Aminobacter MSH1-Mineralisation of BAM in Sand-Filters Depends on Biological Diversity

BAM (2,6-dichlorobenzamide) is a metabolite of the pesticide dichlobenil. Naturally occurring bacteria that can utilize BAM are rare. Often the compound cannot be degraded before it reaches the groundwater and therefore it poses a serious threat to drinking water supplies. The bacterial strain Aminobacter MSH1 is a BAM degrader and therefore a potential candidate to be amended to sand filters in waterworks to remediate BAM polluted drinking water. A common problem in bioremediation is that bacteria artificially introduced into new diverse environments often thrive poorly, which is even more unfortunate because biologically diverse environments may ensure a more complete decomposition. To test the bioaugmentative potential of MSH1, we used a serial dilution approach to construct microcosms with different biological diversity. Subsequently, we amended Aminobacter MSH1 to the microcosms in two final concentrations; i.e. 10⁵ cells mL^-1 and 10⁷ cells mL^-1. We anticipated that BAM degradation would be most efficient at “intermediate diversities” as low diversity would counteract decomposition because of incomplete decomposition of metabolites and high diversity would be detrimental because of eradication of Aminobacter MSH1. This hypothesis was only confirmed when Aminobacter MSH1 was amended in concentrations of 10⁵ cells mL^-1.Our findings suggest that Aminobacter MSH1 is a very promising bioremediator at several diversity levels.     

Degradation and Mineralization of Nanomolar Concentrations of the Herbicide Dichlobenil and Its Persistent Metabolite 2,6-Dichlorobenzamide by Aminobacter spp. Isolated from Dichlobenil-Treated Soils

2,6-Dichlorobenzamide (BAM), a persistent metabolite from the herbicide 2,6-dichlorobenzonitrile (dichlobenil), is the pesticide residue most frequently detected in Danish groundwater. A BAM-mineralizing bacterial community was enriched from dichlobenil-treated soil sampled from the courtyard of a former plant nursery. A BAM-mineralizing bacterium (designated strain MSH1) was cultivated and identified by 16S rRNA gene sequencing and fatty acid analysis as being closely related to members of the genus Aminobacter, including the only cultured BAM degrader, Aminobacter sp. strain ASI1. Strain MSH1 mineralized 15 to 64% of the added [ring-U-¹⁴C]BAM to ¹⁴CO₂ with BAM at initial concentrations in the range of 7.9 nM to 263.1 μM provided as the sole carbon, nitrogen, and energy source. A quantitative enzyme-linked immunoassay analysis with antibodies against BAM revealed residue concentrations of 0.35 to 18.05 nM BAM following incubation for 10 days, corresponding to a BAM depletion of 95.6 to 99.9%. In contrast to the Aminobacter sp. strain ASI1, strain MSH1 also mineralized the herbicide itself along with several metabolites, including ortho-chlorobenzonitrile, ortho-chlorobenzoic acid, and benzonitrile, making it the first known dichlobenil-mineralizing bacterium. Aminobacter type strains not previously exposed to dichlobenil or BAM were capable of degrading nonchlorinated structural analogs. Combined, these results suggest that closely related Aminobacter strains may have a selective advantage in BAM-contaminated environments, since they are able to use this metabolite or structurally related compounds as a carbon and nitrogen source.     

Transformation of the herbicide 2,6-dichlorobenzonitrile to the persistent metabolite 2,6-dichlorobenzamide (BAM) by soil bacteria known to harbour nitrile hydratase or nitrilase

In soil the herbicide 2,6-dichlorobenzonitrile (dichlobenil) is degraded to the persistent metabolite 2,6-dichlorobenzamide (BAM) which has been detected in 19% of samples taken from Danish groundwater. We tested if common soil bacteria harbouring nitrile-degrading enzymes, nitrile hydratases or nitrilases, were able to degrade dichlobenil in vitro. We showed that several strains degraded dichlobenil stoichiometrically to BAM in 1.5–6.0 days; formation of the amide intermediate thus showed nitrile hydratase rather than nitrilase activity, which would result in formation of 2,6-dichlorobenzoic acid. The non-halogenated␣analogue benzonitrile was also degraded, but here the benzamide intermediate accumulated only transiently showing nitrile hydratase followed by amidase activity. We conclude that a potential for dichlobenil degradation to BAM is found commonly in soil bacteria, whereas further degradation of the BAM intermediate could not be demonstrated.     

