The aerobic degradation of aromatic compounds by bacteria is performed by dioxygenases. To show some characteristic patterns of the dioxygenase genotype and its degradation specificities, twenty-nine gram-negative bacterial cultures were obtained from sediment contaminated with phenolic compounds in Wuhan, China. The isolates were phylogenetically diverse and belonged to 10 genera. All 29 gram-negative bacteria were able to utilize phenol, m-dihydroxybenzene and 2-hydroxybenzoic acid as the sole carbon sources, and members of the three primary genera Pseudomonas, Acinetobacter and Alcaligenes were able to grow in the presence of multiple monoaromatic compounds. PCR and DNA sequence analysis were used to detect dioxygenase genes coding for catechol 1,2-dioxygenase, catechol 2,3-dioxygenase and protocatechuate 3,4-dioxygenase. The results showed that there are 4 genotypes; most strains are either PNP (catechol 1,2-dioxygenase gene is positive, catechol 2,3-dioxygenase gene is negative, protocatechuate 3,4-dioxygenase gene is positive) or PNN (catechol 1,2-dioxygenase gene is positive, catechol 2,3-dioxygenase gene is negative, protocatechuate 3,4-dioxygenase gene is negative). The strains with two dioxygenase genes can usually grow on many more aromatic compounds than strains with one dioxygenase gene. Degradation experiments using a mixed culture representing four bacterial genotypes resulted in the rapid degradation of phenol. Determinations of substrate utilization and phenol degradation revealed their affiliations through dioxygenase genotype data.
Phenol and phenolic compounds are important for many industries. They are found in the waste of many industrial processes, such as oil refineries, cooking plants, industrial resin manufacturing, petroleum-based processing plants, pharmaceuticals, plastic manufacturing, and varnish manufacturing industries.1 Their extensive use has led to the widespread contamination of soils, rivers, industrial effluents, and landfill runoff waters. Phenolic compounds have adverse effects on aquatic life, plants and many other organisms, and they can act as substrate inhibitors during the biotransformation process. Thus, it is necessary to eliminate phenolic compounds effectively to protect the environment and to safeguard the health of human beings.2
For the removal of phenolic compounds, biological methods have attracted more attention than physical and chemical methods because many different bacteria are known to utilize phenolic compounds as their sole carbon and energy sources.3 The biodegradation of phenol and its derivatives by bacteria has been extensively studied. A large number of different bacterial species including gram-positive bacteria, such as Bacillus4 and Rhodococcus, and gram-negative bacteria, such as Pseudomonas,5,6Klebsiella, Ochrobactrum, Bordetella, Achromobacter, Halomonas,7Ralstonia8 and Alcaligenes, have been reported to degrade phenolic compounds. Among these genera, the Pseudomonas genus is known to be an efficient degrader of phenolic compounds, and its presence is very well-established in contaminated sites. Pseudomonas sp. CP4 was shown to degrade more than 90% of the initial 500mgL−1 phenol in 24h, and it was an efficient partner in a mixed culture with Pseudomonas aeruginosa 3mT for the degradation of 3-chlorobenzoate (3-CBA) and phenol/cresol mixtures.9
The aerobic degradation pathway of phenolic compounds by bacteria is well-known.10 Despite the vast changes that occur in phenolic compounds in aquatic and terrestrial environments, the degradation of different phenolic compounds usually proceeds through a limited number of metabolic pathways. Most phenolic compounds are first converted to catechol or protocatechuate.11 In the α-ketoacid and β-ketoadipate pathways, catechol or protocatechuate is further oxidized by catechol 2,3-dioxygenase, catechol 1,2-dioxygenase or protocatechuate 3,4-dioxygenase to β-ketoadipate.12,13 This β-ketoadipate is then further converted, with two additional steps, into Krebs cycle intermediates.
To obtain further insight about environmental bacteria that are capable of degrading aromatic compounds, we attempted to collect bacteria that use multiple aromatic compounds and analyze their affiliations from dioxygenase genotype data. This study also includes an analysis of the phenol degradation capability of pure cultures containing both mixed and different genotypes.
