- -

STATE OF CALIFORNIA-HEALTH A N D WELFARE AGENCY GEORGE DEUKMUIAN, Governor

DEPARTMENT OF HEALTH SERVICES 7141744 P STREET SACRAMENTO. CA 95814

Preliminary Assessment Summary

Bethlehem Steel Corporation Pinole Pt. 5000 Giant Road Richmond, CA 94804 EPA# CAT080012354

March 1984

Preparer's name: Carol Sim Toxic Substances Control Division

History and Problem:

Bethlehem Steel Corporation operated a structural steel. galvanizing plant at Point Pinole from 1963 to 1975. Wastes generated from a de-galvanizing process were discharged into a 7.25 acre industrial waste pond. Wastes were acidic, contained high concentrations of zinc.and.slightly..elevated concentrations of lead and chromium.. Discharge terminated when the facility closed.. In 1975, Bethlehem Steel began working with the Regional Water Quality Control Board (RWQCB) and the Department of Health Servised (DHS), to develop an appropriate closure plan for the acid pond. Pinole Point Properties, Inc. purchased the facility in 1978 and took over the development of closure and remedial action plans.. Woodward-Clyde Consultants were contracted to conduct a comprehensive site investigation and propose remedial action.. Two reports, "Point Pinole Waste Pond: Site Investigation and Remedial Assessment", November 1983 and a final report addendum, Feburary 1984 detailed plans for neutralization and disposal of ponded water, sludge disposal and encapsulation of contaminated soil. The plan has been approved by DHS and is pending approval by RWQCB. Implementation of the cleanup should begin in late March or early April 1984..

Recommendation:

The site is currently ranked 66 on the California Superfund list. Cleanup is scheduled to begin within one month. No further action is recommended.

PRELIMINARY ASSESSMENT Region 9

Carol Sim P r e p a r e r ' s Name-. D a t e 3/22/84 - - - - 7------ 7- 7

RRIS turnaround hD Number *080""AT10N ERRIS turnaround -.--

____-__- - - - - ERRIS turnaround

Contra Costa document ------ ? 2. S i t e N a m e ' d o c e n t 1 ~ e t h - d - i

Pinole Point Proper t ies , I n c . 5 . Owner ( A d d r e s s & EPA form 3510-3

Laura Wais t e l e p h o n e no. ) 700 Larkspur Landing Ci rc le , s u i t Larkswur. CA 94939

-

Pinole Point Proper t ies . Inc. &

Laura Wais t e l e p h o n e no. )

Larkspur, CA 94939 (415) 461-3912

EPA form 2070-13 Inac t ive f a c j l i t v E; d i s p a s a l -- 9. S o u r c e A c t l v l t y

--..--- -7 --- EPA form 8900-1 & 1963-1975

Y e a r s o f O p e r a t i o n l e t t e r t o RTdQCB from B e m m - 5 c 1 - m -

3 . S i t e L o c a t i o n

I 1 1 . F a c i l i t y Type IT Report I 1) 2 unlined surface impoundments # F9-8109,-02 (a) ac id pond (7.25 ac res )

ERRIS turnaround 5000 Giant Road

I

C (b) waste s a t e r pond ( 1 7 ac res

document Richmond2 CA 94804

12. waste Type and IT Report Waste p ick le l iquor and wash water ~ e s c r i p t i o n DD # F9-8109-02 from a 54" qalvanizing l i n e .

2/7/81 Mineral impur i t ies include Fe, Zn, Cr, Pb

SOURCE INFORMATION

19. Observed Release

20. Depth to Aquifer

21. Net Precipitation

Net seas. rainfall ! Evaporation +-t- --I I

permeability of unsaturated Zone

~ ~ ~ . . .~~ -- - Physical State

125. Toxicity

.L I-- -. C- - i ( 2 6 . persistence

L- 1--4- I I 127. Waste Quantity

L-- I ---- Ground Water Use

I I - -I---. 29. stance to Well

!