The most-probable-number enumeration of dichlobenil and 2,6-dichlorobenzamide (BAM) degrading microbes in Finnish aquifers

In groundwater subsurface deposits and a topsoil from five aquifers having 2,6-dichlorobenzamide (BAM) in water, we determined the most-probable-number (MPN) of 2,6-dichlorobenzonitrile (dichlobenil) and metabolite BAM degrading microorganisms. Dichlobenil and BAM were combined nitrogen sources in the MPN tubes, which were scored positive at concentrations <75% after 1 month incubation. Aerobic and anaerobic microbes degrading dichlobenil and BAM were common in samples in low numbers of 3.6–210 MPN g dw⁻¹. Additional degradation occurred in high MPN dilutions of some samples, the microbial numbers being 0.11–120 × 10⁵ MPN g dw⁻¹. The strains were isolated from low and high dilutions of one deposit, and degradation in pure cultures was confirmed by HPLC. According to the 16S rDNA sequencing, strains were from genera Zoogloea, Pseudomonas, Xanthomonas, Rhodococcus, Nocardioides, Sphingomonas, and Ralstonia. Dichlobenil (45.5 ± 18.3%) and BAM (37.6 ± 14%) degradation was low in the MPN tubes. Despite of microbial BAM degradation activity in subsurface deposits, BAM was measured from groundwater.     

Using 2,6-dichlorobenzamide (BAM) degrading Aminobacter sp. MSH1 in flow through biofilters—initial adhesion and BAM degradation potentials

Micropollutants in groundwater are given significant attention by water companies and authorities due to an increasing awareness that they might be present even above the legal threshold values. As part of our investigations of the possibility to remove the common groundwater pollutant 2,6-dichlorobenzamide (BAM) by introducing the efficient BAM degrader Aminobacter sp. MSH1 into biologically active sand filters, we investigated if the strain adheres to filters containing various filter materials and if the initial adherence and subsequent degradation of BAM could be optimized. We found that most of the inoculated MSH1 cells adhered fast and that parameters like pH and ionic strength had only a minor influence on the adhesion despite huge influence on cell surface hydrophobicity. At the given growth protocol, the MSH1 strain apparently developed a subpopulation that had lost its ability to adhere to the filter materials, which was supported by attempted reinoculation of non-adhered cells. Analysis by quantitative PCR showed that most cells adhered in the top of the filters and that some of these were lost from the filters during initial operation, while insignificant losses occurred after 1 day of operation. The inoculated filters were found to degrade 2.7 μg/L BAM to below 0.1 μg/L at a 1.1-h residence time with insignificant formation of known degradation products. In conclusion, most filter materials and water types should be feasible for inoculation with the MSH1 strain, while more research into degradation at low concentrations and temperatures is needed before this technology is ready for use at actual waterworks.     

Large-scale bioreactor production of the herbicide-degrading Aminobacter sp. strain MSH1

The Aminobacter sp. strain MSH1 has potential for pesticide bioremediation because it degrades the herbicide metabolite 2,6-dichlorobenzamide (BAM). Production of the BAM-degrading bacterium using aerobic bioreactor fermentation was investigated. A mineral salt medium limited for carbon and with an element composition similar to the strain was generated. The optimal pH and temperature for strain growth were determined using shaker flasks and verified in bioreactors. Glucose, fructose, and glycerol were suitable carbon sources for MSH1 (μ?=?0.1 h^?1); slower growth was observed on succinate and acetic acid (μ?=?0.01 h^?1). Standard conditions for growth of the MSH1 strain were defined at pH 7 and 25 °C, with glucose as the carbon source. In bioreactors (1 and 5 L), the specific growth rate of MSH1 increased from μ?=?0.1 h^?1 on traditional mineral salt medium to μ?=?0.18 h^?1 on the optimized mineral salt medium. The biomass yield under standard conditions was 0.47 g dry weight biomass/g glucose consumed. An investigation of the catabolic capacity of MSH1 cells harvested in exponential and stationary growth phases showed a degradation activity per cell of about 3?×?10^?9 μg BAM h^?1. Thus, fast, efficient, large-scale production of herbicide-degrading Aminobacter was possible, bringing the use of this bacterium in bioaugmentation field remediation closer to reality.     

