WORKPLAN FOR PILOT TESTING OF IN SITU CHEMICAL & … · workplan for pilot testing of in situ chemical oxidation and enhanced in situ bioremediation of chlorinated solvents in groundwater

Prepared for:

Sequa CorporationHackensack, New Jersey

WORKPLAN FOR PILOT TESTING OF IN SITUCHEMICAL OXIDATION AND ENHANCED IN SITU

BIOREMEDIATION OF CHLORINATED SOLVENTS INGROUNDWATER

DUBLIN NPL SITE, PENNSYLVANIA

Prepared by:

GEOSYNTEC CONSULTANTS160 Research Lane, Suite 206

Guelph, Ontario N1G5B2GeoSyntec Project Number TR0099

September 2001

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GeoSyntec Consultants

TABLE OF CONTENTS

Page

1. INTRODUCTION......................,^

2. BACKGROUND.................................^

2.1 Summary of Site Conditions.................................................................................3

2.2 Background on Chemical Oxidation.....................................................................5

2.3 Background on Trichloroethene Biodegradation ..................................................7

2.4 Key Results from ISCO Treatability Studies ...................................................... 10

2.5 Key Results from Biotreatability Studies............................................................ 11

3. PILOT TEST APPROACH AND METHODOLOGY...........................................13

3.1 Pilot Test Objectives.......................................................................................-.13

3.2 Overview of Pilot Test Approach ....................................................................... 14

3.3 Scope of Work.....................................................................................................16

3.3.1 Task 1 -PTA Instrumentation.................................................................... 17

3.3.2 Task 2-PTA Characterization................................................................... 18

3.3.3 Stage I Go/No-Go Decision Point...............................................................21

3.3.4 Task 3-ISCO Demonstration....................................................................21

3.3.5 Stage H Go/No-Go Decision Point..............................................................23

3.3.6 Task 4 -EISB Demonstration.....................................................................24

3.3.7 Task 5-Reporting.......................................................................................26

4. SCHEDULE............................................................................................................27

5. REFERENCES.......................................................................................................-28

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LIST OF TABLES

Table 1: Summary of Published Field Demonstrations of Permanganate Treatment

Table 2: Summary of Laboratory Studies Evaluating Bi ode gradation of ChlorinatedSolvents at Concentrations Approaching Solubility Limits

Table 3: Summary of Field Demonstrations of EISB

Table 4: Schedule of Laboratory Analyses to be Conducted for the ISCO and EISBPilot Testing

Table 5: Summary of Laboratory Analyses to be Conducted for the ISCO Phase of thePilot Test

Table 6: Summary of Laboratory Analyses to be Conducted for the EISB Phase of thePilot Test

LIST OF FIGURES

Figure 1: Site Location, Dublin Borough, Pennsylvania

Figure 2: Site Plan Showing Pilot Test Area and Locations of Existing Wells

Figure 3: Pathways for the Degradation of Chlorinated Ethenes

Figure 4: TCE Biodegradation in Groundwater Microcosms

Figure 5: Conceptual Design of In Situ Recirculation System for Tracer, ISCO andEISB Testing

Figure 6: Schedule of ISCO and EISB Pilot Testing

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1. INTRODUCTION

The remediation of dense non-aqueous phase liquids (DNAPLs) such astetrachloroethene (PCE) and trichloroethene (TCE) has been recognized as a complexchallenge, particularly in fractured bedrock environments. Groundwater remediationapproaches for these types of sites have historically employed groundwater extractionand ex situ treatment (pump-and-treat). Unfortunately, these approaches have beenshown to be ineffective in significantly improving groundwater quality, even afterrelatively long periods (i.e., decades) of operation (Doty and Travis, 1991; USEPA,1992; Bartow and Davenport, 1995; NRC, 1994). The limitations of these pump-and-treat systems relate largely to their inability to significantly accelerate the mass transfer(dissolution rate) of a DNAPL to the aqueous phase, which is the phase that is actuallyremoved from the subsurface during groundwater extraction. By comparison,technologies capable of enhancing DNAPL dissolution into the aqueous phase havestrong potential to shorten the time to achieve site restoration.

In recent years, significant research has been conducted with technologies, such asin situ chemical oxidation (ISCO) and enhanced in situ bioremediation (EISB), that cansignificantly enhance the rate of DNAPL dissolution. Emerging research is showing thatthese technologies can accelerate DNAPL dissolution by order(s) of magnitude, with thepromise of reducing the time for source remediation by a comparable factor. On thisbasis, Sequa Corporation (Sequa) retained GeoSyntec Consultants Incorporated(GeoSyntec) in the spring of 2001 to conduct treatability studies for the Dublin NPL sitein Dublin Borough, Pennsylvania (the Site) to assess the technical feasibility of bothISCO and EISB for aggressive remediation of the TCE source in fractured bedrockbeneath the Site. The results of the treatability studies have been extremely encouraging,indicating that both technologies can rapidly destroy high concentrations of TCE (e.g.,10 to 20 mg/L) in the Site groundwater, with reaction rates from minutes to days. Fieldpilot testing of the ISCO and EISB approaches is necessary to demonstrate theeffectiveness of these technologies under field conditions and to provide data that can beused for a full-scale design, if appropriate.

This Workplan provides the details for design and execution of the proposed pilottest. Section 2 provides background information, including a description of Site

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conditions, overviews of the ISCO and EISB technologies for the treatment of TCE andDNAPLs, and key results of the Site-specific ISCO and EISB treatability studiesrecently completed for the Site. Section 3 presents the objectives, approach andmethodology for the pilot test. Section 4 provides a project schedule. Workplanreferences are provided in Section 5.


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2. BACKGROUND

The following sections provide a brief summary of Site conditions (Section 2.1),background information on ISCO and EISB technologies (Sections 2.2 and 2.3,respectively), and key results from the ISCO and EISB treatability studies (Sections 2.4and 2.5, respectively).

2.1 Summary of Site Conditions

The Site is located at 120 Mill Street in Dublin Borough in Bucks County,Pennsylvania (Figure 1). The 4,5-acre facility was historically used for manufacturing,with TCE used as a degreaser during cleaning and manufacturing processes.

The geology beneath the Site consists of low permeability silty clay overburden to adepth of about 3 to 23 ft below ground surface (bgs), overlying combinations of darkgray shaley siltstone and/or reddish-brown siltstone to depths in excess of 500 ft bgs.The maximum thicknesses of the gray shaley siltstone and the reddish-brown siltstoneobserved in Site borings to date are 86 ft and 180 ft respectively. A fourth, intermediarylithologic unit is a transitional unit characterized by interbedding of both the gray andred beds. In the vicinity of the Site, the bedding strikes between N40E and N75E anddips between 9 and 16 degrees to the NW. Two well-defined joint sets have beenidentified within the study area. The strike of the most prominent set varies from N15Eto N75E. The strike of the secondary joint set varies from N45W to N85W. The dip ofboth joint sets is near vertical. There appears to be a greater percentage of verticalfractures in the boreholes near the Site.

Groundwater at the Site occurs in the bedrock at a depth below about 40 to 50 ftbgs. The water table shows significant fluctuations (up to 6 ft) in response to dailycyclical water use in the vicinity of the Site. Groundwater flow is generally to the northand northwest, dominated by the joint and fracture systems and bedding planes. Thehorizontal hydraulic gradient ranges between 0.004 and 0.118. Hydraulic conductivityvalues for discrete fracture zones vary significantly in wells across the site, from 0.15ft/day to in excess of 3,094 ft/day (e.g., well MW-9S at 106 to 206 ft bgs). Higherhydraulic conductivity values are typically reported in the upper zones and in depth


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intervals straddling contacts between the gray shales and siltstones. Hydraulicconductivities are also higher within the red siltstone. Vertical hydraulic gradients aremoderate and variable, ranging from downward in the southern and northeastern areasof the Site to upwards in the center and northwestern areas downgradient from the Site.

