United States
Environmental Protection
Agency
Off ice of
Emergency and
Remedial Response
EPA/ROD/R09-91/076
September 1991
Super-fund
Record of Decision:
TRW Microwave (Advanced Micro
Devices 901) (Signetics), CA
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United States
Environmental Protection
Agency
Office of
Emergency and
Remedial Response
EPAtRODIR09-91/073
September 1991
&EPA
Superfund
Record of Decision:
Advanced Micro Devices 901
(Signetics) (TRW Microwave), CA
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10272.101
REPORT DOCUMENT A 1100 1" REPORT NO. 1 ~ So A8c1Penfa ~ No.
PAGE EPA/ROD/R09-91/076
Co ,.......... I. AIpart...
SUPERFUND RECORD OF DECISION 09/11/91
TRW Microwave (Advanced Micro Devices 901) (Signetics), CA I.
First Remedial Action - Final
7.~) L I'8rfIIrINno 0rpnIDI0n A8pL MD.
L I"IrtrInIIq Olea""""" N8m8... Add!-. 10. PnItIdfTlIIIIIIWarII UnIt MD.
11. c.mct(C) or ~G) No.
(C)
(0)
12. ........ o....&lhl'l N8m8... AM-. 11. Typ8 of AIpart' P8IIod eo-.d
U.S. Environmental Protection Agency 800/000
401 M Street, S.W.
Washington, D.C. 20460 14.
11. ... u' .-"'-, MD.
11. AII8nd (LImIt: 2DO WOIda)
The I-acre TRW Microwave site is an active semiconductor manufacturing facility in
Sunnyvale, Santa Clara County, California. The site is part of a larger study area that
includes four Operable Units (OUs): the 3-acre Advanced Micro Devices (AMD) 901/902
site, the Signetics site, the l-acre TRW Microwave site, and a lOO-acre offsite
contaminated ground water plume. Land use in the area is predominantly commercial and
industrial. Residential property lies to the north and west of the main facilities and
overlies portions of the offsite ground water OU. Six aquifers are associated with the
study area including a deeper aquifer confirmed only at the TRW and Signetics sites.
Currently, the contaminated ground water is not used as a drinking water supply, but the
State considers several of the aquifers to be potential drinking water sources. The
I-acre TRW portion of the site has changed hands several times from 1968 to present;
however, from 1974 to 1986, TRW used its portion of the study area for manufacturing
semiconductors using solvents, metals, and acids. These substances also were used in
semiconductor manufacturing at the AMD and TRW sites from 1969 to the present and from
1964 to the present, respectively. As a result of responses to an information
questionnaire regarding an underground tanks investigation at the TRW site, a number of
(See Attached Page)
17. ~ An8/y8Ia & D8acripIDn
Record of Decision - TRW Microwave (Advanced Micro Devices 901) (Signetics), CA
First Remedial Action - Final
Contaminated Media: soil, gw
Key Contaminants: VOCs (PCE, TCE), other organics
b. ~T....
Co C06Al1 ~
18. AV8II8bIIIy St8I8n8nt 18. s.a.tIy a.. (ThI8 AIpart) 21. No. of""
None 114
20. &8curtIr a.. (ThIa .....) ZIt. PI1c8
Non~
cs- AJ&.ZI8.11)
...NIIId- on Ar-
(F-, 1f11S.a5)
t' r '._.1 of c-..
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EPA/ROD/R09-91/076
TRW Microwave (Advanced Micro Devices 901)
First Remedial Action - Final
(Signetics), CA
Abstract (Continued)
investigations were conducted that revealed extensive contamination of onsite soil and
ground water. Leakage from the acid neutralization system at the AMD and leakage from an
underground waste solvent storage tank at the Signetics site resulted in a number of
investigations that also revealed extensive contamination of onsite soil and ground water
at both of these sites. Several initial remedial measures have been conducted at the TRW
OU. From 1983 to 1984, an underground waste solvent storage tank and 120 cubic yards of
onsite contaminated soil were removed. From 1984 to present, ground water was pumped and
treated using air stripping, followed by onsite discharge to surface water. Several
initial remedial measures also have been conducted at the AMD OU. In 1983 and 1984, acid
neutralization sumps and about 217 cubic yards of contaminated soil were removed. From
1984 to 1988, remediation of ground water was implemented using extraction wells and
dewatering sumps. Several initial remedial measures also were conducted at the Signetics
OU. From 1982 to present, ground water has been pumped from various site locations and
treated using air stripping and carbon adsorption, followed by air stripping to control
off-gases and reuse of the treated water in industrial processes. Contaminated soil has
been removed from three separate locations, including 4,720 cubic yards of soil from a
waste solvent storage tank area in 1983. In 1989, three vapor extraction wells were
installed to treat contaminated soil. In addition, two ground water extraction systems
pump contaminated ground water from the 100-acre offsite plume. The extracted water is
treated at a neighboring AMD facility using air stripping, followed by liquid phase
granular activated carbon polisher and onsite discharge to surface water or reuse by the
facility. This Record of Decision (ROD) collectively addresses final remediation of soil
and ground water in the four separate OUs within the study area. The primary
contaminants of concern affecting the soil and ground water are VOCs including PCE and
TCE; and other organics.
The selected remedial action for this site includes separate remedies for the four
different OUs of the study area. The remedy for the TRW OU includes continuing onsite
pumping and treatment of ground water using air stripping, followed by onsite discharge
of treated water to surface water. The remedy for the AMD OU includes excavating
37 cubic yards of onsite contaminated soil, followed by offsite incineration and/or
disposal, and backfilling the excavation with clean soil; and continuing onsite pumping
and treatment of ground water using air stripping and carbon adsorption of off-gases,
followed by reuse of the treated water. The remedy for the Signetics OU includes
expanding the onsite soil vapor extraction system; and continuing onsite pumping and
treatment of ground water using air stripping, followed by aqueous-phase carbon
polishing, reuse of the treated water, and vapor-phase carbon treatment of the effluent
air stream.' The remedy for the offsite ground water OU includes continuing and expanding
the pumping and treatment system for contaminated ground water using air stripping and
aqueous-phase carbon adsorption, followed by reuse of the treated water or onsite
discharge to surface water, and offsite regeneration of spent carbon. Each OU also will
involve continuing ground water monitoring, and implementing institutional controls
including deed and ground water use restrictions. The estimated present worth cost for
the rernedialaction for all OUs is $11,900,000, which includes an estimated O&M cost of
$225,000 for the AMD OU; $236,000 for the Signetics OU; and $255,000 for the offsite
ground water OU. No annual O&M cost was provided for the TRW OU.
PERFORMANCE STANDARDS OR
background or total VOCs
clean-up goals are based
TCE 5 ug/l (State).
GOALS: Chemical-specific soil clean-up goals have been set at
1 mg/kg based on State policy. Chemical-specific ground water
on State and Federal MCLs, and include PCE 5 ug/l (State) and
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RECORD OF DBCISION
ADv.aHCED K%CRO DEVXCBS "01/'02
SIGllB'rICS
ftW K%CROWAVS
COMBINED SUPERPUHD SITES
SUH1fYVALB, CALIFORHU
September 11, 1"1
u. S . BHV1:ROHKEH'rAL PROTBCTION AGEHCY
REGION'
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1--- -
PART I.
1.0
2.0
3.0
4.0
5.0
PART II.
1.0
2.0
3.0
4.0
TABLB 01' CONTENTS
DBCLARATION . . . . . . . . . . .
SITB DIlES MID LOCATIONS. . . . . . . .
STATBMEHT 01' BASIS MID PURPOSB . . . . . . . .
ASSBSSKBNT 01' TBZ SIT. . . . . . . . . . . . . . . .
DBSCRIPTIO. 01' TBB RBKBDY . . . . . . . . . . .
. . . .
DECLARATION. . . . . . . . . . .
.......
DBCISION StJMMARY . . . . . . . . . . . . . . . . . . .
SITB BAMB, LOCATIO., AND DBSCRIPTIO. . . . . . . . .
1.1 SITE NAME AND LOCATION. . . . . . .
.1.1.1 AMD 901/902 Operable Unit. . . . . . . .
1.1.2 Siqnetics Operable Unit. . . . . . . . .
1.1.3 TRW Microwave Operable Unit. . . . . . .
1.1.4 Offsite Operable Unit. . . . . . . . . .
REGIONAL TOPOGRAPHY. . . . . . . . . . . . . .
ADJACENT LAND USE. . . . . . . . . . . . . . .
HYDROGEOLOGY. . . . . . . . . . . . . . . . . .
WATER USE. . . . . . . . . . . . . . . . . . .
SURFACE AND SUBSURFACE STRUCTURES. . . .
1.7.1 AMD Operable Unit. . . . . . . . . . . .
1.7.2 Siqnetics Operable Unit. . . . . . . . .
1.7.3 TRW Operable Unit. . . . . . . . . . . .
1.7.4 Offsite Operable Unit. . . . . . .
SITB HISTORY AND BNFORCEKEN'1' ACTIVITIBS . . . . . . .
2.1 HISTORY OF SITE ACTrvITIES . . . . . . . .
2.1.1 AMD Operable Unit. . . . . . . . . . . .
2.1.2 Siqnetics Operable Unit. . . . . .
2.1.3 TRW Operable Unit. . . . . . . . .
2.2 HISTORY OF SITE INVESTIGATIONS. . . . . . . . .
2.2.1 AMD Operable Unit. . . . . . . . . . . .
2.2.2 Siqnetics Operable Unit. . . . . .
2.2.3 TRW Operable Unit. . . . . . . . . . . .
2.3 HISTORY OF ENFORCEMENT ACTIONS. . . . . . . . .
2.3.1 AMD Operable Unit. . . . . . . . . . . .
2.3.2 Siqnetics Operable Unit. . . . . . . . .
2.3.3 TRW Operable Unit. . . . . . . . . . . .
COMKUBITY RBLATIO.S . . . . . . . . . . . . . .
3.1 Community Involvement. . . . . . . . . . . . .
3 . 2 Fact Sheets. . . . . . . . . . . ... . . . . .
SCO.. AND ROLB 01' THB RBSPONSB ACTIO. . . . . . . . .
4.1 SCOPE OF THE RESPONSE ACTION. . . . . . . . . .
4.1.1 AMD Operable Unit. . . . . . . . . . . .
4.1.1.1 AMD Interim Remedial Measure. . .
4.1.1.2 AMD Selected Remedy. . . . . . .
4.1.2 Siqnetics Operable unit. . . . . . . .
4.1.2.1 Siqnetics Interim Remedial Measure
4 . .1. 2 . 2 S iqnetics Selected Remedy. . . .
4.1.3 TRW Operable Unit. . . . . . . . . . . .
4.1.3.1 TRW Interim Remedial Measure
4.1.3.2 TRW Selected Remedy. . . .
1.2
1.3
1.5
1.6
1.7
1
1
1
1
1
3
4
4
4
4
8
8
11
11
11
13
15
16
17
17
20
20
20
22
22
22
23
24
24
25
25
26
26
27
27
28
28
28
29
29
29
29
31
31
31
32
34
34
35
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5.0
'.0
7.0
8.0
4. 1. 4 Offsi te Operable Unit... . . . . . . . .
4.1.4.1 Offsite Interim Remedial Measure.
4.1.4.2 Off site Selected Remedy. . . . .
4.2 ROLE OF THE RESPONSE ACTION . . . . . . .
SUMKARY OF SITE CHARACTERISTICS. . . . . . . . . . .
5.1 SOURCES OF CONTAMINATION. . . . . . . . . . . .
5.1.1 AMD Source Investigation . . . . .
5.1.2 Siqnetics Source Investigation. . . . .
5.1.3 TRW Source Investigation . . . . .
5.2 DESCRIPTION OF CONTAMINATION. . . . . . . . . .
5.2.1 SOIL INVESTIGATIONS. . . . . . . . . . .
5.2.1.1 AMD Operable Unit. . . . . . . .
5.2.1.2 Siqnetics Operable Unit. . . . .
5.2.1.3 TRW Operable Unit. . . . . . . .
5. 2 . 2 GROUNDWATER INVESTIGATIONS. . . . . . .
5.2.2.1 AMD Operable Unit. . . . . . . .
5.2.2.2 Siqnetics Operable Unit. . . . .
5.2.2.3 TRW Operable Unit. . . . . . . .
5.2.2.4 Offsite Operable Unit. . . . . .
5. 2 . 3 AIR INVESTIGATIONS. . . . . . . . . . .
5.2.3.1 AMD 901/902 Operable Unit. . . .
5.2.3.2 Siqnetics Operable Unit. . . . .
5.2.3.3 TRW Operable Unit. . . . . . . .
5.2.3.4 Offsite Operable Unit
SUMKARY OF SITE RISES. . . . . . . . . . . . . . . .
6.1 TOXICITY ASSESSMENT. . . . . . . . . . . . . .
6.2 RISK CHARACTERIZATION. . . . . . . . . . . . .
6.2. 1 Soil. . . . . . . . . . . . . . . . . .
6.2.1.1 AMD 901/902 Soil. . . . . . . . .
6.2.1.2 Siqnetics Soil. . . . . . . . . .
6.2.1.3 TRW Soil. . . . . . . . . . . . .
6.2.1.4 Offsite Soil. . . . . . . . . . .
6 . 2 . 2 Air. . . . . . . . . . . . . . . . . . .
6.2.2.1 AMD 901/902 . . . . . . . . . . .
6.3.2.2 Signetics . . . . . . . . . . . .
6 . 3 . 2 . 3 TRW . . . . . . . . . . . . . . .
6.3.2.4 Offsite . . . . . . . . . .
6.3.3 Groundwater. . . . . . . . . . . . . . .
6.3 PRESENCE OF SENSITIVE HUMAN POPULATIONS. . . .
6.4 PRESENCE OF SENSITIVE ECOLOGICAL SYSTEMS.
6.5 CONCLUSION. . . . . . . . . . . . . . . .
APPLICABLE OR RELBVAlrl' UD APPROPRIATE REQUIREMENTS
(ARARS) . . . . . . . . . . . . . .
. . .
. . . . . .
7.1 TYPES OF ARARS . . . . . . . . . . . . . . . . .
7.2 CONTAMINANT-SPECIFIC ARARS AND TBCS . . . . . .
7.3 ACTION SPECIFIC ARARS AND TBCS . . . . . . . . .
7.4 LOCATION-SPECIFIC ARARS . . . . . . . . . . . .
DESCRIPTION OF ALTERNATIVES. . . . . . . . . .
8.1 REMEDIAL ACTION OBJECTIVES. . . . . . . . . . .
8.2 CLEANUP STANDARDS. . . . . . . . . . . . . . .
8.2.1 Cleanup Standards. . . . . . . . . . . .
8.2.2 Compliance Boundaries. . . . . . . . . .
8.3 REMEDIAL ACTION ALTERNATIVES. . . . . . . . . .
8 . 3 . 1 AHD Operable Unit. . . . . . . . . . . .
38
38
38
41
41
41
41
42
42
43
43
43
43
44
45
45
45
46
46 .
47
47
48
49
49
52
52
55
56
56
56
56
57
57
57
58
59
59
60
62
62
63
63
64
64
65
67
67
67
68
68
70
75
75
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'.0
10.0
11.0
,
PART :I:n:.
1.0
2.0
I
I 0
,
I
8.3.2 Siqnetics Operable Unit. . . . . . . . . 77
8.3.3 TRW Operable Unit. . . . . . . . . . .. 78
8.3.4 Offsite Operable Unit. . .0. . . . . . 79
COKPARAT:IVB UlALYS:IS OJ' ALTERHAT:IVES . . . . . . .. 80
9 ~ 1 NINE CRITERIA. . . . . . . . . . . . . . . .. 80
9.2 ANALYSIS OF ALTERNATIVES. . . . . . . . . . .. 81
9.2.1 AMD Operable Unit. . . . . . . . . . .. 82
9.2.1.1 AMD Soils. . . . . . . . . . .. 82
9.2.1.2 AMD Groundwater. . . . . . 87
9.2.2 Siqnetics Operable Unit. . . . . . . .. 90
9.2.3 TRW Operable unit. . . . . . . . . . .. 94
9.2.4 Offsite Operable Unit. . . . . . . 98
9.3 THE SELECTED REMEDY . . . . . . . . . . . . . . 102
9.3.1 Basis of Selection. . . . . . . . . . . 102
9.3.2 Features of the Remedies. . . . . . . . 103
9.3.3 Uncertainty in the Remedy. . . . . . . . 105
STATUTORY DETERX:IHAT:IOBS . . . . . . . . . . . . . . 106
DOCUKERTAT:IOB OJ' 8:IGB:IJ':ICAHT CBAHGES . . . . . . . . 107
RESPOHSrvENESS SUMMARY. . . . . . . . . . . . . . . 107
:IBTRODUCT:IOB . . . . . . . . . . . . . . . . . . . . 107
REG:IOHAL WATER gUAL:ITY COBTROL BOARD RESPONSES. . . 107
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LIST OF FIGURES
Figure 1 - Location Hap. . . . . . . . . . . . . . . . . . . .
Figure 2 - Operable Unit Hap . . . . . . . . . . .
Figure 3 - AMD 901/902 Site Hap. . . . . . . . . .
Figure 4 - Siqnetics Site Hap. . . . . . . . . . . . . . . . .
Figure 5 - TRW Site Hap. . . . . . . . . . . . . . . . . . . .
Figure 6 - Offsite TCE Plume Hap. . . . . . . . . . . . . . .
Figure 7 - Schematic Hydroqeoloqic Log . . . . . . . . . . . .
Figure 8 - Historical Waste Storaqe Locations, AMD 901/902
Figure 9 -.Waste Storaqe, Siqnetics, 811 E. Arques . . . . . .
Figure 10 - Chemical Storaqe' and Processinq, TRW, 825 Stewart
Dr . ...........................
Figure 11 - AMD 901/902 Groundwater Extraction System. . . . .
Figure 12 - Siqnetics Groundwater Extraction System. . . . . .
Figure 13 - TRW Groundwater Extraction System. . . . . . . . .
Figure 14 - Offsite Groundwater Extraction System. . . . . '. .
Figure 15 - Soil Flux Sample Location Hap. . . . . . . . . . .
Figure 16 - A Zone Plume Boundaries. . . . . . . . . . .
Figure 17 - B Zone Plume Boundaries. . . . . . . . . . .
LIST OF TABLES
TABLE 1 - NPDES DISCHARGE LIMITS, SIGNETICS . . . . . . . . . .
TABLE 2 - NPDES DISCHARGE LIMITS, TRW . . . . . . . . . . . . .
TABLE 3 - NPDES DISCHARGE LIMITS, OFFSITE . . . . . . . .
TABLE 4 - AMD 901, SIGNETICS, TRW DATA SUMMARY . . . . .
TABLE 5 - ADULT CARCINOGENIC RISK, AMD 901/902, SIGNETICS, AND TRW
.........
. . . . .
.................
TABLE 6 - CLEANUP STANDARDS FOR THE CHEMICALS OF CONCERN IN
GROUNDWATER. . . . . . . . . . . . . . . . . . . .
TABLE 7 - HAZARD INDEX AT CLEANUP STANDARDS, AMD 901/902,
Signetics, TRW . . . . . . . . . . . . . . . . . . . . . .
TABLE 8 - CANCER RISK AT CLEANUP STANDARDS . . . .
5
6
7
9
10
12
14
18
19
21
30
33
36
39
51
73
74
34
37
40
53
61
69
71
72
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PART I.
DECLARATION
1.0
SITB HAKES ABD LOCATIONS
. Advanced Mi~ro Devices
901/902 Thompson Place
Sunnyvale, CA 94088
Siqnetics, Inc.
811 East Arques Avenue
Sunnyvale, CA 94088
TRW (FEI) Microwave
825 Stewart Drive
Sunnyvale, CA 94088
2.0
STATIHEIIT OP BASIS ANI) PURPOSE
This Record of Decision ("ROD") presents the selected remedial
actions for the Advanced Micro Devices 901/902, signetics and TRW
Microwave Superfund sites in Sunnyvale, California. This group of
sites has been divided into four operable units (OUs). This
document was developed 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), 42 U.S.C. Section 9601 et. sea.. and, to the
extent practicable, the National Oil and Hazardous Substances
Pollution Contingency Plan, 40 C.F.R. Section 300 et. sea..
("NCP"). The attached ad.ministrati ve record indices (Attachment B)
identify the documents upon which the selection of the remedial
actions are based. The State of California concurs with the
selected remedies.
3.0
ASSBSSKENT OP THE SITB
Actual or threatened release of hazardous substances from these
si tes, if not addressed by implementing the response actions
selected in this ROD, may present an imminent and substantial
endangerment to public health, welfare, or the environment.
4.0
DESCRIPTION OP THE REMEDY
Remedies have been selected for each operable unit. The remedy for
the AMD 901/902 operable unit consists of soil excavation followed
by offsite incineration/disposal, continued groundwater extraction
-------
followed by treatment of the extracted qroundwater with the
existinq air stripper, and reuse of the treated water. The air
stripper includes air emissions control and is requlated by the Bay
Area Air Quality Manaqement District (BAAQMD). Additional
contaminated soils and structures were removed as part of interim
remedial actions.
The remedy for the Siqnetics operable unit consists of vapor
extraction. for soil remediation with continued qroundwater
extraction, treatment of contaminated water with the existinq air
stripper and reuse of the treated water. The qroundwater treatment
system uses multiple air strippers. The initial .air stripper
includes air emissions control and the second set of air strippers
are not controlled. All air strippers meet the requirements of the
BAAQMD requlations. Aqueous phase carbon is utilized. as a final
treatment and serves as a backup system to the air strippinq
systems. Additional contaminated soils and structures were removed
as part of interim remedial actions.
The remedy for the TRW operable unit consists of continued
qroundwater extraction, treatment of contaminated water with the
existinq air stripper and discharqe of the treated qroundwater to
surface water under an NPDES permit. The required qoal for water
reuse is loot. The qroundwater treatment system uses an air
stripper to remove chemicals from the qroundwater. The air effluent
from the air stripper is not controlled. The air stripper meets the
requirements of the BAAQMD requlations and air emission control
will be added to the system if required by BAAQMD.
The remedy for the offsite operable unit consists of continued
qroundwater extraction. The contaminated qroundwater is piped to
the AMD facility at 915 DeGuiqne Drive for treatment by an air
stripper, followed by reuse or discharqe of the treated qroundwater
to surface water under an NPDES permit. The required qoal for water
reuse is lOOt. The qroundwater treatment system uses an air
stripper to remove chemicals from the qroundwater. The air effluent
from the air stripper is not controlled. The air stripper meets the
requirements of the BAAQMD requlations and air emission control
will be added to the system if required by BAAQMD. Additional
contaminated soils and structures were removed as part of interim
remedial actions.
These remedial actions address the principal risks remaininq wi thin
a study area defined by four operable units includinq the area from
approximately Arques Avenue on the south and north to Lake Haven
Drive and bounded on the east by DeGuiqne Avenue and Fair Oaks
Avenue on the West. These risks are addressed by removinq the
contaminants from qround water, thereby siqnificantly reducinq the
toxicity, mobility or volume of hazardous substances. These
response actions will qreatly reduce the possibility of
contamination of existinq potable water supplies and potential
future water supplies.
paqe 2 of 108
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5.0
DBCLUA'l'IOII
The selected remedies are protective of human health and the en-
vironment, comply with federal and state requirements that are
legally applicable or relevant and appropriate to the remedial
action, an~ are cost-effective. These remedies utilize permanent
solutions and alternative treatment (or resource recovery) tech-
nologies to the maximum extent practicable and satisfy the
statutory pret:erence for remedies that employ tJ:eatment that
reduces toxicity, mobility, or volume as a principal element.
Because the remedies will result in hazardous substances remaining
on-site above health-based levels, a five-year review, pursuant to
CERCLA Section 121, 42 D.S.C. section 9621, will be conducted at
least once every five years after initiation of the remedial action
to ensure that the remedy continues to provide adequate protection
of human health and the environment.
John w~ VJ ""-
Deputy Regional Administrator
t:t.f/. q,
Date
Page3 of104
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PART II. DBCISION SUMMARY
This Decision Summary provides an overview of the problems posed by
the Advanced Micro Devices, Siqnetics, TRW Microwave Superfund
sites and an "offsite" area where qroundwater contaminant plumes
have become commingled ("the Study Area"), the remedial
alternatives, and the analysis of the remedial alternatives. This
Decision Summary explains the rationale for remedies selected at
the three areas and how the selected remedies satisfy the statutory
requirements.
1.0
SITB HAME, LOCATION, AND DBSCRIPTION
1.1
SITE NAME AND LOCATION
As referenced above this ROD includes three separate Superfund
sites and an offsite area located in Sunnyvale, Santa Clara County~
California (Fiqure 1). These areas have been combined 'into a large
study area (Fiqure 2). Each of the three Superfund sites and their
commingled plume have been considered separately as one of four
operable units (OUs) within the larger study area. A detailed
discussion of each operable unit is presented in the sections
below.
1.1.1
AMD 901/902 Operable Unit
The Advanced Micro Devices facility (Fiqure 3) located at 901/902
Thompson Place, Sunnyvale California (AMD 901/902) consists of two
low rise buildings connected by a common foyer and entrance. This
is located in an area of low to flat relief about 3 miles south of
the southern extension of the San Francisco Bay in an area broadly
bounded by the Bayshore, Central, and Lawrence Expressways and Fair
Oaks Avenue. This is an industrial park setting dominated by low
rise industrial buildings common in the electronics industry of
Santa Clara County. The industrial park area is dominated by
electronics manufacturers. Mixed commercial and light industrial
use is common immediately surrounding the industrial park area. No
residential property is in the immediate vicinity of the AMD
901/902 operable unit. Some residential property lies to the west
and south of the industrial park. The area to the north of the AMD
901/902 operable unit is part of the industrial park and includes
the TRW operable unit. Land use immediately north of the industrial
park area is mixed commercial property, followed by a predominately
residential .rea further north.
Page 4 of 108
-------
o
IQm,le\
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o
2500
SCALE IN FEET
5000
. l-I.ly"'Jrd
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Muun~i,(Vic:w. -US.!n
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MAP .
AREA
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Fiqure 1.
Location Map of the study Area including:
AMD 901/902, Siqnetics, and TRW Microwave
-------
~
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Figure 2.
Map of operable units
-------
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AMD 901/902 site
Map
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EXPLANATION
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1.1.2
Siqnetics Operable Unit
siqnetics owns and operates a facility located at 811 East Arques
Avenue, in Sunnyvale. This location is part of a larqer complex of
facilities operated by Siqnetics, includinq 440 Wolfe and several,
facilities alonq Stewart Drive (Fiqure 4). This is an area of
Santa Clara County developed as an industrial park, dominated by
low rise buildinqs. The major business activity of the area is
semiconductor manufacture and research and development. The
Siqnetics' facilities are representative of property development in
this area.
