glycels with 1%
no1ybdenum) and waste oil from chemical and refining companies. The
facility was abandoned in 1984 (4). No information vu available
concerning the extent of closure activities or th. current status of the
site.
EJIRO Otfl TAL CON ’ AMIMATION AND PHYSICAL HAZARDS
Limi ted soil, surfac. water, and grotmdwater sampling results were
available for review. The samples collected at the Tex Tin sit, were
typically analyz.d for mtal content only, although radioactive content
was msuured in s.lectsd samples. An analysis for organic contaminants
was apparently not conducted for the sa.pl.a. No quality
assurance/quality conttol information was available for a of the
sampling.
Table 1 suamarizes the contaminants of concern dtected onsits • the media
in which they were found, and a range of concentrations for each
contaminant.
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TABLE I
ON .5 ITE CONTAXINAZITS
‘tEDIA CONTAI1INAZIT RANGE OF CONCENTRATIONS
in ppm
Soil AntimOny 2,590 *
ArseniC 720 *
Copper 130 *
Lead 980 *
Surface T.iatsr Arsenic 0.05 0.94
Ch romi ’. <0.02 . 81
Copper 0.03 60
M.rcury 0.00024 - 0.02
Nickel 0.083 . 535
Zinc 0.175 42.7
Groundwater Arsenic <0.02 - 0.198
Bari a 1.9 6.5
Ca .i ’ 0.01 . 7
Chroait 0.03 - 0.25
Copper 0.08 390
Lead 0.25 • 200
Nanga nesS 6.3 357
Mercury <0.0002 0.011
Nickel 0.02 . 7
Silver 0.07 1.02
Tin 0.018 . 100
Zinc 0.11 . 140
* o ts sample analyzed
Th, single sot]. sample vhich yes available for review via collected in
Dece er 1984 by the Tew DepartoSut of Health Bureau of Radiation
Control in the vicinity of the ]o’v -ISVSI radioactive landfill (5). Four
etsls were d.tectsd at significantlY elevated concentrations jncluding
anti2ofly. axisnic, copper. and lead. Althougb the 130 pp. of copper
detected in the sot] is significantlY elevated over typical background
concentratiOns of coppet. it is not sufficiently elevated tO the point .:
would represent a health concern. The concentrations of antimony,
arsenic, and lead wars sufficiently slevated to raise pot. tial health
concerns. The elevated copper concentration, however. is one more
indication of a possible soil contaai tiOfl problem.
The analytical r.sults of 12 surface water samples collected from 1975
1988 from various locations on the Tex Tin property vets reviewed (5.
and 7). ArseniC. chromi a, copper. mercury, nickel, and zinc wets
detscted at elevated concentrations in some of the samples. Informat
on the sampling protocols used for sample collection, preparation. or
• . . . I,
-------
The groundwater samples reviewed were collected from three on-site
monitoring wells from 1975 to 1980 (6). No recent groundwater monitoriflg
data were available for review. Results of the 1975-1980 groundwater
sample analyses indicate that concentration.s of 12 metals were
significantly elevated, exceeding drinking water standards and long-term
health advisories. The metals of concern detected in the groundwater
samples are arsenic, barium, cadmium, chromium, coppsr, lead, manganese.
mercury, nickel, silver, tin, and zinc. The monitoring wells are screened
at 37-45 feet with the two wells located on th . southern half of the si.:e
showing higher levels of contamination than the one well located on the
northern portion of h. site.
Ambient air samples collected around the p.riastsr of the Tea Tin facility
in 1986 detected several metals at Levels of concsrn. Samplss w.re
collected for an eight-hour period. Tabls 2 lists the contaminant and the
maximum concentration detected.
TABLE 2
OFT- SITE AIR C0NTMINAI TS
CONTAMINANT MAXIMUM VALUE DETECTED -
(ug/m 3 )
Arsenic 2.34
Cadmium 0.64
Chromium 0.40
Lead 4.42
NickeL 0.21
Tin 103.6
No off-site samples were available for soil, groundwater, or surface
water.
Numerous physical hazards were evident on th. site. The large acid pond
which had previously been drained is currently filled with 3.6 feet of
water contributed from infiltration and precipitation . Other hazards
includ, the vastevater trea .nt ponds, slag and ore piles, and other
hazards which are typically associated with an activs industrial site such
as heavy machinery, discarded pip., etc. These materials, along with the
low-level radioactive landfill, would pose a has—rd to children playing on
the site. Although the entire site is currently fenced, portions of the
fence are in disrepair and access to the site ig still possible through
breaches in the fence.
I ; . \:
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POTENTIAL ENVIRONMENTAL AND HUMAN EXPOSURE PATHWAYS
Potential environmental pathways thc].ud contaminated groundwater. surface
water, soil, and air. Potential human exposure pathways include
Lngestion. inhalation, and dermal contact with contaminated groundwater.
surface water, and soils. Inhalation and incidental ingestion of airbort e
particles from plant emissions or entrained dust are also potential
pathways of concern.
DEMOGRAPHICS
Land use in he vicinity of the Tea Tin facility is mixed, with corcial
businesses, residential. areas, and petrochemical complexes all located
within a quarter ails of the sits. The nearest rssid.ntial counity.
with several, hundred homes, is located approximately a quarter of a mile
northwest of Tea Tin, within the city Limits of Tsxaa City. Other homes
are scattered to the vest and east, some also within a quszteE of a mile
The majority of the City of La Marque and Texas City, as veil as the
western section of Hitchcock and all of Bayou Vista. lie within a
three-mile radius of Tea Tin. Population estimates were not available Ear
the area included in the three-mile radius. Mcordi.n$ to 1986 U.S. Census
estiaatss, however, the total. population of these four cities is estimated
to be 65, 300 (8). Several unincorporated areas also lie within the
three-ails radius. Dripk4T g water for each of th. cities is supplied by
the Galvsston Coi ty Mumicipal System. The result of a U.S. Environmental
Protection Ag.noy (EPA) drinking water veil survey conductsd in 1985
identifisd a small. u, aae4 beach co inity that uses private veils
approximately one mile south of th. sits (6). Tb. co i1 lty. which
consists of 60 homes, relies on 25 private veils for drinking water.
Three of the 25 veils are screened b.tween 84-104 feet, within the aquifer
of concern.
Swan Lake, a saline lake, is the nearest surface water body used for
recreational activities. Th. lake is located approximately two miles
southe*st of the sit. and is used primarily for recreational fishing and
crabbing. Cosrcial. fishing and recreational activities also take place
in Galveston My, which is located approximately thres miles southeast of
the Tea Tin site.
Tea Tin is an active copper smelting facility that currently employs 80
people. The petrochemical industry, in general. is $ major employst in
the Texas City-La Marqu. area.
‘1
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EVALUATION AND DISCUSSION
The pri .mary environmental pathway of concern is groundvate . The aqw.fer
of concern underlying the site is the upper unit of the Chicot which
extends from approximately 50 feet below the land surface to approximately
900 feet below the land surface. The flow of water is generally in a
southeasterly direction towards Galveston Bay-. The three groundwater
monitoring wells located onsite are screened at 37.47 feet and have all
shown evidence of contam natjon with metals. The two monitoring wells on
the southern half of the site have shown significantly higher levels of
contamjmatjon than the one well located on the northern half of the site
One investigation report concluded that the groundwater contamination
detected could be attributed directly to the remoant acid ponds located a
the site. Reportedly, these pond.. were poorly constructed and
maintained (6).
The majority of residents living in the vicinity of the Tex Tin facility
are on municipal systems which do not draw water from th. aquifer of
concern. Residents in the unnamed beach cc icy located approximately
one mile south of the site rely on 25 private veils for drinking water.
The majority of the veils in th. beach co aniey are screened in the
Chicot at dspths of approximately 200 feet. Three wells, however, are
,screened in the upper unit of the Chicot at depths between 84.104 feet.
No groundwater samples from these veils vets available for review.
Concentrations of etals which significantly exceed drinking water
standards and long-term health advisories were detected La on-site
monitoring veils. These metals includ, arsenic, barium, cadsium,
chromium, copper, lead, manganese, mercury, silver, and zinc. The
concentraejo of these metals found in th . monitoring veils, if present
in pocabls water supplies, could pose a threat to human health. Surface
water samples collected onsic. since 1975 also revealed high levels of
several metals including arsenic, chromium, copper, mercury, nickel, and
zinc. The elevated metal concentrations could potentially impact
downstream surface water bodies used for recreation and fishing. The
surfacs water drainage pathway from the si t. bypass... Swan Lake, but
eventually empties into Galveston lay. Contaminants in suriacs water
could also infiltrate and contamjna e tbs shallow groumdwacsr at the sire
Possible soil coatamf?latLon vu not veil characterized either onsir. or
offsie.. Th. one soil sample collected on-site which was analyzed
detected sufficient concentrations of antimony, arsenic, copper, and lead
to raise concerns about cbs potential for leaching of the metals into
grouridwarsr, contributions to surface rum-off contamination, re-entrained
dust blowing off-property, and direct human contact with th. soils.
Ambient air monitoring conducted in 1986 detected high levels of metals in
the samples. The values listed in Table 2 indicate that cbs potential
exists for excessive particulate emissio g from the Tim Tin property. No
ambient air monitoring baa been conducted to date in rssidential areas,
the nearest of which is approximately a quarter mile northwest of the Tex
Tin site.
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Lou levels of radioactivity have been detected oltitte in association n:h
the tin, copper, and antimony slags and with the company road.s which have
been graded with tin slag. The Texas Department of Health Bureau of
Radiation Control (BRC) has instituted a radiation monitoring progras at
the Tex Tin site (2). rnitial reports from 3onitoring conducted during
the first quarter of 1989 indicat, elevated radiation levels are present
the site. The radiation levels, according to MC staff, are we]l below
federal occupationsl exposure limits, but are approaching the upper limits
of the range of levels generally considered saf, for the general public
The SRC currently has no plans to recomeend i edi&t. removal of the
radioactive material (primarily th. tin and antimony slag), due to the
apparent lack of consistent exposure opportucjtie, by the general public
The MC baa stressed, hovev.r, the need for eventual removal. Since the
radioactive material is intimately associated with the chemical
contamination at the site, the SEC ha., also stressed that any remedial
activities at the site should includ, contingencies for dealing with the
mixed waste. The SEC plans to contimi. a monitoring program at the Tex
Tin facility (3). (The BRC monitoring results v.re flOt availabl, for
reviev at the tias of this report. In.formation concerning the results was
supplisd by SEC staff. Th. monitoring data will be furnished to the
preparers of this report at a Later date.
Tin and copper slag piles are located in th. open on the Tex Tin property,
without cover or a conea inaent/d iversion system. These slag piles, in
‘addition to being a source of radiation, may also be major contributors to
the surface water, soil, and atmospheric contaajnation praviouzly
detected. The area previously used for dr a storage and the Copper
sulfate piles are also probable contributors to the contamination.
The potential effects of exposure to any of the 13 etals detected at the
Tex Tin facility voul.d dep.nd on a variety of factors such as the route of
exposure (inhalation, ingestion, skin absorption), the concentration of
the metal (dose), and th. toxicity of th. metal. The toxicity of the
metal may be determined by th. chemical form of the metal (organic,
inorganic, valence stats) and the rout. of exposure.
Four of th. metals are of particu lar concern because they have been listed
by the EPA as keovn or probable husan carcinogens. Arsenic and certain
forms of chromjt and nickel have been classified by EPA as Group A, known
human carcinog.ns. Ca jt has been designated as a Group 31, probable
human carcinogen by th. inhalation route of exposure.
Arsenic was detected at elevated concentrations in th. soil, surface
water, and gro at,r samples collected onsit. and in the a ient air
samples collected at the perimeter of the sits. Exposure to arsenic has
been associated with an increas, in l g cancer by th. inhalation exposure
route and also an increas, in th. incidenc, of skin cancer by the
ingestion exposure tøUt. Should people on or offsite be exposed to the
axjmi levels of arsenic detected in the envirotaentaj, media at the Tex
Tin sits, they would be at an increased risk of lt g and skin cancer (9.
10).
-8-
t . 3
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In addition, a number of non-cancer effects may result from arsenic
exposure. The prLncipal acute effect of arsenic ingestion is irritation
of the gastrointestinal tract which may cause pain, nausea, vomiting, and
diarrhea. Long-term Lngestion may also affect the Liver, kidney,
cardiovascular system, skin, and nervous system. Inhalation of inorganic
arsenic dusts or aerosols may cause irritation of the respiratory tract,
as well as symptoms similar to those following ingestion. Finally, dermal
contact with arsenic-containing compounds may also result in skin
Lrritation (9).
Given the limited en ironmental sampling data, it is difficult to assess
the non-cancer health risks-posed by arsenic either on or offsite. In a
wors’ .cas. exposure scenario, in which a person is exposed to the maximum
concentrations of arsenic found in th. air, soil, groundwater, and surface
water, adverse health effects may be expected, particularly in children.
In a more reasonabl. exposure scenario based on the availabl. data,
however, the advers. effects would be unlikely given that the heavily
contaminated groundwater found at th. site is reportedly not used as a
drinking water source. Additional environmental sampling data is needed,
especially off-sit, data, before the potential health risks may be more
accurately assessed.
Elevated levels of chromium were found in groun*ae.r, surface water, and
ambient air samples. The three maj or valenc. states (forms) of chromium
differ in toxicity with the hexavelene (chromium (Vt)J form generally
considered to be most toxic. Trivalent chromium (chromium (111)1 is
believed to be an essential nutrient in small quantities, but large doses
may result in adverse effects. Metallic chromium (chromium (0)j has not
been well characterized in terms of human exposure or potential health
effects (11).
Long. term exposure of industrial workers to chromium compounds has been
associated with increased lung cancer. Chromium (Vt) was implicated
through epidemiologic studies and laboratory studies as the form of
chromium which is most likely responsible for increased lung cancer. The
available sampling data for Tez Tin doss not identify th. form(s) of
chromium detected in th. environmental media (Li).
Inhalation exposure to high levels of chromium compoimda. particularly
chromium (VI), may also result in adverse effects on the nasal oucosa
(including irritation and in severe cases perforation of the nasal
septum), kidney, liver, nervous system, and 4 i,i system. Derual
exposure may lead to skin irritation and sensitization to chromium. Based
on the available data, th. concentrations of chromium detected in the
environmental media at Tax Tin would not be expected to produc. the
non-cancer effects (10, 1.1.).
Nickel was detected in surface water, groundwater, and a ient air samples
at elevated levels. Certain nickel compounds, particularly nickel
subsulfid., have been associated with an increased risk of lung cancer
.9.
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nickel refinery dust vorkets. Occupational exposure to nLckel metal. has
not been associated with art increase in cancer. In animal studies,
however, n .ckel metal and other nickel compounds have produced tumors t
general. all njckelc0flt fhn& compounds should be considered potentially
carcinogeflLc (1.2).
The most prevalent non-cancer effect follow .rtg tuckel exposure Lfl humans
i.s contact dermatitis. Inhalation exposure may produce an allergLc
asthma. Researchers have estimated that 2.5 to 5.0 percent of the general
population may be sensitive to nickel (1.2). Once sensitized, even
exposure may result in an allergic reaction. Animal studies have also
indicated that nickel exposure may adversely affect the iurie system
(increased susceptibilitY to pulmonary infections), kidney, reproductive
system, and the heaatol.OgiCaL and hematopotetic systems (10, 12).
Elevated concentrations of cadmium were detected in groundwater and air
samples. EPA classifies cadmium as a probable human carcinogen by the
inhalation rout. of exposure. An increase in 1.uxt cancer has been
associated with cadmium exposures in both occupational arid animal
studies. There is currently insufficient data to consider cadmium to be
carcinogenic by th. oral route of exposure (1.3).
In extremely high doses cadmium may cause gastroints$ tinal irritation and
irritation of th. respiratory tract. Exposure to the aaxi
concentration of cadmium detected in the groundwater samples collected at
the Tex Tin site could result in gastrointestinal irritation. The levels
of cadmium detected in the ambient air samples collected at th. perimeter
of the facility would not be expected to produce respiratory irritation
In animal studiss, short-term exposures to high levels of cadmium have
also resulted in injury to the liver and testes (10, 13).
Long-term exposures to lower doses of cadmium have resulted in effects on
the kidneys such am kidney StOri . formation, arid respiratory effects
includiflg emphysema. Animal studies have indicated that low-dose exposure
to cadnium over an extended period of time may also cause hypertension and
effects on ths ime” system. nervous system, and reproductive system.
The doses at which these types of effects would be expected to occur in
htt .urtI, if they would occur at all, have not been well characteriZed (10,
1.3).
Lead is another metal of particular concern detected at the Tex Tin site.
Elevated levels of lead were detected in soil, goundvater, arid ambient
air sampl’ss. Exposure tO sufficient quantities of Lead may cause damage
to th. brain arid nervous system. the blood, kidney., digestive system and
reproductive system. Small children axe at particular risk for exposure
to lead, more so than adults, due to their t.ndsnCy to conuima larger
aao*mtS of soil during their routine activities arid because their bodies
absorb a greater amo*mt of the lead in the soil they co at (14, 15).
- .1.0-
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In the one soil sample collected on the Tex Tin site, the lead
concentration was 980 ppm. According to the U S. Centers for Disease
Control, lead concentrations in soil and dust exceeding 500-1000 ppm nay
contribute to increased blood lead levels in children (15). Children
exposed to comparable concentrations of lead in soil in a residential
setting such as that found at Tex Tin would be at an increased risk for
adverse health effects. Airborne lead and lead in groundwater would also
contribute to elevated Lead levels in children, further increasing their
risk.s.
Antimony was also detected in the soil sample at an extremely elevated
concentration. Normal background concentrations of antimony have been
reported as high as 10 ppm, although average background concentrations are
considerably lover (16). The antimony concentration detected at the site
was 2,590 ppm.
The potential advsrse effects of antimony ingestion hay. not been well
characterized. Ther. is, however, information available concerning the
effects of inhalation •xposurs in an occupational setting. The potential
effects associated with antimony includ, dermatitis, irritation of the
upper respiratory tract, eys irritation, and irritation of the
gastrointestina’ tract as v.11 as more serious respiratory effects, such
as pneumoconjosis, Reports from the Soviet Union hay, also indicated chat
femal. metaUurgic workers exposed to antimony aerosols experienced higher
rates of spontaneous late abortions, premature births, and unecologic
problems (17, 18),
Elevated concentrations of mercury vers d.tect.d in groundvac.r and
surface water samples. Organic forms of mercury are generally considered
to be more toxic than inorganic mercury compounds although long-term
exposure to both forms may adversely affect the central nervous system and
kidney. Adverse development arid reproductiv, effects have also been
reported. The severity of the effect will be dependent on the form of the
mercury, the route of exposure, and the concentration. Acute exposure to
mercury compounds may also result in gastrointestinal disturbances (10,
17, 19).
The mazi concentration of mercury found in the groundwater samples
collected at the T.z Tin site significantly exceeds the federal drinking
water sr.Aard and could pos. a threat to public health if the groundwater
was used as a potable supply. Potential ht am exposure to surface water
at the site has not been veil characterized.
Bariun, copper, wga s., silver, tin, and zinc were detected at elevated
levels in the groundwater at the Tex Tin site. Elevated levels of copper
were also detected in soil and surface water, elevated concentration., of
tin in air samples, and zinc in the surface water. These metals, although
posing less of a health hazard, do have the potential to cause adverse
health effects. Th. primary effect of each of th. metals by th. ingestion
route of exposure would b. gastrointestinal irritation. By the inhalation
I ,
-U.
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toute of exposure, the primary effect would be respiratory irritation. n
extremely large doses. barium, nanganese, and organic tin conpouxtd .s could
also adversely affect the central. nervous system (10, 17, 19). Exposure
to large doses of silver may result in a permanent discoloration of the
ski.rt, conjurtctLva, and internal organs known as argyria (20).
As with the other metals detected at the Tax Tin facility in the various
erwironmental media, it is difficult to assess the magnitud. of the ri.sks
posed by these metals based on the Limited environmental sampling data.
The presence of barium, copper, manganese, silver, tin, and zinc, along
ui.th the other metals, in th. groundwater, soil, surfacs water, and a r
samples does indicate widespread contamination.
Additional environmental sampling and characterization of the pathways of
exposure will help further define th. extent of th. health risks posed by
th. contamination.
CONCLUSIONS AND RECO)Ol DAflO14S
The Tax Tin site poses a potential public health concern to on-site
workers, residents living in nearby neighborhoods, and possibly to
residents using privat. wells in the unnamed beach co mity located a
nil. south of the sits.
Potential environm.ntal exposure pathways include groundwater, surface
water, soil, and air eontaathatsd with a variety of metals including
antimony, ars.njc, barium, cadmium, chromium, copp.r, lead, manganese,
mercury, nick.l, silver, tin, and zinc. Possible human routss of exposure
are ingestion, inhalation, and dermal contact with th. contaminated
groundvatsr, surfac. water, and/or soil. Inhalation and incidental
Lngescion of airborne particles from Tex Tin emisaion.s or entrained dust
are also potential pathways of concern.
Since the majority of the environmental, sampling data were collected prior
to 1985 using unspecified protocols; more current, systematic, and
standardized sampling of air, soil, groundwater, and surface water is
needed. Specific recomesudations include:
1. Ambient air monitoring should be conducted both onsits and offsite for
the contaminants of concern. Th. offait. ambient air monitoring
should be conducted in locations with ths greatest potential for human
exposure to emissions from Tex Tin (i.e. residential areas,
playgrounds, etc.).
2. Off-sit. surfac. soil samples (top three inches) should be collected
from nearby residential areas and La those areas where contaminant
migration by either air or water is suspected. Samples should be
analyzed for metal, organic, and radioactiv, content.
-12.
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Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 4
Internal Memo Concerning Tex Tin Corporation; From K. Macko,
District 7 Representative, to George Green, TDWR;
September 26, 1977
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Texas D partment of Water Resources
I”.TEROFFICE MI.MQRA DL q
TO George Green, Chief, Field Sup ort (fi
—______
FROM :
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,.; . f Chemical & Metall .1rg3.cal
xsw =30057
Page 2
a. Ni circuit - Nickel sulfate product. Nickel sludge is
stored in drums in the north end of the smelter build ;.
After st elting, ‘waste sludge’ is sold for ether ‘.e:a1
:ecovery. A small quantity removed during vessel c ear.
.s dumped with the slag from the tin process.
b. Fe circuit - Ferric chloride product. GAF sells the c —
party iron sludge contaminated with the herbicide amthen.
The material is stored in the two areas designated en trte
attached map. Runoff would supposedly flow through the
plant to the pond system. A small quantity removed f:cm
the settling tank is disposed of in acid pond B.
c. Sn circuit - Tin ingots product. Product is received
in the following forms: ore sacks from Bolivia stored
on pallets by Ponds A and B, tin residues in 55—gallon
drums stored in ore storage building, and tin ore piled
along Highway 519. After primary smelting, rich slag is
stored onsite. End slag is produced after the electrolyte
process. Gulf Chemical & Metallurgical is planning to
install a new rotary furnace for tin smelting. This new
process will further remove tin from the end slag.
Recommendations :
That the c npany submit a close—out date for the Metals and Trade
ponds as well as plans for closure and reclamation of the metals.
That they su it volume data on the slag, nickel sludge, ferric
chloride sludge, and plant trash produced.
That Gulf Chemical & Metallurgical repair the dikes at old outfalls
002 and 004.
That the company continue the pollution abatement plan as discussed
on 9/20/77 in Austin.
KAM: tar
Attachments: Annual Compliance
Photo
‘2
Approved Signed: x: 4 i’/ ;
- Date: September 23, 1971
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\
Tex Tin Corporation Mining Waste NFL Site Summary Report
Reference S
Internal Memo Concerning Tex Tin Corporation; From K. Macko,
District 7 Representative, to Steve Cook, TDWR;
March 26, 1979
-------
/
‘__‘ ‘dJ • ‘
Texas Department of Water ResourcesENF0RCE1 r
I\TCROFF ICE \IE 1ORA UL%1
Steve Cook, Enforcement Support Section DATE March 26, 1979.- -
r u :eor e reen, Chief, Field Support Section
PROM Karen A. Macko, District 7 Representative
SUBJECT Gulf Chemical & Metallurgical Company, i.s.w. No. 30057 ,
Texas City - - - ______
Z troducti.on :
Gulf Chemical & Metallurgical was referred to the Attorney Generals
office on Augi.ist 10, 1978, for surface and groundwater pollution
offenses. An annual, inspection of the tin smelter was made on
March 5, 1979, wi,th Ms. Nancy Worst, District 7 Representative,
and Mr. Richard Acuff, Environmental Engineer for the company.
Findings :
Gulf Chemical & Metallurgical had beerr reclaiming metals in three
primary circuits.
1. . Circuit - This unit was torn down 1½ years ago.
flickel sludges are no longer generated.
2. Fe Circuit - Due to the loss of the principal buyer
(City of Houston), ferric chloride production has
decreased. The company no longer buys am .then (a
herbicide) Contaminated iron sludge from GAP
Corporation for this circuit. Disposal of
settling tax k sludge in the acid pond ceased
last August.
3. Sn Circuit — The tin circuit has been modified with
the addition of a rotary furnace.
Rich Electrolyte Rotary Future
Slag ) end’ 1 slag ) end slag - - — ->
(371370) Process (371360) Furnace BE V
APR 1 3 ‘79
‘ V I - fTDWR
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d
c..hc u.cal & Metallurg .cal Company
: ge 2
larch 26, 1979
End slag now generated has an obsLd .an-li .ke
appearance. The material .s dwnped north of the
acid pond. The company has hopes of reclaiming
additional tin from the slag in the future.
The ac d pond continues to leak as evidenced by visual seepage a
—.onitor well reports. Refer to monitor well results in IOM dated
November 17, 1978.) On the day of the inspection, an upstream sar le
at FM 519 had a pM of 6.8. Downstream of the ac .d pond, the H
dropped to 4.0.
The metals and trade ponds have not been closed out. Contaminated
runoff enters the southern drainage ditch along the railroad track
and thence flows to the Wah Charig Ditch.
Company officials and agency personnel met with r. Tom Aubry of the
Attorney General’s staff on March 8, 1979. A final injunction will
be proposed incorporating a time schedule for the closure of the
acid pond, collection of contaminated runoff, and construction of
dikes.
KAM:tmr
Enclosure
Signed: Pi4& (I
Approved: feZ .j .1
(-Frv
) 79
‘JTD
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Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 6
Excerpts From Air Quality Monitoring at Tex Tin Corporation, Final Report;
Texas Air Control Board; February 12, 1987
-------
Tex Tin Corporation
Air Quality Monitoring
Final Report
TEXAS AIR CONTROL BOARD
SapLing an Analysis Division
February 12 1987
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INTRODUCT ION
Te ex T. C:;3 2 Tex sa:.g pc ec Was tre secc’ d a
seieS pe— 3 e j ee exas Air Ccrt’c Board (T CB) unde a cortact
..:r :—e rexas a:e C-S - C ). A e t air sa ;lir.g for part c—
rat5 as C _CC at Tex Tin to deter e heavy metal and
eee a —;cSt
T- e Tex Ti Ccr c-at C1 (formerlY Gulf Chemical and Metallurgical) is a
tin s elte, located in La Marque, Galveston County. The facilitY is
located at t e 1 nterseCtiCfl of State Highway 1U6 (SR i 6) and Farm-t0
‘arket Road 59 (F 519). The site is a 2E—acre tract ar.d has several
in _strial solid waste areas. These industrial solid waste areas include:
five wastehater treatment ponds, a gypsum slurrY pond, an acidic ferric
chlor de pond, several closed acid ponds three inactive impound fleflts. an
area of iron sludge contaminated w th Ambien (a pesticide). several slag
piles. ar.d appcXimatelY 20,000 drurs of s3eflt catalyst. Surface wate”,
scil, and sna .O ground water conta. nati0n have been documented at the
s_te.
In Ap’il, 1986, t o TACS staff members and a staff member from the TWC
traveled to Tex Tin to conduct a preliminarY site survey. During this
s te survey, ‘ ne soil sa—ples. a water sar ple. and a vegetation sa Ple
were collected. Analysis of the sa pleS by tne TACS LaboratorY indicated
the presence of heavy metals in all the samples collected.
1-. August, 1986, the Tex Tin facilit! was sampled bY staff members fron
tne TAC9 and T for particulate matter including heavy metals. Metals,
p—irarili lead, tin, and cad u , ar.d aseniC were detected in sore of the
sa;eS. Sore problems with tr.e sampling were found during the qualitY
assu ar.Ce pccess. so a third sampling t’ip was made tO Tex Tin in late
October, 1984. Arsenic has found ifl the samples taken the second day of
th:S t-2•
t
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RESULTS
.as .—stsa—:. e o A:_ 23, i; . N.Ie soii san::es, cre - -
sa—p..e, a cie vet C sa;e ..ere taken. (See Map 1) The soj.
sar; .es e ’ e c ec :e: frc tne top one mon to o e an cne— a O -e 5 c
of t- e soil ms as5, ret tc Co’ a the mate —ia
c c te ree .:—amnabe in wirdy CO ditj3 . The water sampie
coUecte from the a’i Chang ditch on the southeast side site, and the
vegetation sa le as taken from the west side of the property.
Analysis was performed using the X—ray fluorescence Spectro ,eter (xRF)
system mn the T E laboratory. Sir.ce this analysis was for screening
purposes, values were reported as relative peak size and not as concentra-
tions. Large and very large peaks of lead, iron, nickel, and tin were
detected in many of the samples (see analytical report SS i 5—i, Appendix 2).
The second set of samples were collected in August. These samples were
standard high volume particulate samples except that quartz filters here
used in place of glass fiber filters. The samples were equmlibrate ,
weighed, and analyzed by XRF. Results of the analysis indicated the
presence of lead and arsenic in many of the filters (see analytical repcrt
SS 5—2, Appendix 2). The values for arsenic ranged fron 0.07 to 2.3L
micrograms per cubic meter of air sampled, with a minimum detectable lm-.t
of 0.07. The lead values ranged from 0.2 4 to .142 micrograms per cubic
meter, w tn a nmnmr ir. detection limit (MDL) of 0.1k. Accuracy of the
analysis was 97% based on the analysis of standards as unknown samples.
The precision of analysis (average percent difference of 35 values for t-c
analyses each from two different filters) was —3.1%.
Due to scre qLestlor.s ramsed during e quality assurance review of the
August samples, resarpling of Tex Tin for particulate matter has perfor’r e
during October, 1986. These samples were similar to the previous ones
except that glass f ber filters were used instead of quartz filters. The
samples were eq lxbra:ed, wemg ied. and analyzed on the XRF (see ana yt-
ical report SS 5—3, Appendix 2). These samples did not indicate the
presence of e heavy metals reported mm the August samples. The saTp es
were then extracted with nitric acid and analyzed for arsenic usirg
mmductmvely—coupled plasma ei iss om (IC ) spectronetry. This anaiysis
indicated trie presence of arsenic in several of the samples which as rot
detected by the XRF. The concentrations of arsen c ranged from 0.036 to
0.09L micrograms per cubic meter with a minimum detectable level of 0.01k.
Accuracy of the XRF analysis was reported as 99.8% with an average prec-
sion oF 12.6%. The accuracy of the ICP analysis was reported as 96%, . itn
a precision of —4%.
The August set of filters were analyzed for arsenic by ICP in Novembe—,
1986. Results of this analysis confirmed the presence of arsenic in this
set of samples. The arsenic concentrations ranged between 0.016 and 2.23
micrograms per. cubic meter with an MDL of 0.01k. The accuracy of the
analysis was reported as 98%, and a prec:sion value of 0% difference
between duplmcate analysis.
1\
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¼
FIELD SAMPLING
The f —s : sa— :—g t ’ ; t Tex T.’. as a re.imina—y Site survey. es 5 —s.
—.sc: : a-, rer—y a. ss Cf the T :B • Guy Tid—ore of the T. :
1 tre surve . The sap g tea.— Collected the sanp es fr r
t-e e-.—ete— cf the site, neve- actually gc ng on—site. The soil s — es
we-e cc ec:ed alc-g the fence lines on the west and north toundar:es cf
the fa: 1ity a along the railroad tracks paralleling the southeastern
bo der. The a :e— sample was collected from a County ditch that crosses
the property. Outfalls from the plant, the ore Storage area, and the
waste water treatmert ponds, as well as overflows from the acid ponds feed
into this ditch. Tne vegetat sample was collected alor.g the wester—
fence line nea— scil sample #5. (See map 1)
The soil sanples were Collected from the upper one to one ar d one-half
inch of soil based on the assumption that this layer is subject to
reentrax V ent during stror.g winds. In addition, it is assumed that this
layer s representative of the particulate deposition from the facility.
The vegetation sample was collected to determine what elerrents were asso-
ciated with plants in the area. The dry grass collected is representative
of t e vegetat . that surrc the facility on all sides. The courty
d::c—. that taverses the facility e—pties into a canal that forns the
southern bondary of tne facility. The canal empties into Galveston 2ay.
The results of the preliminary survey samples indicated that anr 1er t
sa.tpling for particulate matter was necessary. The sa1 p1j .ng was perf’orme
during the week of August 4—3, 1955. The sampling team was headed by N’ .
Tom Driscoll (TACS) with assistance from staff of the TAOS Regional Office
tr. Houston a d the Galveston County Health Department. Mr. Guy Tidnore
and ws. Kate ArthLr (T :) acted as oversight personnel.
The sa piing bega- on A .igust 5, 1986 at 4:05 p.m. The high volirne a r
sa.’-.ple—s ( i—v; 5) were located along the boundaries of the facility as
shown or v.a; 2. The upwind sampler was located on the south sioe of the
ca- al (off tie prope—ty). The winds were predominantly fro-r the sout’ a:
to 10 m.p.h. The plant/smelter was in operation and emissions were
observed coming from the stac,c and fugitive emissions were observed co-ing
f-or. e plant building. The sampling was terminated at 8:20 p.m., after
255 liLn ..tes of sampl r.g, because of darkness.
Sampling began on August 6 at 7:55 a.m. The samplers were located as
shown on Map 3. The winds were again from the south at 2 to 7 m.p.h.
Sampling corit iued for 480 minutes, terminating at 3:55 p.m. Between 8.20
and 8.50 a.m. there was a light rainsnower. Nowever, the rain was so
light that sampljng was Continued with no interruptions. The plant was
operating normally and fugitive emissions were observed co xng from the
plant/smelter buildings.
The sampling o4 August 7 was similar to the previous two days. The
samplers were located as shown in Map L4• The wjn g Continued from the
South at 4 to 8 rn.p. . Sampling began at 7: 45 a.m. and continued for ‘S0
minutes, terminating at 3: 4 p.m. Once again the plant/smelter was
operational, with fugitive emissions observed coming from the fac l1ty.
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After- te — :- tea returre tt A .st.-, a quality ass —arce a .t
rate o” t-•e 5a:es a sapli g e;.ip’ er.t. The h vols used as t e
cc :e rot have gas ets arour. the filter hold-down
As e- . e:ec j the appearanCe of the filters, the lack of gaskets allowec
pa—t .ate matte in the air to bypass the filters and not be collected.
Afte a re e of the audit information and filters, it was decided that
resa ;.. .as ecessarj to ensure representative results.
The resarr.pling was scheduled for the week of October 13—17, 1966. How-
ever, heavy rains in the Houston—Galveston area during the previous week
had soaked the grounds and the sampling was postponed until the week of
October 27—31.
The sampling team returned to Texas City—La Marque on October 27, 1986.
The hi-vols had been recalibrated in Austin the week of October 6-10. The
sampling team used the first day to check out the portable generators,
coordinate the sampling with the Galveston County Health District, and
choose suitable sampling sites. The plant appeared to be operating
normally, with visible emissions (both particulates and liquid water)
coming from the smokestack.
On Octobe’ 28 sampling began at 10:15 a.r. The start of sarpling -as
delayed because the upwind Site was located on the Tex T ri propety arid
permission to sample on the property was required. The hi-vols were
located as shown on Map 14• The winds were predominantly from the east
with a slight southeast component. Several large areas of standing wate ’
were noticed close to the fence on the western boundary of the facility,
indicating at the ground was still very wet from the rains the previous
two wee ’s, and tnere appeared to be some run—off from the facility into
the bar dit:r along Sri 1i46. Sampling cont nued for z 80 minutes, te rr.-
nat ng at 6:15 p.m. Du ng the hi—vol set—up, the emissions frori the
stac were getting noticeably weaker, and by the end of the day’s sa—-
pling, had almost completely disappeared.
On October 29, the sampling began at 8:U5 a.m. The h —vols were located
as sriown on Map 5. The winds were again from an easterly d rectiOr.. The
sampling continued for 8O minutes, terminating at 5: 5 p.m. There we-e
only ve-y weak visible emissions from the smokestack and no liquid water
was preser.t with the visible particulate emissions. There as so e site
work in progress during the afternoon. A dumptruck was dumping loads of
what appeared to be slag from the smelter, and a bulldozer was working or.
other piles of slag at a separate location on—site.
On October 30 the hi—vols were located along SH V46 near the bridge over
the canal. However, as the hi—vols were being loaded with the filters the
winds shifted to a more northerly direction and were blowing parallel to
SH i’46. The sampling was discontinued and the team began to relocate the
hi—vols along the railroad tracks across the canal, the southern boundary
of Tex Tin. A..s the hi—vols were being reloaded tO begin sampling, the
winds shifted back to the east. The hi—vols were reloaded into the
sampling van arid once again located along SN 1M6 as shown on Map 6.
Sampling began at 1 :15 p.m.’and continued for 2 ’O minutes, terminati g a:
5:15 p.m. During the sampling, there were no emissions visible from t
srnogestacK and t..iere was no sitework on the facility. A break in the
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a:- : ? -ce c t e -es: bo r a—y —a
rea t e-e as a- a—ea e—e r -otf ! ‘ the tac 1ity ha
ve eta: c- • a- : ere -as an O : y fil /s:t f oat ng on t e wate- :-
ta . ::-. ‘ . -ate’- sa—;e we-e cc:ected S rice the tearn :: a e
aj s .:3::e ccllect::, jars.
-e sa—;:.- tea— ‘ -e:,..rled to Aust on Oct3ber 31. As t ’e sa—;:.i tes—
was lea g Texas Ci:y—.a Marque, it was noticed that Tex Tin ha s:a-te
nc-r-a c e’-a: :ns again. There were Substantial e1n ssior s co i- g frcc the
5r’ okestack, both particulate and liquid water (no visible e’r..sslols
etersination .as tnade). The sar ples were given to the TAS Laboratc -j
for analysis by both XRF and ICP (arsenic only).
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Q JALlTy ASSURANCE
The high vcli. —e air sa:lers use t e Tex Tin sampling were ca i ra•e - .
in Aust -.- g ye week p”ior tc ye t c sampling trips. The sa—p:e—s
we—e au ted withii ore wee of their retu—- f—or sanpling. It has
t e pcst-sanpling a .t that estions were raised concern g the A gus
hi-vol sarpling. Witnc.it gaskets on the filte’ hold—do..n plates, substan-
tial air leaks could exist around the filter. These leaks would allo.
particulate matter in the air to bypass the filter and not be collected.
1 owever, the air would pass through the throat of the hi—vol and be
measured as total volurre of air sampled. A check of the filters indicated
that this had indeed happened. The filters indicated that high—volune ax-
samplers 02531 and #5980 did not have gaskets around the filter hold—do .n
plates. Post—sampling audit of the flow rate indicated that all satr.plers
were within the 15% flow rate error as required by the sampling plan.
The results of the QA audit of the August sampling trip led to the dec-
sion to resa- ple Tex Tin. Class fiber filters were substituted for ye
q.zartz filters, after it was determined that the glass fiber filters
contained no contaminants that would interfere with the analysis.
As stated above, all hi-vols to be used at Tex Tin were calibrated prxo—
to the r being taken to the field. Results of the post—samplx’ g a d t of
the flow rates from the October sampling indicated that all sample-s were
well within the 15% error limit as specified in the sampling plan.
\
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DISCUSS ION
Te es :s :f t:: La. t. s r.n -d tate t a: eav.
—: _— off—s . o, t e Tb-s co—:e—a :
te.- t:-e v j’ ...de:y de e-d. g on the state of tr e g—c -. a
a-: c: —s:.:r s.
Te A.g. .s: sa l.-.g as performed during dry weather with the plant at
nor al pcduc: c-. The production status was determined fro— the amour.t
cf activity at the facility, the emissions from the smokestack, a d t ’ e
fugitive emissions frorn the bu ldings on the facility. The only rainfall
as t e s o —t shc. .e- repo—ted cn the second day. The winds reported were
no-rr al fo— the s..——e- ‘nonths along the Texas coast. The analytical
results should be considered as representative of what would be found in
the ai in the vicinity of a tin smelter. The samples are basically
fugitive emissions frcn the buildings and wind—blown dust stirred—up fc n
the g-o’u d d rir.g normal plant operations. The emissions from the smoke—
s:ac had little effect on the results due to the close proximity of the
sa pers to the pcperty lines of the facility and the height of the
sro estack er.iss.on point above t .e ground.
The lac of filter gaskets on the Co llocated hi—vols lowered the a ou t of
pat c, .ate ratter collected on the filters while the total ai— vc —e
sanpled was not affected. This means that the concentration of a reported
contaninant as at least as great as that reported and probably hig e—.
The lack of gaskets on the filter rtngs allowed air to leak around the
filters and tr.e particulate matter to bypass the filters and no: be
caught. However, tcth t e air passing through the filter and tne air
lea ing around t .e filte- would pass througn the throat of the hi—vol and
be measurec as tne total flow through the hi—vol. This would result in a
g—eater anoi.r.t of a — repcr :ed sam ied than was actually the case. Sirce
tnere s no ..ay tO accurately estimate the amount of air that leaked past
the filter, the results reported should be considered as minimum values. -
The protien of filter gasket leak and resultant minimum—level determina-
tion of e—isssio .s led to a decision to resample Tex Tin. As was stated
in t e field sampling section, heavy rains in the area postponed the
sar%ing for two wee,s. The two-week delay was not sufficient for the
g-our d to dry to the level that existed during the August sampling. There -
were large pools of standing water covering portions of the facility, and
there was also the appearance of water draining from some of the piles of...-
slag visible from the sampling van location. Also, .as stated previously-.--
the smelter appeared to have shut down during the. sampling period since - --
there was little evidence of plant operations except for a dumptruck off-
loading what appeared to be slag from the smelter; into the spoils -area.
The reason for this shut-down has not been determthed. The emissions from
the smokestack on the second and third sampling days appeared to be natu-
ral draft emissions caused by wind flow across the stack exit. .
This change in sampling conditions from the Ai.igust conditions sho ld _
ccnsiiered advantageous to the project.- The AUgust. sampling results
should be considered the base or low point emissions from a facility that
is fully operational, i.e., the emissions are at least this high. The
October results snould be considered as representative of a facility that
is not operating and are the minimum emissions which would come from the
facility. Witr t e above in mind, the results from. —October sampling —
ind.cate tnat there s an ongoing release of arsenic into the air.
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COMPARISON OF ARSENIC LEVELS IN AUGUST AND OCTOBER
T c2 . .a:cra:: use ctively—ccL e lasra (IC ?) spec:-:—e:-,
aflalyze the pa—::cu:ate sa ples fror’ Tex Ti” for arsenic. The I e:-::
is rc-e sens::ve fc arse’ c as sho r by the cetectni .
The results of the sa’1 pling at Tex Tin on iffereit dates will te cca-
using the arsenic results as a basis for cor parison. All values are
reported in micrograms per cubic meter of air. The nini detectatle
level (M0 ) for all samples was O.O micrograms pe” cubic rreter of air.
Sanple ID Location c: :
August 5, 1986 (Day 1)
2981 Upwind <“0.
2982 Along SM 1U6, S of FM 519 Intersectior.
2953 Along FM 519, E of office C i5
295w Collocated along FM 519
2965 Collocated along FM 519 0.032
August 6, 1986 (Day 2)
2986 Upwind — -‘
2987 Located along SM 1 6 near FM 519 Intersection ( ‘ ‘0_
2958 Northwest Quadrant
2989 Collocated along FM 519, North of smelter 2.23
2990 Collocated along FM 519, North of smelter
2991 Along FM 519, E of office c.c 2
August 7, 1986 (Day3) - -
2992 Up - ind ‘ - - <
2993 Northwest Quadrant < “ 2...
299k Along FM 519, near SM 1 6 Intersection
2995 Cclloca:ed along FM 519, Norir of srrel:e-
2996 Collocated along FM 519, North of smelter C.36
2997 Along FM 519, East of office
2998 Upwind
October 28, 1986 (Day 1)
Ui Upwind, along FM 519 at County D tch
0 1/i Along SM 1 6, West of slag piles
Di/2 Collocated along SM 1 16, West of slag piles
D1/3 Collocated along SM 1m46, West of slag piles
Di/ Along SM 1 6, West of slag piles ( “0. -
October 29, 1986 (Day 2)
U2 Upwind, along FM 519 at County Ditch
D2/1 Along SM i 6, West of smelter building C 29.
02/2 Collocated along SM 1m46, West of slag hopper 0.0 2
02/3 Collocated along SM 1 6, West of slag hopper C 236
D2/ Along SH West of slag piles C
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a, 3 ,
aorg ? ‘ a: :..—:y D.tci
C3’ Sr{ 1-.6, hest of s .ag piles
2 c :: cated aong Sr. fl45, v est of slag piles
‘3 C 1ccated a ng SH 1 6, West of slag piles
:3’- A: g sH , est of slag piles
The August s ples we-e collected during dry weather with the plant
ope—ating nornaUy. The October samples were collected after heavy “a r.s
had falen over the area and there we—e several large pools of stand ng
wate- on the plant g—o nds. Also, the October samples were collected nen
the plan: was shut do -n.
None of the upwind sa—ples had arseflic concentrations at or above the
detectabie level. This indicates that there is little or no
bac g—o n ccn:r but n of arsenic to the air entering the Tex Tin
facili: . Similarly, the-e were no down ind arsenic concentrations
repor:e: above backgroun: levels on t .o of the October sampling days.
Most probable causes are that (a) the round was wet from previous rains;
(b) the par.: was no: ope-a :ir .g, ard (c) :e—e was no work going cn
o n-s :e.
W :n d—y weathe— and the plant under what appeared to be normal operating
cor.ditior.s, arsenic was release to the air from the Tex Tin fa:il ty.
Arsenic was detected in samples collected downwind of tne facility on each
of the tr.ree sampling days in A gst. The sarpling teams noted that tr.e—e
were substantial fugt ve emissions cc ir g from the smelter building on
the second sam;l -.g day. Also, there was vehicle traffic on the plant all
:hee days. Probable sources for the a—senic are the smelter building and
t e plant g3 nzs. As van. les trave—se the plant, they could ree-.:—a.n
a-se- c t a: nas se:ted out of the a.r onto tne grounc. In the Octo er
sarpling, arsenic was seen in the downwind samples after vehicles had been
drvir.g cn—site.
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COMPARISON OF LEAD, TIN, AND CADMIUM LEVELS IN AUGUST AND OCTOBER
T :E _at a: use: x—a f1. o’esce ce (X F) spectroscopy to analyze
t e Aug_a: a— 0c:o e sarples for iead, tin, and cad. ium. AU values ae
epor:e —.c—cg a .is pe cutic meter of air. The m rin i, detectatle
le els ‘_) fc a.l samples were O.1U (Pb in Aug), 0.09 (Sn in Aug), 0.10
(Cd in Aug), 0.27 (Pt in Oct), and 0.16 (Sn in Oct). The higher MDLs in
the October sar;l ng result fr the difference in volumes of air sa pled.
Sample locations are as Indicated on the maps in Appendix 1 . (NOTE: A
blank space indicates that the element was not detected in that particular
sample.)
Sample U Lead (Pb) Tin (Sn) Cad ium (Cc)
August 5, 1986 (Day 1)
2931
2952 O.2
2983 0.31
296. 1.25
2985 1 .56
August 6, 1966 (Day 2)
2966
2987
2988
2989 ‘4. 2 103.6 O.6
2990 1.20 27.5 0.15
2991 1.22 1.35
August 7, 1954 (Day 3)
2992
2993
299 0.29 5.95
2995 2.C1 13.9
2994 3.61 25 . 0.17
2997 0.68 2.05
2998
October 28, 1986 (Day 1)
No Pb, Sr., or Cd detected on any samples.
October 29, 1986
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\
Se,era :c-: s.:-s— te a. fc— :e data prese :ec a : .e.
1. r e :ea: :_— c- 5 cc..: te a_:c—:t.:e ex- au5t lead tecase
of :-e_::a:.:- : :-e sa:.e a’c:e:a.se t-e X F does no: .s :.—; s-
ex-a_s: lear f—c— —::e .s .ea .
2. The t.— f :..- c- A g st 5 probably comes frcr. Tex Tin due to sa—::e-
loca:.cr a’ la:< of ti fl the uphind sample.
3. The higr. lea: a- c tir levels found on August 6 result tro— Tex Ti-i
essior.s. s based on sampler locat.on, comparison to cthe— san;le
results, and sa—pe— operato— cor er.ts concerning fugitive e issicr.s frc
the srnelte— bu o. -g.
. The lead and tin levels found on August 7 are representative of typical
plant em ssions. The collocated pair of samplers (2995 and 2996) give
comparable rest lts for both lead and tin. These samplers were located
the a—ea of g—ea:est e ss.c-s a—.d are s bstar.:ially hig e than the o: e-
two sa—;le—5 located do.—-.-: of : .e pla—:. Also no lead o— t: were
detected up ind.
5. The ead detected t e up . d sample in October cculd be aut: :: le
lead.
6. The tin de:ec:e the dc n ind samples cores frcr the slag piles c-
ground at Tex T . The tin was st rred up by the operations of tne
durptruc and/or blloczer cperating on the slag p.les.
As stated n t e F.ed Sa—:l g sect o , the Tex Tin facility as ope—a—
t rg nor—ally d -.-g t-e gst sa—p_ -.g and was shut down duing t e
C:tcbe— sanp_ . . s:, tne gron: as dry in August and -et n :: -.
The prese ce of t e lead .- t e e —issions during the August sanpli g i O. -
cates tr.a: the ea: s being em t:ed fron tne srelte- du r.g tne sre: .g
prccess. Th.s is borne out by the fact that lead was not detected
tne Octobe- sa plin; when tne smelter was shLt down. Fu—ther ore, tne
found i all the sa ;es indicated tnat the tin comes f-or tCt the s e-
ter (prir —y source) and fron tin tnat has settled out of t e ai a-d s
reen:ra —e: bi ve :e traff : or i’ ds.
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I’
\
Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 7
Letter Concerning Tex Tin Corporation;
From I1.L. Ne inan, Tec Tin Corporation,
to Martha McKee, EPA Region VI;
January 25, 1985
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TEX TIN CORPORATION
HIGHWAY 319 • P. 0. BOX 2t30
tEXAS CITY, TEXAS 775922130
rELEX 509411
Jafluary 25, 1985
CERTIFIED MAIL — RE JRN RECEIPT REQtISTED
Martha McKee, Chief
Compl arte Section
USEPA, Region VI
1201 ELm Street
allas, Texas 75270
Re: Site nspectiori Report of April 20, 1984; EPA Site
Number TX 02364
Dear Ms. McKee:
Tex Tin Corporation. formerly Gulf Chemical and Metallurgical Conp rty,
concerned with the bias in and created by the above report. The C a y
must by this correspondence protest the colored report submitted by
site inspector. Please accept the following co ents offered it a sp t:
of cooperation with the Agency. -
The report of subjects chat are not environmental threats, omiss .ort
details concerning present and past environmental corrective ac:Lc s b’ ,’
the Company and utilization of outdated, misinterpreted information, . Led
to give an accurate account of current environmental conditions at the
Texas City Plant.
In particular those items concerning: (1) The acid pond, (2) Radjoact ve
Burial site, (3) Catalyst Storage. (4) Slags, (5) Ratef all run—off ar d
surface vatet contamieation. (6) Emptied ponds, (7) Ground water,
(8) Amiben contaminated iron, (9) Threats ço public heaLth, (10) Cc ttani ta::
of railroad borrow ditch, (11) Inadequate security, and (12) Emphasis f
1979—1917 rsports.
IT i i L Tb. report emphasized “the acid pond” and leads one to c e c i tiorr
that th. pond is creating gross environmental damage while the Con; any
no efforts to alleviate the condition. Nothing could be further f:m the
truth. The Company has been actively pursuing the disposal of the uid
and closure of the pond. At the time of the inspector’s visit and : her
knowledge. ths Company in full cooperation with the Enforcement Di.’; t io of
the Texas Department of Water Resources had:
SUS1 O 1Y 0 nhI4 ’14T1O MITA&5 $ *INIeM$ COI,Oe*T .OM
-------
A. Co .nert:ing in 1979 rie C mpany speit it . ss i
$300,000 to :or.struct an evaporatian system co
cortcerttrae the product In t te a:IJ ponds n an
ac:enpt to be able to sell tne resulting ferr c
chloride. ThIs plant was unsuctessful desp te
efforts made by the company over art 13 onth span
and the expenditure of at least 200,00O in
operatIng costs.
3. Resear hc . developed and submittcd a plan :,
neu:raII:e the acid pond. The plan was ul: .- a:e1.y
discarded w.th the concurrence o the DtJR because
of the volune of sludge ger.er ced.
C. Compiled and submItted an 800 page deepuell
injectIon application to the TDWR. The app1ica .ott
was encouraged by the Enforcement Division,
accepted and approved by the U.t.C. and acted
upon by G fC. The deepvell is to be totally
devoced to the closure of the acid pond.
GCNC had previously nads efforts to mitigate the impact of the acid oc: y
(A) Routing plant side pond leakage through the plant
drainag, system and treating it in the NPDES lime
and settle treatmSnt system.
(8) Da.ing and recirculating contaminated Wah Chartg
ditch water through the plant NPDES system. The
dam was left in place until obviou, flooding of
TM 519 necessitated removal. The Company has
offered to Jerry Saunders, E.P.A., Region Vt, to
install a new dam and treat the ditch waters until
the contents of the acid pond have been injected.
Claims of erosion and berm instability by the inspector were subjective and
uncru.. Asria]. pictures taksn years ago show virtually the same degree of
erosion as exists today. Ths berm. were stable enough to withstand
undiminishad hurricans winds and rain in both 1961 and 1983 without .oss of
th. contents or structural integrity.
Afl the above was known by the inspector who neglected for unknc n reasons
include thorn in the report. Contrary to the impression given by : e repcrt
GQCC has and continues to seek a satisfactory solution to the aci.I pcnd.
Company has contracted Golden Strata Services and McClellan Engt eertng fo
the detail engineering and installation of the dssp well faci.Ity. .e
estimated project cost of 1.2 million dollars should demonstrate the serlo
of the co itmsnt the Company has made to an envirorentally acceptable so
to the acid pond.
\
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tTLM 2 : The re crt raises : sec .. u on:L j
L . ndfilL tich is atart: un:re. T’ e rtuL . L is f ....
xas De rtn tt cf - a.:h - er .i:c-t :.o. S—’ 2 0. T e gLassy -
silLcate slag is :r3tn a i! t study o the xtr ctian f biz th f:— a
bisnuth—uranium c. ly t. ?r ducticn opcra:tons eru never at— ,: .
The slag frorn the pilot was buried in a nanner that net or excecded -1
requirer ents. Approxinately 10.37. of the all .iable urartiun -:
so uried. The site is praperly capped with cLay, - arked above g: d
wi:h four feet of ver: cal granite marker and duly reccrded i tne er:
deed. The site has been inspected by H personnel several tirnes a d —cers
all criteria. All of the above was nade known to the tnspec:or .: uas
neglected in the content and su acion of the report.
ITEM 3 : The report notes spent catalyst and metallic solids rt asscat...
wi.th toxicLty and conca ination. GCMC stockpiled catalyst in ant :.p n
of bu .Lding a plant to extract val.uable metals, i.e. o ngsten. CCXC per-
formed E.P. toxic .ty tests on the catalyst even though the natertaL .as :
considered a waste. The RCRA tests affirmed the noncoxic nonreact e
of the catalyst, therefore the material was consi dered safe for o :s ce a::
GC tC realized the TD was concerned w4.th the catalyst storage t -
data to Mr. Bob Lee, Enforcement, TDWR. The data clearly shows that :e
problem of the catalyst is visual impact rather than envtron ental .a::.
CCMC made further efforts to alleviate TDWR concerts by moving ll,266.CjCO
pounds of catalyst to inside storage for future use and disposing of
6,500,000 pounds of low grade material. The disposal was at C e — as:e
Management’s Port Arthur secure landfill. Marketable r main ng : :aL .s:s
have been retested to RCBA standards. CRA analyses actacrted.
The catalysts have diways been stored inside the dikcd plant area e:e a
contact and nortcontact rainfall is collected and directed to :he N?DES sy :
The inspector was aware of the test results submitted to the TD R, Cc—pany
efforts to remove catalyst from outsidi storage, disposals, ar.d tho
with drainage to the NPDES system.
ITEM 4 : The report noted slag materials generated by the nonferroLs
smelting operations and implied toxicity and water cont inacion. The WR
has collected and analyzed the slags from the operations on numerous o::asi
but have never notified the Company of any adverse results. The Cc’pany
submits the attached analyses on the old and new slags as proof of the i er
nonoxtractabis nonharmful nature of the material. The analyses are fcr :o:
content. E.p. toxicity and the deionized water leachate. The inspector was
avers that tha materiel was inert and disposed on Company property ur. er t
Texaa Solid Waste Code number of 371370.
ITEM 5 : The report claimed contamination of surface water and rainfall
runoff. Ths report led one to asst uncontrolled runoff from all areas of
the plant to adjacent surface waters. To reiterate, the inspector was ova:
that the total plant was bermed, all water collected and pumped to c’e L?D
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Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 8
Excerpts From Potential Hazardous Waste Site Inspection Report,
Gulf Chemical and Metallurgical Company;
EPA; February 21, 1980
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.
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-------
Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 9
Excerpts From Drinldng-water Well Survey at Tex Tin Corporation;
Ecology and Environment; October 4, 1985
-------
REF
£COt.OGY AND ENVIRONMENT, INC.
REGION VI
MEMORANDUM
TO: Keith Bradley, Region VI — RPO
FROM: R. Roblin, FIT — Geologist ØJ
THRU: K.K. Malone, Region VI • RPM
DATE: October4 , 1985
SUSJ: Drinking Water Well Survey at Tex.Tln Corp., Teras City, T X (TX2364)
TDD#R6-85 09.19
.
FIT member, Ray Roblin, was tasked to conduct a drinking water well survey
within a 3 mile radius f Tex.Tln Corp. (Ai A Gulf Oiemical tallurgy), in Texas
City, Texas. This area Includes parts of the cities of Texas City, La Marque,
Bayou Vista and the extreme eastern edge of Hitchcock, Texas. The survey was
conducted on September 30 and October 1, 1985.
The main purpose of this Investigation was to ascertain whether any residents of
the area are presently using groundwater for domestic supplies. The main
aquifers of concern are the t upper sand units which are associated with the
Beairont Formation of late Pleistocene Age. The Seaunont Formation consists
mostly of clay, silt, sand and includes mainly streem channel, point bar,
natural levee and backswemp deposits, and to a lesser extent coastal marsh and
mud flat deposits, Its thicknis is approximately ioo’ In the Investigation
area. Lower stratigraphic Pleistocene units that are not water producers are
the ntgomery Formation and the kntley Formation. These units comprise
approximately 150’ of section. Below thos* units is the Willis Formation also
of Pleistocene Age. This unit consists mostly of clay, silt, sand and minor
5llic eog gravel of granule to pebble grain size. The Willis Is the next lowest
water bearing formation below the $eaIaI ont Formation, and it s thickness is
approximatel 7 75’ (Sellers eta)., 1981).
The Initial Inv. tigation focused on the location and extent of the cities of La
Marque and Texas City’s water lines In relation to the area of concern. Mr. Ron
Fleenor of the titles of La Marque and Texas City’s water department was
Interviewed. He stated that..,.
—City water lines serve all residents within the city limits Inside the
three mile radius from the site.
—La Marque his 3 deep (300’440’) water wells that are maIntained f r
emergencies only and ‘at this time only 2 are operational.
-In a recently annexed area, there were 3 private wells. These wells are
used for lawn watering only.
(Fleenor 9/30/85).
\
-------
The three private wells referred to by Mr. Fleenor Ire located oc tp e % 1 te
approximately 2 1/2 miles. The wells are 30’, 40’ and 120’ in dept
respectively. The wells Ire Shown on the attached map to reference I.
Ms. Fay Fraboni of the Galveston County Municipal Water District
concerning a beach house conrunity that Is located approximately
the site, which is the City of Bayou Vista. SO j
•Bayiou Vista is supplied with water from the Galveston County Systen
uses no ground water (Fraboni 9/30/85).
The convnunity Is identified on the attached map as Reference 2. Directly
of Biyou Vista 1 north of State Road 6, just west of Highland h)vu, is IflOther
small beach house conrunity consisting of approximately 60 homes. These hOmes
are supplied by 25 wells. This information was determined by canvasing the
coemunity. Most ( 95%) of these homes are used only on weekends and
according o resident, Ralph Nefntz of 7115 W. Hunttr ive, Hitchcock, Texas
Mr. Heintz stated that his well is 215’ deep and that most in this COflVflUVIlty Ire -
also approximately 200’ deep. By checking drillers well logs, filed with
T.D.W.R. In Austin, at least 3 of these wells ar between 97’-lOS’ which f ii
the aquifer of concern (TOWR). This community is located on the attached map to
eference 3.
Ms. Rose TelHs, City of Hitchcock Water Department was contacted concerning the
extent of water lines.
—City water lines extend to their city limits in the western edge of the
Investigation area.
-Water is supplied by the Galveston County Municipal System -
(bills 1011/85).
In conclusion, no other industrial or irrigation wells were located within the
lifvestigation ares. The communities within the 3 ails radius of the site are
supplied water by the Galveston County Municipal System. The only domestic
wefla used for drinking water are the 25 wells located in the unannexed beach
house coemunity located wsst of Highland Bayou. At least three of these veils
are in the aquifer of concern.
-------
Tex Tin Corporation Mining Waste NPL Site Summary Report
Reference 10
Letter Concerning Tex Tin Corporation;
From Robin Morse, Esq., Baker and Botts,
to Bob Hannessehiager, EPA Region VI;
July 15, 1985
-------
qO
BAKER 6 BCTTS
.C 5—C -. aZ.
—51 ’ ’ XA3 7 OO2
C_C 0NC 7 229 23’ 1
32 229 730
C* ‘9-2,79
a’O JP11t0 Oar.. t ea
‘0 Cr.r.5 ’tvr. a . C r. 00 (S? ‘ -—
20006 ! S
G—36,375 July 15, 1985
lr. Bob Hannesschlager, Chief
Superfund Branch (6AW—S)
tJ. S. Environmental Protection Agency
- Region VI
1201 Elm Street
InterFirst Two Building VIA
Dallas, Texas 75270 FEDERAL EXPRESS
RE: Tex Tin Corporation - Texas City, Texas
Dear Mr. Hannesschlager:
As counsel for Tex Tin Corporation, we have
recently been informed that the Texas Department of Water
Resources has’ forwarded a Superfund ranking package to
Region VI with respect to Tex Tin’s Texas City, Texas plant.
We have been supplied with a copy of the ranking package by
TDWR and have reviewed it with company representatives. The
purpose of this letter is to inform Region VI that, as
explained below, the TDWR assessment appears to be grossly
distorted and should not serve as a basis for Superfund
action. We would urge Region VI to re ect the referral
action and are ready to work with EPA in order to obtain a
truer understanding of the environmental situation at the
plant.
Beginning with Figure 1, the NHRS Cover Sheet, we
would first note that there is no formal state enforcement
action now pending. The referenced lawsuit was dismissed
for want of prosecution on December 12, 1984.
Ttirning to the next page, entitled “Fact Sheet”,
there are “hazardous waste” facilities at the plant. The
plant’s wastewater is not a listed or characteristic hazard-
ous waste stream under RCRA. As for the referenced acid
ponds, including the 18 miLlion gallon pond alleged to
contain “highly acidic ferric chloride waste”, these units
are all exempt from RCRA pursuant to 40 C.F.R.
g 261.4(b) (7), the exclusion for wastes resulting from the
extraction and processing of ores and minerals. Further—
nore, the company has been pursuing an active program of
neutralization and removal in connection with the old acid
-------
Mining Waste NPL Site Summary Report
Torch Lake
Houghton County, Michigan
U.S. Environmental Protection Agency
Office of Solid Waste
June21, 1991
FINAL DRAFT
Prepared by:
Science Applications International Corporation
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
-------
4/
DISCLAIMER AND ACKNOWLEDGEMENTS
The mention of company or product names is not to be considered an
endorsement by the U.S. Government or by the U.S. Environmental
Protection Agency (EPA). This document was prepared by Science
Applications International Corporation (SAIC) in partial fulfillment of
EPA Contract Number 68-W0-0025, Work Assignment Number 20.
A previous draft of this report was reviewed by Jae B. Lee of EPA
Region V [ (312) 886-4749J, the Remedial Project Manager for the
site, whose comments have been incorporated into the report.
-------
Mining Waste NPL Site Summary Report
TORCH LAKE
HOUGHTON COUNTY, MICHIGAN
INTRODUCTION
This Site Summary Report for the Torch Lake Superfünd Site is one of a series of reports on mining
sites on the National Prionties List (NPL). The reports have been prepared to support EPA’s mining
program activities. In general, these reports summarize types of environmental damages and
associated mining waste management practices at sites on (or proposed for) the NPL as of February
11, 1991 (56 Federal Re2ister 5598). This summary report is based on information obtained from
EPA files and reports and on a review of the summary by the EPA Region V Remedial Project
Manager for the site, Jan B. Lee.
SITE OVERVIEW
The Torch Lake NPL Site is located on the Keweenaw Peninsula of Upper Michigan (see Figure 1).
For over 100 years, the area surrounding Torch Lake was the center of Michigan’s copper muting,
smelting, and milling activities. Over 10.5 billion pounds of copper were processed in the area
between 1868 and 1968 (Reference 2, page 5). Copper-contaminated tailings were pumped, with
process wastewater, into Torch Lake or onto property around Torch Lake (Reference 1, page 1-2).
An estimated 200 million tons of tailings were pumped into Torch Lake, reducing its volume by at
least 20 percent (Reference 2, page 5).
The surface area of Torch Lake is 2,717 acres; it has a mean depth of 56 feet and a maximum depth
of 115 feet (Reference 1, page 1-1). Several small creeks and the Trap Rock River discharge into
Torch Lake (see Figure 2). The Torch Lake watershed is approximately 77 square miles. The
primary land use in the watershed is farming of northern hardwoods and a few dairy and potato
farms. The communities of Lake Linden (population 1,181) and Hubbell (population 1,278) are
located on the west side of Torch Lake (Reference 1, page 1-2). Torch Lake feeds into the
northeastern arm of Portage Lake and then into Lake Superior, via the Portage River. The Portage
Lake and River are part of the Keweenaw Waterway, a shipping channel across the Keweenaw
Peninsula. Torch Lake is 14 miles from Lake Superior (Reference 2, page 1).
In 1983, the Michigan Department of Public Health (MDPH) issued a fish consumption advisory on
all Sauger and Walleye caught in Torch Lake (Reference 1, page 1-6). Also in 1983, the
International Joint Commission’s (UC) Water Quality Board designated Torch Lake as a Great Lakes
1
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Torch Lake
CANADA
FIGURE 1. SITE LOCATION MAP
M
Torch Lake
site
WISCONSiN
MICHIGAN
2
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Mining Waste NPL Site Summary Report
FIGURE 2. TORCH LAKE AND PORTAGE LAKE (HOUGHTON COUNTY,
MICHIGAN)
3
-------
Torch Lake
Area of Concern (AOC). This designation was based on MDPH’s fish consumption advisory, the
frequency of tumor occurrences in fish, the presence of metal-contanlin2red sediments, and the history
of mining and disposal practices in the Torch Lake area (Reference 1, page 1-7).
Torch Lake was listed on the NPL in June 1988 (Reference 2, page 6). The Torch Lake Superfünd
Site has three Operable Units. Operable Unit 1 includes surface tailings and the contents of buried
and submerged drums along the western shore of Torch Lake. Operable Unit 2 includes the
potentially contaminated media in and around Torch Lake. The media to be investigated include soil,
ground water, Torch Lake sediments, surface water, and the biota (Reference 1, page 1-10).
Operable Unit 3 includes other tailings sources in the mid-Keweenaw Peninsula, including the North
Entry, the northern portion of Portage Lake, and tributary areas (Reference 1, page 1-11). In
September 1988, a Remedial Investigation and Feasibility Study were initiated, by EPA, for Operable
Unit 1 (Reference 2, page 6). The Remedial Investigation for this Operable Unit was completed, and
the report was submitted to EPA in November 1990. Remedial Investigations for Operable Units 2
and 3 are currently in progress.
OPERATING HISTORY
Mining of an elemental copper belt extending from the northern tip of Keweenaw Peninsula (100
miles to the southwest of the site) began in the 1860’s. The first copper mill along the shore of
Torch Lake opened in 1868. At the mills, copper was crushed, grinded, and driven through
successively smaller meshes. Copper and crushed materials were separated by gravity in a liquid
medium. The recovered copper was sent to a smelter, and tailings were disposed of with process
wastewaters into Torch Lake or on land around Torch Lake. Mining activities in the Torch Lake area
peaked between the early 1900’s and 1920 (Reference 1, page 1-2; Reference 3, page 2).
Beginning in 1916, technological innovations allowed for the recovery of copper from previously
discarded tailings in Torch Lake. The submerged tailings were collected, screened, recrushed, and
gravity-separated at one of three reclamation plants (Reference 1, page 1-3). These plants included
the Calumet and Hecla (1916), the Tamarack (1925), and the Quincy (1943) (Reference 5, page 2).
Initially, an ammonia-leaching process was used to recover copper and other metals from the tailings
(Reference 1, page 1-3). By 1917, a flotation process that agitated ore, water, oil, and chemical
reagents became economically feasible. The flotation process created a froth that would support
copper-bearing particles. Typically, the reagents consisted of 50 percent coal tar, 15 percent pyridine
oil, 20 percent coal tar creosote, and 15 percent wood creosote. In 1926, xanthates were added to the
process. After the flotation process, the tailings were discharged into Torch Lake (Reference 5, page
2).
4-
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Mining Waste NPL Site Summary Report
During the 1920’s, copper mining had decreased, and processing of mine tathngs had increased.
Beginning in the 1930’s and continuing until the 1960’s, mills operated mainly to recover copper
from tailings piles. The last null closed in 1968. In the 1970’s, copper recovery plants again began
operating in the Torch Lake area. The only discharge to Torch Lake from the copper recovery plants
was noncontact cooling water. By 1986, only one small copper recovery plant was still operating
(Reference 1, page 1-3).
An estimated 5 million tons of copper were produced in the Keweenaw Copper District of Michigan
from the 1860’s to 1968. More than half of this was processed along the shores of Torch Lake.
Between 1868 and 1968, an estimated 200 million tons of tailings were discharged into Torch Lake,
reducing the Lake’s volume by 20 percent and dramatically changing the shoreline (Reference 1, page
1-3).
SiTE CHARACTERIZATION
Copper-ore tailings are present in and around Torch Lake and other areas of the Keweenaw
Peninsula. The sources of contamination in Operable Unit 1 are: (1) tailings and associated debris
and flotation chemicals; (2) drums in the tailings; (3) drums in Torch Lake; and (4) industrial
chemicals. The potential pathways for the transport of contaminants to receptors include air, ground
water, surface water, and sediments. Humans, terrestrial organisms, and aquatic life may be exposed
to contaminants through ingestion, inhalation, and direct contact. The contaminants may become
more concentrated in fish and fauna through bioaccummulation (Reference 1, page 1-9).
Mine tailings are divided into two categories. The first category involves tailings resulting from
crushing and gravitational separation process. The contaminants of concern in this tailings category
are arsenic, copper, lead, and zinc. The second category of tailings includes tailings that were
reprocessed using the flotation process. The contaminants of concern in the reprocessed mine tailings
include arsenic, copper, lead, zinc, and the industrial chemicals used in the flotation process (lime,
pyridine oil, coal tar creosotes, wood creosote, pine oil, and exanthates) (Reference 1, page 1-8).
Drums have been visibly observed in tailings piles on land and identified by geophysical
investigations of submerged tailings in Torch Lake. The contents of the drums are not documented,
but it is rumored that striking mine workers may have placed explosives in some of the drums and
buried them in tailings piles (Reference 1, page 1-9).
5-
-------
Torch Lake
Debris from an electrical materials/copper reclamation facility is mixed with tailings in areas of
Operable Unit 1. The contaminants of concern associated with this reclamation facility are asbestos,
metals, and Polychiorinated Biphenyls (PCBs) (Reference 1, page 1-9).
Drums
In 1989, magnetometry and Ground Penetrating Radar were used to detect buried and submerged
drums in tailings piles (Reference 1, page 2-1). EPA Technical Assistance Team (EAT) personnel
collected samples from eight drums exposed on the surface of tailings in Operable Unit 1 (Reference
1, page 4-2). The sampling analysis indicated that seven of the drums had very low hazardous
constituent concentrations as measured by Extraction Procedure (EP) Toxicity tests. None of the
drum samples were considered hazardous based on Resource Conservation and Recovery Act
characteristics of EP Toxicity. PCBs and pesticides were not found above detection limits in any of
the samples. The eighth drum contained 4,000 parts per million (ppm) of trichioroethylene. It is
suspected that the contents of the drum are not related to mining activities, but rather to illegal
dumping (Reference 1, page 4-2).
The TAT assessment did not indicate that immediate removal of the drums was necessary (Reference
1, page 4-2). Drum identification and sampling was to continue in 1990, but the results were not
included in the November 1990 Remedial Investigation Report for Operable Unit 1 (Reference 1,
page 4-1).
Tailinns
The western shore of Torch Lake is lined with mine wastes from mining and associated activities.
The tailings piles in Operable Unit 1 are subdivided into nine sectors based on historic mining
practices, location, and field reconnaissance work (Reference 1, page 3-2). Surface and subsurface
samples were collected from tailings samples in all sectors (Reference 1, page 2-2). Tailings samples
were analyzed for inorganic and semivolatile organic compounds, moisture content, grain-size
distribution, Atterberg Limits, and cation exchange capacity (Reference 1, page 2-3).
Fifty eight surface samples were collected from a 0- to 6-inch depth and a density of 1 sample per 10
acres. Surface samples were collected to assess the risk from inhalation and ingestion of fugiuve dust
particles (Reference 1, page 2-3). Twelve subsurface samples were collected from a depth of 0 to 3
feet and at a density of I sample per 20 acres. Subsurface samples were collected to obtain the
necessary data to evaluate remedial action alternatives, particularly revegetation and dust control
(Reference 1, page 2-3).
6
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Mining Waste NPL Site Summary Report
Analytical data for the tailings samples from Operable Unit 1 are presented in Table 1. The table
contains the ranges from surface and subsurface samples and background concentrations for the
chemicals of concern.
TABLE 1. SUMMARY OF INORGANIC CHEMICALS OF POTENTIAL CONCERN
DETECTED IN OPERABLE UNiT I TAILINGS (in mg/kg)
Compound
Tailings Concentrations
Surface Subsurface
Native Soil
Concentrations’
Aluminum
5,190 - 37,200
5,410 - 27,200
10,000 - 300,000
Antimony
3 4t.P - 11.7
3.5 - 7.3
—
Arsenic
0.37U 2 - 8.3
0.47 - 14.4
1.0 -40
Barium
5.5 - 135
5.1 -68
100 - 3,500
Beryllium
0.18U 2 -1.7
0.l8U - 1.0
0.1-40
Boron
NA
NA
-
Chromium
10.7 - 46.3
13.6 - 42.7
5.0 - 3,000
Cobalt
5.4 - 52.6
8.5 - 32.8
1.0 - 40
Copper
72.3 - 3,020
699 - 5,540
2.0 - 100
Lead
1.5 - 104
0.38U 2 - 82.8
2.0 - 200
Manganese
103 - 1,080
217 - 703
100 - 4,000
Mercury
0.08U 2 - 1.1
0.09U 2 - 0.24
0.01 - 0 08
Nickel
12.6 -57.3
20.2 - 115
5.0 - 1,000
Silver
1.5U 2 - 8.2
1.5T.P -22.8
0.1 - 5.0
Titanium
NA
NA
1,000 - 10,000
Vanadium
19.2 - 159
25.5 - 121
20 - 500
NA - Not analyzed
‘The source of naturally occurring soil concentrations is Dragun, 1988.
2 lndicates the concentration was below the detection limit and was estimated.
Source: Reference 1, Table 4-1
7
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Torch Lake
Based on the sampling analysis, the Remedial Investigation concludes that the concentration and
distribution of metals appeared to be similar in surface and subsurface samples. Concentration ranges
from subsurface samples were withm or below the range of concentrations found at the surface.
Copper concentrations in tailings samples were elevated above background soil concentrations. In
summary, neither organic nor inorganic compound levels in tailings samples from Operable Unit 1
were found to be dramatically higher than background soil concentrations (Reference 1, page 4-3).
In 1989, the U.S. Bureau of Mines sampled mine-tailings leachate and water quality and concluded
that leachate from Torch Lake mine tailings was extremely low in comparison to leachate from 30
other sites. The U.S. Bureau of Mines analysis indicated that very little metal is being released from
Torch Lake tailings (Reference 1, page 1-6).
The soils in the Torch Lake area are primarily sand and silty barns with some localized clays. The
soils in the area have fragipans that develop 19 to 24 inches below the surface. The fragipans resist
root penetration and water infiltration, directing surface-water flows laterally before penetrating into
the ground-water system (Reference 2, page 4).
A limited soil-sampling program was conducted to determine if particulates are being transported
from tailings piles to nearby residential locations. Nine composite soil samples were collected Each
composite soil sample consisted of four subsamples representing the corners of the property sampled.
Although contamination was not apparent in the samples, traces of tailings and slag were noted
(Reference 1, page 2-4). Complete characterization of the Torch Lake Superfluid Site soils and a
Risk Assessment of soils was not in the scope of the Remedial Investigation for Operable Unit I
(Reference 1, page 4-3).
Table 2 compares soil-sampling ranges with typical background soil concentrations for the
contaminants of concern. Chromium, copper, lead, nickel, and vanadium were measured in most soil
samples. Copper concentrations exceeded background levels in all but one of the samples. Mercury
levels exceeded background conceut [ ations in four of the samples. Arsenic was at levels typical of
background concentrations at eight of the sampling sites (Reference 1, page 4-4).
Soil samples from residential locations generally had concentrations of inorganic compounds an order
of magnitude higher than background concentrations (Reference 1, page 4-4).
8
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Mining Waste NPL Site Summary Report
TABLE 2. SUMMARY OF INORGANIC CHEMICALS OF POTENTIAL CONCERN
DETECTED IN OPERABLE UNIT 1 SOIL SAMPLES (in mg/kg)
Compound
Range of Concentrations
Native Soil Concentrations’
Aluminum
3,140 - 7,600
10,000 - 300,000
Antimony
U 2
—
Arsenic
U’ - 7.00
1.0 - 40
Barium
U’ - 101.00
100 - 3,500
Beryllium
U 2
0.1-44)
Boron
U 2
—
Chromium
5.90 - 20.10
5.0 - 3,000
Cobalt
U 2
1.0-40
Copper
58.30 - 459.0
2.0 - 100
Lead
6.10 - 329.0
2.0 - 200
Manganese
91.40 - 357.0
100 - 4,000
Mercury
0 - 0.47
0.01 - 0.08
Nickel
0 - 33.70
5.0 - 1,000
Silver
l.5U 2
0.1 - 5.0
Titanium
U 2
1,000 - 10,000
Vanadium
11.40 - 26.30
20 -500
‘The source of naturally occurring soil concentrations is Dragun, 1988.
