Figures
Abstract
The genomes of the Betaproteobacteria Alicycliphilus denitrificans strains BC and K601T have been sequenced to get insight into the physiology of the two strains. Strain BC degrades benzene with chlorate as electron acceptor. The cyclohexanol-degrading denitrifying strain K601T is not able to use chlorate as electron acceptor, while strain BC cannot degrade cyclohexanol. The 16S rRNA sequences of strains BC and K601T are identical and the fatty acid methyl ester patterns of the strains are similar. Basic Local Alignment Search Tool (BLAST) analysis of predicted open reading frames of both strains showed most hits with Acidovorax sp. JS42, a bacterium that degrades nitro-aromatics. The genomes include strain-specific plasmids (pAlide201 in strain K601T and pAlide01 and pAlide02 in strain BC). Key genes of chlorate reduction in strain BC were located on a 120 kb megaplasmid (pAlide01), which was absent in strain K601T. Genes involved in cyclohexanol degradation were only found in strain K601T. Benzene and toluene are degraded via oxygenase-mediated pathways in both strains. Genes involved in the meta-cleavage pathway of catechol are present in the genomes of both strains. Strain BC also contains all genes of the ortho-cleavage pathway. The large number of mono- and dioxygenase genes in the genomes suggests that the two strains have a broader substrate range than known thus far.
Citation: Oosterkamp MJ, Veuskens T, Talarico Saia F, Weelink SAB, Goodwin LA, Daligault HE, et al. (2013) Genome Analysis and Physiological Comparison of Alicycliphilus denitrificans Strains BC and K601T. PLoS ONE 8(6): e66971. https://doi.org/10.1371/journal.pone.0066971
Editor: Arnold Driessen, University of Groningen, The Netherlands
Received: March 7, 2013; Accepted: May 14, 2013; Published: June 25, 2013
Copyright: © 2013 Oosterkamp et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Funding: This research was supported by the Technology Foundation, the Applied Science Division (STW) of the Netherlands Organization for Scientific Research (NWO), project number 08053, the graduate school WIMEK (Wageningen Institute for Environment and Climate Research, which is part of SENSE Research School for Socio-Economic and Natural Sciences of the Environment, www.wimek-new.wur.nl and www.sense.nl), SKB (Dutch Centre for Soil Quality Management and Knowledge Transfer, www.skbodem.nl) and the Consolider project CSD-2007-00055. The research was incorporated in the TRIAS (TRIpartite Approaches 469 toward Soil systems processes) program (http://www.nwo.nl/en/research-and-results/programmes/alw/trias-tripartite-approach-to-soil-system-processes/index.html). Flávia Talarico Saia was supported by a FAPESP (the State of São Paulo Research Foundation) scholarship (2006-01997/5). The work conducted by the DOE JGI is supported by the Office of Science of the United States Department of Energy under contract number DE-AC02-05CH11231. Alfons Stams acknowledges support by an ERC (European Research Counsil) advanced grant (project 323009). The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Introduction
Microbial (per)chlorate-reducing bacteria are able to produce oxygen as intermediate during anaerobic respiration with perchlorate and chlorate [1], [2], [3], [4]. This process can create possible advantages in in-situ bioremediation of anaerobic environments where pollutants like aromatic hydrocarbons persist that are more prone to aerobic degradation [1], [5]. Alicycliphilus denitrificans strain BC is able to couple benzene and toluene degradation to chlorate reduction [3]. Strain BC and A. denitrificans strain K601T are members of the Comamonadaceae family of the Betaproteobacteria [3]. A. denitrificans strain K601T was isolated with cyclohexanol and nitrate as substrates [6]. Contrary to strain BC, strain K601T lacks the chlorate-reducing capability. Strain BC, on the other hand, cannot degrade cyclohexanol [3], [7].
Benzene degradation coupled to chlorate reduction was proposed to be an aerobic process, in which oxygen is derived from the conversion of chlorate is used in oxygenase-dependent pathways [3], [8], [9], [10]. Aerobic degradation of benzene and other aromatic hydrocarbons is well-studied [11], [12], [13]. In aerobic microorganisms, benzene degradation may be initiated by Rieske non-heme iron oxygenases, which catalyze a one-step incorporation of dioxygen into their substrates [14], [15] or by two successive monooxygenations. These monooxygenations are catalyzed by distinct multicomponent toluene/benzene monooxygenases, which produce intermediate phenols, and successively by multicomponent phenol monooxygenases, forming catechols [16]. The end product of catechol degradation is acetyl-CoA that can enter the citric acid cycle.
Degradation of aliphatic hydrocarbons, such as cyclohexanol and cyclohexanone can occur via aerobic and anaerobic pathways [17], [18], [19], [20]. Aerobic degradation of cyclohexanol is mediated by monooxygenases that cleave the aromatic ring. A. denitrificans strain K601T degrades cyclohexanol under anaerobic conditions [6]. Likely, in the anaerobic cyclohexanol degradation pathway cyclohexanol is oxidized to 2-cyclohexenone via cyclohexanone. The enzyme that mediates conversion of 2-cyclohexenone is a bifunctional oxidoreductase that catalyzes both the Michael addition of water to 2-cyclohexenone and the subsequent oxidation of the resulting 3-hydroxycyclohexanone to 1,3-cyclohexanedione [7].
We aimed to obtain insight in the physiological properties of A. denitrificans strains BC and K601T and in the pathways involved in degradation of aromatic and alicyclic compounds with different electron acceptors. Therefore, we studied the genome sequences of A. denitrificans strain BC and strain K601T and performed more detailed physiological comparisons of these strains.
Materials and Methods
Cultivation and DNA Isolation
A. denitrificans strain BC (DSM 18852, JCM 14587) was isolated and described previously [3]. A. denitrificans strain K601T (DSM 14773, CIP 107495) was purchased from the DSMZ, (Deutsche Sammlung von Mikroorganismen und Zellculturen GmbH, Braunschweig, Germany). The strains were cultivated in AW1-sulfate medium as described previously [21]. For DNA isolation cells were grown in 1.2L-bottles containing 500 mL medium with acetate (10 mM) and nitrate (10 mM). Cultures were incubated at 30°C without agitation. Cells were harvested by centrifugation and genomic DNA was isolated following the protocol for bacterial genomic DNA isolation using CTAB of DOE JGI (U.S. Department Of Energy, Joint Genome Institute, CA, USA). DNA concentration was measured using Nanodrop (Thermo scientific) and DNA integrity and quality were determined by loading the genomic DNA on a 1% agarose gel with size and concentration markers according to the instructions of DOE JGI.