Materials and methodsMediaYeast extract and peptone were purchased from Oxoid Ltd (Basingstoke, England). The minimal medium (MM) was composed of the following (in gL−1 of deionized water): KH2PO4 1g, Na2HPO4 1.3g, (NH4)2SO4 1g, MgSO4 0.2g, MnCl2·4H2O 0.005g, NaMoO4·2H2O 0.001g, and CuCl2 0.0005g. The pH was adjusted to 7.0. After autoclaving the media at 120°C for 20min, it was supplemented with filter-sterilized solutions of 0.05gL−1 FeSO4·7H2O, 0.02gL−1 CaCl2, and 0.005gL−1 ZnSO4·7H2O 0.005g. Different aromatic compounds were used as the sole carbon and energy sources, respectively. Solid MM plates contained 15gL−1 agar. The LB medium was composed of the following (in gL−1 of deionized water): 10g NaCl, 10g peptone, and 5g yeast extract, pH 7.0.
Isolation of phenol-degrading bacteriaSediment samples were collected at a site near the primary pollutant-emission outlet of a chemical plant located in Wuhan, China. Pollutants have been released into the environment from this site without any control for many years; these pollutants include phenolic compounds, primarily phenol, chlorophenols, and methylaminophenol. The sediment contained approximately 457mgkg−1 phenol, pH 6.36. Sediment samples were collected and then stored in closed containers at 4°C before use. Enrichment cultures were prepared from the sediment slurry using liquid MM medium. Ten grams of slurry was added to 90mL of MM medium in a 250-mL Erlenmeyer flask. Phenol was added at a concentration of 500mg/L. The flasks were incubated at 30°C with shaking (200rpm) for 2 days. The culture suspension was serially diluted and plated onto MM agar medium containing 500mgL−1 phenol.14 The cultures that were capable of forming clear zones were checked for purity by plating them on LB agar. Isolated colonies were gram-stained and examined microscopically. In total, 29 of the 50 pure isolated cultures were stored at −20°C in LB broth containing 20% glycerine.
Growth on monoaromatic compoundsAnalytical-grade monoaromatic compounds (phenol, m-dihydroxybenzene, benzene-1,2,3-triol, 3,5-dinitrosalicylic acid, 4-dimethylaminobenzaldehyde 1,2-diaminobenzene, 2-hydroxybenzoic acid, 2,4,6-trinitrophenol, o-aminobenzoic acid, 4-nitrobenzoic acid, and potassium 2-carboxybenzoate) were prepared as stock solutions at 10gL−1. Each stock solution was filter-sterilized through a 0.2μm filter and added to liquid MM medium at a final concentration of 100mgL−1. The solid culture method was used to determine the carbon source in use; this approach has been accepted and used in many studies.14 The cultures were grown overnight in LB broth (tryptone, 10gL−1; yeast extract, 5gL−1; and NaCl, 10gL−1), followed by two washes with 50mM phosphate buffer and resuspension in the same volume of liquid MM medium, and then 2μL of each of the cultures was spotted onto monoaromatic compound MM plates. In this way, 8 cultures per plate were conveniently tested. Duplicate plates were prepared for each monoaromatic compound, and then they were incubated at 30°C. Each plate was checked for growth after 4 days of culture. MM agar plates without monoaromatic compound were used as controls.
16S rRNA gene isolation and sequencingGenomic DNA was isolated from the bacterial strains that were capable of degrading one or more of the monoaromatic compounds tested using the method developed by Yoon et al.15 Purified DNA was then subjected to PCR amplification. Universal primers were used, with fD1 for positions 7–26 in the Escherichia coli 16S rRNA gene and rD1 for positions 1541–1525 (Table 1). Fifty microliters of each PCR mixture consisted of 3μL of extracted DNA, 2μL of dNTPs (2.5mM), 2μL of primers fD1 and rD1 (10mM), 5 units of Taq DNA polymerase, 5μL of 10×PCR buffer and ddH2O up to 50μL. The thermocycling conditions were as follows: an initial denaturation step at 94°C for 1min, followed by 35 cycles of 56°C for 1min, 72°C for 2min and a final extension at 72°C for 10min using a Personal Biometra Thermal Cycler DNA engine tetrad (Gottingen, Germany). The resulting PCR products were subjected to electrophoresis through a 1.0% (w/v) agarose gel, which was stained with ethidium bromide and visualized under UV light. An approximately 1500bp PCR product was purified with an Omega Bio-Tek E.Z.N.A Gel Extraction Kit, and the purified DNA was cloned into plasmid vector pMD-18 T (Takara, DaLian, China). The clones were checked with PCR to be sure they contained the correct insert size. Sequencing was then performed using M13 universal primers on an ABI® 3730 automated DNA sequencer.16
Names and sequences of primers used in this study.