Pathway and rate-limiting step of glyphosate degradation by Aspergillus oryzae A-F02

Aspergillus oryzae A-F02, a glyphosate-degrading fungus, was isolated from an aeration tank in a pesticide factory. The pathway and rate-limiting step of glyphosate (GP) degradation were investigated through metabolite analysis. GP, aminomethylphosphonic acid (AMPA), and methylamine were detected in the fermentation liquid of A. oryzae A-F02, whereas sarcosine and glycine were not. The pathway of GP degradation in A. oryzae A-F02 was revealed: GP was first degraded into AMPA, which was then degraded into methylamine. Finally, methylamine was further degraded into other products. Investigating the effects of the exogenous addition of substrates and metabolites showed that the degradation of GP to AMPA is the rate-limiting step of GP degradation by A. oryzae A-F02. In addition, the accumulation of AMPA and methylamine did not cause feedback inhibition in GP degradation. Results showed that degrading GP to AMPA was a crucial step in the degradation of GP, which determines the degradation rate of GP by A. oryzae A-F02.     

Novel inositol catabolic pathway in Thermotoga maritima

myo‐inositol (MI) is a key sugar alcohol component of various metabolites, e.g. phosphatidylinositol‐based phospholipids that are abundant in animal and plant cells. The seven‐step pathway of MI degradation was previously characterized in various soil bacteria including Bacillus subtilis. Through a combination of bioinformatics and experimental techniques we identified a novel variant of the MI catabolic pathway in the marine hyperthermophilic bacterium Thermotoga maritima. By using in vitro biochemical assays with purified recombinant proteins we characterized four inositol catabolic enzymes encoded in the TM0412–TM0416 chromosomal gene cluster. The novel catabolic pathway in T. maritima starts as the conventional route using the myo‐inositol dehydrogenase IolG followed by three novel reactions. The first 2‐keto‐myo‐inositol intermediate is oxidized by another, previously unknown NAD‐dependent dehydrogenase TM0412 (named IolM), and a yet unidentified product of this reaction is further hydrolysed by TM0413 (IolN) to form 5‐keto‐l ‐gluconate. The fourth step involves epimerization of 5‐keto‐l ‐gluconate to d ‐tagaturonate by TM0416 (IolO). T. maritima is unable to grow on myo‐inositol as a single carbon source. The determined in vitro specificity of the InoEFGK (TM0418–TM0421) transporter to myo‐inositol‐phosphate suggests that the novel pathway in Thermotoga utilizes a phosphorylated derivative of inositol.     

Aerobic Degradation of Dinitrotoluenes and Pathway for Bacterial Degradation of 2,6-Dinitrotoluene

An oxidative pathway for the mineralization of 2,4-dinitrotoluene (2,4-DNT) by Burkholderia sp. strain DNT has been reported previously. We report here the isolation of additional strains with the ability to mineralize 2,4-DNT by the same pathway and the isolation and characterization of bacterial strains that mineralize 2,6-dinitrotoluene (2,6-DNT) by a different pathway. Burkholderia cepacia strain JS850 and Hydrogenophaga palleronii strain JS863 grew on 2,6-DNT as the sole source of carbon and nitrogen. The initial steps in the pathway for degradation of 2,6-DNT were determined by simultaneous induction, enzyme assays, and identification of metabolites through mass spectroscopy and nuclear magnetic resonance. 2,6-DNT was converted to 3-methyl-4-nitrocatechol by a dioxygenation reaction accompanied by the release of nitrite. 3-Methyl-4-nitrocatechol was the substrate for extradiol ring cleavage yielding 2-hydroxy-5-nitro-6-oxohepta-2,4-dienoic acid, which was converted to 2-hydroxy-5-nitropenta-2,4-dienoic acid. 2,4-DNT-degrading strains also converted 2,6-DNT to 3-methyl-4-nitrocatechol but did not metabolize the 3-methyl-4-nitrocatechol. Although 2,6-DNT prevented the degradation of 2,4-DNT by 2,4-DNT-degrading strains, the effect was not the result of inhibition of 2,4-DNT dioxygenase by 2,6-DNT or of 4-methyl-5-nitrocatechol monooxygenase by 3-methyl-4-nitrocatechol.     