2 lndicates the concentration was below detection limits and was estimated.
Source: Reference 1, Table 4-2
The EPA TAT also collected three soil samples from the east side of Torch Lake during the Torch
Lake Site Assessment. All the metals detected in the soil samples were within typical soil background
concentrations and below maximum concentrations for EP Toxicity, as regulated under 40 Code of
Regulations Part 261 (Reference 1, page 4-4).
9
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Torch Lake
Surface Water
Water enters Torch Lake from the Trap Rock River, and Hammell, Dover, McCallum, and Sawmill
Creeks. The Trap Rock River is the largest discharger into Torch Lake, and the Trap Rock River
Watershed covers approximately 58 percent of the Torch Lake Drainage Basin. An esnrrnited 2,000
kilograms per year of dissolved copper is transported through Trap Rock River and its tributaries into
Torch Lake (Reference 2, page 1). Contamination of the surface water was not addressed in the
Remedial Investigation for Operable Unit I but will be addressed during the Remedial Investigation
for Operable Unit 2.
Ground Water
The U.S. Geological Survey sampled well water in 1968 and 1977. Analysis of the 35 wells in
Houghton County indicated that only 3 had specific conductance greater than 500 micromhos per
centimeter. Sampling results from these two sampling periods indicated a high-quality water source
for general use (Reference 2, page 4).
All ground-waxer wells drilled on the west and north sides of Torch Lake are set in bedrock. Many
Torch Lake communities and seasonal residents now get their potable water from municipal well
systems or from an independent supplier. Some communities, like Hubbell, receive their water
supply from Calumet, a larger community to the northwest (Reference 2, page 4).
In July 1989, TAT personnel sampled seven private wells and two municipal wells (Reference 2, page
10). Only one sampling location had a concentration of either organic or inorganic compounds in
excess of the Maximum Contaminant Levels (MCL) or above removal action levels (Reference 2,
page 20). The sample collected from the Lake Linden municipal well had an iron concentration of
0.33 ppm. This is slightly greater than the Secondary MCL of 0.3 ppm for iron (Reference 2, page
15). A detailed assessment of the ground-water contamination will be addressed during the Remedial
Investigation for Operable Unit 2.
Air
The Michigan Department of Natural Resources (MDNR) collected air samples from four sampling
locations (based on wind and population profiles) to monitor likely exposure points, emissions
sources, and background conditions. Total Suspended Particulates (l’SP) samples were collected for 1
month (from August 14, 1989, to September 13, 1989). Samples were collected for 24-hour periods
every other day, resulting in 62 filters samples (Reference 1, page 2-4). The two filters with the
10
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Mining Waste NFL Site Summary Report
greatest concentration of TSP were further analyzed for arsenic, chromium, copper, nickel, lead, and
zinc (Reference 1, page 2-5). The sampling analysis indicated that mean ambient-air concentrations at
the two selected monitoring stations exceeded mean background ambient-air concentrations for
aluminum, arsenic, barium, copper, magnesium, iron, manganese, and TSP (Reference 6, Table 2).
ENVIRONMENTAL DAMAGES AND RISKS
By the 1970’s, a century of mining waste deposition into Torch Lake had created an environmental
concern. In response to a 1972 discharge of cupric ammonium carbonate leaching liquor from the
Lake Linden Leaching Plant, MDNR reported the discoloration of several acres of lake bottom
(Reference 1, page 1-3). In its investigation, MDNR found 15 water-quality parameters within ranges
commonly encountered in similar Michigan lakes. Heavy metal concentrations m lake sediments were
within the ranges measured at 28 background locations, except for arsenic, chromium, zinc, and
copper, all of which had elevated levels. Plant and benthic invertebrate analysis did not indicate any
water-quality changes (Reference 1, page 1-4).
Three months after the spill, researchers from Michigan Technical University (MTU) cited the spill as
the cause for a temporary depletion of oxygen, elevated copper levels, increased pH, and increased
carbonate alkalinity. Bioassays indicated that portions of the Lake were toxic to macroinvertebrate
amphipod species (Reference 1, page 1-4).
Torch Lake has supported a diverse fish population; although the fish biomass has remained the same,
there has been a change in the dominant predator fish species. The change in dominant species may
be a result of changes in turbidity or lake chemistry (Reference 1, page 1-4).
In 1973, an MTU graduate student observed abnormalities and lesions in Sauger and Walleye, and
reported this finding to the MDNR. Subsequent pathological tests revealed that these two species
were affected by three types of neoplasms (including hepatomas, dermal fibromas, and gelatinous
masses) (Reference 1, page 1-4). In 1983, MDPH issued a consumption advisory for Saugers and
Walleyes caught in Torch Lake (Reference 4, page 1). This fish-consumption advisory was still in
effect as of November 1990.
Solely on the basis of the fish-consumption advisory, the UC’s Water Quality Board, in 1985,
designated Torch Lake as a Great Lakes AOC. In 1987, MDNR presented the UC with Phase I of a
Remedial Action Plan for Torch Lake. The plan called for the annual stocking of Walleye and
Sauger and a 1988 sampling of these species (Reference 4, page 1). In March 1990, MDNR reached
11
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Torch Lake
the conclusion that the 1988 sampling data did not support the continued fish-consumption advisory
for these species (Reference 4, page 3). MDNR reached this conclusion for the following reasons:
• Only 4 of the 56 fish samples bad mercury concentrations that exceeded 0.5 milligrams per
kilogram (mg/kg) consumption advisory action limit, and none exceeded 1.0 mg/kg. The fish
from Torch and Portage Lakes were among the least contaminated fish in Michigan’s Fish
Contaminant Monitoring Program (Reference 4, page 1).
• No internal or external growth abnormalities were observed on 458 fish collected. Cancerous
growths were not found on any fish livers during either the 1988 or 1985 fish collection and
sampling periods. MDNR acknowledges that liver neoplasrns (cancerous growths) have
declined to near background levels, but additional studies need to be conducted to determine
the background frequency of liver cancer in fish (Reference 4, page 1).
• Saugers have been in steady decline in Torch Lake since the 1960’s, and this has been
attributed to a decrease in lake turbidity. Saugers are a turbid-water species and when the
Lake water cleared after mining operations ceased, the Saugers lost their competitive advantage
over other fish species. Torch and Portage Lakes are no longer considered important Sauger
sports fisheries (Reference 4, page 3).
• Bioassays of Torch Lake surface water and sediments have not indicated the presence of
carcinogenic substances (Reference 4, page 3).
In a study of heavy-metal concentrations in Torch Lake sediments and mining wastes, it was
concluded that, although the tailings are directly contaminated with arsenic, chromium, copper, lead,
tin, and zinc, the water in Torch Lake is not directly contaminated with heavy metals. Furthermore,
heavy metals may be entrained in wind currents, but they do not represent a serious human health risk
(Reference 1, page 1-5).
The copper and hydrologic budgets were calculated for Torch Lake to determine the amount and
sources of copper entering Torch Lake. Over 96 percent of the copper input is from surface runoff,
3 percent is from precipitation, and 1 percent is from ground-water inflow. Copper loss occurs by
outflow into Portage Lake. The copper budget indicates an annual net loss of dissolved copper.
However, copper concentrations have been relatively stable for the past 14 years. Therefore, it was
determined that precipitation, complexation, dissolution, absorption, and diffusion control dissolved
copper concentrations (Reference 1, page 1-5).
In a 1988 Preliminary Health Assessment for Torch Lake, the Agency for Toxic Substances and
Disease Registry (ATSDR) concluded that the site is a potential public health concern because of
12
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Mining Waste NPL Site Summary Report
possible exposure to unknown etiological agents that may create adverse health effects over time.
Although Torch Lake is currently contaminated with mine tailings, there are no known health effects
linked to this contamination. The incidence of cancer deaths from 1970 to 1981 was cited at or below
the State average for age-adjusted stomach-cancer mortality. Furthermore, ATSDR concluded that
there was no indication that human exposure is currently occurring (or has occurred in the past)
(Reference 1, page 1-6).
According to the EPA Region V Remedial Project Manager, the Risk Assessment section that
accompanies the Remedial Investigation for Operable Unit 1 is still under review and will be
forwarded to EPA in June 1991. Quantification of the ground- and surface-water pathways were not
included in the scope of work for the Operable Unit 1 Remedial Investigation. Ground-water
contamination from Operable Unit 1 tailings is being addressed in the Operable Unit 2 Remedial
Investigation. Likewise, surface-water and sediment contamination are being addressed in the
Operable Unit 2 Remedial Investigation. The potential contamination from the drums in the tailings
of Operable Unit 1 will only be addressed after additional drums are located and sampled (Reference
1, page 5-1).
REMEDIAL ACTIONS AND COSTS
The Torch Lake area has undergone a number of remedial actions since the closing of the last mill in
1968. Previous remedial actions include:
• Since the 1960’s, attempts have been made to establish vegetation on tailings deposits on the
shoreline of Torch Lake (Reference 1, page 1-8)
• The Portage Lake Water and Sewage Authority has sprayed sewage sludge on the tailings to
promote vegetative growth on the southwest end of the Lake (Reference 1, page 1-8)
• As per the Torch Lake Remedial Action Plan, annual restocking and periodic sampling of
Saugers and Walleyes have been accomplished (Reference 1, page 1-8)
• The wastewater u eatment facilities in the communities surrounding Torch Lake have been
upgraded (Reference 1, page 1-8).
13
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Torch Lake
Remedial actions for the Torch Lake Superflind Site are still under development. None of the three
Operable Units have documented a remedial action in either a Record of Decision or a Feasibility
Study. The Feasibility Study for Operable Unit 1 is still under development, and will be completed in
fiscal year 1991.
CURRENT &IATUS
The Remedial Investigation for Operable Unit 1 was completed and submitted to EPA in November
1990. The Feasibility Study is still under development and should be available by the end of fiscal
year 1991. Field investigations for Operable Units 2 and 3 were completed in 1990, and as of May
20, 1991, the data was being reviewed. The Remedial Investigation for Operable Unit 2 will be
submitted to EPA in June 1991. The Remedial Investigation for Operable Unit 3 should be completed
by the end of fiscal year 1991.
14
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Mining Waste NPL Site Summary Report
REFERENCES
1. Final Remedial Investigation Report, Operable Unit 1: Torch Lake, EPA Contract No. 68-W8-
0093; Prepared for EPA by Donahue & Associates, Inc.; 1990.
2. Site Assessment for Torch Lake, Houghton County, Michigan, Report, EPA Contract No. 68-01-
7367; Prepared for EPA by WESTON-Major Programs TAT; 1990.
3. Superfund Fact Sheet: Torch Lake Superfund Site, Houghton County, Michigan; EPA Region V,
1989.
4. Fish Growth Anomalies in Torch and Portage Lakes, 1974-1988, Houghton County, Michigan,
MIIDNRJSWQ-90/029; MDNR, Surface Water Quality Division; 1990.
5. Technical Memorandum Number 1; From Jeffrey D. Maletzke, Donahue & Associates, Inc., to
Lori Ransome, Donahue & Associates, Inc.; July 28, 1989.
6. Technical Memorandum Number 7; From Lori Ransome, Donahue & Associates, Inc., to Project
Files; February 9, 1990.
15-
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Torch lAke
BIBLIOGRAPHY
Donahue & Associates, Inc. Final Remedial Investigation Report, Operable Unit 1: Torch Lake,
EPA Contract No. 68-W8-0093. 1990.
EPA Region V. Superfund Fact Shea: Torch Lake Superfund Site, Houghton County, Michigan.
1989.
Lee, Jae B. (EPA). Personal Communication Concerning Torch Lake to Mark Pfefferle, SAIC. May
20, 1991.
Maletzke, Jeffrey D. (Donahue & Associates, Inc.). Technical Memorandum Number 1 to Lori
Ransome, Donahue & Associates, Inc. July 28, 1989.
MDNR, Surface Water Quality Division. Fish Growth Anomalies in Torch and Portage Lakes,
1974-1988, Houghton County, Michigan, MIIDNRJSWQ-90/029. 1990.
Prepared for EPA by WESTON-Major Programs TAT. Site Assessment for Torch Lake, Houghton
County, Michigan, EPA Contract No. 68-01-7367. 1990.
Ransome, Lori (Donahue & Associates, Inc.). Technical Memorandum Number 7 to Project Files.
February 9, 1990.
16
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Torch Lake Mining Waste NPL Site Summary Report
Reference 1
Excerpts From Final Remedial Investigation Report, Operable Unit 1:
Torch lake, EPA Contract No. 68-W8-0093; Prepared for EPA
by Donahue & Associates, Inc.; 1990
-------
EPA REGION V.
ARCS PRO GRAM
ENGINEERS
SCIENTISTS
a.
—-—- ----— .. --
VOLCM! 1
.-
?IMA.r,
R t* Iii STIGAi’IQI R a T
OP AaL DNIT I
y*
i*z, INV!STIGAT J(/PZAsxaxLfl’y $7 y
ac ToN NI
1990
— -
•
.
EPA Contract.
684V8 OO93
Us.
I
I
Donohue & Assocfates, ho.
-------
FINAL R.V IAL INVESTIGATIOtI R. RT
0P ABLE UNIT I
TOR £
R LAL I ESTIGATION/F SIBIL ’Y STUDY
ucaToN irry, NI IGAJi
1990
I CULO’ti a )
Lorraine S. Ransome,
12-2/- O
Ph.D.
Site Manager
Date
Donobu, & Associates, Inc.
fl .
/ 2 •3 I-
Roman M. Gau, P.E.
ARCS Project Manager
Donohue & Associates, Inc.
/ - /-,4•
Mich eJ. L. Crosser Date
Technical Services/Quality Assurance Manager
Donohue & Associates, Inc.
-------
A Contract No.: 68—W8— 0 093
Work Ass gn ent NO.: 02—5LS8
Don t u. Project No.: 20011
- VOLU? j
FINA.L. R. IAL INVESTIGATION R ORT
OP ABLE UNIT I
XE
R. IAL INVESTIGATION/FEASIBILITY STUDY
BOUGETON CW T , ICGAN
IIOV 1990
Prepared for:
U.S. Environmental Protection Agency
Emergency and Remedial Response Branch
Region V
230 South Dearborn Street
Chicago, Illinois 60604
The document has been prepared for the U.S. Environmental Protection Agency.
The eat,raaj contained herein is not to be disclosed to, disculied with, or
made available to any person or persons without the prior expressed approval
of a responsible official of the U.S. Environmental Proteet on Agency.
-------
Torch ike p 1 ,75 Section No.:
Fi aj, RI Report — 0 Revision NO.: 0
EPA Contract No. 68 —Wg—0093 Date: November 1990
1.0 !N’i’NOC t
1 • 1 ! .P05m 0? R OR ?
Donebul & Associates, Inc. (Donohue) is submitting this Remedial Investigauon
( %) Report for Operable Unit I (CU I) for the Torch Lake Superfund Site.
This RI Report is submitted to the U.S. vironmental Protection Agency (EPA)
in responSe to Work Assignment No. 02—SLS8 under Region V ARCS Contract
No. 68i180093.
The rationale and scope of work for the Torch Lake Remedial Investigation/
Feasibility Study (RI/PS) is described in the Torch Lake RI/PS Final Work Plan
(Revision 1) (Donohue, 19895). The Torch Lake RI/VS will be conducted as
three operable units. CU I includes the primary contaminant sources of
surface tailings and drum contents in the primary study area. on the western
shore of Torch Lake. This CU has been identified as possibly requiring
separate and earlier remediatien than other media, from a human risk
perspective. CU II includes other potentially contaminated media in the
primary study area. These comprise soil, air, surface water, and Torch
Lakes’s submerged tailings, sediment, groundwater, and biet*. CU III incL des
ether tailings contaminant sources in the sid—Kew naw Peninsula, including
the North try, the northern portion of Portage Lake, and tributary areas.
This report suarizss the RI p,rform.d for CU I which includes primary nonta-
min.ant sources in surface tailings on the western shore of Torch take. The RI
was performed to collect and evaluate data to supplement existing data and
form th . basis for assessing: (1) physical characteristics of CU I, (2) type
and extent of contamination of CU I, (3) environmental and human health risics
associated with CU , and (4) the need for and methods to remediate CU I.
Activities documented in this report include waste characterization of CU 1
tailings and drums, characterization of dust emissions, air pathway exposure
modeling, limited characterization of soil, and assessment of human hea 1th
impact.
This introductory chapter presents site background and history, a suary cf
the RI/VS Work Plan rationale and approach including the division of the site
into three operable units, and the organization of the remaining chapters of
the RI Report for CU I.
1. • 2 ST?t I CR JND
1.2.1 Site Location * d Description
The location of the Torch Lake Sup.rfund Site is shown on Figure 1—1. It is
located en th. Reweenaw Peninsula in EougPzton County, Michigan, at 47M lati-
tude, 88’W longitude. Torch Lake is tributary to Portage Lake, which is part
of th. Reweenaw Waterway that flows to Lake Superior. Torch Lake is about
14 mi by water from Lake Superior. Torch Lake has a surface area of
2,717 acres, a mean depth 0f 56 ft. a maximum depth of 1.15 ft. and a volume of
5.2 x iO ft 3 . The Trap Reck River and several small creeks discharge itto
‘1
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Torch Lake RI/PS Section No.: 1
F aal RI Report — O I Revision NO.: 0
A Contract . 68—w8—0093 Date: NOvember 1990
Torch Lake. Its watershed is approximately 77 ii 2 . The watershed s forested
with ..condltOWtb northern hardwoods, and supports a few dairy and potato
f 5 oniy percentage of the watershed is residential or comaerciaj..
The comaunities of Lake Linden (pop. 1181), Hubbell (pop. 1278), and Mason a:e
located Ofl the vest side 0 f Torch Lake. Torch Lake is used for fishing,
boating. limited contact recreation (svimaing), non—contact cooling water
supply. treated municipal. waste assimilation, and wildlife habitat (Michigan
Department of Natural Resources, 1987).
1.2.2 Site HistorY and Response Actions
The following sect ions describe- industrial history, environmental problees and
studies, regulatory actions, and response actions pertaining to the Torch Lake
Superfund Site.
1.2.2.1 Industrial History
Torch Lake is located in Nichigans copper mining district. For 100 years,
th. lake was the site of milling and smelting facilities, a repository for
copper mining and milling wastes, and a part of the waterway used for trans-
portation to support the industry. PRC Lagineering, Michigan Technological
a versity (WIU) (Rose, V.1., et al 1986), and NR (Michigan Department of
Natural Resources, 1987), have compiled chronologies of Torch Lakes copper
industry. The following si ary of the chronology is relevant to the types of
hazardous materials potentially impacting the environment.
Deposits of native (elemental) copper are found in a belt extending from the
tip of the Keweenaw Peninsula southwest over a distance of 100 miles. Copper
sined in the region was native copper, found as a metal. Copper mining opera-
tions had begun on the Keweenaw Peninsula by the 1860s. The first mill opened
en Torch Lake in 1868. At the mills, copper was extracted by crushing or
stamping the rock into smaller pieces, grinding the pieces, and driving then
through successively smaller meshes. The copper and crushed rock were sepa-
rated by gravimetric sorting in a Liquid medium. The copper was sent to a
smelter. The crushed rock particles, called tailings or stampsands, were
discarded with mill processing water, typically by pumping into the lake or
waterway. The milling process was not efficient, and copper was lou in the
discarded tailings.
Mining output, milling activity, and tailings production peaked in the Torch
Lake area in the early 1900* to 1920. Mining company records from this tine
describe bow mill tailings were pumped out into Torch take and deposited on
property around Torch Lake. All of the mills were located on the west shore
of the lake.
In about 1916, advances in technology allowed recovery of copper from tailings
previously deposited in Torch take. Dredges were used to collect submerged
tailings. which were then screened, recrushed, and gravity—separated. An
amaonia leaching process involving cupric aoniua carbonate was used to
recover copper and other metals from conglomerate tailings. A flotation
process sade it economically feasible to recover copper from old tailings .n
l —2
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Torch Like RI/VS Sect ion M c .: 1
Final RI RepOrt OU I Revision Mo.:
A Contract Mo. 68—W8—0093 Date: November 1990
Torch take and was used for reelaaation at Torch Lake eills by 1917. The
flotation process involved agitating ore, water, oil, and cheticals to produce
a froth that would support copper—bearing particles. During the 1920s, cheni-
cal reagents were used to further increas, the efficiency of the flotation
process. The chemical reagents included lime, pyridine oil, coal—tar
creosetes, wood creosote, pine oil, and xanthates. These were used in various
cctbinatiens depending on the ore and process water. After leaching or flota-
tion at reciasation plants, chemically treated tailings were returned to the
lake, resulting in increased turbidity.
During the 19205, uining activities decreased, whereas tailings processing per
mine increased over the previous decade. In the 1930. and 1940s, the Tetch
take sills operated mainly to recover tailings in Torch Lake. In the 1950s
copper sills were still active, but by the late 1960. copper milling had
ceased. The last sill closed in 1968.
Over S million tons of native copper were produced from this area, and sore
than half of this was processed along the shores of Torch take f roe the 1860.
until 1968. Between 1868 and 1968 at least 200 million tons of tailings were
dumped into Torch Lake, filling at least 20 p.rcent of the lake’s original
volume. These deposits resulted in drastic changes to the shoreline.
In the early 1970$, exploratory research was conducted in the Centennial Mine,
resulting in a devatering discharge into Slaughterhouse Creek, a Trap Rock
River tributary. A small copper recovery plant continues to operate in
Kubbell, and discharges non—contact cooling water into Torch Lake (Science
Applications InternationaL Corp.. 1986).
1.2.2.2 Ristory of virenmental Problems and Studies
In the 1970s, environmental concern developed regarding the century—Long
deposition of tailings into Torch Lake. aigh concentrations of copper and
other heavy titals in Torch Lake water or sediments, toxic discharges, and
fish abnormalities prompted tiny investigations into long— and short-term
impacts attributable to sine-waste disposal.
The academic and regulatory communities have produced an extensive amount of
data, research, scientific Literature, and reports regarding Torch Lakes
complex environmental problems (Michigan Department of Natural Resources,
1987; Rose, LI., at al., 1986: Warburton, 1986: Michigan Water Resources
Commission, 117.3: Wright et al., 1973, Black et al., 1982; U.S. EPA, 1987;
Sp.nce, 19 1ts).
In 1972, cuprie ammenium carbonate leaching liquor was discharged into the
north end of Torch Lake frau storage vatii at the Lake Linden Leaching Plant
The Michigan Water Resourcs Commission (MWPC) investigated the spill (MWRC,
1973) and rsported that discoloration of several acres of lake bottom indi-
cated previous discharges. No deleterious effects to surface water quality.
alga., fish, or benthic uaerotnvertebrates were detected three months after
tne discharge. To assess effects f roe the spill, MWRC compared results from
its 1972 investigation to data from a 1970 MWRC investigation. £xcept for
1—3
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Torch lake RI/VS Se tiø No.:
Final RI Report - CU I Revision No.: 0
EPA Contract $0. 68—W8—0093 Date: November 1990
chloride and copper. 15 water quality parameters surveyed were within ranges
comeonly encountered in Michigan lakes of tIfls tip. c1iiorid. concentr t
had decreased because of the termination of mine dewat.ring and the effect of
naturaL lake flushing. Dissolved copper COnCifltX jons remained high, sinilar
to 1970 levels. Heavy metal concentrations in Torch Lake sediments were
within es measured at 28 background Locations in Michigan, except for
elevated levels of arsenic, chromium, zinc, and copper. Plant and benthic
invertebrate analysis did not indicate changes in water quality. Copper can-
centration s in Torch Lake fish were found to be less that those measured in
1970. Mercury was found in fish in 1972, but this was attributed to the use
of analytical techniques that were more sensitive than those previously
available.
MTU researchers also examined the alteration of Torch Lake water quality after
the 1972 discharges (Wright it aL., 1973). The cupric aonius carbonate
spills were cited as factors in temporary water quality changes, namely the
depletion of oxygen through the conversion of aonia to nitrate, elevated
copper levels, increased pH, and increased carbonate alkalinity. Bicassays
suggested that portions of the lake were toxic to a macrojnv,rtebrate amphipod
specie.
A diverse fish population has occupied Torch Lake and supported productive
food and sport fishing. Although game fish biomass has remained constant.
changes in the dominant larger predator species, from sauger to waLley. and
northern pike, and lack of sauger reproduction and juveniles have been
reported. Impacts to dominant fish predator species may have been due to lage
chemistry or turbidity/habitat changes. I 1973, abnormalities and lesions i.n
Torch take sauger and walleye were documented by an M1’U graduate student and
reported to the . Subsequent pathological research was conducted in l 79.
1980, and 1983, and indicated that these two species from Torch Lake were
commonly affected with three types of neoplasms including hepatomas, dernal
fibromas, and gelatinous masses. No virus particles were observed, and the
livers were found to be frequently atrophic. Pug—headedness in perch has also
been observed at an incidence of greater than 1 percent, which is significant
for fish.
Mnthic communities have been reduced in areas of copper tailings, and bio-
assays have shown the tailings to be toxic (bCI , 1987).
W U researchers, under contract with the ?W$R, have conducted numerous utud es
to determine possible impacts of copper mining wastes on the environment f
the Torch Lake area. Five studies are discussed in the 1986 Project CO:p).e-
tion Report (L.ddy, 1986) and are summarized here.
A four—month tumor induction study was conducted in the laboratory to examine
the effect on fish liver histology following static exposure to creosote and
xanthate flotation agents in the presence of Torch Lake sediments. Causal
relationships with Liver abnormalities or tumor occurrence were not concluded.
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TorCh Lake RI/VS Section No.: I
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A Contract Ho. 68—i18—0093 Date: Novesber 1990
The e vironaentaj fate of xanthates and creosotes was exanined using LLbrary
and laboratory studies. Xanthate fats was studied by following the degrada-
tion of pure coapounds in the laboratory. The rats and necr aniss of degrada-
tion was related to pH. and it was concJ ded that xanthates would net be
expected to persist in the environeent beyond one year. Torch Lake sediment
extracts were analyzed for ten typical crosote polycyclic aromatic hydro
carbon (PM) cospenents. Eight Of these coxpounds were nor detectable in the
sedisent •ztraets. Chrysene and benzo(ajpyrene were detectable, but the
sources could not be deterained. Airborne particulates f tea fuel combustion
as well as aining pollutants say have contributed to the PM content of Torch
Lake sedisent.
A study regarding tuner incidence and parasite surveys of perch, valleys, and
sauger free Torch Lake reported that parasite species and tuners were observed
in the thres fish species, and abnormalities were observed in perch, but no
direct relationship between parasites and tusors was found.
In a study of heavy setals in Torch Lake sedisents and sining wastes, sedi—
sent, tailings, and airborne dust sanples were analyzed for netal.s and mineral
coeposition. It was concluded that though the sedinents were enriched wLtPt
arsenic, chrosius, copper, lead, tin, and zinc, Torch Lake water s not
directly contaninated with heavy metals, and though winds stir up dust f ton
staapsands, it is unlikely that airborne heavy setals represent a serious
hu a health probles. The chrosiun, lead, tin, and zinc enrichasnt of seth—
sents in the vicinity of Hubbell is anomalous in reference to local sineral
deposits, and is attributed to contaaination fros electrical debris and asso-
ciated slag at the reclanation plant near Hubbell.
The copper budget for Torch Lake was calculated with the hydrologic budget to
detersine the asount and sources of copper entering Torch Lake. Over
96 percent of the copper input is free surface runoff. 3 percent is from pre—
cipitation, and less than 1. percent is f roe groundwater. Copper loss occurs
by outflow through Portage Lake. Considering external factors only, the
budget indicates an annual net loss of dissolved copper. However, no signifi-
cant changes in copper concentrations have occurred in the past 14 years. It
was therefore concluded that internal processes (precipitation, cosplexat ion.
dissolution, adsorption, and diffusion in sedisent pore water) control
dissolved copper concentrations.
In 1988, V researchers conducted a eagnetosetry investigation of a small
area of staepsuds. The investigation indicated the presence of buried
aetallic objeéts near an area where many barrels are rusored to have been
buried (Speece. l9lSb).
Ia 1988, collected 495 fish, including LI species, f roe Torch Lake and
Portage take (Hichigan Depaztsent of Natural Resources, 1989). No sauger were
captured, and this rarity was attributed to the fact that turbidity in the
waters has decreased. No suspicious growths were observed, either externally
or internally, during fish collection or liver preparation. Livers f eon
32 valleye and bullheads were analyzed. One walleye f roe Portage take had
abnormal liver cell develepsent, but this was not confirmed as a tumor. The
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Torch Lake RI/iS Section Ne.: 1
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other 31 livers vere normal. The !CNR report Compared these data to prev.o s
studies and concluded that these data strongly suggest that liver tumor
inducing agents above background concentrations no longer exist in the Term
Lake — Portage Lake fishery. LO I Contaminant levels in fish flesh further
suggest reconsideration of the fish Consumption advisory.
In 1988, the Agency for Toxic Substances and Disease Registry (ATSDR) released
its Preliminary Health Usesament for Torch Lake (popE, 1988). Site bac c—
ground. previous investigations, site visit, potentially contaminated nsd a.
potential environmental and human exposure pathways, and demographics we :.
evaluated and discussed.
Based on the information reviewed, it was concluded that the site is of poten-
tial public b.altb concern because of possible exposure to presently unknown.
etiolocic agents at levels that may result in adverse health effects over
time. Although Torch Lake is polluted with copper and other contaminants, no
known health effects were linked to the problem. The incidence of cancer
deaths over the period 1970—1981 was cited as at or below the state average
for ag.—adjusted cancer mortality except for stomach cancer. Stomach cancer
in the locale vu linked with the predominantly Scandinavian descent of the
population.
The ATSDR report recoenended additional investigations regarding: (1) rumors
about dumping of chemicals and barrels into th. lake, (2) contents of barrels
found in and around the lake, (3) private well sampling and analysis; (4 fish
population reproduction and tumor incidence; (5) causative agent of fish
tumors; (6) human health risk from fish consumption. The ATSDR report also
receenended cleanup of abandoned buildings and industrial, scrap materials
which constitute physical hazards on the shoreline of Torch Lake.
The ATSDR concluded that although there is currently a potential, for human
exposure to contaminants, there are no indications in the review conducted for
the ATSDR Health Assessment that human exposure is actually occurring at the
present time or has occurred in the past. Therefore the site is not being
considered for follow ap health studies at this time. ATSDR will reevaluate
th. site for fellovup if data become available suggesting human exposure is
occurring or has occurred.
In 1989, the Bureau of Nines (U.S. Department of Interior, 1990) performed
laboratory evaluations of tailings and water samples from Torch Lake to deter-
mine the potential for metals to adversely affect Torch Lake. In general,
metal concentrations of leaehates from Torch Lake tailings samples were con-
cluded to be extremely low when compared to tailings at over 30 Other sites.
Bureau of Nines results indicated that very little metal is being released
f row the Torch take tailings.
1.2.2.3 History of Regulatory Actions
Because of the incidence of fish tumors, in 1983 the Nichlgan Department of
Public Health ( Pt) announced an advisory against the consumption of Torc
Lake sauqer and valleye. Although no human health effects were associated
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Torch Lake RI/F’S Section Nc.: 1
Final RI Report OU I Revision No.: 0
CPA Contract No. 68W80093 Date: November 1990
with fisI consumption, MDPR issued the advisory as a preventive measure untLi
the causative factors 0 f fish tuners and the potential risks to humans Could
be identified. Th• advisory is still in effect.
In 1984, the Sarard Ranking System was applied by EPA to score the Torch Cake
Superfund Site. The site was defined as Torch Lake, the northern end of
Portage Lake, and the North Entry to Lake Superior, because at these locations
copper concentrations were significantly above background values. The back-
ground samples were obtained f roe the southern end of Portage Lake and the
South Entry.
In 1985. the U.S. CPA initiated a responsible patty search for the Torch rake
waste disposal site. Three potentially responsible parties (PRPs) were
identified and issued notice letters. En August 1988, negotiations with these
three PEP5 were concluded. In June 1988, the Torch Lake Superfund Site was
placed on the U.S. CPA National Priotity List (NPL) for funding under the
Comprehensive Environmental Response, Compensation, and Liability Act
(c a.A). A federal—lead RI/VS was initiated at the site in October 1988.
Torch Lake is on the Act 307 Michigan Sites of Environmental Contamination
Priority List. In 1905, Pl1’U researchers were awarded funds f roe the MDNR
through Act 307 to study fish tumor problems in Torch Lake.
In 1983, the International Joint Coemission Water Quality Board designated
Torch Lake as a Great Lakes Area of Concern (AX). An AX s defined as art
area with known i.pairment of a designated use. The ACC is confined to Torch
Lake and its shores on the basis of the fish consumption advisory, tumor
frequency, eta2—contaminated sediments and their impact on biota. and the
history of mining waste disposal. In 1985, the State of Michigan designated
Torch Lake as a Category 2 AX based on the information base available and
programs underway. In the case of the Torch Lake AOC, the causative factors
were unknown and an investigation was underway. The site can be removed from
the AX list when evidence is presented that the designated uses have been
restored.
The ICNR completed a *uedia.t Action Plan (RAP) for Torch take in 1987. The
primary goal of the RAP was stated as the removal of the fish consumption
advisory on the basis of its issuance. The objectives of the RAP were to
assemble and suarize all exioting data, identify impaired designated uses.
identify problem sources, identify data gaps, propose further investigations.
and propose alternatives to restore designated uses.
The impaired uses of Torch take were identified as: (1) fish consumption
because of th. ) P! advisory affecting sport fishery for saug.: and walleye.
and (2) the reduced bsnthic eacroinvertebrate coemunity in locations where
mine tailings have been deposited. In the RAP, the ICfl recoended that t e
AX be reclassified because: external fish tumors have been associated vitPt
viral infections, fish tumors are co on in Great Lakes populations, all ote:
fish in the coemunity did not exhibit abnormal growths and can be used for
food; the fish sove freely to Portage Lake and take Superior; although not
aesthetically pleasing, tumors from fish do not transmit cancer to humans;
bioassays of Torch take sediment and water have been negative for eutagenLc
activity; tumor—inducing agents have net been identified in Torch rake.
1—7
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Torch L.4ke RI/FS Sict ion No.: I
Final. RI Report — OU I Revision No.: 0
A Contract No. 68—W8—0093 Date: November 1990
In September 1988, the Stat. of Michigan issued a lett.t of assuranc, to
enable the A to conduct an RI/YS for the Torch Lake Superfuad Site. this
letter recomeended continuation of r s previous studies.
1.2.2.4 History of Response Actions
Attempts to establish egetatjon on stampsand deposits on the shoreLines of
Torch Lake have been cOnducted sinc, the l960s (L.ddy, 1986. and Science
Applications International Corp., 1986). The Objectives of 5tampsa d vegeta-
tion include stabilizing the shoreline and reducing airborne parricuj .at,s.
The Portage Lake Water and Sewage Authority has spray—irrigated sewage sludge
on tailings to promote vegetation at the southwest end of the lake.
The Village of Lake Linden has been developing recreational facilities with a
bathing beach, camping area, park, and boat ramps at the north end of Torch
lake.
In Hubbell and Lake Linden, debris around the smelters and from the shore1 e
has been reoved.
Proposed •ct include restocking and monitoring sauger or valley, in Torch
Lake, monitoring Torch Lake water and fish tissue, and natural transporrat on
and burial, of copp,g—angjcbed sediments in Torch Lake (P NR, 1987). MT J
researchers disagreed with IWNR’s restocking proposal, monitoring plan.
funding level, and natural sedimentation processes proposal, and proposed
other research to identify alternatives for remedial, action. In the 1987 RAP.
the LCi stated that other remedial actions for the fish consumption impair-
sent cannot be proposed sines causes of fish tumors have not been determined;
other remedial actions for the contaminated sediment problem have not been
proposed because of the expanse and volume of the sediments. Other reviewers
oppose the restocking plan because it would encourage fishing and consumpt n.
and becaus. it may not be Logistically possible.
Vastevateg treatment is being upgraded In the surrounding comeun tjes.
1 • 3 INIYlAL SI?! !VAL 2I AND DtSI I OP OP ABL5 ONITS
A detailed initial, evalsation of the site is contained in the Final Work Plan
(Revision 1) (Donahue, l9I9a .
1.3.1 T me and Volume of Waste Prese
The types and ipproximate amounts of vast, present in OU I and the potential
centaajia ts usociated with each are sumearized in Table 1—1. Copper ore
tailings are present in and around Torch Lake and at other locations on the
ew.anav Peninsula in tremendous quantities. The estimated total of 200 mil-
lion tons of ore tailings which were discharged into the lake can be divided
into two categories. Tb, first includes tailings :esu1ti g from the stamping!
gravim.t:ic separation process. Contaminants of concern in tailings from this
process include copper, arsenic, chromium, lead, and zinc. The second
category i c1udes tailings reprocessed using the flotation process. The
flotation process used lime, pyridine oil, coal tar cr.osoe,s. wond creosote
pine oil, and zanthates.
4 ?
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Torch take RI/PS Section No.: L
Final RI Report — CU I Revision N e.: 0
A Contract No. 68 IS—0093 Oats: November 1990
Drums are pres.nt in the tailings and submerged in Torch lake. The Pte$en e
of exposed drums has been confirmed visuai.ly. The presence of buried and
submerged drums has been indicated hi? geophysical investigations conducted by
A Technical Support Unit and ergency Response Team prsonnel. A br ef
geophysics survey conducted by researchers at NYU also showed an anomaly which
may indicate additional buried drums (Spence, 1988b). The nature of the mate-
rial disposed of in drums is not documonred. Because explosives WItS used n
larg. quantities during mining operations, and because workers, angry over
local area strikes were rumored to have put explosives in drums, one or more
drums could contain explosives.
Debris associated with an electrical materials copper reclamation faei1 ty .s
mixed with tailings over a portion of the sit.. Some scrap material was
burned, and some was disposed near the facility. The contaminants of concern
associated with electrical material reclamation include PC3 5, metals, and
asbestos.
1.3.2 Pctentiaj Migration Pathways
Contaminant sources and potential migration pathways are shown on Figure 1-2.
the Conceptual Site Model. Primary contaminant sources include (1) ta lings
with associated debris and flotation chemicals, (2) drums in the tailings.
(3) drums in Torch Lake, and (4) industrial chemicals. Industrial chemicals
are included as a possible contaminant source because of a reported discharge
of leaching liquor directly to the lake (MWRC. 1973).
Primary release mechanisms include dust emissions, infiltration, runoff, and
erosion from tailimgs: leaks fro. drums in the tailings and in the lake: and
spills and discharges of industrial chemicals. These releas. mechanisms
result in secondary contaminant sources including contaminated soil, surface
water, and sediments. Secondary release mechanisms include dust emissions ar d
infiltration from soil, and infiltration through sediments.
Potential contaathant transport pathways to receptors includ, air for dust
emissions, groundwater flow to water supplies, and surface water and seth—
mints.
Receptors incled. ku*s via ingestion, inhalation, and dermal contact, and
terrestrial, and aquatic environmental, species through ingestion, irthalatLon,
and direct contact. Through bioaccumulaticn, fish and other fauna can serve
as sources to both human and environmental receptors through ingestion.
1.3.3 ! dentificatjqn of O erabl,e Units
The Hazard Rankimg System scoring package defined the Torch Lake Superfund
Site to includi Torch Lake, th. North £ntry (to take Superior), and the
mortharn portion of Portage take, where copper concantrations are signif I—
eantly above the background established by the southern portion of Portage
Lake and the South try. This area is shown on Figure 1—3.
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Torch take RI/PS Section No.: 1
Final RI Report 00 I Revision No.: 0
k Contract NO. 68W$0093 Date: November 1990
During project ecoping meetings, representatives from epA, Don frue, MD ffi ,
0.5. Fish .nd Wild Life Service, and the Bureau of Mines reached COfl5efl5 $
that operable units (00) wi1 l be defined for the site for the following
reasons:
o The Torch Lake Sit. as defined in the Hazard Ranking System is large
and complex.
o The most important waste sources and the receptors are in close
proximity over a relatively small portion of the site.
o Remediatien of contaminant sources, if necessary, will be expedited
by completing the RI/PS and ROD for the tailings adjacent to the
take.
o Information obtained from a relatively small portion of the site,
containing serious sources and important receptors, can be used to
determine the need for additional information throughout the rest of
the site and to help develop and focus the scop. of work for col-
lecting additional information.
o There is a substantial amount of background information available for
the site as a whole that must be reviewed. In addition there are on-
going studies concerning the site as a whole that, when completed,
will help determine the scope for the remaining work. This back-
ground in.foraation can be reviewed while work proceeds on the smaller
area.
The primary study area includes Torch Lake and its surrounding shore. The
boundaries of the primary study area, shown on Figure 1—4, are the Feweenaw
Fault line along the northwest side of the lake Eammell Creek to the north.
the topographic ridge line on the east, and a line extending from Gooseneck
Creek in th. southwest corner of Torch take eastward along Upper Point Mills
Road and Baulaaa Road to the eastern boundary on the south. Included in this
area are the towns of lake Linden, Eubb.ll, and Mason on the west side of
Torch lake. The primary study area was delineated because the environmental
problems here are more readily defined, and focusing on this area will pcov de
earlier information on potential remedial action alternatives. This approach
will prevent delays in remedial action for Torch Lake and will provide back-
ground information for planning for the remainder of the site.
00 I includes ‘the primary contaminant sources of surface tailings and drum
contents in the primary study area, on the western shore of Torch take. This
00 has been identified u possibly requiring separate and earlier remediat ion
than other media, from a human risk perspective.
00 II includes other potentially contaminated media in the primary study area.
These comprise soil, air, surface water, and Torch Lakes’s submerged tailings,
sediment, groundwater, and biota.
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Torch Lake RI/IS Section No.: 1
Final RI Report — CU I Revision No.: 0
EPA Contract No. 68—W8—0093 Date: November 1990
CU III includes other tailings contaminant sources in the mid—Keweenaw Penin-
sula, including the North Entry, the northern portion of Portage Lake, and
tributary areas.
00 II or III may be divided into additional operabl, units if data indicate
that separate study and remediation will, be most effective. CU III may be
integrated with 00 I for later stages of the RI/F ’S if evaluations performed in
early RI/Fl tasks indicate that this is appropriate.
1.4 OP ABLE UNIT I ACTIVITIES AND ORCANIZATION OP REPORT
Remedial investigation activities associated with OU I were conducted to eval-
uate the elements of the Conceptual Site Model highlighted on Figure 1—5.
Specific activities included waste characterization of CU I tailings, geo-
physical investigations for drums in CU I tailings, sampling of drums that
were accessible from the surface, characterization of dust emissions from CU I
tailings, characterization of soil in the immediate vicinity of receptors, a :
pathway exposur. modeling, and assessment of human health impacts. Waste
characterization activities included investigation of parameters needed to
evaluate potential remedial. actions.
Chapters 2 through 6 of this RI Report for 00 I present details of the 00 I
study area investigation, and discussions of th. physical. characteristics of
the study area, the nature and extent of 00 I contamination, contaminant fate
and transport, and the CU I baseline risk assessment. In general, results and
conclusions from 00 I RI activities are discussed and integrated in the text
of the Report, while media—specific data and evaluations are presented in
Technical Memoranda. Chapter 7 presents conclusions and discussion of uncer-
tainties. Technical Memoranda are included in Appendix A. The Baseline Risk
Assessment Report for CU I is presented in Appendix B (found in Volume 2 of
this report).
ARCS/R/TQRc&P.I/AA4
1—Il
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Torch take RIfTS Section NO.: 2
Final R I Report — CU Revj j 0 No.: 0
A Contract No. 68—wB—0093 Date: November 1990
2.0 5 DY AREA INVESTIGA,
This chapter describes field activities and physical and chemical, nonitori
associated with sit. and waste characte tion of CU I. The remedial tny .
tigation for 00 I included a review of the mining archives at Michigan
Technological University INTO), field reeonnaisunce, drum investigation
including geophysical surveys for locating drum,, drum sampling to determ .,
drum contents, surface tailings sampling, subsurface tailings sampling, so j
sampling in the imsediate vicinity of human receptors, and air sampling and
meteorological monitoring. This chapter summarizes these activities which are
dis uss.d in sore detail, in the referenced Technical Memoranda (Appendix A).
3.1 ? LOCICAL u iv Sfl’y AR ,iy SEARS
A ?I O R iA.IWjI 0? ?AxLIiics
Doaotiu. conducted a search of mining company records at the MTU archives to
better understand the industrial activities that i5p eted the Torch r.ake
Superfimd Site and CU I in particular. Information obtained in the archive
search and from field recenflais ce is presented in Technical Memorandum
Number I (TM 1) in Appendix A. Information documented in TM 1 was used to
divide the CU I tailings along the vest side of the lake into sectors based on
homogeneity of tailings type and source. Nine sectors were identified for
separate sampling.
General Locations of these sectors are shown in Figure 2—1. Surface features
and past and present land use in the vicinity of CU I are discussed further n
TM 1. and Chapter 3 of this report.
2.2 omc
Geophysical surVeys to detect buried and submerged d:ums and sampling and
analysis of exposed drums on the surface of CU I tailings were performed n
1989 to locate buried drugs and characterize drum contents. Additional, drLm
investigation activities are planned for 1990.
2.2.1 CeoDhysical Investioat ions
Geophysical survey activitie, for CU I are discussed in detail in TM 2
(Appendix A). Geophysical survey activities were conducted by Denohue,
Region V A Technical Support Unit, and Great lakes National Program Off. :.
(GLNPO) staff. . The purpose of the geophysical investigations was to delineate
suspected drum disposal areas within CU I tailings piles and off—shore in
Torch take. Nagn.tem,try and ground penetrating radar (CU) investigations
were conducted on CU I tailings piles to Locate buried drums. CPA and sub-
botto. profile (seismic) investigations were conducted in Torch lake to locate
submerged drums.
As described in ( 2, magnetometer and CPA surveys were conducted at the
Centerline Apartments area in Lake Linden, the staapmill, site in Tamarack
City, and the sewage settlement pond site. Reference baseline and a 100— :j
SO—foot grid were surveyed at each location. Survey grid markers labeled .
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Torch Lake RI/li Section No.: 2
Final RI Report — 0 I Revj*ion No.: 0
A Contract No. 68—W8—0093 Dati: November 1990
north and east grid coordinates were placed along the survey lines. Detai..s
concerning the geophysical. survey investigations are explained in TM 2.
Results are discussed in Section 4.1.1.
The marine GPR system consisted of recording equipment and a GPR antennae.
The location of the boat was determined with Loran C Navigation and nari ed on
a strip chart recorder. The marine GPR was net effective in locating sub-
merged drums because the depth of water penetration was limited to approxi—
mately 20 feet.
The subbottom profiler system consisted of recording equipment with a seis mic
source and receiver. The location of the boat during this survey was deter—
mined with Loran C Navigation and marked on a strip chart recorder. The
subbottom profiler mapped several near—shore areas and conducted several
transects across the lake, both north—south and east—west. Technical. d ff
cult es terminated the survey without a complete coverage of the lake as
proposed in the Final Work Plan.
2.2.2 Drum Samolinc
Zn June 1999, A Technical Assistance Team (TAT) sampling personnel collected
samples from eight surface drums and five surface soil Locations along t?te
northern and western shoreline of Torch Lake. Drum and soil samples col-
lected, the matrix of each sample, and the analytical parameters analyzed for
each sample are su arized in Table 2—1. Details of the sampling program.
including maps shoving general sample locations, are presented in T N 3
(Appendix A).
2.3 ? AILINOS SAIt.IWG
2.3.1 Introduction
Tailings in CU I were sampled and analyzed to characterize their potential as
a contaminant source. for risk assessent purposes, and to provide data needed
to evaluate remedial action alternatives.
Tailing samples were collected from all nine sectors delineated in TM 1.
Approximate sampling locations are shown on Figures 2—2, 2—3, and 2—4. Survey
Locations of sampling points are presented in TN 4. Samples were collected
from the surface (0— to 6—inch) and subsurface (0— to 3—foot) depths.
Sampling procedures for surface tailings and subsurface tailings are reported
in TN 4 and TN. 5, respectively. Details of tailings sampling procedures are
also presented in the RI/VS Field Sampling Plan (Revision 1.) (Donebue, l9B9b .
Deviations fro. procedures described in the Field Sampling Plan are recorded
in TN 4 and TN S. . Also included in TN 4 is a su ary of visual descripticrs
for each sector.
In addition to tailings sample collection activities, field monitoring for
alpha/beta/gamma radiation was completed using a Monitor 4 detector. Meas-
urenants were recorded for composite subsampl.s. Tailings samples were
2—2
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Torch Lake * 1 /7 5 Section No.: 2
Final P.1 Report — O I Revision No.: 0
A Contract Mo. 68—W8—0093 Due: NOvembe 1990
analyzed for inorganic and sesivolatile organic compounds, which compris, a].].
.p nds on As Target Compound List with the exception of cyanide, as well
as fez the physical parameters of moisture content, grain size dist:ibuti n,
Atterberg Limits, and cation exchange capacity (TM 8).
2.3.2 Surface Samples
Surface tailings samples were collected to assess risk by exposure from dermal
contact and inhalation of fugitive dust. A total of 58 surface tailings
sample composites were collected from the 0— to 6—inch depth at a density of
one composite sample per 10 acres. As described in TM 4, the surface tai ] .i g
sampling and decontamination procedures were conducted in accordance with the
Torch Lake RI/PS Field Sampling Plan, Quality Assurance Project Plan, and
Health and Safety Plan (Donobue. 1989 b,c,d). Descriptions of texture,
Munsell color, vegetation, debris, and special features were recorded.
Samples were collected from areas that contained tailings. Grab samples were
obtained from sliae deposits (very fine grain size material), crushed slag,
and the slag pile to further characterize these materials.
2.3.3 Subsurface Samples
Subsurface tailings samples were collected to obtain data necessary to evalu-
ate remedial action alternatives, particularly stabilization and dust control
by vegetation. Twelve subsurface tailings eo.posite samples were coll.cted
from the 0— to 3—foot depth at a density of one sample p .r 20 acres. Proce-
dures used and observations recorded during collection of subsurface taillngs
samples are presented in TM 5.
A total of 23 subsurface excavations were conducted during the sampling pro-
gram. Prior to intrusive work, excavation locations were checked for buried
metallic objects with a metal detector. Radiation measurements were taken
from composite samples at each location. Hach excavation was also screened
with an 1u photoionizatien detector upon completion of th. excavation.
Photographs were taken at each sample location.
Subsurface conditions encduntered at Sector 3 preventsdezcavat ion to 3 feet.
Construction debris and gravel sized slag allowed digging with a shovel to
only 2 feet below grade. Therefore, the composite sample was collected from a
depth of 0 to 2 feet at this location.
Observations during subsurface tailings sampling at Sector S suggested that
the two sampling locations were located in tailings materials derived from
different sources. Although both areas consisted of aaygdaloidal basalt
tailings, the sample collected at Location 2 was coaxser—grained with a Lower
percentage of fine—grained tailings than the sample from Location 4. There-
fore, separate samples and decontamination procedures were conducted at both
locations.
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!occh .*ke RI/F5 Section No.: 2
F na1 RI Repoct — 0 I Revision No.: 0
A Contract No. 68—U—0093 Date: Movember 1.990
2.4 SOIL SAI LIP G
Liaited soil sampling VII performed to obtain preliminary information
regarding whether air—born. particulate materials are being transported from
00 I tailings sources to res d.ntial yards in t e primary study area. Soil
samples were collected from nine residential yards in take t.inden, Hubbell.
Tamarack City, and Mason, as well as from the take Linden football field.
racb sampl, was composited from four subsample. collected from the C— to
4—inch depth. Sample Locations and procedure, are described n detail Ln
TM 6. Soil samples were analyzed for semivolatile organic and inorganic
compounds.
Ten composite soil samples were collected, each comprised of four subsampies
representing the corners of the property sampled. Samples were collected
using an lI—inch, 3/4—inch diameter silt probe driven to a depth of 0 to
4 inches. Samples were analyzed for Routine Analytical Services (RAS) inor
ganic compounds and extractable compounds.
In general, the soil cores obtained consisted of various hues of grayish— and
brownish—brown, dry to damp silty sand. In most eases, a 1— tO 2—inch root
zone and darker topsoil was evident. Although signs of contamination were nor
apparent, traces of tailings and/or slag were noted. Descriptions were
recorded on soils data forms.
Additional details of the soil sampling and sample handling procedures are
recorded in T N 6 (Appendix A). Deviations from the Field Sampling Plan
(Donobue, l9 19b), are documented in TM 6.
Additional soil samples were also collected by SPA TAT personnel, and these
procedures and results are reported in TM 3.
2 • S
Ambient air samples were collected at Torch take to provide data to support an
air pathway analysis as a component of the baseline risk assessment for OU I.
Air monitoring and mods..inq data were obtained to characterize the airborne
transport of fugitiv, dust fret tailings, and to estimate emission rates and
concentrations of air contaminants to assess actual or potential receptor
exposure to air contaminants.
Michigan Department of 9atural Resources ( NR) personnel conducted the Tor:h
take air sampling program according to the procedures described in the To:c
take RI/PS Yield Sampling Plan (Donohue, 1989b) and the Quality Assurance
Project Plan (Denobue, 19890). Four sampling Locations were selected based
upon wind and population profiles to monitor likely exposure points, emiss crs
sources, and background conditions. Total suspended particulate (TSP) high
volume samplirs were operated over a 1—month period from August 14 to Sep-
tember 13. 1989. Samples were collected for 24—hour periods every Other day.
resulting in collection of 62 filters of TSP, including f lvi field blanks ad
five duplicates. Filters were analyzed for TSP at EPA’s Region V Central
2-4
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Torch LaU RI/PS Section Io.: 2
RI Report — O I Revision No.: 0
A Contract tb. 68—W8—0093 Dite: Novs .r 1990
Regional Laboratory. The two samples vith the highest TSP from sanpl,r
and the highest TSP from the duplicate sampler wers analyzed for 26 metals
including arsenic chromium. copper, nLcks l, Lead, and zinc.
Further details concerning the air sampling and meteorological monitoriflg
program irs provided in TM 7 (Appendix A). TM 7 includes NRs dOCUOent.d
report.
ARCS/RtrOR.RI/AA4
‘p -
2-S
-------
Torch 4k. RI/IS Section 4o.: 3
F na1 RI Report — 0 I Revision N e.: 0
A Contract Me. 68—W8—0093 Due: November 1990
Jacobsville Sandstone occur along the northwest margin of Torch take. Inned
ately adjacent to Torch take, bedrock crops out in Large areas beneath a th n
cover of glacial drift. The Portage Lake Lava Series consists of basalt and
andesitic Lava flows with interbedded conglomerates and sandstones. The
Jacobsville Sandstone is a Light red to bleached white, fine— to coarse—
grained feldspathic sandstone.
3.1.1.4 Historic Mining Practices
In addition to the tailings piles, abandoned tine works including stamp n lls
and smelters are a prominent surface feature throughout the region. The
tailings were often processed near a waterway. Therefore, many of th. shore—
lines of the lakes and rivers of the region are dotted with the ruins of
former stamp tills and smelters. The greatest concentration of these ruins s
along the western shore of Torch take.
3.1.2 TaIlings Surface Features
Th. western shore of Torch take is Lined with tailings piles and the asso—
outed stamp mill and smelter ruins attributable to past copper mining
- practices. This section provides detailed descriptions of surface features of
CU I tailings, which are themselves the prominent surface feature in the
primary study area. I tailings were divided into nine sectors as shown on
Figure 2—1 based on information obtained in a search of MTU archives and field
reconnaissance work as reported in TM I.
In the following sections, each sector is described in detail. Surface fea-
ture physical and Locational information for all sectors are sumearuzed in
Table 3—1 ., and additional descriptive information is provided in TM 1 and TM 4
(Appendix A).
3.1.2.1 Sector 1
Sector 1 (Figure 2—2) encompassás approximately 110 acres of red conglomerate
tailings. Tb. tailings consist of primarily dusky red to reddish brown, fine.
and medium silty sm_nd. In addition to being one of the Largest tailings piles
along the west shoreline of Torch Lake, Sector 1 exhibits the greatest relief
of any of the sectors. Relief La the north—central portion of the sector is
on the order of 20 to 30 feet. As is the case with many of the sectors,
Sector I baa Little or no relief along its perimeter. Vegetation is sparse
except along the northern perimeter adjacent to the Trap Rock River and in
those areas where vegetation has been actively encouraged through the addition
of topsoil and planting of pine trees. Vegetation is primarily confined to an
area surrounding the swage ponds and public campground. Areas of stressed
vegetation are also evident. Surface features unique to Sector 1 include an
abandoned Landf 111. and associated miscellaneous surfac. debris, sewage ponds.
a public beach, campground, and park. Sampling and analysis to characterize
the abandoned Landfill or the sewage ponds were not within the scope of the
field activities conducted for the CU I remedial investigation. Slime patches
consisting of broken chips resembling weathered shale and dry powder—like t e
clayey silt are apparent at the surface. Slime is the mining engineering t,cs
for the fin.—grained material produced during the copper reclamation process
3—2
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?0 Ch L.ake RI/IS Section No.; 4
Final, RI Raport — 00 I Revsjcn No.: 0
£PA Contract No. 68—V1—0093 Date: November 1993
4 • 0 T I A OP uTMaBa om
This chapter presents the results of CU I site and waste characterization fot
both atu:al chemical components and contaminant compounds, for the media
sampled in CU I RI field investigation activities. These media include drums.
00 I tailings, soil, and air. This chapter emphasizes the chemicals of poten-
tial concern for this site which were identifi.d in data evaluation performed
for the Baseline Risk Ma.ssmnt (Appendix B).
4.1 UH
The 1989 drum investigation included both a geophysical survey to attempt to
define the extent and location of drums buried in 00 I tailings, and sampling
and analysis of surface drums to determine the nature of their contents. RI•
activities related to identifying the nature and extent of drum wastes will
continue in 1990 when additional exposed, buried, and submerged drums will be
staged and sampled. Therefore, this report presents the results of initial
activities only. £valuation of the nature and extent, fate and transport
characteristics, or risk associated with drum—related contamination will be
performed and presented after additional drum investigation activities ace
conducted.
4.1.1 G.o bysiea]. Survey
The results of the geophysical survey of 00 I tailings are discussed in deta.L
in TM 2 and in TN 9. The ground penetrating radar data from the three tail-
ings sites investigated were difficult to interpret because of the complex
appearance of the signal reflection. This was attributed to the extensive
metallic debris in 00 I tailings fill areas. Also, radar target data did not
correspond to magnetic data.
The radar record from the Stampaill Site indicated radar targets that may
include buried drums or ether cylindrical metallic objects. The Stampeill
Sit. radar targets did not correspond to magnetic anomalies indicating that
the buried objects are non—ferrous (not iron or steel). Only a few radar
targets were recorded at the Centerlin• Apartments Site, and these did net
correspond to the magnetic anomalies. This indicates that these targets are
also mon—ferrous materials. The non—magnetic radar targets may be attribu-
table to large boulders of copper which did not go through crushers in the
stampmilli, and were often thrown into the tailings piles.
Radar targets were not found at the Stampmill and Centerville Apartments Sites
at the locations of magnetic anomalies, suggesting that (1) scrap iron or
steel may also be found at these locations, or (2) the magnetic anomalies are
outside of the spacing of the radar lines.
The radar targets at the Sewage Pond Site did correspond to magnetic anom-
alies. These targets have the best chance to be buried drums. However, cr
all magnetic anomalies were associated with radar targets.
4-1
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Torch take RI/PS Section No.: 4
Fuial R I Report — 00 1 Revjsj No;: 0
SPA Contract MO. 68 —w8—0093 Date: November 1990
Test pit excavations are required to verify whether the radar targets or
magnetic anomalies represent buried drums. Test pit excavations and drum
sampling are scheduled for 1.990.
4.1.2 Analysis of Surface Drum Contents
As discussed in Section 2.2.2. SPA TAT personnel sampled th. contents of eLght
drums found exposed at various locations on the surfac, of 00 I tailings. The
analytical data reported in TN 3 indicate that for seven of the drums, the
concentration of hazardous constituents was very low as measured by the EP
toxicity test. None of the drum waste material sampled is considered hazard-
ous based on R A characteristics of £2 toxicity. PcBs and pesticides wire
not found above method detection limits in any drum. In general, only traces
of volatile and semivolatil. organic compounds were found. One overturned and
leaking drum from a Subbell sampling location contained 4,000 ppm of trL—
chloco.thylene (TCZ). It is suspected that this drum is not related to past
site operations, but rather to a recent unauthorized disposal.
The TAT assessment did not indicate tnat immediate removal, of the drums was
necessary.
4.2 ? AILI 5
Radiation readings above background were not measured for any tailings sampi.
(TM 4).
Analytical chemistry data for CU I tailings samples are presented and dis-
cussed in TM 10. A summary of the ranges in concentration of chemicals of
potential. concern measured in surface and subsurface tailings samples is shawn
in Table 4—1. This tabl, also presents naturally occurring, native soiL c:n—
centrations. The data and discussion in TM 1.0 provide the following con-
clusions regarding the distribution of chemicals in CU I tailings.
Detectable ammuats of semivolatile organic compounds were measured in surface
(0 to 6 inch) tailings samples in all sectors. Ris(2—ethy lhexyl)phthal ,ate
(B ) was the most widespread, and was measured in all sectors except
Sectors 4, 7, and 9. The highest concentrations and th. Largest number of
seaivolatil.e organic compounds were measured in Sectors 3 and I. ?if teen
base/neutral, extractable compounds, primarily polycyclic aromatic hydro-
carbons, were detected in Sectors 3 and a. The highest concentrations of
semivolati].e organic compounds measured were for benzo(b)fluoranthene or
benzo(k)fluorantbene in Sector I.
Semivolatil. organic compounds were also measured in subsurface tailings
samples taken from the 0 to 3 foot depth in aU sectors except Sectors 4 and
9. The largest nuxher of subsurface semivolat Lie organic compounds and the
highest concentrations were also found in Sectors 3 and S.
The distributions and concentrations of semivolati l ,e organic compounds were
similar foc surface and subsurface tailings samples. Sectors 3 and I . where
seaivolatil. organic compounds were detected, were the same sectors where
4—2
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TABLE 4-1
SV? IARP OP 4ICAL.S OF POTVITIAL CONC .N
DCT!CT IN OP ABLZ ONIT I TAILINGS
TORCB LAX! RI/PS
AUGUST, 1989
Rartpe of Conc.ntratiorts, m jk
Su fac. Tai1in s Subiurfac. Tai.1 n a
Nat v, So 1
Ccncsntrat or.s.
Orqanie ConDeunds
bi s ( 2!tbythsxyl)
phtb aj.at.
PAHa
Napht a1.n,
2 —Met y lflap th ,n.
AeenapbThyl,n,
P1uori.nt ani
Pyren
Bonzo (a) anthracen.
Cbry..ns
B.nzo C b) f1uoraat ,n.
B•flzO(k)f1 Oganths .
B.nzo(a)pyT.ns
Indsne(1,2, 3—cd)
pyr.n.
Dibsazo(a,b)
anthracsn.
Bsnzo(q , .i)
perylsa.
Inorgan Ic Con o n4 ,
A luainua
Ant iaony
Ar s.n I c
Bag Iua
B.ryll. Lus
Boron
Cbroaiua
Cobalt
Copper
Lied
Manqan..•
5.190 — 37,200
3.40 — 11.7
0.370 — 8.3
5.5 — 135
0.1ev — 1.7
N/A
20.7 — 46.3
5.4 — 52.6
72.3 — 3.020
2.5 — 2.04
203 — 1,080
5.410 — 27.200
3.5 — 7.3
0.47 — 14.4
5.1 — 68
0.130 — 1.0
N/A
23.6 — 42.7
8.5 — 32.8
699 — 5,540
0.380 — 82.8
217 — 703
10,000 — 300,000
1.0 — 40
100 — 3,500
0.3. — 40
5.0 — 3.000
1.0 — 40
2.0 — 100
2.0 — 200
1.00 — 4,000
0.0503 — 0.440
0.0693 — 0.440
0.08.7 — 0.430
1 — 5
0.0373 — 0.440
0.123 — 0.430
0.0493 — 0.440
0.350 — 0.430
0.0393 — 0.440
0.0733 — 0.430
0.0473 — 0.440
0.0483 — 0.430
0 — 0.04
0.0543 — 0.440
0.063 — 0.430
0 — 0.015
0.0463 — 0.440
0.0223 — 0.430
0 — 0.01
0.0573 — 0.56
0.0253 — 0.430
0 — S
0.0673 — 0.56
0.0663 — 0.430
0 — 0.03
0,0483 — 0.440
0.0663 — 0.430
0.023 — 0.430
0 — 0.01.5
0 — 8
0.0913 — 0.440
0.1403 — 0.430
0 — 0.015
0.0143 — 0.440
0.0663 — 0.430
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Torch Lake RI/PS Seet on NO.: 4
Final R I Report — CU I Revision No.: 0
A Contract o. 68—W8—0093 Date: November 1990
railroad ties, tar roofing, or coal debris were documented in the field
sampling logs (see Table 3—1). Sectors 3 and 8 were t only sectors wtere
the presence of coal at sampling locations was documented. All of the sem.-
volatile polycyclic aromatic hydrocarbon chemicals of potential concern are
documented as being derived from coal, coal—tar, wood preservative sludge, or
petroleum sources (Verschueren, 1983).
Inorganic compounds of potential concern including chromium, cobalt, copper,
lead, nickel, and vanadium were found in most sectors at varying concen-
trations.
Arsenic was found in Sectors 1, 3, 5, 6, and 7. Arsenic was found in sub-
surface samples for Sectors 3 and 6. Arsenic levels in slag samples exceeded
typical native soil levels. Mercury was detected in all samples from
Sectors 3 and 8 at concentrations exceeding typical soils.
The concentration and distribution of metals appeared to be similar in tt e
surface and subsurface samples. For inorganic cOnstituents, the ma3ority of
the subsurface tailings concentrations are within or below the rang, of con-
centrations found at the surface.
In general, copper concentrations measured in tailings are elevated above the
range generally found in soils. This is expected because of the occurrence of
native copper in the Keweenaw Peninsula.
Slime material, the fine—grained tailings material deposited in layers in the
tailings, contained higher concentrations of chromium than tailings samples.
Th. concentrations of other inorganic compounds such as arsenic, copper, and
lead are similar in slime samples and tailings samples.
Slag material, produced by smelting high copper concentrate produced in the
stamping and flotation processes, exhibited higher concentrations of arseruc,
chromium, copper, and lead than the concentrations measured in the tailings
samples.
In suary, neither organic nor inorganic compound levels measured in 00 I
tailings are dramatically higher than those found in naturally—occurring
soils.
4.3
Soil chemistry analytical results are presented and discussed in TM 11. Den
composite residentiai soil, samples were collected and analyzed during 00 I RI
activities to assess contaminant distribution from tailings sources. The
results are discussed here although neither complete characterization of Torch
Lake .superfund Site soils nor assessment of risk attributable to soils was
within the scope of CU I U activities. A sumeary of the ranges of chemicals
of potential concern measured in soil, samples and naturally occurring soil
concentrations are shown in Table 4—2.
‘—3
-------
TABLE 4—2
SWoiAPS 0 ? ICALS 0? P I 1TIAL C0Nc .N
DL ’EC w IN SOIL SAMPLES
TORCE LAKE EXITS
AUGUST. 1.989
Range of
Concent &t ions.
Native So 1
Concentrations,
Oroa.nic Compounds
bis(2—Etbyib.xy l)
p thaLat.
PAHI
Napbt .a3.n.
2—M.tby lnaphtha l.n.
Aeenaprithy l.ne
P enanthzen e
Pyrens
Bin2o(a)a thraeen e
Chrysene
Banzo( b ) fluoranthan.
Benzo( k ) fluoranthen.
Bsnzo(a)pyrsne
Indeno(1 ,2 ,3—ed)pyren e
D benzo(a, )anthracsne
B.nzo(gh. i)p.rylen.
0.800 — 3.8
U — 0.0713
U — 0.054J
U — 0.133
0.0493 — 1.900
U — 0.0923
0.0453 — 2.600
U — 1.500
U — 1.600
U — 1.500
U — 0.670
U — 1.600
U — 0.630
U — 0.2903
U — 0.670
0 — 0.04
0 — 0.015
0 — 0.01
0—5
0 — 0.03
0 — 0.01.5
0—8
o — 0.015
0 — 0.02
Inorganic Co oeu ds
Aiuainua
Mt imony
A z senic
Bartue
B.ryLl iua
Boron
Chzo2iu
Cobalt
Copper
Lead
Manganese
3.1.40 — 7,600
U
U — 7.00
U — 101.00
U
U
5.90 — 20.10
U
58.30 — 459.0
6.20 — 329.0
91.40 — 357.0
10,000 — 300,000
1.0 — 40
100 — 3,500
0.1 — 40
5.0 — 3.000
1.0 — 40
2.0 — 100
2.0 — 200
100 — 4.000
150 — 925
1—5
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TA3L.E 4-2
SU Q ART OF 4ICAr s OF PO’r!NTIAL CONC N
D TECT IN SOIl. SAI T. .U
TORCH tAKE KI/TS
AUGUST, 1989
(cont .nued)
Range of Native Soil
Concentrations, Concentrati orts,
Mercury 0 — 0.47 0.01 — 0.08
Nickel. 0 — 33.70 5.0 — 1.000
Silver 1.5U 0.1 — 5.0
Titaniua U 1,000 — 10,000
Vanadiua 1.1.40 — 26.30 20 — 500
o U indicatu Compound vu not detected and the numerical value i dicat.i
th. contract required quantitation limit, ad ustsd for dilution and
prcent aoisture (organics) or ths iastum.nt detection limit
(inorganic.).
o N/A indicates chemical, flOt analyzed for in this tedium.
o .7 Indicate, this value is estimated.
o PM denotes polycyclic aromatic hydrocarbon compounds.
o Source of naturally occurring native soil concentrations is Dragian
(1988).
-------
Torch Like RI/IS Sectiø No.: 4
?inal RI Report — OD I Revision No.: 0
EPA Contract Mo. 68—W8—0093 Date: Nev.m ,r 1990
Semivolatile organic compounds were measured in most of the ten soil samples.
Base/neutral extractable and TIC hydrocarbons wire the most widely distri-
buted. Semivolat .le organic compounds detected at levels higher than
naturally—occurring levels in sails include: fluoranthen., pyrene, benzo(a)
anthracene, benzo(b) fluoranthen., benzo(k) fluoranthene, indeno (1,2,3—ed)
pyrene, and benzo(g,h,L) perylene.
Inorganic compounds of potential concern. including chromium, copper, lead.
nickel, and vanadium were measured in most of the soil samples. Copper, lead.
and mercury were detected at concentrations exceeding native soil concen-
trations. The measured capper concentrations were higher than typical native
soil levels for all soil samples except fer that from the football field.
High concentrations of lead and mercury were measured in one soil sample fr n
Lake Linden. The sampling team did net observe anything that might explain
tte high Lead and mercury concentration in this sample. High mercury levels
were also measured in four samples from Lake Linden and Mason. Arsenic wag
measured in S of U soil samples, at levels typical of naturally occurring
soils.
EPA Technical Assistance Team (TAT) personnel also collected soil samples
during a Torch Lake Site Assessment (TM 3). Three samples from Locations of
suspected contamination in Hubbell and Mason and a background soil sample from
the east side of Torch Lake were analyzed for volatile and semivolatile
organic compounds, toxicity metals, total metals and cyanide. Methylene
chloride. phenanthren., fluoranthene, pyrene, chrys.ne, and di—n—octyl phtPa-
ate were detected from a soil sample collected directly underneath a drum.
tie pesticides or PcHs wire detected. EP toxicity metals concentrations were
below wimus concentrations (40 erR 261). All of th. metals detected were
within the typical concentration ranges of metals in soils.
The inorganic compounds measured in the ten residential soil samples collected
for the RI field investigation (TM 11) are generally an order of magnitude
higher than concentrations measured in the TA? background soil sample col-
lected from the east sid. of Torch Lake (TM 3).
4 • 4 ARISC OP ?AILIN $ A SOIL SXSt’IT
In general. semivolatile organic compound levels were orders of magnitude
higher in soil samples than in tailings samples. Arsenic, chromium, and
copper coacsntration.s ate generally similar in soil samples and tailings
samples. The bighst Level of lead measured was detected in a soil sample.
rot both tailings and soil sample., contaminant compounds were distributed in
a non—homegeneous manner. There was no pattern of distribution which sug-
gested impact of tailings—derived compounds to residential soils. The sporad-
ic distribution, the lack of geographical proximity, and the concentrations
measured suggest that detected compounds ate unrelated between these media.
4— 1
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Torch Lake RIfTS Seeti n No..: 5
Final. R I Report — CU I Revision No.: 0
EPA Contract so. 68—118—0093 Date: NoVembet 1990
5.0 CCIPZMCIWFI’ TATE A TRAK y
This chapter addresses potential routes of contami na t migration and Conta —
nant persistence and mobility for chemicals of potential concern in ocj i
tailings.
5 • 1 r ,r iriAL OP NI A?ION
The remedial investigation and risk assessment for Operable Unit I address the
potential routes of migration highlighted in Figure 1—5. Contaminant aigra—
tion from CU I tailings could occur by generation of particulate material, or
by infiltration, runoff, or erosion. Contaminant migration could also occur
from secondary sources such as soil.
Particulate generation may occur when fugitive dust is generated by wind
erosion of exposed tailings. Vehicular travel over contaminated tailings also
creates dust and may be a source of airborne contaminants. Evaluation of the
air exposure pathway was conducted by emissions and air modeling as part of
the Baseline Risk Assessment (Chapter 6 and Appendix B).
Quantification of other migration pathways was not part of the scop. of this
investigation. Contaminant infiLtration from CU I tailings will be addressed
by collection and analysis of groundwater samples from beneath CU I tailings
during the CU II RI, and by leaching tests conductid by the Bureau of Mines.
Conta iit. . t runoff and erosion will also be addressed after colleetio of
surface water and sediment samples in the CU IX RI. The potential for contam-
inant migration from drums in CU I tailings will be addressed after additional
investigations to locate and sample drums to determine the nature and extent
of drum—derived contamination.
The significance of contaminant migration by infiltration, runoff, or erosion
routes is limited by the persistence and mobility of the contaminant types
detected in CU I tailings. Contaminant persistence and mobility are discussed
below for CU I chemicals of potential concern.
S • 2 R!AC1U.5? P SI3T MD IC3jLI
There are severs.), mechanisms that can affect contaminant fate and transport in
the environment. These include transformation mechanisms (such as biotrans-
formation, hydçolysis, oxidation, and precipitation); phase change mechanisms
(such as volatilization, sorption, ion exchange, and dissolution); and trans-
port mechanisms (such as advection. diffusion, complezation/ chelation, and
particle—facilitated transport). These mechanisms can cause Loss, movement,
change, or retardation of contaminnate in the environment. The potential for
these mechanisms to contribute to contaminant fate or transport in CU I
tailings is determined by the chemical and physical properties of the tailings
and of the compounds of interest. The chemicals of potential concern identi-
fied for CU I tailings include primarily polycyclic aromatic hydrocarbons
(PARs) and inorganic compounds. The fate and transport characteristirs of
these classes of compounds are discussed in the following sections.
S— i
-------
Torch Lake Mining Waste NPL Site Summary Report
Reference 2
Excerpts From Site Assessment for Torch Lake,
Houghton County, Michigan, Report, EPA Contract No. 68-01-7367;
Prepared for EPA by WESTON-Major Progrants TAT;
1990
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SITE ASSESS)cENT
FOR
TORCE LAZE
EO G ToN COtJNTY, MXCEI3pj
Prepared for:
U.S. Envizon entaj Protection Agency
Region V
230 South Deaber Street
Chicago, I11inei
CONTRACT NO. 68—01—7367
T DO 5—8906—06 and 06A
Prepared by:
WESTON-Maj or Pro grans
Tecbnicaj. A3sista cs Tea.
Region V
FEBRUARY 1990
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1.0 SIT D SCRTPTTON
• Torch Lake is located on the Kveenav Peninsula in Houghton County,
Michigan (Figure 1). At its southern end, it feeds into Portage
Lake, which is part of the Keveenaw Waterway that opens into Lake
Superior. Torch Lake is located approximately 14 miles north of
the Keveenaw Bay. The lake has a surface area of 2,717 acres, a
mean depth of 56 feet. and a maximum depth of 115 f..t. The towns
of HubbeU (population 1,278), Lake Linden (population 1,200),
Quincy (population approximately 10) and Mason (population
approximately 50), are located on the west side of Torch Lake
(Figure 2).
The Torch Lake area is a remnant boom town from the late nineteenth
and early twentieth centuries, when the local copper mining
industry was at its peak. Although populations have declined, the
Torch Lake area is still maintained as a habitat for wildlife and
a recreational area for fishing, boating, and swimming. Many
peopl. currently own cottages at or near the lake which they use
on a seasonal basis. Torch Lake is also used for a non—contact
cooling water supply and for treated municipal wastewater
assimilation.
1.1 Toooara hv
The topography of Torch Lake is governed primarily by the various
rock lithologies and faulting processes of th. area. Within three
miles west of Torch Lake, the relief ranges from 600 feet to 1,200
feet. To the east, relief is considerably lower due to the more
easily eroded bedrock. Also noted to the east are numerous lakes
and wetlands which are characteristic of a recently glaciated
plain.
1.2 Surface Water
The major sources of inflow to Torch Lake are Trap Rock River, and
Mammell, Dover, McCallum, and Sawmill Creeks. The largest is Trap
Rock River which discharges directly into the north end of Torch
Lake. The Trap Rock River watershed covers approximately 46 square
miles and 58% of the total Torch Lake Basin. As a result of the
mining industry, tributaries to the Torch Lake Basin transport an
abundance of stored mine tailings. It is estimated that 2,000
kilograms pe year of dissolved copper is transported through
tributaries into Trap Rock River and eventually deposited into
Torch Lake. Transport of these tailings during high magnitude
discharge is expected during the winter thaw flooding events.
1.3 Geolocv
Most of the western shoreline of Torch Lake is composed of variable
sized tailing material. The material ranges from pebbles to coarse
sand to fine silt. The remaining constituents of the shoreline
sediments ar. conglomerate and basaltic rock indigenous to the
Upper Peninsula.
1
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The Xewesnaw Peninsula is underlain by Precambrian rocks ° er wt j
glacially transported deposits are lain. Multiple advan 055 and
retreats during glacial episodes have scoured the resistant bedrock
and infilled many of the alluvial valleys. The various types ce
glacial deposits that are found in the region include till,
lacustrine, and outwash.
1.4 Soils
The soils in the area consist primarily of sandy and silty loams.
These types of soils develop from till, outwash, Holocene alluvium,
and reddish clays. In local areas, the reddish clays are deposited
between the ground surface and the bedrock. Soils in the glacial
deposits are spodosol, which develop under forest vegetation and
tend to concentrate iron and aluminum oxides within the reddish
clay “5 horizon. The soils in the area tend to have fragipans
which develop 19 — 24 inches below the surface. The fragipans
resist root penetration and water infiltration, directing the flow
of water laterally before penetrating into the ground water system.
1.5 Ground Water
The U.S. Geological Survey conducted well water sampling in 1963
and 1977. Analysis of those samples indicate that of 35 wells in
Houghton County, only three had a specific conductance greater than
500 microahos per centimeter (umho/cm) (EPA, 1981). The data from
the analysis of the Houghton County well water samples also showed
most of the wells contained very low levels of chloride, sulfates
and dissolved solids. The pH ranged from 5.0 — 9.0 for the 35
wells. During the time of these tests, analysis of the data
indicated a good quality water source for the general area.