This is an area of low topoqraphic relief in the southern portion
of the Santa Clara Valley. Surface drainaqe in the area is to the
north, toward San Francisco Bay. Veqetation is limited to qrass
and shrubs. Residential development has occurred in the area south
of the Siqnetics facility within the last two years. The area
immediately west of the Siqnetics OU is park land. The area
immediately north of the Siqnetics OU is the former Sunnyvale Hiqh
School property, which is currently used as an electronics research
and development facility. This area includes a track and ball field
for recreational use by employees.
1.1.3
TRW Microwave Operable Unit
The former TRW Microwave facility (TRW) is located at 825 Stewart
Drive, Sunnyvale, Santa Clara County. Aerotech Industries and this
site were wholly acquired by TRW Microwave in 1974 and was operated
by TRW Microwave from July 1974 to Auqust 1986. The property was
purchased by Tech Facility 1, Inc. in 1987. Some assets at this
site were acquired by FEI Microwave, Inc. in July 1987. The
manufacturinq facility is currently operated by FEI Microwave, Inc.
This location is near the intersection of the Lawrence Expressway
and Route 101 (Fiqure 5). This is an area of the Santa Clara Valley
of low topoqraphic relief. The drainaqe in the area is toward the
north to San Francisco Bay. The facility is located in an
industrial park settinq dominated by low buildinqs separated by
paved parkinq lots, fields and streets" with some landscapinq. The
dominant activity in this area is related to the semiconductor
industry, thouqh the industrial park is bordered by residential
property particularly to the north.
paqe 8 of 108
-------
-
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Figure 4.
Signetics
site Map
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TRW Microwave site Map
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1.1.4
Offsite Operable Unit
The study area for the offsite operable unit begins north of the
Siqnetics operable unit (Figure 2) and extends north of Duane
Avenue in an area bounded approximately by the Sunnyvale East
Drainage Channel on the west and Santa Paula Avenue on the east.
The study area extends north of Highway 101 to just north of
Lakehaven Drive. The actual offsite operable unit is loosely
defined as-the area inside the 5 ~g/l (Figure 6) isopleth for TCE
in groundwater. This covers an.area of about 100 acres and includes
commercial and residential property. The area south of Duane Avenue
is industrial property and includes the former SUnnyvale High
School Buildings currently used as an industrial research and
development facility. Commercial and retail property is mixed with
multiple unit residential property along the north side of Duane
Avenue. The remainder of the offsite area is residential property,
including approximately 600 single family residential units and the
former San Miguel Elementary School. The Elementary School'
currently is used as a daycare facility' for the community and
houses a Headstart Program for Sunnyvale.
1.2
REGIONAL TOPOGRAPHY
The Study Area is located in the Santa Clara Valley which is a
gently-sloping alluvial plain, flanked by the Diablo Range to the
east-southeast and the Santa cruz Mountains to the west-southwest.
The Study Area is located toward the center of the valley. The
Santa cruz Mountains are located several miles southwest of the
Study Area. The San Francisco Bay is located approximately 4 miles
north of the Study Area.
1.3
ADJACENT LAND USE
The study area site is a broad area extending to just north of the
Bayshore Freeway, bounded on the south by the Central Expressway,
and bounded east to west by the Lawrence Expressway and Fair Oaks
Drive (see Fiqure 1). The facility is located in an industrial
park setting bordered by residential areas. The area to the east is
dominantly commercial and retail space. The area immediately to the
west of the study area is mostly residential property. The land to
the north of the study area is a mix of multiple and single family
residential property including several large trailer park
development. and retail centers.
Approximately 60' of the study area acreage is devoted to
industrial and commercial use. The former San Miguel School
facility accounts for about 5' of the study area with the remainder
used as residential property. The recreational facilities within
the surrounding areas include a park along Fairoaks which includes
ball fields and tennis courts.
Page 11 of 108
-------
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Figure 6.
Offsite TCE Plume Map
-------
1.4
HISTORICAL LAND USE
Land use in Santa Clara County, until the late 60' s, was
agricultural, predominantly commercial fruit orchards. Development
of light industrial manufacturing facilities began in the late
50's. As the area developed a reputation as a center of the micro-
. electronics industry, development accelerated through the 70' s.
This, alon~with increased demand for residential property related
to the increased industrialization, has limited agriculture to
isolated locations and the fringes of the Santa Clara Basin.
All of the industrial facilities within the study area were built
on land that had previously been used for agriculture and all were
desiqned and built as electronics manufacturing plants. While
manufacturing processes have varied among the facilities and
through time, the manufacturing processes at these sites have
involved the use of solvents, caustics, metals, and acids. The
current trend is a decline in the importance of manufacturing and
increased emphasis on research and development activities.
1.5
HYDROGEOLOGY
Stratigraphy in the valley surrounding the study. area is
characterized by interbedded and interfingering sands, silts and
clays. These sediments were deposited in complex patterns by
fluvial-alluvial systems draining the uplands to the south with
sediments deposited as the streams flowed north toward the Bay.
The nomenclature applied to the water bearing units in the study
area is representative of the hydrogeology within the Santa Clara
Groundwater Basin. A number of shallow water bearing units are
separated from deeper aquifers by a thick persistent aquitard. The
shallow units may be subdivided into a variety of zones depending
upon depth, .li tholoqy and lateral persistence. These zones are
frequently labeled as A and B zones (Fiqure 7). The deeper aquifer
is commonly referred to as the C aquifer and the clay layer
separating the upper and lower water-bearing zones is commonly
referred to as the B-C aquitard. The aquitard has been reported to
be between 50 and 100 feet thick in Santa Clara Valley.
Six local aquifers have been identified through the investigation
in the study area and the deeper, B-C aquitard (Fiqure 7) has been
confirmed at both the TRW and Siqnetics operable units. Regional
investigation has indicated that deeper aquifers do exist in the
Santa Clara Valley Groundwater Basin and are probably present in
the project area. The shallowest water bearing zone has been
designated the A zone and generally occurs from 6 to 25 feet below
the ground surface. This is the most persistent, permeable unit
near 825 Stewart Drive and generally contains from 1 to 19 feet of
permeable material. The next unit has been designated as theB1
aquifer and generally occurs from 25 to 55 feet below ground
Page 13 of 108'
-------
REGIONAL
DESIGNA nON
.20'
TYPICAL
LITHOLOGY
... .-. 35'
A ZONE
15'
81 ZONE
.40' ~ - 5'
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- 82 ZONE
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B-C AQUIT ARD
-105'
C AQUIFER
Fiqure 7
schematic Hydrogeologic Log
-------
surface and contains 0.5 to 15 feet of permeabie materials. The
next unit has been designated as the B2 aquifer and occurs from 45
to 55 feet below the ground surface. It generally contains from 6
to 8 feet of permeable material. The next unit, the B3, is
relatively thin and only encountered in a few borings at the TRW
site. It consists of from 1 to 5 feet of permeable material. The
next unit, B4, begins from 82 to 86 feet below ground surface and
. contains 1 to 4 feet of permeable material. The deepest unit
identified .at the TRW site is aquifer B5. This aquifer occurs from
116 to 123 feet below ground surface and contains 5 to 7 feet of
permeable material.
The static groundwater flow direction within the study area is to
the north-northeast in all aquifers. The vertical gradient has
been documented to be upward under normal conditions in the study
area. The flow direction and vertical hydraulic gradient may be
reversed locally in the vicinity of groundwater extraction wells
operating in the A, B1, B2, and B3 aquifers.
1.6
WATER OSE
CUrrently, groundwater from this basin provides up to 50' of the
municipal drinking water for the 1.4 million residents of the Santa
Clara Valley. In 1989, groundwater accounted for approximately
128,000 of the 315,000 acre feet of drinking water delivered to
Santa Clara Valley Water District customers. This water is produced
from the C aquifer. Groundwater contamination is limited to the
shallow A and B water bearing zones (see Section 1.5 above).
Prior to the conversion ot agricultural land throughout the Santa
Clara Valley to industrial use in the late 1960's and early 1970's,
groundwater in this area was used as irrigation supply and for
other agricultural purposes. No supply wells completed in the
contaminated shallow aquifers have been identified. On March 30,
1989, the Regional Board incorporated the State Board Policy of
"Sources of Drinking Water" into the Basin Plan. The policy
provides for a Municipal and Domestic Supply designation for all
waters of the State with some exceptions. Groundwaters of the
State are considered to be suitable or potentially suitable for
municipal or domestic supply with the exception of: 1) the total
dissolved 80lids in the groundwater exceed 3000 mg/L, and 2) the
water source does not provide sufficient water to supply a single
well capable of producing an average, sustained yield of 200
gallons per day. Based on data submitted as part ot the Remedial
Investigation report, the RWQCB has determined that neither of
these two exceptions apply to the A and B zones in the study area.
Thus, the A and B zones are considered to be potential sources of
drinking water by RWQCB. EPA agrees with this determination. .
AMD 901/902, TRW Microwave and Signetics were proposed for
inclusion on the National Priorities List (NPL) (see Section 2.3)
primarily because of the potential threat from past chemical
Page 15 ot 108
-------
releases to the quality of this valuable resource. The major
concern at the site stems from the potential migration of
contaminants in the Upper Aquifer Zone down to the Lower Aquifer
Zone through abandoned or poorly sealed wells or natural conduits
through aquitard material. Municipal water supply wells are
generally perforated in the Lower Aquifer Zone. All water supply
'wells located within an approximate one mile radius of the study
area are perforated from 190 to 390 feet below ground surface.
CUrrently, . the nearest municipal drinking water supply well
downgradient of the study area is a Santa Clara Valley Water
District well, which is located more than 1000 feet. north of the
site. No pollutants have been found in this well to date.
CUrrently, there are no known users of ground water from the Upper
Aquifer Zone. The Regional Water Quality Control Board (RWQCB) has
identified potential beneficial uses of the shallow ground water
underlying and adjacent to the study area. These beneficial uses
include industrial process water supply, industrial service water
supply, municipal and domestic water supply and agricultural water
supply. These are the same as the existing and potential
beneficial uses of the ground water in the Lower Aquifer Zone.
A well search for abandoned wells in a 3350 acre area encompassing
the study area was completed in December 1986. This includes over
one mile in all directions and over three miles in the downgradient
direction. The focus of the well search was to identify wells that
potentially may form migration pathways to. the deeper aquifer. The
search identified 177 possible well locations. Of these wells 76
are identified as destroyed. Only four wells that might act as
potential migration conduits to deeper aquifers were identified.
One of these wells is a Santa Clara Valley Water District (SCVWD)
well more than 1000 feet downgradient of the site. Testing of the
well has shown no evidence of contamination. Of the remaining three
wells, two wells are listed as destroyed in SCVWD records. The
remaining well is a cathodic protection well maintained by Pacific
Gas & Electric. This type of well is frequently installed to
inhibit rust in underground pipelines. These wells are typically
. shallow (i.e. pipeline depth) and cased with steel. No additional
data was available on the other well. and attempts to field check
the well location were unsuccessful.
Two municipal supply wells were identified by the potential conduit
study. Well 1D number 1845 is a City of Sunnyvale water supply
well. This well i8 over 3000 feet upqradient of the known
groundwater contamination plume. Well 1D number T6SR1WS29N2
T6SR1WS29 is also upqradient of the groundwater pOllution plume and
is shown in Santa Clara Valley Water District records as destroyed.
1.7
SURFACE AND SUBSURFACE STRUCTURES
Surface and subsurface structures involving the use of chemicals is
limited to the AMD 901/902, Signetics and TRW Microwave operable
Page 16 of 108 .
-------
uni ts . These are the only areas were chemical use has been
documented. The structures are similar within each operable unit,
however the number and location is different enough to warrant a
discussion focused on each operable unit.
1.7.1
AND Operable Unit
"The surface area included in the AMD 901/902 operable unit is
approximately 3 acres with the physical surface structures covering
about 0.6 acres. Subsurface structures at the AMD 901/902 facility
include both structures installed in vaults below engineered grade
and structures installed directly into native soils. These
structures include waste solvent tanks and acid neutralization
systems (ANS). One above qrade waste solvent tank in the Pad II
area (Figure 8) was installed in 1972 or earlier. This tank was
removed in 1982 and replaced with a 1000 gallon below qrade steel
unit. This new tank. installed in a coated concrete vault, is still
in use. "
Separate acid neutralization systems were maintained for each
fabrication facility (901 and 902). The acid neutralization system
for the 901 facility was installed in the Pad I area (Figure 8) in
1968 and removed in 1982. The ANS tor AND 902 was installed in the
Pad II area in 1972. This system was excavated and removed in 1984.
Each system consisted of a single coated concrete tank of about
2000 gallon capacity.
New acid neutralization systems were installed in 1982. The A-
system for AMD 901 and the B-system for AMD 902. Both systems are
fiberglass reintorced tanks installed in below grade coated vaults.
Each system consists of three tanks with a total capacity of 2000
gallons.
1.7.2 Siqnetics Operable Unit
Above qround structures at the Siqnetics facility include the 811"
East Arques building, a building at 440 Wolfe and buildings at 830
and 815 Stewart Drive (Figure 2). The remedial investigation has
included qroundwater monitor wells, soil samples and/or soil gas
studies near all tour buildings. The investigation has focused on
underqround structures and the primary source of contamination at
the 811 East Arques building.
In general underqround structures at the Siqnetics facility can be
qrouped into three categories; diesel tanks, waste solvent storage,
and waste water storage or treatment tanks. A waste solvent tank
located on the west side ot the 811 E. Arques building was removed
in 1982 (Figure 9). Waste water treatment tanks located north of
the 811 building were removed in 1984.
Page 17 of 108
-------
"PAD ][ "
ACID
NfUTRALllA "ON
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ABOVEGROUND
WASTE SOL VENT
TANK
(1982)
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WASTE DRUM
STORAGE
(1982)
-
.PAD J[ "
WASTE DRUM
STORAGE
(1982)
..... IN PlIO. I-MI/6IIW IfJIIt
-- IIU aPO . "... -... " IJ-M1fIID lIIIII'J
SCAlf:
1" = 90'
@
DIIACrIar IIIW
Figure 8.
Historical Waste storage Locations at AMD 901/902
(with removal dates in parentheses)
-------
--a- 2 -41!!!!!!!!
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SIGNETICS
811 BUI LDING
---- ..........
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Figure 9.
Waste storage Locations at Signetics
I
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100 ,",
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currently four underground diesel .fuel tanks are in place on the
west side ot the 440 Wolfe building and one underground diesel tank
is in place on the east side of the 811 E. Arques building.
Groundwater monitor wells located downgradient of the diesel tanks
are monitored quarterly. Two underground waste solvent tanks are
located on the west side of the 811 East Arques facility near the
waste water treatment plant. The facilities on the east side of the
811 East Arques building are located in concrete vaults. Two waste
water equalization tanks are located at the northeast corner of the
811 East Arques and two additional waste water neutralization tanks
are locatea at the northeast corner of the 440 Wolfe facility.
Groundwater monitoring wells are also located downgradient of these
tanks.
1.7.3
TRW Operable Unit
The former TRW Microwave facility at 825 Stewart Drive is one of
three structures on an approximately 1 acre site. The investigation
has been focused on the 825 Stewart Drive building. Two below
ground facilities have been documented at the TRW site. These
include an acid neutralization system north of the building and a
waste solvent storage tank (Figure 10). The acid neutralization
system was installed in 1968 when the facility began operation. The
first tank in a series of four underground waste solvent tanks was
installed in 1970 and was replaced sequentially in 1973, "1976, and
1980. The final underground solvent tank was removed in 1983. The
acid neutralization system was removed in 1986 and replaced by a
three tank above ground system.
1.7.4
Offsite Operable U~it
Structures within the offsite operable unit are primarily retail or
residential. The exceptions to this is the former Sunnyvale High
School site just north of the Signetics 440 Wolfe facility (Figure
2) and the San Miguel School site located near the corner of San
Miguel and Alvarado Avenues (Figure 2).
2.0
SITB HISTORY AND ENFORCEMENT ACTIVITIES
Separate Orders have been prepared by the RWQCB for each onsite
Operable Unit (AMD, Signetics and TRW) with joint tasks for the
Offsite OU unit. This course has been taken due to the commingling
of the groundwater plume in the offsite area. The Companies are
encouraged to submit joint reports when feasible. A joint RIfFS was
completed and served to further define the groundwater contaminant
plume. If joint reports are not coordinated and submitted, each
company is still individually responsible for the joint tasks in
these Board Orders.
Page 20 of 108
-------
t',. C'hemlcal'
" Storage Yard 1f
:~:. ' ,):$;
Underground Solvent Tank
Existing & Former (umillate 1983)
Acid Neutralization System--...IIIJ
'.
--_..... -.'.-"----.
MIC Assembly
(prior to 1987)
, I
IFM Assembly
(since 1987)
Metal Plating ;
Shop (prior to 1986) ,
N
1
EXPlANATION
..:,;', ExlstlrQchemlcal
:p ,.': processing or S1orIg8 818.
rA Former chemical processing
LLJ or storage area
o
I
101.
I
Figure 10.
Chemical storage and Processing Locations
at TRW Microwave
-------
2.1
HISTORY OF SITE ACTIVITIES
As discussed above, conversion of the aqricultural land in the
Santa Clara Valley to industrial use beqan in the late 50's and
escalated in the 60' sand 70' s with the establishment of Santa
Clara as a center of the electronics industry. The three industrial
facilities included in this ROD have been a part of this pattern of
development:.
2.1.1
AMD Operable Unit
AMD 901 has been used as a semiconductor manufacturinq facility
since 1969 to the present. Manufacturinq operations at AMD 902
beqan in 1972 and are still active. The manufacturinq process at
these two facilities involved the use of solvents for cleaninq and
deqreasinq, acids for etchinq, caustics for acid neutralization and
some arsine and chromium in the manufacturinq process.
Initial investiqation at the AMD 901/902 site beqan in 1982. with
the investiqation of leakaqe from an acid neutralization system
near AMD 901. This leakaqe was investiqated and the acid
neutralization system was removed durinq 1983. In 1984 the
investiqation expanded to include the acid neutralization system at
AMD 902. Polluted soils were found near both acid neutralization
systems.
The polluted soils were identified as point sources that had
resulted in qroundwater pollution with volatile orqanic chemicals
(VOCs). Further investiqation and interim remedial actions followed
the soils investiqation.
The oriqinal development of the property was bequn by Johnson and
Mape. The property at 901 Thompson Place was acquired from Johnson
and Mape by B/G Manaqement in 1977. The property at 902 Thompson
Place was acquired from Johnson and Mape by Mr. and Mrs. Edwin
Rosenthal in 1974. Partial interest in the 902 property was sold by
Mr. and Mrs. Rosenthal in 1982. The remaininq interest was sold in
1984. The purchase of these interests was converted into two
undivided sot interests in the property at 902 Thompson Place for
Research Group 82-1 and Thompson Place 2, limited partnerships.
These are the current property owners of record for AMD 901/902.
AMD has been the sole tenant and operator of the facilities and has
assumed responsibility for the cleanup actions at the site.
2.1.2
Siqnetics Operable Unit
Siqnetics has operated a semiconductor manufacturinq facility at
the 811 E. Arques Avenue since 1964. The manufacturinq processes
employed at this location have utilized various orqanic solvents,
acids, corrosives, and metals. CUrrent chemical usaqe is similar to
past patterns, with the exception of the closure of the plating
paqe 22 of 108
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operation at 811 E. Arques, which has eliminated some potential
sources of aetal pollution, and the elimination of chemicals
containing chromium, phenol, trichloroethylene (TCE) , and
perchloroethylene (PCE).
I~itial investigation at the site began in February 1982 with the
detection of a leak in an underground waste solvent storage tank.
The presence of contaminated soil was verified during the tank
.removal. Following additional investigation of the Signetics main
campus facility (440 Wolfe, 815 Arques, 830 Arques) the waste
solvent tank area has been identified as the principal source of
contaminants on the Signetics site.
All storage and treatment facilities have been updated and either
relocated above ground or doubly contained. Hazardous materials
from other nearby Signetics facilities are stored at the 811 E.
Arques site, under the authority of the Resource Conservation and
Recovery Act (RCRA), prior to offsite disposal at an appropriate
commercial disposal facili ty. Recent facili ty inspections and
reporting indicate that the facility is in compliance wi th the
requirements of its RCRA permit.
2.1.3
TRW Operable Unit
Initial operation as an industrial facility began in 1968 when
Aerotech Industries began assembling and testing microwave
components at this site. The first semiconductor manufacturing
began in 1970. Aerotech Industries and this site were acquired by
TRW Microwave in 1974 and was operated by TRW Microwave from July
1974 to August 1986. The property was purchased by Tech Facility 1,
Inc. in 1987. Some assets at this site were acquired by FEI
Microwave, Inc. in July 1987. The manufacturing facility is
currently operated by FEI Microwave, Inc.
While processes have varied throughout the history of the site,
chemical usage has remained relatively constant. Solvents, metals,
and acids have been involved in the manufacturing process. FEI
Microwave is currently manufacturing electronic components at the
facility. .
As a result of responses to an information questionnaire regarding
underground tanks investigation of pollution at the 825 Stewart
Drive site was initiated 1983 at the request of Board Staff. The
initial phase of investigation produced evidence of soil pollution
with a variety of volatile organic chemicals (VOCs). Investigation
at the site has focused on the location of an underground solvent
storage tank and acid neutralization system.
Additional soil work was completed in 1983 and initial groundwater
investigation began in July 1983. In addition to VOCs, metals were
detected in soil near the acid neutralization system. A more
comprehensive soil investigation was completed in 1988 to address
Page 23 of 108
-------
possible polluted soil that might still remain near the identified
point sources. All underground storage and treatment systems for
sol vents and acids have been removed and replaced with above ground
systems.
2.2
HISTORY OF SITE INVESTIGATIONS
Initial investigations at all three industrial sites were initiated
as a resul~ of an information questionnaire regarding underground
tanks. This questionnaire was mailed by the RWQCB to over 2000
industrial facilities in Santa Clara County as a follow-up to the
discovery of groundwater contamination at other sites in Santa
Clara County. .
The sites were proposed for inclusion on the National priority List
or Superfund list between 1984 and 1988. As required by Superfund
proposed final Remedial Investigation and Feasibility Study reports
(RI/FS) were submitted on behalf of AMD, TRW, and signetics (the
Companies) in January 1991. Final RI/FS reports were submitted in
March 1991. The Regional Water Quality control Board (RWQCB)
adopted an Order approving the joint RI/FS and a final Remedial
Action Plan that will encompass cleanup at the four Operable Units
including AMD, signe~ics, TRW Microwave and the offsite area.
2.2.1
AMD Operable Unit
Two possible sources of pollution have been identified at the AMD
901/902 OU. These include acid neutralization systems south of the
AMD 902 building and north of AMD 901 (Figure 8). Soil pollution
was the highest near the AMD 901 acid neutralization system. During
removal of the system, soil with up to 186,000 ~g/kg of
trichloroethylene (TCE) was excavated. Due to proximity of the
building not all of the polluted soil could be removed from the
southern portion of the excavation.
Additional investigation of source area soil was completed in 1988.
This investigation confirmed the presence of polluted soil beneath
the excavation for the acid neutralization system removed near the
AMD 901 building. The maximum concentrations detected in soil
include 242,000 ~g/l of 1,2-dichlorobenzene (DCB), 35,000 ~g/l of
tetrachloroethylene (PCE), 80,000 ~g/l of TCE, and 72 ~g/l of 1,1-
dichloroethylene (l,l-DCE). The estimated volume of soil remaining
in this area containing levels of total VOCs higner than 1 ppm is
37 cubic yards. .
An acid neutralization system was also removed from the vicinity of
AMD 902 in 1984. The maximum concentration of soil pollution
detected during the investigation of the neutralization system was
1200 ~g/kg of TCE, directly beneath the former tank location. No
other soil pOllution above 100 ~q/kq was detected during this
removal action. Based on analysis of soil following the excavation
and concent~ations of pollutants in groundwater in the area of the
Page 24 of 108
-------
excavation no additional investigation of the AMD 902 source area
was required.
2.2.2
Signetics Operable Unit
Initial investigation at the site began in February 1982 with the
detection of a leak in an underground waste solvent storage tank.
- The presence of contaminated soil was verif ied during the tank
removal. FOllowing additional investigation of the Signetics main
campus facility (440 Wolfe, 815 Arques, 830 Arques) the waste
solvent tank area has been identified as the principal source of
soil and groundwater contaminants on the Signetics eite.
Following the discovery of the leak in the waste solvent tank west
of the 811 E. Arques building a systematic review of potential
source area. was completed. Five possible source areas were
investigated in detail and a more wide ranging soil gas survey was
completed in an attempt to locate a possible unknown source. The
areas investigated include the former underground waste solvent
storage tank, the 440 Wolfe facility, Main Campus diesel tanks,
Main Campus wastewater neutralization tanks, and the former
location of wastewater neutralization tanks north of the 811 Arques
facility (Figure 9). In addition a soil gas survey was completed in
the vicinity of the 815 Stewart Drive building.
The results of these investigations have identified two probable
source areas of volatile organic chemicals (VOCs) within the
Signetics OU, the former underground waste solvent tank area and
the former 811 Arques wastewater neutralization tank area. Based on
the results of these investigations other source areas are not
anticipated.
2.2.3
TRW Operable Unit
As a result of responses to an information questionnaire regarding
underground tanks circulated by the RWQCB, investigation of
pollution at the 825 stewart Drive site was initiated in 1983 at
the request of Board Staff. The initial phase of investigation
produced evidence of soil pollution with a variety of volatile
organic chemicals (VOCs). Investigation at the site has focused on
the location of an underground solvent storage tank and acid
neutralization system (Figure 10).
Additional soil work was completed in 1983 and initial groundwater
investigation began in July 1983. In addition to VOCs, metals were
detected in soil near the acid neutralization system. A more
comprehensive soil investigation was completed in 1988 to address
possible polluted soil that might still remain near the identified
point sources. The excavation was expanded to the limits allowed by
the proximity of the building. This area was identified as a point
source for chemicals that resulted in groundwater pollution.
Page 25 of 108-
-------
Additional investigation was completed in 1988, as required under
RWQCB Order 88-015, since some contaminated soil was left in place
near the former location of the underground waste solvent storage
tank. The maximum concentration of total VOCs detected in the
vadose zone near the solvent storage tank was about 4 ppm. The
maximum concentration of total VOCs in saturated zone soil in this
area was approximately 34 ppm. Based on these estimates, and making
liberal assumptions regarding concentration and volume, it is
estimated that the vadose and saturated soils in this area contain
at most three pounds of TCE.
Soil investigation near an underground, acid neutralization system
(ANS) was also carried out during the closure of the system in
1986. Some soil samples contained elevated levels of metals,
however no elevated levels of VOCs were detected during this
investigation. This area is not considered a source area for
pollutants currently detected in the groundwater. Extraction tests
on soil from the ANS excavation area indicate that the inorgani~s
would not be expected to impact groundwater.
