An evaluation of permeable reactive barrier projects in California

Muegge, John P.; Hadley, Paul W.

doi:10.1002/rem.20228

Cited by 15 publications

(8 citation statements)

References 5 publications

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“…Fe 0 is currently used in groundwater remediation and wastewater treatment [25][26][27][28][29], and drinking water production at household level [30][31][32][33][34][35][36]. Despite existing patents on water treatment using Fe 0 in treatment plants [12,37,38], no concept comparable to the one presented here could be found.…”

Section: Metallic Iron In Drinking Water Treatment Plantsmentioning

confidence: 99%

Metallic iron for safe drinking water worldwide

Noubactep¹

2010

Chemical Engineering Journal

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a b s t r a c tA new concept for household and large-scale safe drinking water production is presented. Raw water is successively filtered through a series of sand and iron filters. Sand filters mostly remove suspended particles (media filtration) and iron filters remove anions, cations, micro-pollutants, natural organic matter, and micro-organisms including pathogens (reactive filtration). Accordingly, treatment steps conventionally achieved with flocculation, sedimentation, rapid sand filtration, activated carbon filtration, and disinfection are achieved in the new concept in only two steps. To prevent bed clogging, Fe 0 is mixed with inert materials, yielding Fe 0 /sand filters. Efficient water treatment in Fe 0 /sand filters has been extensively investigated during the past two decades. Two different contexts are particularly important in this regard: (i) underground permeable reactive barriers and (ii) household water filters. In these studies, the process of aqueous iron corrosion in a packed bed was proven very efficient for unspecific aqueous contaminant removal. Been based on a chemical process (iron corrosion), efficient water treatment in Fe 0 beds is necessarily coupled with a slow flow rate. Therefore, for large communities several filters should work in parallel to produce enough water for storage and distribution. It appears that water filtration through Fe 0 /sand filters is an efficient, affordable, a flexible technology for the whole world.

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Section: Metallic Iron In Drinking Water Treatment Plantsmentioning

confidence: 99%

Metallic iron for safe drinking water worldwide

Noubactep¹

2010

Chemical Engineering Journal

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“…As a consequence, CFCs such as 1,1,2-trichloro-1,2,2-trifluoroethane (CFC-113) are common groundwater contaminants . Although the manufacture of CFCs has been phased out under the 1987 Montreal protocol because of their stratospheric ozone depletion potential, releases of CFCs into groundwater from various legacy sources, such as landfills, leaking equipment, and historic spills remain a challenge for environmental cleanup. − CFC-113 has been identified at many sites as a major or a co-contaminant together with chlorinated solvents, often chlorinated ethenes, − which are frequently detected groundwater contaminants . While phylogenetically diverse bacteria can dechlorinate tetrachloroethene (PCE) and trichloroethene (TCE) to cis -1,2-dichloroethene ( cis -DCE), only members of the genera Dehalococcoides ( Dhc ) and Dehalogenimonas (Dhgm) are known to completely dechlorinate cis -DCE to environmentally benign ethene. , Despite the co-occurrence of CFC-113 and chlorinated solvents in the environment, the impact of CFC-113 and its potential transformation product(s) on reductive dechlorination of chlorinated solvents, in particular, chlorinated ethenes by organohalide-respiring Dehalococcoidia are not known.…”

Section: Introductionmentioning

confidence: 99%

“…Several transformation intermediates, including 2,2-dichloro-1,1,1-trifluoroethane (HCFC-123a), 2-chloro-1,1,1-trifluoroethane (HCFC-133), 1-chloro-1,1,2-trifluoroethane (HCFC-133b), chlorotrifluoroethene (CTFE), and trifluoroethene (TFE) were detected (Figure ). Zero valent iron (ZVI) − and naturally occurring reactive mineral phases − have been reported to mediate abiotic transformation of halogenated organic compounds. Specifically, ZVI has been demonstrated to degrade CFC-113 to HCFC-123a and CTFE (Figure ), and permeable reactive ZVI barriers have been implemented for in situ remediation of CFC-113-contaminated groundwater .…”

Section: Introductionmentioning

confidence: 99%

Biotic and Abiotic Dehalogenation of 1,1,2-Trichloro-1,2,2-trifluoroethane (CFC-113): Implications for Bacterial Detoxification of Chlorinated Ethenes

Mack

Seger

et al. 2019

Environ. Sci. Technol.