Degradation and mineralization of nanomolar concentrations of the herbicide dichlobenil and its persistent metabolite 2,6-dichlorobenzamide by Aminobacter spp. isolated from dichlobenil-treated soils

2,6-Dichlorobenzamide (BAM), a persistent metabolite from the herbicide 2,6-dichlorobenzonitrile (dichlobenil), is the pesticide residue most frequently detected in Danish groundwater. A BAM-mineralizing bacterial community was enriched from dichlobenil-treated soil sampled from the courtyard of a former plant nursery. A BAM-mineralizing bacterium (designated strain MSH1) was cultivated and identified by 16S rRNA gene sequencing and fatty acid analysis as being closely related to members of the genus Aminobacter, including the only cultured BAM degrader, Aminobacter sp. strain ASI1. Strain MSH1 mineralized 15 to 64% of the added [ring-U-(14)C]BAM to (14)CO(2) with BAM at initial concentrations in the range of 7.9 nM to 263.1 muM provided as the sole carbon, nitrogen, and energy source. A quantitative enzyme-linked immunoassay analysis with antibodies against BAM revealed residue concentrations of 0.35 to 18.05 nM BAM following incubation for 10 days, corresponding to a BAM depletion of 95.6 to 99.9%. In contrast to the Aminobacter sp. strain ASI1, strain MSH1 also mineralized the herbicide itself along with several metabolites, including ortho-chlorobenzonitrile, ortho-chlorobenzoic acid, and benzonitrile, making it the first known dichlobenil-mineralizing bacterium. Aminobacter type strains not previously exposed to dichlobenil or BAM were capable of degrading nonchlorinated structural analogs. Combined, these results suggest that closely related Aminobacter strains may have a selective advantage in BAM-contaminated environments, since they are able to use this metabolite or structurally related compounds as a carbon and nitrogen source.     

Identification of the biochemical degradation pathway of triazophos and its intermediate in Diaphorobacter sp. TPD-1

Triazophos is one of the most widely used organophosphorus insecticides usually detectable in the environment. A bacterial strain, Diaphorobacter sp. TPD-1, capable of using triazophos and its intermediate, 1-phenyl-3-hydroxy-1,2,4-triazole (PHT), as its sole carbon sources for growth was isolated from a triazophos-contaminated soil in China. This strain could completely degrade 50 mg l⁻¹ triazophos and PHT to non-detectable level in 24 and 56 h, respectively. During PHT degradation, three metabolites were detected and identified based on tandem mass spectrometry (MS/MS) analysis. Using this information, a biochemical degradation pathway of triazophos by Diaphorobacter sp. TPD-1 was proposed. The first step involved in the degradation of triazophos is the hydrolysis of the P–O ester bond of triazophos to form PHT and o,o-diethyl phosphorothioic acid, then the triazol ring of PHT is subsequently cleaved to form (E)-1-formyl-2-phenyldiazene. Subsequently, (E)-1-formyl-2-phenyldiazene is transformed to 2-phenylhydrazinecarboxylic acid by adding one molecular of H₂O. Finally, the carboxyl group of 2-phenylhydrazinecarboxylic acid is decarboxylated to form phenylhydrazine.     