All ground water wells drilled on the north and west side of Torch
Lake are set in bedrock due to the bedrock’s high stratigraphic
position. Many of the Torch Lake communities and seasonal
residents have converted their homes to a municipal well, water
system or the Gregori. water system, an independently owned well
water supplier. Other communities, such as Hubbell, receive their
water supply frc larger cities, such as Calumet to the northwest.
2.0 SITE ACXGR0UN
Torch Lake .is located In the copper mining district of the upper
peninsula of Michigan. Deposits of native copper extend 100 miles
southwest, in a belt beginning at the tip of the Xeweenaw
Peninsula. Copper mining began on the Xeweenaw Peninsula in the
1860$ with the first mill opening on Torch Lake in 1868. Milled
copper was extracted by crushing or wstampingN the rocks into
smaller pieces. The extracted copper was then sent to a smelter
and melted. The remaining crushed rock particles, called
“tailings’ or ‘stampsands ’, were discarded with the mill processing
water into Torch Lake or the Keweenaw waterway. Mining output,
4
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milling activities and tailings production peaked in the Torch Lake
area in the early l900s to 1920. AU of the mills were located on
the north shore of the lake. Records from the mills describe
pumping of tailings into Torch Lake as well as deposition of
tailings on property around Torch Lake.
In around 1916 and 1917, new tachnology was introduced to extract
copper which utilized lime, pyridine oil, coal—tar creosotes, wood
creosote, pine oil, cupric ammonia and xanthates. After the
extraction, the chemically contaminated water was returned to the
lake.
In the Torch Lake area ever 10.5 billion pounds of native capper
were processed. Between 1868 and 1968 at least 200 million tons
of tailings were dumped into Torch Lake, filling at least 20
percent of the original volume of the lake, resulting in drastic
changes in the geography of the shoreline.
In the 1920s, workers angry during local mill strikes were rumored
to have concealed explosives in drums. Information from local
residents indicates that the explosive drums may have been left
along the shores of Torch Lake, and may have eventually been placed
in the Lake.
In the 1970s, the Michigan Water Resources Commission (MWRC)
collected baseline data on the chemical profile of the water and
the biota of Torch Lake. In 1972 a large volume of cupric ammonium
carbonate was discharged from storage tanks located at the Lake
Linden Leaching Plant into Torch Lake. The MWRC investigated the
spill, and determined that no significant deleterious effects from
the spill had occurred to the surface water quality, algae and
fish, based on comparisons to the data from the 1970 study.
Michigan Technical University (MT 7) researcher’s have contributed
numerous studies on the impact copper mining wastes have had on
the water quality and biological integrity of the Torch Lake area.
Some examples of studies conducted by MTU are: “Tumor Induction
Study” of fish liver histology; the “Environmental Fate of
Xanthates and Creosotes”; the “Tumor Incidence and Parasite Survey
of Perch, Walleys, and Sauger from Torch Lake, Moughton County
Michigan”; and the “Copper Budget for Torch Lake”.
Torch Lake presently receives industrial discharge from mining and
non—mining industry. In 1980 the Peninsula Copper Industry
Recycling Plant, owned by the Venture’s Group, began operations
which includes discharging its non—contact cooling water into Torch
Lake. Exploratory research at the Centennial Mine in 1980 resulted
in a dewatering discharge into the Slaughterhouse Creek, a
tributary of Trap Rock River which flows into Torch Lake.
5
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In 1983, the Michigan Dpartment of Public Health (MDPH) issued an
advisory against the consumption of all saug.r and valley. from
Torch Lake because of the number of fish that had derma]. tumors.
The advisory was issued as a precautionary measure until the
causative factor(s) of the fish tumors and the potential risk to
humans could be identified. The advisory was still in affect at
the time of Technical. Assistance Team (TAT) sampling in July 1989.
In 1983, the International Joint Commission Water Quality Beard
designated Torch Lake as a Great Lakes Area of Concern (AOC). An
AOC is defined as an area with a ]a ovn impairment of a designated
use. The AOC is confined to Torch Lake and its shores on the basis
of the fish consumption advisory, tumor frequency, metal-
contaminated sediments, the impact on biota, and the history of
mining waste disposal. In 1986 a study by the 1’Q DR determined that
the lake sediments are heavily contaminated with heavy metals such
as copper, zinc, tin, and lead. on June 10, 1988, Torch Lake was
placed on the National Priorities List (NPL), under the
Comprehensive Environmental Response, Compensation and Liability
Act (CERCLA), and en September 28, 1988 a Remedial Investigation,
Feasibility Study (R.t/FS) was initiated by the U.S. Environmental
Protection Agency (U.S. EPA), with Jae Lee as U.S. EPA Remedial
Project Manager (RPM).
3.0 SITE -INSPECTION
On June 21, 1989, TAT was tasked by the U.S. EPA to perform a site
assessment and collect samples from abandoned drums and visually
contaminated soils along the northern perimeter of Torch Lake • On
July 17, 1989, TAT was additionally requested to collect
residential and municipal veil water samples.
3.1 Drum and Soil Samnlinp
On June 21, 1989, TAT members Steve Renninger, Prank Beodray, and
Louise Raimondo were met by U.S.EPA On-Scene Coordinator (OSC)
Walter Nied and RPM Lee in the town of Lake Linden located en the
shores of Torch Lake. TAT conducted sampling of drums and
potentially contaminated soils along the shorelin. of Torch Lake.
Eight drum and five soil samples were collected along the northern
and western shoreline of Torch Lake (Table 1). Air monitoring was
conducted in the sampling areas with a photoionization detector
- 10.2 ionization potential probe) and radiation meter. TAT
sampled two locations at Lake Linden. At the first sample
location, which was situated along the debris—covered shoreline of
Torch Lake (Figure 3), three drum samples were collected (S-57, S-
58, S—59). A soil sample (S—65) was collected from a man—made
tailings island covered with stunted conifer vegetation. Sample
S-60 was collected near an abandoned building from corrugated
material used for roofing which had weathered and fallen to the
ground (Figure 4). Th. TAT documented the presence of unidentified
drums containing wastes, steamlines with deteriorated insulation,
6
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and two storage tanks within the abandoned warehouse. No ambient
air readings exceeded background levels at the Lake Linden sampling
locations. -
TAT then collected samples from drums located in the southern
extent of the city of Hubbell, which is locally referred to as
Tamarack City. Drum.. were sampled in three separate arsas in
Hubbell (Figure 4). The first drum sampling area was located along
the debris—covered shoreline of Torch Lake. On. drum sample (S-
61) was collected because it was believed to be representative of
all the drums • TAT photodocumented the drums scattered along the
shorelin, and into the shallows of Torch Lake. The second drum
sampling area in Hubbell was located away from the shoreline in a
heavily vegetated area. Sample 5—62 was collected from an
overturned drum which was observed to contain a black, tar-like
waste that had partially spilled onto the soil. Two samples, S-63
and 5-64, were collected at the third sampling location from the
soils adjacent to two transformer pads, where local residents had
previously reported fluid spills. No readings were recorded above
background during air monitoring at the Hubbell sampling locations.
The final sampling locations were near the town of Mason (Figure
5). TAT conducted air monitoring in the sampling areas recording
no ambient air readings above background levels. Two locations
were sampled by TAT in a wooded area containing randomly dispersed
55—gallon drums. A total of four samples were collected: one solid
(5—67), from an overturned, uncovered drum: on. soil (S—68),
collected directly underneath a drum; and two liquid (S-66 and S-
69), from drums that contained liquids.
A background sample (5—70) was collected on the east side of Torch
Lake. Analytical parameters are summarized in Table 1. The
samples were analyzed by National Contract Laboratory Program (CLP)
Laboratories and ATEC Associates, Inc.
3.2 Ground Water Sam lin
On July 18, 1989, TAT members Beodray and Anne Anderson returned
to Houghton, Michigan, to conduct water sampling of residential and
municipal wells in or around Torch Lake. The purpos. of the well
water sampling was to determine whether the potential contamination
of Torch Lake had affected ground water quality. Air monitoring
with the KNU was conducted on a sample-by—sample basis.
TAT sampled the water of six private residential wells, two
municipal wells and one well providing water to 40 renters in the
town of Mason (Table 2). All private veil water samples were
collected along the northern shore of Torch Lake along State Route
41 (Bcotjack Road) and Trap Rock Road (Figures 6 and 7). The
following objectives were used in determining the well locaticrs
to be sampled: wells which were located in do ., proximity to
suspected sources of contamination; were of shallow depth; were
screened in suspect formations; were located in close proximity t:
the lake: and/or serve a large number of people (>30 individuals)
1*
-------
Samples were collected from the spigot located Closest to the veil.
and prior to any water treatment system or holding tank. All
samples were analyzed for volatil, organic compounds (VOCS) and
hazardous substance list (ESL) metals, and two samples were
additionally analyzed for acid and base/n ,i ,g (ABN) and cyanide,
under TAT Analytical Services TDD#5-8907—i.,4, by WCstOn -GUlf Coast
Labs.
4.0 ANALY’TI L RKStlt T1
The analytical results from the TAT sampling are suarjzed in
Tables 3—7.
4.1 Drum and Soil Sam liyia
The EP toxicity metals data, summarized in Table 3, indicates that
mone of the material sampled is considered hazardous based on the
R RA characteristics of EP toxicity (all levels were below the
aximum concentrations established in 49 CFR Part 261).
nalyticaj. results of the RCRA/asb.stos analysis are su arized in
Table 4. The material sampled for RCPA parameter analysis was not
considered to be hazardous based on RCRA characteristics. Asbestos
analysis indicates that the roofing tile material contains 3 0-40
percent chrysotile asbestos.
Organic analysis of the samples is sl.lmmarized in Table S. None of
the samples contained pesticides or PCBs above method detection
limits. The sample from Hubbell-Drum #2 ($62) contained 4000 ppm
trichloroethene (TCE) and 34 ppm bis(2 ethylhexyi)phthaja , .
Samples S—se and S—66 contained methylen. chloride at $ ppm and 3
ppm respectively, but methylene chloride was also detected in the
background sample. Contaminants detected at estimated levels
include: acetone, benzene, 2-hexanone, xylene, tetrachlorethene,
b.nzoic acid, phenanthr.ne, fluoranth.ne, pyr.ne, chrysene, di-n-
octylphthalate, naphtha1ene and 2 —methylnaphthalene. Additional
tentatively identified organic compounds for the samples are
s ummarized in Attachment A. The analytical results of the total
HSL metals and cyanide analysis for th. background soil sample are
summarized in Table 6. All of the levels detected were within the
typical concentration ranges of metals in soil. Total metals and
cyanide analytical results for the remaining samples were not
available at the time of writing.
4.2 Ground Water Sam iing
Analytical results of the TAT veil vater sampling are summarized
in Table 7. The sample collected from the Village of Lake Linden
Municipal well (5—77) contained iron levels (0.33 ppm) greater than
the secondary maximum contaminant level (SMCL) of 0.3 ppm. None
of the organics detected in the samples were at levels above the
MCL or removal action level (ML).
15
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Torch Lake Mining Waste NPL Site Summary Report
Reference 3
Excerpts From Superfund Fact Shcet:
Torch Lake Superfund Site, Houghton County, Michigan;
A Region V; 1989
-------
Background continued from Page
Torch LaKe s estern shore the larger
comrrlunities or 1-loughton Hancock
and Calumet lie 10-15 miles further to
the flest Wetlands bound the lake on
the east Torch Lake is used ror fisning
ooating s imrriing ion-contact cool irg
%ater supply and iId1ife nabitat In
addition treated astewater from the
regional se age lagoon system is dis-
charged into Torch Lake
History of Mining Operations
attheSite -
For approximately 100 years. from 1868
to the late 1960s. Torch Lake .as the
site of copper milling and smelting racil-
itres and was a dumping ground for cop-
per mining and milling wastes. All of
the mills were located on the west side
or the lake Copper was extracted by
crushing or stamping’ the rock into
smaller pieces grinding the pieces. arid
driving them through successively
smaller meshes Until the earls 1900s.
the copper and crushed rock were then
seoarated using gravity The cooper was
subsequently sent to the smelte and
the crushed rock particles called “tail-
ings” or “stampsands,” were discard-
ed with the mill processing water typi-
call} into the lake or waterway. Because
or tne inefficiency of this early milling
process. substantial amounts of copper
remained in the discarded tailings.
B 1916 reclamation plants were using
ne processes to recover additional cop-
per rrom the discarded tailings. One of
these processes invoi ed creoging up
the tailings combining them ith sater
and oil, and agitating the mixture to
produce a troth upon %‘nich copper-
bearing partictes would float. During
the 1920s. a ariet or chemicals here
used to rurther increase the erficienc or
this process Atter the process was com-
pleted. the chernicali treated tailings
were once again dumped back into
Torch Lake.
B ’ the time the last copper mill had
closed in 1968. over 10 5 billion pounas
of native copper had been produced
from this area. More than halt of this
amount had been processed along the
shores of Torcri Lake Between 1868 arid
1968. approiumatei 200 million torts of
tailings were oumped into Torch Lake
filling in at least 20 percent of the lakes
original volume. These deposits created
small tailings peninsulas” in the lake
and resulted in other changes to the
original shape of the shoreline.
nvironmentaI Actions to Date
Environmental concern about the cen-
tur -long deposition of tailings into
Torch Lake began in the early 1970s.
High levels of copper and heavy metals
(such as arsenic and chromium)
found in Torch Lake water, sediments.
and tailings, chemical spills and other
toxic discharges. and fish tumors have
prompted marty investigations into the
possible impacts of mine-waste disposal.
Numerous regulatory actions have been
taken b state, national and Interia-
tional agencies. For example in 1ST?
the Michigan Water Resources Comma-
sion studied the impact of a chemical
spill into the northern end or Torch
Lake at the Lake Linden Leacrung Plant
In 1983 the Micrugan Department or
Public Health announced an aa isor
against consuming Torch Lake sauger
and walleve because or reported aonor-
malities and lesions in tne sh A full
chronology of significant reguLatory
agenc activities at the Torch Lake ste
is presented on page 4) Ho %eve the
causes and full extent or tl’e environ-
mental problems related to Torcri Lai e
remain unclear.
In 1984. U S EPA designated Torch Lake
as a Superfund site, adding it to the -
National Priorities List a roster r
uncontrolled hazardous aste sites eli-
gible for federal investigation and
cleanup funds. LS EPA took this
action based n,.’]i the eie ateo ic’ &s
ôT ’ and heavy metals to_nd n
Torch Lake water sedime ts a tail-
ings. (2) the 1972 chemical spill ‘ito : e
north end or Torch Lake and 31 tie
1983 fish consumption aa .sor In
1985. L S. EPA began a searcri ror
Potentially Responsible Parties
(PRPI arid has so far ident fied and
concluded negotiations with three PRPs
In 1988 the State of Michigan issued a
letter of assurance enabling L S EPA to
conduct a long-term RL’FS Specifics
about the EPA investigation to Degin
later this month are presented in the
following section.
. RI/FS Activities Planned for the Torch Lake Site
As mentioned earlier, the entire Torch
Lake Superfund site is quite large,
encompassing all of Torch Lake. the
northern half of Portage Lake. the North
Entry to Lake Superior. and tributary
areas. Furthermore, nine different kinds
of samples may need to be collected and
analyzed: (1) tailings, (2) surface
water, (3) ground water, (4) drums.
(5) soil, (6) wetlands. (7) sediments.
‘S.. (8) air and (9) biota. especially the fish
‘ population (see Figure 2).
Because of the magnitude of the site arid
the diversity or sampling and analysis
that may be necessary. U S. EPA has
divided the site into three segments’
called Operable UnIts (015) (Figure 3).
Operable Unit 1 (01’ 1) includes the sur-
I face tailings on the western shore of
Torch Lake. Operaoie Unit 11(01’ II)
includes other areas or potential con-
tarnination in and around Torch Lake.
including soil ground . .ater submerged
tailings, sediment sur-race %ater and
biota. Operable Unit Ill consists or other
tailings sot rces in the rnid-Keweenaw
Peninsula. including the orth Entry,
the northern portion of Portag Lake.
and tributary areas. Separate RI ‘FSs wit
be conducted for each Operable Init
The RL/FS for 015 1 vi l begin ‘s: and is
discussed in more detail r : i xt
page.
iri age..
•2
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O k
Torch Lake Mirung Waste NPL Site Summary Report
Reference 4
Excerpts From Fish Gro ih Anomalies in Torch and Portage Lakes,
1974-1988, Houghton County, Michigan, MI/DNR/SWQ-90/029;
MDNR, Surface Water Quality Division;
1990
-------
MI/DNR’SVO—90 /i
MIC!’CAN DEPA.RTMENT OF JAITRAL RESOURCES
SL’RFACZ ATER QUALITY DIVISION
‘.ARCH 1990
STAFF REPORT
ISF GROWTH ANCMALIES EN TCRCM AND POPTAGE LAKES
1974— 198
HOt. CFToN COLTNTY, MICHIGAN
Fellc ing the report and descr .ption of several anomalous growths in
sauger and walleyes from Torch Lake (Black et al; 1982). the Micni an’
Department of Public Health ( PH) issued a fish consumption advisory f r
Torch Lake vall.ye and sauger in 1983. In 1984. the lake (Figure 1) as
designated as a 307 site under the Michigan Environmental Response Act,
Act 307 of 1982. Also in 1984, the U.S. EPA designated Torch Lake, as
veil as other locations in the area having minIng wastes, as a Super _
site. Site evaluation by EPA is ongoing. In 1985, the International
:othz Coission’s (IJC) Water Quality Board designated Torch Lake as a
Great Lakes Area of Concern (AOC). sol.lv on th. basis of the fish
consumption advisory limited to sauger and valley. (IJC, 1985). A
remedial action plan (RAP) was completed for Torch Lake by the c iga
Department of Natural Resources ( ©NR) Surface Water Quality Div s.:n and
presented to the IJC in 1987 (Evans 1987).
In the RAP, several activities were to be undertaken by the . WNR.
Walley. or sauger were to be stocked annually for a period of years and
water and fish were to be sampled in 1988 in Torch Lake, as well as the
adjoining Portage Lake. WaLleyes have since been stocked annuaUy,
except for one year when sauger were stocked. Fish were collected in
1988 as planned and analyzed for contaminants and tumors. The purpose
of this report is to present the fish contaminant and tumor data and
compare it to other data where appropriate.
FINDINGS AND CONCLUSIONS
1. Organic contaminants were at trace level, in tissues from fish
collected in Torch and Portage Lakes. Only four (4) of the 56 fish
samples analyzed for mercury had concentrations that exceeded the
0.5 mg/kg consumption advisory action limit and none exceeded 1.3
mg/kg. Overall, the fish from these lakes are among the least
contaminated fish enc unt.red in the Michigan Fish Contaminant
Monitoring Program.
2. No internal or external grovth anomalies were observed among the
458 fish collected in 1988. No liver n.oplasms (cancerous grovtns)
were found among the 47 valleyes collected in 1988 nor in 25 wal.eyes
collected in 1985. The incidence of liver neeplasms has apparet.v
declined and may now be near normal background levels, however,
additional itudy is needed to more accurately determine normal
background tumor fr ncies, eipec a.1iy .n o aer and larger
-------
3. Saugers were not collected in 1988 followIng an extended perIod of
population declne which began in the 1960’s. Sauger are a tur d
water fish and once the waters cleared, as copper ore milling decreas
and then stopped. sauger were apparently no longer able tc out—
conpere other game fish. Sauger, for all practical purposes, are ‘o
longer important to the sports fishery of Torch and Portage Lakes.
. Bicassays of the water and sediments of Torch Lake, have not
indicated the presence of a carc nogenic substance. Tie data do
not support the basis for the continuance of thIs spe i ’Tc. _ !
E sumption advisory. -________
BACKGROL ’ND
Torch Lake, locatec on c ’e Ceweenaw Peninsula and tributary to Portage
Lake and _ake Superior, came to the national forefront in 1982 when
abnormal or tumorous growths were described from the liver, spleen, and
mesenceries of the lake’s old sauger and walleve. The highly visible
external tumors on these species have been associated with viral
Infections and are coon in Great Lakes populations. Other fish in :-e
diverse fish counities of Torch and Portage Lakes have not exhibited
either external or internal growths considered abnormal.
The Michigan Department of Public Meai.ch issued a fish consumption
advisory on Torch Lake sauger and walleye in 1983 even though these flsr
move freely into Portage Lake and Lake SuperIor. The advisory was Lss..ed
as a precaution, until the causative agent or agents, if present, In
Torch Lake could be determined. No tumor inducing agents have been
Identified, either by chemical analysis or bioassays, at levels that
would cause the high ir cidence of liver tumors.
Consumption of fish with tumors or abnormal growths, while aesthetica .lv
displeasing, is not known to transmit tumors to humans. Since ‘or:h Lake
was the center of an outstanding sauger fishery for many years prior to
the closing of the riparign copper mills and smelter, it seemed reasonable
to concentrate considerable study effort on Torch Lake and the copper
industry for possible fish tumor inducer,. Several, studies were
completed and have been si srjzed in the RAP (Evans, 1987). Tumor
induction studies of the appropriate copper flotation chemicals have not
been ca.plet.d.
Torch Lake received approximately 200 million tons of copper ore
tailings between the late 1860’s and the 1960’. (Markham 1986). Over
20 percent of this 1100 hectare lake (present mean depth 17 me e:s was
filled with tailings, and relatively small amounts of industr:al and
municipal trash. Raw sewage and mine pumpag. were also discharged to the
lak.. Similar types of waste were discharged to Lake Superior and
Portage T.aks.
Stamping the copper ores and recovering the native copper via a
relatively inefficient process initially, and considerable copper was
known to exist in the coarse tailings (stamp sand.) in the lake. In
1915, leaching of conglomarate tailings and ores with cupric aonlu:
—3—
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Torch Lake Mining Waste NPL Site Summary Report
Reference S
Technical Memorandum Number 1;
From Jeffrey D. Maletzke, Donahue & Associates, Inc., to Lori Ransome,
Donahue & Associates, Inc.; July 28, 1989
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General
The history of copper mining in this region and subsequent deposition of
tailings in Torch take, spans a period of approximateLy 100 years, f ton the
late 1860’s to the late 1960’s. The copper mined was found in conglomarate
and amygdaloid forms. Coogloserate is formed by compaction and cementat on of
river—deposited gravel, with copper in interstitial spaces. Amygdaloid is
derived when vesicles formed in cooling lava become fiUed with copper.
Once mined, the ore was transported to silts along the western shore of Torcn
rake (Figure 1) where the ore was crushed (or stamped. The copper and
crushed rock were separated by qravimetric sorting in which the difference in
specific gravity between the copper and the crushed rock permitted the copper
to be concentrated and extracted. The waste sands (tailings) produced from
these operations were discarded, typically by pumping into Torch take. Va1. es
equal to one—fourth of the total copper were lost in the waste sands.
Beginning about 1916, spurred by war time economy and advances, in setalli rgy,
the tailings were dredged from the lake, screened, :.c:ushed, and gravity
separated at one of three reclamation plants. From oldest to youngest r ese
plants included the Calumet and Becla (1916), the Tamarack (1925), and Pc
Quincy (1943) (Figure 1). At these plants, an aonia leaching process . as
used to recover copper from conglomerate tailings, and a flotation process was
uied to extract copper from both conglomerate and amygdaieid tailings.
The leaching process involved the dissolution of metallic copper in a c’.ipric
amaoniua solution containing an excess of amsonium carbonate. With the copper
dissolved as either cuprous or cupric amaonium carbonate, steam distil1ar .on
was employed to cool. and condense the careen dioxide and aonia. thereby
facilitating recovery of the copper. teaching accounted for 40 percent nf tte
copper reclaimed from the original stamp sands.
The flotation process involved agitation of ore, water, oil, and chemicals to
produce a froth, supporting copper—bearing particles. Typical reagents
consisted of 50 percent coal tar. 15 percent pyridine oiL, 20 percent coa 1 ar
creosote, and 15 percent wood creosote. In 1926, xanthates were introduced.
Prior to the use of xanthatsi, onLy conglomerate tailings were treated by
flotation. Approximately 0.05 pounds of potassium and sodium xanthate e e
used per ton of or. in combination with 0.15 pounds of pine oil per eon f
ore. Pine oil contained wood creosote. Flotation accounted for 10 percent of
the copper reclaimed in the original stamp sands.
After reclamation, the chemically treated tailings were returned to ?orth
Cake. The present Location and extent of the tailings presumably reflects me
final, placement after processing by tne respective reclamation plants.
The following discussion stems directly from maps and descriptions found in
the EITU archives, as well. as f rem field reconnaissance. During field recon-
naissance the location and extent of the tailings, as well, as other notable
features, were sapped on air photos (Figures 2 through 6). Tailings were tr en
assigned to sectors as indicated en the air photos and Figure 7. Each sector
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&
Torch Lake Mining Waste NPL Site Summary Report
Reference 6
Technical Memorandum Number 7;
From Lori Ransome, Donahue & Associates, Inc., to Project Files;
February 9, 1990
-------
TABLE 2
PD - Field Duplicate
Space — Analyzed for but not detected
AA — Ambient Sa.pie
TSP — Total Buupended Part iculates
DETECTED INORGANIC COMPOUNDS (ug/m 3 )
AIR TSP SAHPLES
TORCH LAKE RI/VS
August 1909
AAO I
AAO I
8/18/89
8/26/89
AAO2
AAO2
Haeon
AAO3
VU AAO3
AAO3
Aluminum
Arsenic
Boron
Barium
Calcium
Cadmium
Chromium
Copper
Magns. urn
Iron
Manganese
Nickel
f in
Titanium
Zinc
TSP
0.227
0.110
0.00191
0.144
0.151
0.2 30
0.291
0.00447
0.0145
0. 0322
20
Dackground
AAO4 AA O4
8/26/89 9/5/0
0.201
0.0017
0 • 0517
0.002
0.799
0. 00917
0.20 1
0.2 30
0 • 2)7
0 .00406
0. 00427
0. 00805
0. 0544
22
0.132
0. 0016
0. 0294
0.00151
0.620
0.0858
0.153
0.169
0. 00221
0.266
0.0625
0.0032
1.0553
0. 02 76
0. 00192
0.100
0.266
0.316
0. 00564
0. 0149
0.0555
21
0.345
0.0005
0. 0708
0. 00282
0.975
0. 00)69
0.117
0.336
0.451
0. 00915
0.405
0. 0944
0.00)15
1.11
0.17)
0.300
0.516
0.0104
0. 0 374
0.121
32
0.127
0.0013
0.035
0. 00 165
0.964
0.0800
0.190
0.164
0.00184
0.179
0.00 13
0. 03 46
0. 00206
0.840
0.0795
0.233
0.254
0. 00488
0. 009 76
0. 0575
25
0.219
0.00 I
0.000
0.002
I .0
0.075
0.103
0.110
0.002
0.009
0.0353
0.0526 0.102
21 30
0.0480 0.06 1
18 14
ARCS/R/TORCHI.R I/AC)
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Mining Waste NPL Site Summary Report
United Nuclear Corporation
Churchrock Site
Gallup, New Mexico
U.S. Environmental Protection Agency
Office of Solid Waste
June 21, 1991
FINAL DRAFT
Prepared by:
Science Applications International Corporation
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
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It’
DISCLAIMER AND ACKNOWLEDGEMENTS
The mention of company or product names is not to be considered an
endorsement by the U.S Government or by the U.S. Environmental
Protection Agency (EPA). This document was prepared by Science
Applications International Corporation (SAIC) in partial fulfillment of
EPA Contract Number 68-W0-0025, Work Assignment Number 20.
A previous draft of this report was reviewed by Ricky McCoy of EPA
Region V I [ (214) 655-6730], the Remedial Project Manager for the
site, whose comments have been incorporated into the report.
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Mining Waste NPL Site Swnmary Report
UNITED NUCLEAR CORPORATION
CHURCHROCK SITE
GALLUP, NEW MEXICO
INTRODUCTION
This Site Summary Report for the United Nuclear Churchrock Site is one of a series of reports on
mining sites on the National Priorities List (NPL). The reports have been prepared to support EPA’s
mining program activities. In general, these reports summarize types of envirorunental damages and
associated mining waste management practices at sites on (or proposed for) the NPL as of February
11, 1991 (56 ral Register 5598). This summary report is based on information obtained from
EPA files and reports and on a review by the EPA Region VI Remedial Project Manager for the site,
Ricky McCoy.
SITE OVERVIEW
The United Nuclear Corporation (UNC) Churchrock Site is an inactive uranium mill and tailings-
disposal site located in an isolated area of McKinley County, 15 miles northeast of Gallup, New
Mexico. The Mill was operational from 1977 to 1982. The Mill, designed to process 4,000 tons of
ore per day, used the conventional acid-leach solvent-extraction method to extract uranium. The
waste tailings were pumped to a 100-acre tailings-disposal area (see Figure 1). According to
radioactive materials license records, between 3.4 and 3.6 million tons of acidic tailings were
disposed of at the site. In May 1982, UNC closed the Mill to await better uranium market
conditions; the market did not improve, and UNC announced that the Mill would not reopen
(Reference 1, pages ES-I, ES-3, 1-4, and 1-5). In 1987, UNC submitted a closure plan for
decommissioning the Mill to the Nuclear Regulation Commission (NRC).
Arsenic, cadmium, lead, molybdenum, cobalt, manganese, chromium, and radionuclides (including
uranium and thorium) are the constituents of concern at the site. Although no people reside within
the site boundary, adjacent land includes the Navajo Indian Reservation to the north and land to the
east and south held in trust for the Navajo Tribe and administered by the Bureau of Indian Affairs.
Ten wells are located in slightly over a 3-mile radius of the site; the closest is 12,000 feet northeast of
the site. Four of these wells are operational, and are used for both livestock and domestic purposes
Land use is primarily grazing for sheep, cattle, and horses (Reference 1, pages ES-l through ES-3, 2-
15, and 2-16). Contaminants in the Alluvial Aquifer and/or deeper aquifers at concentrations
exceeding clean-up standards include aluminum, arsenic, cadmium, cobalt, manganese, molybdenum,
1
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United Nuclear Corporation
I.
.I.
— . .
,I__ —
FIGURE 1. SITE MAP
2
Pisuat (Is
SITE LXAICN MAP
I.HTW P4JO..EAR Slit
4 XICO
0
, ,
c.l
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Mining Waste NPL Site Summary Report
nickel, selenium, nitrate, Total Dissolved Solids (TDS), radium 226 and radium 228, and gross alpha
(Reference 2, Table 6).
In October 1979, the New Mexico Environmental Improvement Division (NMEID) ordered UNC to
implement a discharge plan to control contaminated tailings seepage which was responsible for
ground-water contamination. Ground-water pumping and evaporation was initiated in 1981. From
1979 to 1982, UNC neutralized tailings with ammonia and/or lime (Reference 1, page 1-4).
In 1983, the Churchrock site was placed on the NPL. In early 1987, UNC submitted a reclamation
plan to the NRC for decommissioning the mill and began to address monitoring, tailings-seepage
control, and general decontamination. A Memorandum of Understanding (MOU) between EPA
Region VI and NRC Region IV was signed in August 1988, this MOU provided that EPA would
address ground water outside the disposal site, while NRC would address surface reclamation and
source control.
Remedial Investigation efforts were initiated by EPA Region VI in 1984 (Reference 2, page 5). In
1988, a Record of Decision (ROD) describing the remedy at the site, selected in accordance with
Comprehensive Environmental Response, Compensation, and Liability Act (CERCLA) and local
applicable or relevant and appropriate requirements (ARARs), was signed by EPA Region VI in
concurrence with the State of New Mexico and NRC. The ROD estimates the present value costs of
future remedial actions, using a 10 percent discount rate, to be approximately $17 million dollars over
a 10-year period (Reference 2, Declaration, page 1 and Summary, page 41).
OPERATING HISTORY
The Churchrock Uranium Mill was licensed under a radioactive-materials license in May 1977, and
began milling operations in June 1977. The Mill was designed to process 4,000 tons of ore per day
using conventional crushing, grinding, and acid-leach solvent-extraction methods to produce uranium.
The ore processed ax the site (average ore grade 0 12 percent uranium oxide) came from UNC’s
Northeast Churchrock and Old Churchrock mines as well as the nearby Kerr-McGee Quivera mine
The crushing, grinding, and milling process produced an acidic waste of ground ore and fluids
referred to as tailings. Tailings waste was pumped to a 100-acre disposal area where between 3 4 and
3 6 million tons of tailings were disposed (Reference 1, pages 1-1 and 1-4; Reference 2, page 4).
UNC’s tailings-disposal area is located directly east of Pipeline Canyon. The tailings-disposal area
was subdivided by cross-dikes into cells identified as the South Cell, Central Cell, and North Cell
areas. Two soil-borrow pits are in the Central Cell area (Reference 2, page 1) (see Figure 1)
3
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United Nudear Corporation
(Reference 4). In July 1979, the dam on the South Cell breached, releasing approximately 93 million
gallons of tailings and pond water to the Rio Puerco River. The dam was repaired and clean-up
actions were taken (Reference 1, page 1-4; Reference 2, page 4).
In October 1979, NMEIID ordered UNC to implement a discharge plan to control tailings seepage that
was responsible for ground-water contamination. In 1981, UNC implemented a ground-water
pumping system that withdrew ground water and returned it to a lined pond for evaporation
(Reference 1 page 1-4; Reference 2, page 4). In response to NMEID concerns that acid solutions in
tailings were major factors in mobilizing contaminants, UNC added lime or ammonia to the tailings
from 1979 to 1982 (Reference 1, page 1-4).
In May 1982, UNC announced that it was going to temporarily close the Churchrock Uranium Mill
due to depressed uranium market conditions. The market did not recover, and UNC closed the
facility. In 1987, UNC submitted a closure plan to NRC to decommission the Mill (Reference 1,
page 1-4; Reference 2, page 4).
SITE CHARACTERIZATION
EPA conducted a Remedial Investigation, completed in August 1987, to determine the nature and
extent of ground-water contamination in aquifers present at the site. EPA concluded that three
primary aquifers of concern existed, the Alluvial Aquifer and the Zone 1 and Zone 3 Aquifers of the
Upper Gallup Sandstone (Reference 1, page ES-6). The Alluvial Aquifer has been contaminated by
mine discharges and tailings seepage. Several distinct plumes exist, the major one extending
southwest from the South Cell for at least 1 ,000 feet downgradient. Other plumes extend to the
north. Numerous contaminants exceeded National Primary and Secondary Drinking Water Standards
(DWSs) (Reference 1, page ES-9).
Source Characterization
Tailings solids are believed to be the main source of contamination on the Churchrock site. Tailings
solids- and liquids-source sampling was not conducted during the Remedial Investigation. However,
analytical results characterizing these materials were obtained from previous investigations conducted
by UNC in February 1986 and by NRC in April 1987 (Reference 1, page 5-1). Tailings fluids were
characterized as acidic, high dissolved solids water with sulfate, ammonia, and sodium as the
prmcipal ions. Metal concentrations, particularly aluminum and iron, were very high [ each over
1,000 milligrams per liter (mg/I)]. Radioactivity (thorium 230) was also high [ 10,000 to 50,000 pico
Curies per liter (,pCiIl)]. Additional data offered by NMEID suggested ammonia concentrations as
4
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Mining Waste NPL Site Summary Report
high as 4,000 mg/I; nitrate as high as 17 mg/I; and arsenic as high as 1.87 mg/I. NRC’s 1987
sampling showed a pH of 3 34, TDS over 58,000 mg/I, ammonia over 5,800 mg/I, thorium 230 of 13
pCi/I, iron of 2,700 mg/I, lead of 3.34 mg/I, and radium 226 of 24 Pci/i. The Remedial Investigation
suggested that the tailings-liquor chemistry may have been variable throughout its discharge history
(Reference 1, pages 5-1 through 5-3).
Surface Water
The original goal of the Remedial Investigation’s surface-water studies was to determine the amount
of infiltration occurring along Pipeline Canyon at the tailings-disposal area. This data was to be used
to understand the recharge characteristics of the aquifers present at the Churchrock site, as well as to
determine the quality of the surface water. At the time of the Remedial Investigation studies, Pipeline
Canyon had a perennial flow since 1968 as a result of mine dewatering from the Kerr-McGee and
UNC mines. During active periods of dewatering, surface-water gauging indicated a loss of nearly
200 gallons per minute (gpm) of perennial flow along Pipeline Canyon over a distance of less than 1
mile through the study area due to evaporation and seepage. Following the cessation of mine
dewatering by UNC in 1983 and Kerr-McGee in 1986, the Canyon returned to its natural, ephemeral-
drainage patterns. This has resulted in a substantial decrease in the volume of water that can infiltrate
into ground water (Reference 1, pages ES-5, 5-3 through 5-5).
Surface-water sampling was conducted prior to the cessation of mine discharges (i.e., before reversion
to ephemeral flow). Water quality was governed by mine discharges, precipitation, and upgradient
surface water. TDS concentrations were approximately 500 mg/I. The major anions were
bicarbonate and sulfate, and the prominent cations were calcium and magnesium. Contaminants
detected in surface water are listed in Table 1 (Reference 1, page 5-6).
Low metal concentrations were believed to be a function of the pH. It was also noted that, because
infiltrating surface waters would dissolve constituents as they pass through the alluvium and bedrock,
surface-water quality would not necessarily reflect ground-water background quality. Radiological
analyses indicated the presence of radionuclides, which were attributed to the source rock in the mines
(Reference 1, pages 5-6 and 5-7).
5
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United Nuclear Corporation
TABLE 1. CONCENTRATION OF CONSTITUENTS IN SURFACE WATER
Constituent
Concentration
(mg/I)
pH
7.6to8.6
Aluminum
0.73
Barium
0.48
Iron
0.19
Manganese
0.03
Nickel
0.06
Vanadium
0.05
Zinc
0.04
Ground Water
Complex ground-water flow patterns exist on the site. This is partly due to numerous fractures and
fissures present in the bedrock units. In addition, Zone 2 of the Upper Gallup Sandstone is a shale in
some areas, acting as a barrier between Zones 1 and 3, which otherwise are hydraulically connected
with each other and with the Alluvial Aquifer. The Mancos Shale, located beneath Zone 1 of the
Upper Gallup Sandstone, acts as a barrier to mitigate vertical migration into the lower aquifers
(Reference 1, page ES-7). To analyze contaminant migration in the ground-water, a total of 33 test
borings were drilled on the site (29 monitoring wells, and thur observation wells). The borings
ranged from 62 to 263 feet deep with an average depth of 160 feet (Reference 1, page 3-5).
The aquifers of concern include the Alluvial and Zones 3 and I of the Upper Gallup Sandstone, all of
which are hydraulically connected. These Aquifers were sampled and analyzed in March, May, and
August 1985 and were identified and characterized as described below.
Alluvial Aquifer
The Alluvial Aquifer receives water from surface-water infiltration through Pipeline Canyon and from
recharge from precipitation and seepage from the tailings ponds (as noted, surface-water infiltration
would be substantially lower since the cessation of mine discharges in 1986). Overall, flow direction
is to the southwest along the axis of Pipeline Canyon (although seepage from the ponds had caused a
6
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Mining Waste NPL Site Summary Report
mound in local ground-waxer levels). EPA has identified several distinct, high-TDS plumes in the
Alluvial Aquifer that may be the result of mine water, tailings, or other sources. The major plume
extends southwest of the South Cell of the tailings ponds at least 1,000 feet downgradient of the site.
TDS values up to 20,000 mg/I were found. The plume extent downgradient has not been determined.
Other plumes extend north of the tailings ponds.
In 1985, the alluvial plumes contained numerous contaminants above the Primary and Secondary
DWSs. Maximum pollutant concentrations found in alluvial ground water included nitrate (greater
than 300 mg/I), sulfate (greater than 8000 mg/I), selenium (0.4 mg/I), manganese (20 mg/I),
molybdenum (0.28 mg/I), and cadmium (0.125 mg/I). Gross-alpha activity exceeded Primary DWSs
in six wells, with levels ranging from 16 to 45 pCi/I, compared to the Maximum Contamination Level
(MCL) (after subtracting uranium and radon activity) of 15 pCi/I. Water from one alluvial well had a
gross-beta activity in excess of 50 pCi/I. The radium 226 and 228 standard of 5 pCi /I was exceeded
in two wells. Concentrations of thorium and uranium isotopes indicated little migration away from
the tailings ponds (Reference 1, pages ES-7, ES-9, and 6-4).
Zone 3 Upper Galluo Sandstone
The major flow system in the Zone 3 Aquifer is to the northeast from the North Cell of the site. In
1985, the Zone 3 Aquifer had been severely impacted by contaminants leached from the north tailings
cell. A large, elongated plume had migrated more than 2,000 feet from the tailings-disposal site at a
rate of 337 to 450 feet per year from 1979 to 1985. TDS concentrations near the source were greater
than 15,000 mg/I with pH values of less than 3. Major ions affecting water quality included ammonia
(100 mg/I), sulfate (8000 mg/I), and nitrate (35 mg/l). Radionuclides (radium 226 and 228, thorium
230, uranium 238, and gross alpha and beta) were present at very high levels onsite and much lower
(but still elevated) levels offsite. Metals concentrations a1 o decreased with distance from the source
(Reference 1, pages 5-46, 5-48, 5-49, 6-5, and 6-6).
Maximum metal concentrations exceeding Primary and Secondary DWSs in EPA monitoring wells on
tribal lands to the east included manganese (55 mg/I), arsenic (1.8 mg/I), cadmium (0.277 mg/I),
chromium (0.135 mg/I), and beryllium (0.254 mg/I). Radionuclides were also found in waxer from
Zone 3 Wells on tribal lands 800 feet from the pond (Reference 1, page 6-5).
Zone I Unoer Gallup Sandstone
The Zone 1 Aquifer exhibited predominant flow to the north and received waxer from the same
sources as Zone 3. Contamination in Zone 1 was less ext than in Zone 3. Contaminants were
7
C
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United Nuclear Corporation
migrating from the North Cell to the northeast and east. A second plume from Soil-borrow Pit 2,
located within the Central Cell, had moved downgradient to tribal grounds to the east. TDS
concentrations rangmg from 6,000 to 7,000 mg/I, pH values from 4 to 5, and high nitrate
concentrations exceeding 100 mg/I were measured in monitoring wells on tribal lands (Reference 1,
pages ES-12, 6-7, and 6-8).
Fate and Transport of Mobile Contaminants
• Arsenic - Arsenic is mobile in an aqueous systems at moderately acidic pHs. Low arsenic
concentrations (on the order of 0.1 to 0.6 mg/I) are present in the tailings area because at
very low pH, the arsenate adsorption on iron oxyhydoxide is at its highest level. This creates
an arsenic “reservoir” of adsorbed arsenic. As the pH increases, some of the arsenic is
released and is mobile. As the oxidation-reduction decreases, most of the arsenic previously
adsorbed were into solution and can be transported. Arsenic was found in onsite Zone 1 and
3 Wells at levels over the 0 05 mg/I DWS (at levels up to 2.5 mg/I). The 1985 arsenic
distribution was a combination of oxidation-reduction and ground-water flow (Reference 1,
pages 5-62 and 5-63).
• Molybdenum - In ground water, molybdenum travels (in solution) as an anion, and is not as
easily attenuated as arsenic. Leachate characterization of the tailings for molybdenum was not
available; however, values along the tailings embankment northeast of the North Cell
indicated molybdenum values of 0.2 to 0.7 mg/I. Wells further downgradient had much
higher molybdenum values (up to 59 mg/I in Zones 1 and 3 Wells). This increase in
molybdenum concentration with distance could not be explained at the time (another natural or
anthropogenic source or an earlier “slug” load from the tailings area were suggested as
possible explanations) (Reference 1, pages 5-65 and 5-66).
• Manganese - Manganese is relatively mobile because it typically remains in solution until the
Ph reaches 8.0 and above. Manganese was typically present at the outer edge of the
contamination plumes. Manganese is present in the tailings; and wells in all three Aquifers
throughout the study areas exhibited manganese concentrations above the Secondary DWS
(Reference 1, page 5-66).
• Cadmium - Cadmium, like manganese, is relatively mobile. Sorption onto sediments and
manganese oxide occurs as Ph increases. Adsorption onto organic materials and minerals,
coprecipitation with metal oxides, and substitution in carbonates also control cadmium
mobility. In 1985, cadmium was not present above the 0.005 mg/I detection limit in wells
near the tailings ponds with low Ph values. Downgradient wells exhibited sporadic
concentrations above the source concentration, suggesting that the cadmium may be inherent
to natural geologic media or reflective of a previous slug loading (Reference 1, pages 5-68
and 5-69). Historic sampling by NMEID indicates a different cadmium distribution:
cadmium was rarely found away from the tailings ponds. Away from the ponds, cadmium
was reportedly absorbed or precipitated (Reference 1, page 5-69).
L
8
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Mining Waste NPL Site Summary Report
• Radionuclides :
- Radium 226 and 228 - No measurement of radium activity in the Zone 1 Aquifer exceeded
the Clean Water Act standard of 5 pCi/I. Only two of eight Alluvial wells exceeded the
standard. Eleven of 15 Zone 3 Wells had levels ranging up to 47.6 pCi/ I; radium activity
levels decreased rapidly downgradient of the tailings ponds (Reference 1, pages 5.72
through 5-75).
- Thorium 230 - Mobility of thorium at the site was a function of pH. Thorium can remain
in solution ax pH values below 5 (as is the case near the ponds); at higher pH (as is the
case downgradient of the ponds), thorium precipitates and is immobile. High thorium
levels were found only in Zone 3 Wells, from 41,000 pCi/I near the North Cell to about
0.2 to 0.4 pCi/I near the edge of the pond. Thorium was determined not to be migrating
far from the ponds (Reference 1, page 5-76).
- Uranium 238 - Most wells showed uranium 238 activity over 15 pCi/I (an “arbitrary”
value selected in the Remedial Investigation to reflect the alpha activity standard).
Uranium 238 activity was found to decrease rapidly away from the core of the contaminant
plume (Reference 1, pages 5-76 and 5-77).
- Gross Alpha - Gross alpha readings (without subtracting radon) above 15 pCi/I were found
throughout the site and in all aquifers of concern. Zone 3 Wells had the highest gross
alpha concentrations, up to 3,000 pCi/I in areas where TDS concentrations exceeded
10,000 mg/I. Downgradient, near the fringe of the plume, values decreased to about 100
pCi/ i Outside the plume, activities were in the vicinity of 50 pCifl Generally, Zone 1
activity levels decreased significantly downgradient from the source (Reference 1, page 5-
77).
ENVIRONMENTAL DAMAGES AND RISKS
In July 1979, the dam on the South Cell breached, releasing 93 million gallons of tailings and pond
water to Rio Puerco River. In October 1979, the State ordered UNC to implement a discharge plan
to control the tunings seepage deemed responsible for ground-water contamination. In 1981, UNC
implemented a ground-water pumping system that withdrew ground water from site aquifers and
returned it to Borrow Pit 2 for evaporation (Reference 2, page 4).
UNC began tailings neutralization (in late 1979) to reduce the mobilization of contaminants; this
continued until early 1982. Neutralization involved the addition of anunonia or lime to the tailings.
In 1983, EPA designated the Churchrock site an NPL Site and initiated a Remedial Investigation
effort (Reference 2, page 4).
9
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United Nuclear Corporation
A Risk Assessment, based on ingestion of ground water contaminated at 1985 levels, estimated excess
lifetime cancer risks for arsenic and radionuclides (the only carcinogens among the contaminants).
The excess lifetime cancer risk from arsenic ingestion was estimated as 1 x 10 (based on a maximum
arsenic concentration) to 1.2 x 10 (average concentrations).
For radionuclides, the excess cancer risks was estimated to be 1.8 x 10’ to 6.5 x 10 In addition,
estimated daily intakes of cadmium, manganese, and nickel were estimated to exceed health-based
standards for noncarcinogens (Reference 3, pages ES-6, 4-13, 4-19, and 4-20). These estimates were
all based on a “future-use scenario,” in which it was assumed that wells would be constructed for
domestic use in each of the clean-up target areas (Reference 3, page ES-6). However, EPA has found
no current exposure from ground-water ingestion from currently operating domestic and livestock
wells within 4 miles of the site (Reference 2, page 23).
REMEDIAL ACTIONS AND COSTS
As noted previously, UNC cleaned-up a 1979 release of tailings and pond water, and conducted
activities to neutralize tailings from 1979 to 1982 (Reference 1, page 1-4). In addition, UNC
implemented a ground-water pumping system in 1981 that withdrew contaminated ground water for
treatment and evaporation in a lined pond (Borrow Pit 2) (Reference I, page 1-4). As of August
1987, a total of 27 wells were actively pumping ground water for neutralization and return to Borrow
Pit 2. The average pumping rate was 30 gprn (43,200 gallons per day) (Reference 1, page 5-24).
In 1981, EPA conducted a preliminary evaluation of the UNC Churchrock Site by assessing existing
data and conducting Site Assessment Inspections. In 1982, an additional sampling inspection was
conducted, and in 1983, EPA included the site on the NPL. EPA conducted a Remedial Investigation
from March 1984 to August 1987 (Reference 2, page 4). The Feasibility Study Report was released
in August 1988. A ROD, describing the final EPA remedy at the site, was signed in September 1988
by the Region VI Administrator, and verbal concurrence was given by the State of New Mexico
(Reference 2, page 5). The final remedy, as well as available cost data, are described below.
Remedial actions addressing source-control and onsite surface reclamation will be implemented by
UNC, as directed by NRC. These activities are to be integrated and coordinated with remedial action
for the Ground-water Operable Unit (described below) (Reference 2, Declaration, pages 1 and 4).
The selected remedy for the Ground-water Operable Unit is intended to prevent further offsite
migration of contaminants by containing, removing, and evaporating contaminated ground water. The
10
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Mining Waste NPL Site Summary Report
remedy for the Ground-water Operable Unit is comprised of the following elements (Reference 2,
Declaration, pages 2, 3, and 4):
• Installation of a monitoring-well system in all three aquifers to detect increases in extent or
concentrations of ground-water contaminants at (and outside of) the tailings-disposal area
• Continued operation of existing seepage (i.e., ground water) extraction systems in Zone 1 and
3 Aquifers
• Containment and removal (by extraction wells to be installed) of contaminated ground water
from the Upper Gallup Zone 3 and southwest Alluvium Aquifers
• Evaporation of ground water removed from Aquifers using lined evaporation ponds and spray
equipment to enhance evaporation
• Implementation of a performance monitoring and evaluation program to allow a determination
to be made of the adequacy of the remedial action outside of the disposal area.
According to the ROD, the capital cost of the ground-water remedy was estimated to be $12 million;
the present-worth estimate (using a 10 percent discount rate) was estimated to be $17 million over a
10-year period. These costs were estimated “without detailed engineering data,” so actual costs were
reported to depend on a number of factors, including direct and indirect remedial action start-up
costs; size of evaporation system; well-system performance; duration of pumping; and future changes
in such fuctors as clean-up criteria (Reference 2, pages 41 and 42).
CURRENT STATUS
Remediation of the Churchrock site is on-going. UNC submitted a 1989 review of ground-water
corrective action to EPA and NRC. This report describes the corrective-action program. This
report, based on limited monitoring data, (third and fourth quarters of 1989), stated that the extraction
wells in Zone 3 are operating (as intended) by removing seepage from the target area and creating a
hydraulic barrier to further migration of tailings seepage. Eighteen Zone 3 Wells were extracting an
average combined total of about 51 gpm (about 8 gpm, prior to start-up of 12 new wells in August).
Water was sent to the lined evaporation ponds. Additional Zone 3 Wells are to be installed in 1991
(Reference 4, pages 2, 3, and 9).
Data (second, third, and fourth quarters of 1989) for the Zone 1 Aquifer showed corrective action
will be a long-term process. Although Borrow Pit 2 was dewatered, ground-water and pH levels hail
remained stable, and the plume had migrated about 150 feet downgradient (Reference 4, pages 4 and
10).
11
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United Nuclear Corporation
Data for the Southwest Alluvium Aquifer was collected during the fourth quarter of 1989,
immediately prior to (and following) the initiation of pumping. Data were said to provide a
preliminary indication that the ground-water withdrawal system was working as planned (by beginning
to reverse water-level gradient and creating a hydraulic barrier to flow). Three Extraction Wells
began pumping (extracting ground water) from Zone I in August 1989, and had an average combined
total flow rate of about 20 gpm (Reference 4, pages 5 and 10).
Two 5-acre lined evaporation ponds began operation in January 1989. Misters installed in 1988 were
used in the summer, both to control wind-blown tailings and to dispose of extracted ground water
(Reference 4, page 5).
Although not part of the Ground-water Operable Unit remedy, UNC also began source-control
activities. In 1989, UNC reported that the North Cell had been regraded and covered with an interim
soil cover to eliminate ponded water and minimize infiltration in the Zone 3 Aquifer (Reference 4,
pages 5, and 6).
EPA, NRC, the State Authority (NMEID), and the Navajo Tribe have analyzed the annual review and
have included some modifications in the remediation plan. These modifications, including the
addition of ground-water monitoring wells, have been completed. According to EPA, the agencies
and the Navajo are currently reviewing UNC’s 1990 review of ground-water corrective action to
assess the effectiveness of remedial activities and modify them as necessary.
12
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Mining Waste NPL Site Summary Report
REFERENCES
1. Draft Final, Remedial Investigation Report, United Nuclear Corporation Churchrock Site;
Prepared for EPA Region VI by CH2M Hill (under Contract 68-01-7251); August 1988.
2. Record of Decision, United Nuclear Corporation Ground-water Operable Unit, EPA Region VI;
September 30, 1988.
3. Public Comment Draft, United Nuclear Corporation Churchrock Site Operable Unit, Feasibility
Study, Gallup, New Mexico; EPA Region VI; August 1988.
4. Ground-water Corrective Action, Churchrock Site; Prepared for UA/C Mining and Milling by
Canonie Environmental Annual Review; 1989.
I ’
1’
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United Nuclear Corporation
BIBLIOGRApHY
EPA Region V I. Public Comment Draft, Umted Nuclear Corporation Churchrock Site Operable
Unit, Feasibility Study, Gallup, New Mexico. August 1988.
EPA Region V I. Record of Decision, United Nuclear Corporation Ground-water Operable Unit.
September 30, 1988.
McCoy, Rich (EPA). Personal Communication with Maria Lea, SAIC. October 17, 1990.
Prepared for EPA Region VI by CH2M Hill (under Contract no. 68-01-7251). Draft Final, Remedial
Investigation Report, United Nuclear Corporation Chuxchrock Site. August 1988.
Prepared for UA/C Mining and Milling by Canonie Environmental Annual Review. Ground-water
Corrective Action, Churchrock Site. 1989.
14
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United Nuclear Corporation Mining Waste NPL Site Summary Report
Reference 1
Excerpts From Draft Final, Remedial Inv tigation Report,
United Nuclear Corporation Churchrock Site;
Prepared for EPA Region VI by CH2M Hill
(under Contract 68-01-7251); August 1988
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EXECUTIVE SUMMARY
The Churchrock uranium mill and tailings disposal site is
the subject of this Remedial Investigation (RI). The mill
and associated disposal site is owned by the United Nuclear
Corporation (UNC). The facility was in operation from 1977
to 1982. In 1983, it was placed under the interim National
Priorities List (NPL) . This RI is part of the Superfund
process to investigate sites placed on the NPL by the U.S.
Environmental Protection Agency (U.S. EPA). Since commence-
ment of the study, UNC has decided to permanently close the
facility due to a poor uranium market and has submitted a
reclarration plan to the Nuclear Regulatory Commission (NRC).
The objectives of the RI are to determine the nature and
extent of groundwater contamination in three aquifers at the
site. The ultimate goal of the RI is to collect sufficier.t
data in order to prepare a feasibility study to address the
contaminated groundwater. Data collected during this RI
form the principal data base for the RI. Previous UNC and
New Mexico Environmental Improvement Division (NMEID) inves-
tigations, and the closure plan have been used to refine EPA
collected data. The non-EPA data is used qualitatively
because it was not collected with the same QA/QC require-
ments.
SITE DESCRIPTION
The Churchrock site is located in northwestern New Mexico
about 15 miles northeast of Gallup, New Mexico. The site is
in Section 2, Township 16 North, Range 16 West, in McKinley
Ccunty, New Mexico (Figure ES-i). The Churchrock site is in
an isolated area. There are no people living within the
DF 6D/O46 ES-i
-------
site boundary. Adjacent land ownership includes the Navajo
Incian R€servation to the north and Bureau of Indian Affairs
trust land to the east and south. The closest public use
‘ ll is about 12,000 feet northeast of the site. Ten wells
are located in slightly more than a 3—mile radius of the
site. Fcur of these wells were operational and sampled.
The wells are used for livestock and domestic purposes. The
area is semiarid and receives between 10 to 11 .nches of
rain per year. The mean temperature is about 48°F.
SITE HISTORY
The uranium mill facility was licensed under a radioactive
materials license in May 1977. Milling operations began in
dune 1977. The mill, designed to process 4,000 tons of ore
per day, used the conventional acid leach, solvent extrac-
tion method to extract uranium. The waste product, tail-
ings, as pumped to the 100—acre tailings disposal area.
According to the license records, between 3.4 and 3.6 mil-
lion tcrs of tailings were disposed of at the site.
In May 1982, TJNC announced a temporary closure of the Church-
rock uranium mill to await better market conditjon . The
rrill did not reopen because market conditions did not improve.
During the early part of 1987, UNC submitted a reclamation
plan to the NRC for decommissioning the mill. UNC’s current
orisite activities at Churchrock are limited to the following:
o Compliance monitoring activities
o Seepage collection system operation at the
tailings impoundment
o Tailings dust control
o Decontamination and sale of selected mill
equipment
o Operation of an enhanced spray evaporation system
of water contained in Borrow Pit No. 2
DF% 6D/048 ES—3
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SITE PHYSICAL DATA
SURFACE WATER
Drainage frori the site iS through Pipeline Canyon. As a
result of discharge fror the UNC ar.d Kerr-McGee mines, this
stream contained year-round flow. Pipeline Canyon is no ’
an ephemeral drainage due to the cessation of mine dischar-
ges in February 1986.
During the RI fieldwork, the surface water gaging study
cated that there was about a 2 OO—gallon—per..mj loss
perennial flow along Pipeline Canyon over a distance of
than a mile through the study area. This loss was
attributed to evaporation and seepage.
GEOLOGY
The stratigraphy at the site is divided into two main coxnpe—
rier,ts: the surficial unconsolidated deposits (Cuaternary
alluvium) and the underlying consolidated bedrock units.
The Quaternary alluvium is the ma er aurficial unconsolida-
ted deposit at the site. This deposit consists of a mixture
of sand, silt, clay, and to a lesser amount, gravel. Tluck•
nesses are in excess of 120 feet with an average of 50 feet.
The deposit’s general stratigraphic sequence in places con-
sists of finer material at the top with coarser material at
the bottom.
The main bedrock
Gallup Sandstone
Tongue member of
Cretaceous age.
is up to SC feet
sandstone. Zone
aceous shale and
units of ccncern at the site are the Upper
(Zones 1, 2, and 3), and the Upper D-Cross
the Mancos Shale. All bedrock units are of
Zone 3 of the Upper Gallup Sandstone, which
thick, contains a medium— to coarse—grained
2 (10 to 20 feet thick) contains a carbon-
coal with thin sandstone lenses. Zone I is
of
less
DFW6D/048
ES-5
-------
sandstone similar to Zone 3, but son ewhat finer in cram
size with thicknesses of up to 90 feet. A carbonaceous,
uissile shale represents the Mancos at the site.
There are three principal structural zones at the site:
Pipeline Canyon lir,eaimment, Fort Wingate lirmeaznent, and Pine-
dale nionoclmne. These structural features inmpact the site
hydrogeology by affecting groundwater flow directions.
HyDpoczCLor.1
There are three aquifers of concern iaentified at the site:
c Alluvium
o Zone 3 of the Upper Gallup Sandstone
o Zone I of the Upper Gallup Sandstone
The alluvial aquifer received water fror losses through
Pipeline Canyon, recharge from precipitation. and seepage
from the tailings ponds. The overall flow direction is to
the southwest along the axis of Pipeline Canyon. The
results cf U.S. EPA pump tests indicate that the aquifer has
transn mssmvities and storage coefficients of up to 6,5 5 ga ]-
ions per day per foot and 0.09, respectiveLy. Groundwater
velocities in the alluvium along Pipeline Canyon are about
2 feet per day.
The Zone 3 aquifer receives water frozmm the vaimme sources as
the alluvial aquifer. Where Zone 3 is in contact with the
alluviwr , the alluvium also directly provides water to the
Zone 3 aquifer. The flow direction of the Zone 3 aquifer is
north and easterly. The results of the U.S. EPA pu p tests
indicate that the aquifer has average tranemissivitiss nd
storage coefficients of 1,032 gallons per day per foot and
0.02, respectively.
D!W6D/048 ES—6
-------
The Zone I aq i er receiVes water from sources similar to
the Zone 3 aquifer. In sox e areas, these three aquifers
have the sane piezometric surface and are assumed to be
hydraulically connected. The flow direction of the Zone 1
aquifer i.s north. The results of the pump tests from other
studies irtdxcat that the aquifer has transinissivities and
storage coefficients of about 150 gallons per day per foot
and 0.05, respectively.
Groundwater flow directions at the site are complex. The
area contains numerous fractures and faults which may affect
flow direction and velocity in the bedrock more than the dip
of the rocks. In portions of the Site, the Zone 2 shale
unit, may provide art effective barrier to communication
between the two sandstone aquifers. In places 1 all three
aquifers of concern are in hydraulic connection, indicating
they are not hydraulically isolated units. The Mancos
Shale, located beneath the Zone 1 sandstone, is considered a
barrier to further vertical migration into lower aquifers.
Figure £5—2 sumrrarizes the flow paths described abcve.
ALLUVIAL AQUIFER CONTAMINATION
The depiction of groundwater contamination in the alluvium,
Zone I, and Zone 3 aquifers is addressed in the RI by the
reporting of analytical values collected during the RI and
other investigations. The plumes identified in the RI tray
be the result of mine water, tailings or other sources. In
the feasibility study, EPA will address target areas for
groundwater cleanup. These target areas will look at exceed-
ances of Applicable or Relevant and Appropriate state and
federal public health and environmental Requirements (ARARs)
and pathways f;otr the tailings ponds to the target areas.
ARARs will also be developed in the feasibility study. The
PcI will serve as a data base for these assessments.
FW6 /048 ES-7
-------
The alluvial a .fer at the site has been impacted by mine
discharges and ilings seepage. Several distinct, high
total dissolve, solids (TDS) plumes have been found in the
site alluvium (Figure E53). The major alluvial plume
extends southwest of the southern cell a minimum of
1,000 feet downgradi.ent of the site. The limit of this
plume, which has T S values UP to 20,000 mg/L, has not been
determined. Another alluvial TDS plume extends about
800 feet north of the ponds. Another plume is found north
and upgradient of the tailings pond. The alluvial plumes
contain numerous contaminants above National Primary and
Secondary Drinking Water Standards. Concentrations of
nitrate (>300 mg/Li, sulfate (>8,000 mg/L), selenium
(0.4 mg/Li, manganese (20 mg/I.), and cadmium (0.125 mg/LI
have been found in the site alluvial groundwater.
Radionuclides in the groundwater of the alluvial aquifer are
primarily represented by gross alpha activity. Values above
the gross alpha primary drinking water standard were found
in the water from six of the alluvial wells. These waters
exhibited gross alpha activities ranging from 16 to
45 pCi/L. Water from one alluvial well had a gross beta
activity in excess of the 50 pCi/L standard. The radium—226
and -228 standard of 5 pCi/L was exceeded in the water from
two alluvial wells. Concentrations of thorium and uranium
isotopes in the alluvial groundwater indicate little
migration away from the ponds.
ZONE 3 CONTAMINATION
The Zone 3 aquifer has been severely impacted by contami-
nants that have leached from the northeast portion of the
north tailings cell (Figure ES—4). An elongate TDS plume
has migrated more than 2,000 feet from the disposal site.
This contaminant plume migrated at a historic rate of between
DFW6D/048 . ES—9
-------
337 and 450 feet per year from 1979 to 1985. TDS concentra-
tions near the source are above 15,000 mg/L with pH val s
below 3.0. High ammonia (100 mg/U, sulfate (8,000 mg/I.),
and nitrate (35 mg/I.) are the major ions that affect water
quality. Metal concentrations in the Zone 3 plume exceed
primary and secondary water quality standards; however,
these concentrations typically decrease with distance from
the source. Contaminants have migrated toward the tribal
lands east of the site. Table ES—i su narizes elevated sin-
gle observation contaminant levels in groundwater on tribal
lands. These data are a compendium of UNC, NMEID and EPA
sampling.
Radionuclide distribution in the Zone 3 aquifer indicates
that activity levels decrease with distance from the source.
Thoriuijn and uranium activities decrease from 41,000 and
7,000 pCi/L to less than 1 and 55 pCi/U, respectively, over
a distance of 800 feet. Radionucljdes have also been found
on tribal lands in water from Zone 3 wells, Table ES—i.
ZONE 1 CONTAMINATION
The extent of contamination in Zone 1 is not as extensive as
in Zone 3 (Figure ES—4). TDS plumes for the Zone 1 aquifer
indicate that contaminants are leaving the Bite from the
northeast section of the north ta .lings cell and migrating
to the northeast and east (Figure ES—5). Another plume is
migrating eastward from borrow pit No. 2 and has moved to
the tribal lands east of the site. Contaminant velocities,
as determined by TDS distribution, have been estimated at
100 feet per year during the 1979—1985 timeframe.
DPW6D/ 048 ES-12
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4
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UMIED SITE
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Section 1
INTRODUCTION
The remedial investigat on of the United Nuclear Corporation
(UNC) uranium mill facility in Churchrock, New Mexico, was
conducted from March 1984 to October 1987. This report pre-
sents the work performed, the data gathered and the conclu-
sions for the RI.
An RI is part of the Superfund process. This introductory
section defines the Superfund process, describes the Church-
rock s ite and the site’s background, provides an overview of
previous investigations at the site, presents the objectives
and goals of RI activities, and depicts the organjzatjo of
the remainder of the report.
SITE BACKGROUND
The UNC Churchrock site is located in northwestern New Mexico
about 15 miles northeast of Gallup, New Mexico, (Figure 1-1).
The site is in Section 2, Township 16 North, Range 16 West,
in McKinley County, New Mexico.
The Churchrock uranium mill facility (Figure 1—2) was licen-
sed under a radioactive materials license in May 1977. Mil-
ling operations began in June 1977. The mill, designed to
process 4,000 tons of ore per day used the conventional acid
leach, solvent extraction method to extract uranium. The
ore processed at the site primarily came from two of UNC’s
nearby mines: Northeast Churchrock and Old Churchrock. Ore
was also obtained from the nearby Kerr—McGee mine. The ave-
rage ore grade processed at the mill was approximately 0.12
percent uranium. The acid leach process produced a wet,
DFW6E/ 032 1—1
-------
acidic waste, cor inonly referred to as tailings. The wet
tailings were pu nped to the tailings disposal e i sa. n esti-
mated 3.4 to 3.6 million tons of tailings were disposed in
the ponds.
In July 1979, the dam on the south cell breached releasing
approximately 93 million gallons of tailings and pond water
to the Rio Puerco. The dam has since been repaired. The
resulting spill clean up was conducted according to criteria
imposed by state and federal agencies at that time. This
event led to closer examination of the site.
In October 1979, the the New Mexico Environmental Improve-
ment Division (NMEID) ordered UNC to implement a discharge
plan to control contaminated tailings seepage which was
deemed responsible for groundwater contamination. In 1981,
UNC implemented a groundwater pumping system that withdrew
groundwater for treatment and evaporation in a lined pond.
This of fsite migration of rad.icactivity and chemical consti-
tuents .nto the groundwater, in addition to surface water
and air emissions, prompted the inclusion of Churchiock onto
the National Priorities List of Superfund sites.
NMEID suggested that UNC investigate neutralization of the
tailings because the acid solutions with the tailings were
believed to be a mayor factor governing contaminant trans-
port. UNC began tailings neutralization with a onia in
late 1979. In early 1982, neutralization with lime was ini-
tiated. Tailings neutralization ceased later that year.
In May 1982, UNC announced that they were going to temporar-
ily close the Churchiock uranium mill because of depressed
uranium market conditions. The market did net recover and
UNC decided to permanently close the facility. During the
early part of 1987, UNC submitted a closure plan to the Nu
D7W6Z/C32 1—4
-------
lear Regulatory Comnussion (NRC) for deco issioning the
mill. UNC’s current onsite activities at Churchrock are
1irn .ted to the following:
o Compliance monitoring activities
o Seepage collection system operation at the
tailings impoundment
o Tailings dust control
o Decontamination and sale of selected mill
equipment
o Operation of an enhanced spray evaporation system
that sprays water from Borrow Pit No. 2 and wells
from the seepage collection system
SUPERPUND PROCESS
Under Section 104(a) of the Comprehensive Environmental
Response, Compensation and Liability Act of 1980 (42 U.S.C.
)9004(a), 1982), called CERCLA or Superfur*d and the Super-
fund Amendments and Reauthorization Act (SARA) of 1986, the
United States Environmental Protection Agency (U.S. EPA) is
authorized to respond to an actual or threatened release
into the environment of a hazardous substance or a release
or substantial threat of release of a pollutant or contami-
nant that may present an u ninent or substantial endanger-
ment to the public health or the environment.
U.S. EPA has developed the Superfund process to identify
potentially hazardous sites of concern; to evaluate the
extent of the release and threatened release of hazardous
substances, pollutants, or contaminants; and to develop and
implement measures to contain these hazards. This process
consists of the following five steps:
DFW6E/032 1—5
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With the exception of the breach of the south cell, embank-
ment in 1979, there are no direct surface water discharges
fror the tailings ponds to the stream in Pipeline Canyon
(U.S. EPA, 1985). Flow around the tailings ponds is diverted
by ditches and the embankments formed by the tailings ponds.
One major drainage east of the site in Sectjon 1 contains
several stock ponds and dams. These ponds currently contain
no water. In fact, the westermmost pond which has a 4 00-foot-
long embankment is breached from a failure during a storm
event.
CLIMATE
Meteorological data indicate that rainfall averages between
10 and 11 inches in the Gallup, New Mexico, area. The major
precipitation events occurs between July and August and Dec-
ember and February. Summer precipitation events are charac-
terized by local and sometimes violent afternoon and early
evening thunderstorms. Lake evaporation rates for the area
are about 50 inches per year. Based on the precipitation
and evaporation rates, the climate is classified as semiarid
(Raymondi and Conrad, 1983).
The mean annual temperature, according to the United States
Weather Bureau at Gallup, New Mexico, is 48.5°F. Daytime
highs usually are between 80° and 90°F in the summer and 40°
to 50°F in the winter. Winter lows below OF are not uncom-
mon in the Gallup area (Raymondi and Conrad, 1983).
DEMOGRApHY AND LAND USE
The Churchrock site is in an isolated area. There are no
people living within the site boundary. The closest down-
gradient public—use well (No. 15X—303) is about 2,700 meters
to the northeast (Figure 1—2). This well is owned by the
DFW6E/ 036 2—15
-------
Bureau of Indian Affairs (BIA) and is used for culinary
water and.water .flg stock. This well is completed in the
upper Galli.p Sandstone and is downgradient of the site. it
is not clear whether it intersects Zone 3 or both Zones I
and 3. Other closer wells are W C monitoring or industrial
use wells (Rogers and Associates, 1985).
There are 10 wells within a slightly more than 3 mile radius
of the site. Four of these wells are in use and have been
sampled. These wells are for livestock and domestic use.
The U.S. EPA Mitre Model rating lists well No. 15X—303 as
the closest well.
IJNC owns Section 2 which contains the mill and disposal faci-
lities (Figure 1—2). In addition, UNC owns Section 36,
northeast of the disposal site. This section contains many
of the pumpback wells and the Rerr-McGee mine offices. The
remaining land that surrounds the mill and disposal ponds
include Sections 1, 3, 11, and 35. These lands are held in
trust for the Navajo Tribe and administered by the E lk.
Land north of Sections 35 and 36 (Figure 1—2) is within the
exterior borders of the Navajo Indian Reservation, owned by
the Nava o Tribe, held in trust by the federal government,
and managed by the Elk.
With the exception of the mine and mill activity, the land
use is primarily grazing for sheep, cattle, and horses.
DFW6E/036 2—16
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4 observation wells or piezorneters (Figure 3-1 ). Water lev-
els were measured in the monitoring and observation wells.
TEST BORINGS
A total of 33 test borings were drilled at the Bite to
install 29 monitoring wells (Nos. EPA-i through EPA-28 and
EPA-22A) and 4 observation wells (Nos. EPA—iSA, EPA—15B,
EPA-15c, and EPA-15D. The drilling was Conducted from Novem-
ber 11, 1984 through February 12, 1985. These borings were
advanced by air and mud rotary techniques. The initial eight
borings were drilled using mud rotary techniques. Subsequent
drilling was performed by air rotary techniques which proved
to be quicker and less expensive.
A total of 5,312 feet of drilling was completed for the
installation of the monitoring and observation wells. The
borings ranged in depth from 62 to 263 feet deep with an
average depth of about 160 feet. Figure 3—1 depicts the
monitoring and observation well locations. Table 3—1 Bumina—
rizes depth, hole diameter, and other pertinent data regard-
ing the borings and wells. Boring logs are contained in
Appendix B.
Table 3—1 reflects the aquifer in which the well was screenea.
In two wells, over drill of the boring resulted in extension
of the sand pack below the screened interval. At well
No. EPA—06, the Screen and the sand pack extend into Zone 2,
but do not penetrate Zone 1. Because Zone 2 is an aquitara,
water levels and quality from well No. EPA-06 should reflect
Zone 3. Well No. 19 was screened in Zone 3, however, the
borehole was drilled through Zone 2 and 5 feet into Zone 1.
The annulus below the screen wa backfjljed with fine sand.
The anrtulus in the screened zone was backfjjled with coarse
sand and gravel. At this location, Zone 1 is not saturated
DFW6E/037 3—5
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Section 5
DISCUSSION OF RI FINDINGS
In Section 2 the regional setting and some of the pre—RI
studies were described. These data, additional data sources
from Section 4, and the RI field studies were combined to
understand the characteristics of the site. These site—
specific characteristics are described in this section and
are divided into four main subsections: source characteri-
zation, surface water, geology, and hydrology.
SOURCE CRARACTERI ZATION
Source sampling of tailings solids or liquids was not con-
ducted by EPA during the RI. Analytical results of tailings
liquids presented in this section represent analyses from
previous investigations. UNC has prov .ded EPA with tailings
liquid analyses based on samples from well Nos. 633 and 635
in 1987. The UNC data exhibit high nitrate values, but the
predominant nitrogen species is an onia. These data are
portrayed in Table 5—1. Also, in this table is an example
of a one—time tailings liquid sample from well No. 633.
This well, completed in the south cell, and the UNC data may
be used to characterize the resident tailings fluids.
From these analyses, the tailings fluids are characterized
as an acidic, high dissolved solids water with sulfate,
ammonia and sodium as principle ions. Metal analyses par-
ticularly aluminum and iron are very high (over 1,000 mg/L).
Radioactivity as represented by Th—230 is also very high
(10,000 to 50,000 pCi/L). NRC sampled tailings liquor in
April 1987 in order to idetnify hazardous constituents pre-
sent in the ponds. Table 5—1 depicts these data. Analyti-
cal results are consistent with UNC and other available data.
r
DFW6N/O ll 5—1
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Ta 1e 5 —1
PRCBA LE TAILINGS LIQUXO CNEMISTRY
Well NP C
u c No. 633(2) Sa 1e
Para eter Units Su nary 2/26/86 Apr .1 19E7
p .i S.U. 1 — 3 1.71 3.34
TD S n g/L 38,462 — 61,932 46,793 56,860
A luii r ur. zig/L 1,167 — 2,906 2,860 2.100
Manganese g/L 100 100 210
ng/L 1,450 — 5,500 438 5,860
N .trate mg/ I. 75.5 — 282 1.84 (SC
Th—230 pC ./L 1,064 — 277,733 — 13
Conduct v ty um2 os/c ’ — 17,718 -
Ca1 i . mg/I. 240 460
Magnes .uTh mg/I. 287 1,100
Sod .u mg/L 526 890
Potass Ifl mg/L 4 -
Bi.ca:benate mg/I - 0 (1
Ch1or .de mg/L 253 580
Si 1fate etg/L 24,813 43,581 28,209 41,000
Arse n .c mg/I. 0.024 0.208 0.65 (0.60
Se leni .um mg/L 0.001 0.161 0.29 <1.2
Iron mg/I. 4,350 2,7CC
Lead mg/L 0.6 3.34
Caa um mg/I. 0.013 0.24
mgJL — 10 20
Mo1ybr um mg/L. <0.05 — 0.15 — <0.24
Ra—226 pC ./L 13 — 24
Ra—22 6 pC ./L. 2.6 —
Range for 3 samples collected and analyzed by UNC.
( 3 )onet .me samp1 .ng event. Analytical data is also presented in Append .x 0.
Total Radon (226 + 228)
Dr.6E/C48
-------
No source sampling of the tailings solids was conducted by
U.S. EPA. U.S. EPA has contacted UNC to deternu.ne if
leachate tests of tailings solids analyses have been per-
formed.
NNEID data suggest ammonia concentrations as high as
4,000 xng/L; nitrate as high as 17 rng/L; and arsenic as high
as 1.87 mg/L. These supplemental data indicate that the
tailings liquor chemistry may have been variable throughout
its discharge history.
SURFACE WATER
The original goal of the surface water studies was to deter-
mine the amount of infiltration that was Occurring along
Pipeline Canyon at the tailings disposal area. This data
was to be used to understand the recharge characteristics of
the aquifers of concern at the Churchrock site. Following
collection of the RI field work, the mine discharges to Pipe-
line Canyon ceased. The stream reverted to its premining
ephemeral condition and the amount of recharge available to
the aquifer decreased significantly.
In order to factor out the water added to the surface water
system by the Kerr—McGee discharge, the outflow was subtrac-
ted at each location from the Kerr—McGee discharge to calcu-
late net loss or gain. These data are presented in Table 5-2.
Values that are negative, theoretically indicate loss of
water through evaporat on or seepage into the alluvial or
bedrock Systems.
The data in Table 5-2 also indicates that other sources,
such as runoff, have contributed partially to flow-in
Pipeline Canyon. For example, flow typically increased at
the first measuring point downstream of the mine discharge.
DFW6H/Qji 5—3
-------
Table 5-2
NET LOSS 0 GAIN OF £LO AT SU F) ! WAT SMPLE POINTS
LOCATIONS
A B C/c’ E 110 ’ H I 3
Y a 4, 1995 0 — 99 352 * — —
Nay 5, 1985 0 — — — —63 —160 —358 —394
May 10, 1985 0 — 203 529 197 13 —31 —4E8
Ne.y 11, 1965 0 —135 — —
Jure 8, 1985 0 — —414 — —369
Ju ,e 17, 1985 0 632 —253 -507 —289 —161 —112 -201
19. 1985 0 729 649 1751 212 115 —113 —342
N IE: All flow va1 es are th çalloris per sthute.
Loc.etioos
A ‘ Ke rr— McGee outflow
B Sa p1e Po t below Kerr-McGee 4Lsc azse
c a Culvert No. 1 Inflow
O • Culvert Ko. I Outflow
£ e Culvert 14o. 2 lnflev
a Culvert No. 3 Inflow
a Culvert No. 3 Outflow
H • Strear Profile I
I $ Strea Proflle 2
.7 Streaa ProfiLe 3
* Reflects average of isfiow a d outflow.
DFW6E/042—2
-------
This location had an average increase of 409 gpm, which 2!
attributable to upgradient runoff. AU. flow measurements
downstrean of culvert No. 3 indicated that there was a loss
through evaporation or seepage into the ajluvi and rock
systems. The average of the last three sample points (H, I,
and J) indicate an average loss of 193 gpm. These results
compare favorably with calculations made by Raymondi arid
Conrad (1983) using LJNC data. In their study of the flow in
Pipeline Canyon, they reported an average loss of 250 gpm
along the stream from a point ust upstream of the tailings
ponds to one downstream of the LINC property.