TCE and related breakdown products such as 1,2-dichloroethene (1,2-DCE) andvinyl chloride (VC) are the primary chemicals of concern in groundwater at the Site.The highest TCE concentrations have typically been detected in groundwater samplesfrom the Fire Tower Well (FTW; see Figure 2), with concentrations ranging up to55,000 (ig/L at a depth interval of 458 to 478 ft bgs. Elevated TCE concentrations havealso been detected in nearby shallow (<100 feet) wells BCM-1 (18,000 u.g/L, June 2001)and MW-4 (2,000 (ig/L in June 2001). The concentrations of TCE in groundwatersamples from the FTW suggest the likely presence of TCE DNAPLs within the bedrockin the vicinity of the FTW and well BCM-1. The DNAPL TCE will be expected toserve as a long-term source of groundwater contamination unless treated using directaggressive measures.

The highest 1,2-DCE and VC concentrations have similarly been detected in theFTW, with concentrations ranging up to 780 and 25 [ig/L respectively. Data from arecent (June 2001) groundwater sampling event indicates that ethene (theenvironmentally-acceptable end product of TCE degradation) was not detected atappreciable concentrations at any of the wells sampled. Overall, the rate and extent ofintrinsic biodegradation of TCE in the Site groundwater appears to be limited by theabsence of key nutrients (electron donors) required to mediate the intrinsicbiodegradation reactions.

The distribution of TCE in the groundwater has historically extended to distances ofnearly 2,400 ft to the north, northwest and west. The longest axis of the TCE plumeappears to be oriented in a northwesterly direction (N40W, similar to the orientation ofthe secondary joint set). TCE concentrations decline exponentially with increasinghorizontal distance from the FTW. Furthermore, the TCE plume has been shrinkingover time, apparently due to attenuation processes such as dispersion, dilution, sorptionto aquifer materials and/or diffusion into the rock matrix, and intrinsic biodegradation.


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2.2 Background on Chemical Oxidation

Laboratory studies and emerging field applications have demonstrated that ISCOcan be an effective technology for degrading chlorinated solvents in soil andgroundwater. The key benefit of the ISCO approach is that it provides significantlyenhanced dissolution and destruction of the target contaminants within a relatively shortperiod of time (i.e., months) by comparison with standard pump & treat approaches(which require 10s to 100s of years to restore groundwater quality to comply withARARs). This is particularly true for sites where remediation is controlled by the rateof dissolution of DNAPLs and/or matrix diffusion/counter-diffusion effects, such as forfractured bedrock sites.

Various oxidants have been used in laboratory and field applications, includingpermanganate (MnO4~), Fenton's reagent (hydrogen peroxide and a ferrous iron catalyst)and ozone. Of these, permanganate offers significant advantages because it is lessreactive with aquifer solids (resulting in less oxidant waste) and is typically more stableand safer to handle, requires no pH adjustment, and produces less heat and insoluble gasin the treatment zone (by comparison with Fenton's reagent). The challenges associatedwith delivery of an unstable gas phase oxidant such as ozone below the water tablelimits the applicability of ozone use for groundwater remediation.

The reaction between permanganate and chlorinated ethenes (e.g., TCE) involvesan attack on the carbon-carbon double bonds, which ultimately mineralizes the targetcompound to harmless inorganic products such as carbon dioxide (COi), water andchloride. At typical MnO4" application concentrations, the destruction half-lives oftarget contaminants such as TCE are typically on the order of a few minutes (Yan andSchwartz, 1999).

To date, ISCO applications using permanganate have been documented in thescientific literature for more than 20 sites, encompassing a wide range of site conditionsand contaminant distributions, and using a variety of oxidant delivery techniques. Table1 provides a summary of documented ISCO field applications using permanganate(Mn04~) for both porous and fractured media. Several key demonstrations arehighlighted below.


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The first significant field evaluations of ISCO using MnCV were conducted in asand aquifer at Canadian Forces Base (CFB) Borden near Toronto, Ontario (Schnarr andFarquhar, 1992; Schnarr et al. 1998). These field demonstrations were conducted withina double-walled sheetpile cell (3.0 m x 2.5 m x 1.0 m) that isolated the treatment zonefrom the surrounding aquifer. The first demonstration evaluated MnCV oxidation of aresidual PCE source while the second demonstration evaluated MnCV oxidation of amulti-component TCE/PCE DNAPL distributed as both pooled and residual DNAPL.The results of the first demonstration illustrated that rapid removal of residual DNAPLcould be achieved, providing one of the best examples in the scientific literature ofcomplete site restoration. However, the rate of degradation of pooled DNAPL in thesecond demonstration was limited by the low surface area to volume ratio. A field studyconducted by Hood et al. (1997) in the sandy aquifer at CFB Borden confirmed theconclusions of Schnarr et al. (1998) and Schnarr (1992), namely that DNAPL residuals(consisting of PCE, TCE, and TCM) can be rapidly remediated using MnO4".

Subsequent to these initial investigations, a MnCV flush in a sand aquifercontaminated with a substantial quantity of TCE DNAPL was performed at the LaunchComplex 34 facility at Cape Canaveral Air Force Station in Florida (IT Corporation,2000). Pulses of MnCV were delivered into the source zone through drive-pointinjection. The reduction in DNAPL mass resulting from oxidant injection was estimatedto be 84%, with mass reduction estimates in the groundwater ranging between 83% to95%. At this site, no evidence of permeability reductions resulting from precipitatedMnOz in the matrix was observed. Hydraulic conductivity measurements performedafter oxidant injection were either comparable to or slightly higher than pre-testmeasurements, a result which is consistent with theoretical calculations reported byHood (2000).

More recently, field demonstrations of ISCO have been conducted in fracturedbedrock environments. For example, Bryant et al. (2001) conducted a field study ofTCE oxidation using MnO4" at Edwards Air Force Base (California) in a fracturedgranitic bedrock containing dissolved phase TCE and cis-l,2-DCE. Approximately7,500 gallons of a 1.8% solution of MnCV were injected in batches through eightinjection points over a period of 5 days. Monitoring results indicated that thedemonstration achieved a radius of influence of up to 55 feet horizontally and 28 feetvertically. Post-treatment monitoring has indicated that n on-detectable concentrationsof TCE and cis-l,2-DCE in groundwater persisted for 60 days after MnO4" injection.


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After 143 days, TCE and cis-l,2-DCE concentrations in two of the wells reboundedslightly (but were still three orders of magnitude less than the maximum pre-oxidantinjection concentrations), while the remainder of the wells contained non-detectableconcentrations of TCE and cis-l,2-DCE.

Evidence also exists for the potential of ISCO to treat contaminants in lowpermeability materials, such as clays and rock matrices. These data suggest that ISCOhas potential to control slow matrix counter-diffusion and rebound following initialtreatment. For example, Siegrist et al. (1999) evaluated MnCV treatment of a lowpermeability, fractured clay formation. Induced horizontal fractures in the clay werefilled with a grout composed of 0.1-0.3 mm MnCV particles in a mineral-based gel.Diffusion of the permanganate into the clay fracture matrix over ten months providedsufficient oxidant to degrade 70-100% of TCE spiked at concentrations as high as 4.1g/kg, suggesting that oxidation was a promising treatment strategy for low permeabilitymedia in which diffusion processes limit the rate of mass removal.