Growth Experiments
To determine the substrate spectrum of the A. denitrificans strains, different electron donors were tested in duplicate batches with nitrate (10 mM), oxygen (5% in headspace) or chlorate (10 mM) as electron acceptor. Late log-phase cells of strain BC grown on acetate (10 mM) and nitrate (10 mM) were used as inoculum (5%) for all batches except for batches with aromatic compounds as substrate. In these batches late log-phase cells grown on either benzene (repeated feeds of 0.5 mM) or acetate (10 mM) and chlorate (10 mM) were used as inoculum (5%–10%). Physiological properties of strain K601T were described before [6], but additional substrate tests were performed. Late log-phase cells of strain K601T grown on acetate (10 mM) and either oxygen (5% in headspace) or nitrate (10 mM) were used as inoculum in these tests. Growth was monitored by visual observation of turbidity and the decrease in electron acceptor and donor concentration. Analytical procedures were as described previously [3].
Genome Sequencing, Assembly and Annotation
High molecular weight genomic DNA of A. denitrificans strains BC and K601T was provided to the DOE JGI. For cloning and a combination of Illumina GAii and 454 shotgun sequencing [22], [23], a combination of small and large insert libraries were prepared. For strain BC the Illumina GAii shotgun library generated 32,476,780 reads comprising 1,169 Mb and for strain K601T this generated 28,774,946 reads comprising 2,186 Mb. A 454 Titanium standard library generated 198,756 reads for strain BC and 637,992 reads for strain K601T. For strain BC a paired end 454 library generated 83,659 reads comprising 191 Mb and for strain K601T this generated 314,193 reads comprising 281.7 Mb of 454 paired end data. All general aspects of library construction and sequencing performed at the JGI can be found at http://www.jgi.doe.gov/. The initial draft assembly of strain BC contained 120 contigs in 3 scaffolds and the draft assembly of strain K601T contained 175 contigs in 2 scaffolds.
The 454 Titanium standard data and the 454 paired end data were assembled together with Newbler, version 2.3. The Newbler consensus sequences were computationally shredded into 2 kb overlapping fake reads (shreds). Illumina sequencing data were assembled with VELVET, version 0.7.63 [24], and the consensus sequences were computationally shredded into 1.5 kb shreds. We integrated the 454 Newbler consensus shreds, the Illumina VELVET consensus shreds and the read pairs in the 454 paired end library using parallel phrap, version SPS - 4.24 (High Performance Software, LLC). The software Consed was used in the following finishing process [25], [26], [27]. Illumina data were used to correct potential base errors and increase consensus quality using the software Polisher developed at JGI (www.jgi.doe.gov/software). Possible mis-assemblies were corrected using gapResolution (www.jgi.doe.gov/software), Dupfinisher [28], or sequencing cloned bridging PCR fragments with subcloning. Gaps between contigs were closed by editing in Consed, by PCR and by Bubble PCR primer walks (Cheng, unpublished). To close gaps and to raise the quality of the finished sequence, a total of 511 additional reactions were necessary for strain BC, for strain K601T a total of 415 additional reactions were necessary. The total size of the genome of strain BC is 4,835,713 bp and the genome size of strain K601T is 5,070,751 bp.
The final assembly is based on 191 Mb and 227 Mb of 454 draft data for strains BC and K601T, respectively. This provides an average 40× coverage for the genome of strain BC and an average 45× coverage of the genome of strain K601T. Additionally, the final genomes are based on 650 Mb and 2,099 Mb of Illumina draft data for strains BC and K601T, respectively, which provides an average 135× coverage of the genome of strain BC and an average 416.3× coverage of the genome of strain K601T.
Genes were identified using Prodigal [29] as part of the Oak Ridge National Laboratory genome annotation pipeline, followed by a round of manual curation using the JGI GenePRIMP pipeline [30]. The predicted CDSs were translated and used to search the National Center for Biotechnology Information (NCBI) nonredundant database, UniProt, TIGRFam, Pfam, PRIAM, KEGG, COG, and InterPro databases. These data sources were combined to assert a product description for each predicted protein. Non-coding genes and miscellaneous features were predicted using tRNAscan-SE [31], RNAMMer [32], Rfam [33], TMHMM [34], and signalP [35].
The complete final assemblies were released on September 3 2010 (strain BC) and on January 7 2011 (strain K601T). The genomes were implemented in GenBank. For strain BC the accession numbers are CP002449 (chromosome), CP002450 (megaplasmid), CP002451 (plasmid). For strain K601T the accession numbers are CP002657 (chromosome) and CP002658 (plasmid).
Bidirectional BLAST Analysis
The genomes of A. denitrificans strains BC and K601T were compared using bidirectional BLAST analysis. The FTP server of NCBI (http://www.ncbi.nlm.nih.gov/Ftp) was used to download the protein sequence files obtained from the genome sequences of strains BC and K601T. Bidirectional best hits were obtained by BLAST using a similarity threshold of 50% and a sequence length mismatch of 80 to 120% [36].
Comparative DNA and Cellular Property Analysis of Strains BC and K601T
The G+C content, DNA-DNA hybridization and cellular fatty acids analysis were performed by the DSMZ (Braunschweig, Germany). For cellular fatty acid analysis, strains BC and K601T (DSM 14773T) were grown under identical conditions, i.e. acetate (10 mM) and nitrate (10 mM) in 2L AW-1-sulfate medium at 30°C [21]. ANI and TETRA of strain BC against strain K601T and against Acidovorax sp. JS42, were determined using the software program JSpecies (http://www.imedea.uib.es/jspecies/). ANIb, ANIm and TETRA are calculated as described by Richter and Rosselló-Móra [37].
Results and Discussion
Comparison of Strains BC and K601T
The genomes of A. denitrificans strains BC and K601T have been annotated [38]. Based on 16S rRNA gene sequence analysis A. denitrificans clusters in the family Comamonadaceae of the Betaproteobacteria [3]. Strains K601T and BC showed 99.7% 16S rRNA gene similarity [3]. This study reveals that the three 16S rRNA gene copies present in each genome are identical for both strain BC and K601T, but have different gene location and orientation in each of the strains (Table S1), indicating that the genomes have a different topology. However, the general characteristics of the genomes of strains BC and K601T are similar (Table 1). Furthermore, the strain-specific fatty acid methyl ester patterns of strains BC and K601T are similar (Table S2).