Pipeline Canyon has had a perennial flow since 1968 as a
result of mine dewatering from the Kerr—McGee and UNC mines
(Raymoridi and Conrad, 1983). Prior to the dewatering, the
stream was an ephemeral drainage. Following cessation of
dewatering by UNC in 1983 and Kerr-McGee in 1986, the stream
has made a return to its natural state. Field Visits in
August 1987 (1 year following the termination of Kerr-McGee’s
discharge), revealed that there was no flow in the stream.
This, of course, has resulted in a decrease in the volume of
water that can infiltrate into the groundwater system.
Although not a part of the RI, determination of the flow
volume through the canyon may be required in assessing reme-
dial actions in an FS. Canonje (1987b) used the probable
maximum flood (PM?) as the basis to calculate flow in the
channel for the UNC reclamation plan. Through the use of
the Soil Conservation Service Synthetic Triangular Unit
Hydrograph method, the peak flow rate was calculated as
25,000 cfs. For reference, the maximum flow measured along
Pipeline Canyon during the field investigation was 7.4 cfs
or 0.03 percent of the P 141.
DFW6H/ol1 5—5
-------
The surface water samples collected along Pipeline Canyon
represent water quality that is available for recharge to
the aquiferi. The quality of the water is governed by the
quality of the mine discharges, natural precipitation, and
upgradient surface water.
Because these surface waters will dissolve constituents as
they pass through the alluvium and bedrock, the surface
water quality does not necessarily indicate background water
quality of the aquifers. Tables D-5 and D—6 in Appendix D
depict the water quality of these samples.
The surface water samples are characterized by TDS concen-
trations of approximately 500 mg/L. As was the ease with
groundwater, the manor anions are bicarbonate and sulfate
and the predominant cations are calcium and magnesium. The
waters were near neutral to slightly alkaline (pH of 7.6 to
8.6). Metal concentrations were low which may be a function
of the pH. Average metal concentrations of the four surface
water samples collected by U.S. EPA were:
Aluminum 0.73 mg/L Nickel 0.06 mg/L
Barium 0.48 mgIL Vanadium 0.05 mg/L
Iron 0.19 mg/L Zinc 0.04 mg/L
Manganese 0.03 mg/L
Antimony, arsenic, beryllium, cadmium, chromium, cobalt,
copper, lead, mercury, molybdenum, selenium, silver, thal-
lium, and tin were not detected in the surface water samples
collected during the Phase I field investigation. Detection
limits were according to CLP requirements.
Radiological analyses performed on two surface water samples
do indicate the presence of radioriuclides. Their presence
is largely a function of the source rock in the mines.
DFW6 H/O ll 5—6
-------
Radlonuclides with the exception of radium decreased in con-
centratior from Culvert No. 1 downstream to stream profile
No. 1. The distribution between the two sampling points
were:
Stream
Culvert No.1 Profile No. 1
Rad iurn—226 0.94 pCi/L 7.99 pCi/L
Thorium-23 0 0.402 pCi/L 0.297 pCi/L
Uranium_238 432 pCi/L 71 pCi/L
Gross Alpha 207 pCi/L 90 pCi/L
Gross Beta 98 pCi/ I . 75 pCi/ I .,
*unccrrected for U-238 and Radon
The decrease, with the exception of radiwn, downstream may
be a function of dilution or attenuation and precipitation
along the stream bed.
GEOLOGY
As described in Section 3, a total of 33 borings were dril-
led in the RI for the purpose of .nstalling 29 monitoring
wells and 4 observation wells. More than 300 wells and bor-
ings had been installed at the UNC property prior to this
investigation. Many of the wells were completed across sev-
eral geologic and hydrogeologic horizons. One of the objec-
tives of the RI was to compliment the studies in areas to
the northeast of the facility where contaminant migration
was occurring in the Upper Gallup Sandstone (Zones 1 and 3).
Because of this, many of the borings exceeded 200 feet in
depth and considerable time was required. This resulted in
a drilling program that concentrated more on the logging of
drill cutting samples every 5 feet rather than continuous
coring of the bedrock. As a result, many of the logs cannot
provide detailed stratigraphic information on such items as
rock characteristics, fractures, and structures.
C DFW6Jq/O j 5—7
-------
Zone 1 has very similar recharge relations as Zone 3. In
areas where Zones 1, 3, and/or the alluvium have the same
piezometriC ..surface (Figures 5-2 through 5—3), the units are
assumed to be hydraulically connected. Review of the cross-
sections in Figures 5—3 and 5—5, indicate that faulting and
fracturing has placed the Zone 1 aquifer in position with
Zone 3. In these areas, the Zone 1 aquifer will receive
additional recharge from Zone 3.
WATER LEVELS AND FLOW DIRECTIONS
Comprehensive groundwater levels were measured by Canonie
(1987a) for May 1986. These measurements depict groundwater
levels within 3 months after cessation of Kerr-McGee’S mine
discharge to Pipeline Canyon. In order to determine water
level responses following the end of mine water discharges
to Pipeline Canyon, piezometriC maps were constructed for
August 1987. These maps (Figures 5—8, 5—9, and 5—10) show
changes that have occurred in about a year following mine
discharges. The maps were developed from the August 1987
water level measurements and supplemented by UNC quarterly
monitoring reports and trends observed by Canonie data. The
predominant flow directions and changes in piezometric sur-
faces are described below for each of the aquifers of con-
cern.
As a precurser to the discussion of groundwater level mea-
surements, it is necessary to briefly discuss the pumping
system at the site. At the time water level measurements
were taken in August 1987, a total of 27 wells were actively
pumping water from the groundwater systems for neutraliza-
tiori and return to borrow pit No. 2. The average pumping
rate was 30 gpzn or 43,200 gallons per day. Table 5-3 lists
the pumping wells at the site. The effects of the pumping
DFW6H/O11 5—24
-------
The following sections address the contau.nant plume distri-
bution for the aquifers of concern at the site.
Zone 3
Figure 5-15 presents the TDS isoconceritration map for the
Zone 3 sandstone. Review of this map indicates a lobate
plume with widths (as delineated by TDS concentration) of
1,100 to 1,400 feet and a length in excess of 3,500 feet.
The plume originates, as indicated by maximum TDS values, in
the northeastern quadrant of the north cell of the tailings
disposal area. In the area of maximum contamination (TDS
values greater than 10,000 rngiL), specific wells had the
following TDS concentrations: No. 613 (15,460 mgIL),
No. 610 (11,140 mgIL), No. EPA—06 (11,453 mg/L), and
No. TWQ—1OD (15,186 mg/L).
Comparison of plume geometry and trend with the groundwater
flow directions in August 19S7 (Figure 5—9) reveals two
important observations. The general trend of the plume is
towards the northeast and is identical •to the direction of
decreasing piezometric surfaces. Additionally, the thin,
elongated zone of TDS concentrations between 6,000 and
1(. ,000 mg/L occurs in the same area where the piezometric
surface has slight fluctuations in the vicinity of well
Nos. EPA—2 and EPA-3. In this area, the piezometric sur-
faces are lower than would be expected. This may represent
increased transrnissivity due to fractures or rock lithology.
Analysis of the core log reveals that the core recovery was
poor and the rock was poorly cemented and friable. These
attributes suggest a high transmissivity.
Two wells in the highest concentration of the plume were
sampled during the RI field work. These wells include Nos.
fr”
DFW6H/011 5—46
-------
610 and EPA—6. Review of the previous water quality tables
in Appendix D confirms that these two wells usually con-
tained the highest concentrations of most parameters. Typi-
cal water quality for this zone of the plume is:
Ammonia >100 xng/L
2 to 4
Sulfate >8,000 mg/L
Nitrate 6 to 35 mg/L
Analysis of changes in parameter concentrations with
distance can be made by comparing the above values with the
analytical results from wells further downgradient in the
plume. For example, well Nos. EPA—b and EPA—12 are
approximately 2,500 to 3,000 feet downgradient of the source
cc groundwater contamination. Ammonia and nitrate levels in
these wells have historically been below 1. mglL, indicating
that through oxidation, dilution, or other form of
attenuation, the concentrations have decreased.
For these downgradient wfrlls, pB has increased relative to
the center of the plume, but still remains slightly acidic
(6 to 6.5). More conservative and readily solubilized spe-
cies such as sulfate and chloride are lower.
In order to estimate a plume migration rate, the midpoint
for the 4.000 to 6,000 mg/L zone of the plume was selected
to represent the extent as of 1985. This point was chosen
to be the vicinity of well No. EPA—12 which is approximately
2,700 feet from the northeast edge of the tailings pond
where tailings rest directly on top of the Zone 3 aquifer.
Assuming the migration started at the time of tailings dis-
posal (1977) a minimum TDS plume migration rate of about
337 feet per year was obtained. It is likely that migration
probably did not start until 1979 when saturation of the
DFW6H/01l 5—48
-------
tailings and bedrock occurred. It was also at this time
when NMEID first noticed discharges and ordered a seepage
control plan-for the site. Using the 1979 to 1985 time-
fran e, the migration rate of the plume would be 450 feet per
year. Therefore, based on analytical results, Zone 3 plume
rtugration rates are between 337 and 450 feet per year.
When calculating the migration rates for chemical compounds
at this site, several important factors must be considered.
First of all, the rates are “average” rates and do not
reflect current migration rates. Movement was calculated on
the basis of distance travelled versus the time the sample
was collected following tailings disposal. Actual migratior
rates may have been initially faster and slowed at later
times, or vice versa. Also of importance is the influence
of the pump back wells. These wells were installed after
disposal and before the 1985 sampling. This is of impor-
tance because the wells have influenced movement as verified
by their cones of depress .On in the piezometric surface
maps.
The calculated average migration rates cannot be effectively
applied to post-1985 predictions because of the pumping
wells. These rates would overestimate the future extent of
the plume.
Zone I
Figure 5-16 is the T S isoconcentratiOn diagram for the
Zone 1 sandstone. Review of this figure indicates two sepa-
rate broad plumes of groundwater contamination. The south-
ern plume emanates from the eastern edge of the central cell
and borrow pit No. 2. The shape of this plume suggests a
radial flow from the source. The second plume is another
4
l}
FW6H/0l1 5—49
-------
associated with 3err—McGee is the probable source of th. s
anomally... Information requested from Kerr—McGee should
provide further insight into the nature of this second
source.
The contar ination of the southwest alluvium by nitrate is
attributed primarily to leaching from the tailings pond.
The distribution of high nitrate values is analagous with
the TDS plume which is shown to emanate from th. southern
disposal cell. The argument by Billings that high nitrate
in the alluvium comes from natural salts conflicts with the
low nitrate levels found in well Nos. EPA—22A and 21.
These wells are upgradient of the central, south, and most
of the north tailings cell and are therefore not impacted by
nitrate.
METALS
Review of metal analyses included sampling events durir g the
RI and historical data as presented by NMED (Appendix G).
Table 5-4 lists the maximum metal concentrations for wells
sampled by U.S. EPA during the remedial investigation. This
table also contains standards which could be used as poten-
tial applicable or relevant and appropriate requirements
(APAR’S).
Froii this table, the following parameters were determined to
be above the standard.
Arsenic Manganese
Beryllium Selenium
Cadmium Zinc
Chromium Molybdenum
iron
FW6N/Cll 5—60
-------
With the exception of iron and manganese, the above metals
and their distribution will, be discussed in the following
subsection. Iron is a secondary drinking water star4dard.
Iron migration rate would be slower than manganese (another
secondary drinking water standard); therefore, discussion of
manganese chatacteristics should conservatively represent
iron. Zinc was only slightly above secondary drinking water
standard. In addition, historic data (Appendix G) for zinc
is limited.
Arsenic
The primary drinking water standard for arsenic is 0.05 mgIL.
Arsenic is mobile in the aqueous system at moderately acidic
pM values. However, as pM increases and sediments, clay, or
argillaceous material, are available, precipitation and/or
oxidation with subsequent adsorption will occur. Arsenates
have fairly high mobility and are not attenuated easily.
One of the major controls on arsenate mobility is the pre-
sence of iron hydroxides. As evidenced by high iron concen-
trations in groundwater, the abundance of iron hydroxides
may adsorb much arsenic. Near the tailings ponds arsenic
concentrations are in the order to 0.1 to 0.6 mg/L. Wells
in this imnediate vicinity (Figure 5—18) which represent the
range include:
Concentration
Well ) c. ( mg/L )
335 0.42
TWQ— 1 1D 0.52
TWQ—360 0.06
320 0.2
TWQ—156 0.5
610 0.6
611 0.1
DFW6H/011 5-62
-------
Review of the data indicates that alluvial wells rarely have
concentrations abcjve 0.05 mg/I.. This may be due to adsorp-
tior. on the clay minerals and iron hydroxides.
Distribution of arsenic in bedrock wells, both Zone 3 and
Zone 1, indicates that transport of arsenic is evident (Fig-
ure 5—18). Arsenic has been detected up to 1 mg/I. in the
following wells:
Concentration
Well No. mg/L
5018 1.91
EPA— 13 1.06
EPA-lO 2.5
EPA—i 1.6
EPA-3 1.8
Low arsenic concentrations are present in the tailing area
because at low pM the arsenate adsorption on iron exyhydr-
oxide is at its highest level. This creates a arsenic Nreser_
voir” of adsorbed arsenic. As the pH increases, scme of the
arsenic is released and is mobile. As the Eh (oxidation—
reduction) decreases, most of the arsenic previously adsorbed
goes into solution and can be transported. The current dis-
tribution as a combination of pH-1h and groundwater flow.
Other wells which have been found to have historical arsenic
values above the .05 mg/L drinking water standard. These
include well Woe. EPA-5, EPA—6, EPA—il, EPA—16, EPA—lB. and
436.
Se 1 en ium
The primary drinking water standard for selenium ii 0.01 mg/L.
Seleniwr. usually has a low mobility in groundwater systems.
DFW6h/011 5—63
-------
scope of the RI, but may relate in part to the previously
mentioned proto ore pile and associated ponds.
Molybdenum
No molybdenum standards have been developed for active ura-
nium processing sites. however, a proposed standard of
0.1 mg/L was proposed in September 1987, for groundwater at
inactive sites (40 dR 192.02). This value was used to dis-
cuss potential contamination at the Cburchrock site. UNC
has analyzed the or for molybedenwr and found concentra-
tions of less than 1 to 70 mg/kg. Leachate characterization
of the tailings for molybdenum is not avail b1e. Table 5—1
contains data supplied by UNC from wells in the ponds that
report values up to 0.15 mgIL.
In groundwater, molybdenum travels as an anion ($004) and is
not as easily attenuated as selenium or arsenic. Instead it
travels as a conservative species in solution, much like the
chloride ion.
Values along the tailings embankment and the pump back wells
northeast at the north cell indicate molybdenum values of
0.2 to 0.7 mg/L. However, wells further downgradient have
much higher molybdenum values. Maximum values of molybdenum
in selected Zone I and 3 wells downgradient (Figure 5—18) of
the site Include:
Concentration
‘ e1l No. ( mg/L )
EPA—i 42
EPA—li 59
EPA—13 5.6
411 2.4
401 5.9
430 1.6
DFW6H/0ll 5—65
-------
Thc occurrence of higher molybdenum values in distant down-
grad .ent wells than in wells close to the site cannot be
explained with the current data. One explanation may be the
presence of another (presently not identifiable) natural or
man—made source. Slug flow from the tailings pond may also
be an explanation for the molybdenum distribution. This
latter explanation refers to the introduction of a single
discrete impulse of contamination into the groundwater sys-
tem. This contamination could move as a single discrete
body downgrad2ent. Current data is not sufficient to refute
or prove either of potential, explanations.
Manganese
The secondary drinkir.g water standard for manganese is
0.05 mg/L. This stanoard was developed mostly for aesthetic
(taste and discoloration) properties. Manganese has a high
mobility because when it becomes solubiliaed it typically
remains in solution until the pH reaches 8.0 and above. It
is typically at the outer edge of contaminant plumes. Man-
ganese is present in the tailings as exhibited by the con-
centration of 100 mg/i. in well No. 633.
Review of manganese historical data in Appendix F reveals
that more than 50 alluvial, Zone 1 and 3 wells have manga-
nese concentrations above the secondary drinking water stan-
dard. Values of manganese have been found up to 15 mg/i. in
Zone 1 wel.& No. EPA-7, and 55 mg/i. in Zone 3 well No. EPA—6
east of the site (Figure 5—18). All of the U.S. EPA Zone 1
and 3 wells northeast of the site exceeded the standard.
Alluvial wells throughout the study areas exhibited manga-
nese concentrations above the standard. Th. southwest allu-
vial wells had concentrations up to 19.8 mg/i. at well
o. 630. The northern alluvial wells have historical manga—
nese concentrations of 0.1 to 1 mg/i..
DFW6H/Oi.l 5—66
-------
In general, manganese concentrations in alluvium were lower
than in bedrock. This is probably due to the generally more
alkaline pN and higher adsorptive qualities of the alluvium.
Beryllium
Beryllium has a very low aqueous solubility and is quickly
piecipitated or adsorbed onto solids after entering the
aqueous environment (U.S. EPA, 1979). In near neutral pa
waters, beryllium will precipitate as 3e(OX) 2 . Beryllium
concentrations in fresh surface water are typically less
than 1 ppb.
Review of the data base in Appendix G indicates that beryl-
lium was not a routine analytical parameter. Data from
U.S. EPA sampling represents the majority of beryllium samp-
1ing at the site. No data on beryllium concentrations in
the tailings are available.
Based on U.S. EPA sampling results, beryllium was found in
several monitoring wells. These wells and their respective
concentrations include:
Concentration
Well No .
EPA—3 0.089
610 0.126
611 0.022
EPA—6 0.254
The data suggest that beryllium is present in or has been
mobilized by the acidic tailings. It has only b.en found in
wells w ith acidic pH values. No detectable beryllium was
four d in alluvial wells. Well No. 611 is the only Zone 1
DFW6h/Ol,1 5-67
-------
well which contains detectable beryllium. Therefore, it can
be concluded that beryllium has not migrated more than
600 feet in the Zone 1 aquifer. Beryllium in Zone 3 is
found farther from the tailings pond as evidenced by its
presence at well Nos. EPA-3 (1,200 feet), EPA—6 (900 feet),
and 610 (750 feet). In summary, beryllium has been found
offsite two wells, at concentrations above the io6 cancer
ribk water quality criteria standard.
Cadmiutr
Unlike beryllium, cadmium has been analyzed in the tailings
liquids. Well No. 633 exhibited a concentration of
0.013 rng/L. The results of the U.S. EPA sampling is the
main data base for cadmium distribution.
In comparison with most heavy meta1 , cadmium like manganese
is relatively mobile. Sorption onto sediments and manga-
nese oxide occurs as the pH increases. Adsorption onto
organic materials (coal), minerals, coprecipitation with
metal oxides and substitution in carbonates also control
cadmium mobility (U.S. EPA, 1979). In carbonate ground-
water, cadniiu solubility would be about 0.1 mg . at a pH of
7 and 100 mg/L at a pH of 5.
In the U.S. EPA sampling, cadmium was found above the prl.-
mary drinking water standard of 0.01 mgIL in the following
wells (Figure 5—18):
Concentration
Well No. ( mg/L )
EPA-3 0.013
EPA—4 0.143
EPA—S 0.113
DFK’6H/0l1 5—68
-------
EPA—6 0.277
EPA-7 0.033
EPA—li 0.088
EPA—13 0.021
EPA—14 0.045
EPA—20 0.038
EPA—23 0.05
EPA—24 0.099
EPA—25 0.125
625 0.018
The concentrations in well Nos. 610 and 611 which are close
to the ponds ano have low pH values do not exhibit cadmium
concer.trations above the 0.005 mg/L detection limit. The
sporatic distribution in Figure 5—18 and downgradient con-
centrations above the source concentrations suggests that
the cadmium may be inherent to natural geologic media or the
distribution may be reflective of slug flow which is discus-
sed at the end of the wmetaln subsection of this report.
Historical sampling by NI’ EID indicates a different cadmium
distribution. MNEID (1987) has indicated that cadmium is
rarely found Noffsite (away from the tailings pond). Rather,
when found, cadmium has been only in groundwater with acidic
concentrations, close to the tailings ponds. Away from the
ponds, cadmium reportedly is absorbed on clays or precipi-
tated as a carbonate or with iron oxides and hydroxides.
Chromium
Chromium is found in trivalent and hexavalent forms in aque-
ous systems. However, chromium analyses it. the U.S. EPA
sampling were reported as total chromium. The trivalent
form readily torms an insoluble hydroxide precipitate in
neutral waters. However, )iexava lent chromium is not easily
DFW6H/0l1 5—69
e )
-------
sorbed on clays or hydrous metal oxides. At neutral pN,
hexavalent chron ium will typically be present in greater
concentrations than the trivalent form. The ma or atten at-
ing mechanism for hexavalent chromium is sorption onto car-
bon (U.S. EPA, 1979).
The historical data base for chromium is mostly from the
U.S. EPA sampling events. For these samples, the niaximun
chromium concentrations that were greater than the primary
drinking water standard of 0.01 mg/L include:
Concentration
Well No. ( mg/LI
504B 0.03
610 0.268
611 0.014
EPA—6 0.135
EPA-27 0.029
From these data and the chromium distributions shown in Fig-
ure 5-18, chromium is not considered a significant ofisite
contaminant. Chromium appears to be limited to the area of
the northeast pw!tpback system and quickly decreases down—
gradient from this area.
ORGANIC COIIPOtJNOS
Organic analyses were performed on three ground ater samples
from the following well Nos.: 610, 611, and 625. These
samples were collected during the May 1985 sampling. The
results of the analyses are contained in Appendix D—4.
Five volatile compounds were found in the three wells. The
compounds and range of concentration were: methyl .sne
F 6H/O1l 5—70
-------
RADIONUCLIDES
Samples analyzed for radiological constituents are presented
in Tables D-6, D-7 and D—8 in Appendix D. The analytes
included Radiwn—226, Eadiuzt—228, Thorium—230, Uranium-238,
Gross Alpha, and Gross Beta.
Comparison between U.S. EPA and historical data is not pos-
sib].e for the radionuclides. Historical radiological analy-
ses were typically icr uraniuit concentration as expressed in
n 1 y/L. In contrast, U.S. EPA data was measured as activity
and expressed in pCi/L. If all uranium isotopes were
analyzed, it would be possible to get a rough estimate of
uranium concentration from the activity values. However,
only U-238 was analyzed. Therefore, no conversions of
activity to mass were made. Discussion of radionuclides are
based on U.S. EPA data.
Gross alpha discussions represent gross alpha data with
U—238 subtracted out. EPA guidelines for gross alpha
reguire subtraction of U—238 arid radon activity. Radon was
not analyzed by the CLP, therefore, it could not be sub-
tracted. -
Radiur i-226 and Radium—228
The Clean Water Act. (CWA) has a standard which governs the
concentration of radium in water. This standard combines
the concentrations of Ra-226 and Ra—228. The combined
guideline under the CWA is 5 pCi/L. Table 5—5 depicts which
saiTples exceeded this standard. A total of 13 wells with
18 observations over 5 pCi/L were recorded (Figure 5-19).
Concentrations of radiurn—226 (Ra-226) in the March 1985
sampling event ranged from 0.009 pCi/L in well No. EPA—25 to
a high of 117 pCiIL in well No. EPA—lB (an alluvial well
DFW6H/0ll 5—72
-------
Table 5-5
GPfl y.Fp ANALYSE$ WITh ELJVATTh RADIOACIIVITY VALUES
Radium Th-23 0 0-738 Gross Alpha Gross Beta
Well No. Aquifer Oate pCi/L t > 1 pCI/L. t ? j pCi/L ? !ijCiIt. pCi/L %
Zone 3 3/as — — — 20.2 12 60 44 —
EPA-S Zone I 3/0 5 - — - — 15.6 17 70.2 81 — -
EPA-S Zone I 5/85 - — - — — — 21.7 79 — —
EPA—6 Zone 3 3/85 5.4 10 2.05 35 719 II 151 77 308 20
EPA-9 Zone 3 3/hIS 7.4 35 - — — — — — — —
EPA-b Zone 3 3/85 — — - — 30 16 46.1 39 - —
EPA-JO Zone 3 5/ 1 1% 15.4 97 - — 53.9 17 69.1 36 -
EPA-li Zone 3 3/85 - — — — 68.8 12 150.7 23 - —
EPA-Il Zone 3 5/8% 18.0 71 - — 82.9 17 175.1 19 - —
EPA-13 Zone 3 3/05 21.0 19 — — — — — — -
EP?i— 13 Zone 3 5/0% 9.3 2 37.8 60 — —
EPA—IS Zone 3 3/85 — — 55 13 111.8 20 - —
CPA—IS Zone 3 5/ 9 5 7.5 61 50.6 II 15.4 31 — —
EPA-be Zone 3 3/OS 13 5 71 13 109 24 — —
r.PA—19 Zone 3 3/05 23.3 23 — — 26.5 60 — —
EPA-20 Alluvial 3/85 17.3 70 — - — —
EPA— f l AI)u. ia l 5/85 — — 18.1 35 — —
CPA-22 Zone I 3/es 18.7 17 45 40 — —
EPA—23 Alluvial 5/85 15.9 17 31.3 49 — —
EPA-75 AlluvIal 3/85 — — — — 64.1 63
EPA—27 AlluvIal 3/8% — — — — 17.7 12 17.4 94 — —
EPA-2 8 Alluvia) 3/OS — — — — — — 15.7 86 — —
EPA-28 Alluvia) 3/85 19 15 — — — — 17.7 81 — —
610 Zone 3 3/85 17.6 28 11,340 5 7,612 11 —3,061 S 03.6 10
610 Zone 3 5/85 23.4 21 4,243 6 737 13 — — 504 9
6)1 Zone 1 3/0 5 — — 70.8 12 134 12 116.8 19 113 24
611 Zone) 5/ 05 — — 19.0 14 110 12 118.5 17 100 22
— 625 AlluvIal 3/8% 7.05 15 — — 70 IS — — — -
Value reflects sithiraction of 0-238, however, radon was not analyteil.
-------
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FIGUR( 5-19
RADIONUCLIDE DISTRIBUTION
IMTED NUCLEAR S11t
CHI O1ROCK, N(W MEXICO
-------
southwest of the site). The values for well No. EpA- 18 were
anomalously high and Probably reflect a poor analysis. A
duplicate sample at well No. EPA—l8 revealed an Ra—226 value
c ± 13 pCi/L. This latter value appears reasonable in con-
sideration of the concentration in Veils in this area: wel l.
No. .PA—13 (Ra—226 of 11.4 pCi/L) and well No. EPA—S (Ra—226
of 8 pCi/L). Excluding the anomalously high value at well
No. EPA-l8, the next highest observation was at well
No. 610. This well located in Zone 3 northeast of the north
cell had Ra—226 concentrations of 47.6 pCi/L in March 1985.
Reanalyses in May 1985 revealed similar findings. The two
highest values at the Site were well Nos. 610 (25 pCi/L) and
EPA—13 (9.5 pC2./L).
Ra—228 concentrations exhibited &ini.jj.ar trends to Ra—226.
Elevated concentrations of Ra—228 were found in the Zone 1
and 3 well Nos. (EPA—6, EPA—19, EPA—l3, and EPA—iS) east and
northeast of the north cell.
Trends of radiun. -226 and -228 in groundwater may be deter-
mined from Figure 5—19. For Zone 3, the maximum combined
radium activity occurs at well No. 610. Here activities as
high as 47.6 pCi/L have been measured. This activity decrea-
ses rapidly away from this point. For example, all the down—
grathent wells are less than 25 pCi/L and many are below to
CWA standard. This significant reduction occurs in dis-
tances of several hundred feet in some wells.
In Zone 1, no radium activities exceeded the CWA standard.
It is concluded that radiu m 1 activity is not migrating in
this unit. Only two alluvial wells exceeded the radium stan-
dard. These included well Nos. EPA—28 (19 pCi/L) and 625
(7.05) pCi/L. The occurrence of the anomalously high value
at well No. 625 cannot be currently explained.
\
DFW6}j/011 5—75
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Therjwfl -230
Thorjwn—230 (Th—230) is a radionuclide that was found in the
groundwater in concentrations ranging from less than 1 pCi/ I.
to a maximwrt of 41,340 pCi/L in well No. 610. Very few
w 1ls exhibited concentrations above 1 pCi/L (Table 5-5 and
Figure 5—19). These wells were all completed in the Zone 3
aquifer and are in the sa ne region as the elevated Ra-226
and Ra—228 levels. As was the case with Ra—226, the dupli-
cate sailple for well No. EPA—18 had anomalously high Th-230
values.
Review of the thorju distribution and co7nparjso with the
TDS Zone 3 plume (Figure 5—15) indicates that in the high
TDS area around well No. 610 concentrations of thorium are
very high (up to 41,000 pCi/L). flowever, these values
significantly decrease to about 0.2 to 0.4 pCi/I. at the edge
of th plume. It can be concluded that Th-230 is not
migrating far from the tailings ponds.
Thorium distribution at the site reflects the control of pH
on the SOlUbility of thorium. At pH values below 5.0 (near
the ponds), thorium can remain in Solution. At near neutral
to alkaline pH values, thorium precipitates and is iriunebile.
Uranium—238
Analyses for Uranium -238 (U-238) ranged from a high of
7612 pCi/I. in well No. 610 to a low of 3.1 pCi/I. in well
No. EPA—7. Alluvial wells generally had concentrations of
less than 20 pCi/I.. However, well No. 625 did show concen-
trations above 70 pCi/I. in the first sampling round. No
drinking water standard is available for uranium activity.
In order to isolate wells with appreciable U—238 activities,
a scmewhat arbitrary value of 15 pCi/I. was chosen. This
value reflects the alpha activity standard and uranium—23E
DFW6H/o11 5—76
-------
is an alpha emitter. Table 5—5 lists the wells that
exceeded this value. Fifteen wells were $hCMn to exceed the
15 pCi/L value. These wells also exceeded the radium stan-
dard.
Review of igure 5—19 indicates that U-238 activity rapidly
decreases away from the core of the T S plume. Nowever,
U—238 has been found outside of UNC property at elevated
conceritrat ons. For example, well No. EPA-6 exhibited a
uranium activity of 219 pCi/L.
Gross Alpha and Gross Beta
Gross alpha and beta are twc parameters for which the CWA
does have stanoards. For gross alpha. the maximum contami-
nant level after subtracting uranium and radon activity is
15 pCi/L. Radon values were not analyzed: therefore,
Table 5-5 depicts groundwater analyses which do not aubtract
radon activity.
Gross beta is a direct reading. A limit of 50 .pCi/L exists
under the CWA. Only six occurrences above the value were
found in the groundwater analyses. Of these occurrences,
only one well was completed in the alluvial aquifer. This
well No. 625 is in the southwestern portion of the site.
Gross alpha readings above 15 pCi/L (without subtraction of
radon) are ubiquitous throughout the site and in all aqui-
fers of concern. However, in review of Figure 5—19, several
trends can be made. Zone 3 wells have highest gross alpha
concentrations in the T S plume where concentrations exceed
10,000 rr.g/L. ) ere 1 activities were up to 3,000 pCiIL. Down’
gradient near the fringe of the plume values decreased to
about 100 pci/L. Outside the plume, activities ar. in the
vicinity of 50 pCi/L.
DF W6fl/011 5—77
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ALLUVIAL AQUIFER CONTAMINATION
The alluvial aquifer has been impacted by the mine water
discharges and tailings leachate. Several di t t high TDS
plumes have been found at the site. The manor plume extends
southwest from the southern cell, down the stream valley.
This plume extends a mir.izmim of 1,000 feet past. the southern
cell. The extent of the plum, is beyond the furthest down—
gradient monitoring well. Post RI field investigations by
TJNC found TDS levels in excess of 20,000 mg/L in the south-
west alluvium. UNC has attributed these concentrations to
natural levels in the Mancos Shal, beneath the alluvium.
Investigations from theR! work indicate anomalously high
TDS concentrations in the alluvial aquife , near the Mancos
Shale contact. At this time it cannot conclusively be shown
what is the source of these anomalies.
Another plume, as evidenced by TDS concentrations, has been
she to radiate from the north cell. The extent of this
plume is smaller (less than 800 feet) than the southwest
alluvium plume. The manor reason the southwest plume
extends further is becaus, of higher groundwater velocities
beneath the stream chan ,l.
Alluvial contaminants, in addition to TDS include nitrate
(in excess of 200 mg/LI, and sulfate (in excess of
8,000 mg/LI. Heavy metals hav, also been found at concen-
trations above water quality standards. Among these are
selenium (0.4 ag/L), manganese (20 mg/U, cadmium
(0.125 mg/L), and molybdenum (0.28 mg/L).
Radionuclj , in the alluvium are primarily represented by
gross alpha activity. Values above the gross alpha primary
drink j .g water standard wer, found in six alluvial wells.
These wells exhibited gross alpha activities ranging from 16
to 45 pCi/ I .. One veil. had a gross beta activity in •XCeSS
DFb6H/012 6—4
-------
of the 50 pCi/L standard. The radiwn-226 and —228 standard
of 5 pC /L was exceeded in two alluvial. wtlls. Thorium and
uranium isotopes were shown not to migrate away from the
ponds the alluvium.
ZONE 3 CONTAHINATION
The Zone 3 aquifer has been severely impacted by contami-
nants that have leached from the northeast portion of the
north tailings cell. An elongate TDS plume has migrated
more than 2,000 feet from the disposal site. This contami-
nant plume has m .grated at a historic rate of between 337
and 450 feet per year between 1979 and 1985. TDS concentra-
tions near the source are above 15,000 mg/L with pH values
below 3.0. K .gh ammonia (100 mgfL), sulfate (8,000 mg/L),
and nitrate (35 mg/L.) are the ma or ions that affect water
quality. Heavy metal concentrations in the Zone 3 plume
exceed primary and secondary water quality standards, how-
ever, these concentrations typically decrease away from the
source. Heavy metals have migrated into the tribal lands
east of the site. Maximum concentrations on tribal lands
include: cadmium (up to .277 mg/L) chromium (.135 ag/L),
manganese (55 stg/L) , arsenic (1.8 mg/L), and beryllium
(.254 mq/L). Table 6—1 summarizes typical maximum contami-
nant levels in groundwater on tribal lands.
Radionuclide distribution in Zone 3 indicates that activity
levels decrease very rapidly from the source. Thorium and
uranium activities have been shown to decrease from 41,000
and 7,000 pCi/ I. to less than 1 and 55 pCi/L, respectively,
over a distance of 800 feet. Radicnuclidss have also been
found at of fsite locations (tribal lands) in Zone 3 wells.
e11 No. EPA-6 which is about 800 feet from the disposal
pond had the following radionuclide activity lsv•ls:
CFW6H/0 .2 6—S
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Activity
Radionticlide ( pC i/L )
Radium-226 and —228
Thorium 230 2.05
t.ran iun —238 219
Cross Alpha 153.
Gross Beta 308
ZONE I CONTA1 1NATION
The Zone 1 aquifer has also been contaminated by site acti-
vit.ies. The extent of contamination, however, je not as
extensive as in Zone 3. TDS plumes for the Zone 1 aquifer
indicate that contaminants are leaving the site from the
northeast section of the north tailings cell and migrating
to the northeast and east. Another plume ii migrating east-
ward from bo;ro pit No. 2 and has encroached onto the tn-
b 1 lands east of the site. both of the Zone 1 contaminant
plumes have traveled at Least 800 feet from their sources.
Contaminant velocities, as determined by historical TDS dis-
tribution, have been estimated at 100 feet per year between
1979 and 1985.
The Zone 1 contaminant plumes, on the tribal lands are char-
acterized by TOS concentrations between 6,000 and 7,000 mg/L,
acidic pH (4-5), and high nitrate concentrations (above
100 mg/L). Metal in groundwater on the tribal lands have
had concentrations up to 0.143 mgIL of cadmium, 1 mg/L of
arsenic and 15 mg/I. of manganese (Table 6—1).
Radionuclides activities are highest near th. north cell of
the tailings pond (well No. 611). Here, thorium (29 pCi/I.),
uranium (134 pCi/I.), gross alpha (117 pCi/I.), and gross beta
(lOS pCi/ I.) attain maximum Zone 1 levels. Radionuclides do
DFW6H/ 012
-------
not, however, travel very far in the Zone 1 aquifer. At th
five Zone 1 wells on the tribal lands, only gross alpha acti-
vity exceeded water quality standards. Gross alpha activity
in these four wells ranged from 10.9 to 22.2 pCi/L.
INTERRELATIONSHIPS OF THE AQUIFERS
One of the goals of the investigation was to determine the
degree of interrelationship between site aquifers. RI punp
tests showed little drawdown in wells within the same unit
as the pumping well. Therefore, the aquifers were not
stressed” enough to produce drawdown in lower or upper aqui-
fers and no conclusion can be made on the interconnectivity
of the aquifers. Review of previous testing has indicated
that, in places, the aquifers are hydraulically connected.
This phenomena is also indicated in hydrogeologic cross-
sections where pi.ezometric surfaces for the three aquifers
are near identical at seine locations. In portions of the
site, there appears to be no hydraulic connection between
the aquifers. This is evidenced by substantial piezometric
head differences between aquifers.
RECOMMENDATI ONS
The RI was responsible for filling previously identified
data gaps and supplementing or verifying information ocliec-
ted to date at the site. The need for additional RI work is
dependent upon the scope of the FS. Assuming that the FS
applies only to the remediation of the groundwater, the fol-
lowing are potential data gaps and future activities.
The principal data gap for the remediation of groundwater
contamination is characterization of the source, the tail-
ings pond. A detailed characterization would include
DF 6H/0l2 6—8
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United Nuclear Corporation Mining Waste NPL Site Summary Report
Reference 2
Excerpts From Record of Decision, United Nuclear Corporation
Ground-water Operable Unit;
EPA Region VI; September 30, 1988
-------
RECORD DECISION
UNITED NUCLEAR CORPORATION
GROUNDWATER OPERABLE UNIT
McKinley County, New Mexico
SEPTEMBER 1988
U.S. ENVIRONMENTAL PROTECTION AGENCY
REGION VI, DALLAS, TEXAS
Reference 2
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DECLARATION
FOR THE
RECORD OF DECISION
SITE NAME AND LOCATION
United Nuclear Corporation
McKinley County, New Mexico
Groundwater Operable Unit Remedial Action
STATEMENT OF PURPOSE
This decision document presents the remedial action for the Groundwater
Operable Unit of the United Nuclear Corporation (UNC) site selected by the
United States Environmental Protection Agency (EPA) in accordance with the
Comprehensive Environmental Response, Compensation, and Liability Act of
1980 (CERCLA), as amended by the Superfund Amendments and Reauthorization
Act of 1986 (SARA), and the National Contingency Plan (NCP).
STATEMENT OF BASIS
The decision is based upon the administrative record for the United Nuclear
Corporation Superfund Site. The attached index (Appendix E) identifies the
items which comprise the administrative record upon which the selection of
this remedial action is based.
Remedial action for the Groundwater Operable Unit is part of a comprehensive
response action for the United Nuclear Corporation Superfund Site. Remedial
activities addressing source control and onsite surface reclamation will be
implemented by United Nuclear Corporation under the direction of the U.S.
Nuclear Regulatory Commission (NRC), pursuant to the facility’s NRC license,
and integrated with the Environmental Protection Agency’s selected remedy for
the groundwater operable unit. Agency responsibilities for remedial action
at the United Nuclear Corporation Site are delineated in a Memorandum of
Understanding (MOU) signed by the EPA and C in August 1988. (Appendix I)
The Nuclear Regulatory Conmission and the State of New Mexico have reviewed
the proposed plan for.remedjal action, as identified in the remedial
investlgation/feasjbjljty study (RI/FS), and proposed Plan of Action Fact
Sheet, and support the remedy described in this Record of Decision.
(Appendices F, G)
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2
DESCRIPTION OF SELECTED REMEDY
The Operable Unit for the United Nuclear Corporation site addresses high
levels of radiological and nonradiological constituents that have seeped
from tailings into groundwater outside the tailings disposal site. The
hazardous substances of primary concern are arsenic, cadmium, cobalt,
nickel, radium—225/228, selenium, and gross alpha. The tailings seepage
has contaminated portions of the shallow alluvial groundwater system and
underlying Upper Gallup Sandstones.
The selected remedy for this operable unit Is designed to contain, remove,
and evaporate contaminated groundwater resulting from tailings seepage
outside the tailings disposal area thus preventing further migration of
seepage into the environment. The remedy is comprised of the following six
elements.
1. Implementation of a monitoring program to detect any increases in the
areal extent, or concentration of groundwater contamination at, and
outside of, the boundary of the tailings disposal area .
Evaluation of geochemical and hydrological information indicates that a
tailings seepage mound exists in the tailings disposal area resulting in
migration of contaminated groundwater into the alluvium, as well as under-
lying Zone 1 and Zone 3 Upper Gallup sandstones. Tailings seepage has
migrated outside the tailings disposal area in each of these three aquifers,
and there is the potential for further downgradient migration. For these
reasons, a monitoring program will be established prior to the installation
of extraction wells in each aquifer.
The monitoring program will consist of a groundwater monitoring network
comprised of a series of wells to measure water levels and water quality.
The monitoring points shall be located upgradient, downgradlent, and cross—
gradient of seepage plumes In order to further define the extent of contami-
nation in Zones 1 and 3 of the Upper Gallup Sandstone, and the southwest
alluvium. The extent of contamination in each aquifer, and concentration
of contaminants in each well, shall be used to identify the most effective
pumping well locations.
2. Operation of existing seepage extraction systems in the Upper Gallup
aquifers .
Because seepage from tailings has migrated into underlying Zone 1 and Zone
3 sandstones, the selected remedy includes operation of the East
pump—back wells in Zone 1 and the Northeast pump—back wells in Zone 3 until
adequate dissipation of the tailings seepage mound has been achieved.
Operation of these two pump—back systems will be integrated with active
seepage remediation that may be required by the NRC inside the tailings
disposal area, and with active seepage collection as required by EPA outside
the disposal area.
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3
3. Containment and removal of contaminated groundwater in Zone 3 of the
Upper Gallup Sandstone utilizing existing and additional wells .
Active remediation of Zone 3 outside the tailings disposal site will be per-
formed in areas contaminated by tailings seepage. The full extent of the
tailings seepage plume will be determined during remedial design, prior to
extraction well installation, and will be delineated on the basis of ground-
water flow directions in the aquifer in conjunction with identification of the
margin or amount by which standards are exceeded for hazardous constituents
in groundwater.
Seepage collection in Zone 3 will be designed to create a hydraulic barrier
to further migration of contamination. Final well locations will be guided
by observed saturated thicknesses in Zone 3, and the extent of the tailings
seepage plume as defined above. Data obtained during performance monitoring
of the extraction system should be used to determine the optimum rate of
pumping, and extent and duration of pumping actually required.
4. Containment and removal of contaminated groundwater in the southwest
alluvium utilizing existing and additional wells .
Active remediation in the southwest alluvium will be performed in areas
contaminated by tailings seepage. The extent of the tailings seepage plume
outside the tailings disposal area will be determined prior to extraction
well installation. Delineation of alluvial contamination will be based on
groundwater flow directions in the aquifer in conjunction with identification
of the margin or amount by which standards are exceeded for hazardous consti-
tuents in groundwater.
Seepage collection in the southwest alluvium will be designed to create a
hydraulic barrier to further migration of contamination while the source is
being remediated. The number of extraction wells required, and their final
locations, will be determined from the observed saturated thicknesses in
the alluvium, and the extent of the tailings seepage plume as defined above,
during the remedial design phase. Data obtained during performance monitoring
of the extraction system should be used to determine the optimum rate of
pumping, and extent and duration of pumping actually required.
5. Evaporation of groundwater removed from aquifers outside the disposal
area using evaporation ponds supplemented with mist or spray systems to
enhance the rate of evaporation .
Tailings seepage extracted in pumping wells will be directed to an evapora-
tion disposal system consisting of lined evaporation ponds and mist or
spray evaporation systems. Inflow to the evaporation disposal system will
be from current and required extraction wells outside and/or within the
tailings disposal area. The evaporation pond system, coupled with mist and
fy /
I c )
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4
spray evaporation systems, will be sized and operated in order to provide
sufficient evaporative capacity for maintenance of a reasonable operational
water balance. Optimization of the evaporation disposal system should occur
during the first several months of operation.
6. Implementation of a performance monitoring and evaluation program to
determine water level and contaminant reductions in each aquifer, and
the extent and duration of pumping actually required outside the
tailings disposal area .
In order to evaluate predicted reductions in contaminant concentrations
with time in a particular aquifer, and declines In pumping rates, a
performance monitoring program shall be implemented. Performance
monitoring during active seepage remediation will allow a determination to
be made regarding the adequacy of groundwater remedial actions outside the
tailings disposal area at the United Nuclear Corporation site.
These elements comprise remedial action in the groundwater operable unit at
the United Nuclear Churchrock site. The Nuclear Regulatory Con nission has
directed United Nuclear Corporation to submit a reclamation plan addressing
source control and surface reclamation measures at the site under the
Company’s Source Material License. Upon approval of a final reclamation
plan, both groundwater and source control/surface reclamation remedial
actions will be Integrated and coordinated to achieve comprehensive
reclamation and remediation of the site.
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Table 6
COMPOUNDS EXCEEDING STANDARDS
North South Sec. 36
Conta.mjriar Zone 3 Zone 1 Alluvium Alluvium Alluvjtim
Aluminum X x
Arsenic x X
Cadmium X X X x
Cobalt X X X
Manganese x x x
Molybdenum x X X X
Nickel X X X
Selenium X X x
Nitrate x x X X
TDS X X x X x
Ra—226—229 X
Gross Alpha x x x x x
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1. SITE LOCATION AND DESCRIPTION
The United Nuclear Corporation (UNC) Churchrock site is located approxl—
rnately 17 miles northeast of Gallup, New Mexico, in Mckinley County (Figure
1). United Nuclear Corporation, also referred to herein as the potentially
responsible party (PRP), operated the site as a uranium mill facility within
UNC—owned Section 2, TownshIp 16 North, Range 16 West (Figure 2). The site
includes an ore processing mill and a tailings pond area which cover about
25 and 100 acres, respectively. The tailings pond area is subdivided by
cross—dikes into three cells identified as the South cell, Central cell, and
North cell. In addition, two soil borrow pits (Pits No. 1 and No. 2) are
present in the Central Cell area. Sorrow Pit No. 2 is currently used for
storage of recovered and neutralized water extracted by three well systems
operated by UNC. These pumpback wells are currently used to remove contami-
nated groundwater from Zones 1 and 3 of the Upper Gallup Sandstone.
The area around the site is sparsely populated and includes Indian tribal
and allotted trust land as well as UNC-owned property. Section 36, Township
17 North, Range 16 West, located northeast of the site, Is owned by UNC and
bounded on the north by the Navajo Indian Reservation. The nearest resi-
dence Is located approximately 1.5 mIles northwest of the site. The nearest
groundwater well is located 1.7 miles northeast of the perimeter of the site.
Four known operating wells are located within a four mile radius of the site.
2. SITE STATUS
2.1 Site History
The UNC uranium mill was granted a radioactive materials license by the
State of New Mexico in May 1977 and operated from June 1977 to May 1982.
The mill, designed to process 4,000 tons of ore per day, used a conven-
tional crushing, grinding, and acid leach solvent extraction method to
extract uranium. The ore processed at the site primarily came from two of
UNC’s nearby mines: Northeast Churchrock and Old CPturchrock. Ore was also
obtained from the nearby Kerr—McGee (Quivira) mine. The average ore grade
processed at the mill was approximately 0.12 percent U 3 O (EPA, 1988).
The crushing, grinding, and milling processes produced a i acidic waste of
ground ore and fluid, con only referred to as tailings. The tailings were
pumped to the tailings disposal area. An estimated 3.5 million tons of
tailings were disposed In the ponds (EPA, 1988).
Prior to llcensingof the UNC mill, uranium mining began in the area north
of the present site. In 1968, the northeast Churchrock mine began operating
and removed and discharged mine water. Water discharged from this mine, and
later the iiv1ra mine, percolated into the ground and added water to the
alluvial and Upper Gallup aquifers underlying much of the site. Limited
monitoring of groundwater during the period of mining, and prior to operation
of the mill, indicated water quality was variable.
t)
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4
In July 1979, the dam on the south cell breached, releasing approximately
93 million gallons of tailings and pond water to the Rio Puerco (EPA,
1988). The darn was repaired shortly after Its failure. Cleanup of the
resultant spii 1 was conducted according to criteria imposed by state and
federal agencies, including EPA, at that time.
In October 1979, the New Mexico Environmental Improvement Division (NMEID)
ordered UNC to implement a discharge plan to control contaminated tailings
seepage. The tailings seepage had been deemed responsible for groundwater
contannnatlon. In 1981, UNC implemented a groundwater pumping system that
withdrew groundwater from the site aquifers and returned It to Borrow Pit
No. 2 for evaporation (EPA, 1988).
UNC began tailings neutralization In late 1979, and continued the process
until early 1982. Neutralization Included the addition of anronla or lime
to the tailings; neutralization has also been conducted several times
during the history of the mill operation (EPA, 1988).
In May 1982, UNC announced that they were going to temporarily close the
Churchrock uranium mill because of depressed uranium market conditions.
The market did not recover and UNC subsequently decided to close the facil-
ity permanently (EPA, 1988).
The offslte migration of radionuclides and chemical constituents Into the
groundwater, in addition to surface water and air emissions, prompted the
placement of the UNC site onto the National Priorities List (NPL) of Super-
fund sites in 1983.
EPA’s RI field activities at the UNC site were conducted from March 1984 to
August 1987. The objectives of the RI field activities were to determine
the nature and extent of groundwater contamination in the three aquifers at
the site.
During early 1987, UNC submitted a closure plan to the NRC for reclamation
of the mill site. This plan has been under review by the NRC since then and
s formally approved in September 1988. On August 26, 1988, EPA and the
NRC signed a Memorand of Understanding (MOU), a copy of which Is attached
a Appendix I, which provides for the coordination of EPA’s remedial action
with the U.S. Nuctear Regulatory Comisslon (NRC) required site reclamation
action. UNC’s current activities at the site are limited to (1)
compliance monitoring activities, (2) an Improved seepage collection system
operation, (3) dust control, (4) decontamination and sale of selected
equipment, and (5) enhanced spray evaporation of water contained in Borrow
Pit No. 2.
2.2 Response Historl
In 1981 EPA conducted a preliminary evaluation of the UNC site consisting
of an assessment of existing data and a site inspection. The site, then
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5
regulated by the State of New Mexico under ‘agreement state’ status with
the NRC, was subsequently included on the Superfund Interim Priority List.
In late 1982 EPA conducted an additional sampling inspection. In 1983 the
site was formally placed on the National Priorities List of Superfund sites.
EPA began the RI in August of 1984 and fIeldi rk began In early 1985 after
site access problems were resolved. The RI, which addresses groundwater
outside the byproduct materials disposal site, was released In August 1988.
EPA also released a FS report In August 1988 along with a proposed plan of
action fact sheet for the UNC site groundwater operable unit. EPA held a 29-
day public coninent period and a public meeting.
2.3 Enforcement History
During 1982 and 1983, EPA and IRIC engaged In extensive negotiations with
the aim of entering an agreed upon Administrative Order on Consent for
conduct of investigative and remedial activities at the site In response to
groundwater contamination. Itt August of 1983, after UNC declined to coninit
to an Order on Consent to promptly address groundwater concerns, EPA sent
notice letters to UNC indicating Its plans to conduct its o i Remedial
Investigation (RI) and Feasibility Study (FS).
In September of 1983 LINC objected to EPA’s decision to conduct its o t
RI/FS, stating that EPA had no authority under CERCLA with respect to the
site, and that EPA’s work would interfere and be duplicative of UNC’s own
efforts. EPA continued with development of its plans for a CERCLA RI/PS,
but progress was slowed as UNC denied EPA access to the site to conduct
RI/PS activities from April through September 1984.
In August 1984 UNC filed suit against EPA for declaratory and injunctive
relief in U.S. District Court for the District of New Mexico (No. 84—1163—
JB) seeking to prevent EPA conduct of the RI/FS. In September of 1984, EPA
obtained and executed an Administrative Warrant to conduct preliminary RI
activities. EPA also filed an action in the same District court seeking
injunctive relief and an Order In Aid of Access (No. 84—1409—98). During
the months of October through December 1984, UNC and the United States
filed numerous motions, in relation to both cases no. 1163 and no. 1409.
In December of 1984 U.S. District Court dismissed case no. 1163 ‘wIthout
prejudice’. UNC also Informed the Department of Justice of its intention
not to interfere with EPA access to the site to conduct the RI/PS, and
work on the study was able to proceed. In April of 1985, the U.S. District
Court entered an order granting EPA access to the UNC site for the purpose
of conducting the RI/PS. (UNITED STATES OF AMERICA v. UNITED NUCLEAR
CORP., 610 F. SUPP. 527 (D.N.M.,1985))
In June of 1986 the State of New Mexico returned Its authority to regulate
uranium mills back to the NRC. This Regulatory change prompted the develop—
N
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23
The locations of operating wells sampled by EPA in 1987 are shown in Figure 9.
Primary drinking water standards were not exceeded in any of the samples.
Well 15K-303 and the Gray Well were the only samples containing
radiological activity above 1 pico curie per liter (pCi/I), with 15K—303
containing 12.0 + 2.7 pCI/I beta and 1.6 + 0.1 pCi/I radium 226, and the
Gray Well containing 2.5 + 3.0 pCi/I aiphi and 5.6 + 3.6 pCi/I beta. These
activities are below the rinking water standards, and related to natural
background levels in area groundwater. The state standard for total
dissolved solids (1000 mg/I) was exceeded in samples from all four wells,
while the state standard for sulfate (600 mg/I) was exceeded in 15K—303.
The state standard for Iron (1.0 mg/L) was exceeded In wells 16F—606 and 15K—
303, and that for manganese (0.2 mg/I) exceeded in well 15K—303.
The principal exposure pathways through which humans might potentially
become exposed to contaminants in the future are:
o ingestion of groundwater from wells outside the tailings disposal
area In each of the contaminated target areas if water supply wells
are ever installed before completion of remedial activity
o inadvertent ingestion of surficial tailings solids
EPA concluded from its public health assessment in the Feasibility Study
that adverse health or environmental hazards could result if no action was
taken to prevent exposure to groundwater contaminants found at the site.
The public health assessment assumed ingestion of groundwater at contaminant
concentrations equal to those measured during the 1985 RI sampling events
(Tables 4 and 5). This assumption was conservative since dilution and
dispersion expected to occur if seepage were allowed to continue to migrate
downgradient from the site would likely further reduce the concentration of
contaminants from the concentrations assumed. The remedy selected for the
UNC groundwater operable unit is designed to contain and remove groundwater
contaminated by tailings seepage thereby preventing continued downgradient
migration of seepage and reducing significantly the amount of radiogenic
and nonradiogenic constituents released into the environment. Groundwater
remediation coupled with source control remedial action required by NRC
will allow further improvements in groundwater quality at the UNC site.
NRC-required source control measures, which address surficial contamination
from windblown tailings solids and control of groundwater evaporation
residues, are expected to eliminate significant potential risks to human
health and the environment via the direct contact, air emissions, or surface
exposure routes.
4. COMMUNITY RELATIONS
On April 6, 1987. EPA held its first con nunity meeting on the UNC site to
discuss the status of on—going investigations at the site, and to clarify
the respective roles of EPA and C In coordinating site reclamation.
Navajo translation was provided and NRC was in attendance. Fact sheets
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41
spray evaporation systems. Inflow to the evaporation disposal System will
be from current and required extraction wells outside and/or within the
tailings disposal area. The evaporation pond system, coupled with mist and
spray evaporation systems, will be sized and operated in order to provide
sufficient evaporative capacity for maintenance of a reasonable operational
water balance. Optimization of the evaporation disposal system Should
occur during the first several months of operation, and shall Include pilot
testing to determine the optimun pH for water evaporation.
6. ImplementatIon of a performance monitoring and evaluation program to
determine water level and contaminant reductions in each aquifer, and
the extent and duration of pumping actually required outside the
iTiings disposal area .
In order to evaluate predicted reductions in contaminant concentrations
with time in a particular aquifer, and declines in pumping rates, a
performance monitoring program shall be Implemented. Monitoring well
locations shall be chosen at critical points to allow effectiveness
evaluations of hydraulic capture zones In collecting tailings seepage.
Performance monitoring during active seepage remedlation will allow a determ-
ination to be made regarding the adequacy of groundwater remedial actions
outside the tailings disposal area at the United Nuclear Corporation site.
Monitoring data will also be used to aid in making any modifications in
remedial action outside the tailings disposal area, in order to meet CERCLA
requirements.
These elements comprise the selected remedy for the groundwater operable
unit at the United Nuclear Churchrock site. As previously mentioned the
Nuclear Regulatory Comisslon has directed United Nuclear Corporation to
submit a reclamation plan addressing source control and surface reclamation
measures at the site under the company’s Source Material License. Upon
approval of a final reclamation plan, both groundwater and source contro)/
surface reclamation remedial actions will be integrated and coordinated to
achieve comprehensive reclamation and remediation of the site.
6.2 Cost of Selected Remedy
The estimated capital cost of the selected remedy is $12 million and the
present-worth estimate using a 10 percent discount rate is $17 million over
a 10-year period. This Is approximate and made without detailed
engineering data. The actual final cost of the selected remedy will depend
on a number of factors which Include:
o material and labor costs, extraction well development, competitive
market, conditions, and others direct and indirect costs related to
the startup of remedial activity;
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42
o achievable flow rates from extraction wells, and therefore, the size
of the enhanced mister/pond evaporation system necessary to
accormnodate these flows;
o changes in operat ofl and maintenance costs related to well system
performance;
o changes in contaminant concentrations and pumping rates over time
resulting from groundwater extraction arid source control activities
which may constrain the required duration of pump ng; and
o changes in parameters such as cleanup criterion, should significant
additional information on background levels of constituents result
in any significant adjustments of such parameters.
6.3 Statutory Determinations
Section 121 of SARA requires the selected remedy to be protective of human
health and the environment, be cost effective, use permanent solutions and
alternative treatment or resource recovery technologies to the maximum extent
possible, be consistent with other environmental laws, and have a preference
for treatment which significantly reduces the toxicity, volume, or mobility
of the hazardous substances as a principle element. EPA believes that the
selected remedy best fulfills the statutory and selection criteria as compared
to the other solutions evaluated herein.
1. Protective of Human Health and Environment
The selected remedy, by containing and removing tailings seepage, will sub-
stantially reduce groundwater contamination in aquifers outside the byproduct
materials disposal site. Contaminant concentration in impacted aquifers
will be reduced to MARs to the maximum extent practicable. The selected
remedy, in conjunction with NRC—directed source control remedial action
should effectively mitigate and minimize potential threats to human health
and the environment. Implementation of the selected remedy will not cause
unacceptable short—term risks or crossmedia impacts.
2. Cost Effective
The selected remedy offers the lowest cost of all the treatment alternatives.
Compared to other treatments alternatives, it is equally effective in remov-
ing contaminants in the alluvial and Upper Gallup Zone 3 aquifers, and Is
equally implementable. As rev1ously mentioned, the characteristics of the
Upper Gallup Zone I aquifer limit the implementability and reliability of
an extraction well network (e.g. Alternative 1) In significantly decreasing
contaminant levels in this aquifer.
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41
United Nuclear Corporation Mining Waste NPL Site Summary Report
Reference 3
Public Comment Draft, United Nuclear Corporation
Churchrock Site Operable Unit, Feasibility Study,
Gallup, New Mexico; EPA Region V I; August 1988
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PUBL:C COMMENT DRAFT
UNITED NUCI.EAR CORPORATION CHURCHROCX SITE
OPERABLE UNIT FEASIBILITy STUDY
GALLUP, NEW MEXICO
AUGUST 1988
Reference 3
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CLEANUP CRITERIA
Concentrations of contaminants in each of the aquifers were
compared to federal and state standards and background levels.
Wells that had aroundwater samples with one or more cor.tami-
nants exceeding standards or background levels were used to
develop target areas for groundwater cleanup. Contaminant-
specific Applicable or Relevant and Appropriate Requirements
(ARARs) identified as cleanup criteria for the tJNC site were:
Federal Safe Drinking Water Act (SDWA) Maximum Contaminant
Levels (MCLs); New Mexico Water Quality Act (MNWQA) standards;
and Health and Environmental Protection Standards for Uranium
and Thorium Mill Tailings. Table ES-3 summarizes the
contaminant—specific ARARs.
For the purposes of the OUFS, background levels are based on
postnuning, pretailings conditions and have been set by EPA
and NMEID based on currently available information. Should
additional information become available that would signifi-
cantly alter the estimation of background levels, such in-
formation would be evaluated in terms of its impact on
remedial actions in each aquifer.
PUBLIC HEALTH RISK ASSESSMENT
A public health risk assessment was conducted for the no-
action alternative following guidelines established in the
Superfund Public Health Evaluation Manual (EPA, 1986). Two
exposure scenarios were analyzed: current and future use.
The current use scenario evaluates exposures from consumption
of groundwater from existing domestic and livestock wells.
The future use scenario assesses exposures that result from
consumption of groundwater from hypothetical domestic use
wells located within each of the cleanup target areas.
Results of the public health risk assessment indicate that
potential excess lifetime cancer risks from ingestion of
arsenic 9 ntazninated g 9 undwater at the site range from
1.0 x 10 to 1.2 x 10 . Potential excess cancer death
risks fro ingestion of 5 radionuclides at the site range from
1.8 x 10 to 6.5 x 10 . Evaluation of noncarcinogenic
risks at the site indicate that estimated daily intakes for
several contaminants exceed established health—based levels.
SCREENING OF RESPONSE ACTIONS, TECHNOLOGIES,
AND PROCESS OPTIONS
Response actions, technologies, and process options that are
potentially suitable for application to the clean-up target
areas were developed and screened. The first step in the
screening process was the identification of the remedial
ES-6
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The remaining radiOlOgical contaminants were evaluated on
the basis of 0 carciJt0geflic health effects. These contarni—
riants were assessed in terms of toxicological end points
sucn as neurotoxicitY, behavioral toxicity, hepatotoXiCity,
renal toxicity, hematologiC toxicity, reproductive toxicity,
and teratogeniCitY.
Table 4-9 presentS summaries of toxicity profiles of the
11 indicator chemicals for both carcinogenic and noncarcirio
genic effects.
TOXICITY SUM RIES- ADI0NtJCLIDES
Radii.utt—22 6 , radium22 8 , thoriwn23O, and uraniuxn-238 have
been detected in the groundwater at the site. Once ingested,
each of these radioriuclideS accumulate to some degree in
human bone tissue. The radioactive decay of these materials
produces alpha, beta, and gamma radiation, which may deliver
significant radiation doses tO the bone t ssue. Bone cancers
have been observed among individuals who were exposed to
radium in the course of luminous-dial manufacturing and among
patients who received radium medicinally during the early
years of this century (Eisenbud, 1987). Leukemia has been
observed in increased frequency among groups exposed to ion-
izing radiation, such as the survivors at Hiroshima and
Nagasaki. Also, thorium can be taken up by the liver and
uranium by the kidney.
RISK ASSESSMENT
Quantitative health risks are calculated using the exposure
and toxicity information presented previously. Health risks
are presented in terms of both carcinogenic and noncarCiflO
gertic effects.
The methodology used in this risk assessment is based or. the
Superfund Public Health Evaluation Manual (EPA, 1986). For
carcinogenic contaminants via the ingestion pathway, the
estimated lifetime cancer risk (R) was calculated using the
following model:
R p xd
where:
p = cancer potency (kg day/mg)
d = lifetime average intake (mg/kg/day)
The excess lifetime cancer risk is the incremental increase
in the probability of contracting cancer over a 70—year
period.
4—13
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the boundary of Section 2 in each of the target areas. The
contar.ir.ant concentrations that exist under this scenario
are assumed to-be equal to concentrations measured during
the 1985 RI sampling events (Tables 4-1 and 4—2) . This as-
sumption is cor.servative. Dilution and dispersion occurrinc
as the plume migrates doungradient from the site will likely
further reduce the concentration of contaminants from the
concentrations assumed.
For the future ingestion scenario, the rate of groundwater
ingestion is assumed to be two liters per day for a 70-kg
adult and one liter per day for a 10—kg child. Daily in-
takes have been estimated for both the adult and child using
the maximum and mean values for each contaminant. The rnaxi-
mum and mean values have been calculated for each target
area (north alluvium, south alluvium, Zone 1, and Zone 3).
The two northern alluvial target areas have been combined
for this public health assessment. The calculated daily
intakes of nonradiological contaminants for the future in-
gestion of contaminated groundwater are presented in
Table 4-7.
The 70—year lifetime doses due to ingestion of radionuclides
are presented in Table 4-8 for both maximum and mean concen-
trations for the future use scenario.
TOXICITY ASSESSMENT
Some of the general toxicological effects associated with
exposure to nonradiological indicator chemicals and
radionuclides found at the site are summarized in this sub-
section. Eleven nonradiological indicator chemicals were
selected for discussion of toxicological characteristics.
These 11 chemicals were selected based on their frequency of
occurrence at the site, concentration, and potential toxic
effects. Exclusion of a chemical from this summary does not
imply that exposure to these substances is without risk.
All chemicals detected may contribute, in varying degrees,
to potential risks from the site.
TOXICITY StTh2 !ARY--NONRADIOLOGICAL CONTAMINAWI’S
The metals and inorganics included in this assessment can be
divided into two categories based on type of health effect:
carcinogens and nortcarcinogens. Carcinogens are those con-
taminants that may cause or induce cancer; EPA has various
categories for potential carcinogens that are based on
weight—of—evidence. Some metals may cause cancer by one
exposure route but not by other routes. Arsenic is the only
nenradiological contaminant detected in the groundwater that
EPA currently considers carcinogenic via the ingestion route.
4—10
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The remaining nonradiological contaminants were evaluated on
the basis of noncarcinogenic health effects. These cor.tami—
nants were assessed in terms of toXicolog ,cal end points
such as neurotoxicity, behavioral toxic .ty, hepatotoxicitv,
renal toxi tv, hematologic toxic ty, :e roductive toxicity,
and teratogeriicity.
Table 4—9 presents summaries of toxicity profiles of the
11 ind .cator chemicals for both carclnogenic and noncarcino—
genic effects.
TOXICITY S RiES-- DIoNucLIDES
Radiu.rn-226, radiuzn—228, thorium-230, and uranjuln—238 have
been detected in the groundwater at the site. Once ingested,
each of these radionuclides accumulate to some degree in
human bone tissue. The radioactive decay of these mater ,als
produces alpha, beta, and gamma radiation, which may deliver
significant radiation doses to the bone t:ssue. Bone cancers
have been observed among individuals who were exposed to
radium in the course of luminous—dial manufacturing and among
patients who received radium medicinally during the early
years of this century (Eisenbud, 1987). Leukemia has been
observed in increased frequency among groups exposed to ion-
izing radiation, such as the survivors at Hiroshima and
Nagasaki. Also, thorium can be taken up by the liver and
uranium by the kidney.
RISK ASSESSMENT
Quantitative health risks are calculated, using the exposure
and toxicity information presented previously. Health risks
are presented in terms of both carcinogenic and noncarcino—
genic effects.
CARCINOGENS-—NONR.ADIONUCLIDES
The methodology used in this risk assessment is based on the
SuPerfund Public Health Evaluation Manual (EPA, 1986). For
carcinogenic contaminants via the ingestion pathway, the
estimated lifetime cancer risk (R) was calculated using the
following model:
R = px d
where:
p = cancer potency (kg—day/mg)
d = lifetime average intake (mg/kg/day)
The excess lifetime cancer risk is the incremental increase
in the probability of contracting cancer over a 70-year
period.
4—13
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The cancer potency factor converts estimated intakes directly
to 1.ncrernental risk. (This factor is based on an upper 95-
percent confidence limit on the probability of response per
un t intake of a chemical over a lifetime, i.e., only 5 per-
cent chance that the probability of response could be
greater than the estimated value on the basis of the
experimental data used.) If the exposure assessrent is
conservative, the resultant health risk that is calculated
is also conservative. Consequently, the calculated risk may
overestimate the actual risk associated with consuming
groundwater at the site.
EPA’s cancer potency factor for arsenic, as listed in the
Integrated Risk Information System (IRIS) , is 15 kg-day/mg.
Since EPA published this value, a scientific panel and the
Risk Assessment Forum have recommended that it be reduced to
1.5 kg-day/mg. This reduced value has been used to calcu—
lated carcinogenic health risks.
The excess lifetime cancer risk froir arsenic ingestion has
been calculated using both the mean and max3xnwn intake values
for the future exposure scenario. The adult intake was used
rather than the child intake because the risk conversion
number is for 70 years of ingestion. Table 4—10 presents
the excess lifetime cancer risks for future ingestion of
arsenic from the various groundwater aquifers. Arsenic
concentrations detected in samples from Zone 3 have the
highest estimated excess lifetime cancer risks: th! esti-
mated risk using the maximum concentration is lxl.0 , and_ 2
the estimated risk using the mean concentration is 2.5x10
It should be noted that these estimated lifetime cancer
risks are based on arsenic concentrations that range from
0.03 to 2.4 mg/i in Zones 1 and 3. The arsenic MCL of
0.05 m l corresponds to an excess lifetime cancer risk of
2.lx l O
Table 4-10
POTENTIAL EXCESS LIFETIME CANCER RISKS
FROM INGESTION OF ARSENIC IN GROUNDWATER--
FUTURE USE SCENARIO
Excess Lifetime Excess Lifetime
Cancer Risk Cancer Risk
Zone
Zone
1
3
Maximum Concentrations Mean Concentrations
4.3 x 1o 1.2
1. Ox lO 2.SxlO
A
F . ,’
4—19
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CARCINOGENS--RADIONUCLIDES
Radionuclides that are deposited in the body could produce a
variety of cancers (EPA 76, NAS 80) . EPA ’s Office of Radia-
t.cn Prograr’s (ORP) indicates that risks due to rad onuclide
exposure should be calculated in terms of c ncer fatalities.
The ORP uses a conversion factor of 2.8x10 excess risk of
death from cancer from whole body exposure to one millii-em
of radiation. Table 4-].]. presents the estimated risk of
death from ingestion of radionuc ljdes detec-ted in the various
groundwater aquifers under the future use scenario. Zone 3
also has the highest estimated health risk for ingestion of
radionuclides: the estimated excess risk from ingestion of
thoriu 9 23o is l.5x10 using the maximum concentration and
1.3x10 using the mean concentration. The excess Lifetime
risk of death from ingestien 5 of radionucl des under the cur-
rent use scenario is l.7x10 and 7.8x10 based on the max-
a.muzn and mean Ra-226 concentrations, respectively.
NONCARCINOGENS
Exposure to noncarcinogens has been assessed by comparing
the estimated daily intake of contaminants to reference doses
(RfDs) or Acceptable Intakes for Chronic Exposure (AICs).
RfDs and AICs are estimates of an exposure level that would
not be expected to cause adverse health effects when expo-
sure occurs for a significant portion of the lifespan. For
those indicator chemicals selected, RfDs and AICs have been
developed for cadmium, manganese, nickel, and selenium.
These values are presented in Table 4—12. To assess the
overall potential for noncarcinogenic effects posed by in-
gestion of multiple noncarcinogenic contaminants, a hazard
index (HI) approach has been used. For this method, which
assumes dose additivity, the ratios of estimated daily intake
to the RfD or AIC for each contaminant are summed (EPA, 1986).
As the HI approaches a value of one, the concern for possible
noncarcinogenic health effects is increased.
Table 4-12
RfDs AND AICs USED IN THE RISK ASSESSMENT
Contaminant RfD or AIC (mg/kg/day )
Cadmium 000 29 a
Manganese 0 22 b
Nickel 0.02
Selenium 0003 a
aAIC from Superfund Public Health Evaluation Manual (EPA,
1986)
bRfD IRIS Data Base (EPA, 1987)
4—20
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I ’ ,
United Nuclear Corporation Mining Waste NPL Site Summary Report
Reference 4
Ground-water Corrective Action, Churchrock Site;
Prepared for UAJC Mining and Milling by
Canonie Environmental Annual Review; 1989
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2
identified as Zone 3 and Zone I of the Upper Gallup Sandstone and the
Southwest Alluvium. These formations are described in the Geohydrologic
Report (GHR) (Canonie, 1987b), the EPA’s Feasibility Study (EPA, 1988a),
and the EPA’s Remedial Investigation (EPA, 1988b).
The corrective action at the Church Rock site described in the RD consists
of extraction of tailings seepage from Zone 3 and the Southwest Alluvium.
Limited seepage extraction from Zone 1 was to continue until dewatering of
Borrow Pit No. 2, which is the source of tailings seepage in Zone 1, is
completed. Figure 1-1 is a site orientation map that provides an overview
of current site conditions and the target areas where corrective action is
being implemented. The remedial action target areas were delineated in the
RD (Canonie, 1989). For Zone 3 and Zone 1, acidic pH and calculations of
travel distance were used to determine the extent of the target area. For
the Southwest Alluvium, chloride concentrations greater than 100 milligrams
per liter (mg/l) and calculations of travel distance were used to determine
the extent of the target area. A summary of the remedial actions completed
in 1989 is presented below.
1.2 Remedial Activities
l.2. Zone 3 Remedial Action
Remedial action in Zone 3 consists of pumping the existing northeast pump-
back and new extraction wells located in or adjacent to the target area
located northeast of the North Cell of the tailings impoundment. The
existing northeast system consists of six wells pumping at an average
combined rate of approximately 8 gallons per minute (gpm). Figure 1-1
shows the location of the system. The wells were installed in 1983 as
required by the New Mexico Environmental Improvement Division to control
migration of tailings seepage. The wells have been pumping continuously
since that time and have extracted a portion of the seepage migrating from
the North Cell of the tailings impoundment.
The purpose of the new extraction well system is to create a hydraulic
barrier to further migration of the plume and to dewater the remedial
CanonteErwironniental
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3
action target area shown on Figure 1-1. The extractable volume of the
target area in Zone 3 is estimated to be 200 million gallons or less. The
system of wells is designed to remove this volume in 6 1/2 years of opera-
tion. However, monitoring of hydrogeologic Conditions during remediation
will determine the duration and magnitude of pumping actually required.
Figure 1-1 shows the locations of the new extraction wells. As shown, a
total of 12 new wells, numbered 701 through 713, were installed in 1989.
These wells comprise Stage I of the Zone 3 system described in the RD. The
remaining Stage II wells are scheduled to be installed in 1991 with the
number and location to be determined based on the performance of the
Stage I wells.
Originally, a total of 13 wells was proposed for the first stage of well
installation . However, the results of the aquifer test conducted in the
first five wells installed (708 through 712) indicated that Well 704 would
have a low yield and, by Interfering with adjacent extraction wells, could
cause a net loss of system capacity by reducing the productivity of sur-
rounding wells. United Nuclear sought and received approval from the NRC
arid EPA for exclusion of the well from the program in June 1989.
The new Zone 3 extraction wells began pumping on August 7 and 8, after
installation of the distribution lines was conipieted. The wells have
pumped continuously since that time with a combined average flow rate of
approximately 43 gpm. This rate is less than the rate of 60 gpm assumed
during the system design because the hydraulic properties of the formation
limit the productivity of the wells. The extraction wells are monitored
daily for water level, Instantaneous pumping rate, and cumulative volume
pumped so that adjustments to system operation can be made as needed.
Evaluation of the performance of the system is based on the data collected
since the third quarter sampling event in July 1989.
1.2.2 Zone 1 Remedial Action
Tailings seepage in Zone 1 originated from its subcrop in Borrow Pit No. 2
and migrated to the east of the Central Cell of the tailings impoundment.
CanonteEnvironmental
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4
Figure 1-1 shows the )ecation of Borrow Pit No. 2 in relation to the plume
in Zone 1. The remed ai action for Zone I consists of dewatering Borrow
Pit No. 2 and conti.nuation of pumping from the existing north cross dike
and east pump-back wells until the pit is dewatered. Additional pumping in
Zone 1 has been determined to be infeasible due to the low transrnissivity
of the formation within the target area (Canonie, 198Th; EPA, 1988a).
In accordance with the schedule presented in the PD, Borrow Pit No. 2 was
dewatered in 1989. In fact, dewatering was completed at the end of April
1989, which was approximately 6 months earlier than anticipated at the time
the RD was submitted. Since Borrow Pit No. 2 is dry, remedial activities
for Zone 1 consist of monitoring water levels and water quality in 10 wells
located east and northeast of the pit. Although Borrow Pit No. 2 is dry,
the existing pump-back wells continue to operate as required by the NRC
License and the EPA in the A0 (EPA, 1989). Evaluation of the performance
of the Zone 1 remediation is based on the data collected since the second
quarter sampling event in April 1989, when Borrow Pit No. 2 was dewatered.
L2.3 Southwest Alluvium Remedial Action
Remedial action for the Southwest Alluvium consists of pumping three ex-
traction wells comprising a barrier/collection system in the target area
shown on Figure 1-1. The system is located downgradient of the southern
edge of the South Cell of the tailings impoundment and upgradient of the
Points of Compliance (POC) wells designated by the NRC for the Southwest
Alluvium. The location, spacing, and pumping rates for the wells were
designed to establish a hydraulic barrier to further migration of seepage
through the alluvium while the source is being remediated.
Figure 1-1 shows the location of the three extraction wells (801 through
803) and four monitoring wells (804 through 807) that were installed in the
Southwest Alluvium. The wells were installed in August 1989 and began
pumping on October 16, 1989. The wells have pumped continuously since that
time with a combined average flow rate of approximately 20 gpm. This rate
is higher than the rate of 17 gpm assumed fordevelopment of the system
design. As with the Zone 3 system, the extraction wells are monitored
CanonteEnvircnrner.tal
-------
5
daily for water level, instantaneous pumping rate, and cumulative volume
pumped so that adjustments to system performance can be made as needed.
Evaluation of the performance of the system is based on the data collected
since the fourth quarter sampling event in October i Bg.
1.2.4 Evaporation Disposal System
Seepage collected by the extraction wells is being disposed of by evapora-
tion. The evaporation disposal system is designed to dispose of the ex-
tracted tailings seepage by the end of 1996. As shown on Figure 1-1 the
system consists of two, five-acre lined evaporation ponds equipped with an
evaporation mist system and a separate mist or spray evaporation system
installed on the surface of the tailings. The evaporation disposal system
has been installed and is operating entirely within the tailings disposal
area. Details of the design and construction of the system are presented
in Amendment I of the Reclamation Plan (Canonie, 1988a), the Technical
Specifications (Canonie, 1988b) and the As-Built Report (Canonje, 1989c).
The lined ponds were constructed in October 1988 through January 1989
and began operation on January 3, 1989. The misters were installed in
spring 1988 and have been used during the summer months to help control
Windblown tailings and dispose of the water from the extraction wells and
Borrow Pit No. 2.
Between January and April 1989, water discharged to the ponds consisted of
water pumped from the existing northeast, north cross dike, and east
pump-back well systems and from Borrow Pit No. 2. Since Borrow Pit No. 2
was dewatered in April 1989, only water from the existing and new extrac-
tion wells has been discharged to the system.
L.2.5 Source Control - Surface Reclamatig
Another component of the remedial action is the surface reclamation of
tailings. Surface reclamation activities related to source control began
in May 1989 and will continue until October 1997, when reclamation is
-------
6
scheduled to be completed. Beneficial effects from the reclamation ac-
tivities are to be realized by placement of a cover over the tailings
impoundment to p revent infiltration of precipitation. A description of,
and technical specifications for, the surface reclamation activities are
presented in the Reclamation Plan (Canonie, 1987a).