| Primer | Sequence (5′–3′)a | Fragment length (bp) | References |
|---|---|---|---|
| fD1 rD1 | AGAGTT TGATCCTGGCTCAG AAGGAGGTGATCCAGCC | 1519 | Winker and Woese (1991)40 |
| CAT2-3f CAT2-3r | TGATCGAGATGGACCGTGACG TCAGGTCAGCACGGTCATGAA | 821 | Alquati et al. (2005)41 |
| Cat1-2f Cat1-2r | AAACCCGCGCTTCAAGCAGAT AAGTGGATCTGCGTGGTCAGG | 650 | Marta et al. (2006)27 |
| PRO3-4f PRO3-4r | CTAYAARACCWSCGTSSYGCGC GATCAYCGGRTCGCCYTSG | 490 | This study |
The sequences were edited to remove vector contaminants and primer sequences. To identify the sequences, the cloned sequences were compared with the 16S rRNA gene sequences of existing bacteria in the NCBI database. Related sequences were obtained from the GenBank Nucleotide database using the BLAST search program. All the sequences were edited to a common length and aligned using the ClustalW program. A phylogenetic tree was constructed by neighbor joining method. To test the stability of the groups, a bootstrap analysis of 10,000 replications was performed with a MEGA version 4.1 program.17,18
Amplification of dioxygenase genesThe templates for PCR amplification were the genomic DNA that was isolated from the gram-negative bacteria that were used previously for 16S rRNA gene amplification. The catechol 2,3-dioxygenase gene and catechol 1,2-dioxygenase gene were amplified with CAT2-3f/CAT2-3r primers and Cat1-2f/Cat1-2r primers, respectively (Table 1). The degenerate PCR primers PRO3-4f and PRO3-4r were used to amplify a 490-bp fragment of the protocatechuate 3,4-dioxygenase gene (Table 1). Primer pairs PRO3-4f and PRO3-4r are based on the coding sequence for the beta subunits of protocatechuate 3,4-dioxygenase found in P. aeruginosa (X60740), Pseudomonas putida (D37783) and Ralstonia pickettii (CP001068). These strains were used as positive controls to determine whether one or more of the dioxygenase genes are present in the 29 isolates used in this study. Each PCR mixture with a final volume of 25μL contained 0.2mM dNTP, 20pmols of each primer, 1μL of extracted DNA and 2 units of Taq DNA polymerase with 1× Taq polymerase buffer. The PCR touchdown thermocycling conditions were as follows: an initial denaturation at 94°C for 3min, followed by 35 cycles with 94°C for 30s, annealing temperature step-downs of 0.3°C (from 60.2°C to 50°C) for 1min, and 72°C for 2min, with a final extension of 7min at 72°C. Product formation was confirmed by 1% (w/v) agarose gel electrophoresis, followed by ethidium bromide staining and visualization under UV light. The dioxygenase genes were cloned, sequenced and analyzed as described in sections “16S rRNA gene isolation and sequencing” and “Sequence analysis”.
Degradation of phenolPhenol degradation experiments were performed in liquid MM medium containing 500mg/L phenol in triplicate flasks. A culture was grown (50mL) in LB liquid medium overnight at 30°C with shaking at 200rpm, and it was harvested and rinsed twice with 50mM phosphate buffer. For each single culture experiment involving only one bacterial species per flask, a freshly prepared 2% (v/v) inoculum of Pseudomonas sp. PH11, Pseudomonas sp. PH7, or Ralstonia sp. PH19 was used. For the mixed culture experiments, which involved a combination of all three bacteria per flask, 0.67% (v/v) inoculums of Pseudomonas sp. PH11, Pseudomonas sp. PH7 and Ralstonia sp. PH19) were used. The flasks were then incubated at 30°C with shaking at 200rpm. Samples were taken at 6h intervals and analyzed for phenol content. The abiotic controls consisted of preparations that were incubated under the same conditions using autoclave-killed bacteria. To determine the quantity of phenol present in the liquid medium, the colorimetric assay developed by Martin was performed.19 Phenol reacts with 4-aminoantipyrin and forms a red indophenol dye under alkaline conditions. The absorbance of this dye was measured at 460nm in a Beckman Coulter DU800 UV/Vis Spectrophotometer. The phenol concentration was determined by comparing the absorbance value with that of a standard curve for phenol (0–500mgL−1). All the tests in this study were performed over three independent experiments.