The results of these and other studies demonstrate that DNAPLs can beaggressively remediated through oxidation using MnCV in both porous and fracturedmedia, and that MnCV can diffuse into the fracture matrix promoting destruction ofchlorinated solvents that may otherwise diffuse out of the rock matrix following initialtreatment. In this manner, MnCV has the potential to prevent or limit the effects ofchemical rebound resulting from matrix counter-diffusion.

2.3 Background on Trichloroethene Biodegradation

Research and field observations have shown that microorganisms that naturallyexist in subsurface environments (e.g., groundwater) possess the ability to biodegradechlorinated VOCs such as PCE and TCE to non-chlorinated, environmentally-acceptable end products such as ethene, CC>2, water and chloride (Major et al., 1991 and1995; Edwards and Cox, 1997). While these biodegradation reactions can occur under awide range of environmental conditions, the dominant TCE biodegradation mechanismin most groundwater environments is reductive dechlorination, which involves thesequential replacement of chlorine atoms on the alkene molecule with hydrogen atoms.Under reducing conditions, TCE serves as an electron acceptor and is dechlorinated viacis~l,2-DCE and VC to ethene. Simple organic carbon compounds such as alcohols


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(methanol, ethanol), organic acids (lactate, acetate, oleate), sugars (molasses) or edibleoils (canola oil) serve as electron donors in the dechlorination reaction. Figure 3 showsthe biodegradation pathways for the chlorinated ethenes that have been detected in theSite groundwater.

Specific dehalorespiring bacteria such as Dehalococcoid.es ethenogenes are knownto mediate the complete dechlorination of PCE and TCE to ethene (Maym6-Gatell et al.,1997). While sulfate-reducers and methanogens appear to possess the ability to mediatethe initial steps of dechlorination of PCE and TCE to cis-l,2-DCE, the specificdehalorespiring microorganisms appear to be required to mediate further and completedechlorination of cis-l,2-DCE via VC and ethene. Unfortunately, these dehalorespiringmicroorganisms do not appear to be ubiquitous at all sites. As a result, dechlorination ofPCE and TCE stalls at cis-l,2-DCE at many sites, resulting in accumulation of the cis-1,2-DCE dechlorination intermediate. Fortunately, research in the last few years hasresulted in the isolation of several stable, natural, non-pathogenic microbial consortiathat are capable of mediating complete dechlorination of TCE to ethene, and fielddemonstrations discussed below have shown that these microorganisms can be added toaquifers (a process termed bio augmentation) to promote PCE and TCE dechlorination toethene at sites where this activity otherwise does not occur (or does not occur at asufficient rate to meet remedial objectives). One such dehalorespiring microbial cultureis referred to as KB-1. This culture has not been genetically modified in any manner; itis simply an enrichment derived from naturally occurring bacteria found in soil andgroundwater where TCE degradation occurs. Microbial testing has consistently foundthe KB-1 culture to be free of pathogens.

Several applied field demonstrations have recently been completed or are currentlybeing conducted to assess EISB of DNAPL source areas in fractured bedrock media. Forexample, Sorenson et al. (2001) recently conducted a field study of enhanced dissolutionof a residual TCE source area in a fractured basalt aquifer in Idaho. High concentrationsof electron donor (sodium lactate) were injected into the subsurface. Rapidbiostimulation was observed and enhanced reductive dechlorination of TCE wasobserved about 5 weeks after the initial lactate injection. Accelerated mass transfer ofTCE was observed due to enhanced dissolution of the TCE DNAPL, and dissolutionand mobilization of the TCE by the concentrated lactate. After 21 months, TCE was


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below detection limits in the source area and the flux of TCE to outlying wells hadstopped.

Similarly, GeoSyntec is conducting EISB bioremediation demonstrations involvingbioaugmentation to treat TCE in fractured bedrock groundwater at the CaldwellTrucking Superfund Site in Fairfield, New Jersey and an industrial site in Boston,Massachusetts. At the Caldwell Trucking Superfund site, the field demonstrationinvolves EISB of a TCE DNAPL source area in fractured basaltic bedrock in a test areameasuring approximately 120 feet wide, and 40 feet long. Electron donors (methanol,lactate and acetate) are added on a weekly basis in a batch mode via multiple injectionwells. Electron donor addition and bioaugmentation (with KB-1) commenced inFebruary 2001. Results to date (August, 2001) indicate an order of magnitude decline inPCE/TCE concentrations, with an accompanied increase in the concentration of cis-1,2-DCE, VC and ethene. There is evidence that cis-l,2-DCE production has peaked and isstarting to decline. TCE concentrations in the well containing the highest TCEconcentration (680 mg/L) have declined by 90%. Furthermore, the use of molecularprobes specific to Dehalococcoides ethenogenes, the dehal ore spiring bacteria present inthe introduced TCE-degrading culture (referred to as KB-1) has demonstrated that thismicroorganism has become distributed throughout the test area.

The second demonstration involves EISB via bioaugmentation at an industrialfacility in Boston. Spent organic solvents, primarily trichloroethene (TCE) werereleased to unconsolidated soils through a dry well, located interior to the mainmanufacturing building. The TCE is suspected to have traveled downward to the basalunit of fractured bedrock along building pilings. A laboratory microcosm study usinggroundwater from the bedrock aquifer showed that augmentation with dehalorespiringmicroorganisms (the KB-1 culture) was necessary in order to initiate completedechlorination of TCE to ethene. The test area is located directly downgradient from thedry well where concentrations of TCE range from 30 to 120 mg/L. Due to the proximityof the pilot test area (PTA) to the Boston harbor, sulfate and chloride concentrations inshallow bedrock are elevated, at approximately 400 and 5,500 mg/L, respectively. Thetest is comprised of an injection well, extraction well, and three monitoring wells.Preconditioning the pilot test area was performed for 3 months by amending the testarea with electron donors used to support the growth of the dehalorespiring bacteria.During the pre-conditioning phase, TCE dechlorination to cis-l,2-DCE was observed,


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but further dechlorination to VC or ethene was not. Sulfate concentrations andoxidation/reduction potential (ORP) decreased linearly over the preconditioning period.The test area was bioaugmented with dehalorespiring bacteria (KB-1) in the fourthmonth (June, 2001) of the pilot test, and has resulted in dechlorination of the TCE andcis-l,2-DCE to ethene within the first month after bioaugmentation.

In addition to the field demonstrations showing that dehalorespiring bacteria can beadded to contaminated sites to promote complete dechlorination to ethene, laboratoryresearch studies are showing that the dehalorespiring bacteria are capable of promotingdechlorination in the presence of DNAPL. For example, Yang and McCarty (2000) andCope and Hughes (2001) have reported PCE and TCE dechlorination at concentrationsas high as the solubility limits of these compounds. Furthermore, these studies havedocumented the effect of dechlorination in accelerating the rate of DNAPL dissolution.For example, in laboratory column studies, Yang and McCarty (2001) observed a factorof 5 increase in the PCE DNAPL dissolution rate, whereas Cope and Hughes (2001) andCarr et al. (2000) have observed increases in DNAPL dissolution rates in the range of 5to 14 times natural rates. Table 2 provides a summary of bench-scale studies that haveevaluated the biodegradation of chlorinated solvents at near-solubility concentrations, insome cases reporting the enhancement factor of the dissolution rate compared todissolution through physical process (e.g., flushing) alone. Table 3 provides a summaryof EISB demonstrations that have been conducted for DNAPL source sites and fracturedbedrock sites, through either electron donor addition alone, or in combination withbioaugmentation (addition of dehalorespiring bacteria).