The G+C content of A. denitrificans strains K601T and BC is 66.0 and 67.6 mol%, respectively, as determined by conventional methods [3], [6]. These values are comparable to those determined from the genomic DNA sequences of strains BC and K601T, which gave values of 67.9% and 67.8%, respectively. Experimental DNA-DNA hybridization of strain BC against K601T showed 74.5±3.5% similarity. Based on the genome size difference this value seems low, but the genome of strain K601T is about 7% larger than the genome of strain BC. Genome size differences may affect DNA-DNA hybridization values. However, the experimental error of DNA-DNA hybridization is too high for the genome size difference to have an effect. For species circumscription, a cut-off point of 70% DNA-DNA hybridization similarity is generally used. This cut-off point corresponds to 95% average nucleotide identity of genes present in both strains tested [39]. Based on this cut-off for average nucleotide identity, a tetranucleotide frequency correlation coefficient of >0.99 may support species delineation [37]. Values for average nucleotide identity (ANI) and the tetranucleotide frequency correlation coefficient (TETRA) can be determined using the software programme JSpecies [37]. According to JSpecies, the ANIb (BLAST calculation of ANI) value of strain BC compared to K601T is 98.71% and the ANIm (MUMmer calculation of ANI) value is 99.60%, both well above the threshold of 95% for circumscribing species. The TETRA value was 0.9995, which is above the boundary of 0.99. In summary, ANIb, ANIm and TETRA values also indicate that both strains belong to the same species. As a comparison, we determined the values when comparing strain BC and another member of the Comamonadaceae family, Acidovorax sp. JS42, to which strain BC is closely related. In this case the ANIb value was 84.11%, the ANIm value 87.04% and the TETRA value 0.9756, confirming that these strains are different species, while there was 97% 16S rRNA similarity between the strains.
Bidirectional BLAST analysis showed that strain K601T contains 857 proteins that are not present in strain BC and that strain BC has 721 proteins not present in strain K601T (Fig. 1). An overview of the main metabolic pathways deduced from the genomes of the A. denitrificans strains is depicted in Fig. 2, and specific pathways for strain BC or K601T are indicated. Lists of genes involved in these pathways are given from Table S3, S4, S5.
The amount of protein sequences present only in strains K601T (left) and BC (right) and in both strains (center) is shown in the VENN diagram. 172 protein sequences of strain K601T and 154 of strain BC could not be assigned (for instance duplicates of sequences).
Pathways are indicated using arrows. Black arrows indicate pathways of both strain BC and K601T, red arrows indicate pathways of strain BC, and blue arrows pathways of strain K601T. Red gene numbers indicate genes of strain BC (geneID is Alide_red gene number) and blue gene numbers genes of strain K601T (geneID is Alide2_blue gene number).
Chlorate, Nitrate and Oxygen Respiration Pathways
In contrast to strain K601T, strain BC contains a megaplasmid harboring the genes involved in respiratory chlorate reduction (Alide01) [38]. To date, it is unknown if the megaplasmid can be transferred to other strains, e.g. to strain K601T and if this plasmid allows other strains to grow by respiratory chlorate reduction.
Alide_4611–4614 encode subunits of a DMSO reductase family type II enzyme, or more specifically these genes encode chlorate reductase. Chlorate reductase is composed of four subunits encoded by the clrABCD genes (Alide_4611–4614). The chlorite dismutase gene (cld, Alide_4615) is transcribed in opposite direction (forward) compared to the genes encoding chlorate reductase (reverse). The gene cluster for chlorate reduction of strain BC is highly similar to the cluster of Ideonella dechloratans (Fig. 3), though it is not known whether the genes are plasmid-encoded in this bacterium [40], [41]. In Dechloromonas aromatica strain RCB genes encoding perchlorate reductase and chlorite dismutase are clustered and located on the chromosome (Daro_2580–2584, GenBank accession number of genome CP000089). These genes are clustered in D. agitata as well [42]. Recently, it was found that the genes encoding (per)chlorate reductase and chlorite dismutase in these Dechloromonas strains and two other (per)chlorate-reducing bacteria are located on a genomic island in the chromosomes [43].
The gene cluster for chlorate reduction comprises of chlorite dismutase (cld), chlorate reductase subunit A, B, C and D (clrA, clrB, clrC, clrD), and in I. dechloratans it also includes an insertion sequence (ISIde1). The numbers represent the location of nucleotide differences (in red) of strain BC compared to I. dechloratans counted from the first nucleotide of each gene. The scale bar represents 500 bp. Sequences for the chlorate reduction gene cluster of I. dechloratans were obtained from the EMBL nucleotide sequence database (accession numbers AJ296077 and AJ566363).
Three types of nitrate reductases are known, the dissimilatory membrane-associated Nar, the dissimilatory periplasmic Nap and the assimilatory cytoplasmic Nas. Nas is exclusively involved in assimilatory nitrate reduction to ammonium [44], [45]. Nar and Nap differ with respect to chlorate reduction; Nar can catalyze chlorate reduction, but Nap cannot or only poorly reduce chlorate [46], [47], [48], [49]. Strains BC and K601T have a functional Nar (the gene product of Alide_0508–0511 in BC and of Alide2_0465–0468 in K601T), but no functional Nap or Nas.
Putative nitrite reductase, nitric oxide reductase and nitrous oxide reductase encoding genes (nir genes: Alide_2156–2162 in BC and Alide2_2345–2351 in K601T, nor genes: Alide_0128 in BC and Alide2_0119 in K601T, and nos genes: Alide_3077–3083 in BC and Alide2_1364–1370 in K601T) indicate that nitrate is reduced to N2, which is in accordance with physiological tests [3], [6].