Biodegradation and metabolites of 2-methylquinoline by acclimated activated sludge under aerobic and denitrifying conditions

2-Methylquinoline is a common organic contaminant in environment. Its degradation in wastewater treatment system has not been fully explored. In this study, batch experiments were conducted to investigate the biodegradation of 2-methylquinoline by activated sludge under both aerobic and denitrifying conditions. The results showed that 2-methylquinoline was degraded under both conditions, but the degradation under aerobic condition was significantly faster than that under denitrifying condition. Total organic carbon (TOC) residues were detected in the final effluent under both conditions, indicating the formation of recalcitrant metabolites. Further analysis identified 1,2,3,4-tetrahydro-2-methylquinoline, N,N-diethyl-benzenamine, and 4-ethyl-benzenamine as common metabolites under both conditions. 4-Butyl-benzenamine and 2,6-diethyl-benzenamine were additional metabolites under the aerobic condition, whereas 2-methyl-4-quinolinol was exclusive to the denitrifying condition. Most of these metabolites were further degraded during the treatment process. 1,2,3,4-Tetrahydro-2-methylquinoline, however, remained in the final effluent under both conditions, implying its persistence in the environment. It can be concluded that 2-methylquinoline undergoes the similar degradation pathway under both treatment conditions.     

Oxidation of syringic acid by extracellular peroxidase of white-rot fungus,Pleurotus ostreatus

The oxidative degradation of syringic acid by the extracellular peroxidase ofPleurotus ostreatus was studied. Three products formed in the oxidation of syringic acid by the peroxidase in the presence of O₂ and H₂O₂ were identified as 2,6-dimethoxyphenol, 2,6-dimethoxy-1,4-dihydroxybenzene, and 2,6-dimethoxy-1,4-benzoquinone. A free radical was detected as the reaction intermediate of the extracellular peroxidase-catalyzed oxidation of acetosyringone. These results can be explained by mechanisms involving the production of a phenoxy radical and subsequent decarboxylation. This is the first time that 2,6-dimethoxyphenol has been identified in extracellular peroxidase-catalyzed reactions.     

In vivo NMR metabolic profiling of Fabrea salina reveals sequential defense mechanisms against ultraviolet radiation

Fabrea salina is a hypersaline ciliate that is known to be among the strongest ultraviolet (UV)-resistant microorganisms; however, the molecular mechanisms of this resistance are almost unknown. By means of in vivo NMR spectroscopy, we determined the metabolic profile of living F. salina cells exposed to visible light and to polychromatic UV-B + UV-A + Vis radiation for several different exposure times. We used unsupervised pattern-recognition analysis to compare these profiles and discovered some metabolites whose concentration changed specifically upon UV exposure and in a dose-dependent manner. This variation was interpreted in terms of a two-phase cell reaction involving at least two different pathways: an early response consisting of degradation processes, followed by a late response activating osmoprotection mechanisms. The first step alters the concentration of formate, acetate, and saturated fatty-acid metabolites, whereas the osmoprotection modifies the activity of betaine moieties and other functionally related metabolites. In the latter pathway, alanine, proline, and sugars suggest a possible incipient protein synthesis as defense and/or degeneration mechanisms. We conclude that NMR spectroscopy on in vivo cells is an optimal approach for investigating the effect of UV-induced stress on the whole metabolome of F. salina because it minimizes the invasiveness of the measurement.     

Pathways of hydrocarbon dissimilation by aPseudomonas as revealed by chloramphenicol

Pseudomonas aeruginosa cells pre-grown on a particular hydrocarbon will oxidize other hydrocarbons as well. Degradation of these hydrocarbons proceeds to a point — depending on their structure — where new enzymes are needed for further degradation. Lack of these enzymes causes accumulation of products. However, secondary adaptation processes tend to decrease yields of intermediates, in particular when adaptation rates are high.By inhibiting these secondary adaptation processes with chloramphenicol (CAM), the amounts of various intermediates could be increased.Propionic acid was accumulated from heptane by hexane-grown cells in yields up to 60% (molar) calculated on heptane converted. The effect of CAM suggests that propionic acid is not subject to -oxidation (acrylate pathway) but is degraded via methylmalonate by adaptive enzymes.2-Methylhexane was converted for 30–40% (molar) intoiso-valeric acid by heptane-grown cells. A known pathway ofiso-valeric acid oxidation incorporates a carbon dioxide fixation step, and lack of this enzyme in heptane-grown cells probably causesiso-valeric acid accumulation.Heptene-1 incubation with heptane-grown cells resulted in a 30–40% conversion into 4-pentenoic plus 2, 4-pentadienoic acids. 6-Heptenoic acid was detected occasionally. A predominant attack at C₇ of the heptene-1 molecule is indicated at least for heptane-grown cells. Attack on the saturated end of the molecule seems well in line with the assumption that alkane oxidation by these bacteria is effected by oxygen transferring enzymes operating on a methyl group, as opposed to the action of a dehydrogenase and formation of an -olefin as the intermediate.     

