FOUR BACILLUS SP . SOIL ISOLATES CAPABLE OF DEGRADING PHENOL , TOLUENE , BIPHENYL , NAPHTHALENE AND OTHER AROMATIC COMPOUNDS EXHIBIT DIFFERENT AROMATIC CATABOLIC POTENTIALS

Two novel Bacillus sp. were isolated from a soil sample from a bank of the Tamiš river in close proximity to a petrochemical facility. They were capable of utilizing a broad range of aromatic compounds as a sole source of carbon and energy (including phenol, benzene, toluene, biphenyl, naphthalene). The isolates were designated as Bacillus sp. TN41 and TN42, based on their 16S rDNA sequence. Their catabolic potential was compared to two Bacillus sp. strains (PS1 and PS11) isolated from the rhizosphere of the endemorelict plant Ramonda serbica. Specific activities of phenol hydroxylase, catechol 1,2-dioxygenase and catechol 2,3-dioxygenase were analyzed from crude cell extracts of the isolates, as well as the temperature and pH effects on enzyme activity. Although all four isolates had the ability to degrade a similar range of aromatic compounds, the specific activities of the enzymes indicative of aromatic compound catabolism of TN isolates were 2 to 90-fold lower compared to the PS isolates. Phenol hydroxylase and catechol dioxygenases exhibited broad temperature (10°C-80°C) and pH (4-9) activity ranges in all four Bacillus isolates. While phenol inhibited both phenol hydroxylase and catechol dioxygenases in the TN strains, it was an inducer for phenol hydroxylase in the PS strains.


INTRODUCTION
Soils and groundwater are preferred sinks for complex contamination.As a result, different chemical, biological, and biochemical properties of soil can be profoundly altered.Their main effect is the continuous loss of soil functions in sustaining the survival of living organisms.Phenol, toluene, benzene and polyaromatic hydrocarbons (PAHs; i.e., naphthalene, phenanthrene, anthracene, etc.) are ubiquitous in the environment as complex mixtures and have been recognized as an environmental contamination problem of worldwide magnitude (Andreoni and Gianfreda, 2007).Aromatic pollutants emerge as a result of human activities, but they occur naturally as well.Oil refineries and phenolic resin industries are major producers of phenolics.On the other hand, organic matter decomposition products contain phenol.Furthermore, higher plants under stress conditions synthesize phenolics as reactive oxygen species scavengers and release them into the soil.The majority of these substances are highly persistent in ecosystems in unaltered, less degradable chemical forms because of their low water solubility, their intrinsic chemical stability, and high recalcitrance to degradation (Andreoni and Gianfreda, 2007).Therefore, hydrocarbonpolluted sites can represent a long-term source of pollution and pose a severe risk to environmental health.
Removal of aromatic hydrocarbons from the environment employs different methods, such as physical, chemical and biological techniques (bioremediation).The bioremediation approach appears to be the most efficient with regard to commercial and environmental aspects (Andreoni and Gianfreda, 2007;Schie and Young, 2000).
The first step in the aerobic biodegradation of phenol includes its oxygenation by phenol hydroxylase (PH) to form catechol which undergoes ring fission that can take place between the two hydroxyl groups, involving the action of catechol 1,2-dioxygenase (C12O), or proximal to one of the two hydroxyl groups involving the action of catechol 2,3-dioxygenase (C23O).Most other aromatic compounds are first converted to substituted catechols and than degraded by C12O or C23O (Andreoni and Gianfreda, 2007).
The aim of this work was to isolate phenol-degrading microorganisms, preferably Gram positive Bacillus (as most of the known aromatic degraders are Gram negative Pseudomonads and closely related species), from soil collected in close proximity to a petrochemical industry (contaminated with various aromatics).We report on the isolation, characterization and identification of two novel Bacillus strains.In addition, we compared their aromatic degradation ability to two Bacillus strains isolated previously from rhizosphere soil with a naturally elevated concentration of phenolics (Djokic et al. 2011).We also examined the activity of the key enzymes involved in phenol and other aromatic compound degradation.