I 30. population Served (by Ground Water)

i

I REGION: 0 9 U. S. ENVIRONMENTAL PROTECTION AGENCY OFFICE OF EMERGEllCY AND REMEDIAL RESPONSE

DATA BASE UPDATED 8 3 / 0 9 / 0 1 T . 1 - ERRIS TURNAROUND DOCUMENT

PAGE: 1 4 7 RUN DATE: 0 3 / 0 9 / 0 1 RUN TIME: 20:31:02

S I T E DATA EPA I D NO.: CAT080012354 SHEET 0 1 *********

(ACTION r *-* - FOR DATA ENTRY USE ONLY)

SF I D : *-* *-* *-* S I T E NAME: BETHLEHEM STEEL CORP PINOLE PT SOURCE: R SOURCE COUNTS (NOT UPDATABLE)

w-+ u-x STREET: 5 0 0 0 GIANT RD CONG. OIST. i 0 7 i4OTIS: 0

NATL PRIORITY: N CITY: RICHMOND ST: CA Z I P : 94804-- STS: 0

HRS: *- - X CNTY NAME: CONTRA COSTA CNTY CODE: 0 0 1 HND115: 0

DATE (YY/MMI: *-I-* LATITUDE: 38/00/00.0 LONGITUDE: 122/20/25.0 COIIPDSITE: 0

LCSPONSE TERMINATION [CHECK ONE IF APPLICABLE): PENDING *-* NO FURTHER ACTION *-* OTHER: o

ENFORCEMENT DISPOSIT ION (CHECK ANY THAT APPLY): NO VIABLE RESPONSIBLE PARTY *-* VOLUNTARY RESPONSE *-* ENFORCED RESPONSE *-* COST RECOVERY *-*

RESPONSE *-* ( X I S I T E DISCOVERY ( S D ) EVENTS

*-* (XI PRELIMINARY ASSESSMENT (PA)

*-* ( X I S I T E INVESTIGATION ( S I ) *-/-* 8 1 / 1 0 *-* *-* *-* REMEDIAL ACTION I R D ) *-/-* *-'-* I-* 1(-x *-* *-* *-* *-* REMOVAL ACTION I R V ) *-'-* *-C* *-*

I

ENFORCE *-* ENFORCEMENT INVESTIGATION ( E I ) El-* *-/-* * - X-x EVENTS

*-* ADMINISTRATIVE ORDER ( A O t *-/-* *-C* *-I x-x

JUDICIAL ACTION (JAB *-* ' t i -* *-/-* *-* *-*

Final Heport Addendum

Point Pinole Waste Pond: Site Investigation and Remedial Assessment

Prepared for

East Bay Regional Park District 11500 Skyline Boulevard

Oakland, CA 94619

February 28, 1984

Woodward-Clyde Consultants One Walnut Creek Center

100 Pringle Avenue, Walnut Creek, CA 94596

One Walnut Creek Centt 100 Pmole Avenue Walnut treek. CA 94596 41 5~945-3000

WoodwardGlyde Consultants

February 28, 1984 90040B

East Bay Regional Park District 11500 Skyline Boulevard Oakland, CA 94619

Attention: Mr. Thomas H. Lindenmeyer, Environmental Coordinator Mr. Ken Burger, Waste Management/Water Quality Specialists

Re: Point Pinole Waste Pond, Site Investigation and Remedial Assessment

Gentlemen:

Attached is an addendum to Woodward-Clyde Consultants' Final Report of November 7, 1983 on the subject project. This addendum addresses the requirements of the State Department of Health Services and Regional Water Quality Control Board that were raised during our meeting with the agencies on January 23, 1983 and subsequently outlined by the RWQCB's letter of February 1, 1984.

Four areas have been raised as requiring supplemental investigations or modifications:

1. Additional considerations for sludge handling during treatment of pond fluid.

2 . Further investigation of the elevated zinc concentration in Well No. 2, located near the northeast corner of the waste pond.

3 . Design changes for the encapsulation cover design based on EPA guidelines.

4. Further testing of zinc in surface soils of marsh area to the north of the waste pond.

The results of our work in each of these topics is provided under separate headers in the attached report addendum.

Woodward-Clyde Consultants appreciates this opportunity to assist the EBRPD in this matter, and we look forward to future opportunities to provide our services.