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Chlorofluorocarbons including 1,1,2-trichloro-1,2,2-trifluoroethane (CFC-113) often occur in groundwater plumes comingled with chlorinated solvents such as trichloroethene (TCE). We show that CFC-113 inhibits reductive dechlorination by Dehalococcoides mccartyi (Dhc) in a concentration-dependent manner, causing cis-1,2-dichloroethene (cis-DCE) stalls. Following a 17-day exposure of Dhc-containing consortium SDC-9 to 76 μM CFC-113, cis-DCE dechlorination activity did not recover after CFC-113 removal. River sediment microcosms demonstrated that CFC-113 was subject to microbial degradation under anoxic conditions, and chlorotrifluoroethene (CTFE) was observed as a transformation product. No degradation of CFC-113 was observed in killed controls and in incubations with reactive minerals including mackinawite, green rust, magnetite, and manganese dioxide. In vitro experiments with reduced corrinoid (i.e., vitamin B 12 ) mediated reductive dechlorination of CFC-113 to CTFE and trifluoroethene (TFE) followed by reductive defluorination of TFE to cis-1,2-difluoroethene (cis-DFE) as an end product. This biomimetic degradation of CFC-113 to cis-DFE was also demonstrated in vivo using the corrinoid-producing homoacetogen Sporomusa ovata, suggesting the cometabolic microbial reductive dechlorination and reductive defluorination of CFC-113 to cis-DFE is feasible under anoxic in situ conditions. The CFC-113 degradation intermediates CTFE, TFE, and cis-DFE did not inhibit TCE dechlorination by Dhc, indicating that the initial reductive transformation step can overcome cis-DCE stalls.

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“…In practice, it is assumed that PRBs filled with ZVI must work efficiently for at least 10 years to be environmentally more effective in relation to other remediation technologies [23]. In the case of using parameters estimated from laboratory studies, longevity is considered to be approximately proportional to the thickness (b) of a barrier [24]. Finally, in calculating the optimal thickness, workable longevity (10 years) and evaluation of the minimum thickness (the thinnest layer of reactive materials that may reduce concentrations of contaminates to target levels) should be examined.…”

Section: Prb Designmentioning

confidence: 99%

Optimization Model for the Design of Multi-layered Permeable Reactive Barriers

Połoński

Pawluk

Rybka

2017

IOP Conf. Ser.: Mater. Sci. Eng.

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Abstract. Permeable reactive barriers (PRBs) are employed as in situ groundwater remediation technology. The installation of PRBs is usually a major investment, where one of the biggest cost drivers are material costs. PRBs are barriers against contaminants moving under the natural gradient, however not against groundwater contaminants. The most common construction of a PRB is a single barrier, but in the case of contaminant mixtures a multi-layered construction, i.e. a combination of different reactive materials and removal processes, is required. The most important parameters for PRB design are dimensions. The barrier must be long enough to treat the entire width of the plume (dimension perpendicular to groundwater flow) and should extend to and be keyed into an impermeable layer. The problem is to determine the optimal thickness of a PRB, which should provide a residence time appropriate for reducing the concentration of contaminants to the desired effluent concentration. In PRBs, design is accomplished using numerical methods or simulators, which are useful to predict the scenarios and evaluate the resulting groundwater flow systems to specific site conditions. On the other hand, numerical methods are complicated and may have significant errors if the discretization is too coarse or is incorrectly aligned. This paper deals with a simple, conceptual model of a one-approach optimization method for multi-layered PRB design. Based on literature and laboratory test results (residence time, density and hydraulic coefficient), a selection of layers of reactive materials was determined. Considering the lowest cost of the reactive materials, the required thicknesses of activated carbon, zeolite and zero valent iron were calculated using two different algorithms. The simple model may be used for preliminary barrier design and cost calculations. Using the optimization model in a preliminary design stage, it is possible to reject the PRB concept and avoid losing time for the complicated analysis.

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An evaluation of permeable reactive barrier projects in California

Abstract: Permeable reactive barriers made of zero-valent iron (ZVI PRBs)

Cited by 15 publications

References 5 publications

Metallic iron for safe drinking water worldwide

Metallic iron for safe drinking water worldwide

Biotic and Abiotic Dehalogenation of 1,1,2-Trichloro-1,2,2-trifluoroethane (CFC-113): Implications for Bacterial Detoxification of Chlorinated Ethenes

Optimization Model for the Design of Multi-layered Permeable Reactive Barriers

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