A. denitrificans strains BC and K601T are facultative anaerobes [3], [6]. In the presence of oxygen, cytochrome oxidases catalyze the reduction oxygen to water, resulting in proton translocation and generating ATP by electron transport phosphorylation [50], [51]. Several cytochrome oxidases are known [52]. The genomes of strains BC and K601T encode cytochrome oxidases that can be used under aerobic and micro-aerophilic (high-oxygen affinity) conditions. Cytochrome c oxidase genes are present (Alide_2815, 2816, 3608, 3609, 3487, 3488 in strain BC and Alide2_1643, 1644, 3908, 3909, 3953, 3954 in strain K601T). Furthermore, the genomes contain genes encoding cytochrome o ubiquinol oxidase (Alide_1992–1995 in strain BC and Alide2_2246–2249 in strain K601T) that are employed at high oxygen concentration. At low oxygen concentration, high-affinity cytochrome oxidases are used. The genomes of strains BC and K601T contain cytochrome bd ubiquinol oxidase coding genes (Alide_2141 and 2142 in strain BC and Alide2_2330 and 2331 in strain K601T) and cytochrome c oxidase cbb3-type coding genes (Alide_3325–3328 in strain BC and Alide2_1119–1122 in strain K601T). An overview of genes involved in respiration in A. denitrificans strains BC and K601T is shown in Table S4.
Degradation Pathways of Aromatic and Alicyclic Compounds
Strains K601T and BC are able to degrade benzene and toluene with oxygen, but not with nitrate as electron acceptor (Table 2), indicating that oxygenases are involved in the initial degradation steps of these aromatic compounds. In previous research, two oxygenase-coding genes involved in the initial successive oxidation reactions (BC-BMOa) and the subsequent cleavage of catechol (BC-C23O) were identified in the Alicycliphilus strains [3]. Monooxygenases that catalyze the conversion of benzene or toluene to phenol or methylphenol (benzene/toluene monooxygenases) and of phenols to catechols (phenol monooxygenases), belong to an evolutionary related family of soluble diiron monooxygenases [53]. Based on their alpha subunits, which are assumed to be the site of substrate hydroxylation, phenol as well as benzene/toluene monooxygenases can be differentiated within this family [53], [54]. Genome analysis confirmed the presence of a multicomponent phenol monooxygenase (Alide_0323–0328 in BC; Alide2_0270–0275 in K601T) [3]. The absence of other benzene/toluene mono- and/or dioxygenases suggests that the phenol monooxygenase is responsible for both the hydroxylation of benzene (and/or toluene) to (methyl-)phenol and the subsequent hydroxylation of (methyl-)phenol to (methyl-)catechol. Hydroxylation of the benzene ring catalyzed by phenol monooxygenases has been reported [16]. Phenol monooxygenase of Pseudomonas stutzeri strain OX1 transforms benzene and toluene to catechol and 3-methylcatechol (via phenol and 2-methylphenol), respectively [55]. Moreover, toluene-2-monooxygenase of Burkholderia cepacia strain G4 oxidizes toluene to 3-methylcatechol [56]. Although often lacking among phenol hydroxylase clusters [53], both strain BC and K601T contain a gene coding for a ferredoxin (Alide_0329 in BC; Alide2_0276 in K601T) clustered with the phenol monooxygenase encoding genes. Furthermore, the phenol monooxygenase gene clusters contain genes encoding sigma54 specific transcriptional regulators (Alide_0322 and 0334 in BC; Alide2_0269 and 0279 in K601T) (Fig. 4). The protein products of Alide_0322 and Alide2_0269 have homology to regulatory proteins comprised in previously described phenol monooxygenase gene clusters, such as DmpR of Pseudomonas sp. strain CF600 (45% homology on protein level) that regulates transcription based on direct interaction with aromatic compounds [57]. A similar multicomponent phenol monooxygenase cluster is present in the close relative Acidovorax sp. strain JS42 (Ajs_0206–0210, which has 72% similarity on protein level) [58]. D. aromatica strain RCB and Comamonas sp. strain E6 contain similar monooxygenase clusters with 76% and 86% identity on protein level, respectively [59], and D. aromatica strain RCB also contains a benzene/toluene monooxygenase gene cluster.
In this gene cluster a gene coding for a transcriptional regulator (R) and a gene coding for a ferredoxin (Fe) were also found. Both strains BC and K601T have highly similar gene clusters (99%) with differences only in subunit B2 and B4. The numbers represent the location of the nucleotide differences (in red) of strain BC compared to K601T counted from the first nucleotide of each gene. The scale bar represents 500 bp.
Benzene and toluene degradation leads to the formation of (methyl)catechol. There are two routes of aerobic catechol degradation, the meta- and the ortho-cleavage pathway. All genes involved in the meta-cleavage pathway of (methyl)catechol degradation are present in the genomes of strains BC and K601T. We confirmed the presence of genes encoding a catechol 2,3-dioxygenase in strain BC as reported previously [3] and found homologous genes in strain K601T (Alide_0330 in BC; Alide2_0277 in K601T). This catechol 2,3-dioxygenase catalyzes the extradiol cleavage of catechol to 2-hydroxymuconic semialdehyde. Among the 16 sequenced strains of Comamonadaceae only in five strains catechol 2,3-dioxygenase genes are present [54]. Acidovorax sp. JS42 contains a catechol 2,3-dioxygenase homologous to that of strains BC and K601T with 92% similarity on protein level (Ajs_0214) [58]. Further degradation of 2-hydroxymuconic semialdehyde can proceed via the hydrolytic or the oxalocrotonate branch of the meta-cleavage pathway [60]. Genes encoding enzymes involved in both of these branches are present in the genomes of strains BC and K601T (Fig. 2). The hydrolytic branch is used when toluene is converted via 3-methylcatechol and involves degradation of 2-hydroxymuconic semialdehyde to 2-oxopent-4-enoate. The enzyme catalyzing this conversion is a 2-hydroxymuconic semialdehyde hydrolase (Alide_0336 in BC; Alide2_0281 in K601T). Methyl-catechol and catechol are converted to 2-oxopent-4-enoate using the oxalocrotonate branch of the meta-cleavage pathway, which proceeds via a dehydrogenase, tautomerase and decarboxylase (Alide_0335+0340+0342 in BC; Alide2_0280+0285+0287 in K601T). Finally, 2-oxopent-4-enoate is converted to acetyl-CoA that can enter the citric acid cycle and the genes encoding the enzymes involved in this conversion are Alide_337–339 in strain BC and Alide2_282–284 in strain K601T.
Strain BC, but not K601T, also contains all genes essential for ortho-cleavage of catechol. In this pathway, catechol is converted by catechol 1,2-dioxygenase (encoded by Alide_2650) to cis,cis-muconate, which via muconolactone, 3-oxoadipate-enol-lactone, 3-oxoadipate and 3-oxoadipyl-coA, is converted to acetyl-coA (Alide_2647+2648+2651+3513+3514 of strain BC) [61]. Strain K601T lacks genes coding for catechol 1,2-dioxygenase, muconate cycloisomerase and 3-oxoadipate-enol-lactonase, rendering the ortho-cleavage pathway incomplete.