Reagents
Phenol, benzene, toluene, styrene and other aromatic compounds used as a sole carbon source, as well as antibiotics and other salts, were of analytical grade and purchased from Sigma-Aldrich (St Louis, MO, USA).Pfu DNA polymerase, T4 DNA ligase, O`Gene 100 bp DNA Ladder and pUC19 plasmid were purchased from Fermentas (Burlington, Can-ada).Tryptic soy broth, soluble starch, casein, and other media components were purchased from Becton Dickinson (Sparks, MD, USA).Oligonucleotide primers were obtained from Invitrogen (Darmstadt, Germany).The QIAprep spin plasmid mini-prep kit, QIAEX II gel purification kit, and QIAquick PCR purification kit were purchased from QIAGEN (Hilden, Germany).

Isolation of bacteria from soil
Soil samples were collected from the rhizosphere of Ramonda serbica and from river banks in close proximity to the petrochemical facility.Isolation of bacteria from the rhizosphere of R. serbica was previously described (Djokic et al., 2011).Similarly, bacteria were isolated from river bank soil by drying and then sieving the soil under aseptic conditions to a particle size of approximately 2-4 mm.Sterile potassium phosphate buffer (9 ml; 50 mM, pH 7.2) was added to the soil sample (1 g) and the suspension was vigorously mixed by vortexing for 5 min to homogenize the sample.Serial dilutions were performed to obtain a 10 -5 dilution of the original soil sample.The serial dilutions were spread-plated on starch casein agar (SCA) containing soluble starch (10 g l -1 ), casein (1 g l -1 ), KH 2 PO 4 (0.5 g l -1 ), MgSO 4 (0.5 g l -1 ) and NaCl (3 g l -1 ) and supplemented with antifungal cycloheximide (50 µg l -1 ) and phenol (2 g l -1 ).Plates were incubated at 30ºC for 7 days.CSA is known to promote the growth of actinomycetes (Hopwood, 1985).Various isolates were selected by visual differentiation of contrasting colony morphology.These bacteria, referred to as phenol-tolerant bacteria, were transferred to a mineral salts medium (MSM) containing Na 2 HPO 4 .12H 2 O (9 g l -1 ), KH 2 PO 4 (1.5 g l -1 ), MgSO 4 .7H 2 O (0.2 g l -1 ), CaCl 2 (0.002 g l -1 ), trace element solution (1 ml l -1 ) (Schlegel et al., 1961) and phenol (400 mg l -1 ) as a sole source of carbon and energy.When necessary, the medium was solidified by adding 1.5% (w/v) bacteriological agar Becton Dickinson (Sparks, MD, USA).
To monitor phenol degradation ability, MSM liquid cultures (50 ml in 250 ml conical flasks, 1% inoculum) were grown with shaking at 200 rpm in an incubator at 30 o C for 7 days, supplemented with initial phenol concentrations ranging from 200-2000 mg l -1 in 200 increments.After the incubation period, to determine the biomass yield as cell dry weight, aliquots of the cultures (2 ml) were centrifuged at 5000 × g for 10 min at 4 0 C (Eppendorf 5804 R bench top centrifuge) and the cell pellets were washed in potassium phosphate buffer (50 mM, pH 7.2) two times prior to application of the cells to the glass fiber membranes (Whatman).Cell suspensions were filtered through previously weighed membranes which were then dried at 90°C until a constant weight was achieved.
To test the ability of the isolates to use other aromatic compounds as a sole source of carbon and energy, the strains were spread onto MSM plates and the carbon source was supplemented via a vapor phase by adding in a sterile Eppendorf plastic tip (50 µl) and placing the tip in the lid of the Petri dish.In the case of naphthalene and biphenyl, a couple of crystals (approximately 5 mg) were similarly placed on the lid of the Petri dish.After 2-4 days of incubation at 30°C the plates were screened for the presence of colonies.Growth was confirmed by comparison with control plates without substrate and 20 mM glucose as a carbon source.