As shown on Figure 1-1, the reclamation activities completed in 1989 in-
cluded regrading and placement of the interim soil cover in the North Cell.
Regrading of the North Cell is an important step for source control for
Zone 3 because the seepage present in this unit originated from tailings
liquids in direct contact with the sandstone exposed in the northeast
corner of the North Cell [ GHR (Canonie, 1987b)]. The regrading and recon-
touring of the tailings materials, shown on Figure 1-2, eliminates ponded
water and minimizes infiltration. In addition, placement of the compacted
soil cover provides a low permeability layer that also minimizes infiltra-
tion. Permeability testing of the interim cover material provided values
of 1.4 x io6 centimeters per second (crn/sec), 3.9 x io8 cm/sec, and 3.5 x
io8 cm/sec. These values confirm that the compacted soil cover serves a
barrier to infiltration. As a result, further seepage recharge to Zone 3
is minimized.
L3 Performance Monitoring
A program of performance monitoring was established to evaluate the success
of the remedial action in meeting the design expectations. Performance
monitoring may indicate that the objectives have been met and the remedy is
complete. The results of the monitoring may also indicate that achievement
of all cleanup levels in a reasonable time period Is technically impracti-
cal and that establishment of Alternate Concentration Limits (ACLs) or a
waiver to meeting certain contaminant-specific Applicable or Relevant and
Appropriate Requirements (ARARs) is necessary. A detailed description of
the monitoring program is presented in the RD (Canonie, 1989a). Figure 1-2
presents the locations of the wells included in the performance monitoring
program.
CanonieEnvircn ’-- i
-------
9
they were collected in mid-July, immediately prior to startup of the sys-
tem. The fourth quarter data represent conditions after three months of
pumping (August through October).
The results of the evaluation indicate that the .extraction wells are per-
forming as designed and are successful in:
1. Capturing and extracting seepage in the remedial action target
area; and
2. Creating a hydraulic barrier to further migration of tailings
seepage.
For example, the saturated thickness of the formation has been reduced by
more than 20 feet in the center of the well system. The area where draw-
down caused by the wells equals or exceeds 10 feet is approximately 52
acres. This area of intense dewatering incorporates 90 percent of the
Zone 3 target area.
Additional confirmation of the performance of the well system is provided
by a comparison of actual field conditions and conditions predicted by the
computer simulation. The location and configuration of the contours of
saturated thickness based on the fourth quarter water level data are simi-
lar to those generated by the computer simulation. The similarity of the
contour plots indicates the system is operating as predicted in the RD
(Canonie, 1989a).
The preliminary pH data provide confirmation that the wells are extracting
seepage. Comparison of the data from the third quarter and the fourth
quarter sampling events Indicates that the areal extent of tailings seepage
represented by acidlc pH was reduced by half, from approximately 72 acres
to 34 acres, during the first three months of system operation.
CanonteEnvironnier ta].
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10
Zone I - Performance Monitoring Evaluation
The Zone 1 performance monitoring evaluation utilized data collected during
the second, third, and fourth quarter 1989 sampling events. The second
quarter data represent initial conditions since they were collected at the
end of April, immediately prior to dewatering of Borrow Pit No. 2.
The results of the Zone 1 performance monitoring evaluation indicate that
water level and pH measurements remained stable for the period between
second quarter 1989 (when Borrow Pit No. 2 was dewater.ed) and fourth quar-
ter 1989. The plume, represented by acidic pH, has migrated approximately
150 feet downgradient from that delineated by the remedial action target
area in the RD (Canonie, 1989a). Since the target area was established
based on data collected in 1986, this distance is approximately one-third
less than would be expected using the velocity of 115 feet per year to 148
feet per year calculated in the RD (Canonie, 1989a). Given the low per-
meability of Zone 1, dissipation of the mound will be a long-term process
and identifiable changes or trends in water level and pH will occur in
small increments.
Southwest Alluvium Performance Monitoring Evaluation
The Southwest Alluvium performance monitoring evaluation utilized data
collected during the fourth quarter sampling event in October 1989 and
water level readings obtained in December 1989 specifically for this re-
port. The fourth quarter data represent initial conditions since they were
collected immediately prior to startup of the extraction wells.
The results indicate that the extraction wells are performing as designed.
Because the wells did not start operating until mid-October, the monitoring
data provide only a preliminary indication of the effects of the extraction
wells. However, review of the water l vel data indicates that the extrac-
tion wells are beginning to cause a reversal of the water level gradient
and creating a hydraulic barrier to flow.
CanonteErjviror:.
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I ’
Mining Waste NPL Site Summary Report
U.S. Titanium Superfund Site
Nelson County, Virginia
U.S. Environmental Protection Agency
Office of Solid Waste
June21, 1991
FINAL DRAFT
Prepared by:
Science Applications International Corporation
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
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p 1
DISCLAIMER AND ACKNOWLEDGEMENTS
The mention of company or product names is not to be considered an
endorsement by the U.S. Government or by the U.S. Environmental
Protection Agency (EPA). This document was prepared by Science
Applications International Corporation (SAIC) in partial fulfillment of
EPA Contract Number 68-WO-0025, Work Assignment Number 20.
A previous draft of this report was reviewed by Kim Hurnmel of EPA
Region III [ (215) 597-1727], the Remedial Project Manager for the
site, whose comments have been incorporated into the report.
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Mining Waste NPL Site Summary Report
U.S. TITANIUM SUPERFLJND SiTE
NELSON COUNTY, VIRGINIA
INTRODUCTION
This Site Summary Report for the U.S. Titanium site is one of a series of reports on mining sites on
the National Priorities List (NPL). The reports have been prepared to support EPA’s mining program
activities. In general, these reports summarize types of environmental damages and associated mining
waste management practices at sites on (or proposed for) the NPL as of February 11, 1991 (56
Federal Re2iSter 5598). This summary report is based on information obtained from EPA files and
reports and on a review of the summary by the EPA Region Ill Remedial Project Manager for the
site, Kim Hummel.
SITE OVERVIEW
The U.S. Titanium NPL Site covers approximately 175 acres of a former titanium dioxide
manufacturing plant (milling and ore-processing plant) located within Nelson County, Virginia, in the
rural community of Piney River, on the north side of the Piney River. Superfund remedial efforts are
specifically directed toward seven locations on the site, comprising a total of about 50 acres
(Reference 1, page 5).
The site has had many different owners during its course of operation. According to EPA Region Ill,
P.R. Corporation is the most recent owner, having acquired the property sometime after 1987
(although the exact date was not known). U.S. Titanium was the owner prior to P.R. Corporation.
The plant began operation in 1931 under the auspices of the Virginia Chemical Corporation, which
owned and operated the facility until July 1944. American Cyanamid Corporation operated the
facility from 1944 to 1971. It owned the facility until 1973; the 2 years post-operation (i.e., 1971 to
1973) were spent negotiating facility-closure plans with the State Water Control Board (SWCB). Mr.
S. Vance Wilkins purchased the site from American Cyanamid in 1973. He owned it until 1976,
when he sold it to U.S. Titanium (Reference 5, page 1).
The American Cyanamid Corporation appears responsible for the majority of waste generated and
stored at the facility. During American Cyanamid’s 27 years of operating the facility, about 80,000
cubic yards of copperas waste (i.e., ferrous sulfate) was produced. This waste was stored onsite as a
stockpile for later sale as a commercial product (the type and purpose of the product was not defined
in the available literature) (Reference 5, pages 1 and 2; Reference 2, Volume 1, pages 6 and 7).
A
1
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U.S. Titanium Superfund Site
However, the copperas waste stockpile was never sold commercially, and in December 1980, the
wastes were buried onsite under State orders (Reference 2, Volume 1, page 8). Prior to burying the
copperas waste, the facility owner that followed American Cyanamid (S. Vance Wilkins, the owner
from 1973 to 1976) attempted to reduce runoff associated with the large stockpile of copperas
material by installing a State-permitted temporary leachate-collection and recirculation system (No-
Discharge Certificate No. 1W-ND-407) (Reference 5, page 1).
Due to these various modes of copperas management prior to its final burial, several separate and
distinct areas were identified as possible sources of cOnt2minatiOn. These areas, combined with other
locations used in the plant’s manufacturing and/or wastewater treatment processes (e.g., an
evaporation pond, an unreacted ore-waste pile, two sedimentation ponds, a settling pond, and a
drainage area that receives the majority of the surface-water runoff from the site) comprise seven
distinct and separate areas of concern (see Figure 1). Table 1 provides a brief description of each of
these areas (Reference 1, pages 5 through 9; Reference 2, Volume 1, pages 3 through 5).
U.S. Titanium improperly managed the temporary leachate-collection and recirculation system
installed by Vance Wilkins. Contaminated runoff from the stockpiled copperas then entered the Piney
River and caused six major fish kills (of over 228,837 fish) between July 1977 and June 1981. The
1977 fish kill prompted SWCB to begin enforcement activities on the site. In September 1977,
SWCB ordered U.S. Titanium to pay for the fish kill and submit a plan to dispose of the waste
copperas. Although the company paid for the fish, it did not provide the requested disposal plan.
During deliberations with the company, another serious fish kill occurred in August 1979, which
prompted SWCB to request the Circuit Court of Nelson County to order U.S. Titanium to bury the
copperas by December 31, 1980. In response to the court order, U.S. Titanium contracted with New
Enterprise Construction Co., to dispose of the copperas waste from Area 2. The waste was buried in
a clay-lined, capped, burial pit, now referred to as Area 1. Burial was completed on December 12,
1980 (Reference 5, page 2; Reference I, page 8).
After several site inspections and assessments by EPA, the site was listed on the NPL in September
1983. Following a civil action by the Commonwealth of Virginia against American Cyan2mid and
others for damages caused by the site, American Cyananiid was found liable for the damages.
American Cyanamid signed a stipulation and order with the State establishing a schedule for
completion of a temporary source control action, a Supplemental Remedial Investigation, and a
Feasibility Study for the site. A Record of Decision (ROD), developed in accordance with
Comprehensive Environmental Response, Compensation, and Liability Act, was signed by the Region
111 Administrator and concurred by the Commonwealth of Virginia in November 1989. The ROD
estimated a treatment cost of $5,895,000 (Reference 2, Volume 1, pages 4 through 8; Reference 1,
pages 8 and 9).
2
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FIGURE 1. MAP OF U.S. TITANIUM SITE
S uri.e: Reference I, page 7
2.
:1
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U.S. Titanium Superfund Site
TABLE 1. BRIEF SUMMARY OF THE AREAS OF CONCERN FOR
SUPERFUND REMEDIAL ACTIONS
NPL Area of
Concern
Description
Area I
Clay-lined, capped, burial pit where copperas from Area 2 was landfilled in
1980. Area 1 encompasses about 2 acres and contains about 16,000 cubic yards
of copperas.
Area 2
Former Copperas Stockpile, located on the slope east of Area 3. Area 2 covers
approximately 8 acres. Copperas from manufacturing operations was deposited
here from 1949 to 1971.
Area 3
Contains the Evaporation Pond operated from 1974 to 1980. The Pond covered
about 2 acres and was part of the system to prevent discharges to the Piney
River under a State No-Discharge Certificate.
Area 4
Unreacted Ore-waste Pile. The Pile is about 1 acre and consists of clean outs
from reactor vats used in the titanium dioxide process and dredge materials
from the Sedimentation Ponds in Area 5.
Area 5
Contains 2 Sedimentation Ponds used to remove settleable solids from plant
wastewater prior to discharge to the River. The approximately 7-acre area lies
in the 100-year floodplain of the Piney River.
Area 6
Settling Pond used to recover phosphate ore, a by-product from titanium dioxide
production._The_Pond covers about 1 acre.
Area 7
Drainage area receiving most of the surface-water runoff from the site and flow
from the tributaries. The area covers about 1 acre and lies within the 100-year
floodplain of the Piney River.
Source: Reference 1, page 5
OPERATING HISTORY
The Piney River plant began operations in 1931 under the ownership of the Virginia Chemical
Corporation. Operations at the site by Virginia Chemical included the production of titanium dioxide
pigment from native ilmemte ore (using the sulfate process) and production of phosphate through the
digestion of native apatite ore with sulfuric acid (Reference 2, Volume 1, page 3). Titanium ore for
the titanium dioxide production was obtained from mining operations directly south of the Piney River
(Reference 1, page 8). The source of the apatite ore for phosphate production was not specified in
the references. The wastestream resulting from these early operations at the site consisted of spent
4
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Mining Waste NPL Site Summary Report
sulfuric acid, hydrated ferrous sulfate (copperas), diatomaceous earth filter cake, gypsum (from the
phosphate process only), and unreacted apatite and titanium ore. From 1931 to 1944, this
wastestream was discharged directly to the Piney River (Reference 2, Volume 1, page 3).
American Cyanamid Company purchased the site from Virginia Chemical in 1944. American
Cyanaxnid discontinued phosphate production and operated the facility for titanium dioxide production
only; wastestreazns were still discharged directly to the Piney River. Beginning in 1947, American
Cyanamid constructed a State-permitted Settling Pond to remove settleable solids from the
wastewater. This Settling Pond is now referred to as Area 5. In the early 1950’s, the company
employed partial neutralization of the wastewater; and by 1955, it had eliminated suspended solids
from the effluent and had significantly reduced sulfuric acid discharges. A Neutralization Lagoon was
installed and became operational in 1957. By 1961, wastewater was being neutralized to a pH of at
least 5; flow- and pH-monitoring equipment had been installed on the effluent stream; and a sulfuric
acid recovery plant was being operated continuously (Reference 2, Volume 1, pages 3 arid 4).
American Cyanamid ceased all operations in 1971. At the time of closure, American Cyanamid
undertook a study to determine what could be done to reduce the acidic discharges from the Copperas
Stockpile which had accumulated between 1949 and 1971 (approximately 80,000 cubic yards of the
material had been stored for sale as a commercial product). The area where the copperas had been
stored is now referred to as Area 2. The SWCB approved American Cyanantid’s plans for the
excavation and subsequent burial of the copperas in a clay-lined landfill on the south side of the Piney
River on April 5, 1973 (Reference 2, Volume 1, page 4).
Prior to plan implementation, however, American Cyanainid sold the site to Mr. S. Vance Wilkins (in
1973) with the stipulation that he complete its plan (American Cyanamid paid him $100,000 as part of
the sales agreement to do this). Rather than implement American Cyanamid’s plan, Mr. Wilkins
opted to install a temporary copperas leachate-collection and recirculation system consisting of a lower
collection lagoon located in the southern portion of what is now referred to as Area 2; an upper
Evaporation Pond in an area now referred to as Area 3; and a pumping system for transferring the
leachate from the lower Collection Pond to the Evaporation Pond. The leachate-collection and
recirculation system installed by Mr. Wilkins was granted a 3-year State No-Discharge Certificate
(No. IW-ND-407) on December 23, 1974. Mr. Wilkins never implemented the State-approved plan
for burial (Reference 2, Volume 2, page 7).
Mr. Wilkins sold the site to U.S. Titanium Corporation in March 1976. U.S. Titanium failed to
operate and maintain the leachate-collection and recirculation system installed by Mr. Wilkins. This
failure resulted in the first of six major fish kills, in 1977 (Reference 1, pages 1 and 2). The failure
of U.S. Titanium to maintain this “no-discharge ’s system led SWCB to take enforcement actions
S
½
I i j 5
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U.S. Titanium Superfund Site
against the facility, as described above. In summary, the State ordered U.S. Titanium to develop a
disposal plan for the copperas. Actual burial of the copperas (as defined in the plan) began on
October 2, 1980, and was completed by December 12, 1980. Final grading, channel improvements,
and seeding and mulching were completed by January 16, 1981. (This disposal area is now referred
to as Area 1) (Reference 2, Volume 2, page 8).
Concurrent with the copperas burial, EPA began preliminary investigations of the site. These
ultimately resulted in the placement of the site on the NPL in December 1982.
SITE CHARACTERIZATION
The site is located in the Piedmont physiographic province, about 5 miles east of the Virginia Blue
Ridge Mountains. The elevation ranges from 618 feet in the Piney River near the drainage area
(Area 7) to 726 feet on top of the copperas burial pit in Area 1. The bedrock under the site is
igneous and metamorphic. Two distinct sets of nearly vertical fractures are present in the bedrock
and have approximately northwest-southeast and northeast-southwest orientations (Reference 2,
Volume 2, pages 42 through 46; Reference 1, page 12).
Characterization of Contamination
NUS Corporation, under contract with EPA, prepared a Site Inspection Report of the U.S. Titanium
site, dated July 27, 1983. NUS used available sampling and monitoring data as the basis for its
conclusions. An initial Toxicological Impact Assessment (January 1983) of the site was based on data
collected by EPA Region III (Central Regional Lab) on August 4, 1982, and data collected by SWCB
on January 7, 1982. The conclusions reached in the early assessment were later confirmed by
additional sampling and analysis performed by Ecology and Environment cm November 1982) Both
of these investigations indicated the following: (1) high concentrations of toxic metals in leachate
(arsenic, cadmium, chromium, lead, and nickel); (2) high sulfate and low pH in surface waters
originating from the site; (3) contamination of ground water with metals, sulfate, and high acidity;
and (4) probable (but undetermined) impacts on the nearby Piney River (Reference 3, page 1;
Reference 4, pages 1-1 through 1-2).
EPA and the State considered these Site Inspections and other data (e.g., the Supplemental Remedial
Investigation) when compiling the October 1989 ROD. In the ROD, they concluded that problems
from the site were associated with acidified soils throughout the site and the buried copperas, both
resulting from the titanium dioxide operation; no conclusions were made about damages from the
phosphate operation. Leaching of these areas caused high levels of iron and acidity and metal
6
4 ,
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Mining Waste NPL Site Summary Report
contamination (aluminum, cadmium, chromium, copper, nickel, and zinc) in ground and surface
waters. These reported levels of contamination in both media violated surface-water criteria (see
Table 2) (Reference 1, page 13). Table 3 provides a description of the acid-related problems at the
site.
Two soil groups exist at the site, one associated with the more upland areas, and the other
characteristic of the floodplain. In the upland areas, the site is underlain by a soil of residuum
(saprolite) derived from the weathering of the underlying parent bedrock material. It is composed
primarily of clay and silty clay of the Cullen Association. The soils of the floodplain are
heterogeneous alluvial deposits of gravel, sand, silt, and clay. The approximate boundary between
the saprolite and alluvial soils lies along the base of the hill where Areas 1, 2, and 3 are located
(Reference 1, page 12; Reference 2, Volume 2, page 34).
Soil surveys conducted as part of the 1983 Site Inspection indicated that, “in most cases soil metals
were elevated but generally unremarkable.” The highest metal concentrations found at the site
occurred in samples collected from the copperas pile, which revealed very high levels of iron —
nearly 50 percent by weight, or 496,000 milligrams per kilogram (mg/kg) (Reference 3, page 3).
Metals that warrant toxicological concern were not detected in soil samples at unusually high levels.
Lead, for example, was detected in one sample at a concentration of 190 mg/kg. The Site
Investigation stated that lead occurs in all soils with a mean total concentration of 15 mg/kg and a
range of from 2 to 200 mg/kg. Similarly, levels of arsenic, chromium, and other metals were found
in some soil samples at the high end of the range normally found in uncontaminated soils (Reference
3, page 3).
Soil acidity at the site is a problem, however. Soil samples taken from the Copperas Pile and a soil
sample taken from the eroded face of the treatment lagoon demonstrated very acidic solutions,
ranging in pH from 2.6 to 3.6, when diluted with distilled water. Leaching or percolation of runoff
into these soils, which are rich in ferrous salts (iron content ranged from 320,000 to 496,000 mg/kg),
results in unusually high acidity, as is evidenced by the low pH of several surface- and ground-water
samples from the site. High acidity, in turn, results in dramatic increases in the solubiities of most
metals in water. This increased leaching potential also is reflected in several of the aqueous samples
examined (Reference 3, page 3). The data presented in the ROD further demonstrated that leaching
and runoff from the site affects ground- and surface-water quality in the area, as levels of pH and
certain metals in both media were in violation of established water-quality criteria (see Table 2).
Table 3, provides additional information on the acidity problems of the site (Reference 1, page 14).
7-
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U.S. Titanium Superfund Site
TABLE 2. MEAN CONTAMINANT CONCENTRATIONS IN SURFACE-WATER
DISCHARGE AND GROUND WATER AT THE U.S. TITANIUM SITE
UNITh [ in milligrams per liter (mg/l)J
Contaminants
Surface-water
Discharge’
Ground Water 2
Surface-water
Criteria 3
Aluminum
200
200
0.087’
Arsenic
<0.01
0.028
0.190
Cadmium
0.013
0.047
0.0003
Chromium
0.355
0.084
.0116
Copper
1.355
0.45
0.0025
Nickel
0.692
2.67
0.023
Zinc
1.56
19.27
0.047
Iron
267
698
1.0
pH
2.4
3.1
6to9
Acidity
1,446
2,090
—
‘Report by J. Novak, Virginia Tech; 1984.
2 Morris, Ph.D. Th is, Virginia Tech; 1984.
3 Virginia Water Control Board.
‘EPA Ambient Water Quality Criteria; 1988.
5 NUS; 1983.
‘Cr(V1) (total recovery).
Source: Reference 1, page 14
(9
8
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Mining Waste NPL Site Summary Report
TABLE 3. ACID-RELATED PROBLEMS AT THE U.S. TITANIUM S1T
NPL Area of
Concern
Acid-Related Probleais
Area 1
The cap system on the burial pit has not functioned properly, allowing water to
infiltrate the unit. The resultant acidic and high-iron leachate has acidified soils
under the pit and contaminated ground water. This area causes about 65
percent of the total acidic discharge at the site. Ground-water samples
downgradient of the pit have had a pH as low as 3.66 and concentrations of iron
up to 2,190 mg/I.
Area 2
The soil under the former Copperas Stockpile is acidified, and ground-water
seepages at the base of the slope have shown a pH as low as 2.66 and a total
dissolved iron concentration of up to 17,720 mg/I. Total acid contribution from
the area is 11 percent.
Area 3
The soil under the former Evaporation Pond is acidified down to the water
table. The pH of ground water in the area is 3.32, with dissolved iron
measured at 4,360 mg/I. This area contributes about 7 percent of the total
acidity.
Area 4
The unreacted Ore-waste pile contains residual acidity from processing. The
soil beneath this area also is acidified (levels were not given). The area
contributes about 4 percent of the total acidity.
Area 5
The two Sedimentation Ponds in this area contain residual acidity from
processing. Storm-water runoff from this area has caused a lowering of pH in
the Piney River. Ground water flowing through this area also becomes
acidified. pH readings from wells in the area have been as low as 3.42, with
total dissolved iron concentrations of up 1,840 mg/I. This area contributes
about 12 percent of the site’s total acidity.
Area 6
This area has no detectable acidity or copperas problems.
Area 7
The soil under this Drainage Area has become acidified. A well downgradient
of the area showed a pH as low as 3.09 and total dissolved iron of up to 570
mg/I. The area contributes about 1 percent of the site’s total acidity.
Source: Reference 1, pages 12 and 13
( 9
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U.S. Titanium Superfund Site
Ground Water
The hydrogeology at the site is typical of the Piedmont of Virginia. Ground water primarily occurs
in the porous, unconsolidated material of the saprolite and, to a much lesser extent, in the fractures
that run through the igneous and metamorphic bedrock. These two units are hydraulically connected
over large distances, although local heterogeneities such as changes in clay content of the saprolite
across a bedrock contact may produce local, partially confined conditions in the bedrock (Reference
2, Volume 2, page 49).
The depth to ground water is about 44 feet on the south side of Area 1. Downhill from Area I, the
water table becomes shallower, intersecting ground surface in the streambeds and springs along the
base of the hill (Reference 1, page 12). Ground water eventually discharges into the Piney River
either directly or via tributaries along the base of the hill containing Areas 1,2, and 3. Observations
during dry periods when the water table is low showed that ground water stopped discharging into the
tributary along the southern base of Areas 1 and 3. During the same dry periods, the stream along
the base of Area 2 continued to receive ground-water discharge, albeit at a much lower rate
(Reference 2, Volume 2, page 59). Ground-water flow within the site originates in the upland area
where Areas 1 and 3 are located and flows in a radial pattern downhill toward the streams
surrounding the base of the hill and to the Piney River (Reference 1, page 12).
Analyses of samples from onsite monitoring wells revealed significantly reduced and variable pH
values which ranged between slightly over 6 (in the deeper wells) to 2.5 (in the shallow and most
contaminated well). Wells dowugradient of the former Copperas Pile Storage Area (Well 7) and
Burial Pit and Settling Pond (Wells 1, 2, and 6) revealed the following:
• Very high concentrations of certain metals [ iron up to 5,570,000 micrograms per liter (gigll),
nickel up to 6,300 gig/I, manganese up to 1,000,000 gig/I, zinc up to 12,000 gig/I]
• Concentrations of other toxic metals (arsenic, chromium, lead, selenium, and thallium) several
times greater than National Interim Primary Maximum Contaminant Levels or Ambient Water
Quality Criteria
• Enormous amouhts of sulfate (up to 18,092,000 gig/I or 1.8 percent in Well 7) (Reference 3,
page 7).
Tabular results of the ground-water monitoring and analysis are presented in Table 4. The locations
of sampling sites are given in Figure 2.
10
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TABLE 4. GROUND-WATER MONiTORING DATA FOR TIlE U.S. TITANIUM SITE’
2.
C ,,
I-
i ’D
In
I
—
—
Parameter
Sample
Da te 3
(Dr. Smith)
UST-RI
(Mrs. ililbish)
UST-R2
UST-W5
or
Well #5
UST-W8
or
Well #8
Well NI
3.6
or
Well #2
41
or
Well #6
46
or
Well #7
25
pH
1/7/82
8/4/82
----
----
- ---
--- -
60
6 35
(62)
6 05
----
4 45
(4 3)
3 4
— (3 7)
2,279
2 8
(2 6)
18,092
Sulfates 2
(mg/I SO 4 )
1/7/82
8/4/82
----
—__ —--
-- --
< 5
12 8
< 5
2,223
< 25
15,000
----
200
> 2,500
31
> 2,500
I
> 2,500
10
As (jig/I)
1/7/82
8/4/82
< 5
< 5
I
< 5
3
< 5
----
160
39 ppb
80
37
191
52
----
Cd (jig/I)
1/7/82
8/4/82
----
< 10
—-
< 10
4
< tO
2
60
----
320
190
200
120
1l70 1
65
530
Cr (jig/I)
1/7/82
8/4/82
----
—_< 10
-- --
< 10’
20
< 10
200
< 10
20
----
100
35 ppb
370
75
[ 2001
280
1,500
Cu (jig/I)
1/7/82
8/4/82
----
- -- .
— - -
65
< 10
< 10
20
2.7
----
3000
150
3.7
3,100
[ II]
600
——
Fe(jtg/I)
1/7/82
----
----
15
2
5,570
1781
200
Pb (jig/I)
1/7/82
8/4/82
—--
< 5
—-
< 5
2
< 5
2
110
----
200
1000
120
467
I SO
[ 191
100
119
Mn (pg/I)
1/7/82
-- --
- ---
.13 —
32 —
4,600
[ 3901
2,800
Ni (jig/I)
1/7/82
8/4/82
----
—_<_20
----
< 20
10
< 20
70
< 20
----
----
----
6,300
1,700
3,800
[ I,400j
2,300
5,900
Zn (jig/I)
1/7/82
8/4/82
----
760
—--
130
730
50
2,100
12,000
----
— 3,800
3,800
4,900 -
1 Dath 1mm samples collected aflcr well systems were purged
2 Notc that the conccntiallOfli of sulfates, iron, and manganese am in mg/I
3 VsJues shown (or Januasy 7, 1982 were samples collected and analyzcd by Virginia SWCB
Results of pit paper calibration of ph meter suspect
(I Results of samples collected before purging, no sample collected afler purging
0 Values determined in laboratory Ii days beyond allowable holding time
Source Reference 4, page 101288
-------
‘ 1.EACIIATE St:FPS
PLATE (I
SKETCh MAP OF
SAMPLING POINTS
?. CROSS-SECTIONS
I
to SCALI
I i
“2
‘3
0
I
cRo 1nwATe:II 5MIPLI$1G POur
- SURFI%C WMFR SNIPLIIIG P0
(I)
I
0
0
FIGURE 2. GROUND-WATER AND SURFACE-WATER SAMPLING LOCATIONS
Source: Reference 4, page 101295
-------
Mining Waste NPL Site Summary Report
Data summarized in the ROD supported the above findings by also showing a low mean pH (3.1) in
ground-water samples and elevated concentrations of certain metals. The data from the ROD were
presented in this report as Table 2 (Reference I, page 14).
The two closest, private drinking-water wells also were sampled for the Site Investigation. However,
both wells are hydraulically upgradient of the U.S. Titanium site, and the parameters tested (mostly
inorganic) were present at low levels or were not detected. Other wells also are hydrologically
isolated from the U.S. Titanium site; therefore, the investigation concluded that no drinking-water
wells appear to be in any imminent danger of contamination (Reference 3, page 7).
Surface Water
The U.S. Titanium site lies within the Piney River Drainage Basin, which is part of the larger James
River Drainage Basin. The Piney River flows in an easterly direction, forming the southern boundary
of the site. Areas 1, 2, 3, and 4 lie on the upland area, while Areas 5, 6, and 7 lie within the
floodplain of the Piney River.
Surface water runs off the site primarily via a drainage channel along the bottom of Area 2 and a
small stream that originates along the western side of Area 1. These two channels merge south of
Area 2 and discharge into the Piney River through a culvert at the downstream end of the property.
A third stream originates to the west of the Sedimentation Ponds in Area 5, flows through the
Sedimentation Ponds, and discharges into the Piney River through a breach in the dike at the
southeastern end of the Sedimentation Pond (Reference 2, Volume 2, page 61).
As discussed previously, runoff from the site resulted in six fish kills from 1971 to 1981. In June
1982, remedial measures were taken to improve conditions at the former Copperas Storage Area
(Area 2) and the final Disposal Area (Area 1). The available documentation for the site states that no
fish kills have occurred since these improvements.
Sampling and analysis conducted for the Site Investigation prior to the June remediation demonstrated
the effects of the site on Piney River water quality. The results of these analyses are presented in
Table 5. Figure 2 pro iides a map of sampling locations. A comparison of upstream and downstream
locations shows an increase in metal concentrations at the downstream location (iron increases from
10 igfl upstream to 510 ig/l downstream; manganese increases from 10 to 130 g g/l; chromium
increases from 10 to 40 ig/1; sulfates increase from 1,900 to 13,800 ig/1; and pH falls from 6.7 to
5.1) (Reference 3, page 5; Reference 4, pages 101287 and 101295).
13-
-------
TABLE 5. SURFACE-WATER MONITORING DATA FOR TIlE U.S. TITANIUM SITE
:1
I
C , )
Parameter
Stations
19 UST-LI
. 1
5
6
7
9
o
18
51
66
—--
29
pH
67
3.0
30
30
30
29
AIk133
—-
—
AIk./AcId
(mg/I calcium
carbonate)
I2/5
Acid/745
Acid/700
Acid/I,270
Acid/I,445
Acid/I ,755
4/22
21 4
-- --
—
Sulfate (mg/I)
I 9
1.658 5
1,459.4
1,813.6
2,240 5
2,7007
13
00-
0001-
052
0042
As(mg/I)
0001-
—
0.073
001-
0.15
0 001-
0 001 -
0 91
0 024
Cd (mg/I)
0001 -
----
0.004
0 003
0004
0008
0 04
001 -
2 7
0085
Cr (mg/I)
0 01 -
—
0 II
0 14
0 08
0 09
001-
001-
39
0110
Cu (mg/I)
001-
--—
0.15
019
008
0.11
051
33
----
——
Fe(mg/I)
001
—
100
230
320
410
002
0.002 -
0 97
0 070
Pb (mg/I)
0 002 -
— - —
0 002
0 I
0 I
0.1
-
-— -
15.5
92
Ni (mg/I)
-—
—
— -
----
----
----
570
--—
013
076
—--
—
Mn (mg/I)
001
— -
67
12
45
002
610
159
Zn (mg/I)
001-
--- -
0.11
0.97
II
14
Source. Reference 4, page 101287
-------
Mining Waste NPL Site Summary Report
Surface-water samples taken in November 1982 suggest that a potentially serious leaching problem
may still exist, despite the remedial measures taken in June 1982. A surface-runoff sample, taken
from a culvert as it enters Piney River, revealed higb levels of iron (424,000 ig/l), manganese
(115,000 ig/l), zinc (2,270 g/l), chromium (55 igIl), nickel (1,278 g/l), copper (170 ig/l), and
silver (24 &g/l). Another surface-water sample taken downstream of the site in November (the
location was not given) also demonstrated that the metals and related contaminants are adversely
affecting Piney River water quality through runoff or infiltration. The downstream sample showed
substantial increases in iron (from less than 50 g/l in the upstream sample to 5,960 g/l) and
manganese (from less than 10 to 390 igIl). The pH decreased from 6.6 to 5.5. Sulfate was not
measured (Reference 4, pages 4-1 and 4-2).
A sampling episode documented in the Supplemental Remedial Investigation also supports the
assertion that runoff from the site may still pose a threat to Piney River water quality. The pH
measurements before and after a “lights (intensity not measured) rain showed a drop in pH from 6.65
to 4.93 as a result of rain-induced site runoff (Reference 2, Volume 2, page 153).
The ROD also documented the contamination potential of the site, presenting data showing that the
acidic nature of the site has led to metal leaching. Data compiled by the State for the ROD showed
that concentrations of metals in surface water at the site exceed surface-water criteria (see Table 2).
The downstream extent of contamination was not well documented in the ROD, although the results
of SWCB sampling (the most recent sampling was in the fall of 1988) demonstrated that the aquatic
invertebrate community in the Piney River has not completely recovered, even at a distance of 3.5
miles downstream (Reference 1, page 15).
Fate and Transnort
Copperas is the primary source of acidity, dissolved iron, and sulfate in discharges from the site.
Copperas is not acidic, but subsequent to dissolution, it produces acidity as the result of a sequence of
reactions (that include oxidation of the ferrous iron to ferric iron and the hydrolysis of the ferric iron
to ferric oxyhydroxides). The net effect of these reactions is that for every mole of copperas
dissolved, 2 moles of excess hydrogen ion are produced, resulting in acidic leachate (Reference 2,
Volume 2, page 159). The highly soluble nature of copperas [ 15.65 grams per liter (gm/i) in cold
waterl inhibits its reprecipitation once it is dissolved by percolating water. After the copperas
leachate is formed in the Burial Pit (Area 1), the dissolved iron, sulfate, and acidity are transported
along two possible pathways. The first pathway is from the Burial Pit down to the water table and
hence with the ground water to points of discharge The second pathway is via surface-water runoff
from the Burial Pit and subsequently to the Piney River. In either case, the pathway taken by any
15
-------
U.S. Titanium Superfund Site
particular dissolved ion from the Burial Pit may involve both intermittent surface- and ground-water
transport (Reference 2, Volume 2, page 168).
In the past, runoff from the U.S. Titanium site (following an unusually heavy precipitation event)
resulted in fish kills in the Piney River that were attributed to a substantial influx of ferrous sulfate
and a reduction in pH. During periods of low precipitation, water enters streams primarily as
subsurface infiltration through granular or porous material. Low pH was noted in a downstream
sample during a time when no leachates were observed discharging into Piney River, possibly
reflecting the substantial contribution of affected ground waters to the River (Reference 3, page 8).
ENVIRONMENTAL DAMAGES AND RISKS
Initial interest in the site was prompted by the 1979 fish kill, although two previous and significant
fish kills also occurred (Reference 1, page 8). Table 6 is a summary of significant documented fish
kills.
TABLE 6. FISK KILLS IN PINEY RIVER
Date
Number of Fish Killed
July 1977
73,056
August 1977
8,940
August 1979
26,136
July 1980
53,980
May 1981
20,482
June 1981
46,243
Total
228,837
This initial interest led to a number of enforcement and legal actions, as documented earlier in this
report. Ultimately, the site was placed on the NPL in September 1983.
16
-------
Mining Waste NPL Site Summary Report
The area surrounding the site is populated by approximately 200 people, most of whom live within a
1-mile radius of the site. The closest residence is approximately 2,000 feet to the west of the site
along State Route 151, across from the former plant building site. The community uses ground water
for its potable water supply. However, the residential wells are hydrologically isolated from the
contaminated ground waxer found on the site. Residential wells to the north and west are upgradient
(ground-water flow is south-southeast), while wells south of the Piney River and east of the site are
hydraulically isolated by the ground-water discharge boundaries associated with the Piney River, and
the unnamed tributary on the eastern side of the boundary. No residential wells exist between the site
and the Piney River (Reference 2, Volume 2, page 31).
Surface-water drainage from the site flows south to the Piney River, which, in turn, flows
southeastward to the Tye River, and subsequently to the James River. The Piney River is not used
for a municipal water supply, but is used for recreation and fishing upstream of the site. The closest
diversion for drinking water is approximately 40 miles downstream on the James River, and is not
subject to adverse impacts from the site (Reference 2, Volume 2, page 32).
The results of the 1983 Site Investigation tend to support those of the Supplemental Remedial
Investigation, as it also concluded that, “ [ t]hreats of a direct nature to human health appear to be
minimal” (Reference 3, page 1).
The greatest impact of the site is the past and potential contamination of surface water. The elevated
levels of metals and acidity in the Piney River water resulting from the site can have toxic effects on
aquatic life. For example, the Site Investigation cited a study documenting the effects of low pH on
Fathead Minnows: a pH value of 6.6 was marginal for vital life functions, while a lower pH reduced
egg production and hatchabiity. At pH levels below 5.2, the fish exhibited abnormal behavior and
deformities. Reported pH levels on the Piney River downstream of the site averaged 5.1 (Reference
3, page 8). Also, the oxidation of large amounts of ferrous ions in water can deplete dissolved-
oxygen supplies. The oxidation process causes the precipitation of ferric hydroxide, which can settle
out of suspension and produce a choking sediment layer on the River’s bottom. These two
phenomena (oxygen depletion and sedimentation) can also have deleterious affects on the River
ecology (Reference 3, pages 8 and 9).
The precipitation of ferric hydroxide has been a problem in the Piney River, as summarized in the
ROD: “ [ tjhese [ ferric hydroxidej sediments are still present today and have disrupted the benthic
community in the river. This in turn has resulted m a decrease in the number and diversity of the
fish population in the river adjacent to and downstream of the site. Low pH discharges can be toxic
to aquatic organisms. Based on sampling as late as fall 1988, the SWCB has concluded that the
17
-------
U.S. Titanium Superfund Site
aquatic invertebrate community has not completely recovered in the Piney River even at a distance of
3.5 miles downstream” (Reference 1, page 15).
REMEDIAL ACTIONS AND COSTS
American Cyanamid began preliminary efforts to address water-quality problems from the site (in
1947) by installing a sedimentation pond to remove settleable solids from the wastewater. Subsequent
activities, completed by 1961, included neutralization of all wastewater to a pH of 5; installation of
flow and pH monitoring equipment on the effluent stream; and continuous operation of a sulfuric acid
recovery plant. American Cyanamid’s efforts focused on wastewater discharges. The site’s
subsequent owner, Vance Wilkins, began addressing the acidic4eachate problem associated with the
Copperas Stockpile by installing a temporary copperas leachate-collection and recirculation system
(permitted by the State on December 23, 1974). U.S. Titanium purchased the site from Mr. Wilkins
in March 1976. In September 1977, SWCB ordered U.S. Titanium to submit a plan for the disposal
of the copperas waste. After several delays and subsequent judicial proceedings, U.S. Titanium
completed burial of the copperas on December 12, 1980. Final grading, channel improvements, and
seeding and mulching were completed by January 16, 1981. Reclamation work and runoff control on
the former Copperas Stockpile area was contracted on May 27, 1982. The recent status of this
reclamation work was not provided in the available information (Reference 2, Volume 2, pages 5
through 9).
A 1979 fish kill spurred regulatory interest in the site. A number of ensuing enforcement and
regulatory activities resulted in the placement of the site on the NPL in September 1983. A ROD
describing the final EPA remedy at the site was completed and signed by the EPA Regional
Administrator and the Commonwealth of Virginia in November 1989. The primary goal of the
remedial action was to control risks posed by acidic discharge to ground water and the Piney River by
eliminating the sources of acidic discharge from the six areas of the site found to be major sources of
contamination. The final EPA remedy, as conveyed in the ROD, and the available cost data are
described in Table 7 (Reference 1, pages 16, 17, 30, and 31).
CURRENT STATUS
The ROD was signed in November 1989. According to EPA Region ifi, the Potentially Responsible
Party, EPA, and the Commonwealth of Virginia completed the negotiation of a Consent Decree for
implementation of the remedial design and remedial action in September 1990. The Consent Decree
was lodged in Federal Court on December 4, 1990, and entered on February 18, 1991. The Consent
1 W
-------
Mining Waste NFL Site Summary Report
Decree does not become effective, however, until the State dismisses a Nuisance Action it currently
has pending against American Cyanamid. This dismissal is expected in the near future.
TABLE 7. SELECTED EPA REMEDIAL ACTIONS FOR THE U.S. TITANiUM SITE
Treatment Component
Approximate Cost
Ground Water
Collection: Passive Collection System’
Treatment: Passive Treatment System 2
$173,000
$431,000
Area 1 - Dissolution and Treatment 3
$3,962,000
Area 2- Surface Repair of Unvegetated Areas
$147,000
Area 3- Improve Surface Drainage
$106,000
Area 4- Drainage Control and Revegetation
$202,000
Area 5- Drainage Control and Revegetanon
$874,000
Area6-NoAction
0
Area 7- Above-grade Dry Neutralization (in combination with wetland)
0
Total
$5,895,000
‘Ground water would be intercepted by a series of subsurface drains and/or trenches installed below
the water table along the base of the hill containing Areas 1, 2, 3, and 4 Gravity flow would feed
the collected water to the ground-water treatment system.
?The treatment system would include an oxidation/settling pond, a constructed wetland, and a
limestone neutralization bed. All residual wastes would undergo Extraction Procedure (EP) Toxicity
testing to determine their waste classification before disposal. Waste determined to be hazardous (as
per Resource Conservation and Recovery Act Subtitle C) would be managed accordingly.
‘According to EPA Region III, the major steps included in the ROD for this procedure are:
(1) dissolution of copperas inside the burial pit; (2) recovery of resulting leachate from the pit;
(3) complete treatment of the leachate using physical and chemical processes; and (4) sludge disposal.
An explanation of significant differences (dated September 26, 1990), allows for an alternate method
of dissolution to be considered during design. Steps 1 and 2 above may be substituted with:
(1) excavation of the soil and copperas mixture from the burial pit; and (2) dissolution of the copperas
from the soil.
19-
-------
U.S. Titanium Superfund Site
REFERENCES
1. Record of Decision, U.S. Titanium Superfund Site, Nelson County, Virginia; EPA; October
1989.
2. Supplemental Remedial Investigation, U.S. Titanium Site, Piney River, Virginia, 5 Volumes;
Prepared for American Cyanamid Company by Hydrosystezns, Inc.; September 17, 1987.
3. A Toxicological Impact Assessment of the U.S. Titanium Corporation Property; NUS
Corporation; January 6, 1983.
4. Site Inspection of U.S. Titanium; NUS Corporation; July 27, 1983.
5. Letter Concerning Status Report of the U.S. Titanium Mine Site; From R.V. Davis, SWCB, to J.
Kenneth Robinson, House of Representatives; August 26, 1980.
20
-------
Mining Waste NPL Site Summary Report
BIBLIOGRAPHY
Davis, R.V. (SWCB). Letter Concerning Status Report of the U.S. Titanium Mine Site to J. Kenneth
Robinson, House of Representatives. August 26, 1980.
Ecology and Environment. Field Investigations of Uncontrolled Hazardous Waste Sites:
A Preliminary Assessment of U.S. Titanium. Undated.
Hydrosystems, Inc. Feasibility Study, U.S. Titanium Site, Piney River, Virginia, 3 VoLumes.
November 10, 1988.
Johnson, E. (EPA). Hazard Ranking System Score Sheet. 1982.
McCarter (SAIC). Telephone Communication Concerning U.S. Titanium Superfund Site to Kim
Hummel, EPA. December 6, 1990.
NUS Corporation. A Toxicological Impact Assessment of the U.S. Titanium Corporation Property.
January 6, 1983.
NUS Corporation. Site Inspection of U.S. Titanium. July 27, 1983.
Prepared for American Cyanamid Company by Hydrosystems, Inc. Supplemental Remedial
Investigation, U.S. Titanium Site, Piney River, Virginia, 5 Volumes. September 17, 1987.
Sitler, Jeffrey A. (Hydrosystems, Inc., Executive Vice President). Letter and Attachment Concerning
U.S. Titanium Superfund Site to Dr. Tim Lange, Virginia Department of Waste Management.
July 18, 1989.
Virginia Department of Waste Management. U.S. Titanium Superfund Site, Nelson County,
Virginia, Record of Decision. October 1989.
21-
-------
U.S. Titanium Superfund Site Mining Waste NPL Site Summary Report
Reference 1
Excerpts From Record of Decision,
U.S. Titanium Superfund Site, Nelson County, Virginia;
EPA; October 1989
-------
RECORD OF DECISION
U. S. TITANIUM SUPERFUND SITE
NELSON COUNTY, VIRGINIA
PREPARED BY
VIRGINIA DEPARTMENT OF WASTE MANAGEMENT
OCTOBER, 1989
I l )
-------
n - I
5
DECISION SUMMARY
SITE NAME AND LOCATION
The U. S. Titanium Site is located at the southern border of Nelson County along the north bank
of the Piney River and east of Vlrgirua R0ut 151, ab .* 40 miles SOUth of Ch tesville in west central
Virginia The Center of the Site is located app ornately at longitUde 790 01’ Q0 ’ W and latitude 370
42’ 30” North. The site es just ea the ru comrnun*y of Piney River. Virginia Figure 1 slows
the general location of the site On the USGS Piney RIver 7.5’ quadrangle topographic map.
The U. S. Titanium site lies on 175 acreS of a former titanium dioxide manufactunng plant
Superfund remedlel elTOI ate cOfl Oifl5d with ap 1fl ately 50 acres of the site. This acreage
contains seven separate and diedn areas which were Identified as possible sources of contamination
and are descnbed below. A site map is sh n in Figure 2.
Areal a clay lined. c’aY capped burial pit where copperas (ferrous sulfate) from Area 2 was
ianctiiUed in 1980. It encompeeses app din & P two acres and conta.ns about 16,000 cubic
yards c i copper -
Area2 is the fanner copperas stockpile area located on the slops eaat of Area a it covers
approximately elgll wee. Coppers. from rnwiii urlflg operations was deposited here from
1949 to 1971. The copperas was burled in Ares 1 in 1980.
/ s coritaine the e apuat1on pond operated between 1974 end 1980 and is located
‘I between Area I and Ares 2. ThIs pond, which covered about two acres, was part ci a system
to prevent discharges tO the Piney River operated under a No.Otscha’gS Certificate issued by
the Vkginls Water Corwol Board ( iWC8). Suiface water n.m-d! and some groundwater
discharges were oollecla’d ins containment pond aid pumped up to the evaporation pond.
AreaA is an urve sd ore pile located sotali of Ares 2. ii covers about one acre and
consists of cl i .oIfl from re ’1 v used in th titaten I6 4di procees and dredged
material from the sedimeu on ponds i i Moe 5.
c 4aIas two asdiniertedon ponds located along the Ptnsy River used to remove
seffl.ale acids from pisi sr prior to dlsc*wge to the river. The ponds cover an area
of appnsdmatsly seven acres aid contain en &uisinely finegralned sediment composed of
unrewed ore, filter cal* end gypsian. This ass N wat*t the 100.yeer floodplain of the Piney
River.
Area 6 contalnm a s ng pond used to recover phosphate or a by-produ from titanium
d1o cIdi prodi chon. it covers about one acre aid is located north of Ares 5.
Aretl is the draEii e asS receiving moat of the saiface water rtm . ci from the site and the
fl from ülbiitaiee . This was is locwad in aoL8he corilir of the alte aid covers about
one we. This area wat*i the i00 .ys floodp of the Plney River.
-------
Figur. 1: LoGetlon M for the U. S. llt*im S
ii Ns on Cour*y, Virgina.
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-------
8
gHISTOPY AND ENFORCEMENT ACTMTIES
In I 931, the Virginia Chemical Corporation began producing titanium dioxide from ulmenite ore
using the sulfate process at the site. The ore was obtained from mining operations directly south of
the Piney River. In the sulfate process the dmenhte ore is treated with sulfuric acid to dissolve the
ttann m dioxide product, waste streams from this process include acid contaminated unreacted ore.
spent sutfunc acid, and saud ferrous sulfate, called ‘copperas.’
In July 1944 American Cyanattiid Corporation purchased the Virginia Chemical Corporation and
operated the plant until It closed in June 1971. FollowIng the plant closure, the site passed through
vanous ownerships including the U.S. Titanium Corporation from which the site received its name.
Six maior fish kills occurred in the Piney River between 1977 and 1981, as documented by the
WJCB, which were attributed to contamination from the sits:
DATE NUMBER OF FiSH Ku fl
July 1977 73.056
August 1977 9,940
August 1979 26,136
July 1980 53,980
May 1981 20.482
June 1981
TOTAL flB,837
The 1919 fish kill prompted the WICB to reque the Circuit Count at Nelson County to order
U. S. Titanium to bury the copperas by December 31, 1980. In response to the court order,, U S
Titanium Corporation contacted New Ezlerpdse Construction Co. to depose at the copperas waste
The copperse waste from the storags p s (Area 2) wee collected and then bulled iri Area 1.
Under cor*rect wst’i EPA, Ecology aid Enwirorunirl submdlsd a Prwinilnwy Assessment report
of the site on Au t 3. 1980. The bur atCOPPer flAres I w completed on December 12, 1980.
A report at a screening Sits k p.ctlon conducted by EPA on August 3 .4 1982, wee released on
November 19, 1982. In DsoorubIr 1982, the U. S. Iltailum sits Wee proposed for indusson on the
National Priority List punsusi to SectIon 106(8) at CERCLA. The site w finally listed on the NPL in
September, 1983.
On Febn*y 1 and 2, 1983, NUS Corporation,- under contract with EPA conducted a site
inspection as pat at a Remedial ActIon Master Plan which wee released In August, 1983. GCA
CorporatIor under corsiact with EPA also conducted a Focut.d Feasibility Study on the nature and
extent at the acdc dlschergSS from the site and svWu d alternative ren dlal actions. The report was
released by EPA on October 9, 1985
Following a cM action filled by the CommQr alth at Vk nla against American Cyanamid
Company and others In Slate Court, based on a n saice action for fish kills and environmental
degradation resulting from the site, a NabIHty judgemert wee rendered against American Cyanamid on
November 7, 1985.
On Apr11 30, 1989, the Attorney General for the Commonwealth at Virginia and American
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9
CyanaIThd Company signed a St1pU O’ Wid Order estab IShiflg a schedule for completion, by
Amencan Cyanamid Company, o( a temporaly source Control action for the copperas bunal pit, a
Supplemental Remedial lrwestig iOfl (SRI), and a Feasibility Study (PS) for the site. The SRI and FS
were conducted by HydrosyatemS under contr w Cyanamid Company and submitted in November
1988 and April 1989 respectively. The SRi characterized the nature and extent of contamination at the
site. The FS descnbed vanous cleanup technologies and how remedial aftemarves were developed,
screened, and evaluated based on these technologies.
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10
HK 1IJGHTS OF COMMUNITY PARTICIPATiON
while the U.S. Titanium site ie located in a predominantly rural area, there has been
considerable interest among residents since the late 1970 ’s, when fish kills began to occur. The local
Blue Ridge Chapter the Sierra Club was formed in response to site events. In addmon, the local
media have followed the site activities consistently.
The post-Rl/FS community participation actlvitles began m April, 1989, when a fact sheet
describing the Remedial I vestigation/Feasibdity Study was mailed to a hat residents, officials, and
media In add ltlOn,dltOIlllal meetings were held with local d lcsais and Sierra Club representatives on
May 18. The Community Relations Plan (CRP) was revised at this time, and a repositones for the
Administrative Record File and other information was established at the Nelson County Memorial Library
and the County MmjhstrislOfl difice. The Proposed Plan was formally released to the public on July
31. A notice announcing the availability the Proposed Plan, the public comment period, and the
Admnatratlve Record F e was published in the Ch j te vlIlç Daily Proa çss on July 31. The Wginia
Deparmierl Waste gemerit (VDWM) also cosponsored an informal woilcshop for Sierra Club
members and other interested citizens on July 31, to explain the Superfund process resources available
to the public, and oinhlne the Proposed Plan. -
The public comilierl period extended from July 31 through September 29, after a 304ay
extension was graled at the request Mnerlcan Cyanarnid. A public mesting was held on Au st
9, where VDWM and EPA representatives reviewed the Proposed Plan and Superfund public
paiticipatlon opportunities in defail The meeting l ed four and a hat houll, and the interest level of
the community was very higit A formal response to qtle8tIolll and commer pi.it forth during the
public meeting aid cornmerit period can be found in Pat Ill this document, the Responsiveness
Summary. Community paiticipatlon activities wifl coritinus through remedial design and remedial action.
A detailed oiMlns community relations activities undertaken with the U.S. Titanium site
community can be found in the Responsiveness Summay (Append A). All studies and documents
pertaining to this sits can be found in the AdrninsstratlvS Record Flies, upon which the decision for
cinoosu remedial altsm ss was based .
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12
i. ’- X’ii ; i I . t
Based on the findings of the SRI and previous site investigations, the following conclusions can
be made regarding the site, the types of contamination, and affected media.
The site is located in the Piedmont physlographic province, about five miles e of the Virginia
Blue Ridge. The elevation ranges from 726 feet on top of the copperas burial pit in Area 1 to 618 feet
in the Piney River near the drainage area (Area 7). T! ie bedrock underlying the site consists of igneous
and metamorphic rocks. Two d Inct sets of nearly vertical fractures are present in the bedrock and
have approximately northwest-southeast and northwest-southwest orientations.
Two sod groups aids at the site. In the upland areas, the soil is a residuum (saproMe) derived
from the weathering of the underlying parent bedrock material. It is composed predominantly of clays
and silts. Within the floodplain, the sod consists of heterogeneous alhMai deposits of gravel, sand, silt,
arid clay. In general, the soil depth decreases from near 60 feet at the top of the slope in Area 3, to
less than one foot near the stream at the base of Area 2.
Groundwater occurs primarily in the porous unconsolidated granular material of the saprolite
and, to a much lesser extere , in the fractures that run through the dense, hard igneous and
metamorphic bedrock These two units are hydraulically interconnected over larger distances. The
depth to water table is about 44 feet on the south side of Area 1. ComIng dawn the valley, the water
table becomes shallower, Intersecting ground surface in ths strewn beds and springs along the base
of the hilL Groundwater flow within the sate originates In the upland area containing Areas 1 and 3,
flows in a radiating pattern dawn bill toward the eams surrounding the base of the bill and to the
Piney River.
The site lies within the Piney River drainage basin, a part of the larger James River drainage
ba_silL Areas 5 through 7 lIe within the floodplain of the Piney River. Surface water drainage runs off
the site primarily via three drainage channels into the Pliley River.
In Area 1, the copperas burial pit, the cap system has not functioned properly allowing water
to infiltrate the pit. The resuftal acidic and high ion content leachats has acidified soils underneath
the pit and contaminated groundwater. Acidic seepages from the burial pit have killed trees and other
vegetation down-gradient from Area 1. This area accoui for about 65 percent of the total acidic
discharge at the site. Malysis of groundwater samples down-gradient of the burial pit have shown a
pH as low as 3.66, and concentrations of total dissolved ion of up to 2190 mg/I, sulfate of up to 14,000
mg/i, and acidity of up to 10,050 mg/I as calcium carbonate .
The sal under ths former copperas stockpli. area, Area 2. is acidified and groundwater
seepages at ths bass the slops have killed the grass stand and formed won sulfate deposits. The
acidic contribution from this area is 11 percent . Malyses of samples from seeps at the base of Area
2 have shown a pH as low as 2.66 and concentrations of total dissolved won of up to 17,720 mg/i,
sulfate of up to 45,000 mg/I, and acidity of up to 41,000 mg /I as calcium carbonate.
The sod under Area 3, the former evaporation pond, is acidified upto the water table. Total
acidic contribution from this area is about 7 percent . The most recent analysis of groundwater from
a well located w*hln Area 3 has shown a p11 of 3.32, and concentrations of total dissolved won of 4.360
mg/i, sulfate of 54,000 mg/I, and acidity of 40,500 mg/I as calcium carbonate.
Area 4, the unreacted ore waste pile area, contains residual acidity from processing. The soil
underneath this area is also acidified. Four percent of total acidity at the site is attributable to this area.
p .’
‘1
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13
Ares 5. whIch coritaine the two sedimentation ponds, contains residual acidity from processlng
During atorm ever U irosion of sediments by atorm run-off has resulted in a significant lowering c i’ thi
pM in the Pin Rivir. In addition, groundwater flowing through this ares is acidified by conta with
the a e prior to discharge tO the Pinsy River. Ares 5 accounts for 12 pircirt of the total acidity at
the ts Analysis of samples from well located on ths noflhsem edge of this area have shown a
pM as low a 3.42, and COflCirtatlOflS of total dissolved Won of up to 1.840 mg /I, sulfate of up to 5,400
mg/L andacdupto3. Q U1tbC
Ares 8, the s Mng pond used to rec er phosphate ore has no diteotable copperas or acidity
problem. There is also no groundwater contamination.
The soil under Ares?, the drainage ares receiving moat of the surface run-off from the site, has
become acidified aid cortilbiles abO(* one percent to total site acidity. Analysis of samples from a
wel down-gradient of Ares?, have shown $ pH U low 3.09. and concer*r*IonS of total dissolved iron
of u p t o570rflG 1 ,$U i fW 5O i ’ up 2 400 mg/ aid acidity of up to 1,542 m calcium carbonate.
The acidic nature of the site his also led to the leaching of other metals such as aluminum,
copper, zinc, cadmium and nickel from on site soils. The concentration of these metals W surface
water and groundwater at the sits wiN as that of Won. erceed surface water criteria çrable 1)..
Figure 3 sh the percerltags cor*ilbt*lofl by ares to acidic cortaninetlon at the site
Area S • 0%
___ Ares 7
is
Area 5
12%
Area 4
Ares 3
7%
Figure 3: Cordrb.dlon by Ares T Mdc Cor minUIon
gtie U. S. martin aft..
• Area2
11%
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14
TABLE 1: MEAN CONCENTRAflON 81 SU ACE WATER OISCHAR &
GROUNDWATER AT ThE U. S. TITAMUM SiTE
Unts in mg/i
Suilace’ SurfaceC
Water Goundb Water
Contaminafl Discharce Water Cnterta
Al 200. 200. 0 • 087 d
As’ <0.01 0.028 0.190
Cd 0.013 0.047 0.0003
Cr 0.335 0.084 .011
Cu 1.355 0.45 0.0025
NI 0.692 2.67 0.028
Zn 1.56 19.27 0.047
Iron 267. 698. 1.0
pH 2.4 3.1 6 -9-
Acd 1446 2090
a Source: Reposi by J. P4ov c, V nla Tech (1984)
b Source: Mcrrt’ Ph.D. Thsil Vl i1i Tech (1984)
C. Source: VL IIIIa Water Cor*ri Boa’d
d. Source: USEPA M1b 1111 Water Qu ty Crtterla (1988)
a Source: NUS (1983)
1. Cr(Vl) itctal recovesy)
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15
SUMMARY OF SiTE RIS1
Without remedial action, the site wiU continue to contaminate groundwater and surface water
in the Piney River sub-basin. Acidified soils and buned copperaS wastes will continue to leach
contaminants into the groundwater. The dissolutiOn of copperas produces acidity as the result of a
sequence of reactions that include oxidation, of the ferrous iron to fernC iron, and hydrolysis of the fernc
iron to femc oxytiydroxide. The net effect at these reactions is that for evely mole of copperas
dissolved, two moles of excess hydrogen iron (H) are produced resulting in the acidic leachate.
Groundwater eventually discharges into the Piriey R er either directly or by way of two site tnbutaneS
Surface water run-off from the site erodes acidic sediments and discharges them into the river.
These discharges can contain high iron concentrations and have low pH values. The hugh iron
concentrations have resulted in the deposition of femc hydroxide sediments at the bottom of the river.
These sediments are still present today and have disrupted the benthic community in the river. This
in turn has resulted in a decrease in the number and diversity of the fish population in the river
adjacent tO and downstream of the sits. Low pH discharges can be toxic to aquatic organisms. Based -
on sampling as late as fall 1988 the State Water Control Board has concluded that the aquatic
inveitebrate community has not completely recovered In the Piney RIver even at a distance of 3.5 miles
downstream. -
Actual or threatened releases of pollutants from this site, if not addressed by implementing the
response action selected ui this ROD, may present substantial endangerment to aquatic I de in the Piney
River.
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16
SCRIFflON OF *L1 tA1WES
Several alternatives were evaluated in detail to determine which would be moat effective in
achieving the goals of CERCLA. and in particular. achieving the remedial oblective for the site. The
detailed analyses of remedial alternatives for the vanous areas of the site are briefly described below
NO ACT1ON
Capital Costs: $ 21.000’
Annual 0 & M: $156000’
FNe Year Review $133,000’
Months to Implement 3’
The Superfund program is required to evaluate the No Action’ aftern ve. Under this
alternative, no remedial on would be taken to prevent contarniflalOr’ from entering groundwater or
the Piney River. SIte access controls, deed restrictions. and maintenance of on site roads would be
performed. In addition monitoring of the groundwater and surface water would be performed along
with a formal review of the site condition every five years. ARMS associated with surface water ar
groundwater would nct be attained.
The remedial ob$ecdvee for the site would nct be met by the no action alternative and impacts
on the benthic community in the Piney River would continua The no action alternative does flOt meet
SARAs preference for permanent treatment.
GROUNDWATER COU.ECTION SYSTEM
Alternative GW-2, Passive Groundwater Collection
Capital Costs: $142,000’
Annual 0 & M Costs: $2,000’
Months to Implement 3’
Groundwater would be W*ercepted by a serlee of suba rfaCO drains aid/or trenches installed
below the wetir t lS ‘ong the bass of the h containing Areas 1,2,3. and 4. Gravity fiow would be
used to feed the callsctSd water to the groundwater veetineil system. Measures would be taken to
prevent the f uk11On of Won sa deposits in the collection system durtng periods of low flow
Uncontaminated suifacS water run-cl? would be diverted away from the collection system.
Groundwater would be collected fOr treatment until the groundwater qualhty achieves a level
which allows It to be dischaged directly into the Pinsy River. The discharge limits for this site
necessary to meet water quah y itaidards In the Piney River aid so comply with the Clean Water Act
(CWA) end Virginia Water Control Bøard (VWCB) regulations flayS been determined by VWCB and are
presented in Append I
AU costs and in plemerfladon times are estimated.
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17
GROUNDWATER TREATMENT SYSTEM
Altematwe WT-2 Passive Water Treatment
Capital Costs: $119,000’
Annual 0 & M Costs: $20000’
Months to Implemeft 6’
erns of the treatment system would include an oxidation/setthng pond, a
constructed wetland, and a limestone neutralization bed.
The o od losvsettllflg Pond would be capable of complete removal of iron and sulfur elements
from the collected groundwater. Its design would mlize ex lng knowledge of acid mine drainage
treatment where the use of oxidation/SettlIng ponds is a standard techniqua Such treatment systems
often utilize alkaline chemicals tO raise the pH of the water and cause metals to precipitate. The sulfur
element would also be precipitated. The oiodisiorv’satthflg pond would make up for any loss in the
performance of the wetland.
Wetland vegetation works in conjunction with anaerobic bacteria to remove iron and sulfur
species from the water wi increase in the pH can also be e,cpecled . The wetland would be protected
from a 100-year flood by constructing a berm around it.
Should the presence of cther metals in the aifluert from the wetland make the discharge
requirements set by the WJCB non-attainable aid thus prevent direct discharge intO the Piney River,
additional physical or/and chemical treatment steps would be installed.
The limestone bed would a a final polishing step for pH adji.istmeffl before discharge ol
the effluent to the Piney River.
An eight-foot high, locked chain-link fence would be installed around the wetland for the
protection of the community, on site workers, aid game and wild Routine maintenance of the entire
groundwater system would include restocldng of ths watlaid wIth n plaits, dredging of the oxidation
pond and wetlaid, periodic effluent and wdlueil monitoring. The monitoring program for groundwater
treatment is presented in Appendb L
All resit1 wastes would have to undergo Eatr lOfl Procedure Toxicity (EP Tax) testing to
determine they dau, 1GalOfl before dlapos W as that fail under RCR Subtitle C (Hazardous
Waste) would be managed scccrdlng to di. Virginia l 4azwdous W s Management Regulations
(VHWMR) and epØicablS RCRA Laid Diapoesi Restrictions (LDRs). W s that we classified as RCRA
Subtitle 0 (Sold W e) would be managed eccording to the W nha Sold w . Management
Regulations (VSWMR). The oxldatiQn/s 11flg pond, di. wetlaid aid the neutralization bed would be
constructed aid operated according to V)MMR or VSWMR (Including mir mum technology
requiremerds). The Cummonwsith of Vk 9 nla is a RCRA dslegat 4 State AU RCRA ai.ithosity has been
delegated to the Commonwealth of WginIa exce thou under the 1984 H dOUS and Solid Waste
Miendmerits Q -l$WA).
All costs and implementation times are estimated.
4)
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A
30
S cT Y
Based upon consideration of the requirements of CERCL.A the detailed analysis of trie
alternatives, and public comments, bcth EPA and the Commonwealth of Virginia have determined that
the following combination of alternatives is the moat appropnate remedy for cleaning up the site
ES MATED
TPEATh T O ON2ff COST
Groundwater
Collection: Passive Collection Syatem (GW.2) 173000
Treatment: Passive Treatment Syatem (WT-2) 431,000
Area 1: In-situ Dissolution and Treatment (Al-la) 3 .96Z000
Area 2: Surface Repair of Urwegetated Areas (A2.4) 147,000
Area 3: Improve Surface Drainage (A3-3) 106,000
Area 4: Drainage Control and Revegetatlon (A4-4) 2 ,000
Area 5: Drainage Control and Revegetatlon (A5-4) 874,000
Area6: NoActlon(A6-1) 0
Area 7: Above-grade Dry Neutralization (A7-7) 0
çui combination with wedan
TOTAL 5,895 000
The selected remedy cor ats of d ok1Ion aid ueanerl of copperas waate in Area 1
Drainage controls and revegetalon uld bs nplemerited in Areas 2,3.4 and 5 Area 6 requires no
remedial action . Aciddlsd sod i Area 7 would be musd w i lime to neutralize any leachate.
Groundwater would be colle ed by using subsurface dralns and trenches with tre ent in a
conatructed wederid . The wedand treesnent would be supplemented with active treatment processes
necessary to meet sat dlschergs requirumerss.
Some changes m be made to the selected remedy as a resu of the remedial design arid
con on p ae
Ren ediatIon Goals
The purpose of this response action is to control risics posed by acidic discharge into
groundwater and the Piney River. By eliminating moat of the sources of acidic discharge into the rrver.
the remedial action will prevent future fish kills and atop further leaching of metals and continued
degradation of the Piney River. This remedy will address all th sci areas of the site that have teen
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31
found to be the sources of contamination.
Since no Federal or State ARAR5 exist for soils, the action level for the in-situ dissolution and
leachate collection remedy for Area I would be ermined using fete and transport modeling to
determine the level 10 whiCh acidic producing potential of the sod should be reduced in order to ensure
that the leaching of contaminants to groundwater arid suitace aer above levels prot ive
Piney River es determined by the SWCB would not continua At a minimum, the leaching shail not
cause the Piney River to exceed State Water Quality Standarde.
The termination of in-situ dissolution and leachete collection would be determined using the
results of sod boring tests, and fete and transport modeling to estimate the potential of groundwater
contaminatiOn that could result from the migration of l ’GSIdIJ l coiiamniliwita in the soiL The leaching
process shall be stopped when (1) sod boring teats show that no signlllcarit amount of copperas
remsins in the pss, and (2) the residual acidity in the formation is such that if leached into groundwater
and discharged into the Piney River would not violate the ARARS for the river.
Discharge from Area I ulo the wetland would only be allowed when the water to be discharged
is comparable to the quality of ir luent water into the wetland and provided such additional discharge
capacity would not adversely affect the performance of the wetland. In any case, no discharge would
be allowed untd the dissolution process is near compleXfl. Any discharge into the Piney River must
meet the discharge limits set forth in Append L
All solid w es generated during the remedlatlon proces . would be subjected to EP To?
testing and then disposed of according to VI4WMR and RCRA-LDRS (FederaO or the VSWMR.
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U.S. Titanium Superfund Site Mining Waste NPL Site Summary Report
Reference 2
Excerpts From Supplemental Remedial Investigation,
U.S. Titanium Site, Piney River, Virginia, 5 Volumes;
Prepared for American Cyanamid Company by Hydrosystems, Inc.;
September 17, 1987
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VOLUME 1 OF 5
SUPPLEMENTAL REMEDIAL INVESTIGATION
U.S. TITANIUM SITE
PINEY RIVER, VIRGINIA
EXECUTIVE StTh ARY
SEPTEMBER 17, 1987
PREPARED FOR:
AMERICAN CYANAMID COMPANY
ONE CYANAMID PLAZA
WAYNE, NJ 07470
PREPARED BY:
HYDROSY5TEMS, INC.
P0 BOX 348
DUNN LORING, VA 22027
301026
J-tYDROSYSTEMS ..c____
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Volume 1
rI
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EXECUTIVE SU (ARY
1.0 PURPOSE
The purpose .of the supplemental Remedial Investigation (SRI) is
to augment the existing data base relating to the nature and
extent of the acidic discharges at the U.S. Titanium Site in
Piney River, Virginia (referred to as the “Site”).
Numerous data gaps were identified in previous studies. Several
of these data gaps were of major importance to the understanding
of the extent of the problem, while other data gaps were
important to the evaluation of alternative remedial actions.
The previous site investigations did not provide a comprehenSi\Le
investigation of the surface water and groundwater quality
impacts. No previous study was conducted to estimate the
relative contribution of each area to the contamination of
surface- and groundwater. The previous studies did not address
the pathways of contamination or the geochemical controls on
leachate production and migration.
The SRI is intended to supplement the previous studies by filling
gaps in the existing data base according to the following
objectives:
• Characterize the extent and nature of contamination in
each of the seven areas and groundwater.
• Characterize the hydrogeolOgy to provide data for
evaluation of the significance of the groundwater
contamination component to acidic discharges and for the
1. 301025
_______________HYDROS”SVS
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2.2 SITE HISTORY
The Piney River plant commenced operations in 1931 under the
ownership of-the virginia Chemical Corporation. Those operations
included: (1) the production of titanium dioxide pigment from
native ilmenite ore via the sulfate process and (2) production of
phosphate through the digestion of native apatite ore in sulfuric
acid. As a result of the titanium dioxide and phosphate
operations, the plant produced a waste stream consisting of
dilute sulfuric acid, hydrated ferrous sulfate (copperas),
diatomaceous earth filter cake, gypsum (from the phosphate
process only), and unreacted apatite and titanium ore. From
1931 until 1947, the wastewater stream was discharged directly
to the Piney River.
In July of 1944, American Cyanamid Company acquired the plant and
property. American Cyanamid Company operated the plant for the
production of titanium dioxide only.
In 1947, American Cyanamid Company constructed a State permitted
settling pond to remove settleabi. solids from the wastewater.
This settling pond is now referred to a. “Area 5.” In the early
1950’s, American Cyanamid Company employed partial neutralization
of the wa.te iter, and by 3.955 had eliminated suspended solids
from the effluent and had significantly reduced sulfuric acid
discharges. This wa, followed by the installation of a
neutralization lagoon which became operational in 1957.
By 1961, American Cyanamid Company had achieved the following
results:
3. 3O1O iO
- _______________________________________HYDAOSYSTEMS ____
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1. Al]. wastewater was neutralized to a pH of at least 5.0.
2. Flow and pH monitoring equipment were installed on the
effluent stream.
3. A sulfuric acid recovery plant was in continuous
operation to reduce sulfuric acid discharges.
In 1971, American Cyanamid Company ceased all operations at the
Piney River plant. Also in 1972, American Cyartamid Company
commissioned a study of the acidic discharges from the copperas
stockpile, where an estimated 80,000 cubic yards of copperas had
been stored between 1949 and 1971 for sale as a commercial
product. This area is new referred to as “Area 2”. The study
concluded that acidic discharges attributable to the copperas
could be eliminated by moving the copperas to a new clay-lined
landfill on the south side of the Piney River.
On October 31, 1972, American Cyanamid Company submitted plans to
the Stat. Water Control Board (SWCB) for excavation and
subsequent burial of the copp.ra. in a new landfill to be located
on the south side of the Piney River. Approval for this plan was
granted by the Executive Secretary of the SWCB on April 5, 1973.
In 1973, Mr. S. Vance Wilkins purchased the property from
American Cyanamid Company. As part of the sales agreement,
American cyanamid Company paid Mr. Wilkins $100,000 for the
stipulated purpos. of implementing the State—approved plan for
burial of the coppera. on the south side of the Piney River.
301031
4
____________________HYD OSYSEYS —
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Rather than implementing the State—approved plan developed by
American Cyanamid Company, Mr. Wilkins constructed a temporary
copperas leachate collection and recirculatjon system consisting
of a lower collection lagoon located in the southern portion of
what is now referred to as “Area 2”, an upper “evaporation” pond
in an area now referred to as “Area 3”, and a pumping system for
transferring the leachate from the lower collection pond to the
“evaporation” pond.
In March of 1976, Mr. Wilkins sold the Site to the U.S. Titanium
Corporation. U.S. Titanium Corporation’s purchase of the Site
was financed by The Stone Foundation, which held a mortgage on
the property. -
In September of 1977, the SWCB ordered U.S. Titanium Corporation
to submit a plan for disposal of the copperas. U.S. Titanium
Corporation failed to submit the required disposal plan, and the
SWCB filed suit in the Circuit Court of Nelson County seeking a
temporary injunction to require U.S. Titanium Corporation to
apply to the Stats Department of Health for a landfilling permit
for the copperas.
After further judicial proceedings, U.S. Titanium Corporation
and/or Th• Stone Foundation contracted with G.onics, Inc. to
prepare a p.rmit application for disposal of the coppera. • This
application was submitted to the SWCB and Stat. Department of
Health on October 3, 1979 and approved by that department on
March 11, 1980.
3O1O3’
5 _
HYDRQSYSTEMS ____
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On October 2, 1980, New Enterprise Construction Company began -
full—scale burial of the copperas under contract to U.S. Titanium
Corporation and/or The Stone Foundation. Burial was completed on
December 12,1980, and final grading, channel improvements, and
seeding and mulching were completed by January 16, 1981. The
burial area is now referred to as “Area 1”.
During the U.S. Titanium Corporation and/or The Stone Foundation
sponsored burial of the copperas, the U.S. Environmental
Protection Agency, Region III (EPA), contracted with Ecology and
Environment, Inc. to conduct a preliminary assessment of the U.S.
Titanium Site. The resulting report was submitted to the EPA on
August 3, 1980.
On April 7, 1982, the Executive Director of the SWCB disapproved
a site improvement plan for reclamation of the former copperas
storage area submitted by U.S. Titanium Corporation and/or The
Stone Foundation. As a result, Benton G. Tinder was appointed
receiver of the U.S. Titanium Corporation property at Piney
River. On May 27, 1982, Mr. Tinder contracted with R.M. Cash and
G. Burley of Amherst, Virginia, to complete reclamation and
runoff control for the former copperas stockpile area. This
reclamation work was funded from the Governor’s Contingency Fund.
In December 1982, the EPA ranked the U.S. Titanium Site 332nd out
of 418 sites on the National Priorities List published pursuant
to Section 105(8) (B) of CERCLA. On February 1 and 2, 1983, NUS
Corporation, under contract with the EPA, conducted a site
3O1O3
11, -
YDROS’ .S —
-------
- ‘ L.
inspection as part of the development of a Remedial Action Master
Plan (RAMP). The RAMP was released in August of 1983.
In June of .1983, the SWCE authorized the Department of Civil
Engineering, Virginia Polytechnic Institute and State University,
Blacksburg, Virginia, to conduct studies relating to the U.S.
Titanium Site.
In 1985, EPA contracted with GCA Corporation to conduct a focused
feasibility study (FFS) on the nature and extent of the acidic
discharges from several specific areas on the Site and to
evaluate alternative remedial actions. On October 8, 1985, the
EPA released a draft FFS prepared by GCA Corporation and dated
July 23, 1985. Comments on the draft FFS were submitted by
American Cyanamid Company on November 20, 1985.
On November 7, 1985, a liability judgment was rendered against
American Cyanainid Company, U.S. Titanium Corporation, Ronald
Penque and Henry A. Williams,III, principals of U.S. Titanium
Corporation, and Penque—Williams, Inc. in Commonwealth of
Virginia v. U.S. Titanium CorDoration. et al. , a nuisance action
seeking abatement of conditions at the site. In early 1986, the
U.S. Titanium Corporation transferred its Piney River property to
the P.R. Corporation of Piney River, Virginia. One of the
principals of .the P.R. Corporation is Mr. Robert Desmond.
On April 30, 1986, the Attorney General for the Commonwealth of
Virginia and American Cyanamid Company signed a Stipulation and
Order establishing a schedule for completion, by American
Cyanamid Company, of a temporary source control action for the
7 3O1o3 :
HYDRCSYS 4S
-------
copperas burial pit, a supplemental remedial investigation, and a
feasibility study for the Site.
On August 12, 1986, American Cyanamid Company, through a
contract with MYDROSYSTEMS, Inc. of Dunn Loring, Virginia,
completed a temporary source control remedial action at the
copperas burial pit to inhibit leachate production.
2.3 NATURE AND EXTENT OF PROBLEM
Conditions at the U.S. Titanium Site include the chronic
discharge of acidic surface— and groundwater into the Piney
River, the presence of a soil/copperas mixture in the burial pit,
and acidified soil and sediment in other areas of the Site. The
acidic groundwater and surface water do not contain hazardous
constituents and do not present any risk to human health. The
chronic acidic discharges to the Piney River have resulted in
impacts to the aquatic community immediately downstream of the
Site. Recent benthic surveys indicate, however, that the river
recovers below about 1,000 feet downstream and is showing signs
of recovery in the immediate vicinity of the Site.
Due to the inadequate burial of the copperas by the U.S. Titanium
Corporation in 1980, infiltrating water has dissolved copperas,
causing co1la se depressions to form in the surface of the burial
pit. The resulting leachate formed by the dissolution of the
copperas discharges to the surface via seeps around the
circumference of the burial pit and percolates to the
groundwater.
301035
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Volume 2
A 1
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Figure 1.].
Location sap for the U.S. Titanius site in
Piney River, Virginia.
4
1;
4
d1t 11-
. .J V I d
.HYDPCS VSMS
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hi a result of the titanium dioxide and phosphate operations, the
plant produced a waste stream consisting of dilute sulfuric acid,
hydrated ferrous sulfate (copperas), diatomaceous earth filter
(_ _ - ,1
cake, gypsum (from the phosphate process only), and unreacted
apatite and titanium ore. From 1931 until 1947, the wastewater
stream was discharged directly to the Piney River.
In 1947, American Cyanamid Company constructed a sedimentation
pond to remove settleable solids from the wastewater (NUS, 1983,
p. A-2). In April of 1947, the State Water Control Board (SWCB)
issued to American Cyanamid Company, pursuant to Section 1514-b17
of the State Water Control Law, Waste Discharge Certificate No.
34 for the Piney River plant effluent (NTJS, 1983, p. 2-7). This
sedimentation pond is now referred to as “Area 5”.