Sincerely,

David R. Gaboury, P.E. Vice President Project Manager

JDS:DRB/aw Consulting Eng~neers Geologists and Env~ronrnental Scentsts

Off!ces In Other Prncpal Clt!es

TREATMENT SLUDGE HANDLING

During the January 23, 1984, review meeting, DOHS and RWQCB indicated

that the overall plan for treatment of the pond fluid was acceptable.

There was, however, a minor question raised regarding sludge handling

during the treatment operations. While specific details of the treatment

operations in general and sludge handling in particular are best addressed

as part of the final design, additional information in response to the

agencies' questions are provided below. This information supplements

Section 2 of the November report and in particular pages 2-17 through

2-20.

Woodward-Clyde in the November 1983 report, estimated that about O..1

gallons of sludge will be produced for each gallon of pond water that is

treated. Based on the planned design treatment capacity of 100,000

gallons per day, about 10,000 gallons (50 cubic yards) of sludge will thus

be produced daily by the rotary vacuum filter. It is recommended that

after filtration, the solids be conveyed directly to a truck for offsite

reclamation/reuse. A belt or screw type conveyor system will be used to

continuously transport the sludge solids from the scraper side of the

rotary vacuum filter to waiting trucks. The cost of a conveyor for sludge

handling is estimated to be $7,000-,$10,000.

Upon completion of the loading of a truck, the rotary vacuum filter

will be shut down until the next truck is positioned and loading resumed.

Several truckloads of sludge will be produced daily, and a contract should

be arranged with a licensed waste transporter to schedule the sludge

removal in a continuous manner. However, if during operations another

truck is not immediately available for loading, the production of solids

could easily be halted until the next truck arrived and was moved into the

loading position.

On-site sludge storage facilities are not recommended. The zinc

carbonate sludge will be approximately 35 percent solids with little, if

any, free water. This type of sludge is best disposed of with minimal

handling.

ELEVATED ZINC CONCENTRATION IN WELL NO. 2

Groundwater samples collected in Well No. 2 showed zinc concentra-

tions considerably higher than the remaining six wells around the ;pond.

For all the remaining wells, zinc concentrations in the groundwater were

below the current drinking water standard. As stated in the November

report, the boring log and field observations for Well No. 2 suggest that

a local peat layer may provide a pathway for zinc migration from the waste

pond. The agencies have required that further investigations be conducted

to more fully define the conditions of Well No. 2.

The information and discussion below supplements Chapter 3 of the

November report and in particular page 3-10 and 3-11.

As shown in Figure 1, two additional wells were installed in the area

of Well No. 2. These are EB-18 at the northeast corner of the pond and

EB-19, just to the east of Well No. 2. Prior to installation of EB,-18,

Well No. 1 provided the only information of groundwater conditions along

the east side of the pond.. In the timeframe of the additional investiga-

tions, it was not feasible to install a well directly to the north of Well

No. 2, in the Southern Pacific Railroad right-of-way.

The wells were installed to a depth of about 30 feet, with the bottom

10 feet screened for groundwater monitoring. The wells were developed and

groundwater samples were taken and tested for zinc concentrations, pH, and

conductivity. Soil samples of the well borings were also taken, but not

tested at this time. Well logs are provided as Attachment 1 to this

report addendum.

Table 1 lists the zinc concentration in groundwater samples from the

seven previously installed wells and from EB-18 and EB-19. Both new wells

show zinc levels that are consistent with the remaining wells (except No.

2) and are well below the drinking water standard of 5 mg/l.

Although there are valid concerns for the elevated zinc levels in

Well No. 2, this situation should not be unexpected. In a waste pond such

as this, with minimal engineering for containment, there will very likely

0 200 400 Feet -

EXPLANATION (Approximate)

6 Monitoring well installed 8/83

8 Monitoring wells installed 5/82 Soil boring drilled 8/83

Soil boring drilled 12/80 0 Surface roil sample locations 0 Monitoring wells installed 2/84

(not surveyed) Project No

900408 Point Pinole Waste Pond

~.

SITE MAP WITH SOIL BORING

-Clyde- AND MONITORING WELL LOCATIONS F i g u r e 1

TABLE 1

ZINC CONCENTRATION RESULTS FOR GROUNDWATER SAWLES

Well No.