2.3
HISTORY OF ENFORCEMENT ACTIONS
The three industrial sites have been proposed or included on the
National Priorities List (NPL) and have been regulated by Regional
Board Orders as separate entities, as indicated herein:
2.3.1
AMD Operable Unit
a.
October 1984
site proposed for inclusion on
the National Priorities List
(NPL)
b. September 1985
c. June 1986
d. December 1987
e. April 1989
Waste
Adopted
Site formally added to the NPL
Discharge
Requirements
Site Cleanup Requirements Adopted
RWQCB Order .#89-56, Revised Site
Cleanup Requirements Adopted,
approving RIfFS workplan and
associated tasks,
f.
June 1991
RWQCB Order '91-102, Revised site
cleanup requirements, approving
the RIfFS and proposed plan
adopted.
Page 26 of 108
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2.3.2
Signetics Operable Unit
a.
April 16, 1983
b.
october 1984
c.
September 18, 1985
d.
December 16, 1987
e.
July 20, 1988
f.
April 1989
g. July 1989
h. october 1989
i. June 1991
2.3.3 TRW Operable Unit
a. June 1984
b. october 1985
c. January 1988
d. June 1988
Waste Discharge
Adopted,
Site proposed .for inclusion on
the National Priorities List
(NPL),
Requirements
Waste Discharge
Adopted,
Requirements
Si te Cleanup
Adopted,
Requirements
Waste Discharge Requirements
Adopted approving RX/FS workplan
and related tasks,
RWQCB Order #89-058 Revised Site
Cleanup Requirements Adopted,
approving RX/FS workplan and
related tasks.
Waste Discharge
Amended,
Requirements
EPA drops proposal to include
Signetics on the HPL,
RWQCB Order #91-104, Revised site
cleanup requirements, approving
the RX/FS and proposed plan
adopted.
Cleanup
Issued
and
Abatement
Order
Discharge
Requirements
Waste
Adopted
Si te Cleanup Requirements Adopted
Site proposed for inclusion on
the National Priorities List
(NPL) .
Page 27 of 108
-------
e.
April 1989
RWQCB Order #89-057 Revised site
Cleanup Requirements Adopted,
approving RIfFS workplan and
related tasks.
f. September 1989
g. February 1990
h. June 1991
Reissued Waste
Requirements Adopted
Site formally added to the NPL
Discharge
RWQCB Order #91-103, Revised site
cleanup requirements, approving.
the RIfFS and proposed plan
adopted.
3.0
COJDlt1HITY llELATIONS
3.1
community Involvement
An aggressive Community Relations program has been ongoing for all
Santa Clara Valley Superfund sites, including AMD 901/902,
Signetics and TRW Microwave. The Board published a notice in the
San Jose Mercury News on March 13, 20, and 27, 1991, announcing the
proposed final cleanup plan and opportunity for public comment at
the Board Hearing of March 20, 1991 in Oakland, and announcing the
opportunity for public comment at an evening public meeting to be
held at the Westinghouse Auditorium, Britton at East Duane Avenue,
in the City of Sunnyvale on Thursday March 28, 1991. Based on
community response the 30 day comment period from March 20, 1991
through April 19, 1991 was extended an additional 30 days through
May 20, 1991.
In response to comments received at the March 20, 1991 meeting, an
additional meeting was held in early May. The initial focus of this
meeting was on parents of children utilizing the San Miguel School
facilities. After further discussion with other community members
the focus of the meeting was broadened to include the surrounding
community. FOllowing this meeting several additional informal
meetings were held with community members and group~ during the
extended public comment period.
Additional comments regarding the proposed cleanup plan were
received at the RWQCB meeting June 19, 1991. These comments
emphasized citizens concern regarding vapor emission in the offsite
area and the impact of the Superfund status of the offsite area on
local property values.
3.2
Fact Sheets
Fact Sheets were mailed to interested residents, local government
officials, and media representatives. Fact Sheet 1, mailed in
Page 28 of 108
-------
December 1989, summarized the pOllution problem, the results of
investigations to date, and the interim remedial actions. Fact
Sheet 2, mailed in March 1991, described the cleanup alternatives
evaluated, explained the proposed final cleanup plan, announced
opportunities for public comment at the Board Hearing of March 20,
1991 in Oakland and the Public Meeting of March 28, 1991 in
Sunnyvale and described the availability of further information at
. the City of Sunnyvale Library and the Regional Board offices.
Fact Sheet 3, a summary and refinement of Fact Sheet 2, was hand
delivered to all residences in the offsite area in early May to
announce the May 7 meeting at the San Miguel School.. Fact Sheet 4
describing the final proposed plan and containing a summary of
responses to key communi ty issues was hand deli vered to all
residences in the offsite area and mailed to a 400 person mailing
list in early June.
c.o
SCOPE AND ROLE OF TBZ RESPONSE ACTIO.
4.1
SCOPE OF THE RESPONSE ACTION
The remedies selected and described in this ROD include the
existing interim remedial measures. The interim remedial measures
have included the removal of leaking underground tanks, acid
neutralization systems, and some contaminated soils, containment
and extraction of contaminated groundwater, and treatment of
extracted groundwater. The remedies selected and interim remedial
measures to date are explained by operable unit in the following
sections.
4.1.1
AMD Operable Unit
4.1.1.1
AMD Interim Remedial Measure
Onsite interim remedial actions began in 1983 with the removal of
the acid neutralization sump and about 103 cubic yards of soil at
AMD 901. Not all of the polluted soil was removed due to possible
structural damage to AMD 901. In 1984, the acid waste
neutralization sump and about 114 cubic yards of soil were removed
from the vicinity of Building 902.
Remediation of the groundwater began in 1984 with the installation
of two dewatering sumps and one extraction well to contain the
onsite pollution. One sump extracts water from the shallow A
Aquifer; the other two systems extract water from the B1 Aquifer.
Three additional extraction wells were installed in 1988 to enhance
the containment of the groundwater pollution in the B2 Aquifer.
The extracted groundwater is treated by an air stripper with vapor-
phase GAC emission control, and all of the effluent is reused as
process water at the AMD 901/902 facility. Figure 11 shows the
layout of the groundwater extraction and treatment system.
Page 29 of 108
-------
----..-. -..-- .-.
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. /I
SIGNUICS t.... , ,
8.. II
\\
\\ E EXPLANATION
"
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~... ,.so
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d (A - ,....)
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DeCUICMI IIIIIVI ow . .. ...
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Figure 11.
AMD 901/902 Groundwater Extraction System
-------
L_- -
4.1.1.2
AMD Selected Remedy
Excavation and offsi te treatment and disposal is the selected
remedy for the 37 cubic yards of contaminated soil that remains
beneath AMD Buildinq 901. The selected remedy for the AMD onsite
groundwater is the continuation of the present groundwater
extraction and treatment system involvinq air strippinq with carbon
adsorption of the offqas as permitted by the BAAQMD.
The treated qroundwater is currently reused as process water by the
manufacturinq facility. All industrial process water is discharqed
to the sanitary sewer, and thus indirectly to the publicly owned
treatment works (POTW). This discharqe is controlled by a permit
from the POTW and is subject to EPA pretreatment requlations. The
discharqe to surface water from the POTW is also controlled by an
NPDES permit. The POTW has operated within all limits set by the
NPDES permit.
The manufacturinq operation will be eliminated at the AMD 901/902.
facility in the near future and AMD has applied for an NPDES permit
for the discharqe of the treated effluent from the qroundwater
treatment system. No permit has been issued and discharqe limits
have not been established. It is probable that the discharqe limits
will be similar to those recently established tor the AMD 915
facility included in this ROD as Table 3. A deed restriction will
be included in the remedy to prohibit the installation of onsite
wells until the qroundwater remediation is completed.
4.1.2
Siqnetics Operable unit
4.1.2.1
Siqnetics Interim Remedial Measure
Contaminated soil has been removed from three separate locations,
an underqround solvent storaqe tank located west of the 811 E.
Arques buildinq, a waste water neutralization tank area, also north
of the 811 E. Arques buildinq, and soil removed durinq the
construction of the extraction trench at Siqnetics' 440 Wolfe
facility. Approximately 4,720 cubic yards of soil was removed from
the area of the waste solvent storaqe tank area in 1983. The
volume removed from the wastewater tank area is unknown, however,
based on analyses of soil from the excavation, it appears that all
soil above 1 ppm total VOCs was removed from this area. The soil
removed from the area of the 440 Wolfe trench is insiqniticant and
does not represent soil removal from a source area.
Previous soil investiqations have not documented a source area for
the elevated. levels of contaminants detected in wells north of the
811 Arques buildinq. Based on results of a 1988 soil vapor
extraction test, three additional vapor extraction wells were
installed in 1989 and the system continues to operate.
Siqnetics operates six separate qroundwater extraction systems in
paqe 31 of 108
-------
the vicinity of 811 E. Arques (Fiqure 12). In 1982, initial
extraction of groundwater in the A aquifer began shortly after the
discovery of pollution. This was accomplished with the basement
dewatering sumps surrounding the 440 Wolfe Building, downgradient
of 811 E. Arques. Similar systems also operate in the northern
portion of the 811 Building and the wastewater treatment building.
Three other extraction systems were designed and installed
specifically to contain polluted groundwater to the Signetics
property. . An extraction trench system was installed in the A
aquifer north of 440 Wolfe Road in 1984 and operation began in
1985. Operation of this trench has been continuous with the
exception of maintenance. Due to low water levels resulting from
the drought and long term groundwater withdrawal, the system has
been operating cyclically.
An extraction trench was installed in the A Aquifer north of the
811 E. Arques Building in 1984. The intent of this trench was to
intercept polluted groundwater that may have come in contact with
the polluted soil remaining in place at the 811 site. After an
initial period of effective recovery of polluted groundwater, this
trench became ineffective. This is again an effect of the low
water levels resulting from the current drought.
The third groundwater extraction system consists of a series of six
wells north of the Signetics facility at 815 E. Stewart Drive.
This system was intended to prevent further migration of polluted
groundwater downqradient to the north across the Signetics property
boundary. The system consists of three A Aquifer wells, one B1
Aquifer well, and two B2 Aquifer wells. Operation of this system
began in 1987 and, with the exception of downtime for maintenance
operation, has been continuous to date. Extraction rates from the
B2 Aquifer were increased in 1990.
All extracted groundwater is treated by a common treatment system
utilizing air stripping and carbon adsorption on air stripper
offgas and as final polish on the water. The treatment system is
located at the 440 Wolf Road Building. The treated groundwater is
currently lOOt reused as industrial process water or for nonpotable
uses. In the event of temporary plant shutdown the water will be
discharged to surface waters following treatment under an NPDES
discharg~ permit.
4.1.2.2
Siqnetics Selected Remedy
The selected remedy for the Siqnetics property combines soil and
groundwater cleanup measures and expands the existing interim
remedial measure's systems. Groundwater extraction from the A and
B Aquifers will be enhanced by the installation of some additional
extraction wells and an increased pumping rate at the 440 Wolf
extraction trench. The soil vapor extraction system will also be
Page 32 of 108
-------
'-
.-----
~
o
:c
o
c:
»
r ---..J-- Z ~
t.
l
(
a'''..
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=:--~ :':":"'- -...
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..... 48_-
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1=-'_- -..-
. - - ---- -:"".:' :.:=-
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--
Figure 12.
Signetics G .
Extracti roundwater
on System
-------
expanded by the addition of at least four-more vapor extraction
wells. The vacuum pumps and the carbon treatment units would be
expanded ta accommodate the additional wells. Deed restrictions
will prohibit the installation of drinking water wells until the
remediation is completed.
The discharge to _surface water is controlled by NPDES Permit No.
CA0028720. The limits for this discharge includes instantaneous
maximum limits for specific contaminants and limits for receiving
waters including pH, nitrogen and dissolved oxygen. This permit
includes limits for the discharge of two waste streams, one from a
reverse osmosis treatment system used in the manufacturing process
(Waste 1) and the other (Waste 2) the discharge from the
groundwater treatment system. The discharge limits were
established following EPA guidance and represent the best available
technology. A complete list of discharqe 11mi ts is included as
Table 1.
TABLE 1 - NPDES DISCHARGE LIMITS, SIGNETICS -
Waste 001
Constituent
Instantaneous
Maximum Limit
(mg/l)
Total dissolved solids
Chlorine
2000
0.0
Waste 002
Constituent
Instantaneous
Maximum Limit
(#£g/l)
Trichlorofluoromethane
1, 1, 1-trichloroethane
Tetrachloroethylene
Trichloroethylene
Ethylbenzene
Dichlorobenzene
1,1 Dichloroethylene
Xylenes
5
5
5
5
5
5
5
5
4.1.3
TRW Operable Unit
4.1.3.1
TRW Interim Remedial Measure
Interim actions to deal with soil pollution began in 1983 with the
removal of the underground waste sol vent storage tank and some
associated-polluted soil. Additional soil was removed from this
Page 34 of 108
-------
same area in 1984. All the polluted soil could not be removed due
to the proximity of the foundation of the 825 Stewart building to
the excavation. The total soil removed for oftsite disposal from
the solvent tank areas was 120 cubic yards. Soil pollution near
the waste solvent tank was investigated again in 1988 to determine
what levels of soil pollution remain in place near 825 Stewart.
The highest levels of soil pollution sampled in the unsaturated
-zone by this investigation were 4 ppm total VOCs. Levels of VOCs
found in the saturated zone were as high as 34 ppm.
Investigations in the area of the underground acid neutralization
system and its associated piping system were completea in 1985 and
1986. No VOCs were detected in either area, however some areas of
possible metals pollution were located.
Initial actions to deal with groundwater pollution at the TRW
operable unit began in 1984 with the installation of an eductor in
the waste solvent tank excavation. Additional extraction wells
were created in 1984 by the conversion of some existing monitoring
wells. Groundwater extraction currently involves seven extraction
wells, three A Zone wells, three B1 Aquifer wells, and one B2
extraction well (Figure 13).
The extracted groundwater is treated by an air stripping system at
the 825 Stewart site. Uncontrolled air emissions are currently
regulated by a BAAQMD permit for this site. After treatment, the
water is released to Calabazas creek under an NPDES permit.
4.1.3.2
TRW Selected Remedy
The selected remedy for the onsite plume at TRW consists of
continuing with the present groundwater extraction and air stripper
treatment system. It air emissions exceed those levels permitted
by the BAAQMD, air emissions control technology will be added to
the air stripper. Treated effluent will continue to be discharged
to Calabazas creek under an NPDES permit.
The discharge- to surface water is controlled by NPDES Permit No.
CA0028886. The limits for this discharge includes instantaneous
maximum limits for specific contaminants and limits for receiving
waters including pH, nitrogen and dissolved oxygen. The discharge
limits were established following EPA guidance and represent the
best available technology. A complete list of discharge limits is
included as Table 2.
Page 35 of 108
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AMD
927
AMD
925
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o
(f)
Q.
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'0
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DO S _.. -..-----...- - - -_. r .
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EXPLANA TION
o
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SIGNET/CS
8<18
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Figure 13.
Extraction System
TRW Groundwater
I" <'-'17
811 ,~
S/GNET/CS
830
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5-83
5-02
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-------
TABLE 2 - NPDES DISCHARGE LIMITS, TaW .
Constituent
Instantaneous
Maximum Limit
("g/l)
VOC's
Trichlorofluoromethane
1, 1, 1-trichloroethane
Tetrachloroethylene
Trichloroethylene
1,1 Dichloroethylene
vinyl Chloride
1,2-Dichloroethylene
Methylene Chloride
Total VOC's
5.0
5.0 .
4.0
5.0
5.0
0.5
6.0
5.0
25 . O.
AROMATICS
Ethylbenzene
Dichlorobenzene
xylenes
Total Petroleum
Hydrocarbons
5.0
5.0
5.0
50.0
METALS
Arsenic
Cadmium
Chromium (VI)
Copper
Cyanide
Lead
Mercury
Nickel
Silver
Zinc
20.0
10.0
11.0
20.0
25.0
5.6
1.0
7.1
2.3
58.0
1.
The pH of the discharge shall not exceed 8.5 nor be less
than 6.5.
2.
Toxicity: The survival of rainbow trout in 96-hour
bioassays of the effluent as discharged shall be a median
of 90' survival and a 90 percentile value of not less
than 70'
'The total. VOC limit is the sum of all EPA 601 compounds.
Page 37 of 108
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4.1.4
Offsite Operable Unit
4.1.4.1
Offsite Interim Remedial Measure
Two offsite groundwater containment extraction systems have been
. installed (Figure 14). The Duane Avenue Extraction system,
consisting of nine extraction wells, is located just south of Duane
Avenue, approximately 1200 to 2100 feet downqradient (north) of
AMD, Siqnetics, and TRW facilities. This extraction system was
installed and began operation in 1986. The Duane Avenue system
extracts water from the A, B1, B2, B3, and B4 Aquifers.
A second extraction system consisting of fourteen wells, along
Alvarado Avenue, approximately 2700 to 4300 feet downqradient
(north) of the AMD, Siqnetics and TRW facilities, was completed in
1988. operation of the Alvarado Avenue system began in October
1988. This system extracts water from the A, B1 and B2 Aquifers.
All extracted groundwater is transferred by a piping system to the
AMD 915 DeGuiqne facility where the water is treated by an air
stripper followed by a liquid-phase GAC polisher. About 30% of the
treated water is used as process make-up water by the AMD 915
facility and the remainder is released to a storm drain tributary
to Calabazas creek under an NPDES permit. Uncontrolled air
emissions are currently requlated by a BAAQMD permit.
4.1.4.2
Offsite Selected Remedy
The selected remedy for the offsite commingled plume involves the
expansion of the current extraction system with some additional
wells and a continuation of the current air stripper treatment
system. The air stripper will include air emissions control if
emissions exceed levels permitted by the BAAQMD. Treated effluent
will continue to be reused as much as possible with the balance
being released to Calabazas Creek under an NPDES permit.
The discharge to surface water is controlled by NPDES Permit No.
CA0028797. The limits for this discharge includes instantaneous
maximum limits for specific contaminants and limits for receiving
waters including pH, nitrogen and dissolved' oxygen. The discharge
limits were established following EPA quidance and represent the
best available technoloqy. A complete list of discharge limits is
included~as Table 3.
Page 38 of 108
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~ COll3881
~IUIA
COIMS81 t
~
~
<
~
~
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~ COII181
~EL:A~ I
1
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. 400
SCALE IN FEET
800
N
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EXPLANATION
COIIIA
~A~
.. .. COIIIA
CX)II1;:.J I LCOIII81
COII1OA:J
~CO"8Z
COI8IM
COIIIIS
COIl1I1Z .
&1racdan WeD
\.NCE HAVEN ORNE
/
Fiqure 14.
Offsite Groundwater Extraction System
-------
TABLE 3 -NPDES DISCHARGE LIMITS, OFFSITE
Constituent
Instantaneous.
Maximum Limit
(pg/l)
VOC's
Trichlorofluoromethane
1,1,1-trichloroethane
Tetrachloroethylene
Trichloroethylene
1,1 Dichloroethylene
Vinyl Chloride
cis-1,2-DichloroethYlene
trans-1,2-Dichloroethylene
Methylene Chloride
Total VOC's
AROMATICS
Ethylbenzene
Dichlorobenzene
Trichlorobenzene
Xylenes
Total Petroleum Hydrocarbons
INORGANICS
Arsenic
Cadmium
Chromium (VI)
Copper
Cyanide
Lead
Mercury
Nickel
Silver
Zinc
..~..
. ..
.'...
~otal of constituents for EPA 601 analytes
Page 40 of 108 .
5.0
5.0
5.0
5.0
.5.0
0.5
5.0
5.0
5.0
10.02
5.0
5.0
5.0
5.0
50.0
20.0
10.0
11.0
20.0
25.0
5.6
1.0
7.1
2.3
58.0
-------
4.2
ROLE OF THE RESPONSE ACTION
The purpose of the actions at AMD/Siqnetics/TRW is to control the
migration of polluted groundwater from the sites and to capture and
remediate existinq contaminated groundwater. The intent of these
actions is to expedite cleanup of groundwater at these sites and to
- prevent further movement of contaminated groundwater downgradient
and potential vertical migration into aquifers that currently serve
as drinkinq water sources.
The IRKs for groundwater have contained the groundwater
contamination plume to the sites and greatly limited the leadinq
edqe in the offsite area. Vertical migration has been limited and
the toxicity, mobility, and volume of contaminants have been
reduced. The final qoal of this response action is to allow the
future use of the shallow groundwater as a possible source of
drinkinq water.
5.0
SUMMARY OF SITE CHARACTERISTICS
5.1
SOURCES OF CONT~NATION
5.1.1
AMD Source Investiqation
Two possible sources of pollution have been identified at the AMD
901/902 OU. These include acid neutralization systems south of the
AND 902 buildinq and north of AMD 901 (Fiqure 8). Additional
investiqation of source area soil was completed in 1988. This
investiqation confirmed the presence of polluted soil beneath the
excavation for the acid neutralization system removed near the AMD
901 buildinq. The maximum concentrations detected in soil include
242,000 ~q/l of 1,2-dichlorobenzene (DCB), 35,000 ~q/l of
tetrachloroethylene (PCE), 80,000 ~q/l of TCE, and 72 ~q/l of 1,1-
dichloroethylene (l,l-DCE). The estimated volume of soil remaining
in this area containing levels of total VOCs higher than 1 ppm is
37 cubic yards.
An acid neutralization system was also removed from the vicinity of
AND 902 in 1984. The maximum concentration of soil pOllution
detected during the investigation of the neutralization system was
1200 ~g/kg of TCE, directly beneath the former tank location. No
other soil pollution above 100 ~g/kg was detected during this
removal action. Based on analysis of soil following the excavation
and concentrations of pollutants in groundwater in the area of the
excavation no additional investigation of the AMD 902 source area
was required.
A soil gas survey was completed around the AMD 901/902 buildings in
October 1989 to estimate the possible extent of soil contamination
and to attempt to locate any undocumented source areas. TCE was the
predominant contaminant in vadose zone soil gas ranging as a high
Page 41 of 108
-------
as 350 ~g/l and averaging 63 ~g/l in 19 out of 20 sample locations.
The distribution of soil gas contamination was not indicative of
additional source areas.
5.1.2
Signetics Source Investigation
Following the discovery of the leak in the-waste solvent tank west
of the 811 E. Arques building a systematic review of potential
source areas was completed. Fi ve possible source areas were
investigated in detail and a more wide ranging soil gas survey was
completed in an attempt to locate a possible unknown source. The
areas investigated include the former underqround 'waste solvent
storage tank, "the 440 Wolfe facility, Main Campus diesel tanks,
Main Campus wastewater neutralization tanks, and the former
location of wastewater neutralization tanks north of the 811 Arques
facili ty. In addition a soil gas survey was completed in the
vicinity of the 815 Stewart Drive building.
The results of these investigations have identified two probable
source areas of volatile organic chemicals (VOCs) within the
Siqnetics OU, the former underqround waste solvent tank area and
the former 811 Arques wastewater neutralization tank area (Figure
9). Based on the results of these investigations other source areas
are not anticipated.
5.1.3
TRW Source Investigation
Two possible sources of pollution have been identified at TRW.
These include an acid neutralization system and an underground
solvent storage tank area (Figure 10). Initial soil pollution
investigations focused on the area near the underqround solvent
waste storage tank in 1983. Additional soil samples were collected
in July of 1984; the soil in these samples contained a variety of
VOCs including trichloroethylene (TCE), tetrachloroethylene (PCE),
and 1,2-dichloroethylene (1,2-DCE). The waste solvent storage tank
and some associated 80il was removed in 1983. Additional soil
removal was completed in 1984. The excavation was expanded to the
limits allowed by the proximity of the building. This area was
identified as a point source for chemicals that resul ted in
qroundwater pollution.
_.
Additional~ investigation was completed in 1988, as required under
RWQCB Order 88-015, since some contaminated soil was left in place
near the former location of the underqround waste solvent storage
tank. The maximum concentration of total VOCs detected in the
vadose zone near the solvent storage tank was about 4 ppm.
Page 42 of 108
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5.2
DESCRIPTION OF CONTAMINATION
5.2.1
SOIL INVESTIGATIONS
5.2.1.1
AHD Operable unit
. Soil pollution was the highest near the AHD 901 acid neutralization
system. During removal of the system, soil with up to 186,000 ~g/kg
of trichloroethylene (TCE) was excavated. Due to proximity of the
building not all of the polluted soil could be removed from the
southern portion of the excavation. .
An acid neutralization system was also removed from the vicinity of
AHD 902 in 1984. The maximum concentration of soil pollution
detected during the investigation of the neutralization system was
1200 ~g/kg of TCE, directly beneath the former tank location. No
other soil pollution above 100 ~g/kg was detected during this
removal action. Based on analysis of soil following the excavation.
and concentrations of pollutants in qroundwater in the area of the
excavation no additional investigation of the AMD 902 source area
was required.
5.2.1.2
Siqnetics Operable Unit
Initial investigation of soil pollution began in 1982 following the
report of a leak in an underground solvent storage tank. Analyses
of soil samples from this initial phase of investigation indicated
that onsite soil was polluted with up to 8100 ppb TCE, 16,400 ppb
l-,l-,l-trichloroethane (TCA), 18,100 ppb xylene, and 79,000 ppb
butyl acetate.
Soil samples were collected from the base of the excavation at
various times in 1982. This follow-up investigation of polluted
soil remaining in place after the removal of the solvent storage
tank detected a variety of organic solvents. The greatest
concentrations detected were for TCE at 63,000 ppb, TCA at
1,700,000 ppb and PCE at 1,000,000 ppb.
The initial tank excavation was utilized as part of a larger
excavation for the installation of a new subsurface wastewater
treatment plant. Prior to beginning the larger excavation, a series
of borings was made throughout the planned excavation area. The
borings extended through the vadose zone into the saturated zone at
depths of 18 to 19.5 feet. Several soil "hotspots" were identified.
The maximum contamination that was detected was in boringS-54 with
6,700 ppb of TCE, 12,000 ppb of TCA, and 23,000 ppb of PCE. The
excavation removed soil into the saturated zone, at a depth of
about 20 feet. Based on the analysis of soil samples from the
borings this excavation should have removed all vadose zone soil
containing VOCs qreater than 1 ppm total VOCs. However, based on
the absence of verification samples from the construction
Page 43 of 108
-------
excavation, additional A zone groundwater monitor wells were
installed in 1989 downgradient of the excavation. Low levels of
VOCs (19 ppb TCE) have been detected in these wells. These levels
are probably ~ot indicative of remaining soil contamination in this
area.