In the early 1950’s, American Cyanamid Company employed partial
neutralization of the wastewater, and by 1955 had eliminated
suspended solids from the effluent and reduced sulfuric acid
discharges from 120 tons/day to 90 tons/day (NtJS, 1983, p. 2-11).
This was followed by the installation of a neutralization lagoon
which became operational in 1957 (Nt IS, 1983, p. A5).
By 1961, American Cyanamid Company had achieved the following
results: -
1. All wastewater was neutralized to at least a pH of 5.
2. Flow and pH monitoring equipment were installed on the
effluent stream.
5 30107: ‘
________________HVOAOS —
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3. A sulfuric acid recovery plant was .n cont .nuo
operation to reduce sulfuric acid discharges. (NtJS,
1983, p. 2—12)
On March 21, 1961, the SWCB issued to American Cyanamid Company
Waste Discharge Certificate No. 1312 in replacement of
Certificate No. 34 for the Piney River plant effluent. Thi .s new
discharge certificate was issued to reflect improvements
instituted by American Cyanamid Company in the waste handling
operations. (NTJS, 1983, p. 2—8)
In 1971, American Cyanamid Company closed down all operations at
the Piney River plant. Also in 1971, American Cyanamid Company
commissioned a study of the acidic discharges from the copperas
stockpile where an estimated 80,000 cubic yards of copperas had
been stored between 1949 and 1971. for sale as a commercial
product (NTJS, 1983, pp. ES—i and 2-6). This area is now referred
to as “Area 2”.
The study, conducted by Geraghty & Miller, Inc., concluded that
acidic discharges attributabl, to the copperas could be
eliminated by moving th. copp.ras to a new clay-lined landfill on
the south aids of the Piney River (G.raghty & Miller, Inc.,
1972). -
On October 3.1, 1972, American Cyanamid Company submitted plans to
the SWCB for excavation and subsequent burial of the copperas in
a new landfill to be located on the south side of the Piney River
(NUS, 1983, P. 2—8). On April 5, 1973, American Cyanamid Company
obtained approval from the Executive Secretary of the SWCB for
117 6
1VDi CS”SEYS
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the plan to bury the copperas in the proposed new landfill (NtS,
1983, p. 2—8).
In 1973, Mr. S. Vance Wjlkj s purchased the property from
American Cyanamjd Company. As part of the sales agreeme ,
American Cyanamid Company paid Mr. Wilkins $100,000 for the
stipulated purpose of implementing the State—approved plan for
burial of the copperas on the south side of the Piney River (NTJs,
1983, p. 2—3).
Rather than implementing the plan developed by American Cyanamid,
Mr. Wilkins constructed a temporary copperas leachate collection
and recirculation system consisting of a lower collection lagoon
located in the southern portion of what is now referred to as
“Area 2”, an upper retention pond in an area now referred to as
“Area 3”, and a pumping system for transferring the leachate from
/
the lower collection pond to the upper retention pond. The SWCB
issued a three-year duration State No Discharge Certificate No.
Iw-ND-407 on December 23, 1974, to permit operation of the
leachate collection and recirculation system installed by Mr.
Wilkins (NUS 4 1983, p. 2-8 and personal communication with Tedd
Jett, SWCB).
In March of 1976, Mr. Wilkins sold a portion of th. property
north of th. Piney River to the U.S. Titanium Corporation,
retaining ownership of that part of the property on the south
side of the river and portions of the property on the north side.
U.S. Titanium Corporation’. purchase of the Piney River property
•301073
7
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was financed by The Stone Foundation, which held a mortgage or
the property.
In Septembe .of 1977, the SWCB ordered U.S. Titanium Corporatjor
to submit a plan for disposal of the copperas. U.S. Titani um
Corporation failed to submit the required disposal plans, and the
SWCB filed suit in the Circuit Court of Nelson County see)cing a
temporary injunction to require U.S. Titanium Corporation to
apply to the Stats Department of Health for a landfilling permit
for the copperas . (N t IS, 1983, p. 2—9)
After further judicial proceedings, U.S. Titanium Corporat .on
and/or The Stone Foundation contracted with Geonics, Inc. to
prepare a permit application for disposal of the copperas. This
application was submitted to the SWCB and State Department of
Health on October 3, 1979 and approved by the State Department of
Health on March 11, 1980. (NUS, 1983, p. 2—9)
By May 30, 1980, U.S. Titanium Corporation and/or The Stone
Foundation completed the burial of copperas in a test cell, arid,
on October 2, 1980, New Enterprise Construction Company began
full-scale burial of the copp.ra. under contract to U.S. Titanium
Corporation and/or Tb. Stone Foundation. Burial was completed on
December 1 ,1980, and final grading, channel improvement., and
seeding and mulching ware completed by January 16, 1981. (NtIS,
1983, p. 2—13). The burial area is now referred to as “Area 1”.
During the U.S. Titanium Corporation and/or The Stone Foundation
sponsored burial of th. coppers., the U.S. Environmental
Protection Agency, Region III (EPA), contracted with Ecology and
8 3O1O7
— HYQROSYS EYS —
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g vir0 t Inc. to conduct a preliminary assessment of the u.s.
Titanium Site. The resulting report was submitted to the EPA on
AuguSt 3, 1980 (NTJS, 1983, p. 2—13).
On April 7, 1982, the Executive Director of the SWCB disapproved
a site improvement plan for reclamation of the former copperas
storage area submitted by U.S. Titanium Corporation and/or The
Stone Foundation. As a result, Benton G. Tinder was appointed
receiver of the U.S. Titanium Corporation property at Piney River
(NUS, 1983, p. A—12). On May 27, 1982, Mr. Tinder contracted
with R.M. Cash and G. Burley of Amherst, Virginia, to complete
reclamation and runoff control for the former copperas stockpile
area. This reclamation work was funded from the Governor’s
Contingency Fund. (NTJS, 1983, p. 2—10)
In December 1982, the EPA ranked the U.S. Titanium Site 332nd out
of 418 sites on the National Priorities List published pursuant
Section 105(8) (B) of CERCLA (Nt IS, 1983, p. 2—li). On February
‘1. and 2, 1983, N t IS Corporation, under contract with the EPA,
conducted a site inspection as part of the development of a
Remedial Action Master Plan (RAXP). The RAMP was released in
August of 1983. (NUS, 1983, pp. A—13 and 1—1)
In June of 1983, the SWCB authorized the Department of Civil
Engineering, Virginia Polytechnic Institute and State University,
Blacksburg, Virginia, to conduct studies relating to the U.S.
Titanium Site (VPI, 1984, p. 1).
In 1985, EPA contracted with GCA Corporation to conduct a Focused
Feasibility Study (FFS) on the nature and extent of the acidic
331O ’7
________________________________
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2.0 SITE FEATURES INVESTIGATION
2.1 DEI’IOGRAPHY
The U.S. ‘ri anium Site is located on the Piney River flood plain
and the adjoining hill north of the river and east of State Route
151 near the town of Piney River. The town is primarily zoned
for industrial development. Industries in the area have included
mining, mineral processing, and lumber. Currently, there is at
least one operating rock quarry and two saw mills in the Piney
River area. Since American Cyanamid Company closed the titanium
processing plant, titanium minerals are no longer mined from the
local deposits.
The area is populated by approximately 200 people, with most of
these people living within a one-mile radius of the Site. The
closest residence is approximately 2000 feet to the west of the
1 site along State Route 151, across from the former plant building
Isite.
The community utilizes groundwater for its potable water supply.
However, the residential wells are hydrogeologically isolated
from the contaminated groundwater found on the Site. The wells
to the north and vest are upqradient, while wells south of the
Piney River and east of the Sit. are hydraulically isolated by
the groundwater discharge boundaries associated with the Piney
River, and the unnamed tributary on the eastern side of the
boundary. No residential wells exist between the Site and the
Piney River.
3o1o r
31
_________________ :
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c . .
Surface drainage from the Site flows south to the Piney
which, in turn, flows southeastward to the Tye River, ar
subsequently, to the James River. The Piney River is not used a
a municipal vater supply, but is used for recreation and fishing
upstream of the site. The closest diversion for drinking water
is approximately 40 miles downstream on the James River (NUS
RAMP, 1983), and is not subject to possible adverse impacts from
the Site. Recent biologic surveys have shown that the Piney
River is fully recovered above its confluence with the Tye River.
The point of recovery is between 1000 feet and four miles
downstream of the Site.
2.2 LAND USE
The U.S. Titanium Site is an abandoned mining and ore processing
facility that was used for titanium dioxide and yellow ferric
oxide manufacturing during the American Cyanamid Company
ownership (NUS RAMP, 1983). The processing plant, the
associated settling ponds, and a copperas stockpile area were
located on th. north side of the Piney River in an area covering
approximately 100 acres.
Predominant land use in areas adjacent to the site include rock
quarry operations, logging, and farming. Route 151 and several
railroad right-of—ways lie adjacent to the Sit., and the land in
the surrouftding area is zoned for industrial use (NtJS RAMP,
1983).
The railroad right—of—ways belong to the Blue Ridge Railroad,
which is no longer in business, and the tracks have been removed.
32 301100
__HYD CS
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U
3.0 PHYSICAL SEDTIN
3.]. SOILS
In the upland areas, the Site is Underlain by clay and silty clay
of the Cullan soil association (NUS, 1983, p. 3—2). The scj3. is
a residuum (saprolite) derived from the weathering of the
underlying parent bedrock material. It is a dark reddish clay
loam near the surface, but grades into the parent bedrock at
variable depths across the Site. These residual Soils typically
have a pH of 5. . to 6.0 (GCA, 1985, p. 3—9). Within the flood
plain, the soils consist of heterogen 5 alluvial deposits of
gravel, sand, silt, and clay. The approxj , boundary between
the residual and alluvial Boils lies along the base of the hill
containing Areas i, 2, and 3 (see Plate 2).
3.1.1 DISTRIBUTION AND TNIC)CNESS OF SOILS
Numerous borings and wells Were drilled at this Site by
HYDROSYSTEII.S, Inc. (plotted on Plat. 2) and investigators from
VPI (Morris, 1984, and Mosl.hi, 1984). These borings and wells
were used to dslin.at. the thick ess of soils throughout the
Site. On Sit., th. residual soils range in thickness from just a
few inches flsar the stream bed east of well. 7 in Area 2, to
aPproximately 60 feet along the southe edg. of Areas 1 and 3.
Plate 2 present, the soil thickness data, while logs of the
soil borings are present.d in Appendix E.
3O11O
HYOROSYSTEMS .:.__
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i.e., less than 0.5 in/hr (Bureau of Reclamation, 1978, •
Only six tests had final saturated K values greater than 0.5
in/hr. Thos values, ranging from 0.63 to 0.80 in/hr fall with
the range for silty clay to silty clay loam.
As can be seen in the graphs presented in Appendix I about 13 of
the 21 infiltrometer tests produced fair to good results which
could be fit with an exponential curve with confidence. The
other test results are judged poor due to inadequate data to
produce a curve fit with confidence. However, even the results
for the tests with poor data fall within two standard deviations
of the mean, indicating the results are reasonable.
3.2 GEOLOGY
3.2.1 PHYSIOGRAPHY
The Site is located in the Piedmont physiographic province about
five miles east of the Virginia Blue Ridge. The Site is located
on the Piney River Quadrangle 7.5 minute series topographic map
(U.S. Geological Survey, PR 1984). In the general vicinity of
the Site, elevations (datum is mean sea level) range from 2218
feet at England Ridge 4.5 miles to the northwest of the Site, to
just und.r 6O feet about one mile downstream of the Site en the -
Piney River.. Within the boundaries of the Site, the elevation
ranges from 726 feet on top of the coppera. burial pit in Area 1
to 618 feet in the Pir*.y River near the drainage area in Area 7.
- 3O111O
42
- CS’SEMS
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3.2.2 LITHOLOGY
The bedrock underlying the Site consists of the igneous and
.taniorphic -rocks shown in Figure 3.1. Few detailed studies have
been completed On th. geology near the Site, except for a study
by Hilihouse (1960) on the mineralogy and petrology of the area.
Exposures are so few and poor that petrologic and structural
relationships have been difficult to determine. However, based
on the work of Hilihouse (1960), a general description of the
geology is possible.
Underlying all of Areas 1 and 3 and the northern two-thirds of
Area 2 is a pegmatitic anorthosite , a complex assemblage o
sills (tabular intrusive bodies parallel to the intruded body)
and d .kes (tabular intrusive bodies cutting across the intruded
body) (Hillhouse, 1960). The anerthosite is a coarse—grained,
igneous rock consisting of mere than 90% plagieclase, a calcium-
sodium aluminum silicate with the mineral formula
(Ca,Na)(Al,Si)AlSi 2 0 3 (Mason and Berry, 1968). The anorthosite
is also referred to as the Roseland anorthosite (Hilihouse,
1960).
Underlying the southern •rtd of Area 2, and all of Areas 4, 5, and
6 is what Milihouss (1960) termed the border gnsiss, a complex
unit containing f.ldspathic gneissss, altered augen gneiss,
garnet gn.i.s, graphite gneiss, and lenses of pyroxenite
amphibolits, and psgmatitic anorthosits.
Underlying a small area of the Sits just east of Area 5 is
Nelsonits, which, on th. south side of the river, was the
r 43 301111
LJVP CSYS EMS
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titanium-ore body. The general term Nelsonite has been giv
rocks in Nelson county that consist of apatit. and one or mor
the iron and.titaniUm oxides: ilmenits (F.Ti0 3 ),, rutil. (Ti0 2 ),
or magnetit. c . 3 o 4 . The Nelsonite that occurs at the Site
principally contains ilmenite and apatite, with minor amounts of
magnetite, rutile, plagioclase, quartz, hornblende, biotite, and
chlorite. The Nelsonite is medium grained, .quigranular, and has
a distinct, sugary texture (Hilihouse, 1960). The Nelsonite
contains up to 60% and, in some cases, as high as 90% ilmenite
(Hilihouse, 1960).
Underlying the southeastern corner of the Site in Area 7 is an
altered hypersthene granodiorite, which is m.dium—grained, gray- -
green in color, and characteristically has a gn.issic, or layered
mineralogy. The granodiorite has a complex mineralogy consisting
of biotite, amphiboles, pyroxenes and numerous metamorphic
reaction products (Hilihouse, 1960).
3O11i
__________________________ STEM5
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Fiqur. 3.1. G*nsraliZSd qsoloqic up for th. U.S. TitaniUm Sits,
Pirisy Rivsr, Virginia (fros Hi]]houa•, 1960).
45 301113
vCS ’S MS
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3.2.3 STRtJCTtTRAL GEOLOGY
The structural geology of the region is dominated by the Rose1a
dome, a doubly plunging anticline. All the rocks exhibit a
northeasterly striking, southeasterly dipping gneissocity, or
layered mineralogy (Nilihouse, 1960).
Fractures occur in the bedrock at the Site and are visible in the
outcrops of bedrock in the bottom of the Piney River and the
drainage channel at the base of Area 2. Two distinct sets of
nearly-vertical fractures are present and have approximately
northwest-southeast and northeast-southwest orientations. Field
measurements of strike and dip on 1.7 fractures at the Site were
completed. Analysis of this data indicates an apparent primary
fracture orientation (13 out of 17 fractures) that averages
approximately North 21 West, and is approximately perpendicular
to the strike of the Roseland Dome anticline. An apparent
4secondary fracture orientation averages approximately North 68
1 East, paralleling the strike of the Roseland Dome. These
fractures are nearly vertical. Table 3.2 and Figure 3.2 present
the fracture orientation data and analysis.
These two, nearly—vertical fracture sets oriented at right angles
are indicativi of the horizontal tension caused by the uplift of
the Roseland Dome (spencer, 1969, p. 64).
301114
- 46
IJV OSYSEMS .
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3.3 HYDROLOGY
3.3.1 GROUNDWATER HYDROLOGY
3.3.1.1 OCC RENCE OF GROUNDWATER
The hydrogeology at the Site is typical of the Piedmont of
Virginia. Groundwater primarily occurs in the porous,
unconsolidated granular material of the saprolite and, to a much
lesser extent, in the fractures that run through the dense, hard
igneous and metamorphic bedrock. Thes. two units are
hydraulically interconnected over larger distances. However,
local heterogeneities such as changes in the clay content of the
saprolite across a bedrock contact may produce local, partially
confined conditions in the weathered, fractured bedrock.
Typically, 80% of the wells in the Piedmont region of south-
central Virginia yield less than 20 gallons per minute (gpm)
(Davis and DeWiest, 1970, p. 325). For the Piedmont in general,
90% of the total yield possible is obtained within the upper 300
feet, 85% within the upper 200 feet, and 50% within the upper 135
feet (LeGrand, 1967, p. 5). This is due to the fact that the
fractures become tighter, and the number of fractures decreases
with increasing depth.
However, at the Site, observations of fracture aperture indicate
the fractures are very tight even at the surface. Fractures in
the bed of the stream at the southern base of Area 2 allow very
little seepage of water from above the water fall to below the
water fall.
301117
49
__________________i-1YD S’SEMS
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The hydraulic coflductivjty for clayey saproljte jy Tab1.
estimated from the permeameter tests reported by Moslehi
p. 73).
3.3.1.4 RECHARGE AND DISCHARGE AREAS
Groundwater recharge to the Site occurs over the entire surface
as precipitation infiltrates into th. soil and percolates to the
water table. Groundwater discharges into the tributaries along
the base of the hill containing Areas 1, 2, and 3 and into the
Piney River. Based on field observations during drought periods,
when the water table is low, groundwater ceases to discharge into
the tributary along the southern bass of Areas 1 and 3, passes
beneath the tributary and continues to flow towards the Piney
River. During those same drought periods, however, the stream
along the base of Area 2 continued to receive groundwater
discharge, albeit at a much reduced rats.
3.3.1.5 GROUDWATER-fl w PATHS
Groundwater flow within the Site originates in the upland area
containing Areas 1 and 3, flows in a radiating pattern down bill
towards the streams surrounding the base of the hill and to the
Piney River. Figure 3.5 presents groundwater flow directions
(arrows) superimposed on the groundwater contours taken from
Plate 1.
3O11
59
YDWSYSEN
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3.3.2 SURFACE WATER HYDROLOGY
3.3.2.1 SURFACE DRAINAGE CONFIGURATION
The Site lies within the Piney River drainage basin, which is
part of the larger James River drainage basin. The Piney River
flows in an easterly direction forming the southern boundary of
the Site. Areas 1 through 4 lie on the upland area, while Areas
5 through 7 lie within the flood plain of the Piney River.
Surface water drainage runs of f the Sit. primarily via the
drainage channel along the bottom of Area 2 and a small streaxn
that originates along the western side of Area 1. These two
channels merge south of Area 2 and discharg. into the Piney River
through a culvert at the downstream end of th. property. A third
stream originates to the west of the sedimentation ponds in Area
5, flows through the sedimentation ponds, and discharges into the
Piney River through a breach in the dike at the southeastern end
of the sedimentation pond. Figure 3.6 illustrates the general
surface drainage pattern that currently exists at the U.S.
Titanium Site.
3.3.2.2 SURFACE WATER FLOW CHARACTERISTICS
The Piney Rii#ir flow has been gauged at the Route 151 bridge by
the U.S. G.ologica]. Survey (approximately 0.5 miles upstream of
the Site). The ar.a of the Pinsy River basin above this gauge is
47.6 sq. mj. The mean flow of the Piney River for th. period
1951 to 1986 was 94.7 cfs, while the maximum flow was 38,000 cfs
on 8/20/69, and the low flow was 1.1 cfs on 9/13/66.
301123
61
U
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quality limits established by the Federal and Stat. govt
even during extremely low river flow. This contradicts prey
studies of the sit. which suggested that groundwater discharqe
during low...flow periods would be sufficient to cause water
quality vioiations. ORIGINAL
(ned)
Mother objective of this study was to examine the impacts that
heavy rainfall events, which normally occur in the summer months,
have on river water quality. Specifically, the intent was to
observe the impacts on the river due to weather conditions
similar to those which are thought to have produced earlier fish
kills in the Piney River. Those earlier storms were reported as
being relatively intense summer thunderstorms occurring after a
few weeks of dry weather.
Unfortunately, the summers of 1986 and 1987 turned out to be
severe drought periods. The only significant rainfall event that
occurred during the summer of 1986 was a light rain on August 20.
That rainfall, however, was enough to produce runoff from the
Site both through the culvert and from Area 5.
During that rainfall event, chemical data were collected for
three stations along the river, stations 1, 5, and 6, and from
the culvert, station 7. These data ar. presented below in Table
4.13. As canbs seen, there was a substantial reduction in pM at
station 5. The river water was gray in color, indicating
significant runoff and erosion from Area 5 upstream. This pM
value of 4.93 wa, the lowest pH value recorded during this SRI.
301218 k
153
WYDROSYSTEMS
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5.0 TRANSPORT AND FATE OF CONTAMINA S
5.1 GEOCHEMISTRY OF COPPERAS
Copperas is. the primary source of acidity, dissolved iron, an
sulfate in discharges from the Site. As stated previously
copperas is not acidic, but, subsequent to dissolution, coppera
produces acidity as the result of a sequence of reactions tha
include oxidation of the ferrous iron to ferric iron an
hydrolysis of the ferric iron to ferric oxyhydroxides. Thi
series of reactions is shown in Figure 5.1. The net effect o
these reactions is that for every mole of copperas dissolved, tuc
moles of excess hydrogen ion (H+) are produced resulting in th
acidic leachate.
The solubility of copperas is essentially infinite. Krauskop
(1967, p. 516) lists the solubiljty of ferrous sulfate as >l.c
moles/liter in a solution with just 0.01 moles/liter of sulfate.
The theoretical ratios of sulfate to total dissolved iron to net
hydrogen ion concentration, based on the reactions presented
Figure 5.1 are 1:1:2.
3O12
159
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5. 3 CONTAMINANT TRANSPORT
The highly soluble nature of copperas inhibits
reprecipitat ion once it is dissolved by percolating
water. After the copperas leachate has been formed in the burial
pit in Area 1, the dissolved iron, sulfate, and acidity are
transported along two possible pathways. The first pathway is
from the burial pit down to the water table and, hence, with the
groundwater to points of discharge. The second pathway is via
discharge immediately to the surface of the burial pit with
subseq,.ient transport in surface water to the Piney River. In
either case, the pathway taken by any particular dissolved ion
from the burial pit may involve both intermittent surface- and
groundwater transport.
These pathways are summarized in Figure 5.3 and are discussed in
the following sections under the categories of transport through
the unsaturated zone, transport in the saturated zone, and
transport in surface water.
5.3.1 UNSATURATED ZONE TRANSPORT
5.3.1.1 WATER MOVEMENT ThROUGH UNSATURATED ZONE
In each area-of contamination on the Site, initial transport of
the contamination is through the unsaturated zone, i.e., the soil
above the water table. Due to the nature of the stratigraphy
within the saprolite, it is believed that the movement of
( I . . )
168
J-1YDJ CS (S:VS
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U.S. Titanium Superfund Site Mining Waste NPL Site Summary Report
Reference 3
Excerpts From A Toxicological Impact Assessment
of the U.S. Titanium Corporation Property;
NUS Corporation; January 6, 1983
-------
OR I G ; AL
(fled)
CCRPC A CN
99 C EAGLE SC3- i,
SUVrE 9i e
WA’rN 5 PENNSv v n i 9 7
1 5 S87.9 i Q
A Toxicologjcaj Impact
Asse ment of the
U.S. Titanium Corporation Property
TDD No. F3-82 12..16
EPA No. VA-Ill
Preparation Date: anuar’y 6, I9 3
Presented To: Linda Y. Boornazian, DPO
EPA Region U I
Prepared By:
Kenneth G. 5ymrns, Ph.D. Tox coiogist
Don Senovith, FIT III Manager
io1’ o. ..
-------
U.S. Titanium Corporation Property
TDD No. F3-Z212-16
EPA No. VA-Ill
SUMMARY
Resths of U.S. Titarthsn sam e analyses indicate: I) a high content in leachates
01 to c metals (As, Cd, Cr, Pb, Ni), 2) high siAf ate and low pH in emanating s un ace
waters, 3) contamination of the gow dwater underlying the site with metals, s41 ate
and high acdlty, and 4) probable but undetermined adverse impacts on the nearby Piney
River.
No metals of to cologicaI concern were io sid above analytical detection Lim its
(ito 0 ugh) In the two resloential wells sampied. Both wells, however, appear to be
hy aLdicaUy upgradlent from the slte the dosest private well is more than 1,000 1 eec
to the north of the coppeas burial pit. I.ocal çoundwater flow is likely to be intercepted
by the Piney River, and distant residential wells are at remote risk.
of a direct nat xe to hun an health appear to be minimal. The major
concern is the potential far adverse impacts from en yoi rti -oiis low in pH and high
in ierro suLfate and other metals into Piney River via surf ace run-oils as well as subsurnac
ix ll aticn. Pinsy River is protected for water-contact receation, fish, and wU ile.
Several in den of fish Idils nave occured in the pas two, su equent to burial of
the copperas material on-sit..
PageOne 10130
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tJ.S. TItanium Corporation Property
TDD No. F3—8212-16
EPA No. VA-ILL
SURFACE WATER SAMPLES
Data provioed by sample results of an extensive surface water monitoring survey
conducted by the SWC3, May 5, 19*2, and two Leachate samples collected by EPA/CR!..,
August 4, I9 2, are in uded as attachments to this report (Tame F; please note correc iorts).
Seeps taken near or an the Piney River, directly south of the former coppera.s storage
area, (sample station numbers 6,7,9,10, and UST-L23, were fo d to be highly acidic
(pH 2.9-3.0). !normo amo atts of sulfate were aLso detected up to 2,700,000 ugh).
Su equent to th. removal and burial of the copperas material in anuary of
1981, rtri-off from the poorly stabilized area of the previous copperas storage resu1te
i tt two fish d1ls in May and 3u e, 1981. In 3* .ute, 1 82, remedial measures were taken
to improve conditions of the former copperas storage and final disposal areas (See Site
Inspection Report). Surface water samples taken by the ZWC3 prior to this remedial
action ind1 te subotantlal contamination in leachates emanating from the previous
copperas storage area. A combined ainage sample from two interntittent streams
in this seine area taken by EPA/CRL, subsequent to the me, 19*2 remediaL action,
suggests that a leaching probiem may still east (compare results of EPA/CR!. sample
UST42 and SWCS samples 6,7,9, and 10). Additonal artaLyti L information may be
reqtnred to make this determination.
Comparison of upstream and downstream samples Cd. sample stations 1 and
1*, Tabie F) t11es by the 5WC , May l $2, from the Pirtey River appears to indicate
site-related contamination ox th. river. The downstream sample showed inceases in
iron (from 1014/1 upstream to 10 ugh), manganese (from 10 ugh upstream to 130
ugh), chromium (from 10 ugh 1 upstream to 40 ugh 1), sulfates (from 1,900 ugh upstream
to i3,*00 ugh), and siVtiflcant reduction in pH (from 6.7 to 5.1). It is noteworthy that
thes, parameters are the sam. as those noted in the seeps sampled near or on the P ney
River, as discussed above. Downstream levels of iron, manganese, and pH are in excess
at those recommended in Ambient Waters Quality Criteria and mandated by Secondary
MC I. Stancards for pubic water systems. The potential may also esiSt for poUuton
‘ of the river by arsenic, chromium, and oth metals in this flood-prone area.
-------
“C “
( .i)
U.S. TitarUurn Corporation Property
TDD No. F3- 2l2-I6
EPA No. VA-Ill
EFFECTS ON ACQUATIC SYSTEMS
Past rw -ofi from the U.S. Titanittri site foLlowing rtusuaUy heavy precipitation
hasrestAted nftth dflsint Plriey River (doct ented by Vs. SWC3 7/11/77, 8119/77,
$/2 /79, 7/ Il/ 0, 6/221*1) attributed to a substantial inilux of ferrous sELf ate and reduct.ion
in pH. In periods of low precipitation, water enters streams primarily as sub-sirf ace
irdiltration trrougPt granL & or porous material, and the low pH noted in the downstream
sample during a time wP n no 1ead ates were observed disd arglng into Piney River
may reilect the substantial contribution of affected groundwaters.
Ferrous stgf ate, whld comprises the 4k of the copperu material stored and
tnet buried on-site, Is frequentiy present in undergrOL d waters. Some springs and many
mine areas contain fatly large smotr ts, with the resiit that the streams to whid theY
give rise are at first completoly free of oxygen, low In p11 and quite lifeless.
I.atge amo ta of ferrous sale can produce serious pollution n rivers. Waters
contaminated by ferrous lone are usually ac4 as ferrous ions are o d1zed, ferric hy O de
(odre) is precipitated. In tF* process, dissolved oxygen is co s .uned, caroOrt d1o de
is mar1 dy elevated from natural bicarbonate, and the ferric rty o de formed can
settle out of inert suspension and produce a d ol4rtg sediment over areas in river beds
at ate iticaL for the support or progeneratlon of various freshwater life. According
to Hynes, (T Ecolo of Rimning Waters, University Toronto Press, 1970), it is possible
that the prese%ca of the deposit and the depletion of dissolved oxygen in the water caused
by the rapid o,d n of ferrous ions (immediate oxygen demand) are at least as important
in rninating species as is the low p11.
Downstream sampling of the Piney River revealed a pH value of 5.1. Studies
of crronic pH off ecta on fathead minnows indicated that a p11 value of 6.6 was marginal
for vital life f .a ctions (Momt, D.L, 1973, Water Pee. , 9*7). BeLow this pH, egg produC iOfl
and rtatcl ability were reduced and at pH values below 5.2, fish exhibited abnormal behavior
and deformities. A pH range ot 6.5 to 9.0 is considered suitable tO provide protection
for the life of freshwater zish and bottom-dwelling invertebrate fish-foOd organisms
Y (Q ality Criteria for Water, U.S. EPA, l97 ). 101 ‘313
Page Eight
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/
U.S. Titanium Superfund Site Mining Waste NPL Site Summary Report
Reference 4
Excerpts From Site Inspection of US. Titenium;
NUS Corporation; July 27, 1983
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SITE INSPECTION OF
U.S. TITANIUM
PREPARED UNDER
TDD NO. F3-8212-41
EPA NO. VAD 980705401
CONTRACT NO. 68-01-6699
FOR THE
HAZARDOUS SITE CONTROL DIVISION
U.S. ENV .ONMENTAL PROTECTION AGENCY
3ULY 27, 1983
NUS CORPORATION
SUPERFUND DIVISION
SUBMITTED BY
O .K Q
APPROVED BY
LJOLLJ
DONALD SENOVICH
MANAGER, FIT III
101 ? 6
(Red)
R-585-2-3-18
C.K. LEE
‘3
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—
I . . . -
Site Narne _ fltan:urn
TDD No.: 8212- j
1.0 INTRODUCTION
1.1 Atheriz tjon
NUS Corporation performed this work under Environmental Protection Agency
Contract No. 68-01-6699. This specific report was prepared in accordance with
Tecthi L Directive D ocument No. F3-8212.41 for U.S. Titanium Io ted in N søn
County, Virginia.
1.2 Sco Of Work
NUS Corporation was tasked to review information 11ecred by Ecolo arid
Erivirorwnent during a site ir pection, sam ing, arid well drilling project performed
in November, 1982, under EPA project task number F34108..17 NUS dd not
C nduct a alte vl at.
1.3 Summay
The U.S. Titanium ate is an abandoned milling and ore processing want. The
facility changed ownership several times during the operation. During its
operation, the facility produced about 80,000 cubic yards of cepperas (ferrous
sulfate) wastes. Several waste handing procedures were utilized over the years
(surf ace cues, lagoons, etc) until December 1980, when the wastes were buried on-
ate under stat* orders. (Please see EPA report numbers F3-8008-03 and F3-
810801 7A for further bscl roi.rd information.)
Prior to btwlal on.gte, alx fish kills occurred, 1977-1981, in Piney River. The
Virginia Water Ccmrol Board in’ estipted these fish Idils and has attributed them
to rwi.off from the ppeai waste pile. Presentiy, surface water run-off from the
site is ntro1led tirough e astlng drainage ways toward the south into the Piney
River. (See Plate Sin Section 5.)
1O126
1— 1
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U. S. I$isatta Site Pimey liver. Vi.
• PLP TE 5 Water No.itorl.9 DUe
.1 StatIons
par tsr I 1 10 1! l IST-i l lIST-ti
g (S.U.) 6.1 3.0 3.0 3.0 3.0 2.9 5.1 6.6 2.9
Alt/Mid
(ms/I C.C0 3 ) 12/ 6 USd1741 Acid/i l l Acid/IflO *cid/ 1145 Acid/llSS 4122 33/Alt
S i liatss (‘ill) 1.9 600.5 $459.4 1 0 13. 6 1240.5 2100.1 13. 1 21.4
As (a,/S) 0.001- 0.013 0. 1- 0. 55 0.5- 0.0- 0.001- 4o.61 . ( 0 Oil
Cd (mg/I) 0.001- 0.004 O.003 0.004 0.001 0.001- 0.001- )4o i ozl
Cr (m g/I) 0.01- 0.11 0.14 0.00 0.09 • 0.04 0.01- 2.1 0 085
Cu (mg/I) 0.01- 0.55 0.19 0.00 0.11 0.01- 0.01- 3.9 0 i S O
ii (mg/i) 0.01 100 230 320 410 0.51 3.3
Pb (ag/I) 0.002- 0.002 0.1 0.1 0.1 0.002 0.002- c. 9 l .)* 0 070
Ni (mg/I) $5.5 .92
W a ( ag/I) 0.05 6.1 12 510 0.13 0.16
ii (ag/I) 0.01- 0.11 0.91 1.1 5.4 0.01- 0.02 61.0 1. 59
Froui 101) H 13-V212-IG Report
C ’ Loc tloius see Plate
( .)
U)
sill
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Site Name: US Titanium
TDD No.: F3-8212-41
4.0 TOXICOLOGICAL IMPACT ASSESSMENT
A Toxicolo cal Impact Assessment of the U.S.Titanium site was recently prepared
under TDD No. F3-8212-16 based on res%Ats of samples obtained on August 4, 1982
by EPA Region Ill and Central Regional Laboratory (EPA/CRL), and samples
collected by the Virginia State Water Control Board on january 7, 1982.
Subeequently, Eco1o arid Environment was contracted to have additional
monitoring wells installed. FIT IU sampled these wells and surface waters on the
site in No mber of 1982 under TDD No. F3-8121-41.
Res Ats of the November sampling confirmed previous findings of elevated iron,
manganese, arid other metals in ground and st.rf ace waters. The toxicological
impacts of the inorganics identified are addressed in the initial Toxicological
Impact Assessment of the U.S. Titani n Corporation Property, which is induded as
an attathT lent to this report for purp es of reference. (Please see Appendix A -
1.0)
Groundwater samples from newly ir talled wells indicate lower levels of iron arid
other metals than were found in previous samples taken in late summer by
EPA/CRL from existing wells. It may be noted that concentrations of iron and
other metals in groundwater can fluctuate with changes in weather conditions.
Levels of iron appear, nevertheless, very hi in some aqueous samples taken from
the recently installed monitoring wells (up to 579,000 ug FE/i in MW B-2).
Surface water samples taken in November suggest that a potentially serious
leaching problem may still exist, despite the remedial measures (copperas buried,
regrading, and other repair) ‘taken in :Iune of 1982. A sizf ace run-off sample, taken
from a ci.Avert asit enters Piney River, revealed high levels of iron (424,000 ug/l),
manganese (115,000 ugh), zinc (2,270 ugh), chromium (55 ugh), nickel (1,278 ugh),
copper (170 ugh), and sliver (24 ug/l).
1. •31
4 . -I
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F
%O S A
0
0
11
a
a
0i
0
LEACHATE SEEPS
GRO(JNDWATER SA 1PLING POINTS
SURFACE WATER SAtIPLING POINTS
PLATE 8
SKETCh MAP OF
SAMPLING POINTS
?d CROSS-SECTIONS
f 1
p.
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L
1ç’
U.S. Titanium Superfund Site Mining Waste NPL Site Summary Report
Reference 5
Letter Concerning Status Report of the U.S. Titanium Mine Site;
From R.V. Davis, SWCB, to J. Kenneth Robinson, House of Represents
August 26, 1980
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)j\ ( I , J r) [ \,‘ 1 .C !NJA
‘s I I I / Ii iii:i I \ I.•i )! I i 1 i,
‘ ;:j;’;’: ;;” ‘ O0A;O%t ..,fl
04) ?S7 00% V c m
OCr 7 1S O -
C _ I i
..
VAJ L
Honorable J Kenneth Robinson L FRE0b© AI...
House of Representatives Ficg
Washington, D. C. 20515
Re: U.S. Titanium Corporation, Piriey River, Virginia
Dear Mr. Robinson:
Thank you for your letter of 18 August 1930 concerning the referenced sit a
tion in nelson County. Hopefully, this will bring you up to date on the
status of our efforts to resolve this persistant problem.
As you may recall, U. S. Titanium Corporation is the owner of property loca-
ted in Piney River, Virginia on which is located a stockpile of waste material
known as copperas or ferrous sulphate, which was deposited there by a previous
owner, American Cyananiid Corporation. The Board has been involved with L.S.
Titanium in a regulatory capacity since 1976 and am enforcement capacity as
well, since 1977. U.S. Titanium took possession of two abandoned mine sites
and the old american Cyanamid plant site in 1976. American Cyanamid had
operated a titanium dioxide martufacturing plant at Piney River for many years,
finally closing its operation in 1971. During its operation, American Cyanamid
deposited vast amounts of waste copperas adjacent to the Piney River. Prior to
the closure of tile Piney River Plant, American Cyanamid submitted to the State
Water Control Board staff for approval,a proposal to dispose of the waste
copperas by burial. Prior to implenier 1 ting this disposal plan, however, r. S.
Vance Wilkins bought the property. As part of the sale agreement, American
Cyanamid p3 ld flr. Wilkins a sum of money (5100,000) to dispose of the waste
copperas in accordance with the Board approved plan. Mr. Wilkins, prior to
iriiplementuig -the disposal plan, constructed a Board approved no discharge facil-
ity to collect and contain contaminated runoff from the waste copperas pile bj
ut i li Z i ng a catciunen t has in, pumps, and a larger ovapo ration pond. Thi s faci 1-
i ty cliiiiiiialed thu discharge of acidic rwi tf and seepage from the copperas
pile to tho river which had persisted since stockpiling was begun by tImer, can
Cyanamid. It was Mr. Wilkins’ intention to try to sell the waste copperas
before inçlencntincj the approved disposal plan. This proposal was agrccd to
by the Board’s staff, however, hr. Wilkins was given only until Ucc iiber 1977
to pursue the option of selling the copperas. Bcyond that date the Board re-
quired tnat the copperas be properly disposed of in an approved manner. In
the in terim, Mr. Wi lki ItS was required I u i ’ia I nt i n and opcra Lu the 110 di s charyc
facili ties to prevent discharge of conl,uu linatcd wastewathr to the Piney cr
in accurddncc wi Lii a certi fical.e issu.u.J Iiy the Uuard.
100334
-------
i.
fl:’G 26 ‘ 3 -
to conta ill runoff from the copperas pi le. Al tlOuyh the s ta ff S • es t ga
is icte . it 3f)flC rs tha t heavy ra 111 5 On July 10, 1 1.3 re ’s l :cd
ruiiu f I 1ru i IJic Coppera S p I 1 e en Len Ii J the P1 ‘iey l ver ad k i Ili i
both ne Piney and lye Rivers once again This rlost rOccilt fish kill e p i-
lies tPe ur er1cy in carrying oat the approved burial operat loll cot,
Departrient of health and thc oard have JuriSdicti ii over aH aspects f th
burial opera ti on and propose .o en force their appropni a U’ authority under tre
law and Lh i r rcspec Live pcniii Is La ensurC th I 1lir. cupperus is Lu ri J us
expeditiously as possible Should the investigation currcntly uncicrway deter-
“iiiip th 4 i I. U S. It taut uw i c rLspullcl Ii Ii’ fcir the July 10. l) O Ii h ill ,
staff wi 11 proceed to collect frorii Lh company rap] aceron t costs for the f i
killed and investigative costs incurred by the Coiwnonwea]tr.. Please te advised
that the company has paid the Corinionwedith in full for the fish destroyed as a
result of the past two fish kills.
The staff wishes to assure you that the Conrnonwea]th is doing everything it
can to ensure that this waste is Properly disposed of this year. You ShOu d
also be assured that while this waste, due to its acidic nature, is very toxic-
to fish, it does not appear to represent a hazard to people or Wi ld1ife..i Un-
fortunately, the staff must also relay to yOu that damage to the river f?ren
past discnarges of American Cyanamid and U.S. Titanium is long term, and e p1te
our best efforts, it will take the river some years to return to a near nor nal
condition. Once these discharges are fully abated and the river begins to
recover, the monies collected to replace the fish killed will be available to
begin a restocking program.
Should you have any specific questions concerning the copperas disp sa1 program,
please do not hesitate to contact r r. Tedd H. Jett of the State Water Control
Board’s Valley Regional Office (703/828-2595). Mr. Jett is the engineer in
charge of overseeing the Boardss responsibility for maintaining the no discharge
facility. The actual burial of the waste copperas is the responsibility of
the State Department of Health, fir. Robert H. Forman, Division of Solid and
Hazardous Wastes Management (703/825-6772) should be contacted relative to the
Department’s responsibilities.
Sincerely,
R. V. Davis
Executive Secretary
Li f
cc: BAT, Richmond
i3ureau of Enforcement, Richmond
John Butcher, Attorney General’s Office
VRO File c20-1147,
Mr. Robert II. Forman, R.S.
Slate Department of I calth
Div. of Solid & Hazardous Wastes Management
102 forth Main Street - -
Culpeper, VA 22701
R. Bradley Cht nin j 1OO3 u
Jatites A. Pr tø
r . , ,,
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Mining Waste NPL Site Summary Report
Uravan Uranium Mill
Uravan, Colorado
U.S. Environmental Protection Agency
Office of Solid Waste
June 21, 1991
FINAL DRAFT
Prepared by:
Science Applications International Corporation
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
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DISCLAIMER AND ACKNOWLEDGEMENTS
The mention of company or product names is not to be considered an
endorsement by the U.S. Government or by the U.S. Environmental
Protection Agency (EPA). This document was prepared by Science
Applications International Corporation (SAIC) in partial fulfillment of
EPA Contract Number 68-WO-0025, Work Assignment Number 20.
A previous draft of this report was reviewed by Gene Taylor of EPA
Region VIII [ (303) 293-1640], the Remedial Project Manager for the
site, whose comments have been incorporated into the report.
-------
Mining Waste NPL Site Summary Report
URAVAN URANIUM MILL
URAVAN, COLORADO
INTRODUCTION
This Site Summary Report for the Uravan Uranium Mill is one of a series of reports on mining sites
on the National Priorities List (NPL). The reports have been prepared to support EPA’s mining
program activities. In general, these reports summarize types of environmental damages and
associated mining waste management practices at sites on (or proposed for) the NPL as of February
11, 1991 (56 Federal Register 5598). This summary report is based on information obtained from
EPA files and reports and on a review of the summary by the EPA Region VIII Remedial Project
Manager for the site, Gene Taylor.
SITE OVERVIEW
The Uravan Uranium mill complex is located approximately 90 miles southwest of Grand Junction
along State Highway 141 in Montrose County, Colorado (see Figure 1). The mill was built at Club
Mesa, west of the San Miguel River canyon (Reference 1, page 1).
Standard Chemical Company began radium milling and extraction operations at the site in 1915 and
shifted to vanadium production in 1928. In 1936, Union Carbide Corporation purchased the
operation (Reference 2, page 3). Production shifted again in the early 1940’s to uranium processing
(Reference 3, Volume 2, page 2-1; Reference 2, page 3). Operations continued on and off at the
facility until 1984, when they were suspended (Reference 2, page 1).
Over the course of its operation, the mill generated and disposed of millions of cubic yards of both
solid and liquid wastes. These wastes have potentially hazardous concentrations of radioactive
material (including uramum, radium, and thorium); metals (including selenium, aluminum, arsenic,
zinc, etc.), and inorganic materials (including ammonia, nitrate, sulfates, etc.).
Mining, milling, and waste disposal activities have resulted in:
• Wind and surface-water dispersal of the tailings materials and the uncontrolled release of radon
from the Tailings Piles
1
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Mining Waste NPL Site Summary Report
• Seepage of contaminated liquids into soils and ground water from several areas in the mill
complex and waste disposal areas
• Concentrations of large quantities of wastes in locations that pose a risk to public health and
the environment, based on considerations of the potential for release of hazardous materials to
the environment (Reference 4, page 7).
Disposal practices included the use of solid waste tailings piles and unlined ponds for liquid waste;
most waste management areas are located along the San Miguel River. Seepage from these storage
areas flows toward the river.
The finely ground nature of the tailings makes them particularly susceptible to dispersion through both
air and water media. Because of the high potential for dispersion by wind and seepage into the San
Miguel River, these piles represent a threat to human health at the Uravan site (Reference 2, page 5).
Other exposure routes threatening the health of human populations include inhalation or consumption
of contaminated media and consumption of food items that have been previously contaminated
(Reference 2, page 20). Several small communities and three larger population centers are within 50
miles of the site (Reference 2, page 23). (According to EPA, the 50 residents of Uravan were moved
from company residences, beginning in 1985. The buildings were demolished in 1988.)
A Remedial Action Plan, developed jointly by the State, Union Carbide Corporation, and Umetco,
describes a 10- to 15-year action schedule for site remediation. The cost of these activities is
estimated to be over $40 million. Remediation activities may include removal of contaminated solids
and liquids from the area (Reference 1, page 2).
OPERATING HISTORY
Standard Chemical Company began operating the Uravan Mill facility in 1915 to recover uranium,
vanadium, and radium from mined ores. Ore was received at the Uravan Mill from approximately 60
different underground mines in the Uravan mineral belt, most of which were within 35 to 40 miles of
the mill. Union Carbide bought the facility from Standard Chemical through the U.S. Vanadium
Company in 1936 and continued to process uranium and radium at the site. While in operation, the
mill processed approximately 1,000 tons of ore per day (Reference 2, page 3).
Stockpiled ore was crushed, ground, and then processed onsite. Processing at the mill included hot,
strong acid leaching in a two-stage circuit followed by the recovery of pregnant solutions in
3
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Mining Waste NPL Site Summary Report
The principal waste management areas onsite and in associated areas are:
• Atkinson CreekCrystal Disoosal Area - Unlined storage pit along the San Miguel River
containing 200,000 cubic yards of raffinate crystals (Reference 3, Volume 2, page 2-27).
• Club Ranch Ponds - Six unlined ponds covering 32 acres located along the San Miguel River
that contain 30 million gallons of liquid raffinate and 560,000 cubic yards of raffinate crystals.
• River Ponds - Seven unlined ponds constructed in old tailings piles containing 200,000 cubic
yards of neutralized mill sludge and contaminated soils. The seven ponds are located along
both sides of the San Miguel River. These were used as holding areas for liquid waste
collected in the mill area before they were discharged into the San Miguel River (Reference 3,
Volume 2, page 2-30).
• Tailin2s Piles - About 10 million tons of mill tailings contained in three piles (at two sites) that
are located on the Club Mesa, 400 feet above and west of the mill site.
• Club Mesa Area - Disposal area on Club Mesa consisting of two clay-lined sludge storage
areas, storage ponds, raffinate spray evaporation area, and associated contaminated soils;
contains 250,000 cubic yards of raffinate crystals, 150,000 cubic yards of neutralized sludge,
40,000 cubic yards of contaminated pond material, and 44,000 cubic yards of contaminated
soil.
• Plant Areas - Two plant locations with surficial contamination including containment structures,
ore stockpile area, equipment and auxiliary wastes, and heap leach sites containing 15,000 tons
of ore.
• Town and Adjacent Areas - Several small communities and three larger population centers
located along the San Miguel River are within 50 miles of the site (Reference 2, page 23). Old
tailings and contaminated soil have been found in these areas (Reference 2, page 6).
SITE CHARACTERIZATION
Potential transport mechanisms for each contaminant source are summarized in Table 2. Below is a
discussion of media contaminated by these mechanisms.
5
-------
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-S.
C l ,
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Mining Waste NPL Site Summary Report
TABLE 3. GROUND-WATER QUALITY AT URAVAN COMPARING
GROUND-WATER SAMPLE RESULTS FOR CRP-4 (BACKGROUND
WELL) AND CRP-2 (CONTAMINATED WELL)
Parameter Units CRP-2 CRP-4 LLD’s
uate 11115184 10/18/84
Sample Type Pumped Pumped
Top Casing Elev feet 4941 980 4995 650 0 001
B Cuing EIev. feet 4891 980 4935 650 0 001
Pt,reatic Elev. feet 4927.880 4959 950 0 001
Temp. C 14 14 -2000
Cond © 25 C unrbos 17,136 365 10 000
pH Units 6.64 758 0100
TDS mg/I 27,090 272 10000
So!. Sulfates mg/I 18,560 28 10000
So!. Chlorides mg/I 1,420 4 10000
Sol. Sodium mg/I 783 196 0100
So!. Calcium mg/I 494 454 10000
Sol. Potassium mg/I 378 10 1 0 100
So! Nitrite/N mg/I 002 <0.02 0100
Sol Nitrate/N mg/I 2 <004 0100
So! Ammonia mg/I 1,610 02 1 000
So! Zinc mg/I 0208 <002 0020
So!. Selenium mg/i <0 250 <0.01 0010
Sol Magnesium mg/! 1,202 221 0 100
So!. Manganese mg/I 663 0.028 0050
So! Iron mg/! 26.8 0 059 0 025
So! Carbonate mg/I <1 <1 1.000
Sol. Bicarbonate mg/I 1,960 258 1 000
So! U-Nat pC/l 470 <3 0200
So! Th-230 pC/I 020±050 000±040 3100
So!. Ra-226 pC/ I 240±050 1.10±040 0310
So!. Pb-210 pC/I 040±090 1300±200 4800
So!. Po-210 pC/! 0 10±0 60 .0 05±0.90 1.000
Zinc’ mg/I 063 <001 0.01
Copp& mg/I 007 <001 0.01
Arscn& mg/I <001 <001 0.01
Mercury’ mg/I <00003 <0 0003 0.0003
Cadmiu& mg/i <0 01 <0 01 0 01
Chromiw& mg/! <0.01 <0.01 0.01
Lead’ mg/I <0 01 <001 0.01
Silv& mg/I <0 01 <0 01 0.01
LLD = Lower Limits of Detection
pC/ i = pico Curies per liter
‘CRP-2 sample 10/6/83, CRP-4 sample 10/5/83
Source. Reference 4, page 90
9
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Mining Waste NPL Site Summary Report
It is conservatively estimated that contaminated soil erosion accounts for the following contamination
in the river, although seep water from tailings piles and ponds was also observed to be contaminating
the River system:
• 2.6 to 543 grams per acre per year (gla-y) of arsenic
• 2.4tol7g/a-yoflead
• 0.2 to 0.9 gla-y of cadmium
• 4.6 grams to 34.6 kilograms/acre-year of vanadium
• 8.4 to 729 (g/a-y) of zinc (Reference 3, Volume 1, page 5-40).
Analyses of seep water, precipitates, and dry wash alluvium from the general area of the mill indicate
that these are the likely sources of cont2mination to the San Miguel and Dolores River ecosystems.
Contaminants found in these were elevated; they were also the same as those found in the ecosystem
and in sources such as tailings, rafflnate storage areas, and onsite soils (Reference 3, Volume 1, page
2-5).
Healthy communities of algae and macroinvertebrates were found in the San Miguel River
downstream of the facility, despite high concentrations of metals in their systems. Although fish
populations were not sampled, water quality in the area is below the State of Colorado’s standards for
fish, due to the presence of contaminants (Reference 3, Volume 1, page 2-5). Studies conducted as
early as the 1950’s noted poor water quality in the area. Incidences of oil patches, high levels of
suspended solids, high water turbidity, and reduced fish catches were pointed out by previous
researchers, including Tsivoglou (1955) and Nolting (1956) (Reference 3, Volume 2, page 5-90).
Air
Air contamination at the Uravan site was not addressed in the Remedial Action Plan. However,
provisions for monitoring for radioactive particles during and after site reclamation are discussed.
4,
11
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Mining Waste NPL Site Summary Report
TABLE S. EXPOSURE ROUTES TO HUMAN POPULATION FROM
CONTAMINANTS AT THE URAVAN SITE
Indirect Exposure Routes
1. Inhalation of radon gas and both radiologically and nonradiologically contaminated dusts
which become airborne.
2. Ingestion of contaminated sediments and soils.
3. Consumption of surface water.
4. Consumption of well water.
Indirect Exposure Routes
1. Consumption of fish from San Miguel or Dolores River.
2. Consumption of produce from private garden harvests.
3. Consumption of milk from dairy cows.
4. Consumption of meat from livestock
Source: Reference 2
vegetation. These contaminants will bioaccumulate as a result of consumption by either animals or
humans that are primary or secondary consumers. The high dispersion of contaminants in the area is
attributed to wind transport of contaminated particles (Reference 3, Volume 1, page 2-3 and 2-4)
REMEDIAL ACTIONS AND COSTS
On December 9, 1983, the State of Colorado brought suit against both Union Carbide Corporation
and Umetco for response costs and natural resources damage under the Comprehensive Environmental
Response, Compensation, and Liability Act (Reference 1, page 1). Specifically, Union Carbide
Corporation and Umetco were required to pay between $3.5 and $4.0 million to the State of Colorado
over a 7-year period. This fine included a reimbursement of the State for fees accumulated as a result
of its prosecution of Union Carbide Corporation/Umetco and its future oversight of the Uravan
facility, as well as compensation for damage to the State’s natural resources as a result of the Uravan
facility. Union Carbide CorporationIUmetco were also required to give a 200-acre ($80,000) pristine
area to the State for use as a natural area by the people of Colorado, and $388,000 of senior water
rights on the San Miguel River to the State and a water trust (Reference 1, page 4). Union Carbide
CorporationlUmetco have also agreed to donate a part of the Uravan facility to act as a low-level
13
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Mining Waste NPL Site Summary Report
REFERENCES
1. Executive Summary of the Remedial Action Plan and Consent Decree, State of Colorado vs.
Union Carbide Corporation and Umetco Minerals Corporation (83C2384); Author Not Provided;
1986.
2. Qualitative Health Risk Assessment, Uravan Uranium Mill, Uravan, Colorado; RA Consultants;
July 1986.
3. Final Report, Winter Baseline Investigation of Surface Media in the Vicinity of the Uravan
Uranium Mill, Uravan, Colorado, Volumes I and II; ER! Logan, Inc.; August 11, 1986.
4. Remedial Action Plan, State of Colorado vs. Union Carbide Corporation and Umetco Minerals
Corporation (83C2384); Author Not Provided; 1986.
15
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Uravan Uranium Mill Mining Waste NPL Site Summary Report
Reference 1
Excerpts From Executive Summary of the Remedial Action Plan
and Consent Decree, State of Colorado vs. Union Carbide Corporation
and Umetco Minerals Corporation (83C2384); Author Not Provided; 1986
-------
EXECDTIVE S1 ?4J4ARY OP TEE RV4EDIAL ACTION PLAN AND CONSENT DECREE
STATE OP COLORADO V. DNION CARBIDE CORPORATION AND
DMZTCO MIN ALS CORPORATION, e3C23S4
T metco’s Uravan uranium—vanadium mine and mill complex is
located approximat.ly ninety (90) miles southwest of Grand Junc-
tion along Stats Highway 141. The facilities occupy a portion of
Club Mesa, to the west of the San Miguel River canyon and the
river canyon floor. During its seventy (70) years of operation
the facility has processed millions of tons of ore and disposed
of millions of cubic yards of solid and liquid wastes. Waste
disposal practices have resulted in wind and water dispersal of
contaminated solids (tailings) and liquids (mill process wastes
and seepage) from the disposal areas. These solid and liquid
wastes contain hazardous concentrations of radioactive material
(uranium, radium, and thorium), heavy metals (selenium, aluminum,
arsenic, cadmium, zinc and others) and inorganic contaminants
(ammonia, nitrate, sulfates and others).
I. TEE W ZDIAL ACTION PLAN
Prompted by an awareness of Dravan’s impact on the natural
resources of the stat., legal action was brought against anion
Carbide Corporation (CCC) and øm.tco Minerals Corporation
(Cetco) by the State of Colorado for response costs and natural
resource damages pursuant to the Comprehensive Environmental
Response, Compensation, and Liability Act of 1980 (C CLA ),
which is also known as ‘Superfund. The state’s pleadings also
contained causes of action under Colorado law for nuisance,
negligence, and strict liability in tort.
Representatives of the state, CCC, and Umetco, together
with their expert consultants and counsel, began meeting in March
1985 to develop a program for environmental clean—up at the
øravan PacUity. The product of these lengthy negotiations is a
350 page document entitled Remedial Action Plan (PAP). The RAP
contain.s a 12—15 year schedule of remedial actions. The cost of
the remedial program, as estimated by defendants, exceeds $40
million.
-------
Stipulated penaltiS in the amount of S2S00$l.O,000 per day
are imposed for environ efltallY SSn5it .Ve violations of the RAP,
which are: a discharge to surface water or ground water, and the
failure to notify the stats of such actual or threatened dis-
charges. (See the discussion of this subject as an innovation
in Part III S rov.)
0. Dispute Resolution .
The defendants shall pay the state’s reasonable costs for
ad udiCatiofl of disputes unless the state’s position was unrea-
sonably taken or maintained.
z. Response Costs, Natural Resource Damages, and
Contributi .
$3.S—$4.0 mill.iofl viii be received by the state from
aCC/ metcO during the next 7 years. The cash payments are allo-
cated in such a way as to reimburse the General Fund for expend .-
turd made in prosecution of this matter, to pay the costs of the
state’s future oversight at the ravan Facility, and to compen-
sate the state by a damage award for injury to its natural
resources. Additionally, defendants are transferring a 200 acre
parcel of pristine land tO the state for preservation as a Natu-
ral. Area. valued by defendants at $80,000. Moreover, the def en—
dants viii convey to the state and to a water trust certain
senior water rights on the San Miguel River, having an approx .-
mate value of $388,000. Finally, the defendants have agreed to
make a portion of the Dravaft Facility available for disposal of
Low—level radioactive wastes from the Denver Radium Sit. and Col-
orado School of Mines. It must be emphasized however, that th .s
part of the agreement is only an from the state’s perspec-
tive; the public will. tave an opportufl .ty to coent on the di.s-
posal location of these waste materials once a sit. is actually
selected by the state.
F. Subsequent !nactmeflts .
My subsequent statutory enactments or promulgations of
regulations will, become incorporated only if they are determined
to be applicable and their inclusion is deemed appropriate by the
Special Master and/or u.s. District Court.
G. Release and Reopeners .
The mutual release between the parties extends to civil
liability for all environmental claims arising out of the factual
circumstances of this case. The release will not apply in the
—4-
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“I
Uravan Uranium MIII Mining Waste NPL Site Summary Report
Reference 2
Excerpts From Qualitative Health Risk Assessment,
Uravan Uranium Mill, Uravan, Colorado;
RA Consultants; July 1986
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I’)
QCAZ.ITA:I;t R:sl< ss s tc.’r
L rava.i Urar t M i i i
Urava , Cojorado
Prepared for:
State of Colorado
Dpar ertt of Law
Office of Atto:rtey General
C Z.A L tigat .or Section
Under s bcortt:act to:
GeoTrans Inc.
3300 M.Ltc el1 Lane
Eculder, Colorado 80301
Prepared by:
PA Conzultants
26050 E. J ison Ci.rcle
Aurora, Colorado 80016
3uly 1986
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“p
.o : zr oci
t netco Minerals Corporation (Umetco, a subsidiary of Union Carbide
Corporation ( jcc), has operated a urani n rn.iU and tailings disposal
site at Uravan in MontroSe County, Colorado. Milling and extraction
o erat orts for radi .m first started at this site in 1915, and continued
more recently for vanadii.n and urani extraction until late 1984; since
then operations at the mill have been te çorari1y suspended. Cperaticrz
at the Uravan site have resulted in the disposal of a large ç.ian: ey cf
il1ing , radionuclide extract cn, and other wastes at the site. These
wastes consist of mill tailings, and raffinate as liquid and crysta.Ls.
During active operations air nissions occur from ore crushing, n l: .r :,
metals extraction and yellowcake preparation. The wastes contain ra:er-
a1s, pri rily meta.ls and radionuclides, which in high concent:at or.s
and large amounts can constitute a hazard to the health and welfare of
h an pooulations.
This assessment for the Uravart site presents the results of a a.1 ta—
t ve h .rr n health risk analysis. This risk analysis deterT iines the
source of contaminants by types and characteristic, location and amount,
- and art evaluation of h n health effects. The hazards posed from the
cotatinants are evaluated for the potential to release contar.irtar.ts,
and the pathways and transport mechanisms for the contaminants after
release. H .m t poou.lations at risk from the released contaminants are
determined from the location, ntm ers, habits and resource uses in tne
region around the site. The final step in the risk analysis is to
esti .te the likelihood and extent of health effects based on the potert—
t a1 Cor exposure and dose to the population at risk.
This potential health risk will be assessed using three time refererces.
The first time reference ass es the present conditions at the site
exist into an indefinite time frame and no r nediaticrt occurs. The
second reference examines risks during the period of active site
ramediation which is expected to occur from 1987 ti1 a roxirate1y the
year 2005. The third time frame is post r iediation, with health risks
assessed in the short—term (for 200 years) and long—term (beyond 200
years).
Risk Assessment — Uravan 1 July 23, 1986
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: the tetravalent state. The ion exchange rc it t...zed
fixed-bed on exchange col rts.
U .rn-barrez solution from the ion exchange passed to the vartadi
recovery circuit, and after the vanadiu was extracted, to fi.nal dispos-
al by evaporation in ponds dispersed apart from the regular tai1 ngs
d sposa1 area. Pregnant solut.on containing about 20 grams of urani
per liter passed to the precipitation circuit.
In order to precipitate the urani , pregnant solut on was fed througr.
tanks in series and heated by direct steam injection to about 1200F.
MITcnia was added to the two tanks, the precipitated yellow cake sL : ry
was thickened, and the overflow so1ut .ort passed through filter presses
to recover any fine product. Filter cake was repulped and fed to a
i iltiple-hearth skinner roaster. The dry yellow cake was loaded into
dri.r using an aut tic device to shut off feed when the dr was
filled.
3.1.4 Tailings and raffinate disposal
- Plant tailings from the thickener circuit were p içed to either of two
available tailings areas alternately to allow settling and recovery of
selutior.s for return to the plant. The tailings ponds are located on a
hillside on Club Mesa adjacent to the nu.ll and are somewhat 1im ted .r.
size. M of late 1984, the tailings area enconçassed approxinately 83
acres containing an estimated 10 million tons of tailings. The U:avan
1.i1l site constitutes a large urani mill tailings disposal repository.
Cons u ntly , the radiological and non-radiological contaminants in the
tailings area represstt the source or origin of the greatest potential
health hazard associated with the Uravan Mill (P LS 1984). The tail-
ings materials are finely grounds acidic and retain metallic and rad c-
active cont inants in a i cbi1e state. The tailings material also
retained waste liquids within the tailings piles. Raffinate is the
waste liquid from the milling and extraction process 1 and contains
a itcni t-ali u.rnn salts, with dissolved elemmtts from the ore and spent
reagents from the process. Two principal areas were used for disposal
of this liquid: storage ponds in the San Miguel River Valley and an
evaporation spray area on Club Mesa. Raffinate crystals. a solid
R.isk Msessn t — Uravan S July 23, 1986
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p..ve: Ponds . Seven unlined ponds constructed in old L.ngs piles
containing 200,000 cubic yards of mill wastes and contaninated soils
that are located along both sides of the San Miguel River.
4. TailinoS piles . ?.bout 10,000,000 tons of mill tailings waste con-
tained in three piles in two sites that are located on Club Mesa 400
feet above and west of the mill site.
5. Club Mesa area . Disposal area on Club Mesa consisting of two clay
lined sludge storage areas, storage nds, raff nate spray evapora—
ticn area and associated containirtated soils; contains 250,000 cubic
yards of raffinate crystals, 150,000 cubic yards of neutralized
sludge, 40,000 cubic yards of contaminated pond rr terial and 44,000
cubic yards of contantinated soil.
6. Mill areas . Two plant locations with surficial contamination; con—
ta n structures, ore stockpile area, equip ent and ancillary wastes;
heap leach site containing 15,000 tons of ore.
7. Town and adiacent areas . Lpcated along San tligueJ. River in va.lley
northwest of mill; contain old tailings and contaminated soil.
3.4 T XCITY J?.LU ION
- Data for various locations at the tjravan site, (Tables 3.1 througn 3.3),
indicate the presence of both non—radiological and radiological conta.i—
nants. Table 3.1 (GeoTranS/ .I 198Gb) lists the ch nical corr os:t:ofl cf
solzd waste materials from several source locatiOns. Table 3.2 lists
the ch nical coi OsitiOfl of liquid wastes onsite and contaminated grou-’d—
water c iled from historical and current data (C.eoTrans/ I l986a).
Table 3.3 is a s rnrrary of concentration of materials in water seepage
that has been contaminated with tailings solution and ra.ffinate seepag2.
The non—radiological and metallic contaminants are discussed in Sect Cn
3.4.1.
Due to the locations of the contaminants, cotential hazards exist via
su5 er1ded particulateS as a result f windb1 rifl releases from the
extensive tailings pile area, from the ore pad or storage area, and via
liquid releases from the tailings ponds. Consequently, it is necessary
to evaluate the toxicity of the contaminants in order to assess potent-
ial health risks. The following toxicological data were obtained
prirarily from the following sources: Casarett and Doull’s Toxicology
Risk Pssessmertt — Uravan 7 July 23, l9 6
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.1
is aiso a ss .bil .ty. The tentia1 for 1 vestock to receive a s ..ff. —
cient dose to pose a health threat to h ns eating meat .&nder present
levels is l i and will rer in la.’ during renediation provided livestock
s exc1 ded from contaminated areas on site. .fter reT ediation, the
long-range risks will : in l unless heavily contaminated groundwater
reaches the surface as seeps which, in turn, are then used to water t t
1ivest ck. In a study of cattle and sheep which drank water contamin-
ated f: n a u:ani n mine, elevated levels of Pb—210 and Po—210 (up to
:o i/kg) were measured in the liver and kidney tissue of the cattle
(Rutter.ber , et al 1984)
Du: g the rened ation period, the PAP (1986) specifies drainage diver-
sion d thes and surface runoff control structures for tra ing sedi ne- t
on all the ajor facilities being reclaimed during this period, In add.—
tiort, d . ’atering wells will be installed in growtdweter zones previously
contaminated by seepage on Club Mesa and in the San Miguel R.ive Va ev.
This corttanu.nated water will be evaporated or treated. P .lso during the
renediatiort period, quality control, and perforinartce evaluation will
direct construction and cleanup activities, and will be used to insure
effect veness of the design and engineering.
irt this qualitative estimete of the health risk involved in this re-ed —
tiort programs, it is ass ed that design and engineering specificat c:-.s ,
required to be developed by the PAP (1986) are adequate to control tne
hazardous materials onsite. It is further asst.iiied that the con ‘ne -:
facilities are constructed and perform as designed.
5.0 JT. TION AT RI.
5.1 HUMAN CV 1i AT UWWAN
Since the closing of the tJravan Mill, the population of Uravan has
decreased from 497 in 1984 to a roximately 50 at the present time. The
current population consists of 40 family meters and 10 single cortstruc-
tion workers (JT! C l9e6). It is ass ed that this population will
increar periodically to a roximete1y 100 persons during the renedia-
tion process. Thereafter, the population would then decreas. to a
rrairitenance crew of around five persons and eventually th. site will be
serv ced from Grand Juncticn. There is also the possibility that the
P..is . Msessment —. Uravan 23 July 23, 1936
-------
.r:o s...:face ard ;:: ...- dwate: and w j cors :e a I :ef .:e
Th ti ne, the mov of these contan ,ated Mter a1s
into pathways and subsequent exposure to h i will reach a low eq li—
b:i state which in the long—term risk should be insig,tificant.
I t c. ong—eer , the two containLflent structures, the tailings piles and
t e SLrta.nk Quarry, will r irt onsite as low r.sks. This is due to the
large ao ts of :ontanurLated materials, both radioactive and nerals,
contained in then. The condit ons, in particularly the tailings pi .es,
will per tu: the slow movement of toxic metals and radionuclides into
surrounding media. The tailings piles will re in acidic so tnat metals
w j be in a soluble state, and an unlined foundation w l a.llow a cw
rate of seepage into groundwater. There is also the low pro :1 ty
that erosion processes may cause a breach in the slopes, causing a
release of solid tailings into hieroglyphic Canyon or the San M g e1
River.
In s ray, the overall potential risks to ht. rart health s moderate if
present conditions at the tlravan site were to be maintained. If unr ed—
- iated, the probability under present conditions of an eventual failure
with an ensuing siç ificant release to the environnent is high and te
: sk to h -.an health moderate due to a r 1l population actually at riSk
in the area. During the short 15 to 20 year period of remedial act v —
ties, : sks are slightly higher due to transport and placement of
contaninated materials, and to open exposed surfaces. In the sho:t-:ern
following r nediation, low levels of risk may exist from residual conta—
minatc J surfaces and gro ,dwater. In the long—ter n, the two containntertt
st:uct res, the tailings piles and the Burbank Quarry, will remain a low
risk potential due to th. chemical and physical characterist cs of the
wastes, and to their somewhat exposed topographic position on Club Nesa.
P.isk Assessrent — Uravan 27 July 23, l9 6
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C ”
Uravan Uranium Mill Mining Waste NFL Site Summary Report
Reference 3
Excerpts From Final Report, Winter Baseline Investigation of Surface Media
in the Vicinity of the Uravan Uranium Mill, Uravan, Colorado, Volumes I and II;
ER! Ligan, Inc.; August 11, 1986
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FINAL REPORT
4INTER BASELINE INVESTIGATION OF
SURFACE MEDIA IN THE VICINITY CF
THE URAVAN tJB.ANZt.JM MILL
TJRAVAN. COLORADO
Vo1t xn I
c Jmrt*Jary i.986
Fiald Ir katigatiOr
Ptspsrsd for
Ths Stats of Colorado
D.partmsnt of Law
OfficS of ths Attor7 sy G.nsral
Prsparsd by
x Inc.
973 South Stats tghvsy
Login, UT 8432L
August 11, 1986
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es l:s of analyses f r nesa : p soils 1ic cated si; f arit ni ’-sa
relationships between distance from the Uravan mill site anø sofl
contaminant Concentrations for arsenic, barium, caø m1um, leaa, nickel,
vanadi.sm, zinc, riø gross beta in t e ENE sector, for barium, ca ium, lead,
vanadium, and zinc in the NNW sector, ‘or arsenic, cadmium, nickel,
vana i m, arc zinc in the WNW sector, arid various comolnations of one to
four metals in the other five sectors. S gnificant inverse re]a:,ons i;s
etween distance and vanadium concentration exist f r all se :: s.
Regression analyses also indicated significant inverse relationsnips oe: ee1
distance along the river valley fran the mill and soil concentrations f:r
Cd, Pb, V, and gross al pna in river bench soils. The most wioespreac
contaminant Is vanadium. Further analyses indicate that the Uravan mill r as
had a greater effect on soil concentrations of these contaminants tnan
geologic parent material or mine wor irigs in the area.
Widespread soil contamination on the mesa taps iS inferred t.o oe :-e
result of contaminant transport by winds reflecting regional wind at:a--s.
The effect of local valley wind patterns and strong inversions is reflec:ac
in soil contamination of bench and riparian soils.
Soil contamination above levels known to be toxic to plants extenos t,o
a distance of 7000 test from the Uravan mill site. Concentrations of
contaminants in soil at evel above background were detected to a distance
of 28,000 feet fra the site (points of farthest data collection). :t is
inferred tMt In areas white soil contamination levels exceed levels toxic
to vegetation that plants will exhibit toxic symptoms and reduced
productivity, It Is also inferred that the vegetation will contain elevated
levels of metals and redionucl ides due to increased exposure in contaminated
areas. Data froa past studies (Section 4.2.2 In Volume II of this report)
2-3
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:z jnurn, leac aric nicKel Ifl Sediments showed large increases a acent : :-e
Club Ranch P n s.
0iverse ano a Pareflt1y heal:.’iy flunitles of algae an
iacro1nvertebra:es were f un in t e San Miguel River upstream
downstream of Uravan. Concentrations of rnetais in these organisms were
1;her downstream of Uravan in the San Miguel River than upstream. -ese
induce cadmium, copper, nickel, zinc, aluminum, silver, leac, ‘i
stront um. These Increases Inolcate that sources of contaminants to :‘e ai
fliguel River occur at Uravan anø that bloaccumulation of these is :a ’;
place in tne aquatic organisms. Increases In tfl 5 of these same
contaminants were noted in the Dolores River organisms downstream from :re
confluence with the San Miguel River. Macroinvertebrate densities obseriec
in this sudy indicate dramatically improved environmetal conditions over
those in the 1960’s and early 1970’s when nacroinvertebrates densities were
extremely 1 w.
Ffsh populations were not assessed for this study. Wat.er samoles
collected in the San Miguel River in and below Uravan contained leveis of
aluminum, cadmium, copper, lead, silver, and zinc that exceeded the existing
State of Colorado standards for,flsh. Aluminum was found tO exceed
standards for the entire region of river from u2t below Mturita to the
confluenci with thi Dolores River.
Malyses of seep water, precipitates and dry wash alluvium Indicate
that thes are thi likely sources of contamination to the San Miguel and
Dolores River ecosystems. Contaminants found In these were elevated anc
were the same as those found in the ecosystem and in sources such as
tailings, raffinati storage areas and on—site soils. Direct re’eases of
contaminated water fr s the Club Ranch and River Ponds Into the San Miguel
Rlvtr were also observed and sampled by ERI during thi study.
2—5
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FINAL REPORT
4 NTE EASEI INE INVESTIGATION CT
SURFACE MEDIA IN THE VIC NIT Y OF
THE TJRAVAN IJRANItTM MILL
tJRAVAN, COLOR.A O
Vo1u.zn ZI
I r, of Historic.a.L I for a tiort
s State of C .orado
spar sn: of Law
Off s øf :hs At:3r isy Gn.ral
? *parsd b r
I .cgin, Inc.
g73 South Stats MgPtway
I E.ø$a. S432
I
Ai. St 1, L936
I ERII
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2. SCt C cRACZ IS CS
2. e ai —:ces : n’: ”a :
‘ i eral rec3verJ operaioris s:ar:ac a: : te raean si:a in :;:s. —
S :arcar : e.mical C m any 2rocessed ares : er fcr ec3ve J f rac . ,. — s
o era : cn as closed in :922.
:n :923, a subsidiary f . nion Car i e C3r orat . cn, _ . . :a a:-
mcany, urc asec :ne i 1 and egan rocessinq re f:r anac1 . ‘- ‘
and raCu..m were discar ed in ne :ailinqs material. : 3 5, j.s. /a3: r
a new miii arid estabhshed :he tOwn of Uraian to or:v e ous ng :—
or ers.
: t ie early 940’s, tne U.S. Army Cor;s of !ngineers :eçan r:cess ;
:ne discarded tailings for recovery of uranium for t e Mannat:an Pr ec:.
This processing continued until 1945 uhen the market for uranium deci med
ano the mill was closed. The mill reopened in 1948 to pr auce uran ..ri ce-
a adioactive Materials License issued by :ne Atomic £iier;y C.rrriss :n.
: 1356, union aro lce adoed a solvent extraction prccess ‘or c i
:o :rie uranium process. The mill c:nt nue0 to process cres ‘or randm rc
anaoium until it shut down in November 1984 (0ames anc Moore .373, E..
964).
The ore processed at the Uravan . ‘ i1l contaIned .15 to 0.25 u 3 3 3 .
tO Za V 2 0 5 (Fischer and Hil pert 1952). Other components of tne ore mr.ci.cec
clays, sandstone, limestone, shale, and sall amounts f :y:e.
molyodenite, and copper minerals (Moment 1981). eagents .sseo in
various mill processes included sulfuric acid, anhydrous a onia, s c ..mi
chlorate, hydrogen peroxide, tertiary amine, sulfites, barium chloride, scca
ash, Polyox, and kerosene (Oamu and Moore 1978). Raoionuc’ es
present in the ore includs radon gas, radium, tnorium, polonium, leac ‘c
others in the uranium—238 tcay series (Figure 2.1-1).
0 2..
-------
ThDle .5—1. :—s: ’ :: cs : :r ( es ai: ccre
?a: e:e
C. n:a
On 3asis
?a;a e e
On 3as s
-C
0.0002
CL
504
0.06 — 0.12
23 —
/ 0
‘
3 — 12
11 — 36
3.3
C
g
C
0.C9 — 2.
<0. OCC I
C.3C —
1.8 —
Nd
e
0.02 — O. 5
Mo
0.CCC
Na
0.01 — 0.13
0.336
Ca
0.005 — 0.22
0.108
A
<3.0001
4
.
J
J WV J .l%4
o..
<3.305
<0.5
C:
0. 02 — 0.CO’
Ni
3.02
C:ga i:
—::3
0.3:
17.04 pc_,’ 3
c
Nd a)
(a) Nd • No: da:ec:able.
pY
-------
aoou: 27 ee: :eeo. The c s:as a e jnce 1 a1, :j 5 ‘ee: o
over sancs:one oe r:ok.
2.5 ‘‘e ‘ ccs
The iie’ P r s ncluce seve’i I oL.r.c en:s oca:ec along : e San ;e
ver oe1 :‘e infl si:a ( Fi; re 2.2-: . F,ie of :-e ;cr a e on :-e ii:
sloe of : e San Miguel ver arc 2 crcs on :ie co osl:a :an . The ;cr:s
mere ::ns:r .c: on oLo ail rgs as y excaia:rg 1:o, arc ri s iie : ses
:lrougn, :-e tail ings iia:ar’ai s Then anc , s5oc’a:es , . —
excava:0n5 mere mantie nit, soil. ‘e ncs on tie sice of : e -‘.e-
nave oeen sec as se:thng basins for waters collectec witlil :ne ,,iH ar
;ricr to clscnarge into the San Miguel River. The t oncs on z e o:;os :a
s ide of the river have seen usec to store neutral izec sl cge ;rior to
cisposal On Ci o Mesa. I: has been estlma:ed that aoout 2CO, CO c c jaros
of cOntininated ateria1 is :ontalned in t e River Ponds (Then arc
Associit , .983).
The Riier ;oncs are sit. a:e nlnedlately ac acent to tie San M ;e
ive oeicw tie level of t e ;otant al rnax1mt Then inc sscc a:es
:9a2 . S: rn events an runoff will cause winc orne inc rec1 :a:eo
::mOouncs to enter the San Miguel River syst . This pericoic loac ng iaj
amount to a substantial input.
2.9 L :uld Mill Eff1u.rrt
L iuic dischargi from t.”ie iill has occurred at several points 1nc c1;
3 pernit:e discharge points, :ne sewage plant outfall, seepage from :e
Club Ranch Ponds and tailings ponds and a nia b r of process solution spi s
(PEL R .5 .384).
2-:3
-------
Uravan Uranium Mill Mining Waste NPL Site Summary Report
Reference 4
Excerpts From Remedial Action Plan,
State of Colorado vs. Union Carbide Corporation and
Umetco Minerals Corporation (83C2384); Author Not Provided; 1986
-------
AP?ENDZX :
az zD:AL Ac :cN
S e of CoLorado vs.
Union Carbid. Corporaciort and
U .tco Minerals Corporac.on
83-C-2384
-------
U.bt. It I coni.
!eII1R !_eQn _ !! Ii!!U1Q! !