Although anaerobic benzene degradation was described for some pure bacterial cultures, information about the degradation pathways is incomplete [62], [63], [64], [65]. D. aromatica strain RCB is capable of anaerobic degradation of all BTEX compounds with nitrate as electron acceptor, but A. denitrificans strain BC and K601T cannot degrade these compounds with nitrate while acetate can be degraded with nitrate as electron acceptor (Fig. 5). This is confirmed by the absence of genes that code for known key enzymes for anaerobic aromatic degradation in the genomes of strain BC and K601T, such as benzylsuccinate synthase or ethylbenzene dehydrogenase. Remarkably, these key enzymes are also not present in D. aromatica strain RCB [59]. Strain RCB is able to couple benzene degradation to nitrate reduction, but the occurrence of a strict anaerobic pathway is not proven, and it has been suggested that strain RCB might activate benzene with oxygen produced from the reduction of nitrate or uses hydroxyl free radicals [63], [66]. Oxygen production by nitrite reduction was found in the anaerobic methane degrading Candidatus Methylomirabilis oxyfera [67], [68] and was reported as a possible mechanism for the initial alkane activation in strain HdN1 [69]. A similar mechanism was proposed for benzene and toluene degradation using chlorate as electron acceptor in strain BC [3]. Physiological tests showed that these compounds are degraded in 3 to 5 days in presence of chlorate or oxygen (Fig. 5). Both strains BC and K601T are unable to aerobically utilize ethylbenzene, xylenes and benzoate (Table 2). Accordingly, enzymes involved in the initial steps of degradation of these compounds are not present in the genomes.
Benzene, toluene and acetate degradation is indicated with diamonds. Benzene and toluene concentrations are outlined on a secondary y-axis while acetate and electron acceptor concentrations are indicated on the primary y-axis. Chlorate, nitrate and oxygen consumption is depicted with squares. Chloride production when chlorate is used as electron acceptor is indicated with triangles and no electron acceptor consumption is shown when no significant difference could be observed because of presence of the electron acceptor in abundance.
Cyclohexanol degradation by strain K601T follows a proposed pathway via the intermediates cyclohexanone, 2-cyclohexenone, 3-hydoxycyclohexanone to 1,3-cyclohexanedione and subsequent cleavage of the ring [7]. Genes encoding a three subunit molybdoenzyme (Alide2_4320– Alide2_4322) are present in the genome of strain K601T, but are absent in strain BC. This gene cluster, homologous to carbon monoxide dehydrogenase (CO-DH) and xanthine dehydrogenase (Xdh), is identified as a bifunctional hydratase/alcohol dehydrogenase (MhyADH), belonging to the molybdopterin binding oxidoreductase family with the double function of hydration of cyclohexenone and oxidation of its product 3-hydroxycyclohexanone to 1,3-cyclohexanedione [7]. An ORF located close to the MhyADH shows a sequence (Alide2_4318) with similarity to a flavin-containing domain of fumarate reductase/succinate dehydrogenase and 3-ketosteroid dehydrogenase (KSTD). Based on the reactions catalyzed by those types of enzymes, this sequence might be coding for a cyclohexanone dehydrogenase [7]. Depending on the substrate specificity of the coding enzyme, the conversion of cyclohexanol to cyclohexanone could also be catalyzed by this enzyme. Since members of this group of enzymes are known to catalyze the oxidative hydroxylation of a wide range of aldehydes and aromatic heterocyclic compounds [70] the substrate range of strain K601T might be broader than known so far. More genes closely located to the MhyADH cluster are identified as CO-DH genes (Alide2_4319; Alide2_4326) and are possibly also involved in cyclohexanol degradation.
A cyclopentanol dehydrogenase (Alide2_4312) and, furthermore, more mono- and dioxygenase genes were found in the genomes than the ones we already described, such as an extradiol ring cleavage dioxygenase (Alide_2035 in BC; Alide2_2289 in K601T), a cytochrome P450 (Alide_3136 in BC; Alide2_1311) and several 2-nitropropane dioxygenases (Alide_0303, Alide_0687, Alide_2358, Alide_3754, Alide_3890, Alide_4340 in strain BC; Alide2_0250, Alide2_1856, Alide2_2552, Alide2_4108, Alide2_4236, Alide2_4670 in K601T). This indicates that a broader spectrum of xenobiotic compounds might be degraded by the Alicycliphilus strains. A list of genes involved in degradation of aromatic and alicyclic compounds in strains BC and K601T can be found in Table S5.
Other Physiological Characteristics
Strains BC and K601T were physiologically characterized previously [3], [6]. Additional physiological tests were performed based on the genome sequences. Genome analysis showed that there are no known sugar transporter genes in strains BC and K601T. We did not observe growth of strains BC and K601T with glucose and fructose (Table 2), though previously strain K601T was described to use these sugars [6]. Comparative genome analysis showed that all genes of the tricarboxylic acid cycle are present in strains BC and K601T (Table S3). The two bacteria use carboxylic acids like acetate, lactate, succinate or fumarate as substrates for growth (Table 2). Strains BC and K601T can use the amino acids glutamate and alanine as growth substrates and genes encoding glutamate dehydrogenase (Alide_0201+1063 in BC; Alide2_0190+4027 in K601T) and beta-alanine-pyruvate transaminase (Alide_4363 in BC; Alide2_4693 in K601T) were found in the genome.
Concluding Remarks
Bacteria that degrade benzene and other aromatic hydrocarbons in the absence of oxygen have two strategies for degradation: 1) employment of alternative pathways which are oxygenase-independent [4], [62], [71], [72] and 2) as described here, production of oxygen in the reduction of the electron acceptor to employ oxygenase-dependent pathways. Here we present genome information that shows how A. denitrificans strain BC is able to couple benzene degradation to chlorate reduction. The key genes that code for enzymes that are essential for chlorate reduction and oxygen production are located at a plasmid. A. denitrificans strain K601T lacks this plasmid and thus is not able to degrade benzene with chlorate. The two strains are not able to degrade benzene with nitrate. Only a few pure cultures of anaerobic benzene-degrading bacteria have been described. Azoarcus strain DN11 and AN9, Dechloromonas aromatica strain RCB and JJ and a Bacillus cereus strain were reported to degrade benzene with nitrate as electron acceptor [66], [73], [74], [75]. Recently, Bacillus subtilis and Pseudomonas aeruginosa strains were found to degrade benzene with nitrate and oxygen as electron acceptors [76]. Thus far, it is not clear how these bacteria degrade benzene in the absence of oxygen. One of the options is an aerobic pathway involving oxygen derived from nitrate.