Identification of bacteria
Bacterial DNA was extracted by a method described previously (Nikodinovic et al., 2003).The extracted DNA was subjected to PCR amplification with the 16S rDNA bacteria-specific primers: 27f (Lane, 1991) and 1392r (Marchesi et al., 1998).PCR amplification was performed as described by Marchesi et al. (1998).PCR products were cloned in pUC19 vector and three independently isolated recombinant plasmids for each strain were sequenced on an Applied Biosystems 3130 Genetic Analyzer (Foster City, USA) using M13f/M13r primers (Yanisch-Perron et al. 1985).Homologues were identified by the BLASTN algorithm (Altschul et al., 1997).
The BLASTN program (Altschul et al., 1997) was used to search for similar sequences in the GeneBank database services provided by the NCBI and the Seqmatch tool was used to search for similar sequences compiled by the Ribosomal Database Project-II Release 9.4 (RDP; http://rdp.cme.msu.edu;(Cole et al. 2009)).

Preparation of crude cell extracts
Bacteria were grown in 200 ml of tryptone soy broth (TSB; 30 g l -1 ) at 30°C, shaking (200 rpm).After four days the cells were harvested by centrifugation at 6,000 × g (15 min, +4°C, GSA rotor, Sorvall, USA).For the induction experiments, two hours prior to harvesting phenol was added directly to the medium at a 0.1 mM final concentration.The cell pellet was washed with 50 mM potassium phosphate buffer (20 ml; pH 7.2), followed by centrifugation under the same conditions.The cell pellet was resuspended in lysis buffer (20 ml; 50 mM potassium phosphate buffer, pH 7.2, containing 1 mg ml -1 lysozyme).The suspension was incubated on ice for 30 min.The crude cell extracts were obtained after sonication (6 bursts of 10 s at 15 Hz; Soniprep 150 MSE; Beckenham, UK) and centrifugation at 12000 × g (Eppendorf 5804R bench top centrifuge) for 15 min at 4°C and used for enzymatic tests.Total protein concentration was determined by the method of Bradford using bovine serum albuminum ((Sigma-Aldrich, St Louis, MO, USA) as standard (Bradford 1976).

Enzyme activity analysis
Enzyme assays for the activity of phenol hydroxylase, catechol 1,2-dioxygenase and catechol 2,3-dioxygenase were carried out as previously described.For phenol hydroxylase, the oxidation of 1 mM NADH by the cell extract in the presence of 100 nM phenol was monitored at 340 nm (Neujahr and Gaal 1975).To assay the activity of, catechol 1,2-and 2,3-dioxygenase, 1 mM catechol wasere added to the crude cell extract.For the catechol 1,2-dioxygenase formation of cis molecules, cis-muconic acid was measured at 260 nm (Ornston and Stanier 1966); for estimating catechol 2,3-dioxygenase activity, the appearance of 2-hydroxymuconic semialdehyde was measured at 375 nm (Mars et al., 1997).Assays were carried out in 50 mM phosphate buffer, pH 7.2 at 30°C.A unit of the enzyme was defined as the amount of enzyme catalyzing 1 mmol of substrate per 1 min.Results are shown as enzyme activity per mg of total protein in the crude cell extract.
The effect of pH and temperature on enzyme activity was determined by carrying out reactions in 50 mM sodium acetate (pH 2, 3, 4 and 5), 50 mM phosphate (pH 6 and pH 7), 50 mM Tris-HCl (pH 8 and pH 9) and 50 mM carbonate/bicarbonate buffer (pH 10 and pH 11) at 30°C.The optimum temperature was determined by assaying the enzyme activity at different temperatures, from 10°C to 80°C in 50mM phosphate buffer.