5.2.1.3
TaW Operable Unit
Initial soil pollution investigations focused on the area near the
underground solvent waste storage tank in 1983. Additional soil
samples were collected in July of 1984; the soi1 in these samples
contained a variety of VOCs including trichloroetl;1ylene (TCE),
tetrachloroethylene (PCE), and 1,2-dichloroethylene (1,2-DCE). The
waste solvent storage tank and some associated soil was removed in
1983. Additional soil removal was completed in 1984. The
excavation was expanded to the limits allowed by the proximity of
the building. This area was identified as a point source for
chemicals that resulted in groundwater pollution.
Additional investigation was completed in 1988, as required under
RWQCB Order 88-015, since some contaminated soil was left in place
near the former location of the underground waste solvent storage
tank. The maximum concentration of total VOCs detected in the
vadose zone near the solvent storage tank was about 4 ppm. The
maximum concentration of total VOCs in saturated zone soil in this
area was approximately 34 ppm. Based on these estimates, and making
liberal assumptions regarding concentration and volume, it is
estimated that the vadose and saturated soils in this area contain
at most three pounds of TCE.
Soil investigation near an underground, acid neutralization system
(ANS) was also carried out during the closure of the system in
1986. Some soil samples contained elevated levels of metals,
however no elevated levels of VOCs were detected during this
investigation. This area is not considered a source area for
pollutants currently detected in the groundwater. Extraction tests
on soil from the ANS excavation area indicate that the inorganics
would not be expected to impact groundwater.
The remaining soil contamination is minimal and occurs at depths
greater than ten feet. The maximum vadose zone contamination is
about 4 ppm. With current technoloqy it is not possible to separate
the higher levels of soil contamination in the saturated zone soil
from the groundwater contamination. However the remaining soil
contamination does not present any known impacts that will not be
remediated by the groundwater extraction system.
Page 44 of 108
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5.2.2
GROUNDWATER INVESTIGATIONS
5.2.2.1
AMD Operable Unit
The initial qroundwater monitor wells were installed in 1983
followinq the excavation of the AMD 901 ANS. Additional wells have
been installed each year throuqh 1989. CUrrently there are 30
monitorinq wells and 6 extraction wells at the AMD 901/902 site.
. Samplinq of the AMD 901/902 well field was monthly from March 1985
throuqh February 1986, and bimonthly until 1988. The sample plan
has called for quarterly monitorinq of selected wells since 1988.
Based on'this qroundwater data TCE is the most common pollutant and
has been used as an indicator for qroundwater pollution at AMD
901/902. Initial levels of qroundwater pollution at this site were
as hiqh as 100 ppm of TCE with total VOCs as hiqh as 1000 ppm prior
to the point source removal in 1983. The hiqhest current levels of
qroundwater pollution are about 1 ppm TCE for the onsite area.
currently the onsite pollution extends to a depth of up to 65 feet.
5.2.2.2
Signetics Operable Unit
Groundwater pollution by VOCs was detected durinq the initial
investiqation in 1982. Monitorinq has been continuous for selected
wells on at least a quarterly basis since 1982.. Groundwater
pollution has spread throuqh the upper four aquifers. Additional
wells were installed in 1989 to provide additional characterization
of the extent of vertical pollution. The total number of monitor
wells installed in five water bearinq zones at the Siqnetics OU is
96. The downqradient and lateral extent of contamination of
qroundwater contamination at the Siqnetics OU is difficult to
quantify due to the comminqlinq both laterally and downqradient.
The hiqhest initial concentrations of TCE detected in the A aquifer
was 34,000 ~q/l in 1982 in well S049A. The hiqhest concentration
of TCE in the A aquifer in October 1990 was 22,000 ~q/l in well
S091A with qroundwater from well S049A containinq 12,000 ~q/l TCE.
The concentration in well S091A is an historic low for TCE in
qroundwater from that well.
The hiqhest initial concentration of TCE in the B1 aquifer was 2600
~q/l in 1982 in well S04881 and 25,000 ~q/l in 1983 in well S07581.
currently the hiqhest concentration of TCE in- the 81 aquifer is
20,000 ~q/l at well S065B1. The hiqhest concentration of TCE in
the 82 aquifer was 13,000 ~q/l at well S04882 in 1986, 20,000 ~q/l
in 1988, and 8800 ~q/l at the same well. The hiqhest initial
concentration of TCE in the B3 aquifer was 25,000 ~q/l of TCE in
well S10183 in 1986. CUrrently the hiqhest concentration of TCE in
the B3 is 740 ~q/l, also measured in well S10183. The maximum
concentration in October 1990 in an onsite B4 aquifer well at 811
E. Arques was 13 ~q/l. This is the first occurrence of a chemical
of concern above drinkinq water standards in an onsite B-4 aquifer
paqe 45 of. lOB
-------
well.
The current volume of contaminated groundwater in the A aquifer is
estimated to be 1,3'53,600 cubic feet (10,125,631 qallons) and
10,516,500 cubic feet (78,668,883 qallons) in the B aquifer. This
estimate is based on the surface area of the Siqnetics OU and
average saturated thicknesses for the individual aquifer zones.
5.2.2.3
TRW Operable Unit
The initial groundwater monitor wells were installed at this site
by TRW in 1983, with additional wells installed in ~984, 1986 and
1989. There are twenty-five monitoring wells located within the TRW
operable unit. This includes wells installed by AMD and Signetics
as part of the RI. Monitoring of water levels and contamination has
been carried out on at least a quarterly basis for selected wells
since at least 1986. Based on this data the dominant VOC in the
groundwater is TCE, although l,2-DCE, Freon 113, and PCE are also
frequently detected.
The highest initial levels of TCE in the groundwater were detected
in well T-2A. The highest concentrations of VOCs in the A aquifer
in 1990 were measured in groundwater from wells T-9A and T-7A (see
Appendix 1, fiqure 4), with the most recent concentrations being
approximately 2,300 and 1,700 p.q / 1, respectively. Contaminant
concentrations in these wells may be influenced by migration from
offsite sources. Therefore these wells may not be representative of
A zone contamination at the TRW OU. Well T-2A (Fiqure 13), an
extraction well downgradient of the source area, detected about 100
p.g/l of TCE and 200 p.q/l of total VOCs in the October 1990
samplinq. Groundwater pollution in the deeper aquifers was
originally the most concentrated in well T-2B. currently the
highest TCE concentration in onsite wells is in well T-2B an
extraction well in aquifer Bl, with a concentration of 19,000 p.q/l.
High levels of vinyl chloride (7800 p.q/l) are also detected in well
T-2B.
5.2.2.4
Offsite Operable Unit
It was determined in 1984 that groundwater pollution had migrated
north, downgradient from point sources at TRW (FEI) Microwave, 825
Stewart, and Siqnetics 811 Arques facilities. Initial investigation
began in September 1984. Several phases of investiqation including
two soil gas surveys and the installation of 83 monitor wells, 23
extraction wells, and 22 piezometers. Additional pilot and soil
borings were also completed.
Offsite the pollution extends downgradient to the north for
approximately 4000 feet and to a maximum lateral extent of about
1600 feet. Contaminants have been detected to a depth of up to 100
feet in the B4 zone. Additional monitor wells will be required at
the distal edge of the plume to define the current extent of the
Page 46 of 108
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contamination plume. The pattern of vertical contamination
generally represents the standard model for contaminants that are
heavier than water, in that the depth of contamination increases
wi th distance from the source area.
The current volume of contaminated groundwater in the A aquifer in
the Offsite OU is estimated to be 1,490,600 cubic feet (11,145,974
gallons) and 41,140,000 cubic feet (307,748,571 gallons) in the B
. aquifer. This estimate is based on the surface area of the Offsite
OU and average saturated thicknesses for the individual aquifer
zones.
5.2.3
AIR INVESTIGATIONS
5.2.3.1
AMD 901/902 Operable Unit
As part ot the interim remedial action tor groundwater, an air
stripper is in place at the AHD 901/902 OU. This air stripper has
a carbon unit tiltering the air effluent. current air emissions are
very limited and approximately 4.6 X 10~ pounds per day of TCE is
released into the ambient air. In reviewing the original permit
application in 1985 the BAAQMD estimated the risk related to the
chemical releases trom the AMD air stripper to be 1.6 X 10~. It is
unclear if this evaluation was made with the activated carbon
treatment ot the air effluent in place. What is certain is that
effluent concentration has declined since the original permit to
operate was issued in 1986. This decline would result in decreased
emission from the air stripper with an attendant decrease in risk.
The spent carbon is removed for offsite treatment and disposal.
Volatilization of groundwater contaminants from the subsurface was
not investigated for the AHD 901/902 OU since no current
residential property exists above or adjacent to the plume within
this operable unit. The site is completely paved or covered by
structures with active ventilation systems. The paving may limit
the migration of contaminants and. the active ventilation systems
will limit the concentration of contaminants in indoor air. A
review of this exposure pathway will be conducted to determine the
impact on future potential residents at the five year review
period.
Consideration ot worker safety in the 901 facility due to the
possible off-gassing of VOCs from contaminated soil beneath the AMD
901 building was investigated due to agency comments (Appendix A).
This was not part of the RI/FS and these concerns are considered
more appropriate for requlation and evaluation by California
Occupational Health and Safety Association (CAL-OSHA).
Modeling that was done to estimate migration of vapors from
groundwater in the offsite OU would not apply to exposures in the
901 facility for several reasons. The model assumes that the
Page 47 of 108
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structure has a basement, crawl space, or a perimeter crack to
allow infiltration of the vapors. The AMD 901 is constructed on a
concrete slab and no extensive cracking of the slab has been
observed. Another component of the model is that 100' infiltration
is assumed and a limited number of air exchanges per hour occurs in
the average home. These two factors are major components in the
process of releases of contaminants from soil possibly getting
trapped and concentrated in indoor air.
As part o~ the facility operation all areas of the building have
active ventilation systems which result in a greatly increased air
exchange rates and positive pressure. The active ventilation would
result in the removal of contaminants as they enter the indoor
space and the positive pressure would reduce the infiltration rate.
These two factors in combination would act to limit the possibility
of the vapors entering or becoming concentrated in indoor air in aO
semiconductor manufacturing facility. Active ventilation systems,
sealing of slabs or below ground portions of structure, and
maintenance of positive pressure are major components of systems
designed for remediation of indoor air contamination.
In response to agency concern AMD sampled air in the interior of
the 901 facility with a photoionization detector (PID). PIDs are
not chemical specific, in that they will not indicate what chemical
is being detected, only an approximate concentration of chemicals
in vapor. The detection limit for this method is between 0.5 part
per million (ppm) and 1 ppm. All readings were below the detection
limit. To confirm these results summa canisters of indoor and
outdoor ambient air were collected and analyzed. These results
indicate that the chemicals present at high concentrations in the
contaminated soil, 1, 1-Dichloroethylene (DCE), Trichlorethylene
(TCE), Tetrachloroethylene (PCE) and Dichlorobenzene (DCB), are not
present above 0.25 part per billion (ppb). The worker safety
regulations include allowable exposure for these chemicals from 25
to 200 ppm. These above factors all contribute to the conclusion
that worker exposure to indoor air contaminated by vapors migrating
from contaminated soil is not a significant risk at the AMD 901
facility.
5.2.3.2
Siqnetics Operable Unit
As part of the interim remedial action for groundwater three air
stripper. are in place at the Signetics OU. The air strippers are
operated in sequence with the total flow being fed to one large
diameter stripping tower, the water is then captured and the volume
is split between the two remaining towers. The first air stripper
in the sequence has two parallel lines of eleven 150-pound drums of
granular activated carbon. It is estimated that the primary air
stripper removes about 99' of the total VOCs in the influent. The
vapor phase carbon system reduces air emission risk by over 90%.
The second set of air strippers reduces the remaining l' of the
VOCs by an additional 88' to about 1 ~g/l in the treated
Page 48 of 108
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groundwater effluent. Under regulation of a BAAQMD permit to
operate, the air stripper system is limited to a maximum release of
0.52 pounds per day of VOCs to the atmosphere. The spent vapor
phase carbon is removed for offsite treatment and .disposal.
The risk related to this release from the air strippers was
evaluated after the completion of the FS. This risk was evaluated
using a screening level model. The maximum concentration predicted
. by the model was 0.434 p.g/1. This would result in an estimated
increased cancer risk of approximately 1 X 10~. Non-carcinogenic
effects were also evaluated tor this release and none would be
predicted from the exposure to the maximum concentrations resulting
from the air stripper discharge. .
Volatilization of groundwater contaminants from the subsurface was
not investigated tor the Signetics OU since no current residential
property exists above or adjacent to the plume within this operable
unit. The site is completely paved or covered by structures with
active ventilation systems. The paving may limit the migration of
contaminants and the acti ve ventilation systems will limi t the
concentration of contaminants in indoor air. A review of this
exposure pathway will be conducted to determine the impact on
future potential residents at the five year review period.
5.2.3.3
TRW Operable Unit
As part of the interim remedial action for groundwater an air
stripper is in place at the TRW OU. The air stripper air effluent
is uncontrolled, however due to the combination of low groundwater
effluent conc~ntration and low extraction rate, the air emissions
from the air stripper are limited. It is estimated that the air
stripper releases about 0.84 pounds of VOCs per day. About 90% of
this total discharge is TCE. This release of contaminant is
regulated and permitted by the BAAQMD, however the BAAQMD did not
require risk screening at the time this permit to operate was
issued (1985). Evaluation of the risk included in the FS predicts
that the maximum concentration of VOCs released by the air stripper
at the TRW operable unit is 9.24 X 10.3 mg/m3. Since TCE is a
carcinogen and is the dominant chemical in the stripper influent
and stripper air emissions, the cancer risk related to this air
discharge was evaluated for TCE. The maximum concentration as
estimated by the model would occur at 0.191 kilometers from the air
stripper. Assuming that an individual was exposed to this
concentration for a period of thirty years would result in an
excess cancer risk estimate for this air emissions of 1.79 X 10.s.
5.2.3.4
Offsite Operable Unit
As part of the interim remedial action for groundwater in the
Page 49 of 108 .
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offsite area groundwater is extracted and piped for treatment to
the Advanced Micro Devices facility at 915 DeGuigne Drive in
Sunnyvale. The groundwater is treated by an air stripper followed
by aqueous phase granular activated carbon. The air effluent from
the air stripper is uncontrolled. It was estimated in the FS that
the air stripper releases about one and one-half pounds per day of
VOCs to the ambient air. The release from this air stripper system
was re-evaluated in September 1991. The influent volume and
concentration had declined. Mass balance estimates based on the
current flow rate and concentration indicate that VOC emission has
declined ~o about 300 pounds per year or 0.82 pounds per day. Based
on a model prepared by the California Air Pollution Control
Officers Association the risk related to this release is less than.
1 X 10~. This release of contaminant is regulated and permitted by
the BAAQMD.
The baseline public health evaluation indicated that volatilization
of chemicals from groundwater could reach the surface. The risk
from this exposure pathway was evaluated based an modeling of the
transport of VOCs from groundwater through' soil to the surface and
eventually entering residential buildings through cracks in
concrete slabs. This evaluation predicted a possible excess cancer
risk of 1 X 10~.
Although the predicted risk was within the risk range allowed by
the NCP it was determined that additional investigation of this
pathway was warranted. The decision to proceed with additional data
collection was based on several considerations; this was the only
current pathway that had a high probability of being complete, the
groundwater plume is beneath a residential area including a child
care facility (San Miguel School), and modeling of vapor transport
is poorly developed and relatively speculative.
Additional data was collected through the use of a field flux
chamber. This provides a measure of the qross emission rate for a
known surface area of soil. The intent using this measurement
technique was to eliminate the modeling of vapor transport in the
vadose zone from the estimate. This would still require the
estimation of infiltration rate into structures and the fate of the
contaminants upon entering a structure. The other option considered
was the direct measurement of indoor air from' selected structures.
This approach was rejected due to a lack of sampling protocol for
indoor air and the possible contamination of indoor air by indoor
sources.
Three sampling events for field flux measurements have occurred.
Two separate transects across the known groundwater plume were
included in the field sampling (Fiqure 15). One transect was in the
near source area in open fields. The second transect was near the
San Miguel School. The first transect was intended to provide a
"worst case" estimate of the field flux rate since it crossed the
groundwater plume where concentrations were the highest. The second
transect was intended to be representative of the flux rate in the
residential area.
Page 50 of 108
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Figure 15.
Soil Flux Sample Location Map
-------
Field flux data has measured very low concentrations of VOC's. The
scenario was not as expected, in that TCE has been detected in the
offsite area and not in the near source area. Vinyl chloride was
detected in one of three sampling events at location 6 (Figure 15)
in the near source area. TCE has been detected in one sample
(location 9) from the offsi te area in two sample events and at
location 8 in the most recent sampling. Other chemicals, most
notably 1,1,1-TCA and Freon 113, are frequently detected in soil
flux gas. samples. Correlation between the occurrence of these
chemicals and groundwater is difficult since these chemicals do not
occur frequently or at high concentrations in .groundwater.
The possible exposure to chemicals as a result of air emissions
from groundwater will be evaluated as part of the five year review
for all four operable units (TaW (FEI) Microwave, Siqnetics, AMD
901/902 and the associated offsite operable unit). This is a
relatively new exposure scenario and assumptions related to this
pathway are not well established. In addition, appropriate field
sampling methodologies are not well established'. It is anticipated
that additional data and techniques will be available at the five
year review.
1.0
SUMMARY OP SITB RISES
6.1
TOXICITY ASSESSMENT
A baseline public health evaluation (BPHE) is completed for every
Superfund si te. As part of this assessment the occurrence of
chemicals at a site is investigated to identify those chemicals
whose occurrence and toxicity should be considered in the cleanup
of the site. Groundwater data collected after 1988 and all shallow
soil data was utilized in this evaluation. The BPHE did not
consider the groundwater data on the basis of operable unit where
the data was collected. Rather, since the groundwater is connected
throughout the operable units, geometric mean and maximum
concentration data was applied to the overall site regardless of
location of occurrence.
Based on very conservative assumptions regarding concentration,
distribution, toxicity, analytical data, and potential routes of
exposure, the BPHE for these three combined sites identified
twenty-eight "chemicals of potential concern" (Table 4) from this
database. This included seventeen organic chemicals and eleven
inorganic chemicals. The assignment of a chemical as a carcinogen
in Table 4 is based on its classification as a carcinogen by an EPA
Carcinogen Risk Assessment Verification Endeavor (CRAVE) workshop.
In addition to the criteria outlined above some of the 28 chemicals
were included based on detection in soil and mobility in the
environment though they have never been detected in groundwater.
Page 52 of 108 .
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GROUNDWATER SOIL
CM81cal ClAY! Max Valu. .et/lAnal Max Velu. .et/lAnel
(aall) (aa/ka)
Anti8IIIW 120 6113 12 3/6
Arsenic A 40 1/13 4.6 416
"rl~ D 100 215 300 6/6
lentene A liS IIA 4000 115
C8181~ 11 38 4113 6.9 411
Chlol'Dfona 12 140 12/316 1 3114
Ch...II8lTotal' A' 160 1/13 59 11/11
CocD8r D '" 1/13 190 111
'2-Dlchlorab8n%ene 0 .. DO ... 11176 240 000 "114
1~1.D'cIttoro.tII... .. 12 600 . 251556 IS ... IIA
1 1-Dfchlol"Oetll- C 740 . . 491556 IS MA.
cla-l 2-Dlchlor08thene D 8DOO 1041154 460 11114
t....-l ~Z-.. D 1800 11/154 73 .. 1/14
D ic:hlor08th-
Ethvlbenzene D liS IIA 2 DOO 115
'NOn 113 D 78 000 2091556 II U
Leed 12 110 8113 66 511
Methvlene Chloride 12 520 1116 26 4110
IIlckel D 280 9/13 250 1n
SII".r D 24 3113 liS IIA
Tetndlloroedlene 12 610 881670 35 ,ODD 11131
Thalll~ D 160 8113 3.8 216
Tol- D 115 IIA 3 000 115
1 1.1-Trichloroethane 0 1 .000 144/670 liS IIA
Trlchloroethen8 12 290, DOO 6181670 80 000 23131
Trichlorofluoraaethane D 1.2 41126 liS IIA
VinYl Chlorf. A 32,000 67/670 lID 015
Xvi.... D III IIA 4000 115
Zinc E 1,100 10113 61 711
TABLE 4
AMD 901, SIGNETICS, TRW DATA SUMMARY
liS . lIot S8Ipled
NA . lIot Applicable -
A . (r\OW'I H~ CarclftOl8N
11 . Prob8ble II~ Carclnoeen (l I.had ,,~ 8'Vldlnee, ~te 8'Vld8nce frC18 ani_Is)
12 . Prob8ble II~ Carcinogen (I~te ,,~ wld8nce, ~te 8'Vld8nce fl'C18 ani_Is)
C . POlllble II..." Carcinogen (ll.ited 8'Vld8nce of carcinogenicity, anl_l stYliI.. only)
D . Not Cl..alfied .. to tI~ Cal'cinoeenicity (i~t8 ani_l and h~ data or no data)
E . Not a II~ Carcinogen (~te 8'VId8nc8 of non-carcinogenicity In ~te ani-l or h~ studi..)
, Chromium VI inhalation only
paqe S3 of 108
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As part of risk manaqement, further evaluation of the qroundwater
data in the FS has resul ted in the reduction of the number of
orqanic chemicals to ten chemicals of concern. All of the
"inorqanics were removed from the list of chemicals of concern based
on additional qroundwater samplinq that was not available when the
BPHE was completed and the fact that some of the inorqanics
detected in soil were not used as part of the process at the
operable unit where the BPHE included the inorqanics as chemical of
concern.
.
This final list of "chemicals of concern" includes (shaded in Table
4) 1,2-Dichlorobenzene (1,2-DCB), 1,1-Dichloroethane (l,l-DCA),
1,1-Dichloroethylene (l,l-DCE), cis-1,2-Dichloroethylene (CiS-1,2-
DCE), tranS-1,2-Dichloroethylene (trans-1,2-DCE), Freon 113,
Tetrachloroethylene (PCE), 1,1,1-Trichloroethane (l,l,l-TCA), TCE,
and vinyl chloride.
The rational for selectinq these remaininq ten chemicals as
chemicals of concern is as follows:
1.
1,1-Dichloroethane (l,l-DCA), 1,1-Dichloroethylene (l,l-DCE),
Tetrachloroethylene (PCE), and TCE are probable or possible
human carcinoqens.
2.
1,2-DCB, Freon 113, PCE, 1,1,1-TCA TCE and Vinyl Chloride are
detected in qroundwater at a qreater than 10' frequency.
3.
1,1-DCA, 1,1-DCE, cis-1,2-DCE, and trans-1,2-DCE, are detected
in more than S, of qroundwater samples or are breakdown
products of one of the other chemicals of concern and
therefore miqht reasonably be expected to occur in increased
frequency, distribution or concentration.
1,1-DCA, 1,1-DCE, ciS-1,2-DCE, trans-1,2-DCE, Freon 113, PCE,
1,1,1-TCA, TCE, and vinyl chloride possess physicochemical
properties (relatively hiqh water solubility and relatively
low soil sorption) which promote their dispersion in
qroundwater. In addition all of these chemicals are volatile
and can easily be dispersed into soil qas and possibly the
atmosphere.
4.
S.
1,2-DCB, 1,1-DCE, Freon 113, PCE, 1,1,1-TCA, and TCE, have
been used on site as part of the manufacturinq process. Soil
samplinq has documented the presence of most of these
chemicals as contaminants in soil from source area
excavations.
6.
TCE has been used as an indicator chemical throuqhout the
study area. This is based on the reasons stated above. TCE is
also the chemical most frequently detected in soil and
qroundwater. TCE has been detected in qroundwater at the
qreatest concentration of any of the chemicals of concern, has
paqe S4 of 108
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the most widespread occurrence and
concentration in groundwater samples.
has
the
highest
6.2
RISK CHARACTERIZATION
A Baseline Public Health Evaluation (BPHE) is conducted at every
Superfund .ite to evaluate the risk posed by the .ite in its
existing condition. The BPHE examines .the chemicals present at the
site (see Section 6.1) and the possible routes of exposure to
humans and animals.
Using similarly conservative assumptions, the BPHE also developed
future and current exposure scenarios. For the hypothetical future
exposure .cenarios, it was assumed that the onsite areas of the
site would be developed for residential use and that the
groundwater in the A- and &-aquifers would be used for domestic
water supply purposes. The potential current exposure scenario
considered in the BPHE evaluated inhalation of VOC vapors
originating from the offsite groundwater plume.
Fugitive dust emission or incidental ingestion of soil by
construction workers during hypothetical future construction on the
site were not evaluated as exposure pathways at these sites. This
choice was made because the documented contaminated soil is all at
depths greater than eight to ten feet. Fugitive dust emission is
not a concern in this circumstance. Standard construction practices
in this portion of the Santa Clara Valley would not result in
excavations of this depth.
According to the BPHE, potential future 8Zpo.ure routes at the
Companies site may include ingestion of groundwater containing the
chemicals of potential concern, inhalation of VOC vapors from
groundwater during showering or other domestic uses, and inhalation
of VOC vapors originating from the groundwater. Based on the
absence of known soil "hot-spots", other than those well below
ground surface and beneath buildings, direct contact exposure to
chemicals of concern was not considered further in the exposure
evaluation.
In addition to the above, the BPHE also assumed that the current
cleanup actions would be discontinued and cleanup measures would
not be implemented at any time in the future. Using these
assumptions, the BPHE concluded that the only averaqe 8Zposur8
.cenario for which there would be a potential health risk or an
increased cancer risk greater than 1 in 10,000 was the hypothetical
future domestic use of contaminated shallow groundwater. The most
crucial of these assumptions is that cleanup activity in the study
area would cease. This implies that current concentrations in
groundwater would persist into the future.
The only current expo.ure .cenario identified in the BPHE is indoor
exposure to vapors migrating from the contaminated groundwater in
Page 55 of 108
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the offsite area. This pathway was evaluated for two separate
populations, residents of the offsite area and children attending
the San Miquel school. These cancer risks and health hazard
assessments are based on estimates of the indoor aj,.r concentrations
of the chemicals of concern predicted by mathematical models. The
predicted carcinogenic risk for the average case is estimated to be
about 4 in 100,000,000 for schoolchildren and about 1 in 10,000 for
residents. The model does not predict any toxic effects from this
exposure. This is within the risk range that would be allowable
under EPA guidance after cleanup. EPA methodology will be applied
to reasses.s this exposure within each of the four operable units at
the five year review.
The future u.. .c8nario considered by the BPHE is domestic use of
shallow groundwater beneath the site. This would expose residents
to contaminated groundwater through ingestion of water and
inhalation during domestic use (showering, cooking, etc.). The
greatest potential carcinogenic risk related to the average
exposure through these pathways is approximately 2 in 1000. .
Domestic use is a hypothetical case since shallow groundwater in
the A- and B-aquifers is not currently used for water-supply
purposes and local ordinances prohibit such practice. CUrrently,
there are no plans to use the A- and B-aquifer groundwater as a
drinking water supply.