Nucleotide sequence accession numbersThe nucleotide sequences obtained in this study were deposited in the GenBank Nucleotide database. The accession numbers of the 16S rRNA genes from strains PH1 to PH29 are JN171666 to JN171694, respectively. The accession numbers of the catechol 1,2-dioxygenase gene from Pseudomonas sp. PH11, the catechol 2,3-dioxygenase gene from Pseudomonas sp. PH7, and the protocatechuate 3,4-dioxygenase gene from Ralstonia sp. PH19 are JN171696, JN171695 and JN171697, respectively.
ResultsIsolation of phenol-degrading gram-negative bacteriaThe twenty-nine gram-negative isolates that were used as part of this study all formed isolated colonies when plated on solid MM media. Each isolate was identified on the basis of their morphology and 16S rDNA gene sequence analysis. The isolated strains included 8 (27.5%) Pseudomonas spp., 6 (20.5%) Acinetobacter spp., 6 (20.5%) Alcaligenes spp., 2 Ralstonia (7%) spp., 2 (7%) Bordetella spp., 1 (3.5%) Burkholderia sp., 1 (3.5%) Azospirillum sp., 1 (3.5%) Plesiomonas sp., 1 (3.5%) Sphingomonas sp., and 1 (3.5%) Achromobacter sp.
Taxonomic identification of the isolatesOn the basis of the consensus sequences for the 16S rRNA gene, a phylogenetic tree was constructed using sequences from the 29 strain isolates and representative gram-negative bacteria (Fig. 1). The phylogenetic analysis showed that the 29 aromatic compound-degrading bacteria shared high 16S rDNA gene sequence similarities with one another and belonged to two clusters. Members of the genera Azospirillum and Sphingomonas were supported by a >99% bootstrap value and were well-established within Cluster 2. Members of Cluster 1 possessed much broader specificity and could be divided into two diverse sub-clusters. The Acinetobacter, Plesiomonas, and Pseudomonas genera showed closer relations, supporting a >95% bootstrap value to confirm their positions within Subcluster 1. A close relation between the Ralstonia, Bordetella, Achromobacter, and Alcaligenes genera were supported by a high bootstrap value, and these strains were well-established within Subcluster 2.
Phylogenetic tree of the 29 gram-negative strains isolated in this study and related species. The dendrogram was based on an approximately 800bp segment of the 16S rRNA gene sequence and was constructed by neighbor-joining method. The sequences generated from this study are highlighted in bold text and are compared with other related species. The scale bar indicates a 2% sequence divergence. Bootstrap probabilities are shown near the nodes, and GenBank accession numbers are given in parentheses.
The ability of the gram-negative bacteria to grow on a variety of different carbon sources was tested in liquid media containing one of 11 monoaromatic compounds as the sole carbon source. Among the 29 isolated species, Pseudomonas spp., Acinetobacter spp., Alcaligenes spp., Ralstonia spp., Bordetella sp. PH21 and Achromobacter sp. PH23 were able to utilize at least six of the monoaromatic compounds tested (Table 2). Pseudomonas spp., Acinetobacter spp., Alcaligenes spp., and Ralstonia spp. showed much greater metabolic versatility than the other strains. All the isolates grew well on phenol, m-dihydroxybenzene and 2-hydroxybenzoic acid. These compounds are considered intermediates, which are produced by aromatic substrate degradation via the salicylate pathway.20 O-aminobenzoic acid was also a good growth substrate for 28 isolates. The only exception was Sphingomonas sp. PH20. The Pseudomonas sp. PH7 and PH9 strains were able to utilize all the tested compounds. Seven other isolates, namely Acinetobacter sp. PH3, Acinetobacter sp. PH4, Pseudomonas sp. PH10, Pseudomonas sp. PH11, Pseudomonas sp. PH14, Alcaligenes sp. PH24 and Alcaligenes sp. PH28, were able to utilize 10 different monoaromatic compounds.