PCR-based screening for phenol hydroxylase core regions
Core regions of phenol hydroxylase were amplified using the previously described primers Pheh-3F/Pheh-3R et al., 2009).A 870 bp fragment was amplified under the following conditions: 1) 10 min at 95°C; 2) 30 1 min cycles at 95°C, 1 min at 60.5°C and 1 min at 72°C; 3) a final 5 min extension at 72°C and gDNA of isolates as a template.In the study, gDNA of the strain Bacillus cereus ATCC 14579 was also included as a negative control.

Nucleotide sequence accession numbers
The sequences for 16S rRNA genes were deposited in GenBank under accession numbers EU721601, EU721602, JN118576 and JN118577 for PS11, PS1, TN41 and TN42, respectively.

Isolation and characterization of phenol-degrading bacteria
Aromatic hydrocarbon-degrading microorganisms have been isolated from various environments, mostly polluted sites, however, they are widespread in marine, freshwater and soil habitats (Phale et al., 2007).Plant rhizospheres have proven to be a rich source of these bacteria, as higher plants usually extrude phenolics into the soil providing a suitable niche for the enrichment of phenol degraders (Toyama et al., 2009).Ramonda serbica is a relict plant of the ancient Tertiary flora and an endemic species of Serbia capable of surviving very long dry periods in the state of anabiosis (Quartacci et al., 2002).Due to their specific life cycle, the content of phenolic acids in this plant is at least three times higher than that of other higher plants (Beckman 2000;Sgherri et al., 2004).The rhizospheres of this plant have been proven to be a rich source of phenol-degrading bacteria, although the bacterial community associated with it had limited diversity (Djokic et al., 2010).
From the soil collected from the Tamiš River bank and from the rhizospheres of the endemorelict plant Ramonda serbica we isolated 58 and 13 phenoltolerant strains, respectively.Out of these isolates, strains showing substantial growth on phenol as a sole carbon source were selected for further testing.They included two strains from the river bank sample which were identified by 16S rDNA sequencing (Table 1).As isolates TN41 and TN42 were assigned to the genus Bacillus, we included two Bacillus isolates from the rhizosphere soil sample (PS1 and PS11) for the purpose of comparative study.Isolate TN41 had 99% homology with Bacillus megaterium (GenBank CP001982), while the isolate TN42 had 99% homology with B. pumilus (GenBank JF769748) which was isolated as a halotolerant bacterium from saltern sediments.Isolate PS11 had 98% homology with B. simplex isolated from rape leaves (GenBank GU086427), while isolate PS1 shared only 90% homology with the known B. cereus strain (Table 1).
The selected strains were tested for their ability to grow on a range of additional 14 aromatic substrates as the sole source of carbon and energy on a solid MSM medium (Table 2).These substrates included benzene, toluene, styrene, biphenyl, naphthalene, etc.All of the isolates were capable of degrading 7 aromatic compounds, including benzene, toluene, styrene, bromobenzene, guiacol, biphenyl and naphthalene (Table 2).Under the conditions tested (30°C, medium pH7.2), the strains isolated from the river bank (TN41 and TN42) could grow on 9 and 11 compounds, respectively, while strains PS1 and PS11 could grow on 11 and 14 compounds, respectively.Strains TN41, TN42 and PS11 could grow on the rich medium (TSB) at 43°C, while none of the strains could grow at this temperature on the minimal medium (MSM) containing phenol as the sole carbon source.Strains TN42 and PS1 and PS11 were capable of growing on a rich medium at 4ºC, while only PS1 and PS11 were also capable of growing on minimal medium with phenol as a sole carbon source at this temperature.All four strains were capable of growing in MSM liquid culture supplemented with phenol at different initial concentrations (200 to 2000 mg l -1 ).While they were all capable of growing in the presence of phenol at all concentrations, isolates exhibited growth inhibition at different concentrations.PS1 showed growth inhibition at 1,000 mg l -1 , PS11 at 1,600 mg l -1 , while for the strains TN41 and TN42 growth inhibition occurred at 400 mg l -1 (data not shown).In comparison, wastewaters containing phenol in the range of 5-500 mg l -1 are considered suitable for treatment by biological processes (Whiteley and Bailey 2000).Thus, all four Bacillus isolates have great bioremediation potential, with the PS strains showing growth inhibition on phenol at higher concentrations in comparison to the TN strains.
Apart from our recent report of two Bacillus strains that could degrade a wide range of aromatic compounds and were successfully employed in soil model system experiments (Djokic et al., 2011), only a few other Bacillus strains have been reported to degrade phenol, including B. brevis (Arutchelvan et al., 2006), B. cereus (Banerjee andGhoshal, 2010), B. stearothermophilus (Dong et al., 1992;Gurujeyalakshmi and Oriel, 1989) and B. subtilis (Tam et al., 2006).Banerjee et al. isolated two Bacillus strains from the oil refinery and exploration sites which could grow on phenol (1000 mg l -1 ) (Banerjee and Ghosal, 2010).Nevertheless, none of these strains have been evaluated for the ability to degrade a wide range of other aromatic pollutants.