6.2.1
Soil
6.2.1.1
AMD 901/902 Soil
No shallow (less than 2 feet) contaminated soil is remaining since
the interim remedial actions for soil was effective in removing
shallow soil. Contaminated soil that remains in place is greater
than ten feet in depth. The exposure to contaminated soil through
the dermal contact route was not evaluated since it is unlikely
that contact with the chemicals of concern at AMD 901/902, VQCs,
would occur. Possible exposure of workers to the contaminants
remaining in soil in place at the AMD 901 facility as a-result of
volatilization was investigated and will be discussed below under
risk from air pathways.
6.2.1.2
Signetics Soil
The interim remedial action of excavation and offsite disposal was
effective in removing contaminated soil from the Signetics operable
unit. No additional contaminated soil has been documented,
therefore risk due to direct contact or fugitive dust emission was
not evaluated.
6.2.1.3
TRW Soil
No shallow (less than 2 feet) contaminated soil is remaining since
Page 56 of 108
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the interim remedial actions for soil was. effective in removing
shallow 80il. Contaminated soil that remains inplace is greater
than ten teet in depth. The exposure to contaminated 80il through
the dermal contact route was not evaluated since it is unlikely
that contact with the chemicals of concern at TRW, VOCs and metals,
would occur. Additionally, should dermal contact occur the VOCs
would volatilize into the air prior to significant subcutaneous
adsorption and subcutaneous adsorption of metals is not.
. significant.
6.2.1.4
Offsite Soil
No source areas have been located or are suspected in the offsite
operable unit. Soil contamination would only occur at contact
between the soil and groundwater, which occurs at depths greater
than twelve feet. Concentrations are assumed to be minimal due to
the constant partitioning of chemicals from water to soil and soil
to water. Risk due to direct contact or fugitive dust emission was
not evaluated.
6.2.2
Air
6.2.2.1
AMD 901/902
The risk from the air stripper emissions was evaluated by the
BAAQMD in 1985 prior to providing AMD with a permit to operate the
air stripper. The risk related to the chemical releases from the
AMD 901/902 air stripper was estimated by BAAQMD personnel to be
1.6 X 10~. Flow rate and influent concentration was higher in 1985
than now therefore maximum air concentration and the related risk
would also be lower than that projected in 1985.
The potential for volatilization of chemicals from groundwater to
the surface was evaluated in the BPHE for the hypothetical case
that the "onsite" industrial property at the AMD 901/902,' Signetics
and TRW operable units was converted to residential property. This
evaluation was based strictly on modeling of transport from
groundwater into residences and assuming current groundwater
concentrations for chemicals of concern. The excess cancer risk
estimate, based on this model is 4 X 10.5 for the average case and
8 X 10~ for the maximum case. The non-carcinogenic cancer index
for both the 'average and maximum cases is much less than one.
The portion of the groundwater contaminant plume that currently
beneath the AMD 901/902 operable unit does not represent a current
risk since no residences overlay the plume. The manufacturing
facilities that overlay the plume all utilize active ventilation
systems which would act in two ways to reduce this potential risk,
first the ventilation system, by pumping air into the structure,
creates positive pressure thus reducing the rate of infiltration of
contaminants into the structure and secondly the continued influx
Page 57 of 108
-------
of air.dilutes any contaminants that enter the structure.
In response to aqency concerns reqardinq the presence of
contaminated soil remaininq below the AMD 901 facility, AMD sampled
air in the interior of the 901 facility with a photoionization
detector (PID). PIDs are not chemical specific, in that they will
not indicate what chemical is beinq detected, only an approximate
concentration of chemicals in vapor. The detection limit for this
method is . between 0.5 part per million (ppm) and 1 ppm. All
readinqs were below the detection limit. To confirm these results
discrete samples indoor and outdoor ambient air were collected in
summa canisters and analyzed. This samplinq protoco~ allows much
lower detection limits. These results indicate that the chemicals
present at hiqh concentrations in the contaminated soil, 1,1-
Dichloroethylene (DCE) , Trichlorethylene (TCE) , Tetrachloroethylene
(PCE) and Dichlorobenzene (DCB), are not present above 0.25 part
per billion (ppb).
Worker safety requlations include allowable exposure for these.
chemicals trom 25 to 200 ppm. The worker allowable worker exposures
are risk based, however the assumptions used in assessinq worker
exposure are siqnificantly different from the assumptions used in
,the BPHE. The comparison of the non-detectable levels of the
chemicals of concern to the allowable levels would still indicate
that exposure to indoor air contaminated by vapors miqratinq from
contaminated soil or other sources is probably not a siqnificant
risk at the AMD 901 facility.
6.3.2.2
Siqnetics
As part of the interim remedial action three air strippers are
present at' the Siqnetics 440 Wolfe facility. The air strippers
operate in sequence, with the first air stripper removinq over 99%
of the VOCs from the influent water. This initial stripper does
include control of the air emissions with capture by vapor phase
carbon. The total release of VOCs by all three air strippers is
limited to 0.52 pounds per day by a BAAQMD Permit to Operate. The
risk from the release from the air strippers was evaluated after
the completion of the FS. The maximum concentration predicted by
the model was 0.434 "q/1. This would result in an estimated
increased cancer risk of approximately 1 X 10~. Non-carcinoqenic
effects were a180 evaluated for this release and none would be
predicted trom the exposure to' the maximum concentrations resul tinq
from the air stripper discharqe. The model assumed minimum stack
heiqht, maximum predicted concentration and minimum distance to the
receptors at the property boundary.
The risk related to volatilization of chemicals, primarily VOCs
from qroundwater, was evaluated for all three "onsite" operable
units for a hypothetical future scenario of conversion to
residential property as discussed above in section 6.3.2.1.
paqe 58 of 108
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6.3.2.3
TRW
As part of the interim action and as part of the proposed remedy an
air stripper has been operating at the former- TRW Microwave
facility since 1985. The emissions from this air stripper are
estimated to be 0.84 pounds per day. TCE accounts for over 90t of
this emission. While vinyl chloride is detected routinely in one of
the onsite TRW wells it is not detected in the influent to the
treatment system. This is a function of dilution of the vinyl
chloride by mixing with groundwater from other extraction wells.
Therefore the cancer risk related to this release was evaluated for
TCE. The maximum concentration of VOCs estimated by the California
Air Resources Board PTPLU model is 9.24 X 10.3 mg/m3. The excess
cancer risk related to release of TCE to the ambient air at this
concentration for a 75 year lifetime exposure is estimated to be
1.79 X 10.'.
The risk related to volatilization of chemicals, primarily VOCs
from groundwater, was evaluated for all three "onsite" operable
units for a hypothetical future scenario of conversion to
residential property as discussed above in section 6.3.2.1.
6.3.2.4
Offsite
The only documented emissions within the offsite operable unit is
from the shallow soil. This may be from the volatilization of
groundwater chemicals into ambient air or may represent deposition
in the shallow soil from ambient air. Volatilization of chemicals
from the groundwater was modeled in the BPHE and investigated as
detailed in section 5.2.3.4 above.
Due to the dispersive action of the wind and the low contaminant
concentrations estimated and measured, the risk related to this
exposure pathway in ambient air is nil. The risk from this pathway
was initially estimated based on a two stage model as described
above. Additional risk estimates were made for a maximum and an
average case based on measured, field flux data rather than flux
data estimated by a mathematical transport model. The indoor air
concentration. is still based on a. conservative box model that
assumes a low rate of indoor air exchange and a maximal area of
infiltration. The maximum case assumes exposure for 30 years with
the indoor air concentration modeled from the maximum field flux
rate measured. The average case assumes a 9 year exposure with the
indoor air concentration modeled from the mean of the measured
field flux rates. The estimated risk for the maximum case is 5.75
X 10~ and 9.1 X 10~ for the average case. In each scenario the only
observed carcinogenic chemical of concern was TCE.
The risk related to the operation of air strippers at the AMD 915
site, where the-offsite groundwater is treated, was evaluated after
the completion of the FS. Offgas from the air strippers was
Page 59 of 108
-------
collected and analyzed for cis-l,2-DCE, trans-l,2-DCE, TCE, 1,1,1-
TCA and vinyl chloride in September 1991. This data was then used
in a screening level model developed by the California Air
Pollution Control Officers Association. This model uses average
area wide meteorological conditionsL minimum release point height,
maximum toxicity or carcinogenicity values, and minimum receptor
distances. This model would predict a cancer risk of less than 1
X 10~ and no non-carcinogenic health effects.
6.3.3" Groundwater
Possible exposure to contaminated groundwater as a result of using
this groundwater as a source of domestic water supply was
evaluated. This evaluation considered both direct ingestion of the
groundwater and exposure to contaminants through the inhalation
pathway as a result of showering and other domestic use. The
evaluation was not considered separately for the operable units. It
was assumed that the potential for the migration of the
contaminants to a water supply well in the shallow aquifer were
equal.
The evaluation of the this scenario assumes that no further actions
would occur and that the current contaminant concentrations in
groundwater would be present at the time a domestic well began to
draw water from the shallow water bearing zones. This scenario was
evaluated for both the A and B zone waters, but the numbers
presented here are for the A zone which represents the greater risk
and hazard. The non-carcinogenic hazard ratio and the carcinogenic
cancer risk was considered for two cases, the average case and the
maximum case. The average case assumes a 9 year exposure including
ingestion of 1.4 liters of water per day contaminated with the
chemicals of concern as represented by the geometric mean
concentration in data from 1988 through 1989. The maximum case
assumes a .30 year exposure to these chemicals at the maximum
concentration detected in this same database. This scenario.assumes
ingestion of 2 liters of contaminated water per day for this 30
year period.
The excess cancer risk for the average or representative case based
on the combination of ingestion and inhalation exposure is 2 X 10.3
(Table 5). The excess cancer risk for the maximum case is 5 X 10-1.
The potential cancer risk was evaluated, under the guidance of EPA
Region IX toxicologist, without the inclusion of l,l-DCE as a
carcinogen. Under this guidance modified reference dose was used in
the calculation of the hazard ratio for l,l-DCE. However, based on
guidance from EPA (Risk Assessment Guidance for Superfund), since
the hazard index is greater than one it is not appropriate to
consider l,l-DCE only as a non-carcinogen since this would require
evaluation of the potential non-carcinogenic effects by target
organ and might not correctly represent the potential carcinogenic
effects of l,l-DCE. Therefore, the appropriate cancer risk related
to the ingestion of groundwater is 2 X 10~ for the average case and
5 X 10.1 for the maximum case.
Page 60 of 108
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CHE'" CAL COICEITIIA T lell IEPIESEITATIVE EXPOSUIE COICEITIIATIOI MAXI"" EXPOSUIE
.a/l IIGESTIOI IIHALATIOI TOTAL .a/l IIGESTIOI IIHALATIOI TOTAL
1,1-DCA 18 6 . 10" IA 6 . 10" 600 6 . 10-4 IA 6. 10"
1,1-DCE 9.5 2 . 10" 4 . 10" 6 . 10" 6] 4 . 10" 9 . 10-4 1 . 10'
PCE 610 2 . 10" 1 . 10" 2.1 . 10" 610 4 . 10-4 2 . 10" 4 . 10-4
TCE 560 2 . 10" ] . 10' 5 . 10" ZOO, 000 2 . 10.1 4 . 10.1 6 . 10.1 -
Vlln CMUIiIDE 240 2 . 10" 2 . 10" 2.2 . 10' 18,000 4 . 10" 6 . 10.1 5 . 10"
TOTAL 2 . 10" ] . 10-4 2 . 10" 4. 10" 1 . 10" 5. 10"
TOTAL WID 1,1-DCE 2 .'10" Z. 10" Z . 10" 4 . 10" 1 . 10" 5 . 10"
TABLE 5
ADULT CARCINOGENIC RISK
AMD 901/902. SIGNBTICS. AND TRW
Page 61 of 108
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The hazard index for the representative case is greater than one
and is much greater than one for the maximum case. This indicates
that non-carcinogenic health effects would be expected. Since the
hazard index is qreater than one the actual health hazard would
require further evaluation on a target organ basis. Since the water
is not currently used as a source of drinking water and is not used
without treatment this was not pursued.
It should be emphasized that the shallow qroundwater is not
currently used for local drinking water; local ordinances require
the installation of a sanitary seal through at least the upper 50
feet of the shallow water bearing zones. This would limit use of
the most contaminated groundwater for drinking water.. In addition,
the assumption that all cleanup actions will be discontinued is
intended only to provide a baseline for comparison, and does not
reflect the current situation or future plans within the study
area.
6.3
PRESENCE OF SENSITIVE HUMAN POPULATIONS
The study area is located in predominantly industrial area however,
the groundwater contamination plume does extend downgradient to the
north, beneath a residential area. The extension of the groundwater
contamination plume North of Duane Avenue (offsite operable unit)
may result in as many as 600 residences overlying the groundwater
plume. This includes the San Miquel School, which currently houses
a daycare center and a Headstart Program.
Since the contaminated groundwater has not affected the drinking
water supply the only possible current exposure is through the
inhalation pathway. This exposure pathway was evaluated for
children attending programs at the San Miquel school facility. The
excess cancer risk for both the average and maximum cases was less
than 1 X 10~. The hazard ratio for both the average and maximum
cases was less also less than one. The average case assumed the
children were present for four .hours per day for two years. The
maximum case assumed the children were present for eight hours per
day for four years.
6.4
PRESENCE OF SENSITIVE ECOLOGICAL SYSTEMS
Two endangered species are reported to use South San Francisco Bay,
located approximately three miles north of the Study Area. The
California clapper rail and the salt marsh harvest mouse are
reported to exist in the tidal marshes of the Bay and bayshore.
The endangered California brown pelican is occasionally seen in the
Bay Area, but does not nest in the South Bay. Ranges of the
endangered American peregrine falcon and southern bald eagle
include the Bay Area. The southern bald eagle does not use bay and
bay shore habitats. The peregrine falcon is making a strong recovery
and may be downgraded from endangered to threatened status in
Page 62 of 108
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specific areas, includinq California, in the near future. Nestinq
pereqrines have been noted in the northern bay area, includinq the
Golden Gate Bridqe and Bay Bridqe, however nestinq pereqrine
falcons have not been reported in the South Bay. .
The AMD site Study Area does not constitute critical habitat for
endanqered species nor does it include or impact any "wetlands."
6.5
CONCLUSION
Actual or threatened releases of hazardous substances from the
Advanced Micro Devices, 901/902 Thompson Place, Siqne~ics, 811 East
Arques, and former TRW Microwave facility, 825 Stewart Drive
Superfund sites, if not addressed by implementinq the response
action selected in this ROD may present an imminent and substantial
endanqerment to the public health, welfare or environment. Based
on the fact that a variety of the VOCs detected in the Study Area
pose siqnificant health risks as carcinogens or as noncarcinoqens
and complete exposure pathways exist, EPA has determined that
remediation is warranted.
7.0
APPLXCABLE OR RELEVANT AND APPROPRXATE REQUXREHBlftS (ARARS)
Under section 121(d) (1) of CERCLA, remedial actions must attain a
deqree of clean-up which assures protection of human health and the
environment. Additionally, remedial actions that leave any
hazardous substance, pollutant, or contaminant on-site must meet a
level or standard of control that at least attains standards,
requirements, limitations, or criteria that are "applicable or
relevant and appropriate" under the circumstances of the release.
These requirements, known as "ARARs" , may be waived in certain
instances, as stated in Section 121(d) (4) of CERCLA.
"Applicable" requirements are those clean-up standards, standards
of control and other substantive environmental protection
requirements, criteria, or limitations promulqated under federal or
state law that specifically address a hazardous substance,
pollutant or contaminant, remedial action, location, or other
circumstance at a CERCLA site. "Relevant and appropriate" re-
quirements are clean-up standards, standards of control and other
substantive environmental protection requirements, criteria, or
limitations promulgated under federal or state law that, while not
"applicable" to a hazardous substance, pollutant, contaminant,
remedial action, location, or other circumstance at a CERCLA site,
address problems or situations sufficiently similar to those
encountered at the CERCLA site that their use is well-suited to the
particular site. For example, requirements may be relevant and
appropriate if they would be "applicable" but for jurisdictional
restrictions associated with the requirement. (See the National
Continqency Plan, 40 C.F.R. Section 300.6, 1986).
The determination of which requirements are "relevant and ap-
paqe 63 of 108
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propriate" is somewhat flexible. EPA and the State may look to the
type of remedial actions contemplated, the hazardous substances
present, the waste characteristics, the physical. characteristics of
the site, and other appropriate factors. It is possible for only
part of a requirement to be considered relevant and appropriate.
Additionally, only substantive requirements need be followed. If
no ARAR covers a particular situation, or if an ARAR is not
sufficient to protect human health or the environment, then non-
promulgated standards, criteria, guidance, and advisories must be
used to provide a protective remedy.
7.1
TYPES OF ARARS
There are three types of ARARs. The first type includes
"contaminant specific" requirements. These ARARs set limits on
concentrations of specific hazardous substances, pollutants, and
contaminants in the environment. Examples of this type of ARAR are
ambient water quality criteria and drinking water standards. The
second type of ARAR includes location-specific requirements that
set restrictions on certain types of activities based on site
characteristics. These include restriction on activities in
wetlands, floodplains, and historic sites. The third type of ARAR
includes action-specific requirements. These are technology-based
restrictions which are triggered by the type of action under
consideration. Examples of action-specific ARARs are Resource
Conservation and Recovery Act ("RCRA") regulations for waste
treatment, storage, and disposal.
ARARs must be identified on a site-specific basis from information
about specific chemicals at the site, specific features of the site
location, and actions that are being considered as remedies.
7.2
CONTAMINANT-SPECIFIC ARARS AND TBCS.
Section 1412 of the Safe Drinkina Water Act. 42 U.S.C. Section
300G-1
Under the authority of Section 1412 of the Safe Drinking Water Act,
Maximum Contaminant Levels Goals (MCLGs) that are set at levels
above zero, shall be attained by remedial actions for ground or
surface water that are current or potential sources of drinkinq
water, where the HCLGs are relevant and appropriate under the
circumstances of the release based on the factors in 5300.400
(g) (2) .
The appropriate remedial goal for each indicator chemical in ground
water is the MCLG (if not equal to zero), the federal MCL, or the
state MCL, whichever is most stringent.
California's Resolution 68-16
Page 64 of 108
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- -
I
California's "statement of Policy With Respect to Maintaining High
Quality of Waters in california," Resolution 68-16, affects
remedial standards. The policy requires maintenance of existing
water quality unless it is demonstrated that a change will benefit
the people of the State, will not unreasonably affect present or
potential uses, and will not result in water quality less than that
prescribed by other State policies. .
The FS evaluated groundwater cleanup to background or non-detect
levels. Cleanup to non-aetect levels would increase estimated
groundwater cleanup times by over SO, and add significantly to
cost. The FS also evaluated cleanup levels necessary to achieve a
1 in 1,000,000 excess cancer risk from future ingestion of the
groundwater. This is highly impractical due to the presence of
arsenic. The arsenic concentration would have to be reduced to 1.5
~g/l to approach the 1 in a 1,000,000 excess cancer risk. This is
far below the current MCL for arsenic of SO ~g/l and is probably
below the naturally occurring background of arsenic in groundwater
in Santa Clara County. .
In addition, cleanup of groundwater to below the MCL for the
chemicals of concern may not be achievable due to the technical
difficulties in restoring aquifers by the removal of low
concentrations of any VOC. This is due to the slow desorption of
VOCs adsorbed to the inner pore spaces of soil particles which make
up the aquifer material and VOCs adsorbed to clays and organic
matter in the aquitard. Cleanup to MCL levels would protect the
primary beneficial use of the groundwater as a potential source of
drinking water. For these reasons, MCLs were accepted as
concentrations that meet the intent of Resolution No. 68-16.
7.3
ACTION SPECIFIC ARARS AND TBCS
National Pollutant Discharae Elimination Svstem (NPDES)
NPDES substantive permit requirements and/or RWQCB Waste Discharge
Requirements eWDRs) are potential ARARs for effluent discharges.
The effluent limitations and monitoring requirements of an NPDES
permit or WDRs legally apply to point source discharges such as
those from a treatment system with an outfall to surface water or
storm drains. The RWQCB established effluent discharge limitations
and permit requirements based on Water Quality Standards set forth
in the San Francisco Bay Regional Basin Plan or best available
technology standards.
EPA Office of Solid Waste and Emeraencv ResDonse (OSWER) Directive
9355.0-28
OSWER Directive 9355.0-28 "Control of Air Emissions from Superfund
Groundwater Air Strippers at Superfund Groundwater sites" applies
to future remedial decisions at Superfund sites in ozone non-
attainment areas. Future remedial decisions include Records of
Page 65 of 108
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Decisions (RODs), Siqnificant Differences to a ROD and Consent
Decrees. The four operable units are in an ozone non-attainment
area. This directive requires such sites to control total volatile
organic compound emissions from air strippers and soil vapor
extractors to fifteen pounds per day per facility.. This directive
is not an ARAR, but is a TBC. ARARs with more stringent
. requirements take precedence over the directive.
Bav Area Air Oualitv Manaaement District lBAAOMD} Reaulation 8.
Rule 47
Bay Area Air Quality Management District Board of Directors adopted
Regulation 8, Rule 47. This rule is entitled "Air ~tripping and
Soil Vapor Extraction Operations" and applies to new and modified
operations. The rule consists of two standards:
o
Individual air stripping and soil vapor extraction operations
emitting benzene, vinyl chloride, perchloroethylene, methylene
chloride and/or trichloroethylene are required to control
emissions by at least ninety percent by weight. Operations
emitting less than one pound per day of these compounds are
exempt from this requirement if they pass a District risk
screen.
Individual air stripping and soil vapor extraction operations
emitting greater than fifteen pounds per day of organic
compounds other than those listed above are required to
control emissions by at least ninety percent by weight.
Regulation 8, Rule 47 is an ARAR for the implementation of the
remedy at all four operable units.
o
Bav Area Air Oualitv Manaaement District lBAAOMD} Reaulation 8.
Rule 40
Bay Area Air Quality Management District Board of Directors adopted
Regulation 8, Rule 40, July 1986. This rule is entitled "Aeration
of Contaminated Soil and Removal of Underground Storage Tanks". The
purpose of this Rule is to limit the emission of organic compounds
from soil that has been contaminated by organic or petroleum
chemical leaks or spills; to describe an acceptable Boil aeration
procedure; and to describe an acceptable procedure for controlling
emissions. from underground storage tanks during replacement or
removal. This rule includes standards for aeration, reporting
requirement. and a manual of procedures.
o
Oncontrolled aeration (8-40-301) is limited by a combination
of organic content and volume.
Controlled aeration (8-40-302) requires that the emissions of
organic compounds to the atmosphere be reduced by at least 90%
by weight.
o
Page 66 of 108
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Regulation 8, Rule 40 would be an ARAR for the implementation of
any remedy that includes soil aeration or removal of any soil
containing greater than 50 ppm by weight organic content.
Resource Conservation
Restrictions
Recoverv
Act
(RCRA)
Land
DisDosal
The contaminated ground water contains two spent solvents that are
RCRA listed wastes. TCE is an FOOl listed waste, and TCA is an
F002 listed waste. Adsorbents and other materials used for
remediation of groundwater VOCs, such as activated carbon,
chemical-adsorbing resins, or other materials used in" the treatment
of ground water or air will contain the chemicals after use. RCRA
land disposal restrictions are not applicable but are relevant and
appropriate to disposal of treatment media due to the presence of
constituents which are sufficiently similar to RCRA wastes.
Clean Water Act
Under these provisions, discharges of treated groundwater "to the
local sanitary sewer must comply with local POTW pretreatment
programs. Discharges of treated groundwater to the sanitary sewer
at AMD 901/902 must meet the substantive standards of the City of
Sunnyvale.
7.4
LOCATION-SPECIFIC ARARS
Fish and Wildlife Coordination Act
The Fish and Wildlife Coordination Act is an applicable requirement
for the locations adjacent to Calabazas Creek, Guadelupe Slough and
other tributary streams and marshes.
8.0
DBSCRIPTIO. O~ ALTERNATIVES
8.1
REMEDIAL ACTION OBJECTIVES
Cleanup of groundwater contamination at the AMD/Siqnetics/TRW sites
focuses on the following remedial objectives:
1.
Prevention of the near-term and future exposure of human
receptors to contaminated groundwater and soil;
Restoration of the contaminated groundwater for future use as
a potential source of drinking water;
2.
3.
Control of contaminant migration;
4.
Monitoring of contaminant concentrations in groundwater to
observe the control of contaminant migration and the progress
Page 67 of 108
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of cleanup.
8.2
CLEANUP STANDARDS
8.2.1
Cleanup Standards
Even thouqh shallow qroundwater affected by these sites is not
currently beinq used for drinkinq water, it is a potential drinkinq
water source and must be protected as such. Therefore, the cleanup
standards have been set at state and federal Maximum Contaminant
Levels (MCLs) for drinkinq water. The cleanup standards for nine
of the ten chemicals of concern for these sites are ~e California
MCLs for drinkinq water (Table 6). The exception is 1,2-DCB for
which California has not established an MCL. The cleanup standard
for 1,2-DCB will be the recently promulqated Federal MCL, which
becomes effective July 1992. Settinq the cleanup standards at
these levels fulfills the ARARs and also achieves a risk level
within the EPA acceptable risk ranqe.
For the study area, the carcinoqenic risk at the cleanup standards
for all chemicals listed in Table 6 associated with the potential
future use scenario of qroundwater inqestion and inhalation of VOCs
from qroundwater would be 3.7 X 10-4 (Tables 7 , 8). This risk is
based on all the chemicals in Table 6 beinq present in the
qroundwater any place within the study area. This estimate is based
on assumptions similar to the probable maximum case in the BPHE,
except it assumes a 70 year rather than a 30 year exposure used to
estimate the probable maximum risk scenario in the BPHE.
These assumptions are probably overly conservative, especially the
assumption reqardinq the occurrence of all chemicals. Table 6 shows
which chemicals occur or would be reasonably expected to occur in
which operable unit. Based on these chemicals only, the estimated
excess carcinoqenic risk after cleanup is 6 X 10-6 for the AMD
operable unit and 4 X 10-5 for Siqnetics, TaW, and the offsite
comminqled plume (Table 8). 'In cleaninq up TCE to the 5 ppb
cleanup standard it is quite likely that the concentrations of
other VOCs will be reduced to levels below the 5 ppb ranqe. These
risk values represent the maximum residual risk that would be
probable followinq cleanup.
In addition, these values include 1,1-DCE which is classified by
EPA as a possible human carcinoqen. The classification of 1,1-CCE
as a carcinoqen is based on a sinqle positive result out of
seventeen studies and, based on quidance of EPA reqion IX
toxicoloqist, it is acceptable to exclude 1,1-DCE as a
paqe 68 of 108
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TABLE 6
CLEANUP STANDARDS FOR THE CHEMICALS OF CONCERN IN
GROUNDWATER
AMD 901/902, Siqnetics, and TRW
Sunnyvale, California
APPLIWLE
CIJII(UI) FEDEIAL MCL~ 'EDEtAL MCL" CALIFORNIA MCL OPERABLE UNITS
1,2- Dicbloroh-~ (600) q (600) NA AMD, TRW
.