2.4 Key Results from ISCO Treatability Studies

ISCO treatability studies (batch tests) were conducted with Site groundwater andbedrock materials to: i) estimate the permanganate oxidant demand of groundwater androck materials; ii) assess the potential impacts of oxidation on the inorganic chemistryof the groundwater; iii) assess the potential for the oxidant to destroy chlorinatedsolvents within the rock matrices; and vi) identify performance factors that mayinfluence design and scale-up of a potential ISCO application, including VOCdestruction rates, oxidant reaction rates, and potential geochemical interferences. The


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full methodologies and results form these studies are presented in the ISCO and EISBTreatability Report (GeoSyntec, September 2001).

The results of the groundwater batch tests show that the groundwater matrix doesnot appear to exert any significant demand on permanganate added to the system.Decreases in VOC concentrations were observed following the addition of potassiumpermanganate (KMnC^) after only 24 hours, including the decrease of TCEconcentrations from to below 0.5 U-g/L (reporting limit) using 1.0 g/L of KMnO4. Ofnote, groundwater quality was largely unaffected by the addition of KMnO4.Specifically, the concentrations of most metals decreased, except potassium andmanganese, which are added to the system by the process. Molybdenum concentrationsshowed a slight increase. There was also little precipitation of solids measured as aresult of the oxidant addition.

Batch tests using representative samples of natural fracture faces and bulk rocksamples for both the shale and siltstone from the Site demonstrated that: i) the oxidantdemand for the fracture face and bulk material of the siltstone was essentially zero; andii) the average oxidant demand for the shale (from triplicate samples) was 5.8 g/kg forthe fracture face and 2.6 g/kg for the bulk shale. The results from the batch tests indicatethat the oxidant demand of the fractured rock materials is relatively low and should notresult in significant permanganate demand during field implementation.

Based on the results of the laboratory ISCO treatability tests, it appears that ISCOwill be technically feasible, provided Site hydraulics and oxidant delivery can beadequately understood and accomplished.

2.5 Key Results from Biotreatability Studies

EISB treatability studies were conducted with Site groundwater (from well BCM-1)to: i) evaluate whether the indigenous microbial populations can be stimulated todechlorinate TCE and related VOCs to environmentally-acceptable end products (e.g.,ethene) through the addition of food-grade electron donors (e.g., lactate, sugars or edibleoils); ii) assess whether bio augmentation of the Site groundwater with dehalorespiring(TCE-degrading) bacteria accelerates the rate and extent of TCE dechlorination to


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ethene; and iii) identify performance factors that may influence design and scale-up of apotential ISCO application, including VOC destruction rates, potential microbialacclimation periods, and electron donor metabolism rates. The full methodologies andresults form these studies are presented in the ISCO and EISB Treatability Report(GeoSyntec, September 2001).

The results of the biotreatability studies indicate that the rate and extent of TCEdechlorination is limited when only electron donors (molasses, canola oil, alcohols,organic acids) are added, suggesting that the indigenous microbial populations may notbe capable of dechlorinating TCE at an appreciable rate. By comparison, whengroundwater microcosms were amended with both electron donors and bioaugmentedwith KB-1, a natural, non-pathogenic TCE-degrading bacteria, the TCE was completelydechlorinated to ethene within 13 days following bioaugmentation. Figure 4 shows theresults of the bioaugmented electron donor treatments. In all cases, TCE (starting at inexcess of 5 mg/L) was completely dechlorinated to ethene (an environmentally-acceptable end product) within 50 days. Both cis-l,2-DCE and VC were only detectedas transient dechlorination intermediates (i.e., accumulation was not observed).Furthermore, no inhibitory effect on TCE dechlorination was observed at higherconcentrations, as TCE concentrations in excess of 18 mg/L were easily dechlorinatedto ethene by the TCE-degrading bacteria. Based on the microcosm data, the calculateddechlorination half-lives for TCE, cis-l,2-DCE and VC ranged between 1 and 3 days foreach dechlorination step, which is considered extremely fast.

Based on the results of the laboratory biotreatability tests, it appears that EISB willbe technically feasible, provided Site hydraulics and electron donor delivery can beadequately understood and accomplished.

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3. PILOT TEST APPROACH AND METHODOLOGY

The following sections present: the pilot test objectives (Section 3.1); an overviewof the pilot test approach (Section 3.2); and the methodology for installation,instrumentation and operation of the pilot test (Section 3.3). Methods may be modifiedduring the course of the study based on best judgment and data that comes availableduring conduct of the work. Departures from the proposed methodology and therationale for such departures will be documented in progress reports and the pilot testreport.

3.1 Pilot Test Objectives

The specific objectives of the pilot test will be to:

1. Demonstrate the ability of ISCO to aggressively destroy TCE in situ andsignificantly reduce TCE mass flux from the source zone;

2. Demonstrate the ability of EISB to aggressively destroy TCE in situ andsignificantly reduce TCE mass flux from the source zone;

3. Evaluate impacts of ISCO and EISB on overall groundwater chemistry,including mobilization of redox-sensitive metals or production of byproducts ordegradation intermediates;

4. Assess the benefits of a sequenced ISCO-EISB approach to effectively treat theTCE source area, which will significantly reduce the duration of remedialactivities for the Site;

5. Identify design and operational factors that influence the successful performanceof field-scale ISCO and EISB systems, and optimize, to the extent possiblewithin the proposed scope, operating conditions for field-scale ISCO and/orEISB systems; and


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6. Generate design and cost data to assess the technical and economic feasibilityand duration of potential full-scale applications of ISCO and EISB versus pump-and-treat alternatives that have been considered for the Site.

3.2 Overview of Pilot Test Approach

The pilot test has been designed to collect the data required to evaluate the potentialof ISCO and/or EISB to aggressively treat the suspected TCE DNAPL source in thefractured bedrock. If successful, these technologies will accelerate cleanup of theimpacted portion of the aquifer in comparison to other technologies (e.g., pump-and-treat or monitored natural attenuation). This approach has the potential to significantlyshorten the overall duration of remedial activities for the Site compared to conventionalpump-and-treat remedies.

The proposed PTA will be located in the north corner of the Site, in the vicinity ofthe FTW. Groundwater in this area contains predominantly TCE, with historicconcentrations as high as 55,000 Hg/L in the FTW and 18,000 ug/L at well BCM-1. Thepilot test will employ a phased approach consisting of four main tasks, including: i)PTA instrumentation; ii) PTA characterization and conservative tracer testing; iii) ISCOapplication; and, if required iv) EISB application. The sequenced ISCO-EISB approachhas been proposed based on the relative strengths and compatibilities of eachtechnology. Specifically, TCE destruction rates are much faster with ISCO than withEISB, and therefore it is appropriate to test this approach first to assess whether it iscapable of source remediation as a stand-alone approach (i.e., EISB would not berequired). Furthermore, while EISB can be conducted following ISCO (with anintervening conditioning phase), the application of EISB would typically producebiomass that would reduce the effectiveness of a subsequent ISCO application byexerting demand on the oxidant.

