Biotransformation of Trichloroethylene by a Phenol-Induced Mixed Culture

Shurtliff, Mathew M.; Parkin, Gene F.; Weathers, Lenly J.; Gibson, David T.

doi:10.1061/(asce)0733-9372(1996)122:7(581)

Cited by 33 publications

(23 citation statements)

References 34 publications

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“…Among other methods of remediation (17,20,22), natural and/or engineered bioattenuation has significant potential to degrade TCE from soil and groundwater systems. The biodegradation of TCE can occur either anaerobically through reductive dechlorination (7,29) or aerobically (8,13,15,18,24,27). A bacterial strain that is capable of the latter process is Burkholderia cepacia G4.…”

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confidence: 99%

“…Dehalogenation with this strain is cometabolic and requires a primary substrate such as toluene or phenol in order to generate the toluene ortho-monooxygenase enzyme that is necessary for aerobic TCE degradation (27). The literature describes various degrees of this type of TCE degradation (8,13,15,18,24), and here we investigated its relationship between cell density and removal rate. As a novel aspect of this work, we investigated associated carbon isotope fractionations.…”

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confidence: 99%

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Carbon Isotope Fractionation during Aerobic Biodegradation of Trichloroethene by Burkholderia cepacia G4: a Tool To Map Degradation Mechanisms

Barth

Slater

Schüth

et al. 2002

Appl Environ Microbiol

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The strain Burkholderia cepacia G4 aerobically mineralized trichloroethene (TCE) to CO 2 over a time period of ϳ20 h. Three biodegradation experiments were conducted with different bacterial optical densities at 540 nm (OD 540 s) in order to test whether isotope fractionation was consistent. The resulting TCE degradation was 93, 83.8, and 57.2% (i.e., 7.0, 16.2, and 42.8% TCE remaining) at OD 540 s of 2.0, 1.1, and 0.6, respectively. ODs also correlated linearly with zero-order degradation rates (1.99, 1.11, and 0.64 mol h ؊1 ). While initial nonequilibrium mass losses of TCE produced only minor carbon isotope shifts (expressed in per mille ␦ 13 C VPDB ), they were 57.2, 39.6, and 17.0‰ between the initial and final TCE levels for the three experiments, in decreasing order of their OD 540 s. Despite these strong isotope shifts, we found a largely uniform isotope fractionation. The latter is expressed with a Rayleigh enrichment factor, , and was ؊18.2 when all experiments were grouped to a common point of 42.8% TCE remaining. Although, decreases of to ؊20.7 were observed near complete degradation, our enrichment factors were significantly more negative than those reported for anaerobic dehalogenation of TCE. This indicates typical isotope fractionation for specific enzymatic mechanisms that can help to differentiate between degradation pathways.

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confidence: 99%

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confidence: 99%

Carbon Isotope Fractionation during Aerobic Biodegradation of Trichloroethene by Burkholderia cepacia G4: a Tool To Map Degradation Mechanisms

Barth

Slater

Schüth

et al. 2002

Appl Environ Microbiol

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“…These results suggest that the oxidized intermediates of TCE rather than TCE itself are responsible for cell inactivation. Furthermore, numerous studies have demonstrated the incorporation of radiolabeled TCE into cell biomass (Malachowsky et al 1994;Shurtliff et al 1996) as well as covalent bonding of radiolabeled intermediates onto proteins including the monooxygenases involved in the transformation (Fox et al 1990;Oldenhuis et al 1991;Rasche et al 1991;Newman & Wackett 1997).…”

Section: Microbiology and Biochemistry Of Higher Chlorinated Ethene Bmentioning

confidence: 99%

“…The mineralization of organic carbon in TCE has been indicated by the conversion of [ 14 C]-TCE to 14 CO 2 , which has been recovered in yields of 19-28% (Malachowsky et al 1994;Shurtliff et al 1996;Lontoh et al 2000).…”

Section: Microbiology and Biochemistry Of Higher Chlorinated Ethene Bmentioning

confidence: 99%

Biodegradability of chlorinated solvents and related chlorinated aliphatic compounds