Degradation pathways of cyclic alkanes in Rhodococcus sp. NDKK48

The degradation pathways for cyclic alkanes (c-alkanes) in Rhodococcus sp. NDKK48 were investigated. Strain NDKK48 used dodecylcyclohexane as a sole carbon and energy source, and five metabolites in the dodecylcyclohexane degradation pathway were detected by gas-chromatography/mass spectra. The metabolites were identified as cyclohexanecarboxylic acid, cyclohexylacetic acid, 1-cyclohexene-1-acetic acid, 4-dodecylcyclohexanol, and 4-dodecylcyclohexanone. The strain degrades dodecylcyclohexane via a ring oxidation pathway and an alkyl side chain oxidation pathway. Cyclohexanecarboxylic acid was further oxidized to muconic acid via 1-cyclohexene-1-carboxylic acid and benzoic acid, and the muconic acid was finally used by strain NDKK48 for growth. Methylcyclohexane and cyclohexane were co-oxidized with hexadecane by strain NDKK48. Methylcyclohexane was degraded via a ring oxidation pathway, and the degradation pathway contained part of the Baeyer-Villiger oxidation for ring cleavage. Cyclohexane was also degraded by the same pathway as methylcyclohexane. Thus, strain NDKK48 has two pathways for the complete degradation of c-alkanes.     

A dominant mutation in β-AMYLASE1 disrupts nighttime control of starch degradation in Arabidopsis leaves

Arabidopsis (Arabidopsis thaliana) leaves possess a mechanism that couples the rate of nighttime starch degradation to the anticipated time of dawn, thus preventing premature exhaustion of starch and nighttime starvation. To shed light on the mechanism, we screened a mutagenized population of a starvation reporter line and isolated a mutant that starved prior to dawn. The mutant had accelerated starch degradation, and the rate was not adjusted to time of dawn. The mutation responsible led to a single amino acid change (S132N) in the starch degradation enzyme BETA-AMYLASE1 (BAM1; mutant allele named bam1-2D), resulting in a dominant, gain-of-function phenotype. Complete loss of BAM1 (in bam1-1) did not affect rates of starch degradation, while expression of BAM1(S132N) in bam1-1 recapitulated the accelerated starch degradation phenotype of bam1-2D. In vitro analysis of recombinant BAM1 and BAM1(S132N) proteins revealed no differences in kinetic or stability properties, but in leaf extracts, BAM1(S132N) apparently had a higher affinity than BAM1 for an established binding partner required for normal rates of starch degradation, LIKE SEX FOUR1 (LSF1). Genetic approaches showed that BAM1(S132N) itself is likely responsible for accelerated starch degradation in bam1-2D and that this activity requires LSF1. Analysis of plants expressing BAM1 with alanine or aspartate rather than serine at position 132 indicated that the gain-of-function phenotype is not related to phosphorylation status at this position. Our results strengthen the view that control of starch degradation in wild-type plants involves dynamic physical interactions of degradative enzymes and related proteins with a central role for complexes containing LSF1.

A single amino acid change in Arabidopsis BETA-AMYLASE1 prevents coupling of night-time starch degradation to time of dawn and causes premature exhaustion of starch reserves in the dark.     