PTA characterization activities will include electromagnetic borehole flowmeter(EBF) testing at the FTW to delineate the vertical profile of hydraulic conductivity (K)across the open interval of the well, depth-discrete groundwater sampling to determinethe vertical profile of TCE and assess possible intervals of TCE/DNAPL migration intothe FTW, and conservative tracer testing coupled with depth-discrete sampling to assess

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hydraulic interconnection between the FTW and the pilot test substrate delivery well(BCM-1). These data will be used to improve the understanding of hydraulics in thePTA, and to refine the design of the subsequent ISCO and EISB studies. The data willalso provide the hydraulic information required to demonstrate that the ISCO and/orEISB applications can effectively contain (and if required remove) any amendmentsadded to the groundwater during testing or products produced by the testing, to ensurethe protection of the Dublin Borough water supply.

Following PTA characterization, an ISCO test will be applied within the sourcearea using a recirculation loop approach, as depicted conceptually in Figure 5.Groundwater will be extracted from the FTW, amended with permanganate, and re-injected via well BCM-1. Permanganate addition will be conducted continuously for aperiod of up to 4 months, and performance will be evaluated by monitoring the declinein TCE concentrations, and increase in chloride concentrations in the recirculatinggroundwater. Following the permanganate addition period, groundwater recirculationwill be continued through the PTA to assess the degree of potential rebound in TCEconcentrations, which will be indicative of TCE DNAPL remaining within the test area.The data will be used to estimate the effectiveness of the ISCO application, and toassess the extent to which repeat ISCO applications (number and/or duration) will berequired to reduce the mass flux of TCE to acceptable levels. If a rebound in the TCEconcentration is observed, then an EISB test will be conducted to assess the comparativeeffectiveness of this approach versus repeat ISCO applications. However, if no reboundin the TCE concentration is observed, then ISCO will be considered sufficient as astand-alone treatment.

The EISB test will be conducted using the same basic design and instrumentation asthe ISCO test (Figure 5). Groundwater will be extracted from the FTW, amended withfood-grade electron donors (e.g., lactate, molasses, citrate), and re-injected via wellBCM-1. The recirculation loop will be bioaugmented with natural, non-pathogenicTCE-degrading bacteria that have been added to the subsurface at numerous other sites,including fractured bedrock aquifers (see Section 2.3). EISB performance will beevaluated for a period of 4 to 6 months following bioaugmentation. Performance will beassessed by monitoring the decline in TCE concentrations coupled with the production


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of ethene and chloride in the recirculating groundwater, and the data will be used toestimate TCE biodegradation rates and the effectiveness of the EISB application.

The pilot test is anticipated to require between 12 to 18 months to complete,including the PTA instrumentation and characterization, ISCO application, EISBapplication, and reporting. Following the completion of each project stage, the datacollected will be interpreted and a technical memorandum will be developed,summarizing the results of testing activities and providing an evaluation of thefeasibility of continuing with the next stage of the pilot test.

It is important to note that the proposed pilot testing program is expected to achievea significant degree of source destruction and remediation in the target treatment area,which is beneficial in terms of Site restoration. The pilot test activities, if successful,would be a substantive part of the desired Site restoration activities. Furthermore, thesystem has been designed to accommodate scale-up for potential full-scale remediation(pilot-scale components would not be redundant with full-scale), reducing the time andcosts associated with typical pre-design and installation activities that would be requiredas part of remedy implementation.

3.3 Scope of Work

The pilot test will consist of 5 tasks and 2 Go/No-Go decision points, as follows:

Task 1 - PTA InstrumentationTask 2 - PTA Characterization

Decision Point I - Stage I Go/No-Go DecisionTask 3 - ISCO Demonstration

Decision Point 2 - Stage U Go/No-Go DecisionTask 4 - EISB DemonstrationTask 5 - Reporting.

The following sections present the technical details associated with each of thesetasks and decision points.


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3.3,1 Task 1 - PTA Instrumentation

The first task of the pilot test will consist of instrumentation of the PTA with therecirculation and substrate (tracer, permanganate or electron donor) delivery systems sothat the PTA characterization activities and subsequent ISCO and EISB tests can beconducted without the need for containment and disposal of extracted groundwater.Instead, the extracted water will be amended with the desired substrates and rechargedvia the substrate delivery well (BCM-1). For example, during the EBF and depth-discrete sampling activities (which will involve pumping), the extracted groundwaterwill be amended with bromide or iodide to initiate the tracer test, reducing the volumeof water that needs to be extracted and re-injected to accomplish the desiredcharacterization activities.

Figure 5 presents the conceptual design of the recirculation and substrate deliverysystems. As previously indicated, well BCM-1 will serve as the substrate delivery well;the FTW (or a depth-discrete portion thereof) will serve as the extraction/recirculationwell. System instrumentation will include a dedicated downhole stainless steel pump(Grundfos IOSQ 110 or equivalent). An in-line paddle-wheel flow sensor will be usedto measure the flow rate and total volume of extracted groundwater. Output (4 to 20mAsignal) from the flow sensor will be used to; i) provide feedback control to theextraction well pump to maintain steady flow rates; and ii) control the delivery of tracerand/or electron donor solution to the feed groundwater to maintain a fixed concentrationof these components in the amended groundwater. The recirculation loop will be fittedwith manual sampling ports in advance and downstream of the substratedelivery/mixing system, to allow collection of samples to measure target chemicalconcentrations in the extracted and amended groundwater. Tracer and permanganate orelectron donor will be contained in small storage tanks with secondary containment.System operation will be controlled via a programmable logic controller (PLC) andcomputer that will record the groundwater extraction rates and total, individual in-lineelectrode (pH, ORP, bromide and chloride) measurements, and water levels in theextraction and recharge well at hourly intervals. The key substrate delivery componentswill be housed in a locked, temperature-controlled trailer or shed.


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3.3.2 Task 2 - PTA Characterization

A number of geophysical tests, including temperature logs, gamma radiation,caliper tests, resistance measurements and downhole video camera logs, were conductedon BCM-1 and the FTW by Geraghty and Miller (1995) during the remedialinvestigation work. The temperature log for the FTW shows a profile corresponding tothe natural geothermal gradient in the bottom 260 feet of the well, indicating that flowinto the well is minimal in this lower portion. The top 240 feet of the FTW show atemperature anomaly in the form of a temperature gradient that is opposite to the naturalgradient, which is also seen in the entire length of BCM-1. This anomaly may be theresult of the influence of water recharge immediately preceding the summer months;however, sufficient temperature data (e.g., quarterly data) is not available forconfirmation.

The caliper logs show discrete fracture zones in both wells (BCM-1 and FTW), andthese zones were confirmed during the video borehole imaging. Limited depth-discretehydraulic testing was previously conducted for the FTW by Geraghty and Miller (1995)using packers to isolate five 20 ft intervals of the FTW that correspond to fracture zonesseen in the caliper log. Unfortunately, these data only represent about 20% of the totalFTW well length, of which only 2 intervals were located in the more conductive (i.e.,upper) portion of the well indicated by the temperature logs. Therefore, additional dataare required to provide a more thorough and continuous profile of the: i) ambientvertical flow in the FTW under non-pumping conditions; ii) vertical profile of hydraulicconductivity; iii) vertical profile of TCE concentrations with depth; iv) locations offractures that hydraulically connect wells BCM-1 and FTW; and v) travel times betweenBCM-1 and FTW. PTA characterization activities will include EBF testing, depth-discrete groundwater sampling, and conservative tracer testing to collect these data, toimprove the understanding of the hydraulics in the PTA, and to refine the design of thesubsequent ISCO and EISB applications. Each of these characterization activities arefurther discussed below.