Phenol hydroxylase and catechol dioxygenases activities in crude cell extracts
Having established the excellent potential of four Bacillus strains for bioremediation applications, we analyzed the catabolic pathways of these strains by assessing the enzymatic activity of the aromatic catabolic pathway in the crude cell extracts.Isolates were grown in rich TSB medium and TSB supplemented with phenol (0.1 mM) to assess the phenol hydroxylase and catechol dioxygenases activities in crude cell extracts (Table 3).
Phenol hydroxylase (EC 1.14.13.7) and catechol 1,2-dioxygenase (EC 1.13.11.1) activity was detected in all isolates, under both conditions tested, while catechol 2,3-dioxygenase (EC 1.13.11.2) activity was not detected in the PS1 strain (Table 3).In general, the TN isolates had substantially lower enzyme activities (for all three enzymes, under both conditions) in comparison to PS isolates.The difference ranged from 1.5-fold in the case of phenol hydroxylase (PS1 in comparison to TN42 in the absence of inducer), to 90-fold in the case of catechol 2,3-dioxygenase (PS11 in comparison to TN42 in the presence of inducer).
Phenol hydroxylase activity was highest for the PS11 isolate, and when the isolates were grown in rich TSB medium it was 1.5-, 6.3-and 2.3-fold higher in comparison to PS1, TN41 and TN42 isolates, respectively (Table 3).Similarly, the activity of catechol 1,2-dioxygenase was highest for PS11, being 1.7-fold higher in comparison to the PS1 isolate and 16.7 and 44.8 times higher in comparison to TN41 and TN42 isolates, respectively.The same trend remained for the catechol 2,3-dioxygenase with PS11 activity being 17-and 48.4-fold higher in comparison to the TN41 and TN42 isolates.
The previous report indicated that phenol may act as an inducer of phenol hydroxylase and catechol 1,2-dioxygenase (Djokic et al., 2011), which was confirmed in the case of PS isolates.However, the presence of 0.1 mM phenol in the medium for two hours prior to harvesting had a negative effect on the enzymatic activity of all three enzymes in the case of TN isolates (Table 3).Specific activity decreased from 1.1-fold in the case of C12O for TN42, to 6.4-fold in the case of phenol hydroxylase for the same isolate.Paller et al. found PH to be induced by its substrate (Paller et al., 1995).However, in the literature phenol hydroxylase inhibition by its substrate is more common (Neujahr and Kjellen, 1980;Viggor et al., 2008).Some other inhibitors, such as Cu 2+ and Fe 2+ ions (Saa et al., 2010) and dithiothreitol were also reported (Cadieux et al., 2002).
Isolate TN42 had 2.8 times higher specific activity in comparison to TN41 in the TSB grown cells without addition of phenol, while the activities for catechol 1,2-and 2,3-dioxygenases were 2.8 times lower for the same isolate in comparison to TN41 (Table 3).
We have determined that all the strains, TN41, TN42, PS1 and PS11, degrade phenol via an ortho pathway, by measuring the activity of catechol 1,2-dioxygenase as the formation of cis,cis-muconic acid.Additionally, by measuring the formation of 2-hydroxymuconic semialdehyde which is the product of catechol 2,3-dioxygenase activity, it was shown that strains TN41, TN42 and PS11 utilize the meta pathway of phenol catabolism as well.In only a few instances do bacteria degrade phenol via both pathways (Jiang et al., 2006).