NLIIISAL UAJ ION
O 81 1*88 11181$
IIMOI 11102k
I S ACM
a. .,t.a
1 1181$
ItlOic
“AC M
AU • Slilal
IPuV AsIA 2
rawcIai £
$PIA ASIA 4
ravclai C
SISAl ASIA 8
ra.fla. C
.
10
ci 4
180000
- -
4*0000
21
330000
84
MM
801
NJ ‘CO
lrJ. Jpk.. pcIlq
1080
ROO
*120
4600
010
0000
0.6
ND
520
9300
6
NO
1 0
6200
0.6
ND
1040
Gross bits pcIl
160
1000
*030
4400
620
290
*00
560
1k- hO 1 pcI ! ,
890
U-nIt pcllo
22
21
43
11
64
1.6
1.9
4.1
Oats Iros III *986 Sas.I In. Study
-------
1* 114 S I 1 (CufihInlIsdI
uI £114 CIUS CIUS
IASOISAII 14111 1*1 1 I*uCI 1 0 10 $ I*NCI P9 101 1*1(1 PUSh Pl1C$PlI*II$ £1111114 th u 1*1(1 111(1 £ 10 1 I*u I:i £114 SINCe (I l lS SflCI Liul 14uC. (Ills .6l1.
$914 19111 l Isa Ill l9Ia ivs 2 s ca ,ouos • cc 11111 59 1411 III w.i 14 v&,a ala m*t .j
- — ——--—-- --—- — - -__I!S4?_ -______ _i - - - iv ,! __in • , • s o..
. ! UtMilU. Si ’I
I I SKIM 9 )999 141949 4 6 16 I U1I
4 1 I I $ 1. 59 S I $1 4 $
4 1 1 ) 1 5 50141 1, oo. 1110$ i*iu ‘.yooo .svs.u
a
4 14 )1 4111 109 19 4104 IU I s oo 1 160 161.
£414 4551 $1191 1 1 $4.1 livo lile jul.
10 1 14 919 M I s.
I t z .co (I 0 (I I I . ,
I I
I*II IUtI. •c$l4
a us ala 44 LII 2 10 14 11 4) 96 2 6 0 49 u
II us $14001 11155 114005 16 1 50 4 5 1 I $11 1 I I I a I v
• 655 41 )1 51 55 Sill $600 1 10 4 961 Ii uo lieU siu
•8 115 ISiS $14.0 S $
P. 50 44
4 1s1i *IjIS
(I . .. Sal.
• lal.165 1 106.S •n an.s,In• ( sn 4 SOIl £.r.s. .1 d.l c.Il.cled b.I ....n I llIll Ia .nd IlIlil
1 etC *114M 1 SiivsiaiannS.5 NISlISPIAS Sass SsvSae $91). 0(1 16 5.45465).. • Ssd 416114
$ lass. Iav4a InIs5 spasIc d hs sII599 Is iIr nSa . IllS l,I the S I land ISq..ld .
595(145 .4 hIs ho. .4. pash. uihssSsh bsIN.sn 5.164. $91 1 I $u .r 5914.
4. $S4i(SSI5SlblI 4 1 4$nssrSns ( any. 1951. £v.r. 5. •I hats Iss sSa ,sn4 . co4l.,.d 65115.6 IU1$lII . 6 4 SiSi50.
I Ill 15550. 5914. £vs,s. .4 IS p.shphs.i . • l.s 556.6 •d) 56sPlI i• 51 56 •hI CIl I 8 Ponds. isl9..1p 5944 1. I. .4... $1.01 I I
S II I l ss $954. ISA.S. • IaI •i Ii. 8.65.5.. £1551 4 1.51115 o 1 1 19 .d a*aiiI So £hs 5.1168 p64. 1 01V. $954. 15.5115 III. LACQI
I 55$ 155..• $944 1 1 14 1s fab isapIs. lIssIns d116 .44.6.11 5 5. Pond 1. J . 6ual . $954 IaapSs all. SAIlS.
• I a $915. 5og 5 .o, 5.55 balsam is . 4 and Ch l.nsl Ponds.
• $s and N.m. 91$ Nash., sail b14...an Ci 5.666 PoisdI and Ian Ulsual ussr
-------
2 4 Y RCGZOLCGY
hs regional ground water hydxogeolagy of the ravan area
has been de ri bed. in studies done for anion Carbide by :aes
and Moore (].978), International Engineering Coapany (:981) az.d
z.nvirologic Sy.tesa, Inc. (1983b). These reports may e
ref erTed to for additional discussion. This s’iary c1.. es a
descr ptiofl of water-bearing zone., aquitarda or confin g
layers, and their charactsriitics and interrelationships ar.
dx*ws upon the geologic descriptions given in Section 2.3.
Aquisrs in the craven area are generally U. tsd to the
hydxostratigraphic anita which have sufficient peraeahility to
t jt g owtd water. These sandstone units generally have
variable psrsesnil.itie$ due to grain size, fract rinq, scrt .
and aecondazy esianting. Gro and water in the region is
trans itted via secondery (joint) pexaeability and primary
(interrtnuler) per2ebility._ Secondary perseability in the
region tends to be directional . and highly variable. Mesozoic
Formations capable of trsasiittirig water in sconosic amounts
includs the aJc0ta and 3urro Canyon Formations, the Salt Wash
masher of the Morrison Formation, and ha Entrada, ayenta, ar4
Wingat Sandstones (Figure 2.3-].). Mesozoic strata which a:.
not capable of txanuittinq water in .con ic amounts and which
are there for. cansidared açiitarts indluds the Brushy Basin
member of the Morrison Formation, the erville, inle, and
Moenicopi. formations (Figure 2.3—1).
31.
uy
-------
3.3 CCNC!PT AL ITTR MOD!LS AN AQCIflR CCN A ’: N
3.3.3. C nce tual Acu fe Models
The followinq discussion describes a ncsptuaza cf
t e yd geologic sodsi. for ravan based upon data qer ex asd ..‘
the :anuary 3.986 8331 field investigation. While the f.,
discuss .on focuses on the hydrologic e aract.ristics of the
ayenta and Wingate stx*tigr*phic units, it is inportant
recoqnizs that the Kayenta and the Wingats are in direct
hydrau.3.ic connection and they fora a single açiifer unit. i ey
features of the hydrogeoloqic ad.1 ax.: 1) a 3. -per eab .3. y
Xay.nta-Wthqats seçi.nc$ beneath Club Mesa, and 2) a
Xay.nta-Winqate sequence in the River Valley which has a
high—pera.a.bility in its upper portion (fractured ayenta) a r.d
generaLly has l.ov-psresability at depth (less-fractured
Wingate). The sandstones beneath Club Mesa and at depth
beneath the rivr valley ax. not extensively fractured and .ia s:
is trans.ttted through the sandstones by priaary porosity and.
psrasa.bility. Thu. sandstones contain groundwater in storage
but generally release only n all asaunts of groundwater to
properly constructed wells. Zn contrast, the highly fract . rsd
aysnta. ?oraatior* in the River Valley yields relatively .ar s
aaounts of ground water. Aquif.? tests of wells V-76$, 7—769
and P —L3 support this general model. • Observation v.1 Is
P-lS, -16, - 1 ,7 aM -11 were drilled to test the aquifar
properties of the Xayenta and the Wingate and to collect water
sasples froa the aquifer in these locations • The data fron
83
-------
proqran may be feasible.
ct ir anta in the river valley occur in the fracture
voids in the Xayenta-Winqate sequence and to some extent t
the sandstone rock matrix. Studies by C andra ( 98l) !:r .
Carbide, evealed that within the zone of conteninat n fr: a
Ranch ponds, ca.Lciun carbonate-sulfate crystals save f:r ed.
along the fractures. The significance of these crystal. gr:vths
on the fractures is that the bleed rate of contaninants int e
eractur.s frog the matrix may be relatively slow • However, r.o
extensive study baa been made to confi the extent or
siqni fiance of crystal growth in the fractures. Menitor .nq ef
the groundwater remedial action viii provide the best in-
formation on this issue.
In this type of regime, a groundwater restoration plan
can concentrate on r ving contsm.thanta fr the fractures ef
the sandstones and rely on a slow bleed rate from the matrix t
remove additional contaminants • The sandstone matrix itself
produces very little water relative to the production from e
fracturee. Thus, constructing p ping v.lla in the area of
contamination in the vicinity of the Club Ranch ponds, will
remove most if not al l . of the contamination that can flow freely
to the veil, vitb ’ a relatively short period of tins.
85
-------
Spray Area. Infiltration travels iJ t0 the und .rlyj ng
intuy and exits along the mesa rt2 in seeps and
Vertically dovn tovard the nderlying açaifers. In the area
the C .u.b Ranch Ponds, ragftha:e infiltrated the suxf c a1.
ater a.Ls and the Xay.nta Fer ation directly fro the
the ponds. In ti a this conta.mination a1.ti ately discha es
the San Mig el River.
analyses from perched 1.i uid on Club Mesa id ca a
that some of the raffinat. seepage has been neutraljze4 by
reactions vith ths sedimentary rocks (7.zzvtro1.oqic Systas,, : c.,
1.983*). Thea. analyses also ahoy that the perched 1.iq id.
contains elevated levels of su.lf at., chloride, potassium,
sodium, magnesium, a onta, nitrate, zinc, vanadium, selen.. ,
uranium, arsenic, and mercury. Water quality information fr
ths past monitoring program has .hovn that the total dissolved
solids concentrations of fluids in the Salt Wash on Club Mesa
range from l,38$ to 48,914 milligram. per liter (mg/i), sulfate
concentrations ranged from 30$ to 1.7,30! mg/i, Iania
concentrations ranged from less than 05 to 890 mg/i, and the p
ranged from 3.4 to 1.2. Elevated Levels of sulfates, maqnes2.. ,
chlorides, metals, radionuclides, and other inorganic
constituents ax ’s prss.nt. Wells in the Salt Wash on Club Mesa
from which CC/ matco has cal.1.ected these data include wells
V—763S, V-7643, V 765 and E-7.
Water quality sampling completed o V.768 and V-769 show
87
-------
g owtdwster çaslity axe available. Th data indi te that
le.icags from the Cl.ub Ra1%cb Peztds baa .tqrated into the Kayer-a
Fo atjon js wAoving generally in a down-valley directiort.
Water levels in observation wells also indicate that the
direction of ground vater flow is generally down—valley artd
toward., the river. Total dissolved selid.s (T S) eoncsntrat . s
in the obs.xvatien wells range froa less than 15,000
per liter (q/l) to as auch as 170,000 mg/ I. in wells
downqradtsnt frog the Club Ranch Ponds • Radionueljdes,
dissolved metals, and inorganic contazina.nts are also present a:
elevated l. .l. in the aquifer as shown by monitoring well.
analyses dovngradient of the Club Ranch Ponts (see Table
Bacicground (unconta3inated) groundwater in the Xaysnta ?or at :r
baa T S coacantrations in a range froi 200 to 500 sq/i as shown
in wells p-l, p-4, G-blocic, and F-block.
89
-------
•.5 :;) 2w—
TABLE 3 • 3- i. GR0 ND WATER QUALITY AT AVAN COMPARING GROUND WATER
SA1 LE RESULTS FOR CRP-4 (BACXGROtIND WELL) AND C .P-2
(CONTAMINATED WELL)
PAR)J TER UNITS RP—2 - ‘ S
Date 1 1./15/84 10/18/84
Sample Type Pumped Pumped
Tap Casing E1.ev. ft. 4941.980 4995.650 0.301
B. Casing E1.v. ft. 4891.980 4935.650 0.301
Ph r.atjc Elev. ft. 4927.880 4959.950 0.301
Temp. C. 14 14 -2.3C0
Cand. 625 C umho. 17,136 365 10.000
pM Units 6.64 7.58 0. .00
TDS mg/i 27,090 272 10.300
Sal. Sulfates mg/I. 18,560 28 1.0.000
Sal. Chlorides mg/I. 1,420 4 10.300
Sal. Sodium mg/i 783 19.6 0.130
Sal. Calcium mg/i 494 45.4 10.300
Sal. Potassium mg/I. 378 10.1. 0.100
Sal. Nitrite/N mg/I. 0.02 <0.02 o.ico
Sal. Nitrate/N mg/i 2 <0.04 0.130
Sal. Ammonia mg/I. 1,610 0.2 1.000
Sal. Zinc mg/I. 0.208 <0.02 0.020
Sal. S.l.ni mg/I. <0.250 <0.01 0.010
Sal. Magnesium mg/I. 1,202 22.1. 0.100
Sal. Manganese mg/i 6.63 0.028 0.050
Sal. Iron mg/I. 26.8 0.059 0.025
Sal. Carbonate mg/i <1. <1. 1.000
Sal. Bicarbonate mg/I. 1,960 258 1.000
Sal. U—Nat. pC/I. 470 <3 0.200
Sal. Th—230 pc/I. 0.20+0.50 0.00+0.40 3.100
Sal. Ra—226 pc/I. 2.40+0.50 1.10+0.40 0.310
Sal. Pb—210 pc/i 0.40+0.90 13.00±2.00 4.300
Sal. Po—210 pC/I. 0.i.0 0.60 —0.50+0.90 1.000
Zinc’ m g /I. 0.63 <0.01 0.01
Copper’ sq/I. 0.07 <0.01 0.01
Arsenic’ sq/i <0.01 <0.01. 0.01.
Mercury’ sq/i <0.0003 <0.0003 0.0003
Cadmium’ sq/i <0.01 <0.01 0.01.
mg/I. <0.01 <0.01. 0.01.
L.ad’ s q/I.
-------
Mining Waste NPL Site Summary Report
Whitewood Creek Site
Lawrence, Meade, and Butte Counties, South Dakota
U.S. Environmental Protection Agency
Office of Solid Waste
June 21, 1991
FINAL DRAFT
Prepared by:
Science Applications International Corporation
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
-------
DISCLAIMER AND ACKNOWLEDGEMENTS
The mention of company or product names is not to be considered an
endorsement by the U.S. Government or by the U.S Environmental
Protection Agency (EPA). This document was prepa.red by Science
Applications International Corporation (SAIC) in partial fulfillment of
EPA Contract Number 68-W0-0025, Work Assignment Number 20.
A previous draft of this report was reviewed by Michael McCeney of
EPA Region VIII [ (303) 293-7169], the Remedial Project Manager for
the site, whose comments have been incorporated into the report.
-------
Mining Waste NPL Site Summary Report
WH1TEWOOD CREEK SITE
LAWRENCE, MEADE, AND BUTFE COUNTIES, SOUTH DAKOTA
INTRODUCTION
This Site Summary Report for Whitewood Creek is one of a series of reports on mining sites on the
National Priorities List (NPL). The reports have been prepared to support EPA’s mining program
activities. In general, these reports summarize types of environmental damages and associated mining
waste management practices at sites on (or proposed for) the NPL as of February 11, 1991 (56
Federal Register 5598). This summary report is based on information obtained from EPA files and
reports and on a review of the suimnary by the EPA Region VIII Remedial Project Manager for the
site, Michael McCeney.
SiTE OVERVIEW
The Whitewood Creek Superfund Site is a mine tailings contaminated site located in Lawrence,
Meade, and Butte Counties, South Dakota, on an 18-mile stretch of Whitewood Creek that begins at
the Crook City bridge south of the Town of Whitewood and ends at the confluence of Whitewood
Creek and the Belle Fourche River. From the 1870’s to 1977, tailings and untreated wastewater from
gold mining and milling operations were discharged into Whitewood Creek and were subsequently
deposited along the creek’s floodplain. Twenty-five to 37 million tons of tailings were deposited over
an area 50 to 300 feet wide on each side of the creek, and to thicknesses ranging from less than 1 to
15 feet (Reference 1, page 1, Reference 2, pages 1-8 and 1-23). (See Figure 1.)
Arsenic and cadmium are the contaminants of greatest concern at the site (Reference 1, page 19)
Copper and manganese have also been reported at concentrations exceeding background levels, but
which are too low to be of concern to human health (Reference I, page 12). Elevated levels of
arsenic, cadmium, and other metals have been found in the tailings deposits, the alluvial materials
underlying the tailings deposits, and the surface soils on some of the irrigated lands within the
floodplain adjoining the tailings deposits. Contaminants have been detected in the alluvial ground
water under the tailings deposits, surface water, surface soils, and vegetation (Reference 2, pages 1-
22 and 1-23; Reference 1, page 14).
The total land area of the site is approximately 2,018 acres. The site is mainly woodlands; but the
land that is not wooded is used for agricultural purposes and residences. The residences are scattered
along both sides of Whitewood Creek. Based on 1988 data, 22 households and 5 vacant residential
1
-------
Mining Waste NPL Site Summary Report
properties are located within, or in close proximity to, the site, with a population totaling 85 (63
adults and 22 children). Eighty households, with a population of 283, are within 1 mile of the site
located on either side of the creek, and 168 households, with a population of 647, exist within 3 miles
of the site. The town of Whitewood, located 1 mile west of the site, has a population of 821
(Reference 2, page 1-16; Reference 1, page 1).
OPERATING HISTORY
Homestake Mining Co. (Homestake) first began gold mining near Lead, South Dakota, in the late
1870’s. Approximately 1 billion tons of ore were produced during the operating history of the site.
Mining operations extend to a depth more than 8,000 feet below the land surface The first milling
operations used crude methods to crush ore and recovered gold by gravity or by amalgamation with
mercury. By 1880, more than 1,000 stamp mills were employed to crush the ore to a course sand
size. In the 1920’s, ball and rod mills were brought into use at the mine. The ball and rod mills
created finer-grained tailings, or “shines.”
Mercury amalgamation was used primarily until 1971, when cyanide began to be used exclusively. It
is estimated that between 1/8 and 1/2 ounce of mercury per ton of ore crushed was lost, with 50
percent of this being discharged in the wastestream (Reference 3, pages 1-1 and 1-4)
Tailings and untreated wastewater were continuously discharged into the creek during the 100-year
operating history of the site, excluding a 5-year period during World War II when the mine was
closed. In 1963, up to 3,000 tons of tailings and 12,500 tons of water were being discharged per day
into Whitewood Creek Tailings were discharged directly into Whitewood Creek or its tributaries
from a number of mine operators until approximately 1920, after which Homestake was the only
source of tailings discharge (Reference 3, pages 1-1 and 1-4).
After 1935, sand-sized tailings were typically used to backfill mined areas, and the “shimes,” as well
as some course-grained sands, were discharged into Whitewood Creek. This practice continued until
1977 (Reference 1, page 3). In 1977, Homestake constructed a tailings impoundment in the upper
reaches of the Whitewood Creek watershed at Grizzly Gulch, to treat residual slimes and process
waters. In December 1984, a wastewater treatment system was put into operation to treat waters
from the tailings impoundment and the mine. The plant utilizes rotating biological contractors to
remove cyanide and ammonia; iron precipitation and sorption to remove metals, and sand filtration to
remove suspended solids. The solids are returned to the tailings pond and the water is discharged
into Gold Run Creek, which runs into Whitewood Creek between the towns of Lead and Deadwood.
This discharge is monitored to meet requirements of the Clean Water Act (Reference 1, page 3).
3
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Mining Waste NPL Site Summary Report
adjoining tailings deposits; surface soils in residential yards, gardens, and driveways; alluvial ground
water under the tailings deposits; surface water, and vegetation (Reference 1, page 14)
Ground Water
Three primary aquifers exist in the vicinity of the site: a shallow alluvial aquifer and two deep
bedrock aquifers. The bedrock aquifers are separated from the shallow aquifer by up to 1,000 feet of
relatively low permeability shale. Hydraulic connection between the alluvial and bedrock aquifers is
believed to be limited. Water supply wells in the bedrock aquifers tested during the Remedial
Investigation did not contain contaminants from the tailings deposits (Reference 1, page 12)
Within the shallow aquifer, the water table generally exists in the natural alluvium except during wet
periods of the year when it may rise into the tailings. For most of the year, ground water flows from
the alluvial aquifer into the creek. During high creek flow, lasting from 2 to 8 weeks each spring,
flow is reversed and water flows from the creek as far as 200 meters into the alluvium (Reference 1,
page 12).
Ground water in the tailings deposits, and in the alluvial deposits beneath the tailings, is of greatest
concern at the site. The alluvial aquifer and shallow shale bedrock within the floodplain but outside
the immediate influence of the tailings, and the alluvial terrace deposits that are upland from the
tailings and the floodplain, appear to be uncontaminated (Reference 1, page 12).
Studies completed by Homestake, the results of which were published in “Mineral and Energy
Resources” in 1986, showed that arsenic in the tailings is very immobile and is being released and
transported very slowly and in very small amounts into the downgradient alluvial aquifers, the only
ground water to exhibit elevated levels of contaminants (Reference 2, page 1-68) Levels exceeding
the primary drinking water standards and the South Dakota Drinking Water Standards (DWS) have,
however, been recorded [ with a maximum arsenic concentration of 0.78 milligrams per liter (mg/I),
which is above background levels] (Reference 1, page 16). Movement of arsenic from the tailings to
the ground water results from dissolution of arsenic during those times of the year when the water
table rises into the tailings; dissolution of arsenic from precipitation passing through the tailings, and
incorporation of tailings particles into the alluvium, which probably occurs as the tailings are
deposited. The current slow movement of contaminants could continue for thousands of years
(Reference 1, page 16)
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I
Mining Waste NFL Site Summary Report
material; importation of taihngs material for use as driveway base, and/or overbank sedimentary
deposition of tailings material during past flood events.
Air
Preliminary calculations in the Remedial Investigation/Feasibility Study completed for the Whitewood
Creek site indicated that the concentrations of contaminants and the potential for exposure through the
air pathway was too low to be of concern (Reference 1, page 19).
ENVIRONMENTAL DAMAGES AND RISKS
Systematic studies of the Whitewood Creek area by the South Dakota Depamnent of Health (begun in
1960) quantified the solids and cyanide loading to the creek and recommended further studies In
1965, a study by the South Dakota Department of Game, Fish and Parks determined that aquatic
bottom organisms were not present in Whitewood Creek downstream from the waste discharges
Several additional studies, which focused on the possible serious environmental hazard created by
mercury contamination, led to the discontinuance of mercury in gold recovery operations in December
1970 (Reference 1, page 4).
In the winter of 1974-1975, approximately 50 cattle in a dairy operation adjacent to Whitewood Creek
died of unknown causes. A later study concluded that the cattle had died of arsenic toxicosis resulting
from the consumption of corn silage accidently contaminated by mining wastes that had been
incorporated into fodder during silo-filling operations A study published in 1978 found arsenic
concentrations ranging from 2.5 to 1,530 micrograms per liter (jigll) in ground water from areas with
large tailings deposits (Reference 1, page 4). As a result of these studies, it was concluded that the
Whitewood Creek area would remain highly contaminated until the discharge of tailings was
discontinued. This resulted in the construction of the Grizzly Gulch Tailings Disposal Project by
Homestake, which became fully operational on December 1, 1977, producing a dramatic
improvement in the physical appearance and quality of the creek waters (Reference 2, Volume I,
page 1-9, Reference 1, page 4)
The potential life-time excess carcinogenic risks from exposure to arsenic through ingestion of soils
and ground water within the site (for both the representative and maximum exposed site resident)
were determined to be unacceptable. For the representative and maximum exposed site resident,
ground-water risks were determined to be 1.9 x l0 and 4.4 x 10 , and soil risks were determined to
be 2.4 x 10 and 2.6 x 10 , respectively, all of which are greater than the acceptable Comprehensive
Environmental Response, Compensation and Liability Act (CERCLA) level of 1 x 10 (Reference 2,
7
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Mining Waste NPL Site Summary Report
properties) within the contaminated fringe areas (Reference 1, pages 32 and 40) The major
components of the selected remedy include:
• Cover and/or remove soils in the existing residential areas containing arsenic levels of 100
mg/kg or greater.
• Restrict future development in the 100-year floodplain and tailings deposits as provided through
the county ordinance
• Prohibit excavation of tailings deposits for other uses and prohibit excavation of remediated
areas through the county ordinance, however, mining would be allowed subject to the
regulations of the State of South Dakota.
• Refine knowledge of the extent of contamination and delineate the 100-year floodplain.
Provide detailed maps to define site boundaries and specify activities to support county
ordinances.
• Set up an educational program to inform people about hazards presented at the site and ways to
decrease their personal exposure.
• Continue enforcement of the ban on installation of water supply wells within the 100-year
floodplain (this is already prohibited by a state regulation)
• Continue monitoring the surface waters of Whitewood Creek for significant releases of
hazardous substances.
• Resample remediated residential areas after major flood events (Reference 1, pages 28 through
32).
The estimated net present worth cost for the selected remedy is $882,813, with capital costs totaling
$1,028,000 ($581,000 of which will be spent during start-up and $447,000 of which will be incurred
over the 30-year period). Annual operation and maintenance costs are estimated at $12,000
(Reference 1, page 40).
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Mining Waste NPL Site Summary Report
REFERENCES
1. Record of Decision for the Whitewood Creek Superfund Site, James J. Scherer, Regional
Administrator EPA Region Vifi; March 30, 1990.
2. Feasibility Study, Whitewood Creek, South Dakota; EPA Region VIII, December 8, 1989.
3 Whitewood Creek Study, South Dakota Department of Water and Natural Resources; EPA and
Homestake Mining Company; November 1984.
11
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4 ’
Whitewood Creek Site Mining Waste NPL Site Summary Report
Reference 1
Excerpts From the Record of Decision,
Whitewood Creek Superfund Site;
Jam J. Scherer, Regional Administrator
EPA Region VIII; March 30 1990
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RECORD OF DECISiON
ATTACHMENT A
WHITEW000 CREEK SUPERFUND SITE
DECISION SUMMARY
MARCH 30, 1990
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1ECORD OF DECISION 002131
MARCH 30, 1990
DECLARATION STATEMENT
SITE NAME AND LOCATION
Whitewood Creek Site
Lawrence, Meade, and Butte Counties, South Dakota
STATEMENT OF BASIS AND PURPOSE
This decision document presents the selected remedial action for the
Whitewood Creek site in Lawrence, Meade, and Butte Counties, South
Dakota. This document was developed in accordance with the
Comprehensive Envi.ronmental Response, Compensation, and Liability
Act of 1980 (CERCLA) , as amended by the Superfund Amendments and
Reauthorization Act of 1986 (SARA), and the National Contingency
Plan (NCP) (40 CFR Part 300).
This decision document explains the factual and legal basis for selecting
the remedy for this site. The information supporting this remedial action
decision is contained in the administrative record for this site and is
summarized in the attached decision summary. This decision is based on
the administrative record for this site.
The State of South Dakota concurs with the selected remedy. The State,
however, does not concur on the boundaries of the site.
ASSESSMENT OF THE SITE
Actual or threatened releases of hazardous substances from this site, if
not addressed by implementing the response action selected in this
Record of Decision (ROD), may present an irrtrnrnent and substantial
endangerment to public health, welfare, or the environment.
DESCRIPTION OF SELECTED REMEDY
The remedial action selected by EPA for the Whitewood Creek
Superfund site consists of covering and/or removal of contaminated soils
at existing residential properties and establishment of institutional
controls to restrict access to tailings deposits. Implementation of these
measures will reduce the risk to public health presented by residential
soils, tailings deposits and alluvial groundwater contaminated with
arsenic.
The major components of the selected remedy include:
Cover and/or remove soils in the existing residential areas containing
arsenic levels of 100 milligrams per kilogram or greater.
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• Restrict future development in the 100-year floodplain and tailings
deposits as provided through county ordinance.
• Prohibit excavation of tailings deposits for other uses and prohibit
excavation of remediated areas through county ordinance, however,
rmmng would be allowed subject to the regulations of the State of
South Dakota.
• Refine knowledge of the extent of contamination and delineate the
100-year floodplain. Provide detailed maps to define site boundaries
and specify activities to support county ordinances.
• Set up an educational program to inform people about hazards
presented at the site and ways to decrease their personal exposure.
• Continue enforcement of the ban on installation of water supply wells
with the 100-year floodplain (this is already prohibited by a state
regulation).
• Continue monitoring the surface waters of Whitewood Creek for
significant releases of hazardous substances.
Resample rernediated residential areas after major flood events.
DECLARATION OF STATUTORY DETERMINATIONS
The selected remedy is protective of human health and the environment,
complies with most Federal and State requirements that are legally
applicable or relevant and appropriate to the remedial action. and is cost
effective. A waiver is invoked for complying with maximum contaminant
levels for arsenic under the Safe Drinking Water Act and the water
quality cnteria for protection of human health by consumption of fish
because of the technical impracticability of meeting these requirements
This remedy utilizes permanent solutions and alternative treatment
technologies to the maximum extent practicable for this site. However.
because treatment of the principal threats posed by the site was not
found to be practicable, this remedy does not satisfy the statutory
preference for treatment as a principal element. Treatment is
impracticable because of the large volume of contaminated soils and
tailings deposits, the lack of appropriate treatment technologies, and the
potential for adverse environmental impact.
Because this remedy will result in hazardous substances remaining on
site above health-based levels, reviews of the remedial action will be
conducted no less often than each five years after initiation of the
remedial action, to ensure that human health and the environment are
being protected by the remedial action being implemented.
Ja here
Regional Administrator
EPA Region VII I
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RECORD OF DECISION
ATTACHMENT A
WHITEWOOD CREEK SUPERFUND SITE
DEC 1SION SUMMARY
I. SITE NAME AND LOCATION
The Whitewood Creek Superfund site, a National Priorities List site, is located in
Lawrence, Meade and Butte Counties, South Dakota (Figure A-I). The site is situated
west central South Dakota on the northern perimeter of the Black HilLs, 40 m. les northwest
of Rapid City on Interstate 90. The site lies within portions of Township 6, 7 and 8 Nortr..
Range 4, 5 and 6 East and is mapped on the Rapid City (1.250,000) quadran2le at a
latitude of 44 0 45 0 N and longitude 102°- 104 0 W.
The Whitewood Creek site, a mine tailings contaminated site, encompasses appro rnare!v
2,018 acres along 18 miles of Whitewood Creek floodplain from the Crook City Bnd2e to•
the confluence with the Belle Fourche Rivet. From the 1870s to 1977, tailings were
discharged into Whitewood Creek from upstream gold mining and milling ocerations.
These tailings were deposited along the floodplains of Whitewood Creek an the Belle
Fourche and Cheyenne Rivers.
The primary concerns for potential harm to human health and the environment presented
by the site are exposure to arsenic-nch tailings deposits, and alluvial soil, residential soil.
and alluvial groundwater contaminated with arsenic.
The dominant land use within the site is woodlands. The remaining land within the site s
used for agriculture and residences. The agricultural lands are located in somewhat
discontinuous sections along the edge of the floodplain in areas adjoining and occasior. i ”.
overlapping the tailings deposit areas.
The residences are scattered along both sides of Whitewood Creek. Based on 1938 dam.
22 households and five vacant residential properties are situated within or in close
proxirn.ity to the site with a population totaling 85 (63 adults and 22 children). Eighty
households, with a popuLation of 283, are within a mile of the site on either side of the
creek and 168 households, with a population of 647, exist within three miles of the site.
The Town of Whitewood, located about one mile west of the site, has a population of 82:
1
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II. SITE HISTORY AND ENFORCEMENT ACTiVITIES
History of Operations
1877 to 1977 . The Homestake Mining Company, located in Lead, South Dakota, began
gold mining operations in the Whitewood Creek watershed in the late 1870s, following
development of gold deposits discovered prior to 1850. Mining operations over the last
century have produced about one billion tons of ore from both open pit and subsurface
shafts which currently extend to a depth exceeding 8,000 feet below the surface. The
processing of the ores has changed over the years, resulting in changes in the characteristics
of the waste stream. Methods have become progressively more e cient so that earlier
tailings were coarser and contained more etal than those resulting from present
operations.
The first milling methods were primitive and non-mechanized. Gold was recovered by
gravity or by amalgamation with mercury. By 1880, the early crude methods of rnillin
were replaced with more than 1,000 stamp mills which crushed the ore to a coarse sand
size. The tailings were then discharged to Whitewood Creek or its tributanes. Prior to cie
turn of the century, much of the ore consisted of red-colored minerals which were the near
surface residual oxid .uon products of the original unoxidized ore bodies.
After the turn of the century, the black and green-colored reduced ores from deeper in the
niune, below the zone of oxidation, were the focus of mining activity. The use of ball and
rod mills, brought into service in the 1920s. created finer-grained tailings referred to as
“slirnes.” After 1935. much of the sand-sized portion of the tailings was returned to the
mine to bacl U mined areas. The slirnes” as well as some coarse-grained sands continued
to be discharged directly into Whitewood Creek until 1977, with the exception of ve vea:s
during World War II when the mine was closed. Mercury amalgamation was discontinued
in 1970.
Tailings. consisting of finely ground rock, residual metallic and nonmetallic compounds o:
extracted from the ore, and trace compounds used in the extractive processes. were
transported away from the mine by the water of Whitewood Creek. These tailings were
deposited downstream from the mine with the largest deposits along the banks of
Whitewood Creek between the Crook City Bridge and the confluence with the Belle
Fourche River. The t2ilings remnin along much of this reach of Whitewood Creek and
continue to leach metals to surface and subsurface waters.
1977 to Present . Presently ore is rniUed in crushers and rod and ball nulls. The material
from the rnillin [ process is separated into two size fractions, sand and slimes. These
fractions are treated separately by cyanide leach and carbon filter methods. Residual sanc
material is used to backfiU within the mine. Residual slimes and process waters are DIDCC
to the Grizzly Gulch tailings impoundment in the upper reaches of the Whitewood
watershed.
A wastewater treatment plant now treats water from the tailings impoundment and the
mine. LThis plant utilizes rotating biological contactors to remove cyanide and arrtmon::.
iron precipitation and sorption to remove rnet4J ; and sand filtration to remove suspenu ...
solids. Solids are returned to the tailings pondj Water enters Gold Run Creek whicri
discharges into Whitewood Creek between the towns of Lead and Deadwood. This
discharge is monitored to meet requirements of the Clean Water Act.
3
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a,
History of Site Investigations
The first systematic studies of the Whitewood Creek area were undertaken by the South
Dakota Department of Health in 1960. This work quantified the solids and cyanide loathna
to Whitewood Creek. recommended further study, and re9orted that a comprehensive
water pollution control program was needed, if any benetlcial i.ise was to be made of
Whitewood Creek. A study by the South Dakota Department of Game, Fish and Parks in
1965 determined that aquatic bottom organisms were not present in Whitewood Creek
downstream from the waste discharg s. In 1970-71, a series of studies by the U.S.
Environmental Protection Agency (EPA) and the U.S. Food and Drug Administration
(FDA) were undertaken to document and characterize the discharge of tailings to
Wh .itewood Creek and to deterine the magmtude and extent of the resultant pollution.
These studies, together with one prepared by the University of South Dakota, focused on
the possible serious environmental hazard created by mercury contamination. In
December 1970, results of these studies led to the discontinuance of mercury in gold
recovery operations.
In the winter of 1974-75, about 50 Holstein cattle that were part of a dairy operation
located adjacent to Whitewood Creek. died of unkoown causes. Later, a study by the South
Dakota State University Department of Veterinary Science concluded that the cattle had
died of arsenic toxicosis due to consumption of corn silage that had been contaminated by
the accidental incorporation of mining wastes with fodder during silo-filling operations. A
joint study, conducted by the South Dakota Geological Survey and Water Resources
Division between May 1975 and July 1978, investigated the presence of arsenic in surface
and groundwaters along Whitewood Creek arid the Belle Fourche River and portions of
the Cheyenne River. This study, published in 1978. found arsenic concentrations ran tn
from 2.5 to 1,530 ug/L in grounowater from areas with large tailings deposits.
One common conclusion of all these pollution investigations was that Whitewood Creek
would remain highly contaminated until the discharge of tailings was discontinued. To
comply with new environmental laws, including the Ore Mining and Dressing Effluent
Guidelines. Hornestake Min.ing Company implemented the Grily Gulch Tailings
Disposal project. an impoundment area or tailings storage. The tailings disposal svste n
became operational on December 1, 1977, and no discharge of tailings to Whitewood
Creek has occurred since then.
In 1981, at the request of the governor of South Dakota, the Whitewood Creek site as
placed on the “Interim National Priorities List? Subsequently, on September 8, 1983, the
site was placed on the National Priorities List (NPL).
Following th*-iAuial placement of the site on the Interim National Priorities List. EPA, inc
South Dakota Department of Water and Natural Resources (DWNR), and Hornestaice
Mining Company (Hornestake) entered into a three-party study agreement in 1982 to
conduct a comprehensive study of the site. The study, funded by Homestake and
conducted by Fox Consultants, Inc. of Denver, Colorado, was supervised by a project
advisory committee composed of representatives of each of the three parties. The Fox
study investigated the quality of surface waters, groundwaters, soils, sediments aquatic life
and vegetation in the study area, on an 18 mile segment of the floodplain of Whitewood
Creek above its confluence with the Belle Fourche River. The study used 14 target
substances as indicators of potential public health and environmental threat. The
conclusions, published in a multi-volume report in December 1984, indicated that arsenic
was the contaminant of most significant environmental concern throughout the media
under evaluation.
4
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The report also indicated that, although mercury and cyanide had originally been
contaminants of concern in taiii.ngs discharged from Hornestake Mine, concentrations of
these contaminants at the WhitewOOd Creek Superfund site were near background levels
and therefore not of environmeflta.l Concern at this time.
Simultaneously with the Fox study, two related studies were conducted. Homestaice
assembled a group of consultants led by JA Cherry to assist the project advisory
committee. These consultants studied the hydrogeochemistry of the site and prepared a
report completed in 1985. This report. titled “Hydrogeochemistry of sulfide and arseruc-
rich tailings and alluvium along Whitewood Creek, South Dakotan was published in 1986 in
Mine’al and Enerrj Resources . The second study, an extensive investigation of the surface
water in Whitewood Creek, was initiated in 1982 by hydrolo sts from the U.S. Geological
Survey. The U.S. Geological Survey published a draft report in 1985. Subsequent
published reports and unpublished data are currently available from the U.S. Geological
Survey.
Hornestake and the State of South Dakota submitted a request to EPA in 1983 to initiate
proceedings to delete Whitewood Creek from the NPL and resubmitted the request in
1985. This request was supported by a human health exposure assessment performed by
Hornestake’s contractor, Environ Corporation, which concluded that the site posed no nsk
to human health. EPA, believing that it wa.s premature to discuss deletion until the studies
were completed 1 did not pursue dehsting further.
Homestake also funded several additional studies which included: 1) an evaluation by
Industrial Waste Management Inc. of the water quality sampling results collected by the
U.S. Geological Survey in Wb.itewood Creek before a nd after the installation of the
wastewater treatment system upstream from the CERCLA site; 2) an analysis of the age of
trees growing ott the tailings deposits along Whitewood Creek (for the purpose of dating
these deposits) conducted by Pope and Talbot, Land Forester, 3) an assessment of the
sources, occurrences and mobility of selenium in the Whitewood Creek Basin and a re-
analysis of the selenium concentrations in existing water supply wells along Whitewood
Creek. both performed by Geochemical Erigineerin Inc. Another study by Geocherrucal
Engineering Inc. in October 1988, incorporated additional groundwater quality data and
soil characterization data. For this study, the population residing within the site was
interviewed regarding their habits with respect to the intake of drinking water and locally
grown food crops. The study included testing of water supply wells.
In December 1988, an Mmini tranve Order on Consent was sired by EPA and the
Hornestake Mining Co. This order concluded that the Fox study constituted the functional
equivalent of a remedial investigation, as prescribed by the National Contingency Plan.
The order required that Honiestake conduct a feasibility study (FS) in order to identify and
evaluate alternatives for the appropriate extent of remedial action to prevent or mitigate
the migration, release or threatened release of hazardous substances, pollutants or
contaminants from the site.
In 1989, an FS was conducted by ICF Technolo i Inc. on behalf of Hornestake. Soil data
collected in May, June and July 1989 by Homestake and analyzed by Geochemical
Engineering Inc. was incorporated into this study, along with a report prepared by
Morrison Knudsen Engineers, on the feasibility of removing tailings
Remedial action objectives for the FS were based on EPA’s endaiigerment assessment.
EPA contracted with Batteile Pacific Northwest Laboratory to perform an endangerment
assessment. The first draft was released in January 1988 and comments were provided by
Hornestake in April 1988. A second draft was released by EPA in March 1989 and
5
I
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The shallow groundwater at the site appears in four units which act as a single aqi.uier. I is
useful to describe the four units separately in order to understand the movement of
conrirrnn2nts within the various mediL
• Tailings deposits are generally coarse..grained materiaL with some fine layers (Cru
1 in Figure A-3).
• Alluvial aquifer materials underneath the tailings, which are most directly
i.nfiuenced by water oving through the tailings, are referred to as the down 2rpd e:-:
aquifer (Unit 2 in Figure A-3).
• Alluvial aquifer materials and shallow bedrock shale within the floodplain outside
the immediate influence of the tailings are referred to as the upgradierit agu fer
(Unit 3 in Figure A-3).
• Upland alluvial aquifer terrace deposits are upland away from the tailin2s and
floodplain alluvial materials (Unit 4 in Figure A.3).
The water table along Whitewood Creek occurs mainly in the natural alluvium underlvirz
and adjacent to the tailings. During wet periods of the year. the water table may rise into
the tailings. Some recharge of the shallow aquifer may occur then, as precipitation
infiltrates through the terrace materials and tailings deposits.
In general, the water table slopes toward the floodplain, and during most of the year, there
is a net flow of groundwater from the alluvium into the creek. During high creek flow.
lasting from two to eight weeks each spring, the flow is reversed and water flows from the
creek as far as 200 meters into the alluvium.
Migration of contaminants from the tailings to the alluvium and groundwater occurs at a
slow rate because of the chemistry of the conta.mir ants and tailings deposits (see page i ..;
The upgradient alluvial aquifer and upland alluvial aquifer appear to be uncoritanunate
by tailings materials. Groundwater in the tailings deposits and the downgradient ailuv a
aquifer are of greatest concern to human health.
The bedrock aquifers are separated from the shallow aquifer by up to 1,000 feet of
relatively low permeability shale. The thickness of the shale and the lack of continuous
porous zones in the shale both serve to limit the connection between the alluvial and
bedrock aquifers. Water supply wells in the bedrock aquifers tested in the RI did not
contain contaminants from tailings deposits materials.
Sources and Types of Contaminants
The initial RI studies completed by Fox itt 1984 identified the tailings deposits as the
source of contamination in the study area. Fourteen target substances were investigated as
indicators of potential public health and environmental threat (Table A.l). Arsenic was
considered to be the contaminant of most significant environmental concern throughout
the media under evaluation. Cadmium, copper and manganese were detected at
concentrations above background levels but too low to be of concern to human health. T ’.-ie
remaining substances were either determined to be naturally occurring (sulfate, seleniumi
or present at concentrations near background levels (chromium, silver, nickel, iron.
mercury, lead, zinc and cyanide).
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Affected Media
The RI/FS documented that hazardous substances are present in a variety of media at the
site including:
• Tailings deposits;
• Alluvial materials underlying tailings deposits;
• Surface soils in sor e of the irrigated lands adjoining tailings deposits;
• Surface soils in residential yards, gardens, and driveways;
• Alluvial groundwater undexthe tailings deposits
• Surface water; and
Vegetation.
Potential health impacts and risk assessments are presented in Chapter V. The media
posing the greatest potential risk to human health and the environment are listed below.
The potential for contaminants rrugraung between the media as demonstrated by rerne ial
investigations, especially the Cherry study, is also sumrnanzed below.
Surface Soils in the Tailings Deposit and Fringe Areas
Tailings Deposits (Medium 2, Figure A-2). It is estimated that 21.6 million tons of tailinzs
exist within the site. The t tlings deposits contain concentrations of arsenic (maximum
42.500 milligrams per kilogram or mg/kg) and cadmium (maximum 180 mg/kg) wnicn are
significantly above levels in uncontaminated alluvial soils at the reference site on the Beiie
Fourche River above the confluence with Whitewood Creek (12 mg/kg and 1.5 mg/kg,
respectively).
The tailings have been determined to be the major source of the contamination found :n
other affected media. The ore body from which the tailings are derived is a metaniorprnc
iron magnesium carbonate. The gold is found in veins along with quartz. calcite. iron and
arsenic sulfides and other minor metals.
Oxidation of the iron and arsenic sulfides in the tailings produces a weak sulfuric acid. In
most cases, this a d is buffered by calcium in the carbonates in the ore and from the
exposed sedimentasy rocks. In this buffered environment, the contaxrunants are relatively
immobile. Isolated pockets having an acid environment occur within the tailings and
alluvium, where some arsenic may be mobilized.
Most of the substances are transported in their solid form, rather than in solution. At
present the contaminants contained in the tailings deposits are being released very slowly
into the alluvial aquifers. Small amounts are being transported into the underlying
alluvium. It is anticipated that these contaminants will continue to be released through
both chemical and physical processes at these slow rates for many years.
In all but a few locations (estimated at 25% of the area for purposes of estimating costs of
potential remedial action), the tailings deposits support vegetation indudinggrasses , shrubs
and trees. Most unvegetated areas have a thin gypsum ctust at the surface. This cover
provides some stability for these deposits. The tailings exhibit some instability at the creek
14
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bank edges and where cover is absent. Some of the tailings with their contaminants are
released to the surface waters of Whitewood Creek. It is estimated that 7,000 kg of arsenic
may be added to the surface waters from normal erosion, heavy rainfall and seenage during
a normal year. Periodic flooding events may introduce an addiuonaj 35,000 kg in a single
event.
The potential risk to human health through inadvertent ingestion of tailings was evaluated
as part of the soil exposure pathway.
Alluvial Materials Underlvlri2 Tailings Deposits (Medium 1, Figure A.2). It is estimated
triat at least 10 million tons of alluvium underlie the tailings deposits within the site. The
alluvium u.nderlying the tailings deposits consistently exhibits elevated levels oi arseruc
(maximum 700 mg/kg).
While the contaminants within the alluvium are relatively immobile, they are being
released very slowly to alluvial aquifers, and transported in small amounts to the surface
waters of Whuewood Creek. There may be some scouring of alluvial materials from the
bank into the creek during high river flows. In most instances, the alluvium is covered by
tailings and the contaminants within it are insulated from, and not available to, surface
transport processes, such as erosion or runoff. Because of the covering tailings deposits. rio
human health exposure pathways exist.
! rriepted Soils (Media 3, 4, and 5, Figure A -2). Approximately 83 acres of irrigated
croplarid are located within the site. About one-fourth of the water used for irr:2ation
comes from upgradient alluvial or bedrock aquifers, one-fourth from Whicewood Creek
and one-half from the Belle Fourche River. Only some portions of the total irrigacec
croplanids are contaminated by arsenic. Overbank flooding and windblown tailings
materials probably contributed most of the contamination, although Whitewood Creek
surface water may have contributed small amounts of arsenic to the soil where it is used for
irr itation.
A.rseruc levels are elevated in samples of irng ted soils taken at different locations
throughout the site (maximum 600 mg/kg). There is no indication that contarnina_nts n the
irrigated soils are migrating into the alluvial groundwaters because of the relative
immobility and low concentrations of arsenic in these soils. Contairurinni uptake by crops
occurs to varying degrees, depending on the contaminant. The potential risk to human
health through inadvertent ingestion of contaminated soil; was evaluated as part of the soil
exposure pathway. The potential risk due to ingestion of crops is discussed below in the
section on vegetation.
Surface Soils i iden al Yards. Gardens and Drivewa (Medium 6, Figure A.2). The
contamination in the residential areas is from windblown tailings materials and from
tailings materials inadvertently transported in by dirty work boots etc. or imported for use
as a soil conditioner and driveway base. Three residential properties within the site have
been found to have surface soil arsenic contamination (maximums: lawn 520 mg/kg, garden
540 mg/kg, driveway 2400 mg/kg). In these samples, maximum concentrations were
reported in the 0-6” samples. Concentrations of arsenic in the 18 and 24’ depth samples
were above background for the area but less than 100 mg/kg. Other residential properties
within the site have not been sampled. Approximately 12 residences were estimated in the
feasibility study to have arsenic concentrations greater than 100 mg/kg. The total number
of affected residences and amount of contaminated material will be determined during the
remedial design phase of the Superfund work.
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There is no indication that contaminants contained in these soils are migrating into the
a.Uuvial groundwaters because of the relative immobility and low concentration of arsenic
in these soils.
The potential risk to human health through inadvertent ingestion of contaminated soil was
evaluated as part of the soil exposure pathway.
Down radierit Alluvial Groundwater . The water from the downgradient alluvial aquifer
(Unit 2, Figi.ire A-3) is the onAy groundwater to exhibit elevated levels of co tamrn r1t3.
Concentrations of arsenic (ma.’omum: 0.78 mg/i) are detected above background levels.
These concentrations exceed primary drinking water standards and the South Dakota
Drinking Water Standards.
The water table along Whitewood Creek occurs mainly in the natural alluvium underlvine
the tailings. During wet periods of the year. the water table may rise into the tailings.
Some recharge of the shallow alluvial aquifer may occur then, through infiltration of
precipitation moving through the terrace deposits and the tailings deposits. In general, the
water table slopes toward the floodplain and, during most of the year, there is a net flow of
groundwater from the alluvium into the creek. During high creek flow, lasting from two to
eight weeks each year, this flow is reversed. The effect ot recharge from the stream may be
seen as much as 200 meters from the stream. In the areas where the tailings deposits are
flne .grained with low permeability, loca.hzed perched zones produce small seeps and
springs along the bank of the creek. Gypsum crusts form in places at the surface of the
tailings and at the seeps.
Three mechanisms appear to act in movement of arsenic from the tailings to the
groundwater: 1) dissolution of arsenic during those times of the year when the water table
is in the tailings, 2) dissolution of arsenic when precipitation infiltrates downward through
the tailings and 3) incorporation of tailings particles into the alluvium, which probably
occurred as the tailings were being deposited. Movement of contaminants presently
continues at a slow rate, and could continue for thousands of years.
The potential risk to human health occurs through ingestion of contaminated groundwater
Surface Waters of Whitewood Creek . The concentrations of contaminants (Table A.l) in
surface waters of Whitewood Creek compiy with water quality standards established by
South Dakota for Whitewood Creek and EPA water quality criteria for chronic toxicity to
aqu nc life. Concentrations of arsenic at the U.S.Geological Survey Vale sampling station.
downstream of the site, occasionally exceed the water quality criteria for the protection of
human health from the consumption of fish. These exceedances are due in part to
upstream sources...ajtd to the additional contributions from the tailings deposits along the
creek within the site.
The upstream sources include minor unquanufled discharges of municipal and industrial
wastewaters from the communities of Lead, Deadwood and Whitewood. Minor additional
contamination may be attributed to the few tailings deposits between the Hoinestake Mine
and the beginning of the Whitewood Creek Superfund site at the Crook City Bridge.
Homestake mine discharge also contributes to the upstream loading. Prior to the
installation of the Grily Gulch Tailings Impoundment and Homestakes wastewater
treatment plant, the surface water in Whitewood Creek below the mine was substantially
degraded and incapable of supporting aquatic life. Following completion of the treatment
plant, Hornestake has been discharging to Whitewood Creek under a draft permit from the
State of South Dakota. The allowable discharge concentrations for arsenic (0.184 rng/L
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daily maiumum; 0.105 mg/L daily average) in the treatment plant e uent were developed
to be protective of a cold water fishery usage of Whitewood Creek between I_cad and the
Superfund site using ambient water quality above the discharge, and wasteload allocation
calculations. The present arsenic concentrations in the e i.ient at the discharge point
located near the town of Lead average 0.03 mg/L with m.a amums of 0.06 mg/L
The water quality of Wb.itewood Creek is different as it leaves the site from that encenna
the site. Groundwater seeping through the tailings and alluvium into the creek adds an
average of 365 kg/year of arsenic to the creek. ormal erosion of tai.lings along
Whitewood Creek contributes on the average of 300 kg/year of arsenic and heavy rains
may contribute another 6,000 kg/year. During periodic hood events up to 35,00O kg of
arseruc is added to Whitewood Creek from the erosion of the taThngs . This added toad of
contaminants to the surface water across the site results in art increase of arsenic
concentrauons which varies with the amount of flow in the creek and time of year.
The levels of dissolved arsenic at the downstream end of the site exceed water quality
criteria for the protection of human health from the consump on of fish. The levels also
periodically exceed the National Primary Drinking Water Standards for arsenic of 005
rng/L and have approached the criteria established by the EPA for chronic toxicity to
aquatic life of 0.190 mg/L The observed changes in water quality are related to the
uncontrolled releases from the site throughout the year as well as the processes which lead
to removal of contaminants from the water column to the sediment of the stream bed.
Consequently, the range of observed percent chari2e in arsenic concentrations in
Whitewood Creek reported between 1985 and l98 was from a loss of 80 percent in
September 1985 to an increase of 490 percent in July 1985.
Preliminary calculations in the RI/FS indicated that the potential risk to human health of
ingesting contaminated water is too low to be of concern., in part because there is no
current or anticipated future use of Whitewood Creek surface water for drinking. The
National Primary Drinking Water Standards for arsenic are therefore neither applicacle
relevant or appropriate as a requirement for Whitewood Creek. There are no applicabt
standards for toxicants in the reach of Whitewood Creek within the site. However. tne
EPA. 1986 Quality Criteria for Water document established arsenic levels for preventing
chronic toxicity of 0.190 mg/L which may be considered as a relevant and aoprooriate le’.&
for protection of the semi-permanent warmwater fishery designated by the state for
Whnewood Creek within the site. Due to the potential for exceedances of the national
chronic toxicity criteria, coupled with the uncertain future rates of release of arsenic from
the tailings deposits, EPA has determined that continued monitoring of Whitewood CreeK
water quality is needed.
Ve2etation . Certain native plants growing on the tailings deposit areas contain
concentrauo ’ f arsenic (maximum 240 mg/kg, Table A-i) above that of vegetation frcn
the reference area. Some cultivated crops (alfalfa, for example) contained concentrations
of arsenic elevated above background. but below levels cited as producing reduction in
crop productivity or causing toxic effects itt livestock. Arsenic levels were not elevated
crops for direct human consumption. During the endangerment assessment, consumption
of vegetation was not considered as a transport pathway, because of the low arsenic ieve s
and because arsenic does not accumulate in tissue or increase in concentration as it
progresses up the food chain.
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Contaminants
The media most contaminated by ar e u and cadmium, the cont ‘ ts of greatest
concern for this site, are the downgradleflt alluvial aquifer, tailings deposits. irrigated
croplarid soils and residential soils. Each of these media contribute a portion of the dose
ingested by the exposed populatiOn depending upon the concentrations of contaminants in
the media and the individuals exposure to the media. Section V discusses the volume and
mobility of cootanilfla.titS in these media in greater detail. See Table A.2 for average
concentrations of all substances a.ssessed in the EA. The discussion which follows utlines
assumed exposure patterns for a variety of exposure scenarios.
Pathways
There are a number of pathways by which contaminants from the tailings deposits may
reacri individuals living within or visiting the site. EPA’s EA for the site concluded mu the
pathways which present the highest risk are ingestion of groundwater and in2estlon of
contaminated soil media (tailings deposits, irrigated cropland soils and residential soils).
The existing ranches and potential ranch sites in the Whitewood Creek area could be
expected to utilize groundwater from the upgradierit alluvial aquifer. Ranches could also
hypothetically use the downgrathent alluvial aquifer in the future (See Figure A-2 and A .3)
Some of the ranches exist near tailings deoosits and/or contaminated irrigated soils.
Inadvertent soil ingestion could occur at these ranches during an individual’s lifetime from
such activities as playing, hunting, fishing, cutting wood, gardening, and working in the
yards arid fields. Furthermore, household dust might contain arsenic blown in or
mechanically transported (e.g.. dirty work boots) from tailings and cropland soils. Most
large dust particles which are breathed into the lungs are removed from the lungs by zne
lungs self cleaning action. Contaminants can become incorporated into mucus and
swallowed, in a pathway referred to as incidental soil ingestion.
Additional pathways were also considered. but risk calculations were not developed. Risks
for the consumption of homegrown foodstuffs. the air pathway (through inhalation of
respirable particles) and the surface water pathway were not calculated in the
endangerment assessment because preliminary calculations in the RI/FS indicated
concentrations of contaminants and the potential for exposure through these pathways
were too low to be of concern.
Population Exposure Scenarios
The exposure tothe potential carcinogen, arsenic (Table A ..2), and non-carcinogenic
metals in soil and groundwater via ingestion was evaluated for four exposure scenarios.
These include 1) a representative adult site resident, 2) a representative child site resident.
3) a recreational visitor, and 4) a hypothetical future (maximum exposed) site resident.
Assumptions for ingestion rates are included in Appendix A.
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Alternative 1: No Action
The No Action aiternatwe would consist of no remedial activities.
The current State of South Dakota ban on construction of water supply wells within the
100-year floodplain of Wbitewood Creek between the Crook City Bridge and the
con.th.ience with the Belle Fourche River would continue to be enforced (South Dakota
Water Rl2hrs Rules, Section 74:02:04.26). This regulation prohibits consmiction of wells
that supply water to the public or supply water for bousebold domestic use or for
agricultural purposes. A variance is also provided for in this regulation which may be
granted, if it is shown that a well in this location will not be contaminated from tailings
aeposics and will not cause groundwater pollution. A public health and environmental
evaluation would be conducted evety five years.
AlternatIve 4: InstitutIonal Controls with Covering and/or Removing Surface Soils at
Residential Properties (Including the Restriction of Future Development)
Two activities required to refine knowledge of the extent of sue contamination and define
site boundaries would be completed during remedial design. A survey would be conducted
to define the limits of the 100-year floodplain. Soil would be sampled both at the surface
and at depth to define the tailing deposit areas arid parceLs of land with surface soils
arsenic concentrations greater than 100 mg/kg. Maps compiled during these activities will
be used to support the county ordinances regarding use of tailings deposits and fringe
areas. Al! residential properties within the site which potentially contain soils with arsenic
concentrations greater than 100 mg/kg as detined by this initial sampling of soils would
also be sampled.
To define the boundaries of the tailings deposit areas on both sides of the creek, transect
lines perpendicular to and at selected intervals along a baseline connecting the Crook C. v
Bridge to the point where Whitewood Creek joins the Belle Fourche River would be laid
out on a map and in the field. Parallel baselines may be utilized as needed to
accommodate local obstructions. Surface soil measurements of , or samples for the anal sis
of. total arsenic would be taken along each of these transect lines near the approximate
boundaries of the tailings deposit areas on either side of the creek and at intervajs as
required to idenu the extent of soils with arsenic concentrations greater than 100 mg/kg
The sample locations and associated analytical results would be plotted on a map to define
the boundaries of the tailings deposit areas.
Tailings deoosits will be identified by a statistically significant change in the physical and
chemical c aracterisucs of the surface solids. These parameters may include, but not be
limited to, coIo ’rarncle size, grain size distribution and arsenic concentration.
To define the locations and boundaries of those parcels of land outside and on the fringes
of the tailings deposit areas that have surface soiLs arsenic concentrations greater than 100
mg/kg, sample measurements or samples of the top one inch and at six inches below the
surface of soils would be taken along (or parallel to) each of the transect lines described :n
the previous subsection. These arsenic measurements or soil samples would be taken at
intervals beyond the apparent boundary of the tailings deposit areas until arsenic
concentrau ns at or below 100 mg/kg were detected.
The survey to define the limits of the 100-year floodplain would start with ground truthirig
of existing aerial photographs and maps including Federal Emergency Management
Authority (FEMA) maps. The objective of this task is to analyze the potential for
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redistribution of exisung tailings deposit.s during major flood events by identifying segments
where flood events may result in significant erosion and/or deposition.
Areas around the residential properties with greatest potential exposure tp arsenic
concentrations exceeding 100 mg/kg Lii the surface soils would be remediated as
subsequently described. If the arsenic level exceeds 100 mg/kg within a defined Darcel
around each of the potentially affected residences, the property would be subject d to
remethauon as described below.
The parcel around each of the residences will be based on the most actively used por of
the property including the immediate yard (non-garden) around the reside ice, the
driveway and garden areas. The boundaries of each of the residential parcels and the
subareas within each parcel would be determined during RD/RA. and must be
coordinated with the current resident(s). These areas would be detailed on a resident a1
site map as part of the site plan for each property. It is assumed that the residential parceis
will be approximately two acres, and that gardens will be approximately 90 feet by 180 fee:.
If use patterns exceed this area, then up to 8 acres and 2 acres respectively will be
rennediated. If the residential property is less than two acres, the entire parcel, regardless
of size, would be reniethated x l the arsenic levels as determined from the samoling exceed
100 mg/kg.
A limited number of random samples would be collected from driveways and residential
soils at any of the twenty-two residences which were within the RI study area but are
outside the 100 mg/kg tsopleth. If any sample contains surface soil concentrations greater
than 100 mg/kg arsenic, then a residential parcel would be selected for sampling as
outlined above and rennediated as required.
At the residential parcel subject to potential rennediauon. a garden area desi na:ed for
food production would be identified on the residential site map along with dx ve .avs,
buildings and other physical features. The residential area would be divided into a rd
with the line spacings set at 30 feet. Each of the 900 square foot areas defined by the 2nd
lines would be sampled to determine the arsenic level at the surface and the si.x inch cep:
The two samples for analysis from each 900 square foot area (surface and subsurface)
would be a composite of the less than 2 mm size fraction from each of the four quadrants
of the area. If any of the samples from the surface or subsurface exceed the 100 mg i kg
arsenic level, then that 900 square foot area would be subjected to remediauon.
Samples collected during the RI/PS indicate that where residential soils are contaminated.
arsenic concentrations are above 100 mg/kg in the top twelve inches of soil. Samples taken
from eighteen and twenty-four inch depths were at background levels. It is assumed that .:i
the non-garden .g eas where no invasive activities occur, twelve inches of cover will provice
su cient protection for the residents.
The rennediation of those non-garden yard areas which exceed the 100 mg/kg arsenic !e’. e.
therefore would involve some combination of the following actions to minimize exposure :
the residents to contarninnted surface soils. 1) If topography, building foundation levei
and resident permit, 12 inches of soil cover would be placed. 2) if it is possible to maznt r
topography consistent with immediately adjacent areas, or if the resident requests, the
removal of twelve inches of soil and replacement with twelve inches of clean soil may e
required. 3) If surface soil arsenic concentrations of less than 100 mg/kg can be ach:e. e.:
by removing 6 inches or less of existing soil, this would be done, and sufficient clean so i. s
(20 mg/kg arsenic) would be placed on the excavated areas. In any of these cases, the
areas would be restored to their former vegetated conditions. As noted below, excava: -
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below areas remediated would be prohibited by county ordinance, unless the soil is
demonstrated to contain less than 100 mg/kg arsenic.
In garden areas, the invasive and nuiang activities associated withgardening could result ui
elevated levels of arsenic below that found in the adjacent sods. Twenty-four inches of sod
would therefore be removed and replaced with clean sod from off-site SOUrces (<20 mg/kg
a.rsen ic).
Roadways arid driveways at e snng residential properties are paved with gravel or other
non-asphaluc. non-cement materials. Where the surface soil arsenic concentrations exceed
100 mg/kg, these gravels would be cleaned up. Six inches of e usung gravel would be
removed and replaced with clean imported gravel or road base (< 20 mg/kg arsenic).
Contaminated soil and gravel will be disposed of at an off-site facility approved by EP&
such as the Gri ly Gulch tailings impoundment near Lead, South Dakota. Under section
1214)(3) of CERCLA. any off-site disposal facility used must be operating in compliance
with all applicable Federal law and State requirements. The disposal will be undertaken n
compliance with EPA policy and/or regulations governing off-site disposal of CERCLA
waste.
Following removal and/or covering activities, composite soil samples would be taken at
one inch and at one-half the depth of soil or gravel cover from all remediated areas in the
mariner previously described, and analyzed for total arsenic concentrations. Sampling
density will be suruliar to that required for pre-remediauon sampling. This confirmation
sampling would confirm that arsenic levels have been brought to below 100 mg/kg.
Similar sampling and analysis would also be performed after any flood event that resulted
in inundation of any residential prop ertv within the site.
The arsenic analysis of soils and other material at the site may be performed using an EP.i-
approved laboratory or by a combination of laboratory and field analysis using a.portable
X-ray fluorescence (XRF) instrument. The use of field-portable instruments will be
acceptable after development of EPA-acceptable quality assurance/quality control and
calibration at an acceptable detection limit for the concentrations being analyzed. If
samples are analyzed by F in the field, 15 percent of the initial characterization and
conflrmauonai samples will be split and sent to an EPA-approved analytical laboratory to
confirm the field results and, for conflrmanoriaj samples, that the arsenic levels are less
than 100 mg/kg.
The three counties involved, Meade, Butte and Lawrence, have all expressed a willingness
to enact controls similar to those outlined in Appendix D of the Feasibility Study. These
institutional controls would include:
• County zoning and building permit regulations would be adopted prohibiting
residential and commercial development within the tailings deposit areas arid
prohibiting residential development of properties that exhibit surface soil arsenic
concentrations exceeding 100 mg/kg.
• County regulations would be adopted prohibiting the removal and use of tailings
soils from the tailings deposit areas and prohibiting disturbing remediated areas
below the depth of soil removal/cover unless the soil is demonstrated to contain less
than 100 mg/kg arsenic. Mining of the railings deposits would be allowed subject to
pertinent regulations of the State of South Dakota.
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• Excavation below areas rernediated would be prohibited, unless the soil is
demonstrated to contain less than 100 mgJkg arsenic.
• An education program would be conducted annually to acquaint site residents with
the tennal health hazards associated with exposure to the tailings soils and
downgradient alluvial groundwaters within the site. This education would also
include methods residents can use to minimize incidental ingestion of contaminated
materials. A mechanism to inxor potential property owners of the potential heaith
ha.zards will aLso be included in the education program.
In the event of a flood where contaminated materials potentially were redistitbuted, the
flooded areas would be resanipled. Action would be taken to return any newly
contaminated or re.contarmiiated areas to post-remediation conditions.
The surface water quality of Whitewood Creek would be monitored at the U.S. GeoIo2 lcal
Survey sampling stations near Whitewood and Vale four times a year. These sampztri
events would be conducted in late winter before major snow-melt runoff; during peak
runoff in spring; during the low flow period in late summer; and once immediately
following a major precipitation event. Continued monitoring of Whitewood Creek water
quality is needed to evaluate the effect of uncertain future rates of release of arseruc from
the tailings deposits on the envi.roament. These data will be reviewed during the five.vear
review.
The rules of the Occupational Safety and Health Act would apply to the construction-type
activities carried out to remove and/or cover contaminated soils. It is estimated that it
would take 9 to 18 months to implement the covering and/or removal component of this
alternative.
A review of site conditions (five-year review) would be required every five years to er.sure
that human health and the environment are being protected by the remedial action be:r.g
implemented. This would include, but not be limited to:
Verification sampling within the remediated residential areas.
A review of development activity within the site. If development has taken place
which is inconsistent with specifications as described in EPAs ROD, these
prop erties would be required to be reediated in a manner consistent with the
ROD.
A review of the effectiveness of the education program in alerting present and
potentiajproperty owners to concerns related to the contamination which remains
on site.
• A review of compliance with the monitoring well ban in the floodplain.
A review of the surface water quality data collected from Whitewood Creek to
assure that levels protective of human health and aquatic life are being maintained.
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Alternative 4a: Institutional Controls with Covering and/or Removing of Surface Soils of
Existing Residential Properties (Allowing Future Development)
This alternative would involve the same activities as Alternative 4, but would allow future
development within the contimiflated fringe areas of the lO0-year floodplain outside of the
tailings areas, following remethauon to provide conditions protective of hurr an health.
The counr ’ ordinances to be enacted as additional institutional controls would allow for a
variance in which an approval of plan for cover and/or removal of soils of greater than 100
mg/kg would be required by the South Dakota Department of Natural Resources prior to
development of the land.
• A variance procedure allowing development on lands within the site (but outside the
tailings deposit areas), following appropriate remedianon, would be adopted. A
variance procedure allowing public works developments on land inside the tailings
deposit areas, following appropriate remediation, would also be adopted.
• A potential developer must sample the surface soils of any parcel in the fringe area
determined to contain cont rrunated soils. The sampling program would be similar
to that outlined for residential remediation in Alternative 4 to identify which
portions of the parcel contain concentrations of arsenic greater than 100 mg/kg.
The developer then would submit sample results and a remedial plan to the South
Dakota Department of Natural Resources. This remedial plan would describe
removal., cover or other procedures for bringing all surface soiLs to 100 mg/kg and
would include plans for confirmatory sampling.
• After approval of the plan, the developer may perform the work and confirmatory
sampling. The developer would also assume the obligation of complying with a
county regulation prohibiting the removal or impairment of any covers placed on
the parcel under the plan i.inless pre-approved by the State.
Alternative 5: Institutional Controls with Fencing of Tailings Deposit Areas and Cove ng
and/or Removing of Surface Soils of Existing Residential Properties
This alternative would involve the same activities as Alternative 4 with the addition of
installation of fencing around the perimeter of the tailings deposit areas. A three-strand
barbed wire fence, or equivalent, would be installed, using exisun fencing where availaDle
The purpose of the fence would be to reduce current exposures or site residents to the
elevated surface soil arsenic concentrations by discoura ng access to the tailings deposit
areas. ARAR.s would be the same as for Alternative 4.
AlternatIve 7: .Lastltutlonsl Controls with Partial Soil Cover of Tailings Deposit Areas arid
Covering and/or Removing of Surface Soils of Existing Contaminated Residential
Properties
This alternative would involve the same activities as Alternative 4 with the addition of
placement of soil cover over barren areas (i.e.. devoid of vegetation) in the tailings deposit
areas. Barren areas would be identified based on field observations and review of aerial
photographs. In the places where these bare areas form steep banks along the creek, these
banks would be peeled back to create banks having slopes of no more than 1 horizontal to
3 vertical. The peeled-back tailings materials would be placed in layers on the adjoining
tailings deposits before placement of the soil cover. Six to 12 inches of native soils
imported from off-sue sources would be spread over the barren and/or stabilized tailings
deposits. This cover would be vegetated with native grasses to stabilize it and minimize
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The estimated cost for Alternative 4 to remove/cover con?2n1in ted soils at e sting
residences is $638,392 ($581,000 capital costs. Si 1.000 annual O&M cost). Alternative 4a
adds teszin and removal/cover at 15 additional residences. Costs are estimated to be
$882,813 (!1,028,000 capital costs and S 12,000 annual O&M cost). Alternative 5, which is
similar to 4 with the addition of fencing, is estimated at $1,345,841 (S98 1,000 capital costs
and 531.000 annual O&M cost). Alternative 7, which is alternative 4 with the addition of a
partial soil cover, is estimated at $5,605,254 ($5,471,000 capital costs and $16,000 annual
Q&M cost). Alternative 9 is estimated at $75,054,923 ($107,575,000 capital costs and
S36,000 annual O&M costs).
Criterion 8: State Acceptance
The State of South Dakota concurs.with the selection of Alternative 4a.
Criterion 9: Community Acceptance
Public comments that were received indicated that there Is no concensus on what presents
the best remedial alternative for the arsenlc-cont2lmnated mill tailings along Whitewood
Creek. Some citizens expressed the opinion that the tailings appeared to present no health
hazard and that the No Action alternative was the best solution. An equal number felt that
the tailings pose a hazard to b’-t ” n health and the environment that can only be mitigated
by complete removal (Alternative 9). Other people were in favor of the remedy proposed
by EPA, with reservations about the potential e ect of the remedy on the economics of the
cornunity.
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VIII. THE SELECTED REMEDY
Alternative 4a: In tIt tiø 3l Controls with Covering and/or Removing of Surface Soils of
Existing Residential Properties (Allowing Future Development).
Based upon a review of informatiOn contained in the site Adrrnnictrative Record. EPA has
decided that the most appropriate remedy for the Whitewood Creek Superfund site is to
remove and/or cover contaminated residential soils and restrict access to cofltaffllfl2ted
tailings and groundwater by use ot institutional controls. As described in Section LX below
this remedy is the most protective alternative which would not have adverse effects to the
environment. It also provides the greatest protection in the most cost-effective manner.
It is estimated that it would take approiomately 18 months to implement institutional
controls and remove/cover surface soils of existing residential properties. It is also
estimated that 15 additional properties will be developed through variance from county
ordinance over the thirty year period.
The estimated net present worth for the selected remedy is S882,813 (Table A-7). Capital
costs total S 1,028,000, 5581.000 of which will be spent dunng stan-up, 5447,000 which wiji
be incurred over the thirty year period. Annual O&M costs are estimated to be S 12,000.
At existing residences exhibiting greater than 100 mg/kg arsenic in surface soils, these soils
would be removed and/or covered in garden. non-garden and roadway areas. All material
removed would be placed in a disposal facility approved by the State and EPA which is
designed and constructed to hold wastes that are similar in nature and concentration of
contaminants. Soil sampling would be conducted both on the surface and at depth
following this remedial action to confirm that remedial action goals have been met. Mv
properties developed under variance would be sampled and remediated in a similar
fashion. If rernediated areas should be flooded these areas would be resampled and
appropriate action taken to return any contaminated areas to postremediauon
contaminant levels. A five-year review would be performed five years after retnediation ts
completed. South Dakota Water Rights Rules (Section 74:02:0&26) ban on water wells in
the Whitewood Creek 100-year floodplain would also be continued.
The scope and performance of the remedy selected in this ROD are consistent with the
remedy proposed at the start of public comment because the elements of remedial action
to be implemented are the same. In response to comments received from citizens during
the public comment period, EPA has decided warning signs and notice in deed are not
necessary because the proposed educational program is deemed to be sufficient.
Response Objectives
The response objectives for soil rernediation at Whitewood Creek are to control exposure
through ingestion of cont2i’i 1flated railings deposit soiLs, alluvial soiLs and residential sotl .
or downgradieflt alluvial groundwater. Target cleanup objectives for groundwater are the
Maximum Cont2n1in 1 ’ t Levels. Target clean-up objectives for soils were developed based
on soil concentrauons which correspond to carcinogenic health risks of 1 x 10 ’.
Acceptable contaminant levels for the chemical of concern (arsenic) in residential soils are
100 mg/kg, based on the 1 x 1O target risk levels derived in the endangerment assessment.
This action level would also reduce non-carcinogenic risk to an acceptable leveL A
sumniarf of these calculations are provided in Appendix A of this doc.irnent.
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Whitewood Creek Site Mining Waste NPL Site Summary Report
Reference 2
Excerpts From the Feasibility Study,
Whitewood Creek, South Dakota;
EPA Region VIII; December 8, 1989
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C
PEASIBILIT! STUD!
for
WEITEWOOD CRZER, SOUTH DAZOTA, CERCI BITE
VOLU I
December 8, 1989
Prepared by
ICP Technology
for
Homestake Mining Company
for submission to
U.S. Environmental Protection Agency
Region VIII
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pp 5 and 6), from the 1870’s to the and of the century, many gold
mining companies discharged tailings into Whitevood Creek or its
tr biitaries. During that period, a substantial portion of these
tailings were deposited on and in th. alluvial materials of the
floodplain because the creek was a small meandering stream w .th
insufficient capacity to transport the large quantities of
discharged tailings. Th. deposited tailings and earns alluvial
material filled in the meanders of the creek and thereby
straightened it channel and increased its gradient. , in
turn, caused the creek to dovncut its channel to or near to the
resistant shale which today forms the channel bottom for moat of
the length of the 18—mile stretch. In addition, during flooding
events, tailing, wars deposited in averbank areas throughout the
floodplain. Except at the sheeler .it . which is discussed
below, it i. believed that very little deposition of tailings
occurred after the turn of the century because the increased
sediment carrying capacity of the transformed creek channel
enabled the transport of these tailings do mstrsaa of the Site.
In 1977, the discharge of tailing, into Whitevood Creak was
terminated when Bomestaks put it. tailings impoundment at Grizzly
Gulch into operation.
2.3.1 TeLling. posits
The tailing. deposits laid down ov.r 80 years ago have
remained very stable sinc , the turn of the century as evidenced
by a study of the age of the trees that, today, ar. graving on
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ths deposits (Cherry, •t.a]. 1986a at p 6 and Blatt 1988) and as
further evidenced by aerial photographs. The areas covered by
these deposits are shovn on the map at the end of this doc .nt.
The stratigraphy of the tailings deposit areas generally consiSts
of (1) an upper deposit of tailings ranging from approximately
on. to fifteen feet thick and 50 to several. hundxed feet wide on
each side of th. creek along its full 18—mile length within the
Site, (2) an underlying strata of natural alluvium consisting of
sandy to sandy silt materials with variahi. amounts of intermixed
tailings, and (3) the thick shale strata that forms the floor of
the valley (see Figure 4 of .rry, et.al. 1986b at p 2). It is
eatimat.d that approximately 25 to 37 million tons of tailings
vere deposited in the floodplain vithth the Sits.
At the Sheel.r site, th. deposition history and mechanics
were slightly different. Sometime during the 1930 s a divers ion
channel was constructed along Whitevood Creek near its confluence
with ths Bells Fourche River. Sometime after its construction,
Whitewood Creek brsach.d the h.Imel and deposited tailings over
adjacent areas. Subsequent downcuttinq of the Whitewood Creek
channel routed the creek around this area leaving the youngest
deposit of tailings currently existing vith 4 , the Sits.
1.3.3 flit.voc Creek
From the 1870’s until the cessation of tailings discharges
in 1977, Whitswood Creek carried a heavy susp.nded solids load
arid . hibitsd a grayish, a.sthetically displeasing color. As a
1—8
‘•1
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result, the waters of the creek were sparingly used for
irrigation or stock watering purposes and did flOt provide a
habitat for a permanent fishery. Since the cessation of tailings
discharges, the physical appearanc, and quality of the waters of
the creek have improved dramatically. Except during flooding
conditions, the creek carries clear, aesthetically pleasing water
with no visibi. suspended solids. As a result, it is
occasionally used for irrigation and stock water supply, although
th. principal sources of stock water supplies continues to be
groundwater wells and the principal source of irrigation water
supply is the irrigation system that serves the irrigation lands
in the lower portion of the Site from a diversion on the Belle
Peurch. River upstream from the confluence of Whitevood Creek.
In the upper portion of the Sit., there is some pumping or
diversion of irrigation water from Wbitevood Creak.
Whitewood Creek within the Sit. is duignat.d by the State
of South Dakota for the beneficial uses of warawater,
semipermanent fish propagation and lim.tt.d contact recreation. A
semipermanent varmwatsr fishery does exist in th. creek within
the Sit.. In addition, the Stat. of South Dakota has
occasionally stocked trout in the upper reaches of the creak
within the Stts and in reaches of the creek upstream from the
site. Thu cold water fishery has not been and cannot be
established on a permanent basis becaus. of physical habitat
restrictions, principally high water temperatures and low flows.
In the upper reaches of the Sit., the Whitswood Creek
1 -9
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Corn, hay, alfalfa and mile are the principal crops grown on
the irrigated crop lands (Fc 1984a at p 275). Hay is the
Pr .ncipai crop grown on non-irrigated cropland. These crops are
grown for livestock feed. The rangela.nd is used for grazing
livestock, principally cattle but a f cv sheep and goats
(Geochemical 1988c at pp 5—6). So’e of the ranches maintain
small vegetable gardens and a few fruit tress (mostly apple) to -
produc, food for their own use (Geochemical 1988c at pp 3, 5-6).
1.3.6 Pop 1atio
The population of the Sits i. rural. Fox estimated that 80
households (exclusive of households within the Town of Whitewood)
and a population of 1,104 existed within one ail, on either side
of the 18-mile reach of Wb.itsvood Creek within the Sits, and that
168 households (exclusive of thos* within the Town of Whitswood)
and a population of 1,468 existed within three sties on either
side of th. creek (Pox 1984a at p 260). These 1— and 3—ails
areas cover sore land than the 100-year floodplain which defines
the Sit, and includ the Town of Whitavood (population 821) which
is located outside of th Sits near it. upper end. Thus, these
estimates overstate the number of household. and population that
exist on the Sit. Geochemical. Engin.srjng inventoried
the population, living on or near the Sit. itself and found 23
active household.s and 5 vacant household properties’ (Geochemical
Doss not include Rock or K.iry. The vacant households
are Di.Uingsr, Nelson, Shes],r, Sheeler (two houses) and tide.