Growth on monoaromatic compounds by gram-negative bacterial strains.a
| Organism | Monoaromatic compoundsb | |||||||||
|---|---|---|---|---|---|---|---|---|---|---|
| 1 | 2 | 3 | 4 | 5 | 6 | 7 | 8 | 9 | 10 | |
| Acinetobacter sp. PH1 | + | + | + | + | + | + | − | + | + | − |
| Acinetobacter sp. PH2 | + | + | + | − | + | + | + | + | − | − |
| Acinetobacter sp. PH3 | + | + | + | + | + | + | − | + | + | + |
| Acinetobacter sp. PH4 | + | + | + | + | + | + | − | + | + | + |
| Acinetobacter sp. PH5 | + | + | − | − | − | + | − | + | + | − |
| Acinetobacter sp. PH6 | + | + | − | − | + | + | + | + | + | − |
| Pseudomonas sp. PH7 | + | + | + | + | + | + | + | + | + | + |
| Pseudomonas sp. PH8 | + | + | + | + | − | + | − | + | + | − |
| Pseudomonas sp. PH9 | + | + | + | + | + | + | + | + | + | + |
| Pseudomonas sp. PH10 | + | + | + | + | + | + | − | + | + | + |
| Pseudomonas sp. PH11 | + | + | + | + | + | + | + | + | + | − |
| Pseudomonas sp. PH12 | + | + | + | + | + | + | − | + | + | − |
| Pseudomonas sp. PH13 | + | + | + | + | − | + | − | + | + | − |
| Pseudomonas sp. PH14 | + | + | + | + | + | + | − | + | + | + |
| Burkholderia sp. PH15 | + | + | − | − | + | + | − | + | − | − |
| Azospirillum sp. PH16 | + | − | − | − | − | + | − | + | − | − |
| Plesiomonas sp. PH17 | + | + | − | − | − | + | − | + | − | − |
| Ralstonia sp. PH18 | + | + | + | + | + | + | − | + | + | − |
| Ralstonia sp. PH19 | + | + | + | − | + | + | − | + | − | − |
| Sphingomonas sp. PH20 | + | − | − | + | − | + | − | − | − | − |
| Bordetella sp. PH21 | + | + | − | − | + | + | − | + | + | − |
| Bordetella sp. PH22 | + | − | − | − | + | + | − | + | − | − |
| Achromobacter sp. PH23 | + | + | − | − | + | + | − | + | − | − |
| Alcaligenes sp. PH24 | + | + | + | + | + | + | + | + | − | + |
| Alcaligenes sp. PH25 | + | + | − | − | + | + | − | + | + | − |
| Alcaligenes sp. PH26 | + | + | − | + | + | + | − | + | − | − |
| Alcaligenes sp. PH27 | + | + | − | − | + | + | + | + | − | − |
| Alcaligenes sp. PH28 | + | + | + | + | + | + | + | + | − | + |
| Alcaligenes sp. PH29 | + | + | − | − | + | + | − | + | − | − |
To determine whether catechol 1,2-dioxygenase was present, PCR amplifications were performed using Cat1-2f and Cat1-2r primers, which are specific for the pheB gene of P. putida. The expected 650bp fragment was amplified from genomic DNA that was isolated from all the gram-negative bacteria except for Burkholderia sp. PH15, Pseudomonas sp. PH8 and Pseudomonas sp. PH13 (Table 3). To determine whether the catechol 2,3-dioxygenase gene was present, the CAT2-3f and CAT2-3r primers were used, and they were specific for the xylE gene of P. aeruginosa. The expected 821bp fragment was amplified from genomic DNA that was isolated from only Pseudomonas sp. PH9 and Pseudomonas sp. PH7 (Table 3). No PCR product was generated with the other 27 isolates. To determine whether the protocatechuate 3,4-dioxygenase gene was present, the degenerate primers PRO3-4f and PRO3-4r were used. The expected 490bp fragment from the protocatechuate 3,4-dioxygenase gene was amplified from genomic DNA that was isolated from Acinetobacter sp. PH1, 3–4, and 6; Pseudomonas sp. PH8, 10, and 12–14; Burkholderia sp. PH15; Azospirillum sp. PH16; Ralstonia sp. PH18 and 19; Bordetella sp. PH21; and Alcaligenes sp. PH 24 and 28 (Table 3). No PCR product was generated from the other 13 strains.