1,I-Dic:bloroetbaDeCel NA NA '5.q ALL
1,I-Dic:blo~MI 7 7 .,.'6.:, ... ALL
cia-l,2-Dic:bloroedlale (70) (70) 6 ALL
traDs-l,2-Dicbl~ (100) (100) ql0 ALL
Freoa 113 NA NA . 1.200. ALL
TetnchloroetbeDe(cl (0) (5) 5 AMD, TRW,
OFFSITE
1,1,1- Tricbloroethaae 200 200 200 ALL
Tric:bloroetJ1eDel8l 0 5 5 ALL
Vinyl Qloride181 0 2 0.5 AMD, TRW,
Signetics
Shaded criteria are the selected cleanup standards
(a) MCLG = maximum contaminant level goaL Concentrations in micrograms per
liter .
(b) MCL = maximum contaminant level. Concentrations in micrograms per liter.
(c) Potential or probable human carcinogen.
(d) Possible human carcinogen.
NA = Not available.
() Criteria in parentheses, effective July 1992
paqe 69 of 108
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carcinoqen. If 1,1-DCE is not included as a carcinoqen, a
modified reference dose is used in the evaluation of the non-
carcinogenic hazard quotient. If it is excluded, the estimated
risk at cleanup standards decreases to 6 X 10-6 for Siqnetics and
TRW and 3 X 10-6 for the offsite commingled plume.
The non-carcinogenic hazard index at the cleanup standards, for
all of the chemicals shown in Table 6 associated with the
potential ~uture use scenario of groundwater ingestion and
inhalation of VOCs is 0.44 (Table 7). If only those chemicals
that might be reasonable expected to occur within any operable
unit are considered then the hazard index for this scenario is
0.44 for AND and Siqnetics operable unit, 0.1 for the TRW
operable unit, and 0.2 for the offsite commingled plume (Table
7) .
Cleanup standards for the treated effluent from the air stripper
are set by RWQCB in the NPDES permit process. Cleanup standards
for the air stripper offgas are established by the BAAQMD permit.
process. All of the treatment systems, except for the .
groundwater treatment system at AMD 901/902, are currently
permitted by the RWQCB and BAAQMD. The groundwater treatment
system at AMD 901/902 does have a permit to operate from the
BAAQMD, however since the water is reused as industrial process
water and indirectly discharged to the sanitary sewer system
apermit from the RWQCB is not required.
Operation of the AMD 901/902 site as a production facility by AMD
will cease sometime in late 1991 or early 1992. This will
preclude the indirect discharge of the treated groundwater under
local POTW regulations. An NPDES permit will be required for
discharge of this water, however the discharge limits have not
been established at this time.
There are currently no ARARs established for cleanup levels in
contaminated soil. However, a RWQCB policy of cleanup to
background or 1 ppm total VOCs for soils is a TBC criteria and
has been set as the soil cleanup standard for these sites.
Experience at other sites has shown that this level will prevent
recontamination of groundwater.
8.2.2
Compliance Boundaries
The compliance boundary for contaminated groundwater includes all
groundwater within the plume boundaries indicated in Figures 16
and 17, all groundwater monitored in existing wells, and any
contaminated groundwater identified by additional monitoring
wells installed upon RWQCB or EPA request for the purpose of
monitoring potential vertical or horizontal migration of the
plumes currently located in the A and B Aquifers.
Page 70 of 108
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CONCENTRATION (Cw) SET AT ARARs
HAZARD I NOEX . CD I/RfD CDI . Chronic Dallv Intake RfD . Reference Dose
Cw . ARAR.. TIC. or claeru» . .1.
ORAL I."'''... I ......tIo. TOTAL HI
Rm Rm III
No. CIIEMICAL Cw,..n WOE cm HI
.
I 1,2-DICHLOROBENZEN8 0.100 MCL\B2 0.01 2.168~ 2.168-01 NA 0.00 2.168-01
2 I,I-DCA . 0.005 CA MCL\82 0.100 1.4Je-04 1.4~ 0.1 1.43e-O:J 2.16o-OJ .
3 I,I-DCB 0.006 CA MCL\C 0.009 1.710-04 1.901-0'1 NA 0.00 1.901-0'1
4 cle-I,2-DC8 0.006 CA MCL\D 0.02 1.710-04 U70~ NA 0.00 '.'7.~
, 1ftnI-1,2-DCE 0.010 CA MCL\D 0.02 2.168-04 1.4Je-O'1 NA 0.00 1.4Je-O'1
6 FRIIONlh I.~ CA MCL\D 3 3.430-02 1.140-02 NA 0.00 1.140-0'1
7 PCE 0.005 MCL\82 0.01 1.43e-04 1.4Je-02 NA 0.00 1.4'0-02
. 1,I,I-TeA 0.200 MCL\D 0.09 '.710~ 6.J5e-02 0.3 1.901-02 U",-O'1
9 TeE , 0.005 MCL\82 NA 1.4Je-04 0.00 NA 0.00 0.00
10 VINYL CHLORIDE 0.0005 CA MCL\A NA 1.430-05 0.00 NA 0.00 0.00
'lUl'AL HAZARD INDEX - .42cOO .2Oe-O I .440 +00
IRIS - IRIS ORAL REFERENCE DOSE
DWHA - DRINKINO WATER HEALTH ADVISORY
WQC - NATIONAL AMIIBHT WATER QUAUI'Y CRlI'ERIA FOR PUBLIC
HEALTH
MCL - FEDERAL MCL
CA MCL - CALIFORNIA MCL
WOE - WEJOIrr OF EVIDENCE - SOURCE OF DATA
A - KNOWN HUMAN CARCINOOENS
BI - PROBABLE HUMAN CARCINOOEN (limited human evidence, .dequate evidence from .nimala)
B2 - PROBABLE HUMAN CARCINOGEN (inadequate human evidence, adequate evidence from .nimala)
C - POSSIBLE HUMAN CARCINOGEN (limiled evidence of carcinogenicity, lnimallludiCi only)
TABLE 7, HAZARD INDEX AT CLEANUP STANDARDS, AMD 901/902, Signetics, TRW
T"~-- "'1 _C l'
-------
TABLE 8, CANCER RISK AT CLEANUP STANDARDS
AMD 901/902, Signetics CHEMICAL CONCENTRATION SET TO CLEANUP STANDARDS
and TRW
DETERMINATION OF EXCESS LIFETIME CANCER RISK FOR
CARCINOGENS
EXCESS LIFETIME CANCER RISK - CDI x q*
q* a CANCER POTENCY FACTOR CDI a Chronic Daily
(MG/KG/DAY)-l Intake (MG/KG)
CW = ARARs, TOCs, or cleanup goals
CHE"ICAl Cv IC/L WOE\CLASS Of ORAL f(' CDI liSt( IIiKAlATICII f(' IIiKALATICII 1151 TOTAL
CARCIIiOGEN liSt(
1.1-DCA 0.005 CA Nel\12 9.10.-02 1.43.-04 1.JOe-05 " 0.00 1.]0.-05
1 1-Da 0.006 CA MCl\C 6.ooe-01 1.71.-04 1.0J.-04 1. ZOe+OO 2.068-04 ].0ge-04
PCE 0.005 MCL\l2 5.10.-02 1.43.-04 7.Zge-06 ].JOe-OJ 4.71.-07 7.768-06
TCE 0.005 MCl\l2 1.10.-02 1.43.-04 1.57.-06 1.708-02 2.4].-06 4.00.-06
VIIIYl CHLORIDE 0.0005 CAMCl\A 2.JOe+OO 1.43.-05 ].29.-05 2.95.-01 4.21.-06 ].71.-05
Exass CAlaR II SIC 1.58e-04 2.1].-04 ].71.-04
EXCESS CAla. .1 SIC "/0 ,. 1-DCE 2.78e'05 7.11e-06 1.4ge-05
WOE . YEIGHT 0' EVIDEIICE . SOURCE 0' OAT.
Nel . fEDERAL DRIIIICIIiG WATER MAXI"" catTAlUII..T LEVEL
CAMel . CAllFORlilA DRIIIICIIiG WATER MAXI"" catTMI..IIT lEVEL
. . ICIlCUII HUMAN CARCIIDGEIIS .
., . PROBABLE IUWI CARCINOGEN (l18fted h~ evidence. 8decaate evIdence frC18 .,1_(8)
12 . PROBABLE IUWI CARCIIDGEII (t..--te hl8ln evIdence edeG.Iate evidence frC18 .,1_1.,
C . POSSIBLE IUCAII CARCIIIOGEN (1I.lted evIdence of carcinogenicity. enll..1 studies onlY)
Paqe 72 of 10R
-------
,----
-.- ... .. -----..-.
.
400
.
SCALf IN fEET
IDO
.
-
-H,
EXPLANATION
I
-----_J GJ
~ ..
~ .~ ...
~~
I
I
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L--------------'"
----
----
----
----
,
I
I
I
I
I
I
INdA H&U--
I
I '
I
~
---- ._-
---- Facility/OU boundaries
---- study Area perimeter
Figure 16.
A Zone Plume Boundary at
5 ppb TCE
-------
-- - ~----- ---
..-----.-.
!J
Ii I"""""'~
I ,'/ ""~
, ~!
J ~ I
I I
I I ~/
~-----, I r-~-, .
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I [3J ~ I ~ I I ----.........
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! *~I [J---~ 1 :
1 I- B r::l'
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~ -
EXPLANATION 6..~ ...
~~
.........
'...
-N,-
o
.
«10
.
SCAU It nn
8DII
.
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.. ...... MIl.
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l_-------------
---------_..----~
lMffa .....--
I
I
~
---- Facility/oU boundaries
---- study Area perimeter
- _.- -- ..
Figure 17.
B Zone Plume Boundary at
5 ppb TCE
-------
8.3
REMEDIAL ACTION ALTERNATIVES
Initially, a large number of cleanup methods (technologies) were
screened with respect to their effectiveness, implementability,
and order-of-magnitude cost. The methods which passed this
initial screening were then combined into cleanup alternatives
most applicable to each Operable Unit and evaluated in detail.
8.3.1 .AMD Operable Unit
1"
Approximately 3' cubic yards of residual contaminated soil is
located in the unsaturated zone upqradient of the groundwater
extraction and treatment system. Alternative 1 applies to both
soil and groundwater. Alternatives 2 through 7 specifically
address the soil, and Alternatives 8 through 10 address
groundwater.
AMD Alternative 1: No Action - Monitorina The no action
alternative includes completely stopping operation of the
existing groundwater treatment system which has been
operating for the last 6 years. No additional soil
remediation would be performed. Groundwater monitoring would
continue. Time for the groundwater to achieve compliance
with ARARs is unknown with best estimates in the range of
hundreds of years. The present worth cost is projected to be
$1.5 million.
AMD Alternative 2: Soil Flushina In this alternative,
water would be percolated through contaminated soil to
solubilize VOCs adsorbed to the soil and flush them into the
groundwater. Groundwater would then be treated by an
activated carbon treatment system. This procedure would
reduce the residual concentrations in the soil and increase
the soluble concentrations in the groundwater. It is
estimated this alternative would take hundreds of years to
reduce concentrations of VOCs in soil to the 1 ppm level.
The present worth cost of this alternative is estimated to
be $2.8 million.
AMD Alternative 3: Soil Aeration This alternative consists
of excavating the contaminated soil and tr~nsporting it to
an appropriate treatment area. The soil would be spread out
to a predetermined depth, usually 1 to 3 feet, and
mechanically mixed on a regular basis. The contaminants
would volatilize and be released to the air. Again, it is
estimated this alternative would take hundreds of years to
reduce concentrations of VOCs in soil to the 1 ppm level.
The present worth cost of this alternative is estimated to
be $2.7 million.
Page 75 of 108
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AMD Alternatives 4 throuah 6: Vacuum Extraction eVE): VE
with Heated Air Assist: VE with Steam Assist These three
alternatives involve in situ vacuum extraction whereby VOCs
are removed from the soil by mechanically drawinq or ventinq
air throuqh the unsaturated soil layer. The soil would be
qradually treated as the VOCs are released from the soil
particles. Extraction of the VOC-containinq vapors could be
enhanced by usinq heated air or steam. VOC-laden air would
then be treated with an appropriate treatment system.
Aqain, it is estimated this alternative would take hundreds
of years to reduce concentrations of VOCs in soil to the 1
ppm level. The present worth cost of these alt~rnatives
ranqes from $2.8 to $3.5 million.
AMD Alternative 7: Excavation and Offsite
DisDosal/Treatment In this alternative, the contaminated
soil would be excavated, the buildinq reinforced as needed,
and the excavation backfilled. The excavated 80il would be
treated most likely by incineration and/or disposed offsite.
The concentrations of VOCs in soil can be reduced to the 1
ppm level durinq the duration of the excavation. The present
worth cost of this alternative is estimated to be $2.7
million.
AMD Alternative 8: Extraction - Air StriDDinq with Carbon
Adsorntion of the Offaas This alternative comprises the
current interim remedial treatment system for the
qroundwater (extraction wells, air stripper, and carbon
adsorption of the offqas). Air strippinq as a stand-alone
technoloqy is very effective in removinq VOCs from
qroundwater at the AMD Operable Unit. Carbon adsorption of
the stripper vapor exhaust provides additional treatment.
This alternative is modeled to achieve cleanup standards in
18 years at a present value cost of $2.6 million.
AMD Alternative 9: Extraction - Carbon Adsorntion
Alternative This alternative consists of extraction of
qroundwater usinq the current well system. The extracted
qroundwater could then be passed directly throuqh qranular
activated carbon for adsorption of VOCs. Use of the air
stripper would be discontinued. This alternative would not
change the time to achieve ARARs (18 years) however the
present value cost would increase to $4.6 million.
AMD Alternative 10: Auamented Extraction with Enhanced
Treatment This alternative involves installinq additional
wells on the AMD OU to extract additional qroundwater. The
groundwater would be treated in the existing air stripper
system. An additional carbon adsorption unit would be
installed to provide additional capacity to treat the air
stripper offgas. The increased number of wells would not
result in an increased rate of groundwater extraction,
Page 76 of 108 .
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\
therefore the estimated time to achieve ARARs remains at 18
years. The estimated present value cost of this alternative
is $2.8 million.
AMD Treated Groundwater DisDosal For all three groundwater
remediation alternatives (8 through 10), discharge options
for treated groundwater include: discharge to a publicly
owned treatment works (POTW), discharge to storm drain, and
industrial process applications. currently, AND reuses all
of the treated groundwater in onsite facility uses.
8.3.2
Signetics Operable Unit
Alternatives 1 through 4 combine soil and groundwater remedial
alternatives for the Signetics property.
Sianetics Alternative 1: No Action In this alternative, no
action would be taken to remediate soil or groundwater and
the existing soil-vapor vacuum extraction system would be
shut down. The estimated present value cost of this
alternative is $1.5 million.
Sianetics Alternative 2: No Additional Groundwater or
Vacuum Extraction Alternative 2 comprises the interim
remedial system currently in operation. Groundwater is
extracted using two extraction trenches, six extraction
wells, and three basement dewatering sumps. The existing
soil-vapor vacuum extraction system would continue to
operate. Extracted groundwater would continue to be treated
by air stripping followed by carbon polishing of the
effluent. water. In addition, vapor-phase carbon would
continue to be used to remove residual VOCs from the
effluent air stream from the air strippers. The estimated
present value cost of this alternative is $3.9 million.
Sianetics Alternative 3: Enhanced Groundwater Extraction
This alternative consists of improving the extraction system
to compensate for declining water levels; these declines
have resulted in decreases in contaminant removal rates and
apparent increases in downgradient VOC concentrations. The
existing soil-vapor vacuum extraction system would continue
to operate. The proposed improvements to the groundwater
extraction system are:
o
Increase pumping rate at the 440 Wolfe extraction
trench to decrease the water levels in the trench
o
Install a series of A-aquifer extraction wells north of
the 811 Arques Avenue building
Install piezometers along and north of the 815 stewart
Drive property boundary to assess the current capture
o
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zones
o
Install additional A-aquifer extraction wells
immediately north of the 815 Stewart building, unless
declining water levels preclude extraction
Resume pumping from an existing B1/B2-aquifer
extraction well (5-100B1)
o
o
Initiate groundwater extraction from the B3-aquifer if
onsite VOC concentrations increase siqnificantly.
.
The present value cost of this alternative is $3.9 million.
Sianetics Alternative 4: Enhanced Groundwater lA- and
B-Aauifers) and Vacuum Extraction lA-Aauifer) This
alternative is similar to Alternative 3 except that both the
groundwater and vacuum extraction systems are expanded. The
expanded vacuum extraction system would include four
additional vapor extraction wells and an upgrade of the
blowers and carbon adsorption system. The present value cost
of this alternative is $4.1 million.
8.3.3
TRW Operable 'Unit
Alternatives for remediation of soil have been incorporated into
comprehensive groundwater remediation alternatives for the TRW
property.
TRW Alternative 1: No Action Alternative 1 is a no further
action alternative. All current remedial activities .would
be stopped. The present value cost of this alternative is
$1.0 million.
TRW Alternative 2: CUrrent Groundwater 'Extraction Svstem
With Alternative 2, groundwater extraction from the
7 welll1 educt or system~ groundwater treatment by air
stripping, and groundwater discharge under an NPDES permit
would continue. No additional remedial technology would be
required, although the present system would be upgraded as
part of normal maintenance and replacement. This
alternative would also include deed restrictions on the use
of groundwater in the A- and B-aquifers.
The FS estimates that this alternative would require at
least 7 years of operation to reach compliance with
applicable, relevant, and appropriate requirements (ARARs)
and eleven years to approach non-detect levels of organic
chemicals. The estimated present worth cost of this
alternative is $0.8 million to achieve ARARs and $1.1
million to approach background levels.
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TRW Alternative 3: 50il Flushina and Groundwater
Extraction Alternative 3 combines the components
Alternative 2 with flushinq ot source area soils.
flushinq should increase water saturation ot', and
circulation throuqh, soils, and miqht increase the
for VOC desorption from soils to groundwater, thus
the time for VOC removal from the subsurface soil.
for
Soil
potential
reducinq
The FS estimates that this alternative would require at
least.' years of operation to reach compliance with ARARs
and eleven years to approach non-detect levels ot orqanic
chemicals. The estimated present worth cost of .this
alternative is $0.8 million to achieve ARARs and $1.2
million to approach background levels.
TRW Alternative 4: Partial Excavation and Groundwater
Extraction Alternative 4 consists ot excavatinq the most
hiqhly contaminated soils north and west of the former tank
area, dewaterinq the entire excavated area, and backfillinq
the excavation with clean material. This alternative would'
also include deed restrictions on the use ot groundwater in
the A- and &-aquifers and continued pumpinq, treatment, and
discharqe of groundwater from existinq and two new
extraction wells. This alternative would require
siqnificant enqineerinq controls prior to and durinq
excavation, as well as relocation of operational equipment.
The FS estimates that this alternative would require at
least' years of operation to reach compliance with ARARs
and eleven years to approach non-detect levels of orqanic
chemicals. The estimated present worth cost of this
alternative is $1.6 million to achieve ARARs and $2 million
to approach backqround levels.
8.3.4
Offsite Operable Unit
Remedial alternatives for soil were not addressed for the Offsite
OU because contaminant sources in soil are limited to the
facility properties.
Offsite Alternative 1: No Action The no action alternative
involves no further action to treat, contain, or remove any
of the contaminated groundwater. To implement this.
alternative, planned and existinq remedial measures would be
discontinued. Groundwater monitorinq would continue. Time
for the groundwater to achieve compliance with ARARs is
unknown with best estimates in the ranqe of hundreds of
years. The present worth cost is projected to be $1.9
million.
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Offsite Alternative 2: EXDanded Extraction. Air Striccina.
and Carbon Adsorction: This alternative consists of
continued operation of the existing offsite extraction and
treatment system. The system currently extracts groundwater
from 23 extraction wells. The extracted groundwater is
conveyed through an underground piping system to the
AMD Building 915 treatment facility; the groundwater is
treated by air stripping followed by aqueous carbon
adsorption. CUrrently, about 30' of the treated groundwater
is reused at the AMD facility, with the remainder discharqed
under NPDES permit CA0028797 to the storm drain system. The
spent carbon is removed and regenerated offsite as needed,
approximately every 1.5 years. .
The hydraulic performance evaluation of the extraction
system indicated that because of declining water levels,
hydraulic capture is not being fully maintained in the A-
and B2-aquifers. It is estimated that 5 new A-aquifer
extraction wells (or an extraction trench) and 3 new
B2-aquifer wells may be needed to maintain adequate
capture. Based on results of a simplified model it is
estimated that this alternative could meet groundwater ARARs
in 36 years. The present worth cost for this alternative is
estimated at $4.4 million.
Offsite Alternative 3: Extraction and Carbon Adsorction
This alternative consists of pumping groundwater from the
upgraded offsite extraction systems and treatment of the
water by carbon adsorption. The treated groundwater would
be reused and/or discharged under NPDES permit CA0028797 to
the storm drain system. This alternative differs from
Alternative 2 in that VOC removal is accomplished by means
of a carbon adsorption unit only, rather than by use of a
combined air stripping/carbon adsorption system. The
estimated time to achieve cleanup is 36 years, the same as
Alternative 2. The present worth cost for this alternative
is estimated at $10 million.
'.0
COKPARATIV!: ANALYSZS OF ALTERHATZVES
This section provides an explanation of the nine criteria
select the remedy, and an analysis of the remedial action
alternatives in light of these criteria, highlighting the
advantages and disadvantages of each alternative.
used to
9.1
NINE CRITERIA
The alternatives were evaluated using nine component criteria.
These criteria, which are listed below, are derived from require-
ments contained in the National Contingency Plan (NCP) and CERCLA
Sections 121(b) and 121(c).
Page 80 of 108
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.1.
9.2
2.
overall protection of human health and the environment.
Short term effectiveness in protecting human health and the
environment.
3.
Long-term effectiveness and permanence in protecting human
health and the environment.
4.
Compl~ance with ARARs (ARARs are detailed in Section 7.0).
Use of treatment to achieve a reduction in the toxicity,
mobility or volume of the contaminants.
5.
6.
Implementability.
7.
State acceptance/Support Agency acceptance.
community acceptance.
8.
9.
cost.
ANALYSIS OF ALTERNATIVES
The analysis for two of the nine criteria, State acceptance and
Community acceptance, generally apply equally to all of the
alternatives. Their analysis will be provided at the beginning
of this section.
STATE ACCEPTANCE AND COMMUNITY ACCEPTANCE
The Feasibility Study and the Proposed Plan Fact Sheet were
reviewed by the RWQCB and they concur with EPA's preferred
alternatives, thus providing State acceptance. Based on
questions raised by the community and discussed in the
Responsiveness Summary (Appendix A), there appears to be .
community acceptance for the selected remedies in so far as the
remedies address the groundwater and soil at the AMD, Signetics,
and TRW properties.
There is significant community concern about the potential for
VOCs to volatilize from the offsite groundwater and then migrate
through the soil gas and eventually become concentrated in
confined spaces of buildings in the residential 'area.
Groundwater extraction that proceeds as rapidly as possible is
the selected remedy at all of the sites and addresses this
potential volatilization problem by reducing the concentrations
of contaminants in the groundwater, which, in turn, reduces the
potential for significant levels of VOCs to reach buildings at
the surface. Actual field measurements of the vapor flux at the
soil surface have not indicated a significant problem. Field
measurements will continue and a reassessment of the problem will
be initiated at the 5 year review period, unless the need for
Page 81 of 108
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earlier reassessment is indicated by future field measurements.
At this time, EPA and RwgCB do not believe that selection of an
additional remedial action (e.g., ventilation aids placed in
buildings) will be necessary. For the time being, the community
appears to have accepted this strategy for addressing the
potential volatilization problem.
9.2.1
~ Operable Unit
Of the ten alternatives evaluated for the cleanup of the AMD
property, Alternatives 2 through 7 specifically address the
contaminated soil. Alternatives 8 through 10 specifically
address the contaminated groundwater. Alternative 1 is the no
action alternative for both the soil and the ground water.
9.2.1.1
AMD Soils
AMD Soil:
PROTECTION OF HUMAN HEALTH AND THE ENVIRONMENT
Alternatives 5, 6, and 7 are protective of human health and the
environment because they remove the soil contaminants from the
site either by enhanced vacuum extraction or excavation followed
by offsite treatment and disposal. Only Alternative 7 is
protective in a reasonable time frame. Alternatives 5 and 6
would require hundreds of years to reach the cleanup standard of
1 ppm total VOCs because of the physical properties of some
chemicals of concern, notably DCB and PCE, that make their
removal from soil extremely difficult. Upon implementation,
Alternative 7 will immediately prevent the soil from acting as a
further source of groundwater contamination and will prevent soil
contaminants from vOlatilizing into the soil gas and eventually
migrating into confined spaces of dwellings at the surface.
Without the advantages of heated air or steam assistance
(Alternatives 5 and 6), the vacuum extraction of Alternative 4
would not be effective enough to eliminate the risk from PCE and
DCB. As is the case with Alternatives 4, 5, and 6, Alternative 3
depends on the transfer of chemicals from the soil to vapor. PCE
and DCB are bound too tightly to the soil to be effectively
removed by simple aeration. In addition, the time to reach the
cleanup standards for offsite disposal of the extracted soils in
Alternative 3 would require hundreds of years. Similar physical
chemical properties ot PCE and DeB prevent Alternative 2 trom
effectively removing these contaminants from the soil by using
soil flushing as a form of enhanced groundwater treatment.
Alternative 1 is not protective of human health and the
environment because it would leave all VOC contaminants in place
in the soil.
Page 82 of 108
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AMD soil:
COMPLIANCE WITH ARARS
Alternative 7 is the only 80il remediation alternative that will
comply with all pertinent ARARs identified in Section 7 in a
reasonable amount ot time. It would comply with the RCRA land
disposal restriction by first treating the excavated 80il offsite
with an appropriate technology before disposal. The current
. treatment technology tor removal of the majority ot VOCs in soil
is incineration, which would result in permanent destruction of
the chemicals ot concern. The actual treatment technoloqy will
be determined by LDRs at the time of removal.
Due to the difficulty in implementation of Alternative 7, AMD
will be given up to two years from the adoption of the RWQCB
Order (June 1991) to complete the Alternative 7 soil remedy. All
other alternatives would not comply with 80il ARARs for hundreds
of years.