1—16
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practic.s or vatsr quality conditions in the Whitevo 0 Creak
basin were conducted batwean 1960 and 1982. A review of the..
studies is provided by Fox (1984b in Appendix A). All but one of
these studies were fairly narrowly focUssed and .ost contaifl.d
li it.d data.
The first cosprahensive study of tailings deposit, and
groun wat, . quality on the Sit• was conducted by the South Dakota
Gologjcal Survey in the mid 1970s (Pox 198th at p 29 in Appendix
A). Although this study was complicated by Sonitoring well
construction and analytical problems, it provide, some evidence
of elevated level, of arsenic in the a1.luvja.1. g?oundwa e ,
underlying tailings deposits and increasing concentr tjons of
arsenic in Whitsvee4 Creek as it passes through the Sits.
1. Nature a 4 ten of Coatemj tjom
The investigations conduct.4 by Pox (rsport in 1984a,
1984b, 1984c, 3984d and 1984e) fo d el .vat.4 concentx tjons
(i. e., greater then backgrou Concentrations) of arsenic,
cadmium and other metals in three zone, of sat.rjal situated with
the Sit (i.e., vithj the 10 0-year floodplain of Wh.ttawood
Creek: (1) the tailings deposits, (2) the alluvial materials
underlying these_tailing deposits, and (3) the surface soils in
some of the irrigated lands within the floodplain adjoining the
tailings deposit.. These studies also found th. release or
potential release of arsenic, cadmium and other metals into (1)
the groundvat contained in the alluvium 1n dsr1yinq tailings
1—22
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deposits, (2) the Surface water. of Wh.itewocd Creek, (3) the
native vegetation growing on the tailings deposits, and (4) the
cultivated vegetation grown on irrigated lands within the
floodplain adjoining the tailings deposits.
Subsequent investigations conducted by Geochemical
Engineering, Inc. (Geochemical. 1989a and 1989b) found elevated
arsenic concentrations in the soil, of two existing residential
propert iss (on the Alan and Rioter ranches) located on the fringe
lands outside of the tailings deposit areas but within the Site.
1.5.1 Tailings Deposits
Th. tailings deposits range in thic1 iess from less than one
foot to 15 feet and cover an area from 50 to 300 feet wide en
either sid. of Whitevood Creek over most of its la-mile length
within the Sit. (Pox 2984a at p 61; also see Table 1-1 in this
section for data on the thic3o ess of the deposits). It is
estimated that the total volias of these deposits withir the Site
is 25 to 37 million tons (X&Z l989a at p 13 eM N&I l989b at p
13). These t. i1ings irs readily identified by their color,
texture and position relative to the stream (Fox l984a at p 13).
As explained in Section 1.4, they are the crushed ores remaining
from the extraction of gold in ore milling operations. As such,
they contain varying amounts of the unoxidized or partially
oxidized minerals (azs.nopyrit.s, pyrrhotit.s and pyrites) that
were contained in the parent ores. They also contained varying
amounts of the oxidized mineral products (e.g., arsenates and
1—23
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concentretion of 0 • 4 mg/i in the per• vatez of the
deposits, it is estimated that 40 kg/yr of arsenic are
traflsp .ted out of the tailings deposits and into the
alluvial groundwat.r underlying the dep jts (Chez .y,
et.al 1986c at p 12). This is an eael.). small
a.mow t when compared to the estimatad 45 mjllj
kilograms of arsenic contained in the tailings depos .ts
and the estimated 640,000 ki1og . o arsenic
contained in the underlying alluvj
Ths foregoing conclusions indicate that the arsenic in the
tailings deposit areas is very i mobi1. and is being released and
transported very slowly and in v.ry low amou t into the
underlying dovngradj alluvial g?oun4vat. An analysis of
the distribution of consti ents in the tailings deposits
verjfj this by Providing vide that little
vertical transport of arsenic is now occurring or has occai Ied
over the past 80 years ( erry, eta]. 1986c at p 1). The small
amount of arsenic that is transported into the underlying
alluvium very slightly augmen the large amount of arsenic
already containing in this alluvium, the fate and transport of
which vii]. be discussed in the next s.ctien.
There undoubt. , is loss of tailings and their entrained
arsenic to the surf ace waters of Wh.ttevecd Creek through scouring
It is estimated that 21.6 million tons (19.6 x 1o kg) of
tailings exist vith1 the Site. If these tailings have an
average arsenic cancentr jon of 2,320 ag/kg (derived from Table
1-1), then the total, quantity of arsenic in the tailings is 45
million kilograms.
It is estjms that at least 10 million tons (9 x 10’ kg)
of alluvium underlie the tailings deposits within the Sita. If
this alluvium has an averag, arsenic concentration of 71 ag/kg
(derived from Table 1-1), then the total quantity of arsenic in
this alluvium is 640, 000 kilograms.
1—68
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absence of m.igratlon of arsenic into underlying groundvaters.
There say be sass minor transport of arsenic from the
irrigated (and non—irrigated) cropland soils to ths surface
waters of Whitevood Creek through soil erosion processes. This
contribution cannot be distinguished from that from the tailings
deposits (through scouring and erosion) discussed in Section
1.6.1, and it is included, to the extant that it occurs, in the
estimates given for tailings deposits in that section.
2.• 6 • 4 Arsesia is Residential Property $i li
The above-background levels of arsenic ira the soils of some
of the residential properties vithi-i’ the Site are available f or
crop uptake from the gardens on these properties and human intake
through incidental ingestion of soils be the residents of these
properties. The hu ta health impacts of arsenic intak, through
the consumption of fruits and vegetables grown in the gardens on
these properties are assessed by S!PA (1989) and ( XC ? 2.989).
The human health impact of arsenic intake through the incidental
ingestion of the surface soils on the.. properties is assessed in
EPA’s Final Endangezmsnt Assessment ( acobs 1989).
For the ease reasons stated in Subsection 1.6.3, there is no
indication that th. arsenic contained in the soils of the
residential properties vith4,i the Site are migrating into the
upgradient alluvial groundwater. that underlie these properties
or are migrating to the surfac. waters of lihitevoed Creek.
2—76
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‘l
person who lives in a home located within the tailings deposit
areas and, thus, is exposed to the average concentrations of the
soils of the tailings deposit areas 65% of the time, and who uses
the dovngradj.nt alluvial groundwat.rs for drink water supply.
Put is si.npler terms, the representative Sits resident is one who
encounters the highest probable exposures under current residency
and living patterns, whereas the maximum exposed sit, resident is
one who, in the future, may locata and live in a household
situated in the tailings deposit areas, a possible but unlikely
scenario.
1 • 7 • 1 Potential Cazcinogeni. Risks
The assessment estimates (Jacobs 1989 at Table 6—1) that the
potential lifetime excess carcinogenic risks from exposures to
arsenic through the ingestion of within—Sits soils and
groundwat.r are as follovs:
Soil Total
Representative Sito 1.9 x 2.4 x 10’ 4.3 x 10’
R*sident
Maximum Exposed Sits 4.4 x 20 2.6 x iO 7.0 x
Resident
Recreational Visitor — 8.2 x iO 8.2 x
Referenc Sit. 4.2 x 10 2.6 x 10 5.8 x
Resident
2—81
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The C CLA progras cons idars potential risks that are
greater than 1 x io•’ to be unacceptable. Against this
criterion, the potential risks to recreational visitors and to
the hypothetical resident of the reference site are acceptabl.,
and the potential risks to both representative and axi ii
exposed Site residents are unacceptable. Rowever, with respect
to groundwater, the potential risk fros consuning drinking water
that Ms an arsenic concentration at the National Prinsry
Drinking Water Standard would be 1 x 1O . Therefore, the
potential risk to the representative Sits resident fro. the
consunption of groundwater would be acceptable”.
Froa these estiaates, it is concluded that the arsenic
concentrations in the surfac. soils within the Site present an
unacceptabl. potential risk to residents of the Site. An
exa.aination of the derivation of this potential risk fros these
soils to the representative Sit. resident reveals that it derives
froa three sources: (1) the surface soils of those residential
soils within the Sits that . hibit elevated concentrations of
arsenic, (2) the surface sails of the tailings deposit areas, and
(3) the surface soils of the irrigated croplands within the Sits.
The contributions of the. . sources to this .stiaated potential
risk are as follows:
‘ It should be not.d that the potential risk for
groundwatsrs is associated with the consuaption of drinking water
drawn fro. the upgrsdient alluvial groundwater. wbic are not
iapacted by tailings. Hence this estiaated potential risk is
associated with arsenic concentrations in drinking water supplies
that derive fro. natural causes.
1—82
L
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Residential property soils 2.03 x 10’
Tailings deposit area soils 0.36 x 10’
Irrigat.d cropland soil 0.06 x 10’
Cosbjn.d 2.40 x 10
This partitioning clearly shows that the dosjnant contributor to
the unacceptable potential risk to the repres .n tiv. Sit.
resident frog the incidental. ingestion of within-Sit, soils is
the surface soils on those residential. properties that possess
elevat.d arsenic cencsntratjen as a result of peat deposition or
placesent (as road gravel) of tailings on this properties.
An sxaginatio of tos derivation of the potential. risk frog
within—Sit. soils to the aaxisu exposed sit. resident reveals
that it derives wholly fros potential, residential exposure to the
surface soils of the tailing, deposit areas. Although such
exposure does not currently exist, it is theoretically possible
that it could occur as a result of a person or faxily buiiding
and living in a hos, in ths tailing, deposit areas. In
sI kry, the ass.ss t shows that, with respect to the
incidental, ingestion of withi -sita soils by Site residents, the
soils of existing and potential residential properties located on
the fringe of the tailings deposit areas that exhibited elevated
arsenic conc trat ions present the doainant potential
carcinogenic risk for current 1 iving and exposure patterns, and
the soils of the tailings deposit areas present the dosinant risk
for possible future living and exposure patterns.
Pros the above estisates, it also is concluded that arsenic
1—83
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concentrations in the downgradiant alluvial groundwat.rs present
a possible future unacceptable potential risk (the risk estimated
for the maximum exposed sits resident for groundwater). These
groundvaters do not present a current potential risk because they
are not being currently used for water supply, and because a
Stats regulation prohibits the installation of water supply wells
within the 100-year floodplain of Whitevood Creek within which
these groundwaters are situated.
1 • 7 • 2 Potential Nom-Carcinogenjo ea1th Impacts
The assessment estimates (Jacobs 1989 at Tables 6-2 through
6-6) that the potential hazard indices associated with the
combined exposures to arsenic, cadmium, chromium, copper, lead,
manganese, mercury and nickel through the ingestion of within-
Sit. soils and groundwater are as follows:
Soil Total
Representative Sits 0.54 0.14 0.7
Resident
Maximum Exposed Sit. 3.8 1.1 4.9
Resident
Recreational Visitor — - — 0.05
Reference Sits 0.4 0.0 0.4
Resident
Representative Child — — 1.0
Sit. Resident
2—84
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The C CLA program considers a hazard index greater thai one
to be Potentially unacceptable. Under this Criterion, the
potential flOfl—c cinogenjc health impact, from the ingestj of
within—sit, soil and the consumption of within—Sit. g?oundwa . ,
are acceptable except for the maximum exposed Sit. resident. The
potential health impacts for such an ifldividii l are unacceptable.
Th. cause of these unacceptabi, impact, is the assumed residency
of the maximum exposed Site resident on the tailings deposit
areas and the concomitant high rate, of incidental ingestion of
th. soils in these areas and the Consumption of dovngradj
alluvial groundwater,, exposure not currently encountered by Site
resident, but exposure, that could be sncountsr, in the future
if the tailings deposit areas where to be used for residential
properties and the dovngradj,r alluvial groundwat.zs were to be
used for drinking water supply.
1—85
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Whitewood Creek Site Mining Waste NPL Site Summary Report
Reference 3
Excerpts From Whitewood Creek Study,
South Dakota Department of Water and Natural Resourc ;
EPA and Hornestake Mining Company; November 1984
-------
FOX CONSULTANTS. INC.
DENVER OFFICE
7’O ‘< LNG STREET SUITE 4QQ
DENVER OLOPADO 80215
3C3) 233-7799 Adl inIStMtfve eeerd
S.F F 1 .& N rnber , -)
WIfITEW000 CREEK STUDY
PHASE II
rer arpd
Da jta eoar 7 nL
r j .t tjra esources
of• Air Oual’:y anc S. l ii
, 3 East Caplt3l , Room 219
‘ rre, Suth DaKota 575O1-31 1
3n. c- e 1ining Company
P.O. 875
Lear, South Dakota 57754
‘J.S. Environmental Protection Agency
l 360 Lincoln Street
Denver, Colorado 80295
DreparE j
Fox Consultants, !nc.
710 K 2l1ng Street, Suite 400
Denver, Coi ra 1o fl215
°roject No. 1?t .
NOvC’ ’D. - 193.:
A
7
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1 ’
‘I . ,
I .-)
I - )
J. ) jNT Q Jcflj
The Jh1: wuod Creek Study Focused on ai ihreen i1n segment jr :
‘lood2lain of nitewood CreeK above its corifijence with Relic ur:,
iver arid a five mi1 section of the Belle Fourche River (see 1 it s I iri
riici had ‘ieen irn iacted by the historical —elease ‘if iiltrig s fr r y’ •fl... ;
activities near Lead, South 0akot .
. hitewOod Creek is a tributary a’ tie pi1 Fourcne River, flowin 0r: ’l_
‘east from its source in the Black rli1l of South Dakota past t”e omest e
Mine and tne towns of Lead, Dead ol, and Whitewood before emerging onto :i
floodplain of the 3elle Fourche lvCr on the M’ssouri Plateau. It is fec i .
several small heaciwater streams that enter upstream of the 18 mile segr’en:
under Study. From there Whitewood Creek flows into the Belle Faurcne River at
the d wflstream nci of the 18 mile segment (it shoulct he noted that this .A
mfle stream segment is linear rather than stream ‘riles). The 3e1 1 e Fo.jrt
iver joins the Cheyenne River approximately 13(1 miles fartrier downstream.
The Homestake Mining Company, luc4ted in Lead, South 0akota, began gold
mining operations in the Whitewood Creek watershed in the late 1870’s føll w-
ing development of the gold deposits vfl lch was Initiated prior to 1l SD. -
first milling utilized crude methods to crush the ore and recovered gol 1
gravity means or by amalgamation with mercury. By 1880, the very pri iatie
nonmechanized methods of milling were replaced by more than 1000 stamp -n l
(large blocks of cast iron or steel dropped onto replaceable anvils), cr isr ’ :
the ore to a coarse sand size. The tailings were then discharged to Whitewor c
Creek or its tributaries. Prior to the turn of the century much of trie o ’e
consisted of oxide or hydroxide minerals which were residual oxidation pro-
ducts f the arsenopyrite, pyrrhotite and pyrite mineralization of the ri;-
inal unoxidized ore bodies.
After the turn of the century the deeper, reduced ores from helow “e
zone of oxidation were the focus of mining ct1vity. These ores contained
large percentages of reduced oxidation-state minerals, including arsenopyrite
and pyrrrlotite. The use of cyanide in the milling process also began abou:
this time. As the mining went deeper, maintenance of t e structural integrit y
of the mine ’ älls necessitated backfilling with the coarse fraction ‘i.e.,
sand size portion of the tailings. The finer fraction, referred to as :‘e
slimes, continued to be discharged to the Wh’utewood creek Basin. D iscriar e
from a number of sources ceased in approximately 1920, when Homestake Mini ’s
Company became the only remaining source of tailings discharge.
Mill tailings were discharged directly into Whitewood Creek tflrougrloit
the hundred year history of the mining operations until 1977, with exceptinri
of a brief period (about 5 years) during World War 11 when the mine as
closed. In 1977 Homestake Mining Company, the oniy large commercial rnini;
company remaining in the area, Constructed a tailings Impoun.Jfsent in the uO e
reaches f the watershed. Mining operations over the the last century we
1—1
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53-4
prt,duce(t out 1.000.IILI(J,flflhI ro s of ore anel c rre tly xteod to
zceedin9 8,01)0 feet below Chc? surface. The pr3c ss ny of the ores us
c ’a”ye’1 over the years. as ‘ave he Pxtractlve metallurgy arid t”e crac -’-
ls:ics of the waste stream. Methods fOr th corininutlon and eneficia i r,
t e ores have ecome progressii 1y ur re efficient, as llSCuSSpl abov ,
earlier :311 l ’hJS . ere more coarse and Conl ained nigh r riptil values F. : ,
p r 5anil :oim,n’’ tion , l’H3 .
rli..rctiry alganiation “ e r s as used over t e reat r i..r’c , -
eration and was corinuel until January 1971. The - are va’nus C
uote1 in available literature for tne vol urnes f mercury used md los
‘aste st—earn n cnis rocecs. Juiotes vary from 3n eighth of an ourcC
3l nost i lf an ounce oer ran of ore crush d, with up ti) 5 (1 percent o•
volume being l t to the waste stream. Levels of mercury ‘n the race n;
str arn have heen reported to he as high as 9.1 mg/i (south Dakota Oept. Jf
Health, 196 11) in 19S although average levels were cOnSid r3 1j owe . :ia-
ide has also eei utilized in th gold recovery process since t e rl,
19’lOs, and has been used increasingly to process thQ lower )radeS of re -c
increese gold anc 4 silver recoveries. Since the c ss.itian of mercury se
1971, cyanide nas heøn used exclusively for gold recovery. The tailings a lsc
contatriec considorable quantities nf arsenic whiCh was erived frori rni erais
in tne ore.
Tailings, consisting f finely ;rotind residual etalli: ani
metallic compounds not extracted y the ‘,eneficiation processes. and trace
compounds used in the extractive processes, have been transported and e))s-
Ited y fluvial processes acting in the potion of hitewoot1 Creek downs:-ea’
from ‘he mine. In places tne tailings remain in ahanr1on d channøl —ieaniiers,
bars, and other depositional features and nay h continuing to leach metals
surface and subsurface waters. Reports indicate that in 1963 as ruicil as , rii
tons per day of tailings, together with 12,500 tons per day 3f water, were
being discharged to Whitewond Creek, though this process was ceas i in late
1977. Thus, although direct discharge f the tailings has ceased, the tail-
ings currently in place along Whitewood Creek provide a potential to cause
degradation of ground water quality ‘in the alluvial deposits and of surface
water quality in the UPlitewood Creek valley and downstream area. The po eo-
tial for the release of deleterious chemical constituents from the tailings :
ground water and surface water Is aggravated by the fact that the sul’ i
minerals in the tailings (arsenOpyrite and pyrrntite) can Oxidize when in
contact with water and oxygen. ¼1t1 formation accompanies the ox’i& tlort
process (Cherry, et a )., 1984).
The Comprehensive Environmental esponse, Compensation and Liability c
Jf 1980 (CERCLA) (DL_05_S10) required the President to identify tne 400 fac’ 1-
ities in the Nation warranting tha highest priority tor remedial action. ‘ ‘
order to set tIle priorities, CERCLA requires that criteria he establlsiel
based on relative risk or danger.
On October 23, 1981, Frivirorimenrdl rateCtion Agency (I ISEPA) pubhis e i’
interim list f 115 priority sites unt!r CERCLA. One of the interim sites s
designated was an 18 mile segment of Whitewooci Creek. The Whitewood Cr, ..
site was listed principally upon information provided tO USEPA hy the S:
/
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57
1
Mining Waste NPL Site Summary Report
Wayne Interim Storage FacilityfW.R. Grace
Wayne, New Jersey
U.S. Environmental Protection Agency
Office of Solid Waste
June 21, 1991
FINAL DRAFT
Prepared by:
Science Applications International Corporation
Environmental and Health Sciences Group
7600-A Leesburg Pike
Falls Church, Virginia 22043
-------
‘ c v
j
1
DISCLAIMER AND ACKNOWLEDGEMENTS
The mention of company or product names is not to be considered an
endorsement by the U.S. Government or by the U.S. Environmental
Protection Agency (EPA). This document was prepared by Science
Applications International Corporation (SAIC) in partial fulfillment of
EPA Contract Number 68-WO-0025, Work Assignment Number 20
A previous draft of this report was reviewed by Bob Wing of EPA
Region II [ (212) 264-8670], the Remedial Project Manager for the
site, whose comments have been incorporated into the report.
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Mining Waste NPL Site Summary Report
WAYNE INTERIM STORAGE FACrLITY/W.R. GRACE
WAYNE, NEW JERSEY
INTRODUCTION
This Site Summary Report for the Wayne Interim Storage Facility/W.R. Grace site is one of a series
of reports on mining sites on the National Priorities List (NPL). The reports have been prepared to
support EPA’s mining program activities. In general, these reports summarize types of environmental
damages and associated mining waste management practices at sites on (or proposed for) the NPL as
of February 11, 1991 (56 Federal Reaister 5598). This summary report is based on information
obtained from EPA files and reports and a review by the EPA Region II Remedial Project Manager
for the site, Bob Wing.
SITE OVERVIEW
The Wayne Interim Storage Fadiity/W.R. Grace NFL site consists of 6.5 acres located in Wayne
Township, Passaic County, New Jersey. At this site, thorium and rare earth elements were extracted
from monazite sands between 1948 and 1971 (Reference 1, pages 7 and 8) The facility is located in
a primarily residential area; however, land within .25 mile of the site is also used for commercial,
industrial, and agricultural purposes (Reference 2, page 7). The site is included in the Department of
Energy’s (DOE’s) Formerly Utilized Sites Remedial Action Program (FUSRAP) (Reference 1, page
9).
Constituents of concern are thorium and decay products, radium-226, uranium and decay products,
and radon (Reference 2, page 2). DOE is the Potentially Responsible Party (PRP). The site has been
on the NFL since 1984 (Reference 1, page 9). Preliminary chemical and radioactive characterization
and the removal of wastes from vicinity properties to an onsite storage pile has been conducted
(Reference 1, page 10). DOE is currently conducting the Remedial Investigation (Reference 4).
OPERATING HISTORY
Beginning in 1948, Rare Earths, Incorporated, extracted thorium and rare earths from monazite ore
on the site. W.R. Grace acquired Rare Earths, Incorporated, in 1957 and continued operations until
1971 (Reference 1, pages 7 and 8). After 1971, the site was licensed for storage only (Reference 1,
page 8). Electronucleonics, Incorporated, operated the property from 1975 to 1983, using it for
1
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Wayne Interim Storage Facility/W.R. Grace
office and storage space (Reference 1, page 8; Reference 2, page 10). W.R. Grace retained
ownership until 1984, when DOE acquired the site (Reference 1, page 9). The site is intended to be
an interim storage site until a permanent waste disposal site is established (Reference 1, page 9).
From 1985 to 1987, DOE excavated contaminated material from area property to an onsite storage
area. Areas excavated included a bus maintenance facility, a township park, and property along
Sheffield Brook and Pompton River. Approximately 38,500 cubic yards of waste is stored currently
in an onsite pile, while an estimated 70,000 cubic yards of material is buried onsite (Reference 1,
page 10). The buried wastes contain approximately 76 tons of thorium (Reference 5). Information
concerning the buried wastes are incomplete due to an onsite fire in 1977 which destroyed burial
records (Reference 1, page 8).
SiTE CHARACTERIZATION
Due to limited investigation, incomplete information is available concerning the site. A series of
radiation surveys were conducted from 1981 to 1983 by the New Jersey Department of Environmental
Protection (NJDEP), EPA, and the Nuclear Regulatory Commission (NRC) (Reference 1, page 8). A
report prepared by ERM in 1983 (Reference 6) characterized ground-water contamination at the Site.
Another report prepared in 1983 for the NRC (Reference 7) characterized surface and subsurface soil.
Remedial Investigation field work has been initiated by DOE; however, results are not yet available
(Reference 4).
Ground Water
The geology of the area consists of glacial deposits with a thickness of 20 to 50 feet overlying the
Brunswick formation of sandstone and mudstone. Ground water is found in the unconsolidated glacial
deposits as well as in the underlying bedrock aquifer (Reference 6). Both aquifers are sources of
ground water for public water supply and industrial use, though the bedrock aquifer is the major
source of ground water in the County (Reference 6).
Six onsite wells were installed in the uppermost aquifer in 1982, at depths ranging from 8.5 to 20 feet
(Reference 6, page 3). At least four wells are downgradient of contaminated areas, while two are
very close to contaminated areas. Sampling was conducted in December 1982 and January 1983
(Reference 6, page 3). Results of monitoring do not indicate that gross alpha levels in excess of the
primary drinking water standard of 15 pico Curies per liter (pCiIl) are migrating beyond the facility
boundary. Levels of gross alpha in downgradient ground-water wells ranged from Not Detected (ND)
to 9 pCifl, while levels of gross alpha in ground-water wells close to areas of contamination ranged
2
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Mining Waste NPL Site Summary Report
from 40 to 300 pCi /I. The pH of ground-water samples ranged from 4.6 to 11.5 (Reference 6, Table
2). Information concerning monitoring for other parameters and any additional conclusions on
ground-water contamination were not presented in the available references.
Levels of thorium-232, thorium-228, radium-226, and uranium-238 are summarized below (3n Table
1) for surface and subsurface soil samples at 43 onsite locations (Reference 7, Table 3). Between one
and six subsurface samples were collected from each location at depths of 0.5 to 6.3 meters.
TABLE 1. TOTAL CONSTITUENT CONCENTRATION IN ONSITE SOIL (IN pCilg)
Location
Thorium-232
Thorium-228
Radium-226
Uranium-238
Surface
1.46-3970
1.20-4,000
0.59-930
ND-910
Subsurface
0.40-14,800
0.71-15,700
0.52-1,760
ND-653
No information on background soil levels for this area was presented (Reference 7, Table 3).
Available information from the 1983 Radiological Survey, from which these data were obtained, was
incomplete (Reference 7). Therefore, sample dates, extent of contamination, and offsite
contamination are not known.
ENVIRONMENTAL DAMAGES AND RISKS
Aerial surveys conducted during 1981 and 1982 indicated elevated levels of radiation at the site and at
an area west of the plant site (Reference 1, page 8). Radiological surveys conducted in 1982 and
1983 revealed offsite contamination of ground water, surface water, soil, and sediments with thorium,
radium, and uranium (Reference 1, page 8). According to a separate 1982-1983 ground-water
monitoring survey, data did not show gross alpha levels in the uppermost aquifer migrating beyond
site boundaries at levels above the primary drinking water standard (Reference 6).
Characterization of the confluence of Sheffield Brook with the Pompton River in 1986 suggested that
contamination was confined to the mouth of the Brook, and did not extend downstream into the river.
In addition, following the excavation of portions of Sheffield Brook in 1987, no chemical
contamination attributable to the site remained (Reference 1, page 10).
3
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Wayne Interim Storage Facility/W.R. Grace
The area surrounding the site is primarily residential, with some commercial properties (Reference 2,
page 7). The specific risks associated with the site were not provided in the available references.
REMEDIAL ACI1ONS AND COSTS
Removal of waste from nearby properties to an onsite storage pile was conducted from 1985 to 1987
(Reference 1, page 10). According to EPA, the cost to remove, transport, and dispose of waste
materials from three DOE FUSRAP sites in New Jersey is estimated by the NJDEP to be
$210,000,000. The volume of soil at the Grace site represents approximately 20 percent of the total
volume of waste materials from the three sites.
CURRENT STATUS
An interagency agreement between EPA and DOE for site study and clean-up was signed on
September 17, 1990. EPA is currently reviewing public comments received on the agreement. Field
work is presently being conducted by DOE, although a work plan for the Remedial Investigation
Feasibility Study has not been approved by EPA (Reference 4). Additional Remedial Investigation
field work is expected to be initiated in the fall of 1991, while DOE expects a Record of Decision to
be signed in 1994 (Reference 4; Reference 3).
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Mining Waste NPL Site Summary Report
REFERENCES
1. Federal Facility Agreement; EPA and DOE; September 17, 1990.
2. Potential Hazardous Waste Site Inspection Report; EPA; undated (Ca. 1984).
3. Letter Concerning Planning Documents for Remedial Investigation; From William M. Seay,
DOE, to Bob Wing, EPA; February 26, 1991.
4. Telephone Communication Concerning Current Site Status; From Sue McCarter, SAIC, to Bob
Wing, EPA; January 23, 1991.
5. Letter Concerning Transfer of Property; From B.L. Molbey, W.R. Grace, to Bernard Singer,
Atomic Energy Commission; October 30, 1974.
6. Preliminary Investigation of Shallow Ground-water Contamination at the W.R. Grace Facility,
Pompton Plains, New Jersey; Prepared for W.R. Grace by ERM Southeast, Inc.; March 1983.
7. Radiological Survey of the W.R. Grace Property, Wayne, New Jersey; Prepared for the U.S.
Regulatory Commission by Radiological Site Assessment Program, Oak Ridge Associated
Universities; January 1983.
5
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Wayne Interim Storage Facility/W.R. Grace
BIBLIOGRAPHY
EPA. Potential Hazardous Waste Site Inspection Report. Undated (Ca. 1984).
EPA and DOE. Federal Facility Agreement. September 17, 1990.
McCarter, Sue (SAIC). Telephone Communication Concerning Current Site Status to Bob Wing,
EPA. January 23, 1991.
Molbey, B.L. (W.R. Grace). Letter Concerning Transfer of Property to Bernard Singer, Atomic
Energy Commission. October 30, 1974.
Prepared for the U.S. Regulatory Commission by Radiological Site Assessment Program, Oak Ridge
Associated Universities. Radiological Survey of the W.R. Grace Property, Wayne, New Jersey.
January 1983.
Prepared for W.R. Grace by ERM Southeast, Inc. Preliminary Investigation of Shallow Ground-
water Contamination at the W.R. Grace Facility, Pompton Plains, New Jersey. March 1983.
Seay, William M. (DOE). Letter Transmitting Planning Documents for Remedial Investigation to
Bob Wing, EPA. February 26, 1991.
Stevens, Mary (SAIC). Telephone Communication Concerning Onsite Mining Activities to Bob
Wing, EPA. Undated (ca. July 1990).
6
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I
I
I ,
Wayne Interim Storage FacilitylW.R. Grace Mining Waste NPL Site Swnmary Report
Referef ice 1
Excerpts From Federal Facility Agreement; EPA and DOE;
September 17, 1990
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‘p
LI
UNITED STATES ENVIRONMENTAL PROTECTION AGENCY
AND THE
UNITED STATES DEPARTMENT OF ENERGY
IN THE MATTER OF:
The U.S. Department ) FEDERAL FACILITY
of Energy’s AGREEMENT UNDER
CERCLA SECTION 120
Wayne Interi m Storage Site )
Administrative
Docket Number:
II CERCLA-FFA_0 0102
Based on the information available to the Parties on the
effective date of this FEDERAL FACILITY AGREEMENT (Agreement),
and without trial or adjudication of any issues of fact or law,
the Parties agree as follows:
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including the Site Remedial Tnvestigatjon performed by DOE as
described in Part XI (Remedial Investigation) below and
Attachment 2.
VI. FINDINGS OF FACT
For the purpose of this Agreement only, the following constitutes
a summary of facts upon which this Agre€ment is based. None of
the facts related herein shall be considered admissions by any
Party with respect to any unrelated claims by a Party or by
persons not a Party to this Agreement.
(1) During the 1940s and 1950s, the Manhattan Engineering
District (MED) and its immediate successor, the Atomic Energy
Commission (AEC), conducted several programs involving research,
development, processing, and production of uranium and thorium,
and the storing of their processing residues. Nearly all of this
work involved some participation by private contractors and/or
institutions. Generally, privately-owned and institutionally-
owned sites that became contaminated during this early period of
the nuclear program, and have since been converted to other use,
were decontamjnate or stabilized in accordance with the
guidelines and survey methods then in existence.
(2) However, radiological guidelines have since become more
stringent. As a result, the Department of Energy (DOE) initiated
the Formerly Utilized Sites Remedial Action Program (FUSR.AP) in
1974 with the singular mission of identifying, decontaminating,
or otherwise controlling sites where low activity radioactive
contamination (exceeding current guidelines) remains from the
early years of the nation’s atomic energy program or commercial
operations causing conditions that Congress has authorized DOE to
remedy.
(3) DOE has authority under the Atomic Energy Act to conduct
Remedial Actions at a number of sites around the country. In
addition to its authority under the Atomic Energy Act,
Congressional Committee Reports accompanying the FY 1984 and F?
1985 Energy and Water Development Appropriations Acts, Public
Laws 98-50 and 98-360, respectively, authorized DOE to conduct a
decontamination research and development project at various New
Jersey locations where radioactive contamination is present.
(4) In 1948, Rare Earths, Inc., began to extract thaf±’.
rare earths from xnonazite sands at a six and a half acre Site in
Wayne Township, Passaic County, New Jersey. Upon pasc ; - - -
Atomic Energy Act in 1954, Rare Earths, Inc., received an Atomic
Energy Commission (AEC) license for this processing.
(5) In 1957, the Davison Chemical Division of W.R. Grace
accuired Rare Earths, Inc.
7
4 ; ’
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(6) W.R. Grace continued operations at the site until July,
1971. After 1971, the site was licensed for storage only.
During part of this time Electro-Nucleonics, Inc., rented the
site for office and storage space.
(7) A railroad siding in Pequannock Township, New Jersey, was
used for transfer of radioactive ores from railroad cars to
trucks used to haul the ore the remaining distance (1—2 miles) to
the site. During the transfer, some radioactive ore was spilled,
resulting in contamination of about 400 cubic yards of soil near
the area.
(8) From 1948 through 1971, radioactive processing wastes were
buried on site. Some radioactive processing wastes were released
to storm drains as liquid effluent. The storm drain empties intc
Sheffield Brook, which overflows its banks during periods of
heavy rainfall, causing contamination from the processing
operations to spread to nearby low-lying properties.
(9) In 1974, the Nuclear Regulatory Commission (NRC) assumed
licensing responsibilities formerly held by the AEC.
(10) In 1974 and 1975, the site was partially decontaminated,
then decommissioned and the storage license terminated. Some
buildings and equipment were buried on site. The rest were
decontaminated to then-current criteria. The site was released
for unrestricted use, provided the land deed indicated
radioactive material was buried on site.
(11) A fire in May, 1977, destroyed most of the early records
that could have identified wastes and burial locations.
(12) EG&G performed aerial surveys of the W.R. Grace facility
and areas west of the site in 1981 and 1982 for U.S. EPA at the
request of the New Jersey Department of Environmental Protectior.
(N:DEP). Results indicated radiation levels elevated above
background in these areas.
(13) Further radiological surveys by NJDEP and by Oak Ridge
Associated Universities for the U.S. Nuclear Regulatory
Ccm ission in 1982 and 1983 detailed areas of radiological
contamination in the Sheffield Brook area, the township park, the
right—of-way property, the school bus maintenance facility, the
railroad siding and several other Vicinity Properties, as well as
the W.R. Grace processing facility itself. Thorium, its da_g
isotopes and related radionuclides, including thorium—232,
radiumn-228, radiuxn—226 and uranium-238, were identified in
contaminated soil, surface water, sediments and groundwater to
above background levels and in many cases above the applicable
guidelines and standards. Borehole sampling indicated buried
radioactive material to a depth of at least 16 feet.
8
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In December, 1982, W.R. Grace installed r’i e deep and six
shallow groundwater mon oring wells.
(15) Groundwater in the vicinity of the WISS is found in both the
unconsolidated glacial deposits and the underlying bedrock.
Groundwater in the unconsolidated material in the stratified
glacial deposits is an important source of water for public
supply and industrial use in Wanaque, Pompton Lakes and along the
western side of Wayne Township. However, for the most part,
these unconsolidated deposits have not been extensively explored
and represent a potentially important source of groundwater for
future development. Currently, the Brunswick formation is the
major source of groundwater for public supply and industrial use
in Passaic County.
(16) The W.R. Grace site was proposed to the National Priorities
List (NPL) on September 8, 1983. The site was included on the
NPL on September 21, 1984.
(17) Through Congressional action (PL9B—50) in 1984, the site was
included in DOE’s FUSRAP program whereby DOE was authorized to
conduct a decontamination research and development project
related to the radioactive contaminants. Neither DOE nor its
predecessor agencies had a role in the generation of this
contamination.
(18) On September 18, 1984, DOE accepted the site from W.R.
Grace in compliance with Congressional direction for use as an
interim storage site, pending establishment of a permanent
disposal site. DOE renamed the site the Wayne Interim Storage
Site (WISS). Preparation for on-site interim waste storage
involved demolishing two on—site buildings in 1985 to increase
room for the storage pile, then building a cell complete with
berm, liner, leachate collection system and impermeable covering.
The drainage pattern on the WISS was improved to inhibit
migration of radiological contamination from material buried on
site.
(19) The agreement for DOE to accept the donation of real
property and funds from W.R. Grace provides that it shall not
affect the rights and liabilities of W.R. Grace under other
existing applicable laws.
(20) From November, 1984, to January, 1985, DOE installed six
bedrock (deep) and five overburden (shallow) groundwater
monitoring wells in pairs, making a total of six groundwater
monitoring locations around the perimeter of the site. These
wells were installed as part of requirements for the NJDEP
Emergency Groundwater Permit and New Jersey Pollutant Discharge
Elimination System (NJPDES) permit.
9
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(21) In 1984, DOE established a quarterly envirOnment
onitOriflg program for air, surface water, groundwaters sediments
arid external gamma radiation. To meet NJPDES requirements,
groundwater iS - sampled for radioriuClid5 5 and selected chemicals
each quarter. Annual environmental reports from DOE summarize
the results of the onjtOriflg.
(22) In January and FebruarY, 1985, OOE performed a limited
chemical characterization of the site and found organic and
inorganic compounds and metals. Previous charaCter1Zatbo
indicated that hazardous substances included sulfuric acid,
oxaliC acid, hydrochloric acid, ammonium chloride, sodium
metabisulfate, ammonium hydroxide arid hexamine solutiOnS.
(23) In 1985, DOE remediated the bus maintenance facility by
removing contaminated soils to the WISS. A small section of the
bus maintenance facility still above DOE guidelines was
remediated in 1986 and the propertY was verified as clean.
(24) In 1985, the township park was excavated. A small
remaining area still above DOE guidelines was excavated in 1986
and the property has been verified as clean.
(25) In 1986, two small areas from the front yard of the WISS
and from the right-of—way property were excavated.
(26) Characterization of the confluence of Sheffield Brook with
the PotnptOn River in 1986 by DOE suggested contamination was
confined to the mouth of the brook and did riot extend into the
river or downstream.
(27) Also in 1986, an area along Sheffield Brook was excavated.
In 1987, DOE completed excavation along Sheffield Brook arid into
the mouth of the brook where it entered the Pompton River. All
excavated soils were placed in a storage pile on the WISS.
post exCavati0fl radiolOgiCal surveys of these areas were
performed to ensure that no radionuclide concentrations above DOE
guidelines remained. These excavated properties conform to all
applicable radiological guidelines for their release with no
radiological restrictions on its use.
(28) U.S. PA performed oversight chemical analyses Ori the
Sheffield Brook excavation during the summers of 1986 and 1987 to
determine if chemical contamination remained. The results
verified that no chemical contamination was present that was
attributable to the WISS.
(29) The storage pile at the WISS contains about 38,500 cubic
yards of contaminated material. In addition, about 70,000 cubiC
yards of FUSRAP Waste are buried on the site.
10
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1
Wayne Interim Storage FacilityfW.R. Grace Mining Waste NPL Site Summary Report
Reference 2
Excerpts From Potential Hazardous Waste Site Inspection Report; EPA;
Undated (ca. 1984)
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(•7
Wayne Interim Storage Facility/W.R. Grace Mining Waste NPL Site Summary Report
Reference 3
Letter Concerning Planning Documents for Remedial Investigation,
From William M. Seay, DOE, to Bob Wing, EPA;
February 26, 1991
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U I J Li
Department of Energy
Oak Ridge Operations 91—113
PO.Box200l
Oak Ridge.Tennessee3783l— 8723
February 26, 1991
Mr. Rnbert Wing
Federal Facilities Section
EPA Region II
Jack K. Javits Federal Building
New York, New York 10278
Dear Mr. Wing:
DRAFT WAYNE SCOPING/PLANNING DOCUMENTS FOR EPA REVIEW
Enclosed are ten copies each of the scoping/planning documents for the remedial
investigation/feasibility study-environmental impact study (RI/FS-EIS) for the
Wayne site in Wayne, New Jersey. Each set of documents consists of a work
plan, a field sampling plan which will direct the radiological/chemical/
geological investigations, a quality assurance project plan, a health and
safety plan, and a community relations plan. The geological investigation was
completed in the fall of 1989 and chemical sampling of the storage pile was
completed in the fall of 1990.
As specified in the Wayne site Federal Facilities Agreement (FFA), these
documents are being submitted to the Environmental Protection Agency (EPA) for
review and comment. The FFA also states that a 60—day comment period is
allowed for EPA’s review; therefore, we hope to receive your comments by
April 30, 1991. EPA and subsequent public review of these documents is on the
critical path for initiating the remedial investigation field work this falL P
Any acceleration or delay in the review cycle will directly affect the start
date for the field work.
To expedite and simplify your review, please don’t hesitate to contact me at
any time at FTS 626-1830. You may also feel free to contact Rick Robertson at
Bechtel with technical comments. Rick can be reached at FTS 626—4718. We look
forward to working with you on finalizing the remedial investigation approach
for the Department of Energy’s responsibilities related to the overall Wayne
site.
Sincerely,
William II. Seay, Deputy Director
Former Sites Restoration Division
End osures
cc: Rick Robertson, SNI
Larry Jensen, ANL
Jim Wagoner, DOE-HQ
Peter J. Gross, DOE
-------
Wayne Interim Storage Facility/W.R. Grace Mining Waste NPL Site Summary Report
Reference 4
Telephone Communication Concerning Current Site Status;
From Sue McCarter, SAIC, to Bob Wing, EPA;
January 23, 1991
-------
TELECOMMUNICATIONS
SUMMARY REPORT
SAIC Contact: Sue MeCarter Date: 1123/91 Time: 10:30 a.m.
Made Call ...X... Received Call —
Person(s) Contacted (Organization): Bob Wing, EPA, (212) 264-8670
Subject: Current status of W.R. Grace
Summary: DOE signed the Interagency Agreement on July 23, 1990, and EPA signed the agreement
on September 17, 1990. Even though the agreement had been signed, it went through a public
comment period that ended on November 19, 1990. EPA is now la the process of reviewing these
comments and anticipates completing the review by late February. Once the agreement becomes
effective, EPA can request a schedule from DOE on completing the Remedial Investigation. DOE
has provided EPA with a draft work plan, not submitted for review since it had not received full
clearance from DOE. However, DOE began field work in the absence of a work plan and
Interagency Agreement. Most field work has been done, although no schedule was negotiated. Bob
feels a Remedial Investigation may be available by the fall of 1991. DOE said it expects a ROD in
1994, but EPA has responded unofficially that it does not accept that date. (Also, since the work
plan will most likely be submitted after field work has been completed, EPA has reserved the right
to request additional field work if it does not approve DOE’s work plan.)
Regarding NJDEP’s proposal to ship waste to a disposal facility in Utah, Bob says the Remedial
Investigation/Feasibility Study must be completed and an In-depth characterization of the waste
must be performed before shipments can be considered. The facility may or may not accept the
waste since DOE characterizes It as by- product materials. The Utah disposal permit does not allow
acceptance of this type of waste yet; and, the disposal facility is not equipped with a cell to accept
this type of waste. It must first obtain an amendment to its license and then construct an
appropriate cell to accept W.R. Grace’s waste.
r
-------
I )
Wayne Interim Storage Facility/W.R. Grace Mining Waste NPL Site Summary Report
Reference 5
Letter Concerning Transfer of Property;
From B.L. Molbey, W.R. Grace, to Bernard Singer, Atomic Energy Commission;
October 30, 1974
-------
W.RGC &CO. ”SC -E :
- CrL LE5 L !Ai C E EA MC E. M 22C 3C
Oc.t . : 30, l 74
Mr. Berna.d Siflger
Chief, Materials Licensing
tJnited States Atotnic Energy Ccx issi n
Washington, D. C. 20545
Attention: M. Euchana.n
Re: License STA—422
Gentlenen:
We have applied for a Release of cur property at 868 Sla:k
Oak Ridge Road, Wayne Township, New Jersey, from ?2C Stcra e
License STA—422. This property was inspected on September 2C,
1974, by Mr. Epstein, of the AEC Compliance Section at ing of
Prussia, Pennsylvania. I understand that he recomnended a rcv .
of cur ap lication on th.e basis of his inspection.
On Tuesday, Octob r 29, I called Mr. McClintock to ask hi to
trace our application, which seems to be lost somewhere be .ween
his office and yours. Mr. McClintock informed me that when he
fowarded Mr. Epstein’s report, he reco nended that certa n .te s
of information, not included in Applied Eealth Physics’ dec —
ination report, be developed; namely:
(1) Th total amou.n t of radioactive materials buried c-.
the site,
(2) An evaluation to show that the buried material w: .
not be washed into local streams by erosion of t e
surface of the burial area, and
(3) An assurance that future owners of the property w:
not excavate or in any way disturb the buried
I submit the following in answer to these çuesticnz:
(1) Our records show total burials of 7.7 curies C
thori yr 152,350 pc nds buried in accordance -
1OcFR2O.
-------
wSG CE&co.
1SCN H v1 AL CMSCN
Mr. 3erna d Singer
OCtober 30, 1974
Page 2
(2) The bt. ria1 area was graded, dressed. with cver 6O yards
of fill dirt, and seeded. Nun erc s c e
drainage from the area failed to disclose any :a :—
activity of the noff water. The area is already
generating its own crop of grass and weeds. by
past experience, it will be further stabiljze w .th
fast-growing tree seedlings fron the adjacent woods
within a season or two. The grading was done so as to
enchance proper drainage and minimize erosion. Re:ajne:
walls were erected where deemed necessarv to further
reduce any chance of erosion. Several hard rains have
been experienced since completion of the job, and. no
significant erosion has been observed.
(3) We expect to sell the property to Electro—Nucleonics,
Inc., presently tenants renting office and storage
space, as soon as the facilities arereleased as per
our application. The conditions of sale will inc2 . d.e
a deed restriction against disturbing in any way the
buried material. This restriction will be made bind. .ng
on any future resale of the property.
I trust this will satisfy the quest±ons raised by Mr. McClint:
transmittal of Mr. Epstein’s compliance inspection report. If the:
are any further questions, please don’t hesitate to call me at
(301) 727—3900. - -
Very truly yours,
a
B. L. Mobley
Supervisor
Envirorunental Control
BLM:n bs
cc: Zir. R. McCliatock
C. S. Atomic Energy Coz nission
Directorate of Regulatory Operations
Region I
631 Park Avenue
King of Pri. ssia, Pennsylvania 19406
-------
7
Wayne Interim Storage Facility/W.R. Grace Mining Waste NPL Site Summary Report
Reference 6
Excerpts from Preliminary Inv tigation of Shallow Ground-water Contamination
at the W.R. Grace Facility, Pompton Plains, New Jersey;
Prepared for W.R. Grace by ERM Southeast, Inc.;
March 1983
-------
? LI I ARY tNVESTtCATIO OF SEALLCW GROCND— JAtER
CON AMINAT1ON Al T E W.R. GRACE ACILtiY
PC ION PLJ INS, NEW JEPSEY
March, 1983
Prepared For:
v.a. Grace & Company
Prepared by:
E3M—Se .itheas , tr c.
P.O. E x 881
3re vood, Te essee 37027
-------
as well as the a:a .a .e ..e.. . . .33 . a:e :a: :-
. j . knesS of the unc:r.sol aed ;1.ac.a1. e os_:S e
ity are ex;eced to :a ge f::: 20—30 fee:. The d:.l .r g .og f :-e ;—s _ :o
azesian well repO S a total of 37 fee: of nc sol a: d ce;cs’.:3 a: : s :e.
The 3runswick yornatiori of the Triassic age unde:l ..eS the s L a:
glacial dePosits at the w.a. Grace fac .lity (yi;ure4). This edroc f:: . :
typically consists of a1te nating beds of red4ish—brO . t sandstone and n .ds::ne.
The texture of the bedrock is generally coarser in the northern pare of : e
area than in the southern part. In the general area of the site, the nsw .:k
Fornation typically forms broad valleys between the Watchung Mountains and the
gently rolling lowlands east of the Firs: Watchung Mcunta ns. The underly: g
bedrock generally has amonoclinLi. dip of 10—15 degrees west, however, locally,
steeper dips can be found throughout the area. Minor north trending rtcrnai
faults cut the Triassic rocks in several areas. The 3runswick Tornati:n c:n—
tains vertical joints with the major join: sets being parallel and t:ansve Sa
to the strike of he beds.
a
Ground— 4aer Hvdrology — Ground—water in the vicinity of the U.R. Grace
facility is found in both the unconsolidated glacial deposits a well as :he
derlyin 5r . .nswiCk Formation. The occurence and cveent of grour.d a
the unconsolidated deposits are controlled by in :erg:anular openings in a
POSLS, whereas ground—Water in the consolidated bedrock ocrurs in and :: s
through c.Leava3e ylanes, joints, fractures, and faults. These secor. a?
ings in the coo.solidatd bedrock form a comparatively saLi. t volu.e in c:n ari—
son tn the total vo1 e of rock. These openings also b.cO e fewer and :.; .:er
Vtth increased depth below the land surface.
The total ground— Jaer flow sys:en in Passaic County is a few h n:: : fee:
thick and is conprised of seve ra.1 separated by divides
- — - ——— .— J ..—— - —
-------
sysens in Passaic Co :y are :epor:ed : e gene:a1’ snail w.:n : .a:; s:
sySen de:Lying an area f only a few sçuare nilas. o reg na r:’ :-. :e:
fl:w sysan underlies the entire cot t:y.
The s:rac.f:ed glacial deposits of Quaternary age are an in;or:ar.: scu::!
cf g und-water for pu iic supply and industrial use ..n anaque and ?c ;::n ..akes
and along the western side of Wayne township. However, for the nos: ;a::, : .ese
unconsolidated deposits have not beer extensively expLored and represent a poten-
tially inportant source of ground—water for future deielopent actording t :‘e
t3SGS. These stratified glacial . deposits generally yield larger quantities of
water to individual wells than do the ocher mejor geologic units in Passaic Count
Recorded yields of wells in these unconsolidated deposits range from 4 to 920
gallons per m.inute with the median yields of domestic weLts being approx r.a:alY
16 gallons per minute and those of public and industrial wells being appr: c.nae2
130 gallons per minute. ‘.cst wells tapping the unconsolidated glacial depos::s
are between 50 and 12.5 feet deep.
The Brunswick Formation which underlies the unconsolidated depos 4 .S in the
vicinity of the W.R. Grace facility is the most inportant aquifer in ?assa.: C: .c
This formation is the major source of ground—water for public supply and in us:r
use in the county. !i.lds of public and industrial wells in the .n.Y are
reported to range from 20 to 510 gallons per minute with a median yield of
&;prox.is.ately 130 gallongs per minute. Most of the high yielding wells :a;; n
the Brunswick Po tation are located in the valleys in the more indus’r a1. areas
in Hawthorne, Patterson, Clifton, and Passaic and are located in or on : e f.ar.
of pre-g1.aciai . valleys containing comparatively thicker unconsolidated de;csiS.
These locations are conducive to higher recharge rates to the bedrock a:_ f :.
estic wells tapping the Brunswick Tornation typicaLly have much sna .e: i:eL:
C midian reported yield of approxi; .tCi/ 13 gallons per minute. ‘ :s :ne
-------
ra ‘ e een 2C0 and . .3O fae: deep.
The field ves;aC.CnS tnplenen:ed as par: of :h s ;: .-
:: de :e e grass alpha radiation levels in the shallow ground—waer s’.s:an
underlyin8 the W.R. Grace facility. A total of six shallow g d— a ar cn-
toring wells were installed at the W.R. Grace site dur .ng the weeks of 2ecen e:
13, and Dece_ er 20, 1982. To of these new on—site
th lcse to known waste disoesal s :es.... ._ The f ur
renaming wells were loca:ed weSt of the known areas of waste dis csal : r —
vide nore re ese ’ ‘ ‘ d—water quality downgradient of the fac .. .—
loca :iors of the six on—site monitoring wells are depicted in 1 re .
The six ground—water on1toring wells were drilled and installed by :‘.e
Jaren—Gectge Drilling Conpany under the direct supervision of a staff geol gis:
fron EP , Inc. Each of the ground—water :onitoriag wells was cons:r.Lced of
2—inch pipe equipped with a 5—foot section of 0.02 inch slotted PVC pipe. An
outer protective steel casing was installed at cnitodng wells EN—I, 1N5,
and E 4—6, and. equipped with 1.ocable steel caps. ionitoring wells EN—2 and EN-3
were required to be conpieted flush wtth the ground surface wtth screw-On :a s
be.ng installed. The tat d — ‘—— each of the gr:und—water :
installed at the site are as follows: EN—I. 10 ‘••‘ T—’ i-r—Li
fee jEN—4. 20 feet; EY—5 , 14 feet: p’t 4 ‘ j et . Individual c:._—
Logs depicting construction d.etai3 s of each monitoring well are prov:da:
A;p djx I L
The naterials encountered during the installation of the cn—s
WILLS indIcated prinartly a heterogeneous n.ix:ure of sands, silts, an: clays.
At nonltorlng well EN—i, a brown, silty fine sa d wa encountered f::n a; X
-------
a:e1y 3 t 10 feat. : .oni:cring wells EN—2, N . ., t’.e n;
a:erials :onsis:ed of a .x:’ re of sand, sii:y, and tlay. .aLLs
N—5 and N—6 1 a light g:av sandy mick :a ertal, e1ieved to ossi lv ‘
ate als. was e o ntered in each of these bori s . Due to c.-te d1... ne od
ucilized to install these ortitoring wells, it was iposs b1e to id t:f:’ any
stratification in the underlying deposits. In order to aid in the fu: . :a ;.ass—
ification of the unconsolidated deposits encountered during the installa:.:n of
these monitoring wel1 , as well, as for possible determination of gross a1;r a
radiation concentrations, shelby tube s ples were collected at varying intervals
at each of the on—site monitoring wells. The depth of each shelby tube san;Le
in the an—site borings is’ provided in the drilling logs contained in Appendix U.
Following the completion of installation of the on—site ground-water ncni-
toting wells, the first set of grot d—water samples was collected on De encer 20
and 21, 1982 by E3.M personnel. The in.itial ground—water sa.nple from eath .rell
was collected without purging any water fr the well. Satples from tne .els
were collected utilizing a one—inch PVC bottom-.fi1ling bailer with ind:v .d al
samples being collected in 500 milliliter unpreserved polyethylene sample con-
tainers. Prior to sampling each veil, the depth to water level from the top of
casing was msazwrsd utilizing an electric water level indicator. Tollcwin one
collection of the initial sample at each well, each well, was bailed un: .l one
well, was essentially dry.
Following cnllection of the initial jround—vater samples, two subseçuen
$ PLes vets collected fro each well with the exception of cnitoring !N-
from vt ich only one subsequent sample was collected. The gtcund Jatet sa.n;.es
tOlltct.d subseq’.3ent to the initial sample were collected following ex:es.fe
bailing of each well between collection of water samples. The third sa:e
monitoring well E —6 was not collected due to the tine delays i:: ;:
-------
p1as:i ai rter. a’:e.s .e: a__: ::a_ ad eac . :: _—: _
sa pLi?tg. .a : ‘ 1 eaL: : 3 :a : s --;
Jan a Y 13, 1983, as .re11 as e a:a Le”eL and pM easure r. S
JanuarY 12, are su _a ztd Lfl ta Le I.
e11s ZN—I. N—3, EN—5, and N—6 were sa .ed wL: cu: a : :a:3
r b1e S . Mowever, r itOr _ n .re11s —2 and —4 req .red rec va:Y ;e::c s
approxio.a lY 1. hoer and 3 hours, respectivelY 1 before a cc p1ete one— a1.
sample could be co11eced The on—site artesian well was also sanpied dur g : i..
suzvel with one—ga1L° saples being collected at depths of 5 feet and .90 feet
using a Kaertr sapler. sore detailed disc,. sSiOn of the second san;ling
survey is provided in Appendix III along with the ground-water sanplirt; data
sheets which s ariZe the sa. pling of each onitorirLg well.
-------
Al: toug .ir:her veS? . ati0rt is necnssary t ter ..= :1 a::_.a
rss al; a .n the und at beteath the W. . Crace :
a a .labLe to date do no: show a concentration dis i u :io :u : tc_—
re that gross alp a levels in excess of the pr ry d:.n in watar s:a a:
.5. pCi/li:ar) were igratiztg beyond the boundaries of the fac.liy. - e r
Levels of gross alpha have been detected at locations where they vculd ‘:e a —
pec:ed with decreasing levels being found vtth increased distance fron : e
vasce dIsposal sites. low gross aloha levelsdetected in monitoring veils
N—l, EN—3, and EN—4 located ar the si.te boundarIes reveal gross altha 1a:els
below 15 oCi±il r at these Locations. 1 owever, it shatLid be noted tha:
erogeneouS nature of the uxtderlvin2 2eOlogic materials as well as the i. :er—
: aintie . sscciated with the exact Locations of waste materials cart result in a
highly variable area and vertica.L waste migration pattern.
— I
The gr und—vater level measurements made to date from the on—site nen .::r: g
wells reveal a highly variable ground—water surface beneath the si.ce ( gu:a ).
This is due to the eterogeneOu5 nature of the underlying deposits as as
the presence of the waste disposal. areas. As expected, the higher gr a r
levels are present to the east in th. area of actual waste disposal : e
aoparenr hydraulic gradient being toward the vest. The considerably h . a:
;:cund—’ a:er levels measured in monitoring wells EN—S and EN—6 are most
du* to the presence of waste materials and generally dIstributed nature of :e—
;esits in that area as a result of waste disposal activities. The cc s- ’
1 C j.r ground—water elevation observed in well EN—] when copared to weils E -2,
3, and EN—4 indicates the variability in th. underlying geologic de cs .:S
1t4 their hydrau.lic characterisUcs.
endations
Based upon the united available data base pertaining to geOlO ’.. a-:
-------
f a: .on generated to date du:- g : e f .eld ves a
as part of : .s p:eli. a ’ asseSS e progran is 1in .:ed to : te ar.alyt::al
results of the first series of sa:;les collected d r & the : al e:e
1982 surveY and water level :easureents obtained dur ’.g both tre e:a .ze: 3E2
and the 2anuary 1983 surveyS. The analytical results for the ecet:et
and JanuarY 1983 sampling surveys are provided in tables 2 and 3, respec: .’elY
vith the water level measurenentS from the on—site wells being s .ar d
ab1e 4. Analytical resultS for the .Sanuarf 1983 sanpl.ing survey are no:
available fron the EnvirCn ental Science & Engineeri 4 Laboraor7.
The distribution of gross a.lpha levels detected in the cvo
surveys shows higher Levels in the areas of kna .rn waste disposal s.tes (we .3
C—5 and N—6) with decreasing levels being detected with increased d .s:an:e
frc these known disposa.t sites. Gross alpha levels at wells E —L and -:.
located near the propertY boundaries showed such lower gross 4pha leve.3
than detected in the area of the waste disposal sites.
-------
:A3:. L
:A:Z —r. ;
J.a. CU C — ?C. t N PLAINS, .J.
•;L er Liva!. f:
C
.‘e11 ____ t/t2/83 VL3/
EN—L 5.5 5.38’ 5.84’
6.0 1.15’ 3.30’
EN—3 3.3 0.80’ 2.64’
EN—4 5.0 5.17’ 14.00’
5.3. 4.37’ 4.73’
3.0 4.90’
Ar esLan 5.0 4.13’
*pE paper utilized to obtain field pH readings.
-------
I
:A3LZ 2
GRCSS AL? t :.A .E t .’L S FOR cRc N:- A:zR s tP 3
c’_iC E xR: ;C E 2E i :
wa. GRACE FAcILLrI, pO TON ?:.. NS
Grcss Ai; ta
ci/i
E 1—1 8.0 7+ 2
1—2 6.9 2
6.8 2
11.5 0+ 2
8.0 3+ 2
2—3 6.8 2 2
EN3—L 6.4 2
3—2 7.0 6+ 3
7.0 2 2
4—L 7.3 5+ 2
7.3 3+ 2
4—3 7.3 9 2
4.6 30+10
E 5—2 5.7 90 + 20
E215—3 6.5 40+10
£N6—1 300 .30
E 46—2 300 30
Deep Jell
Surface 9 + 2
Deep ‘Jell
3o to (190’) 5 + z
Dee tell
42 (190’) 11 + 2
• paper uilized cbcai fieL4 pH readingS.
-------
Wayne Interim Storage FacilitylW.R. Grace Mining Waste NPL Site Summary Report
Reference 7
Excerpts from Radiological Survey or the W.R. Grace Property, Wayne, New Jersey;
Prepared for the U.S. Regulatory Commission by Radiological Site Assessment Program,
Oak Ridge Associated Universities; January 1983
-------
RJID OLOGICAL. SURvE j
0? ThE
W.R. G?J CE ?R0P RY
WAYNE, NEW JERSEY
Prepared for
D .vLsjon of Fuel. Cycle aed Mater al Safety
U.S. Nuclear Regulatory Co .ssio
P. V. Frame
Project Staff
.7. D. Berger
R. D. Cc dta
C. R. Volt:
.J. B. Frazier
8. C. Gentry
A. .7. Liu
A. M. Pi,tt
T. .7. Sovell.
C. F. Weaver
T. S. Yoo
Prepared by
Radiological Site Assesa e t Progr
Manpower Education, Research, and Training Diin.sion
Oak RLdge Associated Univera .t ice
— Oak RLdge, Tennessee 37830
FINAL REPORT
January 1983
This report is based on work performed u nder Interagency Agreene t E
No. 40—770—80, t C Fin. No. £—9093 between the U.S. Nuclear Regulatory
Comission and the U.S. Department of Ea.r&y. Oak R dge Assoc.ated
Universities performs complementary work under contract n er
DE—ACO5—760R00033 w .th the U.S. Department of Energy.
-------
AZLE Q CON2ENTS
P a z
Li.st o F es
L .st of Tables.
I: r3duct .Ofl
SLte Descr .pt on
Survey Procedures
Results
DLscussion
$iary
References
Appendices
AppeDd .X A: Glossary of Ter a
Appendix I: thori and Uranii Decay Series
Appendix C: Ground—PeTtetr ifl& Radar Survey of
the W.ft. Grace Site, Wayne, New Jersey
Major A a1ytical Equipment
AftalytiCil Procedux e$
1
2
5
10
18
21
57
AppendiX D:
Appendix E:
7
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TABLE 3
PADIOHIJCLIDK CONCENTRATIONS iN ON—SiTE
iOI $OLE SOIL SAMPLES
S.. I.
L.c.1 10u
D.$h
(..tui)
Tb —3)2
I.dIo.iicIld. C..c..*,.t$0 ( 1tI )
(0.—hI) Th—22S I -7 2 1 1—2)1
II $i.gI•c• 4.31 • 0.39k 4.22 • 0.41 1.20 • 0.13 4.11
0.3 1.11 ± 0.34 I I I 0.14 0.12 • 0.I
1. 13 S.D 5.13 1.09 ± 0.2) 0.1 1 • 0.11 (2.3)
•I $ud .s. 3.4$ ± 0.43 3.34 0.5$ 1.34 0.31 (6.31
0.3 1.14 ± 0.31 0.96 0.23 0.14 • 0.16 (2.3,
1.0 S .D j 0.21 0.93 j 0.24 0.10 0.11 < I I I
S I • t1 .C . ± 0.73 4. 7 0.43 3.19 • 0.40 (3.13
0.3 1.44 0.3$ - 1.3% ± 0.2 1.01 ± 0.30 1.49 0.32
0.13 1.05 j 0.21 1.03 ± 0.1) 0.44 ± 0.11 (3.49
$4 Surisci ).43j 0.61 3.Plj 0.37 I.3O 0.34 (4.7)
0.3 0,, ± 0.14 1.10 j 0.21 0.12 ± 0.11 (2.11
$3 Ivr(ses 4.19 0.46 4.40 j 0.3) $) • 0.31 1.34 ± 0.31
5.3 1.3$ j 0.12 2.01 j 0.32 1.14 ± 0.24 (1.14
56 Sense. 1.47 ± 0.30 1.7) ± 0.31 0.SS • 0.20 (2.51
0.3 1.4) t 0.31 1.43 ± 0.21 1.33 t 0.22 (2.34
I.. 1.32 j 0.31 1.3$ . 0.31 1.0) • 0.20 43.51
S i Iurlse• -i .Ilj 0.49 1.10±. 0.3) 0.19 . 0.33 (1.9)
0.3 o.S ± 0.33 0.01 j 0.31 0.69 • 0.16 (2.9)
0.14 ± 0.21 0. I ± 0.21 0.39 ± 0.14 (2.11
$5 Sw,f.e. 1.47 ± 0.3$ 1.41 ± 0.29 1.12 ± 0.34 (3.11
0.3 1.62 j 0.4) l. ± 0.33 I I) t 0.2$ (2.93
1.0 1.3) j 0.31 1.43 ± 0.33 1.12 ± 0.24 ‘3.3$
$9 Sugisci 1.9$ ± 0.3) I.3 ± 0.3$ 0.65 • 0.21 (3.21
0.3 2.35 ± 0.64 3.6) ± 0.33 0.93 ± 0.23 (3.3)
1.0 4.9 1 ± 0.3$ 4.92 ± 0.1$ 0.09 0.36 3.34 0.52
110 Surlici 3 .1 ± I .) 30.0 ± 1.0 2.11 • 0.54 <6.95
0.5 31.9 ± 1.2 23.3 ± 0.9 1.15 • 0.)6 11.6 0.3
3.6 l.ft • 0.34 1.34 ± 0.30 0.19 ± 0.20 0.6
• 1 1 C BurlicS 136 ± pIp j 3 • .4 • 1.4 39.3 • 0.)
0.5 196 . 3 I II ± 3 • 1.26 33.0 • 0.9
0.15 I 3 II3 ± 3 1.0$ ± 1.1, 5)0
-------
TABLE 3 cont.
RADIOIWCLIDE CONCENTRATIONS IN ON-SITE
OREMOLE SOIL SAMPLES
11.ps
L.casIos
Isd onuct1ds
(...u.) Th—33 1 is—Ill) Th- 12S
Coac.otvsllons
(pCLl 1 )
1.—lu U 2 )1
UI , S ic1ac . 56.0 ± 1.6 45.5 ± I .) 3.60 ± 0.61 11.1 ± 0.1
0.1 *6.6 ± 0.0 0.64 ± 0.60 3.39 ± 0.05 I I.’. ± 0.6
I II S r3.c• $3.6 • 0.0 $2.1 OS 1.52 0.4 U.S • 0.1
0.3 4.4$ j 0.01 4.15 0.64 1.34 0.31 (4.11
1.0 0.60 0.5% 4.04 0.52 0. I j 0.2’,
3.0 1.20 0.30 1.41 0.21 0.60 ± 0.31 (2.63
I I’. SuiI.c. *0.0 j 1.0 11.2 j 0.6 3.79 0.4* 9.19 ± 0.55
0.0 6.40 j 6.55 5.11 . 0.40 1.13 0.34 4.11 ± 0.5*
1.0 6.8 . j 0.10 5.16 0.40 3.59 0.34 (4.0’.
Ifi Sutlecs IflO j 10 ‘4000 ± 30 3U • I I 1,10 1
0.0 102 12 202 ±11 4fl ±1* 559
. 6 4600 j 30 5100 00 163 • 9 ‘001 ± I
U Sr1.ca 1150 10 $130 10 4930 . I 105 I
0.0 065 S 4)1 9 320 ±6 16$ 11
1.0 166 j 7 192 S *11 • 4 121 ± I
all $.vIoe. I II j 0.60 0.02 , 0.51 1.41 • 0.32 41 0 ± 0.1
0.5 33.4 1.6 30.5 ! I I *3.0 0.1 30.2 0.6
1.0 50.6 ± 2.1 1 5.7 j 3.5 0.03± 0.19 40.1 ± 0.5
II I $uil .cs 31.0 1.1 *0.0 ± 0.0 4.41 0.01 40.6 ± 0.1
0.0 7.0 j 1.0 *0.1 ± 0.0 6.13 0.40 36.3 ± 0.1
1.0 31.0 j 1.3 33.5 , 1.0 4.33 • 0.01 16.4 ± 0.1
RIO 1i il.c. 13.1 ± 0.50 10.6 ± 0.1 *5) 0.11 (4.71
0.5 ( 59 (0.10 (1.17 (42.9
1.0 9.37 ± 0.52 10.0 ± 0.1 1.69 • 0.39 *0.0 ± 0.0
iS 1.4$ j 0.41 3.2* 0.35 1.02 • 0.22 3.41 0.50,
3.0 1.31 ± 0.19 1.3$ 0,?) 0.01 • 0.29 (1.60
3.0 1.01 j. 0.20 3.06 ± - 0.31 0.01 0.21 (3.19
4.1 1.9 j 1.0 11.1 ± 0.9 1.01 • 0.61 4.1) 0.00
510 $.iI.e. *95 • I l OS 1 2 0.51 0.97 (*3.1
0.5 990 II 931 ± I I.’. • 4.’. ( 6 1.1
I. ) 541 • 0 II ) ! S *6.2 ± 3.1 7(0 AS
13) $uil.c. 30’. 2 (3 *4.0 • 2.0 31.6 • 0.0
0.) 401 ± 1 316 ! 6 *4.6 1
I. 7 I I I ± 9 3 0 5 ± 5 (l. 6 <09.)
-------
TAILE 3, cont.
R.ADIOPWCLIDE I HICENTRATJONS IN OH-SITE
IOk* IOLE SOIL SAMPLES
lispla
L.c.eI.a
$.$h $adlo.uclld.
(situ .) Th—2)3 (I .—33$) lb—Ill
C..c.s ratIoa jpC&/i)
ta— l I l U- I ).
Ifl Siarlac. 315 I 341 • S $54 ± 4.1 (5 1. 5
6.3 .7510 ± SI 2040 40 tfll O 30 IN ± I
.73 larlac. $04 ± 4 III ± 3 40.3 2.0 (II . )
6.5 61.1 3. 3.1 15.3 1.3 3I. ± (.4 ‘ (5.3
II 115 ± 5 II I ± IS ± 3 (24.4
$Jj latIst. 443 ± I 505 j. 6 23) ± S <49. )
0.5 43• ± 4 436 j4 300 • 3 36.5 .0.7
1.0 25) ± 4 434 ± 4 J .I ± 2.1 451 ± 0.6
$75 lutlaci 41.7 ± 1.4 41.6 ± 1.1 1.14 0.)) ‘1.01
0.3 31.1 (.3 32.0 (.0 5.51 ± 0.4) ‘4.54
I.e l. 3 t 0.41 3.04 ± 0.32 1.11 • 0.33 (2.69
3.S I.$lj 0.)) 1.3$ ± 0.31 0.1$ . 0.20 (3.1)
$24 li.rIac . 14.6 ± 0.0 (5.0 ± 0.7 1.31 ± 0.51 0.14 0.53
0.3 Ii ± (.6 11.1 j 0.0 1.74 • 0.41 (5.04
II 6200 S0O 1440 jS00 101 3.146 106
Sfl l rl.e. 341 j. . 4 31.1 j I.? )4 • 0.60
0.4 3(50 ± 20 3110 20 555 14 44.4 t 1.1
II I lucIac. 71.4 ± (.7 II. ? ± (.0 4.1) 0.36 (6.53
0. 5 p.14 ± 0.1* 10.) ± 0.4 1.31 0.45 2.61 ± 0.4$
(.0 0.51 ± 0.32 0.14 0.11 0.59 t 0.14 (1.34
(.3 0.63 ± 0.35 0.54 ± 0.75 0.11 0.1$ (2.77
3.1 4.34 ± 0.34 4.14 j 0.10 I.? ) j 0.31 (4.1$
$2 3uvEac 114 ± 3 (50 3. 3 10.3 • I.)
0.1 390 ± 3 541 4 41.4 3. 3.0 44.2 t 0.6
5.0 ( (50 10 600 1 14.5 ± 4.6 19.0 I.e
1.5 i (4 1 00 ± 100 (5100 • 400 (430 300 110 I
R luctai 46.1 3. 1.5 44.4 • I. ) 5•)3 0.42 (7.03
(.0 30*0 ± 30 3360 ± 10 34) • I I 33.1 • 1.0
I I I luclacs 34.6 j 1.1 30.0 . (.0 3.43 • 0.31 s se
0.3 10.1 3. 0.9 (3.3 0.1 I.6 • 0.33
1,0 4.02 j 0.41 5.95 0.33 0.90 • 0.76
4.6 35.? 3. (.4 31.0 I I 3.74 0.45 €6.41
-------
TAILE 3 • cont.
RADIONIJCLII)E CONCENTRATIONS IN ON-SITE
BORI IOLE SOIL SAHPLES
Sa.pIs
Lotall..
flpth IadIOeucItd!
(.s$up) TI—233 (la—231) Th—23 1
Ccmc.a1r.t2.. j ciIi)
0.236 U-3)S
Ifl SuvIat. 33.1 ± . 0 36.4 • 0. 3.19 • 0.40 <3.62
0.) 309 ± 3 334 j 3 23.9 .. 2.3 36.3 ± 0.1
I )) lurlacs 47.4 j 2.6 4 .3 • 1.4 0.43 .. 0.76 <0.03
0.3 26.7 2.1 24.) j 0.9 3.03 ± 0.22 < 3. 1)
3.4 lU ± •.43 3.60 ± 0.31 1.19 0.31 (3.37
Ili IurIac* UI ± 3 210 ± 3 36.3 2.6 (21.9
0.) .1 j 2.0 31.2 ± I.) 1.41 • 0.1 ( .l9
0.2 62.0 ± II 61.3 ± 2.6 22.3 0.0
1)2 Iu,(.cs I.SS ± 0.34 2.40 ± 0.30 o.e • 0.22 (1.33
0.) 2.03 0)1 2.11 ± 0.32 0.02 0.2$ (3.37
2.0 2.02 ± 0.42 3.23 j 0.7 0.03 • 0.22 (2.64
3.0 2.06 ± 0.30 2.22 j 0.2) 0.10 0.11 (2.16
3.0 .30 ± 0.30 2.30 ± 0.24 0.11 • 0.11 (2.29
6.1 2.27 ± 0.36 2.20 j 0.10 0.96 ± 0.27 (3.35
Ij Our(.c. 30.0 2.3 3 .S . 1.1 3.)) • 0.5) <6.43
0. 2 1.04 0.32 1.22 ± 0.32 0.76 • 0.12 (2.19
1.0 2.10 ± 0.3 1.23 ± 0.23 0.62 ± 0.21 (2.12
3.0 1.32 ± 0.30 2.26 ± 0.24 0.60 • 0.26 (3.20
2.2 1.51 i. 6.12 1.22 ± 0.72 0.74 ± 0.11 ‘316
Surl.c. $24 ± I • II) ± 2 Il.) • 0.? II.? • 0.6
0.3 60.4 ± I.) 51.6 ± 1.1 30.2 0.? 23.0 ± OJ
03$ Iuel.c. I. I ± 0.33 . 2.62 ± 0.34 1.14 • 0.29 (2.60
2.0 2.33 j 0.29 2.4$ ± 0.24 0.04 • 0.29 (0.20 s
$39 lenses 3.03 • 0.31 1.01 • 0.11 0.02 • 0.20 (2.16
2.0 2.20 ± 0.30 3.32 . 0.30 0.92 • 0.7! ‘3.90
040 Surlecs 3.12 0.43 3.2) 0.37 .19 0.23
0.5 0.00 0.36 1.0$ 0.29 I I 6$ 0.20 (3.66
1.0 0.40 0.32 0.51 ± 0.74 0.33 0.12
24$ 5UI( CS 2.7) j 0.40 3.34 0.12 - 0.39 . 0.10 (3.43
0.5 1.0) ! 0.35 I.IS ! 0.35 0.61 • 0.1? 41.09
I.e o.oi 0.23 - 0.1$ .!. 0.1) 0.17 • 0.11
-------
TAOLE 3, cont.
RADIONUCLIDE HCEPITRA?IONS 1W ON-SiTE
8O8 1OLE SOIL SAMPLES
Sa.p le
Locat ton
Depth
(.eters)
Radionuclide
Concentrationo (pC i ! g)
Th—232
(l.—128)
Th—228
Ra—226
U—238
142
Surface
2.34 ±
0.42
4.22 +
0.37
0.66 +
0.20
<3.07
0.5
2.29 ±
0.35
3.91 ±
0.36
0.10 +
0.20
<3.19
1.0
0.66 ±
0.23
2.51 ±
0.30
0.50 •
0.14
<2.93
1.5
0.76 ±
0.25
2.31 •
0.27
0.40 ±
0.14
<2.09
3.3
2.26 j
0.35
5.66 j
0.40
0.60 j
0.22
<2.63
843
Surf sce
12.9 s
0.8
17.5 ±
0.8
1.t 4 ,
0,36
<5.23
0.5
0.82
0.25
3.22 ±
0.32
0.58 ±
0.18
<2.47
1.0
1.07 ±
0.30
2.55 ±
0.29
0.58 ±
0.20
<2.60
3.6
7.04 j
0.58
8.43 ±
0.55
0.79 •
0.27
1.38 ± 0.41
* Refer to Figure 10.
b Error I. 2 based on counting statistics only.
Underlined sa.ple locations are those identified during
the walkover survey to bsve elevated ezposure rates.
-------
TABLE 4
RADIOIWCLIDE (XDICENTRAT IONS IN SEDIP 1f1 SAMPLES
Th—232 (Ia—228)
Radionucl ide Concentrations (pCi ! g)
Dl
1)2
I))
1)4
1)5
1)6
1 )7
fl8
1)9
NO
1)11
1)12
1)13
1)14
1) 15
Drainage Stream
Drainage Stream
Drainage Stream
Drainage Stream
Drainage Tile
Drainage Tile
Drainage Tile
Storm Sever
Storm Sewer
Storm Sever
Storm Sever
Storm Sever
Storm Sever
Storm Sever
Storm Sever
5.28 ± 0 • 72 b
2.29 ± 0.
4.72 ± 0.64
2.03 ± 0.32
5.12 ± 0.46
9.17 ± 0.78
18.0 ± 1.0
16.8 ± 1.0
23.4 ± 1.0
43.2 ± 1.5
24.7 ± 1.3
383 ±
78.2 ± 1.9
951 ±6
10.9 ± 0.8
5.04 ± 0.56
1.77 ± 0.43
2.75 ± 0.43
1.73 . 0.31
4.70 ± 0.39
9.78 ± 0.59
19.1 ± 0.9
17.5 ± 0.8
25.2 ± 0.9
38.7 ± 1.2
24,4 ± 1.0
327 ±3
70.0 ± 1.6
866 ±s
9.57 ± 0.63
1.70 ± 0.35
0.51 • 0.31
0.76 ± 0.39
0.63 ± 0.20
1.31 • 0.24
1.77 • 0.32
3.04 ± 0.47
3.65 ± 0.48
3.89 ± 0.47
4.12 0.61
3.67 ± 0.51
30.2 ± 1.8
5.37 1 0.77
101 ±
1.49 • 0.33
(4.46
<4.05
<3.84
(3.22
(4.I4
(6. i4
6.03 0.51
13.6 0.6
19.9 ! 0.7
(6.36
24.5 0.8
12.7 • 0.6
46.9 • 1.0
(4.26
Refer to Figure 12. I
Error is 2n based on counting statistics only.
Sample
oC s( iona
Descript ion
Th—2 28
Na —226
-------
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