As aromatic hydrocarbons often accumulate in the anaerobic zones of soil, bacteria that are able to degrade hydrocarbons in the absence of oxygen are important for in situ bioremediation. However, oxygen is often difficult to introduce in soil. Chlorate and nitrate addition is an alternative to stimulate the breakdown of aromatic and aliphatic hydrocarbons. A. denitrificans strain BC has the ability to degrade some aromatic hydrocarbons, but its substrate range is limited. However, the observation that the essential genes for chlorate reduction (chlorate reductase and chlorite dismutase) are coded on a plasmid suggests that the ability to degrade hydrocarbons with chlorate can be transferred to bacteria with a wider substrate spectrum such as e.g. Pseudomonas putida. An important prerequisite, however, may be that the oxygenases possess a high affinity for oxygen.
Supporting Information
Table S1.
Location of the 16S and 23S rRNA genes in the genomes of A. denitrificans strains BC and K601T.
https://doi.org/10.1371/journal.pone.0066971.s001
(DOCX)
Table S2.
Major cellular fatty acids of A. denitrificans strains BC and K601T. Data of a previous study of strain K601T [6] are included.
https://doi.org/10.1371/journal.pone.0066971.s002
(DOCX)
Table S3.
List of genes involved in the citric acid cycle and acetate metabolism in A. denitrificans strains BC and K601T.
https://doi.org/10.1371/journal.pone.0066971.s003
(DOCX)
Table S4.
List of genes involved in anaerobic respiration in A. denitrificans strains BC and K601T.
https://doi.org/10.1371/journal.pone.0066971.s004
(DOCX)
Table S5.
List of genes involved in degradation of aromatic and acyclic compounds in A. denitrificans strains BC and K601T.
https://doi.org/10.1371/journal.pone.0066971.s005
(DOCX)
Author Contributions
Conceived and designed the experiments: MJO TV FTS SW AAML JG WJHvB DHP HJ HS GS PJS CMP AJMS. Performed the experiments: MJO TV FTS SW. Analyzed the data: MJO TV FTS SW MD PJS. Wrote the paper: MJO TV. Corrected the manuscript: FTS SW AAML JG WJHvB DHP HJ HS GS PJS CMP AJMS. Involved in genome sequencing of A. denitrificans strains: LAG HED DCB JCD RT CSH MLL LJH.
References
- 1. Coates JD, Bruce RA, Patrick J, Achenbach LA (1999) Hydrocarbon bioremediative potential of (per)chlorate-reducing bacteria. Bioremed J 3: 323–334.
- 2. Coates JD, Achenbach LA (2004) Microbial perchlorate reduction: rocket-fuelled metabolism. Nat Rev Micro 2: 569–580.
- 3. Weelink SAB, Tan NCG, ten Broeke H, van den Kieboom C, van Doesburg W, et al. (2008) Isolation and characterization of Alicycliphilus denitrificans strain BC that grows on benzene with chlorate as electron acceptor. Appl Environ Microbiol 72: 6672–6681.
- 4. Weelink S, van Eekert M, Stams A (2010) Degradation of BTEX by anaerobic bacteria: physiology and application. Rev Environ Sci Biotechnol 9: 359–385.
- 5. Logan BE, Wu J (2002) Enhanced toluene degradation under chlorate-reducing conditions by bioaugmentation of sand columns with chlorate- and toluene-degrading enrichments. Bioremed J 6: 87–95.
- 6. Mechichi T, Stackebrandt E, Fuchs G (2003) Alicycliphilus denitrificans gen. nov., sp. nov., a cyclohexanol-degrading, nitrate-reducing β-proteobacterium. Int J Syst Evol Microbiol 53: 147–152.
- 7. Jin J, Straathof AJ, Pinkse MH, Hanefeld U (2011) Purification, characterization, and cloning of a bifunctional molybdoenzyme with hydratase and alcohol dehydrogenase activity. Appl Microbiol Biotechnol 89: 1831–1840.
- 8. Rikken GB, Kroon AGM, van Ginkel CG (1996) Transformation of (per)chlorate into chloride by a newly isolated bacterium: reduction and dismutation. Appl Microbiol Biotechnol 45: 420–426.
- 9. Ginkel CGv, Rikken GB, Kroon AGM, Kengen SWM (1996) Purification and characterization of chlorite dismutase: a novel oxygen-generating enzyme. Arch Microbiol 166: 321–326.
- 10. Logan BE (1998) A review of chlorate- and perchlorate-respiring microorganisms. Bioremed J 2: 69–79.
- 11. Cao B, Nagarajan K, Loh K-C (2009) Biodegradation of aromatic compounds: current status and opportunities for biomolecular approaches. Appl Microbiol Biotechnol 85: 207–228.
- 12. Di Gennaro P, Bargna A, Sello G (2011) Microbial enzymes for aromatic compound hydroxylation. Appl Microbiol Biotechnol 90: 1817–1827.
- 13. Morikawa M (2010) Dioxygen activation responsible for oxidation of aliphatic and aromatic hydrocarbon compounds: current state and variants. Appl Microbiol Biotechnol 87: 1595–1603.
- 14. Gibson DT, Parales RE (2000) Aromatic hydrocarbon dioxygenases in environmental biotechnology. Curr Opin Biotechnol 11: 236–243.
- 15. Suenaga H, Koyama Y, Miyakoshi M, Miyazaki R, Yano H, et al. (2009) Novel organization of aromatic degradation pathway genes in a microbial community as revealed by metagenomic analysis. ISME J 3: 1335–1348.
- 16.
Pérez-Pantoja D, González B, Pieper DH (2010) Aerobic degradation of aromatic hydrocarbons. In: Timmis KN, editor. Handbook of Hydrocarbon and Lipid Microbiology. Berlin, Germany: Springer-Verlag Berlin Heidelberg. 799–837.
- 17.
Trudgill PW (1984) Microbial degradation of the acyclic ring. In: Gibson DT, editor. Microbial degradation of organic compounds. New York, NY, USA: Marcel Dekker.