C12O is a biotechnologically important enzyme as its product is a precursor of the industrially important compound adipic acid and represents raw material for new resins, pharmaceuticals and agrochemicals (Di Nardo et al., 2009;Yoshikawa et al., 1993).PH is also used as a biocatalyst for chemical synthesis (Kim et al., 2005), while C23O is mostly used for the biotreatment of wastewaters and in soil decontamination (Guzik et al., 2009).
The way that enzymes respond to temperature and pH is important to many areas of biotechnology.We have also examined the effects of temperature and pH on specific enzyme activity.We have determined the conditions for the maximum specific activities (Table 4).The specific activity of PH was highest for all four isolates at 70°C (Fig. 1a).This was also the case for C12O and C23O (data not shown).This may be due to the fact that many enzymes exhibit higher activity at a temperature at which they are unstable (Eisenthal et al., 2006).Under these conditions (70°C),  phenol hydroxylase activity was still highest for the PS11 isolate in comparison to all other isolates, being 1.2-, 7.9-and 3.8-fold higher in comparison to PS1, TN41 and TN42, respectively (Table 4).Phenol hydroxylase activity was comparable at 10°C and 80°C for the PS1 isolate, while it was 1.8-, 1.7-and 3-fold lower at 80°C in comparison to 10°C for PS11, TN41 and TN42 isolates, respectively (Fig. 1a).In the case of the oxygenases, specific activity remained from 5to 10-fold higher at 80°C in comparison to 10°C for all four isolates (data not shown).Straube reported a temperature range of 10°C to 55°C, with 35°C being the optimum for Rhodococcus phenol hydroxylase (Straube, 1987).In contrast, the optimum temperature for phenol hydroxylase from Bacillus thermo-glucosidasius A7 was reported to be 55°C (Kirchner et al., 2003).Di Nardo et al. reported a temperature range for the C12O from Acinetobacter radioresistens S13 of 10°C to 60°C (Di Nardo et al., 2009).
Phenol hydroxylases of the TN strains could tolerate a broader range of pH conditions and had higher activities at lower pH values, while phenol hydroxylase activity could not be detected at pH 2 and pH3 for the PS strains (Fig. 1b).The maximum specific activity for both TN strains was observed at pH3 (Table 4).In contrast, maximum specific activity for catechol 1,2-and 2,3-dioxygenase was observed at pH values 11 and 10 for PS and TN isolates, respectively (Table 4).Even under optimal conditions for the maximum value for enzymatic activities, the PS strains had higher enzymatic activities in comparison to the TN strains.In the literature, the pH optimum for these enzymes ranges from 5.5 to 8.2 (Ahuatzi-Cacon et al., 2004;Kirchner et al., 2003;Viggor et al., 2008).Catechol 2,3-dioxygenase from Pseudomonas sp.exhibited a pH activity range from 5.5-9.5 (Wei et al., 2009).