PCR amplification of the dioxygenase genes from gram-negative bacterial strains.a
| Organism | Catechol 1,2-dioxygenase gene | Catechol 2,3-dioxygenase gene | Protocatechuate 3,4-dioxygenase gene | Genotypeb |
|---|---|---|---|---|
| PH1 | Positive | Negative | Positive | PNP |
| PH2 | Positive | Negative | Negative | PNN |
| PH3 | Positive | Negative | Positive | PNP |
| PH4 | Positive | Negative | Positive | PNP |
| PH5 | Positive | Negative | Negative | PNN |
| PH6 | Positive | Negative | Positive | PNP |
| PH7 | Positive | Positive | Negative | PPN |
| PH8 | Negative | Negative | Positive | NNP |
| PH9 | Positive | Positive | Negative | PPN |
| PH10 | Positive | Negative | Positive | PNP |
| PH11 | Positive | Negative | Negative | PNN |
| PH12 | Positive | Negative | Positive | PNP |
| PH13 | Negative | Negative | Positive | NNP |
| PH14 | Positive | Negative | Positive | PNP |
| PH15 | Negative | Negative | Positive | NNP |
| PH16 | Positive | Negative | Positive | PNP |
| PH17 | Positive | Negative | Negative | PNN |
| PH18 | Positive | Negative | Positive | PNP |
| PH19 | Positive | Negative | Positive | PNP |
| PH20 | Positive | Negative | Negative | PNN |
| PH21 | Positive | Negative | Positive | PNP |
| PH22 | Positive | Negative | Negative | PNN |
| PH23 | Positive | Negative | Negative | PNN |
| PH24 | Positive | Negative | Positive | PNP |
| PH25 | Positive | Negative | Negative | PNN |
| PH26 | Positive | Negative | Negative | PNN |
| PH27 | Positive | Negative | Negative | PNN |
| PH28 | Positive | Negative | Positive | PNP |
| PH29 | Positive | Negative | Negative | PNN |
To verify the presence of the catabolic genes catechol 1,2-dioxygenase, catechol 2,3-dioxygenase, and protocatechuate 3,4-dioxygenase, PCR-amplified fragments of these genes were sequenced from three different bacteria, namely Pseudomonas sp. PH11, Pseudomonas sp. PH7, and Ralstonia sp. PH19. These strains are capable of degrading multiple monoaromatic compounds (Table 2), and so they were chosen for further studies. The partial nucleotide sequence of the catechol 1,2-dioxygenase gene from Pseudomonas sp. PH11 was 99, 96 and 94% similar to the same gene found in P. putida KT24400, P. arvilla and Stenotrophomonas maltophilia KB2, respectively (Table 4). The partial nucleotide sequence of the catechol 2,3-dioxygenase gene from Pseudomonas sp. PH7 was 99, 99 and 92% similar to the xylEJI104-1 gene present in P. aeruginosa JI104, the nahH gene present in P. stutzeri CLN100, and the catechol 2,3-dioxygenase gene present in Achromobacter xylosoxidans LHB21, respectively (Table 4). The partial nucleotide sequence of the protocatechuate 3,4-dioxygenase gene for Ralstonia sp. PH19 was 95 and 87% similar to the protocatechuate 3,4-dioxygenase gene found in R. pickettii 12J and the pcaH gene found in R. solanacearum strain IPO1609 (Table 4).
Sequence homologies of the dioxygenase genes for phenol-degrading bacteria.
| Organism | Dioxygenase gene (accession number) | Homology | Homologous gene (accession number) | Source |
|---|---|---|---|---|
| Pseudomonas sp. PH11 | Catechol 1,2-dioxygenase gene (JN171696) | 99% | Catechol 1,2-dioxygenase gene (AE015451) | P. putida |
| 96% | Catechol 1,2-dioxygenase (D37783) | P. arvilla | ||
| 94% | Catechol 1,2-dioxygenase gene (EU00039) | Stenotrophomonas maltophilia | ||
| Pseudomonas sp. PH7 | Catechol 2,3-dioxygenase gene (JN171695) | 99% | xylEJI104-1 gene (X60740) | P. aeruginosa |
| 99% | nahH gene (AJ539383) | P. stutzeri | ||
| 92% | Catechol 2,3-dioxygenase gene (GU199432) | Achromobacter xylosoxidans | ||
| Ralstonia sp. PH19 | Protocatechuate 3,4-dioxygenase gene (JN171697) | 95% | pcaH gene (CP001068) | R. pickettii |
| 87% | pcaH gene (CU914168) | R. solanacearum | ||
Pseudomonas sp. PH11, Pseudomonas sp. PH7, Pseudomonas sp. PH10, and Pseudomonas sp. PH8 represent the four different dioxygenase genotypes and can grow well in several monoaromatic compounds. To assess the importance of dioxygenase genes in phenol degradation, these strains were selected to study their abilities to degrade phenol. The degradation of phenol by pure and mixed cultures was studied at a phenol concentration of 500mgL−1 (Fig. 2). A mixed culture of all four bacteria representing 4 different dioxygenase genotypes degraded 15.8% of the initial phenol after 12h of incubation. Within the next 24h, 78.5% of the added phenol was degraded, and after 42h, more than 99.5% of the phenol was degraded. The ability of the mixed culture to degrade phenol (in 42h and 48h) is of interest because the degradation was statistically significantly (p<0.001) more quickly than in the other three pure cultures. Within 48h, Pseudomonas sp. PH7 had a statistically significantly (p<0.001) higher phenol degradation level (99.7%) than those of Pseudomonas sp. PH11 (93.4%), Pseudomonas sp. PH8 (86.3%) and Pseudomonas sp. PH10 (92.1%). During the initial 12h lag phase, Pseudomonas sp. PH7 and Pseudomonas sp. PH11 had relatively higher phenol degradation levels. These levels reached 20.6 and 17.9%, respectively, in comparison with the mixed culture, in which only 15.8% was degraded.