Specific Conductance -

Zinc l J 2 ! L 3

be pockets of groundwater adjacent to the pond with high zinc concen-

trations. However, based on the nine monitoring wells around the pond,

there has been minimal migration of zinc into the groundwater. Regarding

Well No. 2, the data (provided by EB-'7, EB-18, and EB-19, as wel1,as field

observation during the development of Well No. 2) indicate that the

elevated zinc in the groundwater around Well No.2 certainly originated

from the waste pond and is clearly isolated to an area immediately adja-

cent to the pond.

Treatment of the pond fluids and encapsulation of the contaminated

soil will remove or isolate an overwhelming portion of the zinc at the

site.. Additional specific mitigation measures for the elevated zinc in

the groundwater around Well No. 2 are not recommended. There is no

evidence that this groundwater condition poses a threat to human health or

the environment, or that post-closure migration will cause such a threat.

Further pumping of Well No. 2 could, in fact, exacerbate the problem, and

it is recommended that this well be sealed as part of the site closure.

MODIFICATION OF ENCAPSULATION COVER DESIGN

At the January 23, 1984, review meeting, DOHS indicated that the

encapsulation concept was acceptable but that a slight modification in the

cover. design was required. Woodward-Clyde was provided a copy of the

cover design section of an EPA document to use as guidance on the design

changes. These modifications would replace the conceptual design provided

in Section 4.2 of the November report.

Basic Cover Design Changes

Figure 2 provides the conceptual encapsulation design, as modified

based on the EPA guidelines. Overlying the waste would first be a two

layer, low permeability bottom cover consisting of 24 inches of barrier

material and compacted fill (see schematic). The compacted fill will

support a middle drainage layer to intercept infiltration. The final

cover will consist of compacted fill material with a minimum 2 foot

IVEGETATION) SE RESTRICTED)

BARRIER MATERIAL

SURFACE RUNOFF DITCH

n NATURALGROUNDWATER

F I L L PLACED TO GROUNDWATER LEVEL ELEVATION I - ----- ------- PRESENT POND BOTTOM

r* (APPROXIMATE1

\\

~ l n u r e 2 ENCAPSULATION USING EPA

COVER CONCEPT WITHIN POND

Pro'ect No 900406 Point Pinole Waste Pond

Woodward-Clvde Consultants

thickness, followed by a vegetated top. Total cost of the encapsulation

with the cover redesign is estimated to be $ 2 . . 3 million, an increase of

As part of this conceptual design addendum, the sensitivity of costs

to various design parameters was also investigated. Substantial costs

savings are possible, if the thickness of the contaminated soil in the

encapsulation is increased from the 3 feet originally assumed to between 6 - and 10 feet. It is recommended that this design change be refined and - adopted in the final design. It is estimated that this would result in a

cost savings of $500,000, reducing the total encapsulation costs from $2.5

to $1.8 million.

Alternative Location of Encapsulation

Based on the same encapsulation design concept described above

(Figure Z ) , placement of the encapsulation in the ridge adjacent to the

west side of the waste pond was also investigated. The design concept is

shown in Figure 3. The plan would be to excavate materials from the west

ridge to just above the groundwater elevation. The encapsulation would

take place in the excavation starting with 5 feet of barrier material, the

contaminated soil, and finally the cover (see Figure 3). The final

elevation of the encapsulation would roughly conform to the present ridge

area. In the pond, compacted fuel would be used to bring the grade to

above the groundwater level, using material excavated from the ridge and

additional imported fill. The entire area of the present pond would be

regraded for adequate surface drainage which would ultimately be routed

directly through the railroad bed to the north or into the 60" storm drain

on the east side of the waste pond.

Placement of the encapsulation in the ridge area would result in

substantial cost savings. Total costs (based on 6-10 feet of contaminated

soil in the encapsulation) of this plan is estimated to be $1.4 million,

the savings resulting from use of om-site materials and reductions in fill

volumes.