Field

Sierra-Álvarez

2004

Rev Environ Sci Biotechnol

128

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The biodegradability of chlorinated methanes, chlorinated ethanes, chlorinated ethenes, chlorofluorocarbons (CFCs), chlorinated acetic acids, chlorinated propanoids and chlorinated butadienes was evaluated based on literature data. Evidence for the biodegradation of compounds in all of the compound categories evaluated has been reported. A broad range of chlorinated aliphatic structures are susceptible to biodegradation under a variety of physiological and redox conditions. Microbial biodegradation of a wide variety of chlorinated aliphatic compounds was shown to occur under five physiological conditions. However, any given physiological condition could only act upon a subset of the chlorinated compounds. Firstly, chlorinated compounds are used as an electron donor and carbon source under aerobic conditions. Secondly, chlorinated compounds are cometabolized under aerobic conditions while the microorganisms are growing (or otherwise already have grown) on another primary substrate. Thirdly, chlorinated compounds are also degraded under anaerobic conditions in which they are utilized as an electron donor and carbon source. Fourthly, chlorinated compounds can serve as an electron acceptor to support respiration of anaerobic microorganisms utilizing simple electron donating substrates. Lastly chlorinated compounds are subject to anaerobic cometabolism becoming biotransformed while the microorganisms grow on other primary substrate or electron acceptor. The literature survey demonstrates that, in many cases, chlorinated compounds are completely mineralised to benign end products. Additionally, biodegradation can occur rapidly. Growth rates exceeding 1 d )1 were observed for many compounds. Most compound categories include chlorinated structures that are used to support microbial growth. Growth can be due to the use of the chlorinated compound as an electron donor or alternatively to the use of the chlorinated compound as an electron acceptor (halorespiration). Biodegradation linked to growth is important, since under such conditions, rates of degradation will increase as the microbial population (biocatalyst) increases. Combinations of redox conditions are favorable for the biodegradation of highly chlorinated structures that are recalcitrant to degradation under aerobic conditions. However, under anaerobic conditions, highly chlorinated structures are partially dehalogenated to lower chlorinated counterparts. The lower chlorinated compounds are subsequently more readily mineralized under aerobic conditions.Abbreviations: A

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“…Roots provide ideal attachment locations, steady redox conditions, and a steady food supply of exudates consisting of organic acids, enzymes, amino acids, and complex carbohydrates (4,23); hence, engineered rhizobacteria have a niche in which to flourish (the bacterial populations in the rhizosphere are 2 to 3 orders of magnitude larger than those in the outlying soil [4]). Since high levels of phenolic compounds have been found in root exudates (7), these compounds also induce bacterial dioxygenase remediation pathways (20). Along with providing the bacteria with both nutrients and oxygen for chlorinated aliphatic compound degradation, the trees also transport the bacteria throughout TCE-contaminated soil (from surface to aquifer), transport TCE-contaminated water to the rhizosphere, and aerate the soil.…”

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confidence: 99%

Rhizosphere Competitiveness of Trichloroethylene-Degrading, Poplar-Colonizing Recombinant Bacteria

Shim

Chauhan

Ryoo

et al. 2000

Appl Environ Microbiol

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Indigenous bacteria from poplar tree (Populus canadensis var. eugenei 'Imperial Carolina') and southern California shrub rhizospheres, as well as two tree-colonizing Rhizobium strains (ATCC 10320 and ATCC 35645), were engineered to express constitutively and stably toluene o-monooxygenase (TOM) from Burkholderia cepacia G4 by integrating the tom locus into the chromosome. The poplar and Rhizobium recombinant bacteria degraded trichloroethylene at a rate of 0.8 to 2.1 nmol/min/mg of protein and were competitive against the unengineered hosts in wheat and barley rhizospheres for 1 month (colonization occurred at a level of 1.0 ؋ 10 5 to 23 ؋ 10 5 CFU/cm of root). In addition, six of these recombinants colonized poplar roots stably and competitively with populations as large as 79% ؎ 12% of all rhizosphere bacteria after 28 days (0.2 ؋ 10 5 to 31 ؋ 10 5 CFU/cm of root). Furthermore, five of the most competitive poplar recombinants (e.g., Pb3-1 and Pb5-1, which were identified as Pseudomonas sp. strain PsK recombinants) retained the ability to express TOM for 29 days as 100% ؎ 0% of the recombinants detected in the poplar rhizosphere expressed TOM constitutively.

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Biotransformation of Trichloroethylene by a Phenol-Induced Mixed Culture

Cited by 33 publications

References 34 publications

Carbon Isotope Fractionation during Aerobic Biodegradation of Trichloroethene by Burkholderia cepacia G4: a Tool To Map Degradation Mechanisms

Carbon Isotope Fractionation during Aerobic Biodegradation of Trichloroethene by Burkholderia cepacia G4: a Tool To Map Degradation Mechanisms

Biodegradability of chlorinated solvents and related chlorinated aliphatic compounds

Rhizosphere Competitiveness of Trichloroethylene-Degrading, Poplar-Colonizing Recombinant Bacteria

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