Degradation curve of phenol using pure and mixed cultures. Phenol (500mgL−1) was added to the MM medium, inoculated with 2% (v/v) cultures and incubated at 30°C and 200rpm. Statistical analyses were performed with Student's t test in SPSS 17.0 software (SPSS Inc, Chicago, IL, USA), and the error bars represent the means (±SD) of three independent experiments. * The phenol degradation rate of the mixed culture is significantly higher than the rates for strains PH7, PH8, PH11, and PH10 (p<0.001). ** The phenol degradation rate of strain PH7 is significantly higher in comparison with strains PH8, PH11, and PH10 (p<0.001).
Different methods have been used for the elimination of phenol and phenolic compounds, but the use of biodegradation methods is universally preferred because of their lower costs and the possibility of complete mineralization.2 Bacteria that have the ability to use phenol can be used for biodegradation within environments that are contaminated with phenolic compounds. In this study, we describe the isolation and screening of 29 selected phenolic compound-degrading bacterial isolates and the characterization of the dioxygenase genes from three strains by PCR amplification. These strains mostly belong to Pseudomonas, Acinetobacter and Alcaligenes. PCR assays revealed that the three genes were not equally distributed in the isolated strains, and the catechol 2,3-dioxygenase gene was found in only Pseudomonas sp. PH7 and PH9. The mixed culture involved three dioxygenase genes, and it exhibited rapid phenol degradation.
The phylogenetic analysis showed that the 29 phenolic compound-degrading bacteria shared high 16S rDNA gene sequence similarities with one another and belonged to two clusters. Members of Cluster 1 possessed much broader specificity, and they could use anywhere from 5 to 11 substrates with 4 substrates that are consistently conserved throughout these strains (Table 2). Approximately 70% of these strains were members of three genera: Pseudomonas (8 strains, 27.5%), Acinetobacter (6 strains, 20.5%), and Alcaligenes (6 strains, 20.5%). Among the phenol-degrading gram-negative bacteria, Pseudomonas, Acinetobacter and Alcaligenes are regarded as the most common species to be isolated from contaminated sites. The abilities of these species to utilize phenolic compounds in particular have been widely documented.21–23 Cluster 2 has only two members. Interestingly, this small group can utilize at least four substrates (Table 2). The results indicate that bacteria that are capable of degrading aromatic compounds are phylogenetically diverse.