DRAINAGE LAYER

PRESENT GROUND SURFAC:.+

/ %

-J

PROPOSED ENCAPSULATION

D APPROXIMATE GWL I N V ICINITY O F

G R O U N O W A T E R A N D I POND, 1983

\ GRADE FOR DRAINAGE I

EXCAVATE CONTAMINATED MATERIAL

Woodward-Clyde strongly recommends the ridge location be adopted for

encapsulation. In addition to large cost savings, this location will

avoid placement of the encapsulation over the bay muds in the waste pond

area. The bay muds in the area are currently of unknown thickness and

subject to substantial settlement if the encapsulation was placed in the

pond itself. Overall, avoidance of construction in the bay mud will

substantially reduce both construction and post-closure engineering

problems with the design. It is believed that long-term post-closure

leakage potential of the encapsulation will be significantly reduced by

locating the waste in the area of the current ridge to the west of the

waste pond.

ZINC IN SURFACE SOILS

Discussion was held during the January 23, 1984 , review meeting

regarding the significance and proper interpretation of the zinc levels in

the surface soil samples taken around the waste pond and the fresh water

pond, particularly in the marsh to the north of the ponds. RWQCB expres-

sed specific concerns for potential beneficial use impairment in the Bay

system due to migration of zinc from the marsh. In response to RWQCB's

request, the following further investigations have been performed:

o Extraction tests were performed for zinc in surface soils

of the marsh.

o Additional comparisons and interpretations were made, based on

available literature, regarding zinc levels in the marsh and

values measured at other relevant locations.

o The environmental fate of zinc as effecting beneficial uses

of the Bay system was investigated.

Each of these topics are discussed under separate headers below. The

information supplements Chapter 3 (pages 3-8, 9 , 10) of the November

report.

Extraction Tests

As requested by RWQCB, extraction tests were performed to assess the

mobility of the zinc in the soil. A single composite of the previously

collected samples to the north of the culvert draining the fresh water

pond (i.e., a composite of S-5, S-6, and S-7, see also Figure 1) was

tested. A CAM 48-hour extraction test was perfo~med on the composite and

a second extraction, designed to simulate natural rainfall/runoff condi-

tions which could cause migration of zinc, was performed using CAM pro-

cedures except with deionized water of pH 5.5 used as the extractant.

The extraction tests were performed by Brown and Caldwell and the

results (provided in Attachment 2) are as follows:

Sample: Composite of 5-5, S-6, S-7

Total Zinc: 870 mg/kg soil

Extractable, CAM: 780 mg/kg soil 4%

Extractable CAM (except_water-extractant): 3.5 mg/kg soil

The data indicate that zinc is quite extractable (i.e., 90 percent) using

the CAM test, but much less extractable i . . , less than % percent) using simulated rainfall/runoff conditions. The extractability results are

typical for zinc, given the testing procedures.

Comparison of Zinc Levels with Background

The concentrations of zinc in the seven samples of surface soil from

the marsh ranged from 70 to 820 mg/kg, with an average value of 364 mg/kg.

The observed zinc concentrations are higher than naturally occurring

levels; however, there is no evidence that the waste pond is a significant

source of the pollution. Two other potential sources of zinc were iden-

tified in the area -- (1) Garity Creek about 3/4 meters to the northeast of the pond, and (2) a sewage outfall approximately mile to the north-

east, which was operated as a primary treatment unit until taken out of

service in the mid 1960's. Both of these sources discharge fresh water

containing zinc, and are thus subject to metals precipitation upon mixing

with the Bay water. The data is not adequate to determine the relative

significance of these sources of zinc.

No information was found concerning the zinc content of sediment

immediately off Pt. Pinole or in comparable marsh areas. The closest

locations that have been investigated are Carquinez Strait to the north-

east and San Pablo Straits to the south. Liu and co-workers (1975)

reported zinc concentrations ranging from 107 to 156 mgfkg in sediment

samples from Carquinez Strait. The Corps of Engineers (1974) reported 201

mgfkg of zinc in a sediment sample collected in San Pablo Strait. In

addition, 1975 East Bay Municipal Utility District study of a sewerage

outfall just south of the Bay Bridge measured zinc levels in sediments at

six locations with concentrations ranging from 16 to 1060 mgfkg and an

average of approximately 200 mgfkg. To provide additional perspective,

typical street dirt in urban areas contains zinc concentrations of 300

mgfkg.