PCR-based detection of phenol hydroxylase gene
Phenol hydroxylase has been used as a molecular marker of phenol-degrading bacteria (Basile and Erijman, 2008;Sandhu et al., 2009).In addition, phenol hydroxylases can be used as biocatalysts and potential agents for organic syntheses (i.e.indigo dye production (Kim et al., 2005)), thus the detection of novel phenol hydroxylases is of high interest.We have successfully amplified the core region of a large PH subunit in three out of four Bacillus soil isolates (Fig. 2).
In the PCR experiments, using the genomic DNA of four phenol-degrading isolates as a template, fragments of the expected size (870 bp) were obtained for PS1 and PS11 as previously reported (Djokic et al., 2011), while no expected fragment was detected for the TN41 isolate and the expected size fragment was obtained for the TN42 isolate (Fig. 2).The appropriate control reaction with B. cereus ATCC14579 gDNA yielded no detectable fragments (Fig. 2).The primers used were groupspecific primers designed to amplify the core region of a large phenol hydroxylase subunit in Gram positive bacteria (Sandhu et al., 2009).The inability to amplify the PH fragment from the TN41 isolate may indicate that the sequence of this gene is sufficiently different from the primers used.The ob-Table 3. Specific activities of phenol hydroxylase (PH), catechol 1,2-dioxygenase (C12O) and catechol 2,3-dioxygenase (C23O) from cell free extracts of phenol degrading isolates grown at 30°C in rich medium (TSB) and rich medium supplemented with inducer (phenol).a pH 7, b pH 3, c pH11, d pH10, ND = not detected, under conditions tested tained fragments were sequenced and compared to the available sequences in the GenBank database.The sequences of isolates PS1 and PS11 were identical, with closest similarity of 99% observed to the Rhodococcus erythropolis PR4 gene encoding for putative phenol hydroxylase (Djokic et al., 2011).The sequence of TN42 shows 97% sequence identity with the Rhodococcus erythropolis phenol degradation gene cluster.
BLAST analysis showed high similarity between the PH genes from the PS1, PS11 and TN42 strains with those from Rhodococcus erythropolis, with DNA identity of 98%, 99%, and 97%, respectively.High gene sequence similarity between PS1, PS11 and TN42 with Rhodococcus, coupled with the high promiscuity of Bacillus strains, could indicate that these genes underwent a horizontal gene transfer event.
Our aim was to isolate Gram positive bacteria capable of tolerating high amounts of phenol in the soil sample from the river bank in close proximity to the petrochemical facility, and to compare these to isolates from the rhizospheres of phenolic extruding Ramonda serbica.We aimed to isolate either Bacillus or Streptomyces strains for their advantageous spore-forming ability, due to the absence of reports on their applicability in the bioremediation efforts.Although at the beginning of this study the riverbank soil sample provided 4-fold more phenoltolerant isolates in comparison to the rhizosphere sample, we obtained only two isolates with a good capability of utilizing phenol as the sole source of carbon and energy.These novel isolates were designated as Bacillus sp.TN41 and Bacillus sp.TN42.They were found to be less tolerant to higher initial amounts of phenol in comparison to Bacillus isolates from the rhizosphere.In addition, the specific enzyme activities of PH, C12O and C23O were also lower under all tested conditions.Since data on Bacillus wide-range aromatic degrading strains are scant, the present study provides a better understanding of phenol degradation pathways and provides the basis for the possible application of these common soil strains in bioremediation.

Fig. 1
Fig. 1 Effect of temperature (A) and pH (B) on the activity of phenol hydroxylase in the cell extracts of four Bacillus strains (; TN41, ;TN42, ;PS1 and ; PS11).Data is average of two independent experiments.

Table 1 .
Identification and comparison of bacterial isolates, from river bank soil and a rhizosphere associated soil capable of growth on phenol as sole carbon and energy.

Table 2 .
Aromatic substrate range used for the growth of Bacillus isolates TN41, TN42, PS1 and PS11.
a +, confluent growth on MSM agar plate containing the aromatic substrate as the sole source of carbon and energy at 30°C a(Djokic et al. 2011)

Table 4 .
Conditions (pH and temperature)for the maximum specific activity of phenol hydroxylase and catechol dioxygenases of four Bacillus isolates.