In this study, more than ten carbon sources were tested as sole carbon substrates for the 29 isolates, including various monoaromatic compounds. All the strains could utilize 2-hydroxybenzoic acid, which is considered an intermediate product of aromatic substrate degradation via the salicylate route pathway.20 In comparison with the other 7 genera, the strains that were members of the Pseudomonas, Acinetobacter and Alcaligenes genera were able to grow on many more carbon sources (Table 2). Because of their abilities to use a wide diversity of carbon energy substrates, they can compete effectively with other bacteria and become dominant culturable members that are capable of utilizing the phenolic compounds found in contaminated sludge.24
PCR analysis was performed to detect dioxygenase genes encoding catechol 2,3-dioxygenase, catechol 1,2-dioxygenase, and protocatechuate 3,4-dioxygenase, which oxidize catechol or protocatechuate via the α-ketoacid and the β-ketoadipate pathways. The identity of the PCR-amplified fragments was further verified through a sequence analysis of selected strains. The three dioxygenase genes were amplified, which means that both the α-ketoacid and β-ketoadipate pathways serve as general mechanisms for the catabolism of catechol or protocatechuate derived from phenolic compounds.25 However, the three genes are not equally distributed in the isolated strains. The catechol 2,3-dioxygenase gene is found in only two Pseudomonas strains, PH7 and PH9, but the catechol 1,2-dioxygenase gene is found in all the gram-negative bacteria except for Burkholderia sp. PH15 and Pseudomonas sp. PH8 and PH13. The majority of studies on the detection of catabolic genes in contaminated environments have focused on gram-negative bacteria, such as Pseudomonas, Burkholderia, Acinetobacter and Sphingomonas.26 These strains usually carry one or two dioxygenase genes,27 but catechol 2,3-dioxygenases constitute a group of enzymes that are considered crucial for the degradation of a wide range of aromatic compounds in contaminated habitats, and they are present in most aromatic compound-degrading strains.28,29 Because these dioxygenase genes are commonly distributed between plasmids of different sizes and are found on the chromosome,30 a suggestion has been made that these genes may spread to divergent bacteria by horizontal transfer.31 The detection of these genes within the strains isolated from sludge that was contaminated with phenolic compounds provides evidence that these genes may have differentiated during the evolution of different gram-negative bacterial communities.32
An analysis of Table 3 also shows that there are 4 genotypes. Most strains are either PNP or PNN, only three strains are NNP and two strains are PPN. In using a step-wise model of gene acquisition and loss, it is easy to order these genotypes in a parsimonious order (NNP-PNP-PNN-PPN), with the most common genotypes being central. Of the genotypes that were not found (NNN, NPN, NPP, and PPP), only PPP and NNN can be formed from these central genotypes. Clearly, NNN may not be able to degrade phenol and was thus never enriched. PPP may be ‘too costly’ to maintain, but there was an exception (S. maltophilia KB2) that carries the three dioxygenase genes.33 NPN and NPP may be feasible, but because of the prevalence of these genes in this environment, they may occur rarely and by chance and may not related to fitness. Alternatively, catechol 1,2-dioxygenase is under strong selection, with protocatechuate 3,4-dioxygenase under medium selection and catechol 2,3-dioxygenase under weak selection. The frequencies of these genotypes reflect the stable phenotypes that could exist. This finding could be linked to the results presented in Table 2. Strains with two dioxygenase genes can grow on many more aromatic compounds than strains with one dioxygenase gene, except strain PH11. However, Azospirillum strain PH16, which also carries two dioxygenase genes, utilizes only 4 aromatic compounds because of phylogenetic diversity as mentioned above. It is possible that the presence of a second dioxygenase gene reflects differences in the substrate degradation by the cells, as previously noted.34 It is not clear whether these genes are plasmid and/or chromosomally mediated. Further experimentation is required.
To decrease the phylogenetic differences in terms of degradation activity, four Pseudomonas strains (PH11, PH7, PH10 and PH8) that carry different dioxygenase genes and represent the four genotypes of PNN, PPN, PNP and NNP were chosen for phenol biodegradation analysis. The experimental data indicated that the ternary mixed culture (involving three genes) and Pseudomonas sp. PH7 (involving two genes) had fairly high phenol degradation potential. When cells are introduced into a toxic environment, there are a number of different response mechanisms that could have an effect on the degradation and growth properties, and the accumulation of intermediates and/or dead-end products can inhibit enzyme activity. For example, cis-muconate and adipic acid can inhibit catechol 1,2-dioxygenase activity,35,36 and 2-oxopent-4-dienoate can inhibit catechol 2,3-dioxygenase activity.37 The bacteria in the mixed culture and Pseudomonas sp. PH7 carry a total of three and two dioxygenase genes, respectively. The bacteria can degrade phenol via multiple pathways. As a result, a low level of feedback repression in the intermediate products is maintained.38Pseudomonas sp. PH10 also consists of two parallel branches. One branch starts at catechol and the other branch begins at protocatechuic acid. Catechol is cleaved by catechol 1,2-dioxygenase and protocatechuic acid is cleaved by protocatechuate 3,4-dioxygenase. The two branches converge at the same intermediate, or β-ketoadipate enol-lactone, which acts as feedback inhibitor of dioxygenase activity.13,39,11
Conflicts of interestThe authors declare no conflicts of interest.
This work was supported by the Natural Science Foundation of Hubei Province (2014CFB914), and the Fundamental Research Funds for the Central Universities, South-Central University for Nationalities (CZW14001 and CZW15023).