Based on the above data base, the zinc levels in the marsh samples

are of comparable variability, but are about 100 to 150 mgfkg higher

concentrations than the average Bay sediments.

Potential Biological Impact of Zinc in Marsh Sediment

Like other chemical substances, zinc must be absorbed into body

tissues to cause toxicity.. For absorption to occur in aquatic organisms,

zinc must be in a soluble form. Liu and coworkers (1975) have found that

benthic organisms can thrive in sediment with extremely high metal concen-

trations and hypothesized that the absence of effects is due to strong

sediment binding resulting in low aqueous solubility of the metals.

The extraction test performed on soil from the marsh using simulated

rain water revealed that zinc is not easily extracted by rainfallfrunoff.

Although the sediment contained 870 mgfkg of zinc, the extractable amount

was 3.5 mgfkg of soil which is equivalent to 0.35 mgfliter in the water.

Reported acute toxicity estimates (LC50 and EC50 values) for zinc in

marine organisms range from 0.166 mgfl for the hard shell clam (Mercanaria

mercenavia) to 8.3 mg/l for the mummichog (Fundulus heteroclitus). Acute

toxicity estimates for organisms that inhabit the Bay are shown in Table

2. . Acute toxicity estimates for some of the species are less than 0.35

mg/l, the amount estimated from the sediment; thus, for some Bay qrgan-

isms, exposure to interstitial water from the marsh could cause acute

effects. However, the occurrence of acute toxicity is unlikely due to the

fact that the water extraction test is probably a worse case for runoff

concentrations and considerable dilution of zinc will occur in the Bay..

Zinc concentrations capable of causing long-term exposure effects

(chronic toxicity) are considerably lower than those required for acute

effects. However, dilution will probably prevent such concentrations from

being achieved. Another factor which would mitigate acute a.~d particu-

larly chronic effects from occurring is the intermittent nature of

marsh-to-Bay transfer (assuming that major transfer is caused by rain-

fall/runoff). This would reduce the time of exposure of Bay organisms by

zinc.

Marine organisms can accumulate zinc to levels up to about 17,000

times water concentrations (EPA, 1980). There is, however, no evidence

that zinc buildup in tissues of aquatic organisms is detrimental to the

organisms involved. The primary concern over bioconcentration is poten-

tial human health effects. In that the bioconcentration factor for zinc

can be as high as 17,000, exposure to water containing 0.35 mg/l of zinc

(extracted amount) could result in a tissue concentration of about 6,000

mg/kg. (Note: at least 30 days of continuous exposure to 0.35 mg/l would

be required to achieve this level in the tissues). EPA has estimated that

individuals consume about 6.5 grams of seafood per day. This rate of

consumption would provide a daily zinc intake of 39 mg, assuming that the

consumer obtains all seafood from the Pt. Pinole area. This zinc intake

rate is considerably less than that which would occur if an individual

consumed over-the-counter zinc tablets taken as a dietary supplement, at

the recommended dosage regimen. Zinc tablets produced by pharmaceutical

firms contain up to 220 mg zinc per tablet, and one or more tablets per

day is the recommended dosage. The recommended dietary allowance for zinc

is 15 mglday.

Table 2. ACUTE TOXICITY VALUES FOR SAN FRANCISCO BAY SPECIES

Species -- LC5O/EC50(mg/l)*

Invertebrates

Capitella capitata (adult) 3 .. 5 Capitella capitata (larvae) 1.7

Nereis diversicolor 11-55

Mya arenaria 5..2-7..7

Mytilus edulis 2.5-4.3

Nassarius obsoletus 5 0

Eurytemora sp. 4.1

Acartia sp 0..29-0.95

Fish -

Morone saxitalus (striped bass) 0.1-6.8

Onchorhynchus kisutch (coho salmon) 0.95-4.6

Pseudopleuronectes sp.. (flounder) 4..9-18.2

*LC50 = Concentration causing mortality in 50 percent of the tested organisms.

EC50 = Concentration causing non-lethal acute effects in 50 percent of the tested organisms.

In summary, there is a very low potential for the zinc in the marsh soils to cause significant impairment of the Bay system, either by aquatic toxicity or as a human health threat.