Alternatives 3 through 6 involve air emissions that come under
regulation by BAAQKD. Emissions from the vapor extraction
alternatives would comply with air ARARs, but Alternative 3
emissions trom onsite soil aeration may not meet BAAQMD
requirements. Alternative 3 would attain the axc ARAR for
injected water.
Because of the difficulty in removing DCB and PCE from soil under
native conditions, compliance with TBCs is questionable for all
of the Alternatives except Alternative 7 due to the length of
time required to reach the soil cleanup criteria of 1 ppm.
Heated air or steam injection (Alternatives 5 and 6) may enhance
the removal rates, however neither is a proven technology and the
same physical limits may still apply. Alternative 7 would
achieve the soil cleanup criteria by removing all soil that
contains above 1 ppm total VOCs.
Alternatives 3 and 7 would also be required to comply with BAAQMD
Rule 8, Regulation 40.
AMD Soil: .REDUCTION OF TOXICITY. MOBILITY. OR VOLUME OF
CONTAMINANTS THROUGH TREATMENT
Alternative 7 provides the greatest reduction in toxicity
mobility and volume of soil contaminants through excavation
followed by contaminant destruction from an incineration
technoloqy. All other treatment alternatives do not affect the
toxicity of the soil contaminants, but they do reduce their
mobility and volume in the 80il.
Like Alternative 7, Alternative 3 reduces soil contaminant
mobility by excavation. Unlike Alternative 7, the mobility and
volume of the contaminants then increases as aeration of the
soils emits the contaminants into the air.
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Air emissions from the vapor extraction remedies would be
controlled by adsorption of the contaminants onto vapor-phase
carbon. Regeneration of the carbon by an incineration technology
would destroy the contaminants, thus providing' the maximum
reduction in toxicity, mobility, and volume for those
contaminants removed from the soil. Because of physical and
chemical limitations, it would require hundreds of years to
remove enough contaminants from the soils by vapor extraction or
aeration to reduce the total VOCs down to 1 ppm.
Alternative 1 provides no reduction in toxicity, mobility, or
volume.
AMD Soil:
LONG-TERM EFFECTIVENESS AND PERMANENCE
Alternative 7 provides the best long-term effectiveness of
all the alternatives for soil cleanup because the soil
contaminants are removed from the site and eventually destroyed
at an offsite treatment and disposal facility. Removal will
prevent the soil from acting as a further source of groundwater
contamination and will prevent soil contaminants from
volatilizing into the soil gas and eventually migrating into
confined spaces of dwellings at the surface.
Alternative 3 is a reliable way of eliminating the soil as a
source of groundwater contamination, although it would leave
contaminants onsite during the aeration process. However, the
time to reach the cleanup standard for offsite disposal is
estimated to be hundreds of years. This is a function of the
physical properties of some chemicals of concern, notably DCB and
PCE, that makes their removal from soil difficult.
Alternatives 4 through 6 are all dependent upon the transfer of
chemicals from soil to vapor, as is Alternative 3. Alternative 4
would not effectively remove PCE or DCE. Alternatives 5 and 6
are evolving technologies and pilot tests at the site would be
needed to determine their effectiveness. They would remove
volatile contaminants but might leave elevated levels of DCB in
the soil.
Vapor exhaust for Alternatives 4 through 6 would be controlled by
carbon adsorption which is an adequate'and reliable technology-
Contaminant residues on the carbon would be destroyed during
regeneration of the carbon by an incineration technology.
Alternative 2, soil flushing, would take an excessively "long time
to reach the proposed cleanup level of 1 ppm for total VOCs. This
is exacerbated by the low solubilities of some of the chemicals
of concern, particularly DCB.
Alternative 1 provides no long-term effectiveness.
Page 84 of 108
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AMD Soil: SHORT-TERM EFFECTIVENESS
Alternatives l and 2 do not increase the risk to the community
because dovngradient monitoring would alert the community to
possible VOC migration to leading edge wells. The plume would
continue to migrate under Alternative 1.
Alternatives 4 through 6 would cause a minor increased risk
exposure to workers during the construction activities necessary
to install the vapor extraction system.
Alternatives 3 and 7 involve soil excavation which would increase
the chances of exposure of workers and the community to
contaminated dust and volatilized contaminants in the air near
the site.
Due to the difficulty in implementation of Alternative 7, AMD
will be given up to two years from the adoption of the RWQCB
Order (June 1991) to complete the soil remedy. This possible
delay is still protective of human health and the environment on
the short-term because, at this time, the majority of soil in
question is protected from infiltrating surface water by
concrete. This soil is also prevented from coming into direct
contact with the water table by operation of the AMD 901
groundwater extraction system. This extraction system also
controls the migration of contaminated water from the site. This
alternative can achieve Board guidance of 1 ppm total VOCs
immediately upon completion of the removal action.
AMD Soil: IMPLEMENTABILITY
Alternative 1 would be easiest to implement since it requires no
action.
Treatment Alternatives 4 through 6 would be easiest to implement
because they involve in situ technologies. Alternatives 5 and 6
might be slightly more difficult to implement than Alternative 4
because they represent evolving variations of simple vacuum
extraction and pilot tests would be necessary. Permit
requirements can be readily attained.
Alternatives 3 and 7 are not easily implemented because they
would require that operations in the building be temporarily
halted, and adequate construction controls (including dust
minimization) would be needed. Due to the difficulty in
implementation, AMD will be given up to two years from the
adoption of the RWQCB Order (June 1991) to complete the soil
remedy. Permit requirements should be readily attained.
Page 85 of 108
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Like Alternative 7, Alternative 3 is not easily implemented
because it will require that operations in the building be
temporarily halted, and adequate construction controls (including
dust minimization) would be needed. It is unlikely that BAAQMD
permit requirements could be met.
Alternative 2 would be very difficult to implement because
reinjection of the qroundwater would be required. The clay soil
structure at this site would tend to channel the injected water
and, thus -it may not be possible to implement soil flushing
effectively.
AMD Soil:
~
The FS provided cost fiqures for the soil remedies as if
qroundwater monitoring and qroundwater extraction and treatment
would continue for 18 years without any changes to the present
system at AMD 901. The 18-year present worth cost of these
qroundwater activities is $2.6 million based on an annual O&M of
$225,000. The following discussion of costs for soil remedies
has subtracted out theqroundwater costs since they are dealt
with in the analysis of qroundwater remedies for AMD 901 in
Section 9.2.1.2.
Alternative 1 would leave the soil in place without any treatment
or other action. It thus has no costs associated with the soil
portion of the Alternative. Groundwater monitoring would
continue and the associated costs are discussed with the
qroundwater remedies.
The least expensive soil remedies involve excavation and either
offsite treatment and disposal (Alternative 7) or onsite
treatment arid disposal (Alternative 3). While Alternative 3 has
a lower capital cost of $27,000 compared to $47,000 for
Alternative 7, the $6,000 annual O&M cost makes Alternative 3
twice as expensive as Alternative 7, which has no O&M costs. The
18-year present worth costs of Alternatives 3 and 7 are $96,000
and $47,000, respectively. Alternative 7 is the most cost
effective of all the treatment alternatives.
Alternatives 2 and 4 have nearly identical present worth costs
at, $224,000 and $225,000, respectively. Like Alternative 3,
neither ot the.. two alternatives is effective enough to
adequately address the contaminated soil. Alternative 2 has a
capital coat of $86,000 and an annual O'M cost of $12,000, while
Alternative 4 has a capital cost of $63,000 and an annual O&M
cost of $14,000.
The most expensive alternatives involve enhancements of the pure
vacuum extraction offered in Alternative 4. The hot air assist
in Alternative 5 and the steam assist in Alternative 6 have
present worth costs of $327,000 and $943,000, respectively.
Page 86 of 108
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Alternative 5 has a capital cost of $73,000 and an annual O&M
cost of $22,000. The capital cost and annual o&M cost for
Alternative 6 are $122,000 and $71,000, respectively. The cost
estimates for these alternatives are based on 18 years of O&M,
although effective cleanup of the soils by these alternatives
would take much longer than 18 years.
9.2.1.2 AMD Groundvater
AMD GW: PROTECTION OF HUMAN HEALTH AND THE ENVIRONMENT
Alternatives 8, 9, and 10 basically provide equal protection of
human health and the environment because they both extract
groundvater that contains contaminants at concentrations above
drinking water standards and capture the contaminants on either
vapor-phase or liquid-phase carbon followed by their destruction
during carbon regeneration. Extraction prevents further
migration of the plume. Deed restrictions protect against use of
the aquifers before cleanup is completed. After cleanup, these
alternatives are estimated to result in a reduced cancer risk
range, as discussed in Section 8.2.1, of 3.7 X 10"* to 6 X 104 and
a reduced HI of 0.44. All treated water is reused before
ultimate discharge to the sanitary sewer.
Air emissions from Alternatives 8 and 10 are considered
sufficiently protective since they meet BAAQMD permit
requirements while the calculated worst case cancer risk is 1.6 X
10-* and the HI is less than 1.
Alternative 1 provides little reduction of risk since natural
attenuation of groundwater contaminant concentrations could
require more than 100 years compared to the approximately 18 year
cleanup time for Alternatives 8, 9 and 10. While future use of
the contaminated groundwater may be unlikely, a future user of
the contaminated groundwater would be exposed to a cancer risk of
5 X 10'1 and an HI much greater than 1. Finally, Alternative 1 is
least protective of human health and the environment because it
does not include deed restrictions and thus, greatly increases
the chances that an individual will install a well into a
migrating plume.
AMD GW: COMPLIANCE WITH ARARS
Alternative* 8, 9 and 10 would attain all pertinent ARARS iden-
tified in Section 7. The Safe Drinking Water Act MCLs and
California Department of Health Services DWALs would be achieved
by extracting groundwater contaminated above these levels. The
Fish and Wildlife Coordination Act would not be an ARAR for these
alternatives because the groundwater extraction system would
prevent the plume from reaching surface waters or wet lands and
the treatment system would ensure that discharged water was
Page 87 of 108
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protective of human health and the environment.
The RCRA land disposal restrictions would apply to the spent car-
bon from Alternative 8, 9 and 10. The spent carbon would be
treated before reuse or disposal by an incineration process.
Only Alternatives 8 and 10 would need to comply with OSWER
Directive 9355.0-28 and BAAQMD Requlation 8, Rule 47 because of
the air st~ipper emissions. These ARARs are addressed by the
BAAQMD permitting process, and the air strippers bave emissions
control.
The drinking water ARARS would not be attained' by Alternative i
since contamination would be left in place. The Fish and
Wildlife Coordination Act would become an ARAR if the plume
migrated to Guadelupe Slough and other tributary streams and
marshes. California's resolution 68-16 would not be achieved
since the groundwater contaminants would unreasonably affect the'
present .nd potential uses of the upper aquifers. RCRA land
disposal restrictions, BAAQMD Requlation 8, and OSWER Directive
9355.0-28 would not apply to Alternative 1 since it does not use
treatment.
AMD GW:
REPUCTION OF TOXICITY. MOBILITY. OR VOLUME OF
CONTAMINANTS THROUGH TREATMENT
Alternatives 8, 9 and 10 reduce the toxicity, mobility, and
volume of groundwater contaminants by removing greater than 99%
of the contaminants from the extracted groundwater. They
concentrate the contaminants onto granular activated carbon,
which would then be regenerated or properly disposed at a
landfill. Contaminants could potentially be destroyed during
carbon regeneration, making any future release of the removed
contaminants impossible.
Alternative 1 does not reduce toxicity, mobility, or volume since
the groundwater contaminants are allowed to continue migrating.
AMD GW:
LONG-TERM EFFECTIVENESS AND PERMANENCE
Alternatives 8, 9 and 10 include groundwater extraction which is
intended to reduce the level of contamination in the A and B
Aquifer Zones to the cleanup standards indicated in Section 8.2.
Thus, potential risks to the community currently posed by the
site in its present condition are minimized. To ensure that the
maqnitude of residual risks are minimized, the performance of the
groundwater extraction system will be carefully monitored on a
reqular basis and adjusted as warranted by the performance data
collected during operation.
The potential future risk from long-term exposure to volatilized
contaminants that are emitted from the soil and accumulate inside
Page 88 of 108 .
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1-"
residences is addressed by the groundwater extraction system in
Alternatives 8, 9 and 10. Groundwater extraction reduces the
amounts of contaminants that could volatilize into the soil qas
and eventually into surface air. Furthermore, deed restrictions
will prevent the installation of wells in the on-site portion of
the plume until it is cleaned up. Finally, this newly recognized
potential problem will be much better understood by the time the
first five-year review occurs. Fans or other active or passive
ventilation aids could be provided to any affected buildinqs in
addition to continuation of deed restrictions.
Treatment by air strippinq provided by Alternatives'8 and 10 is
reliable for the lonq-term removal of VOCs from the groundwater.
Treatment residuals are expected to be neqliqible based on the
hiqh volatility of the compounds present in the groundwater and
their capture by the vapor-phase carbon after air strippinq.
Treatment by aqueous phase granular activated carbon provided by
Alternative 9 is reliable for the removal of VOCs from the
groundwater. Treatment residuals are expected to be neqliqible
since they will be concentrated on a relatively small amount of
carbon that will either be properly disposed in a landfill or
reqenerated by a destructive technoloqy. If vinyl chloride is
produced as a degradation product from TCE or DCE, it will not be
effectively trapped on the carbon employed in any of the
treatment alternatives.
Alternative 1 provides no lonq-term effectiveness.
AMD GW:
SHORT-TERM EFFECTrvENESS
The short-term impact to the health of workers and the community
will be very minimal for Alternatives 8, 9 and 10 because the
qroundwater extraction system is already in place as the interim
remedial action at the site. There would be no current addi-
tional risks since the plume is already contained and the treat-
ments are protective. Groundwater cleanup time is estimated to
require about. 18 years.
Alternative 1 does not include the implementation of treatment
remedies; therefore, there are no additional risks to the
community. Risks associated with the contaminant plume would
remain at the site for over 100 years until natural attenuation
reduces the contaminant concentrations down to the cleanup stan-
dards.
AMD GW:
IMPLEMENTABILITY
Alternatives 8 and 9 include the same extraction system which is
already in place. Alternative 10 would auqment the extraction
system by the installation of additional extraction wells and
paqe 89 of 108
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emissions-control carbon canisters. These alternatives provide
qroundwater treatment with either an air stripper or carbon
adsorption. Both methods are proven technologies and there are
no technical considerations that prohibit the use of either of
these technologies. In addition, these alternatives are
administratively feasible using existing permits for air
emissions.
Alternativ~ 8 is the easiest to implement since it is already
implemented as the interim remedy at the site. Alternatives 9
and 10 would require modifications to the present extraction
and/or treatment system, but their implementation would still be
relatively easy~ Institutional controls required in Alternatives
8, 9, and 10 are administratively feasible.
There are no technical concerns regarding the implementability of
Alternative 1.
AMD GW:
~
Based on an estimated 18 years to cleanup the A Aquifer and 9
years for the B Aquifer, costs of Alternatives 8, 9 and 10 are
significantly qreater than the 30 years of groundwater monitoring
in Alternative 1. Alternative 8 is the most cost effective since
it will meet all cleanup requirements for a present worth cost of
2.6 million dollars compared to the 2.8 million dollar present
worth cost of Alternative 10 and the 4.6 million dollar present
worth cost of Alternative 9. Alternative 1 has a present worth
cost of 1.5 million dollars, but would be ineffective for
cleanup.
Alternatives 1 and 8 have no capital costs while Alternatives 9
and 10 have capital costs of 37 and 53 thousand dollars,
respectively.
The annual O&M costs for Alternatives 8 and 10 are nearly
identical at 225 and 239 thousand dollars, respectively. The
large amount of carbon for Alternative 9 gives it an annual O&M
cost of 382 thousand dollars. Alternative 1 represents the
annual cost of qroundwater monitoring at 100 thousand dollars.
9.2.2
Signetics Operable Unit
Signetics:
PROTECTION OF HUMAN HEALTH AND THE ENVIRONMENT
Alternatives 2, 3, and 4 basically provide equal protection of
human health and the environment because they all extract
groundwater that contains contaminants at concentrations above
drinking water standards, they all extract contaminants from soil
gas using vapor extraction, and they all capture the contaminants
on vapor-phase carbon followed by contaminant destruction during
Page 90 of 108
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carbon regeneration. Groundwater extraction prevents further
miqration of the plume. Deed restrictions protect against use of
the aquifers before cleanup is completed. After cleanup, as
discussed in Section 8.2.1, these alternatives are estimated to
result in a reduced cancer risk range of 3.7 X 10 ~ to 6 X 10~
and a reduced HI of 0.44. All treated water is reused before
ultimate discharge to the sanitary sewer or irrigated landscape.
Air emissigns from Alternatives 2, 3 and 4 are considered
sufficiently protective since they meet BAAQMD permit
requirements while the calculated worst case cancer risk is 1.5
X 10~ and the HI is less than 1. Air stripper emissions are
qreatly reduced by the vapor-phase carbon control units.
Emissions from the soil vapor extraction system are captured by
carbon control units. Emissions to ambient air are essentially
nil and do meet BAAQMD requirements
Alternative 1 provides little reduction of risk since natural
attenuation of qroundwater contaminant concentrations could
require more than 100 years compared to the approximately 24-36
year cleanup time for Alternatives 2, 3 and 4. While future use
of the contaminated qroundwater may be unlikely, a future user of
the contaminated qroundwater would be exposed to a cancer risk of
5 X 10.1 and an HI much greater than 1. Finally, Alternative 1 is
least protective of human health and the environment because it
does not include deed restrictions and thus, qreatly increases
the chances that an individual will install a well into a
migrating plume.
Signetics:
COMPLIANCE WITH ARARS
Alternatives 2, 3 and 4 would attain all pertinent ARARS iden-
tified in Section 7. The Safe Drinking Water Act MCLs and
California Department of Health Services DWALs would be achieved
by extracting qroundwater contaminated above these levels. The
Fish and Wildlife Coordination Ac~ would not be an ARAR for these
alternatives because the qroundwater extraction system would
prevent the plume from reaching surface waters or wet lands and
the treatment system would ensure that discharged water was
protective of human health and the environment.
The RCRA land disposal restrictions would apply to the spent car-
bon from Alternative 2, 3 and 4. The spent carbon would be
treated before reuse or disposal by an incineration process.
Alternatives 2, 3 and 4 would need to comply with OSWER Directive
9355.0-28 and BAAQMD Requlation 8, Rule 47 because of the air
stripper emissions. These ARARs are addressed by the BAAQMD per-
mitting process and the air strippers have emissions control.
The drinking water ARARS would not be attained by Alternative 1
Page 91 of 108
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since contamination would be left in place. The Fish and
Wildlife Coordination Act would become an ARAR if the plume
migrated to Guadelupe Slough and other tributary streams and
marshes. California's resolution 68-16 would not be achieved
since the groundwater contaminants would unreasonably affect the
present and potential uses of the upper aquifers. RCRA land
disposal restrictions, BAAQMD Regulation 8, and OSWER Directive
9355.0-28 would not apply to Alternative 1 since it does not use
treatment.
Siqnetics:
REDUCTION OF TOXICITY. MOBILITY. OR VOLUME OF
CONTAMINANTS THROUGH TREATMENT
Alternatives 2, 3 and 4 reduce the toxicity, mobility, and volume
of groundwater contaminants by removing greater than 99' of the
contaminants from the extracted groundwater. They concentrate
the contaminants onto granular activated carbon, which would then
be regenerated or properly disposed at a landfill. Contaminants
could potentially be destroyed during carbon regeneration, making
any future release of the removed contaminants impossible.
Alternative 1 does not reduce toxicity, mobility, or volume since
the groundwater contaminants are allowed to continue migrating.
Signetics:
LONG-TERM EFFECTIVENESS AND PERMANENCE
Alternatives 2, 3 and 4 include groundwater extraction which is
intended to reduce the level of contamination in the A and B
Aquifer Zones to the cleanup standards indicated in Section 8.2.
Thus, potential risks to the community currently posed by the
site in its present condition are minimized. To ensure that the
magnitude of residual risks are minimized, the performance of the
groundwater extraction system will be carefully monitored on a
regular basis and adjusted as warranted by the performance data
collected during operation.
The potential future risk from long-term exposure to volatilized
contaminants that are emitted from the soil and accumulate inside
residences is addressed by the groundwater extraction and soil
vapor extraction systems in Alternatives 2, 3 and 4. These
extractions reduce the amount of contaminants that could
volatilize into the soil gas and eventually into surface air.
Furthermore, deed restrictions will prevent the installation of
wells in the on-site portion of the plume until it is cleaned up.
Finally, this newly recoqnized potential problem will be much
better understood by the time the first five-year review occurs.
Fans, other ventilation aids, or passive ventilation aids could
be provided to any affected buildings in addition to the above
deed restrictions.
Treatment by air stripping provided by Alternatives 2, 3 and 4 is
reliable for the long-term removal of VOCs from the groundwater.
Page 92 of 108
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I____~
Treatment residuals are expected to be neqliqible based on the
hiqh volatility of the compounds present in the groundwater and
their capture by the vapor-phase carbon after air strippinq. If
vinyl chloride is produced as a degradation product from TCE or
DCE, it will not be effectively trapped on the carbon employed in
any of the treatment alternatives.
Alternative 1 provides no lonq-term effectiveness.
Siqnetics:
SHORT-TERM EFFECTIVENESS
The short-term impact to the health of workers and the community
will be very minimal for Alternative 2 because the groundwater
extraction and soil vapor extraction systems are already in place
as the interim remedial action at the site. Alternatives 3 and 4
would involve the installation of some additional wells at only a
very minor risk from drillinq activities to the drillers. For
all of these alternatives there would be no current additional
risks since the plume is already contained and the treatments are
protective. Groundwater cleanup time is estimated to require
about 24-36 years.
Alternative 1 does not include the implementation of treatment
remedies; therefore, there are no additional risks to the
community. Risks associated with the contaminant plume would
remain at the site for over 100 years until natural attenuation
reduces the contaminant concentrations down to the cleanup stan-
dards.
Siqnetics:
IMPLEMENTABILITY
Alternative 2 includes the same extraction system which is
already in place. Alternatives 3 and 4 would auqment the
extraction system by the installation of additional extraction
wells and emissions-control carbon canisters. These alternatives
provide groundwater treatment with an air stripper followed by
vapor-phase carbon adsorption. Both methods are proven
technoloqies and there are no technical considerations that
prohibit the use of either of these technoloqies. In addition,
these alternatives are administratively feasible usinq existinq
permits tor air emissions.
Alternative 2 is the easiest to implement since 'it is already
implemented as the interim remedy at the site. Alternatives 3
and 4 would require modifications. to the present extraction
system, but their implementation would still be relatively easy.
Institutional controls required in Alternatives 2, 3, and 4 are
administratively feasible.
There are no technical concerns reqardinq the implementaDility of
Alternative 1.
paqe 93 of 108
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Signetics:
~
Based on an estimated 13 years to cleanup the A Aquifer and 36
years for the B Aquifer usinq Alternative 2 and based on an
estimated 8 years to cleanup the A Aquifer and 24 years for the B
. Aquifer usinq Alternatives 3 or 4, total costs for treatment
alterna~ives are significantly greater than the 30 years of cost
for groundwater monitorinq in Alternative 1. Alternative 4 is
the most cost effective since it will most rapidly meet all
cleanup requirements for a present worth cost of 4.1 million
dollars compared to the 3.9 million dollar present worth costs of
Alternatives 2 and 3. Essentially, the additional 0~2 million
dollar cost of Alternative 4 supports the accelerated remediation
of hot spots. Alternative 1 has a present worth cost of 1.5
million dollars, but would be ineffective for cleanup.
Alternatives 1 and 2 have no capital costs while Alternatives 3
and 4 have capital costs of 252 and 351 thousand dollars,
respectively.
The annual O&M costs for Alternatives 2, 3, and 4 are nearly
identical at 236, 236 and 246 thousand dollars, respectively.
Alternative 1 represents the annual cost of groundwater
monitorinq at 95 thousand dollars.
9.2.3
TRW Operable unit
PROTECTION OF HUMAN HEALTH AND THE ENVIRONMENT
TRW:
Alternatives 2, 3 and 4 are protective of human health and the
environment to rouqhly the same deqree because they extract
qroundwater that contains contaminants at concentrations above
drinkinq water standards. Extraction prevents further miqration
of the plume. Deed restrictions protect against use of the
aquifers before cleanup is completed. After cleanup, as
discussed in Section 8.2.1, all three alternatives are estimated
to result in a reduced cancer risk ranqe of 3.7 X 10~ to 6 X lO~
and a reduced HI ranqe of 0.44 to 0.1 related to domestic use of
groundwater. Any un-recycled treated effluent would meet NPDES
discharqe requirements which are protective of human health and
the envirQnment.
Alternatives 3 and 4, which take a more active role in addressing
the contaminated soil in the saturated A Zone, would not provide
siqnificantly greater protection of human health and the
environment since the location of the contaminated soil is
downgradient from contaminated qroundwater at the AMD 901/902
property and would likely be recontaminated until the upqradient
contamination is cleaned up.
Alternatives 2,3 and 4 all would use air-strippinq to treat the
paqe 94 of 108
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extracted groundwater. The use of an air-stripper is considered
to be sufficiently protective since it does satisfy BAAQMD
requirements which is the appropriate ARAR and would result in an
estimated increased cancer risk of about 1.79 X 10~.
Alternative 1 provides no reduction in risk because it allows the
contaminated groundwater to continue migrating. Natural
attenuation of the groundwater contaminant concentrations could
require more than 100 years compared to the approximately 7 year
cleanup time for the other alternatives. While future use of the
contaminated groundwater may be unlikely, a future user of the
contaminated groundwater would be exposed to a maximum cancer
risk of 5 X 10.1 and an HI much greater than 1. Alternative 1 is
thus the least protective of human health and the environment.
TRW:
COMPLIANCE WITH ARARS
Alternatives 2, 3 and 4 would attain all pertinent ARARS
identified in Sect~on 7. The Safe Drinking Water Act MCLs and
the California Department of Health Services DWALs would be
achieved in approximately 7 years by extracting groundwater
contaminated above these levels. NPDES permit requirements would
be met by proper desiqn and operation of the treatment system.
Closure requirements would be met by achieving MCLs in the
groundwater. The Fish and Wildlife Coordination Act would not be
an ARAR for these three alternatives because the groundwater
extraction system would prevent the plume from reaching surface
waters or wet lands and the treatment system would ensure that
any discharged water was protective of human health and the
environment.
The RCRA land disposal restrictions would apply to the spent
carbon from Alternatives 2, 3 and 4 in the event that it became
necessary to implement air stripper emissions control involving
gas-phase activated carbon. The spent carbon could be treated
before reuse or disposal by an incineration process.
Alternatives 2, 3 and 4 would need to comply with OSWER Directive
9355.0-28 and.BAAQMD Regulation 8 Rule 47 because of the air
stripper emissions. These ARARS are addressed by the BAAQMD
permitting process. If permit modifications become necessary,
emissions could be captured and destroyed by available
technology. Alternative 4 might also be required to comply with
mass emission standards in BAAQMD Rule 40, Regulation 8.