Electromagnetic Borehole Flowmeter Survey

The EBF survey will include two separate tests: the first under ambient static (non-pumping) conditions; the second under pumping conditions. The ambient test will


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identify whether and to what extent vertical flow in the FTW may affect the verticaldistribution of VOCs. The test under pumping conditions will identify the verticalprofile of hydraulic conductivity. For both tests, vertical flow readings will be made atregular intervals throughout the open section of the FTW borehole. For the ambient test,the readings will be made under static conditions. For the test under pumpingconditions, a steady flow field is established by pumping from the well at a constant ratewith the pump intake positioned near the top of the water column in the well (inducingupward flow in the well). The flowmeter measurements are then made at numerousdiscrete vertical intervals. The incremental increase in flow velocity between readings isproportional to the influx of water in the interval between readings, which is in turnproportional to the hydraulic conductivity of the interval. Analysis of these data with theconstant-discharge test data provides a vertical profile of hydraulic conductivity (K)across the open interval of the well. These data will then be used to assess zones of highand low flow within the FTW, which, when coupled with data from the depth-discretegeochemical sampling and tracer testing, will assist in assessing the zones within theFTW contributing TCE and suitable for ISCO and/or E1SB testing.

Depth-Discrete Geochemical Sampling

Upon completion of the EBF survey, groundwater samples will be collected fromdiscrete depths corresponding to the conductive fractures and high K zones delineatedfrom the EBF survey data. The samples will be obtained using a discrete depth sampler(such as the KABIS™ sampler or the Solinst™ Model 425 Discrete Interval Sampler)while pumping from the FTW under the same conditions as the EBF test. The sampleswill consist of a mixture of all groundwater that enters the well from deeper intervals.Mass balance calculations based on the vertical profile of flow in the well enable thevertical profile of TCE in the geologic materials to be determined. Groundwater sampleswill be analyzed on-site for field parameters (dissolved oxygen, oxidation-reductionpotential, specific conductance and pH) and samples will be collected for laboratoryanalysis of VOCs and inorganic chemistry. The data will be used, in association with theEBF and tracer test data to assess zones contributing TCE to the FTW, which will servein refining the design of the ISCO and EISB applications.


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Conservative Tracer Testing

Conservative tracer testing will be conducted to: i) estimate groundwater flowvelocities and residence times under pumping conditions; ii) identify preferentialpathways for hydraulic interconnection between the FTW and BCM-1; iii) estimatedispersion and dilution factors; and iv) estimate the percentage of mass capture by therecirculation system. For tracer testing, groundwater will be extracted from the FTW (orspecific intervals therein), amended with a conservative tracer (e.g., bromide or iodide),and re-injected to the aquifer via well BCM-l. Tracer will be added continuously to there-circulating groundwater for several weeks to establish steady state breakthroughprofiles within fracture zones in the FTW. Tracer will be added at a concentration thatwill be easily detectable by an ion-specific electrode (ISE) as it disperses between theinjection and extraction wells, and that will result in an acceptably small increase intracer concentration over background once its concentration comes into equilibrium inthe recirculation system. Tracer breakthrough in the FTW will be monitored on a semi-weekly basis using the depth-discrete sampling protocol described above. Depth-discrete samples will be analyzed on site using ISE methods, and confirmed throughlaboratory analysis by ion chromatography (1C). Tracer concentrations in the extractedgroundwater will also be measured on an hourly basis by the in-line electrodes in therecirculation system (Figure 5). Wells will also be instrumented with pressuretransducers and data loggers to measure water levels during the test.

Data Interpretation

Analysis of the EBF survey data combined with existing data obtained fromconstant-discharge testing will provide a vertical profile of hydraulic conductivity (K)and will assist in delineating the location of highly conductive fractures across the openinterval of the well. Comparisons between the EBF survey data and the depth-discreteTCE sampling data should provide an indication of which fracture zones contain highTCE concentrations. Including the tracer test data will indicate which of these fracturescontaining high TCE concentrations are hydraulically connected to the injection wellBCM-1, which will dictate whether portions of the FTW should be hydraulicallyisolated through packers for the ISCO and EISB tests. Other hydraulic testing such as asustained pumping test may be required to evaluate the sustainable pumping rate, radius


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of influence and capture zone of the portion of the well isolated using the packer(s). Thedata will be used to refine the design for subsequent ISCO and/or EISB pilot testing.

3.3.3 Stage I Go/No-Go Decision Point

A technical memorandum will be prepared that: i) summarizes the procedures usedand data collected for the PTA Characterization Task; ii) provides an interpretation ofthe hydrogeologic conditions within the PTA; and iii) provides recommendations forproceeding with the ISCO and EISB pilot tests. The evaluation will include anassessment of whether the project objectives can be met given site conditions and abilityto collect representative data over the duration of the ISCO/EISB demonstrations (i.e., ago/no-go decision). The evaluation will also confirm that any amendments added to thegroundwater during testing, or products produced by the testing, can be effectivelycontained (and if required removed) by the pilot test system, to ensure the protection ofthe Dublin Borough water supply.

3.3.4 Task 3 - ISCO Demonstration

The re-circulation loop instrumentation used for the tracer test will be modified, asnecessary, to conduct the ISCO pilot test. The ISCO test will consist of three stages,which will be: i) an initial recirculation period without permanganate addition toestablish an initial steady state recirculation condition; ii) addition of permanganate tothe recirculating groundwater and monitoring of system performance; and iii) post-treatment recirculation without permanganate addition to evaluate the potential forrebound of the TCE concentrations. Details for these activities and system operation andmaintenance are discussed in the following subsections.

Establishment of Baseline Recirculation Conditions

An initial two week recirculation period will be conducted without permanganateaddition to establish initial recirculation steady state groundwater chemistry. FTW andBCM-1 will be sampled for baseline analysis of the parameters listed in Table 4.Groundwater data collected in June 2001 for wells BCM-1, BCM-2 and MW-4 will be


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used to establish baseline geochemical conditions. Information regarding the analyticalmethods, detection limits, container size and type, preservation method, and sampleholding times are provided in Table 5. Sampling of these wells will follow samplingprocedures used previously for routine monitoring at the Site.

Permanganate Addition

Following development of the initial steady state recirculation conditions andbaseline sampling, a concentrated potassium permanganate solution will be metered intothe recirculating groundwater to achieve the desired 0.1% permanganate concentration.This concentration will be added for different pulse durations (e.g., 1 , 4 or 8 hours/day)to achieve different mass loadings of permanganate. The observed trends in TCE,chloride and permanganate will be used to assess the destruction rate and removalefficiency of TCE, as well as determine whether any TCE DNAPL that can be contactedby the permanganate is present. For example, if permanganate breakthrough occursand/or chloride peak concentrations decrease with each injection cycle of permanganate,then TCE DNAPL is being depleted. In contrast, if no increase in chloride peakconcentrations or permanganate breakthrough is observed with repeated applications(e.g., at the one hour/day cycle) but an increase in the chloride levels is observed whenthe duration is increased (e.g., 4 hours/day), then we can conclude that more TCEDNAPL mass is present. Permanganate will be added at each time step for 3 weeks orless if steady state conditions are obtained.