- 18. Dangel W, Tschech A, Fuchs G (1988) Anaerobic metabolism of cyclohexanol by denitrifying bacteria. Arch Microbiol 150: 358–362.
- 19. Norris DB, Trudgill PW (1971) The metabolism of cyclohexanol by Nocardia globerula CL1. Biochem J 121: 363–370.
- 20. Dangel W, Tschech A, Fuchs G (1989) Enzyme reactions involved in anaerobic cyclohexanol metabolism by a denitrifying Pseudomonas species. Arch Microbiol 152: 273–279.
- 21. Weelink SAB, Tan NCG, Ten Broeke H, Van Doesburg W, Langenhoff AAM, et al. (2007) Physiological and phylogenetic characterization of a stable benzene-degrading, chlorate-reducing microbial community. FEMS Microbiol Ecol 60: 312–321.
- 22. Bennett S (2004) Solexa Ltd. Pharmacogenomics J 5: 433–438.
- 23. Margulies M, Egholm M, Altman WE, Attiya S, Bader JS, et al. (2005) Genome sequencing in microfabricated high-density picolitre reactors. Nature 437: 376–380.
- 24. Zerbino DR, Birney E (2008) Velvet: algorithms for de novo short read assembly using de Bruijn graphs. Genome Res 18: 821–829.
- 25. Ewing B, Green P (1998) Base-calling of automated sequencer traces using Phred. II. error probabilities. Genome Res 8: 186–194.
- 26. Ewing B, Hillier L, Wendl MC, Green P (1998) Base-calling of automated sequencer traces using Phred. I. accuracy assessment. Genome Res 8: 175–185.
- 27. Gordon D, Abajian C, Green P (1998) Consed: a graphical tool for sequence finishing. Genome Res 8: 195–202.
- 28.
Han CS, Chain P (2006) Finishing repeat regions automatically with Dupfinisher. In: Arabnia HR, Valafar H, editors. Proceedings of the 2006 international conference on bioinformatics & computational biology: CSREA Press. 141–146.
- 29. Hyatt D, Chen G-L, LoCascio P, Land M, Larimer F, et al. (2010) Prodigal: prokaryotic gene recognition and translation initiation site identification. BMC Bioinformatics 11: 119.
- 30. Pati A, Ivanova NN, Mikhailova N, Ovchinnikova G, Hooper SD, et al. (2010) GenePRIMP: a gene prediction improvement pipeline for prokaryotic genomes. Nat Methods 7: 455–457.
- 31. Lowe TM, Eddy SR (1997) tRNAscan-SE: a program for improved detection of transfer RNA genes in genomic sequence. Nucleic Acids Res 25: 955–964.
- 32. Lagesen K, Hallin P, Rødland EA, Stærfeldt H-H, Rognes T, et al. (2007) RNAmmer: consistent and rapid annotation of ribosomal RNA genes. Nucleic Acids Res 35: 3100–3108.
- 33. Griffiths-Jones S, Bateman A, Marshall M, Khanna A, Eddy SR (2003) Rfam: an RNA family database. Nucleic Acids Res 31: 439–441.
- 34. Krogh A, Larsson B, von Heijne G, Sonnhammer ELL (2001) Predicting transmembrane protein topology with a hidden markov model: application to complete genomes. J Mol Biol 305: 567–580.
- 35. Bendtsen JD, Nielsen H, von Heijne G, Brunak S (2004) Improved prediction of signal peptides: SignalP 3.0. J Mol Biol 340: 783–795.
- 36. Altschul SF, Madden TL, Schäffer AA, Zhang J, Zhang Z, et al. (1997) Gapped BLAST and PSI-BLAST: a new generation of protein database search programs. Nucleic Acids Res 25: 3389–3402.
- 37. Richter M, Rosselló-Móra R (2009) Shifting the genomic gold standard for the prokaryotic species definition. Proc Nat Acad Sci 106: 19126–19131.
- 38. Oosterkamp MJ, Veuskens T, Plugge CM, Langenhoff AAM, Gerritse J, et al. (2011) Genome sequences of Alicycliphilus denitrificans strains BC and K601T. J Bacteriol 193: 5028–5029.
- 39. Goris J, Konstantinidis KT, Klappenbach JA, Coenye T, Vandamme P, et al. (2007) DNA-DNA hybridization values and their relationship to whole-genome sequence similarities. Int J Syst Evol Microbiol 57: 81–91.
- 40. Thorell HD, Karlsson J, Portelius E, Nilsson T (2002) Cloning, characterisation, and expression of a novel gene encoding chlorite dismutase from Ideonella dechloratans. Biochim Biophys Acta 1577: 445–451.
- 41. Thorell HD, Stenklo K, Karlsson J, Nilsson T (2003) A gene cluster for chlorate metabolism in Ideonella dechloratans. Appl Environ Microbiol 69: 5585–5592.
- 42. Bender KS, Shang C, Chakraborty R, Belchik SM, Coates JD, et al. (2005) Identification, characterization, and classification of genes encoding perchlorate reductase. J Bacteriol 187: 5090–5096.
- 43. Melnyk RA, Engelbrektson A, Clark IC, Carlson HK, Byrne-Bailey K, et al. (2011) A comparative analysis of the genomes of four perchlorate reducers reveals a genomic island with novel regulatory and metabolic genes. Appl Environ Microbiol 77: 7401–7404.
- 44. Richardson DJ, Berks BC, Russell DA, Spiro S, Taylor CJ (2001) Functional, biochemical and genetic diversity of prokaryotic nitrate reductases. Cell Mol Life Sci 58: 165–178.
- 45. Stolz JF, Basu P (2002) Evolution of nitrate reductase: molecular and structural variations on a common function. Chembiochem 3: 198–206.
- 46. Bedzyk L, Wang T, Ye RW (1999) The periplasmic nitrate reductase in Pseudomonas sp. strain G-179 catalyzes the first step of denitrification. J Bacteriol 181: 2802–2806.
- 47. Bell LC, Richardson DJ, Ferguson SJ (1990) Periplasmic and membrane-bound respiratory nitrate reductases in Thiosphaera pantotropha: the periplasmic enzyme catalyzes the first step in aerobic denitrification. FEBS Lett 265: 85–87.
- 48. Oosterkamp MJ, Mehboob F, Schraa G, Plugge CM, Stams AJM (2011) Nitrate and (per)chlorate reduction pathways in (per)chlorate-reducing bacteria. Biochem Soc Trans 39: 230–235.