Evidence for aromatic ring reduction in the biodegradation pathwayof carboxylated naphthalene by a sulfate reducing consortium

Naphthalene was used as a model compound in order to study the anaerobic pathway of polycyclic aromatic hydrocarbon degradation. Previously we had determined that carboxylation is an initial step for anaerobic metabolism of naphthalene, but no other intermediate metabolites were identified (Zhang & Young 1997). In the present study we further elucidate the pathway with the identification of six novel naphthalene metabolites detected when cultures were fed naphthalene in the presence of its analog 1-fluoronaphthalene. Results from cultures supplemented with either deuterated naphthalene or non-deuterated naphthalene plus [¹³C]bicarbonate confirm that the metabolites originated from naphthalene. Three of these metabolites were identified by comparison with the following standards: 2-naphthoic acid (2-NA), 5,6,7,8-tetrahydro-2-naphthoic acid, and decahydro-2-naphthoic acid. The presence of 5,6,7,8-tetrahydro-2-NA as a metabolite of naphthalene degradation indicates that the first reduction reaction occurs at the unsubstituted ring, rather than the carboxylated ring. The overall results suggest that after the initial carboxylation of naphthalene, 2-NA is sequentially reduced to decahydro-2-naphthoic acid through 5 hydrogenation reactions, each of which eliminated one double bond. Incorporation of deuterium atoms from D₂O into 5,6,7,8-tetrahydro-2-naphthoic acid suggests that water is the proton source for hydrogenation.     

Microbial community analyses of three distinct, liquid cultures that degrade methyl tert-butyl ether using anaerobic metabolism

Methyl tert-butyl ether (MTBE) is a prevalent groundwater contaminant. In this study, three distinct MTBE-degrading, anaerobic cultures were derived from MTBE-contaminated aquifer material: cultures NW1, NW2 and NW3. The electron acceptors used are anthraquinone-2,6-disulfonate (AQDS; NW1), sulfate (NW2) and fumarate (NW3), respectively. About 1–2 mM MTBE is consistently degraded within 20–30 days in each culture. The 16S rDNA-based amplified ribosomal DNA restriction analysis (ARDRA) was used to analyze the microbial community in each culture. Results indicate novel microorganisms (i.e. no closely related known genera or species) catalyze anaerobic MTBE biodegradation, and microbial diversity varied with different electron acceptors. Tert-butyl alcohol (TBA) accumulated to nearly stoichiometric levels, and these cultures will be critical to understanding the factors that influence TBA accumulation versus degradation. The cultures presented here are the first stable anaerobic MTBE-degrading cultures that have been characterized with respect to taxonomy.     

Degradation of 2,5-dimethylpyrazine by <Emphasis Type="Italic">Rhodococcus erythropolis</Emphasis> strain DP-45 isolated from a waste gas treatment plant of a fishmeal processing company

A bacterium, strain DP-45, capable of degrading 2,5-dimethylpyrazine (2,5-DMP) was isolated and identified as Rhodococcus erythropolis. The strain also grew on many other pyrazines found in the waste gases of food industries, like 2,3-dimethylpyrazine (2,3-DMP), 2,6-dimethylpyrazine (2,6-DMP), 2-ethyl-5(6)-dimethylpyrazine (EMP), 2-ethylpyrazine (EP), 2-methylpyrazine (MP), and 2,3,5-trimethylpyrazine (TMP). The strain utilized 2,5-DMP as sole source of carbon and nitrogen and grew optimally at 25°C with a doubling time of 7.6 h. The degradation of 2,5-DMP was accompanied by the growth of the strain and by the accumulation of a first intermediate, identified as 2-hydroxy-3,6-dimethylpyrazine (HDMP). The disappearance of HDMP was accompanied by the release of ammonium into the medium. No other metabolite was detected. The degradation of 2,5-DMP and HDMP by strain DP-45 required molecular oxygen. The expression of the first enzyme in the pathway was induced by 2,5-DMP and HDMP whereas the second enzyme was constitutively expressed. The activity of the first enzyme was inhibited by diphenyliodonium (DPI), a flavoprotein inhibitor, methimazole, a competitive inhibitor of flavin-containing monooxygenases, and by cytochrome P450 inhibitors, 1-aminobenzotriazole (ABT) and phenylhydrazine (PHZ). The activity of the second enzyme was inhibited by DPI, ABT, and PHZ. Sodium tungstate, a specific antagonist of molybdate, had no influence on growth and consumption of 2,5-DMP by strain DP-45. These results led us to propose that a flavin-dependent monooxygenase or a cytochrome P450-dependent monooxygenase rather than a molybdenum hydroxylase catalyzed the initial hydroxylation step and that a cytochrome P450 enzyme is responsible for the transformation of HDMP in the second step.