Evaluation ofPost-ISCO Recirculation Conditions and Rebound

After approximately two months, permanganate additions will be stopped andextracted water will be recirculated until the TCE concentrations reach a new steadystate. This information will be used to assess if ISCO removed sufficient mass to causea permanent decrease in TCE concentrations, or whether longer-term operation or repeatISCO applications will be required to achieve mass reduction goals.


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System Operation and Maintenance

Routine oversight (e.g., operation and maintenance, and sampling) of the systemwill be performed by ERM, with remote assistance by GeoSyntec. Routine oversightwill consist of regular inspection of substrate/tracer delivery systems and groundwatersampling as outlined on Table 4. System operation will be monitored remotely andconfirmed by weekly site visits to ensure continuous operation and supply ofpermanganate, and to record flow data in case of power outage and reset ofinstrumentation.

Samples will be collected following standard sampling protocols, and analyzed bythe methods identified in Table 5. The laboratory will analyze groundwater samples forVOCs and associated end products (e.g., dissolved manganese, chloride), conservativetracer (i.e. bromide), un-reacted permanganate and dissolved metals. VOCconcentrations will be compared to tracer mass balances to evaluate mass loss of thesetarget contaminants over time.

3.3.5 Stage H Go/No-Go Decision Point

A technical memorandum will be prepared that will summarize the procedures usedand data collected for the ISCO test, and that will provide an evaluation of the ISCOperformance data. The evaluation will include an assessment of whether the projectobjective of TCE source treatment can be met using ISCO alone (i.e., no rebound ofTCE concentrations). The data will also be used to estimate the duration or frequency ofrepeat ISCO applications that may be required to achieve the treatment goals, and thisinformation will be important in evaluating whether EISB should be considered andtested as a more passive polishing technology for source treatment/containment. Basedon this evaluation, a recommendation of whether to proceed with the EISB phase of thetest will be included in the memorandum.


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3.3.6 Task4 - EISB Demonstration

The re-circulation instrumentation used for the ISCO test will be modified, asnecessary, for the EISB pilot test. The EISB test will consist of two stages, which willbe: i) conditioning of PTA redox and geochemical conditions and monitoring of TCEdechlorination through electron donor addition alone; and ii) bioaugmentation andelectron donor delivery to accelerate TCE dechlorination to ethene. Details for theseactivities and system operation and maintenance are discussed in the followingsubsections.

Conditioning of Pilot Test Area Redox Conditions and Geochemistry

The intent of the first stage of biostimulation is to condition the redox environmentof the PTA, following the ISCO test, to provide anaerobic-reducing conditions thatallow favorable reduction of TCE, and that allow introduction and establishment of thenatural, non-pathogenic TCE-degrading culture KB-1. Based on our experience withsimilar groundwater environments, pre-conditioning of the PTA should require 2 to 4weeks, depending on PTA size and baseline conditions and ISCO impacts. Pre-conditioning of the PTA will involve addition of an appropriate carbon source/electrondonor such as sugars (e.g., molasses) or organic acids (e.g., acetate, formate or lactate)to react any remaining permanganate or manganese dioxide precipitates in the PTA,stimulate microbial activity and manipulate redox conditions into an anaerobic andreducing range. Redox conditions (DO and ORP) will be measured in the monitoringnetwork on a weekly basis during the conditioning phase. VOC concentrations will bemonitored on a bi-weekly basis, and some TCE dechlorination to cis-l,2-DCE may beobserved as a result of electron donor addition. Sample collection and handling willfollow standard sampling protocols typically employed for the Site.

Biostimulation, Bioaugmentation & Performance Monitoring

During the aquifer conditioning phase, groundwater samples will be collected foranalysis of TCE and its dechlorination products cis-l,2-DCE, VC and ethene. Based onthe laboratory biotreatability studies, we do not expect that significant cis-l,2-DCEdechlorination to VC and ethene will be promoted by electron donor addition alone;bioaugmentation with natural (i.e., not genetically modified), non-pathogenic


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dehalorespiring bacteria is expected to be required to promote complete dechlorinationof TCE and cis-l,2-DCE to ethene. PTA groundwater monitoring (for VOCs, expectedend products and conservative tracer) will be conducted on a bi-weekly basis to evaluatethe impact of bioaugmentation on the rate and extent of VOC dechlorination. Sampleswill also be collected on a monthly basis for analysis of supporting geochemicalparameters. The pilot test will be operated until VOC dechlorination is complete in therecirculation system, or until sufficient data is generated to predict TCE degradationrates, extents, and to assess technology feasibility at a larger scale. This is expected tobe in the range of 6 to 8 months.

System Operation and Maintenance

Routine oversight (e.g., operation and maintenance, and sampling) of the systemwill be performed by ERM, with remote assistance (as needed) by GeoSyntec. Routineoversight will consist of regular inspection of substrate/tracer delivery systems andgroundwater sampling as indicated in Table 4. To reduce the potential for microbialfouling, electron donor will be added in pulsed mode (once per day) to achieve an initialtime-weighted average concentration of electron donor of 100 mg/L. The electron donordelivery concentration and regime will be refined based on performance data, includingelectron donor consumption rates, VOC degradation rates, and performanceobservations (e.g., fouling). All attempts will be made to prevent well fouling in order tominimize maintenance requirements.

System operation will be monitored remotely and confirmed by weekly site visits toensure continuous operation and supply of electron donor, and to record flow data incase of power outage and reset of instrumentation. Based on previous experience,corrective system maintenance may be occasionally required and will most likelyconsist of replacing fouled recirculation lines. Microbial fouling of theinjection/extraction wells may also occur and may require cleaning by physical orchemical methods to remove biomass from the well surface.

Samples will be collected following standard sampling protocols according to theschedule outlined in Table 4, and analyzed by the methods identified in Table 6. Thelaboratory will analyze groundwater samples for VOCs and associated end products


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(e.g., ethene, ethane), conservative tracer (i.e. bromide or iodide), alternate electronacceptors (e.g., nitrate, nitrite, sulfate), and other indicators of microbial metabolicactivity (e.g., methane, acetate, dissolved iron, sulfide). VOC concentrations will becompared to tracer mass balance to evaluate mass loss of these target contaminants overtime.

3.3.7 Task 5 - Reporting

The data obtained from the PTA Characterization, ISCO and EISB phases of thepilot test will be tabulated, reviewed and interpreted to estimate the rate and extent of insitu TCE degradation accomplished by the technology applications. To the extentpossible, factors affecting ISCO and EISB performance will be identified.Recommendations regarding the technical feasibility of full-scale ISCO or EISBimplementation to treat TCE-impacted groundwater in the suspected source zone, inassociation with plume containment and treatment using the existing OU1 groundwaterextraction and treatment system, will be presented. GeoSyntec will prepare a Pilot TestReport containing detailed study methods, all data generated during the study, ourassessment of the data, conclusions, and recommendations and this information willpublished as an Addendum to the Feasibility Study (ERM, November 2000).


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4. SCHEDULE

The proposed pilot test is expected to require between 12 to 18 months to complete.Figure 6 presents the anticipated schedule for the pilot test, in terms of months fromproject initiation. Mobilization and instrumentation of the PTA will requireapproximately 2 months. PTA characterization is expected to require approximately 2months to complete, including the Stage 1 Decision Point. The ISCO phase of the pilottest will require up to 4 months to complete, depending on the number of steppedpermanganate injections required. If conducted, the EISB phase of the pilot test wouldrequire approximately 6 months to complete, depending on microbial acclimationperiods and biodegradation rates. A Pilot Test Report would be submitted within 2months of receipt of all pilot test data.