Alternative 1 would not comply with drinking water ARARS for at
least 100 years since contamination would be free to migrate.
The Fish and Wildlife Coordination Act would become an ARAR if
the plume migrated to a surface water or other tributary streams
and marshes. California's resolution 68-16 would not be achieved
since the groundwater contaminants would unreasonably affect the
Page 95 of 108
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present and potential uses of the upper aquifers. RCRA land
disposal restrictions, NPDES requirements, BAAQMD Regulation 8,
and OSWER Directive 9355.0-28 would not apply to Alternative 1
since it' does not use treatment.
REDUCTION OF TOXICITY. MOBILITY. OR VOLUME OF
CONTAMINANTS THROUGH TREATMENT
Alternatives 2, 3 and 4 reduce the toxicity, mobility, and volume
(TMV) of groundwater contaminants by removing qreater than 99% of
the contaminants from the extracted groundwater. However, these
alternatives transfer the groundwater contaminants ~o the air
where their toxicity, mobility and volume as air contaminants
actually increases. In addition, some of the VOCs are ozone
precursors. The current air stripper is operating under a BAAQMD
permit that does not require emissions control.
TRW:
Alternative 3 may provide slightly less reduction in VOC mobility
because possible loss of complete hydraulic control as a result"
of soil flushing may increase the mobility of the VOCs.
Alternative 4 may provide slightly greater reduction in TMV if
the small volume of extracted soil is treated with a destructive
technology prior to disposal. Alternative 1 provides no
reduction in TMV.
TRW:
LONG-TERM EFFECTIVENESS AND PERMANENCE
Alternatives 2, 3 and 4 include groundwater extraction which is
intended to reduce the level of contamination in the A and B
Aquifer Zones to the cleanup standards indicated in Section 8.2.
Thus, potential risks to the community currently posed by the
site in its present condition are minimized. To ensure that the
magnitude of residual risks are minimized, the performance of the
groundwater extraction system will be carefully monitored on a
regular basis and adjusted as warranted by the performance data
collected during operation. Although soil flushing in
Alternative 3 is a proven technology, effectiveness at this site
is uncertain.
The potential future risk from long-term exposure to volatilized
contaminants that are emitted from the soil and accumulate inside
residences is addressed by the groundwater extraction system in
Alternatives 2, 3 and 4. Groundwater extraction that proceeds as
rapidly as possible addresses this potential volatilization
problem by reducing the concentrations of contaminants in the
groundwater, which, in turn, reduces the potential for
significant levels of VOCs to reach buildings at the surface.
Actual field measurements of the vapor flux at the soil surface
have not indicated a significant problem. Field measurements
will continue and a reassessment of the problem will be initiated
at the 5 year review period, unless the need for earlier
reassessment is indicated by future field measurements. Fans or
Page 96 of 108
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other ventilation aids could be provided to any affected
buildings. Furthermore, deed restrictions will prevent the
installation of wells in the onsite portion of the plume until it
is cleaned up.
Treatment by air stripping provided by Alternatives 2, 3, and 4
is reliable for the long-term removal of VOCs from the
groundwater. Treatment residuals are expected to be negligible
. based on ~e high volatility of the compounds present in the
groundwater. .
Alternative 1 would provide long-term effectiveness "after more
than 100 years that would be necessary for natural attenuation.
Offsite monitoring may not be reliable for detecting further
downgradient migration. Alternative 1 provides very little lonq-
term effectiveness in comparison to the other three alternatives.
TRW:
SHORT-TERM EFFECTIVENESS
The short-term impact to the health of workers and the community
will be very minimal for the groundwater portion of Alternatives
2, 3 and 4 because the extraction and treatment system is already
in place as the interim remedial action at the site. There would
be no current additional risks since the plume is already
contained and the treatments are protective. Groundwater cleanup
is estimated to require about 7 years.
Alternative 4 is slightly less effective on the short-term than
Alternatives 2 and 3 because of the increased dust containing
VOCs and VOC emissions during excavation of the small volume of
contaminated soil in the saturated zone.
Alternative 1 doesn't include the implementation of a treatment
remedy; therefore, there are no additional risks to the
community. Risks associated with the contaminant plume would
remain at the site for over 100 years until natural attenuation
reduces the contaminant concentrations down to the cleanup
standards.
TRW:
IMPLEMENTABILITY
Alternatives 2, 3 and 4 are easily implemented for the
groundwater extraction and treatment system since it is already
implemented with the required permits in place. Additional
permits would be required tor soil flushing in Alternative 3, but
should be readily obtainable. Institutional controls required
in Alternatives 2, 3 and 4 are administratively feasible.
Excavation is a proven technology, however excavation near a
building poses severe logistical problems for FEI Microwave, the
current occupants of the TRW onsite area. This significantly
lowers the implementability of the soil portion of Alternative 4.
Page 97 of 108 .
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In Alternatives 2 and 3, the soil is addressed by the qroundwater
extraction and treatment system. There are no technical concerns
. reqardinq the implementability of Alternative 1.
TRW:
~
Alternatives 2 and 3 have nearly identical costs. Alternative 2
is sliqhtly less expensive with a present worth cost of $750,379
compared to $827,379 for Alternative 3. Due to the difficulty of
the soil excavation near a buildinq, Alternative 4 is
dramatically more expensive with a present worth cost of 1.6
million dollars. Alternative 1 is the second most expensive
alternative because qroundwater monitorinq would be needed well
beyond the 7 year cleanup time estimated for the other
alternatives. For a 30 year monitorinq period, the present worth
cost would be $984,893.
9.2.4
Offsite Operable Unit
Offsite:
PROTECTION OF HUMAN HEALTH AND THE ENVIRONMENT
Alternatives 2 and 3 basically provide equal protection of human
health and the environment because they both extract qroundwater
that contains contaminants at concentrations above drinkinq water
standards. Extraction prevents further miqration of the plume
and continually reduces the contaminant concentrations, thus
continually decreasinq the potential for volatilized VOCs to
reach siqnificant concentrations inside surface dwellinqs. After
cleanup, as discussed in Section 8.2.1, both Alternatives 2 and 3
are estimated to result in a reduced cancer risk ranqe of 3.7 X
10~~3 X 10~ and a reduced HI ranqe of 0.44 to 0.2. Water
discharqed or reused followinq treatment would meet NPDES
requirements which are protective of human health and the
environment.
Alternative 3 could be considered sliqhtly more protective than
Alternative 2 since it would not involve the transfer of
qroundwater contaminants to the air and would involve the
destruction of the contaminants by -reqeneration of the qranular
activated carbon. Air emissions from Alternative 2 are
considered sUfficiently protective, however, since they meet
BAAQMD permit requirements, while the calculated worst case
cancer risk less than 1 X 10~ and the HI is less than 1.
Alternative 1 provides far less reduction in risk because it
would allow the contaminated qroundwater to continue miqrating
and natural attenuation of qroundwater contaminant concentrations
could require more than 100 years compared to the approximately
36 year cleanup time for Alternatives 2 and 3. While future use
of the contaminated qroundwater may be unlikely, a future user of
the contaminated qroundwater would be exposed to a cancer risk of
Page 98 of 108
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5 X 10.1 and an HI much greater than 1. Al ternati ve 1 is least
protective of human health and the environment, because it does
not include deed restrictions, and thus greatly increases the
chances that an individual will install a well into a migrating
plume.
Offsite:
COMPLIANCE WITH ARARS
Both Alternatives 2 and 3 would attain all pertinent ARARS iden-
tified in Section 7. The Safe Drinking Water Act MCLs and
California Department of Health Services DWALs would be achieved
by extracting groundwater contaminated above these levels. NPDES
permit requireaents would be met by proper design and operation
of either treatment system. The Fish and Wildlife Coordination
Act would not be an ARAR for Alternatives 2 and 3 because the
groundwater extraction system would prevent the plume from
reaching surface waters or wet lands and the treatment system
would ensure that discharged water was protective of human health
and the environment. .
The RCRA land disposal restrictions would apply to the spent car-
bon from Alternative 3 and would also apply to Alternative 2 in
the event that it became necessary to implement air stripper
emissions control involving gas-phase activated carbon. The
spent carbon could be treated before reuse or disposal by an in-
cineration process.
Only Alternative 2 would need to comply with OSWER Directive
9355.0-28 and BAAQMD Regulation 8, Rule 47 because of the air
stripper emissions. These ARARs are addressed by the BAAQMD per-
mitting process. If permit modifications become necessary, emis-
sions could be captured and destroyed by available technology.
The drinking water ARARS would not be attained by Alternative 1
since contamination would be left in place for at least 100
years. The Fish and Wildlife Coordination Act would become an
ARAR if the plume migrated to Guadelupe Slough and other
tributary streams and marshes. California's resolution 68-16
would not be achieved since the groundwater contaminants would
unreasonably affect the present and potential uses of the upper
aquifers. RCRA land disposal restrictions, NPDES requirements,
BAAQMD Regulation 8, and OSWER Directive 9355.0-28 would not
apply to Alternative 1 since it does not use treatment.
Offsite:
REDUCTION OF TOXICITY. MOBILITY. OR VOLUME OF
CONTAMINANTS THROUGH TREATMENT
Both Alternatives 2 and 3 reduce the toxicity, mobility, and
volume of groundwater contaminants by removing greater than 99%
of the contaminants from the extracted groundwater. Alternative
3 concentrates the contaminants onto granular activated carbon,
Page 99 of 108
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which would then be reqenerated or properly disposed at a
landfill. Contaminants could potentially be destroyed durinq
carbon regeneration, making any future release of the removed
contaminants impossible.
. Alternative 2 transfers the qroundwater contaminants to the air
where their toxicity, mobility, and volume as air contaminants
actually increases. In addition, some of the VOCs are ozone
precursors.. The current air stripper is operatinq under a BAAQMD
permit that does not require emissions control. A very tiny
fraction of the qroundwater contaminants will be captured on the
carbon polisher and would be destroyed during reqeneration or .
treated before disposal at a proper landfill.
Alternative 1 does not reduce toxicity, mobility, or volume of
the qroundwater contaminants because they are allowed to continue
miqratinq. -
Offsite:
LONG-TERM EFFECTIVENESS AND PERMANENCE
Alternatives 2 and 3 include qroundwater extraction which is in-
tended to reduce the level of contamination in the A and B
Aquifer Zones to the cleanup standards indicated in Section 8.2.
Thus, potential risks to the community currently posed by the
site in its present condition are minimized. To ensure that the
magnitude of residual risks are minimized, the performance of the
groundwater extraction system will be carefully monitored on a
reqular basis and adjusted as warranted by the performance data
collected durinq operation.
The potential future risk from long-term exposure to volatilized
contaminants that are emitted from the soil and accumulate inside
residences is addressed by the groundwater extraction system in
Alternatives 2 and 3. Groundwater extraction reduces the amounts
of contaminants that could volatilize into the soil gas and even-
tually into surface air. The RWQCB has required the PRPs to
continue measuring soil vapor emissions from selected points
along a plume cross-section on a semi-annual basis for at least
two years. This newly recognized potential problem will be much
better understood by the time the first five-year review occurs.
If necessary, more refined air sampling could be conducted at
that time. Fans or other ventilation aids could be provided to
any affected buildings.
Treatment by air stripping provided in Alternative 2 is reliable
for the long-term removal of VOCs from the qroundwater. Treat-
ment residuals are expected to be negliqible based on the high
volatility of the compounds present in the qroundwater.
Treatment by aqueous phase qranular activated carbon provided in
Alternative 3 is reliable for the removal of VOCs from the -
qroundwater. Treatment residuals are expected to be negligible
Page 100 of 108
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- - -
since they will be concentrated on a relatively small amount of
carbon that will either be properly disposed in a landfill or
reqenerated by a destructive technoloqy.
Alternative 1 provides no lonq-term effectiveness.
Offsite:
SHORT-TERM EFFECTIVENESS
The short-term impact to the health of workers and the community
will be very minimal for Alternatives 2 and 3 because the
qroundwater extraction system is already in place as the interim
remedial action at the site. There would be no cur~ent addi-
tional risks since the plume is already contained and the treat-
ments are protective. Groundwater cleanup time is estimated to
require about 36 years. Uncontrolled air emissions from Alterna-
tive 2 make it sliqhtly less effective in protectinq health and
the environment than Alternative 3 in the short-term.
Alternative 1 does not include the implementation of treatment
remedies; therefore, there are no additional risks to the
community. Risks associated with the contaminant plume would
remain at the site for over 100 years until natural attenuation
reduces the contaminant concentrations down to the cleanup stan-
dards.
Offsite:
IMPLEMENTABILITY
Alternatives 2 and 3 include the same extraction system which is
already in place. Both alternatives provide qroundwater treat-
ment with either an air stripper or carbon adsorption. Both
methods are proven technoloqies and there are no technical con-
siderations that prohibit the use of either of these tech-
nOloqies. In addition, both alternatives are administratively
feasible usinq existinq permits for discharqe or air emissions.
Institutional controls required in Alternatives 2 and 3, are
administratively feasible. There are no technical concerns
reqardinq the implementability of Alternative 1.
Offsite:
~
Based on an estimated 21 years to cleanup the A Aquifer and 36
years for the B Aquifer, costs of Alternatives 2 and 3 are
siqnificantly qreater' than the 30 years of qroundwater monitoring
in Alternative 1. Alternative 2 is the most cost effective since
it will meet all cleanup requirements for a present worth cost of
4.4 million dollars compared to the 10 million dollar present
worth cost of Alternative 3. Alternative 1 has a present worth
cost ot 1.9 million dollars, but would be ineffective for
cleanup.
The annual O&M costs for Alternatives 1, 2, and 3 are 124, 255,
paqe 101 of 108
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and 637 thousand dollars, respectively. The capital cost of
Alternatives 1, 2, and 3 are 56, 208, and 411 thousand dollars,
respectively.
9.3
THE SELECTED REMEDY
9.3.1
Basis of Selection
The selected remedies addressing contaminated qroundwater all
basically entail the continuation of the current IRK, qroundwater
extraction followed by air stripping. In some cases, minor
modifications will be made in the form of additional extraction
wells and increased water reuse. These remedies met all of the
nine criteria and adequately addressed the remedial action
objectives. Implementability and cost effectiveness
distinguished these alternatives from other alternatives that
also met the nine criteria and remedial action objectives. The
selected remedies are relatively easy to implement and, in most
cases, easier to implement than competing alternatives. Except
for the Signetics remedy, the selected remedies were the least
expensive of the competing alternatives and always the most cost
effective. The Signetics remedy costs 0.2 million dollars more
than its two competing alternatives, but is more cost effective
because the accelerated hot spot remediation increases the
overall effectiveness of the groundwater cleanup.
Remedies and alternatives with either liquid-phase or vapor-phase
carbon treatment are advantageous because they involve the
destruction of the adsorbed VOCs during carbon regeneration, thus
providing the maximum reduction in toxicity, mobility, and
volume. Liquid-phase carbon treatment was evaluated as an
alternative for the AMD onsite unit, but it was not selected
because the existing air stripper remedy contains equally
effective vapor-phase carbon emission control at half the present
worth cost. Only the TRW onsite and the off site commingled plume
air strippers do not contain GAC air emission control.
Despite the slight advantages in contaminant destruction offered
by the carbon treatment alternative for the offsite commingled
plume, the existing air stripper without emissions controls was
selected because of several advantages. These advantages include
the fact that the air stripper costs less than carbon adsorption
and is already installed and operating in accordance with current
permits. In addition, residuals from the air stripper could
potentially be captured and destroyed by available emissions
control technology if permit modifications become necessary.
This last point is also true of the TRW air stripper remedy,
which was selected without comparison to a liquid-phase carbon
treatment alternative.
The relatively small volume of contaminated soil in the saturated
zone at TRW is best addressed by the present qroundwater
Page 102 of 108
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. extraction and treatment system. The two alternatives that were
not selected as the remedy are either dramatically more expensive
and difficult to implement or not significantly more effective.
For AMD soils, the selected remedy is excavation followed by
offsite treatment (incineration) and disposal. While some of the
in situ alternatives are easier to implement, the selected remedy
is the only alternative that will meet ARARs in a reasonable
amount of time. It is also the most cost effective alternative
and involves destruction of the contaminants, thus providing the
qreatest reduction in toxicity, mobility, and volume.
9.3.2
Features of the Remedies
The groundwater remedies selected for each of the
AMD/Siqnetics/TRW sites involve institutional controls, continued
groundwater monitoring, and continued groundwater extraction and
treatment with the air strippers that are currently in place.
Existing NPDES permitted discharge of treated water to Calabazas
Creek and existing BAAQMD permitted air emissions will continue.
Basically, these remedies are already implemented and operating
with acceptance form the community and federal, state, and local
agencies. In some cases, minor modifications will be made in the
form of additional extraction wells and increased water reuse.
The total combined cost for the remedies has a present worth of
12 million dollars. The features of these remedies are described
below along with specific soil remedies for some of the sites.
1. Institutional Controls
Deed and well-permit restrictions will protect humans from
exposure to contaminated groundwater below the AMD, Signetics,
and TRW properties during the cleanup period.
2. Groundwater Monitoring
continued groundwater monitoring and soil flux monitoring will
verify plume containment, determine current plume boundaries,
follow the decrease in VOC concentrations as the cleanup
progresses, and verify compliance with RWQCB orders.
3. Groundwater Extraction
continued groundwater extraction from a total of 19 A Aquifer
wells, 2 extraction trenches and multiple building dewatering
sumps which extract from the A zone and 23 B Aquifer wells
distribute a total flow of approximately 225 qpm among four
different treatment system locations. Existing and new well
locations and pumping rates contain the plume and will prevent
further migration of the VOC-contaminated groundwater. The
cancer risk of 5 X 10.1 for a future use of drinking water
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contaminated with vinyl chloride, TCE and DCE will be
continually reduced over an estimated 36-year cleanup period
to a maximum risk of 3.7 X 10~. Thus, groundwater extraction
until drinking water standards are achieved will attain ARARs
and permanently restore the contaminated aquifers to their
maximum beneficial uses.
Enhanced groundwater extraction at the Siqnetics property will
focus on two areas: improved control of contaminant migration
latera1ly in the A zone and, improved control of vertical
migration of contaminants from the 81 and 82 zones to 83 and
84 zones. The enhancement may include modificatiQn of existing
equipment, installation of new wells or trenches and increased
rates of groundwater withdrawal from the deeper aquifers.
Modification of the Alvarado and Duane Avenue offsite
extraction systems and continued groundwater extraction
these modified systems would focus on improving control
A zone plume under the current drought conditions.
from
of the
4. Air stripping
Existing air strippers will remove more than 99' of the VOCs
from the extracted groundwater. In addition, air stripper
effluents from the Siqnetics property and the offsite
commingled plume are polished with liquid-phase carbon. These
treatments allow the effluent to be either reused or
discharged under existing NPDES permits to Calabazas creek
without degrading this surface water or presenting a
siqnificant risk to human health and the environment.
The AMD and Siqnetics property air strippers contain vapor-
phase carbon to control air emissions, while the TaW and
offsite strippers do not currently contain emissions control.
Emissions from the air strippers are considered safe by the
8AAQMD under existing permits. The TRW and off site strippers
will include air emissions control if emissions exceed levels
permitted by the BAAQMD.
The spent carbon from the liquid and vapor phase control units
is tranafarred to a licensed facility where it is regenerated
by ~ of a rotary kiln. Thus, a significant amount of
the ~~e 'ultimately destroyed, further reducing the
toxio.~~i JIObility, and volume of the original contamination.
S. Water Reuse'
currently, more than 50' of the treated effluents are reused
as process makeup water, cooling tower water, irrigation, or
other uses. This percentage will increase dramatically as
reuse of effluent from the offsite air stripper located at AMD
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915 increases from 35' to 65' by the end of 1991. The
required goal is 100' reuse of the 150 to 200 gpm treated
effluent at AMD/siqnetics/TRW as soon as possible.
6. Soil Remediation
The 37 cubic yards of contaminated soil at the AMD property
will be excavated and transported offsite for treatment and
disposal. The treatment will likely involve an incineration
technology resulting in destruction of the VOC contaminants.
This remedy prevents human exposure to the contaminants and
prevents recontamination of the groundwater.
The existing soil vapor extraction system at the Siqnetics
property will be enhanced by increasing the number of vapor
extraction wells and the volume of vapor-phase carbon units
for emissions control.
There is no current exposure pathway for the small volume of
contaminated soils at the TRW site. These soils will be
decontaminated by natural soil flushing. The resulting
contaminated groundwater will be captured and treated by the
current groundwater extraction and treatment system.
9.3.3 Uncertainty in the Remedy
The groundwater remediation remedy for each of the
AMD/Siqnetics/TRW sites involves groundwater extraction followed
by treatment with air strippers. The goal of this remedial
action is to restore the ground water to its beneficial use,
which is, at these sites, a potential source of drinking water.
Based on information obtained during the RI and on a careful
analysis of all remedial alternatives, EPA and the RWQCB believe
that the selected remedy will achieve this goal. It may become
apparent, during implementation or operation of the groundwater
extraction system and its modifications, that contaminant levels
have ceased to decline and are remaining constant at levels
higher than the cleanup standards over some portion of the plume.
In such a case, the system performance standards and/or the
remedy may be reevaluated by EPA.
The selected remedy will include groundwater e~raction for an
estimated period of 12 to 38 years, during which the system's
performance will be carefully monitored on a regular basis and
adjusted as warranted by the performance data collected during
operation. Modifications may include any or all of the
following:
a) at individual wells where cleanup goals have been attained,
pumping may be discontinued;
b) alternating pumping at wells to eliminate stagnation points;
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c) pulse pumping to allow aquifer equilibration and to allow
adsorbed contaminants to partition into ground water; and
d) installation of additional extraction wells to facilitate or
accelerate cleanup of the contaminant plume.
To ensure that cleanup goals continue to be maintained, the
aquifer will be monitored at those wells where pumping has ceased
on an occurrence of every 5 years following discontinuation of
groundwater extraction.
10.0 STATUTORY DXTERMXHATXON8
The selected remedies will comply with Section 121 of CERCLA.
The selected remedies protect human health and the environment
through extraction and treatment of the VOC-contaminated ground
water and the removal of contaminated soils. The reductions in
risk are summarized in Section 9.3.2 of this ROD. There are no
short-term or long-term threats associated with the selected
remedies that cannot be readily controlled. In addition, no
adverse cross-media affects are expected from the remedies.
The selected remedies will comply with all of the identified
chemical, action, and location specific ARARs that are described
in Section 7 of this ROD. In the event that it becomes apparent
that the drinking water ARARs may not be achievable as described
in Section 9.3.3 of this ROD, the system performance standards
and/or the particular groundwater remedy may be reevaluated.
The present worth cost of the selected remedies total $11.9
million dollars for the AMD/Signetics/TRW sites. This total is
the sum of $2.65 million for AMD onsite, $4.11 million for
Signetics onsite, $0.75 million for TRW onsite, and $4.39 million
for the offsite commingled plume. These remedies are the least
costly of the alternatives which are equally protective of human
health and the environment. The selected remedies are already
installed for the most part and are operating in accordance with
current permits for water discharge and air emissions.
The selected remedies use permanent solutions and alternative
treatment., (or resource recovery) technologies to the maximum ex-
tent praq||jjpable and satisfy the statutory preference for
remediev^Bxtirb" employ treatment that reduces toxicity, mobility,
or volumefT|», * principal element. In addition, the remaining
toxicity/^fcobility, and volume of contaminants emitted from the
TRW onsite and the offsite commingled plume air strippers could
be potentially captured and destroyed by available emissions
control technology if permit modifications become necessary.
Section 9.3.2 of this ROD summarizes the key features of the
selected remedies.
Because the remedies will result in hazardous substances
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remaining onsite above health-based levels, a five-year review,
pursuant to CERCLA section 121, 42 V.S.C. section 9621, will be
conducted at least once every five years after initiation of the
remedial actions to ensure that the remedies continue to provide
adequate protection of human health and the environment.
11.0
DOCUJID'l'ATIOB 01' 8ICDlXPICA!I'1' CDJfGB8
There were. no significant changes between the proposed plan and
this Record of Decision.
PART III.
RB8POHSrvBHB88 8UMMARY
1.0
nrraODUCfIOB
This responsiveness summary reviews comments and questions
regarding the Remedial Investigation/Feasibility Study (RI/FS)
and Proposed Final Cleanup Plan (proposed plan) for Advanced
Micro Devices facilities at 901/902 Thompson Place (AMD 901/902)
and 915 DeGuigne Drive (AMD 915), the former TRW Microwave at 825
Stewart Drive (TRW) the Signetics facility at 811 E. Arques, all
in Sunnyvale. A single responsiveness summary was prepared for
this group of Superfund sites because actions at all sites
potentially impact the same local community. The study area that
encompasses AMD 901/902, Signetics, and TRW has been divided into
four area-specific operable units. Separate proposed plans have
been developed for each of these four operable units and for AMD
915.
This summary includes comments received during the 60 day period
from the opening of public comment at the Board meeting of March
20, 1991 through the close of public comment on May 20, 1991. All
comment during this period was received by the RWQCB. Additional
opportunity for comment was given to the public at the RWQCB
meeting on June 19, 1991. This Record of Decision does not
include any significant changes to the proposed plan presented at
the community meeting of March 27, 1991 and does not differ
significantly from the plan adopted by the RWQCB
2.0
RZGIOBaL waTER QUALITY CONTROL BOARD RB8POH8B8
Since RWQCB i. the lead agency for AMD 901/902, Signetics, and
TRW Microwave and received all comments, RWQCB prepared the
Responsiveness Summary (Attachment A). EPA, as the support
agency, has reviewed and concurs with the RWQCB responses.
Written comments were received from Santa Clara Valley Water
District (SCVWD)i Supervisor Ron Gonzales, Santa Clara County
Board of Supervisors; Santa Clara County Office of Education;
Silicon valley Toxics Coalition (SVTC)i San Miguel Homeowners
Associationi California Department of Health Services,
Environmental Epidemiology and Toxicology Branch (EETB); and two
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community members, Gary Holton and John Schwartz. Specific
comments received at the community meeting held at the
Westinghouse Auditorium in Sunnyvale, March 28, 1991, general
comments from an informal meeting held May 7, 1991 at the San
Miguel School site in Sunnyvale and verbal comments received by
telephone during the comment period and two meetings with the San
Miguel Homeowners Association, May 23 and May 30, 1991, will also
be outlined and addressed separately. The comments by SCVWD and
Gary Holton were supportive of the proposed plan, as outlined
above, and " as such will not require a specific response.
The attached Responsiveness Summary is divided into two parts;
Part I provides a summary of the major issues raised by .
commentors and focuses on the concerns of the local community;
Part II is a more technical response to all significant comments.
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