- 49. Rusmana I, Nedwell DB (2004) Use of chlorate as a selective inhibitor to distinguish membrane-bound nitrate reductase (Nar) and periplasmic nitrate reductase (Nap) of dissimilative nitrate reducing bacteria in sediment. FEMS Microbiol Ecol 48: 379–386.
- 50. Brunori M, Giuffrè A, Sarti P (2005) Cytochrome c oxidase, ligands and electrons. J Inorg Biochem 99: 324–336.
- 51. Brzezinski P, Gennis R (2008) Cytochrome c oxidase: exciting progress and remaining mysteries. J Bioenerg Biomembr 40: 521–531.
- 52. Thony-Meyer L (1997) Biogenesis of respiratory cytochromes in bacteria. Microbiol Mol Biol Rev 61: 337–376.
- 53. Leahy JG, Batchelor PJ, Morcomb SM (2003) Evolution of the soluble diiron monooxygenases. FEMS Microbiol Rev 27: 449–479.
- 54. Pérez-Pantoja D, Donoso R, Agullo L, Cordova M, Seeger M, et al. (2012) Genomic analysis of the potential for aromatic compounds biodegradation in Burkholderiales. Environ Microbiol 14: 1091–1117.
- 55. Cafaro V, Izzo V, Scognamiglio R, Notomista E, Capasso P, et al. (2004) Phenol hydroxylase and toluene/o-xylene monooxygenase from Pseudomonas stutzeri OX1: interplay between two enzymes. Appl Environ Microbiol 70: 2211–2219.
- 56. Newman LM, Wackett LP (1995) Purification and characterization of toluene 2-monooxygenase from Burkholderia cepacia G4. Biochemistry 34: 14066–14076.
- 57. Shingler V, Moore T (1994) Sensing of aromatic compounds by the DmpR transcriptional activator of phenol-catabolizing Pseudomonas sp. strain CF600. J Bacteriol 176: 1555–1560.
- 58. Kivisaar M (2009) Degradation of nitroaromatic compounds: a model to study evolution of metabolic pathways. Mol Microbiol 74: 777–781.
- 59. Salinero K, Keller K, Feil W, Feil H, Trong S, et al. (2009) Metabolic analysis of the soil microbe Dechloromonas aromatica str. RCB: indications of a surprisingly complex life-style and cryptic anaerobic pathways for aromatic degradation. BMC Genomics 10: 351.
- 60. Harayama S, Mermod N, Rekik M, Lehrbach PR, Timmis KN (1987) Roles of the divergent branches of the meta-cleavage pathway in the degradation of benzoate and substituted benzoates. J Bacteriol 169: 558–564.
- 61. Harwood CS, Parales RE (1996) The beta-ketoadipate pathway and the biology of self-identity. Annu Rev Microbiol 50: 553–590.
- 62. Vogt C, Kleinsteuber S, Richnow H-H (2011) Anaerobic benzene degradation by bacteria. Microb Biotechnol 4: 710–724.
- 63. Weelink SAB, van Eekert MHA, Stams AJM (2010) Degradation of BTEX by anaerobic bacteria: physiology and application. Rev Environ Sci Biotechnol 9: 359–385.
- 64. Musat F, Widdel F (2008) Anaerobic degradation of benzene by a marine sulfate-reducing enrichment culture, and cell hybridization of the dominant phylotype. Environ Microbiol 10: 10–19.
- 65. Abu Laban N, Selesi D, Jobelius C, Meckenstock RU (2009) Anaerobic benzene degradation by Gram-positive sulfate-reducing bacteria. FEMS Microbiol Ecol 68: 300–311.
- 66. Chakraborty R, Coates JD (2005) Hydroxylation and carboxylation–two crucial steps of anaerobic benzene degradation by Dechloromonas strain RCB. Appl Environ Microbiol 71: 5427–5432.
- 67. Ettwig KF, Butler MK, Le Paslier D, Pelletier E, Mangenot S, et al. (2010) Nitrite-driven anaerobic methane oxidation by oxygenic bacteria. Nature 464: 543–548.
- 68. Wu ML, Ettwig KF, Jetten MSM, Strous M, Keltjens JT, et al. (2011) A new intra-aerobic metabolism in the nitrite-dependent anaerobic methane-oxidizing bacterium Candidatus ‘Methylomirabilis oxyfera’. Biochem Soc Trans 39: 243–248.
- 69. Zedelius J, Rabus R, Grundmann O, Werner I, Brodkorb D, et al. (2011) Alkane degradation under anoxic conditions by a nitrate-reducing bacterium with possible involvement of the electron acceptor in substrate activation. Env Microbiol Rep 3: 125–135.
- 70. Andrade SLA, Brondino CD, Feio MJ, Moura I, Moura JJG (2000) Aldehyde oxidoreductase activity in Desulfovibrio alaskensis NCIMB 13491. FEBS J 267: 2054–2061.
- 71. Boll M, Fuchs G, Heider J (2002) Anaerobic oxidation of aromatic compounds and hydrocarbons. Curr Opin Chem Biol 6: 604–611.
- 72. Carmona M, Zamarro MT, Blázquez B, Durante-Rodríguez G, Juárez JF, et al. (2009) Anaerobic catabolism of aromatic compounds: a genetic and genomic view. Microbiol Mol Biol Rev 73: 71–133.
- 73. Dou J, Ding A, Liu X, Du Y, Deng D, et al. (2010) Anaerobic benzene biodegradation by a pure bacterial culture of Bacillus cereus under nitrate reducing conditions. J Environ Sci 22: 709–715.
- 74. Kasai Y, Takahata Y, Manefield M, Watanabe K (2006) RNA-based stable isotope probing and isolation of anaerobic benzene-degrading bacteria from gasoline-contaminated groundwater. Appl Environ Microbiol 72: 3586–3592.
- 75. Holmes DE, Risso C, Smith JA, Lovley DR (2011) Anaerobic oxidation of benzene by the hyperthermophilic archaeon Ferroglobus placidus. Appl Environ Microbiol 77: 5926–5933.
- 76. Mukherjee A, Bordoloi N (2012) Biodegradation of benzene, toluene, and xylene (BTX) in liquid culture and in soil by Bacillus subtilis and Pseudomonas aeruginosa strains and a formulated bacterial consortium. Environ Sci Pollut Res Int 19: 3380–3388.