Of note, the proposed pilot testing program is expected to achieve a significantdegree of source destruction and remediation in the target treatment area, which isbeneficial in terms of Site restoration. Therefore, the time expended for the pilot test (12to 18 months) would not delay groundwater remediation activities; rather, the pilot testactivities would be part of the overall Site restoration activities. Furthermore, since thesystem has been designed to accommodate scale-up for potential full-scale, the time forremedy implementation, if successful and selected, would be reduced.


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5. REFERENCES

Bartow, G.W., and C.W. Davenport. 1995. Pump and treat accomplishments: A reviewof the effectiveness of groundwater remediation in Santa Clara valley,California, Ground Water Monitoring and Remediation, Spring, 140-146.

Bryant, D., T. Battey, K. Coleman, D. Mullen, and L. Oyelowo. 2001. Permanganate in-situ chemical oxidation of TCE in a fractured bedrock aquifer, Edwards AirForce Base, California, in the proceedings of The First International Conferenceon Oxidation and Reduction Technologies for In-Situ Treatment of Soil andGroundwater, Niagara Falls, Ontario, Canada, June 25-29, 100-103.

Carr, C.S., S.Garg, and J.B. Hughes. 2000. Effect of dechlorinating bacteria on thelongevity and composition of PCE-contaming nonaqueous phase liquids underequilibrium dissolution conditions, Environ. Sci. and Tech., 34(6), 1088-1094.

Cope, N., and J.B. Hughes. 2001. Biologically-enhanced removal of PCE from NAPLsource zones, Environ. Sci. and Tech., 35(10), 2014-2020.

Doty, C.B. and C.C. Travis. 1991. The effectiveness of groundwater pumping as arestoration technology, ORNL7TM-11866, Oak Ridge National Laboratory, OakRidge, TN, May 1991.

Edwards, E.A. and E.E. Cox. 1997. Field and laboratory studies of sequentialan aerobic-aerobic chlorinated solvent bi ode gradation. Accepted for publicationin the proceedings of the Fourth International In Situ and On-SiteBioremediation Symposium, New Orleans, L.A. April 1997.

ERM, November 2000. Feasibility Study, Dublin NPL Site.

GeoSyntec Consultants. 2001. Final Report of a Treatability Study of in Situ ChemicalOxidation and Enhanced Bioremediation of Tri c hi oroethene-Imp actedGroundwater, Former Sequa Dublin NPL Site, Dublin Borough, Pennsylvania,


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Geraghty and Miller, Inc. 1995. Remedial Investigation/Feasibility Study Report forthe Dublin NPL Site, Dublin Borough, Pennsylvania. Volume I, RevisedJanuary 1998.

Hood, E.D. 2000. Permanganate Flushing of DNAPL Source Zones: Experimental andNumerical Investigation, Ph.D. Thesis, Department of Civil Engineering,University of Waterloo, Waterloo, Ontario.

Hood, E.D., N.R. Thomson, and G.J. Farquhar. 1997. In situ oxidation: an innovativetreatment strategy to remediate trichloroethylene and perchloroethyleneDNAPLs in porous media, in the proceedings of the 6" Symposium onGroundwater and Soil Contamination, Montreal, Quebec.

IT Corporation. 2000. In Situ Oxidation Demonstration Test Final Report TreatmentCell C Launch Complex 34 DNAPL Source Zone Oxidation Project.

Major, D.W., E.E. Cox, E, Edwards, and P.W. Hare. 1995. Intrinsic dechlorination oftrichloroethene to ethene in a bedrock aquifer. In: Intrinsic Bioremediation, R.E.Hinchee, J.T. Wilson, and D.C. Downey (eds). Battelle Press, Columbus, Ohio,197-203.

Major, D.W., E.H. Hodgins, and B.J. Butler. 1991. Field and laboratory evidence of insitu biotransformation of tetrachloroethene to ethene and ethane at a chemicaltransfer facility in North Toronto. In: In Situ and On Site Bioreclamation, R.Hinchee and R. Olfenbuttel (Eds.). Buttersworth-Heineman, Stoneham, MA.

Maymo-Gatell, X., J.M. Gossett and S.H. Zinder. 1997. Dehalococcus EthenogenesStrain 195: Ethene production from halogenated aliphatics. In: In Situ and On-Site Bioremediation: Volume 3. Alleman, B.C. AndLeeson, A. (Eds). BattellePress, Columbus, OH.

National Research Council. 1994. Alternatives for ground water cleanup, NationalAcademy Press, Washington DC.


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Schnarr, M.J. 1992. An in-situ oxidative technique to remove residual DNAPL fromsoils, M.A.Sc. Thesis, Department of Civil Engineering, University of Waterloo,Waterloo, Ontario.

Schnarr, M.J. and G.J. Farquhar. 1992. An in situ oxidation technique to destroyresidual DNAPL from soil, in the proceedings of the Third InternationalConference on Ground Water Quality, Dallas, TX, June 21-24.

Schnarr, M.J., C.L. Truax, G.J. Farquhar, E.D. Hood, T. Gonullu, and B. Stickney.1998. Laboratory and controlled field experiments using potassiumpermanganate to remediate trichloroethylene and perchloroethylene DNAPLs inporous media, J. Contam. Hydrol, 29(3), 205-224.

Siegrist, R.L., K.S. Lowe, L.C. Murdoch, T.L. Case, and D.A. Picketing. 1999. In situoxidation by fracture emplaced reactive solids, /. Environ. Eng., 125(5), 429-440.

Sorenson, K.S., R.L. Ely, and L.N. Peterson. 2001, Combining enhanced bioremediationand natural attenuation for cleanup of a TCE-contaminated basalt aquifer, in theproceedings of the Fractured Rock 2001 Conference, Toronto, Ontario, March26-28

USEPA. 1992. Evaluation of Ground-water Extraction Remedies: Phase U, Volume 1 -Summary Report. Publication No. 9355.4-05, Office of Emergency andRemedial Response, Washington, DC.

Yan, Y.E., and F. Schwartz. 1999. Oxidative degradation and kinetics of chlorinatedethylenes by potassium permanganate. / Contam. Hydrol., 37(3), 343-365.

Yang, Y., and P.L. McCarty. 2000. Biologically enhanced dissolution oftetrachloroethene DNAPL, Environ. Sci. and Technol. 34(14)2979-2984.

TR0099VFinal Pilot Test Workplan 30 September 2001

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AR303247


Table 2: Summary of Laboratory Studies Evaluating Biodegradation of ChlorinatedSolvents at Concentrations Approaching Solubility LimitsSequa Dublin NPL Site, Dublin, Pennsylvania

Reference

DiStefano, et al.(1991)Isalou, etal. (1998)

Nielsen & Keasling(1999)Yang & McCarty(2000)Carr, et al. (2000)Harkness, et al.(1999)Yang & McCarty(2000)Cope and Hughes,(2001)

Compound

PCE

PCE

PCE

PCE

PCETCE

TCE

PCE

TestedConcentration

(% of solubility)91mg/L(60%)

lOOmg/L(66%)

DNAPL

DNAPL

DNAPL170rag/L

(15%)300 mg/L

(27%)DNAPL

DechlorinationHalf-life(days)

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FactorND

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AR303254

Monitoring Well

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Site Location, Dublin Borough, PennsylvaniaSequa Dublin NPL Site

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AR303255

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AR303257

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TCE Blodegradation In Groundwater MicrocosmsSequa Dublin Site, Dublin, PA

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