- Open Access
Could petroleum biodegradation be a joint achievement of aerobic and anaerobic microrganisms in deep sea reservoirs?
© da Cruz et al; licensee Springer. 2011
- Received: 20 October 2011
- Accepted: 23 December 2011
- Published: 23 December 2011
Several studies suggest that petroleum biodegradation can be achieved by either aerobic or anaerobic microorganisms, depending on oxygen input or other electron acceptors and appropriate nutrients. Evidence from in vitro experiments with samples of petroleum formation water and oils from Pampo Field indicate that petroleum biodegradation is more likely to be a joint achievement of both aerobic and anaerobic bacterial consortium, refining our previous observations of aerobic degradation. The aerobic consortium depleted, in decreasing order, hydrocarbons > hopanes > steranes > tricyclic terpanes while the anaerobic consortium depleted hydrocarbons > steranes > hopanes > tricyclic terpanes. The oxygen content of the mixed consortia was measured from time to time revealing alternating periods of microaerobicity (O2 ~0.8 mg.L-1) and of aerobicity (O2~6.0 mg.L-1). In this experiment, the petroleum biodegradation changed from time to time, alternating periods of biodegradation similar to the aerobic process and periods of biodegradation similar to the anaerobic process. The consortia showed preferences for metabolizing hydrocarbons > hopanes > steranes > tricyclic terpanes during a 90-day period, after which this trend changed and steranes were more biodegraded than hopanes. The analysis of aerobic oil degrading microbiota by the 16S rRNA gene clone library detected the presence of Bacillus, Brevibacterium, Mesorhizobium and Achromobacter, and the analysis of the anaerobic oil degrading microbiota using the same technique detected the presence of Bacillus and Acinetobacter (facultative strains). In the mixed consortia Stenotrophomonas, Brevibacterium, Bacillus, Rhizobium, Achromobacter and 5% uncultured bacteria were detected. This is certainly a new contribution to the study of reservoir biodegradation processes, combining two of the more important accepted hypotheses.
- Petroleum biodegradation
- oxic environment
- anoxic environment
- 16S rRNA gene
- petroleum biomarkers.
Much of the petroleum of the Campos Basin has been altered by microbial degradation decreasing the value of the residual oil. This is a major problem for the global economy (Magot et al. 2000; Cord-Ruwich et al. 1987; Connan 1984; Head et al. 2003). The action of aerobic bacteria (Roling et al. 2003; Orphan et al. 2000; Borzenkov et al. 2006) in petroleum reservoirs is supported by the presence of sufficient oxygen and of nutrient supplies provided by meteoric waters (Connan 1984; Voordouw et al. 1996). The rapid biodegradation of n-alkanes and other biomarkers has been reported with pure aerobic cultures as well as with consortia (da Cruz et al. 2008).
However, biodegradation of crude oils has also been observed in the absence of oxygen and anaerobic heterotrophic microorganisms requiring nitrate, sulfate, iron, manganese or carbon dioxide as electron acceptors (Borzenkov et al. 2006; Palmer 1993; Taylor et al. 2001) are responsible for crude oil biodegradation (Rahman et al. 2002; Balk 2007, Jones et al. 2008; Wilkes et al. 2000). Addtionally, Jones et al. (2008) observed sequential removal of hydrocarbons under methanogenic conditions after 686 days.
The goal of the present study was to investigate the potential of aerobic bacteria, anaerobic bacteria and mixed consortia obtained from samples of petroleum formation water and oils from Pampo Field (Brazil) to degrade petroleum biomarkers.
Geological and geochemical bulk data.
Sat. HCs (%)
Arom. HCs (%)
Lagoa Feia Formation (coquinas)
Macaé Formation (calcarenites)
The aerobic experiment was carried out following the methodology previously described by da Cruz et al. (2008). The aerobic biodegradation process was stimulated by adsorbing oil on sterilized sand and by using 2 g wet cells/30 mg P1 oil/40 mL aqueous Zinder medium (Zinder et al. 1984). The cells were centrifuged from the enrichment experiment as previously described (da Cruz et al. 2008). Aerobic consortia was set up in Erlenmeyer flasks incubated in a shaker with temperature and agitation control (30°C and 150 rpm) during 60 days. Laboratory anaerobic and mixed (aerobic/anaerobic) consortium experiments were set up in 50 mL glass serum bottles sealed with butyl stoppers and aluminium crimps containins resazurin as redox potential control. The bottles were incubated at 30°C during 30 days (with agitation control) and then at 55°C for up to 180 days (without stiring). A gas system fitted with an oxygen sensor and with a regulated atmosphere of nitrogen (80%) and carbon dioxide (20%) was used in the preparation and incubation of the anaerobic and mixed microorganism consortium. Each consortium biodegradation experiment was composed of 40 mL of Zinder nutrient medium (Zinder et al. 1984) containing sources of organic substrates, nitrogen, phophorus, vitamins and trace minerals, made up in Milli-Q water and 30 mg of non-biodegraded oil (P1 from Pampo Sul Field, Campos Basin, Brazil). For the control experiments the same components were used without crude oil to evaluate the consortia in the absence of oil. Perchlorate was added as an oxygen supply for the mixed consortia and the biodegradation processes were stimulated by adsorbing oil on sterilized sand. The experiments were carried out in duplicate and controls of consortia and Zinder medium were included. Samples were processed following a strict protocol and the anaerobic experiments were run in sealed vials and compared to the control experiments. Volatile losses were taken into account by comparing both experiments. The microbial consortia was slightly dependent on the oil storage period, causing oscillations. A reference aerobic bacterial consortium was discussed by Sette et al (2007).
The hydrocarbon contents from each sampling were subjected to extraction with dichloromethane every 10 (aerobic consortia) or 30 days (anaerobic and mixed consortium). Hydrocarbon fractions were obtained by silica gel chromatography using hexane as eluent for GC-MS analyses. Gas chromatography was carried out with a Hewlett Packard 5890 instrument connected to a Hewlett Packard 5970-MSD mass detector, fitted with a MDN5S coated capilary column (30 m length, 0.25 mm internal diammeter, 0.25 μm film thickness). The GC conditions were: split injection (10:1), with He as carrier gas at 1 mL/min. The data were obtained in both full scan and single ion monitoring (SIM) modes, at 70 eV ionization energy. The temperature program was adapted to each biomarker class. The injector temperature was set at 300°C. The analyses of n-alkanes (m/z 71) were performed with the temperature program: 80°C (hold 2 min) to 270°C at 4°C/min and at 10°C/min to 300°C (hold 25 min). For the analyses of hopanes and homohopanes (m/z 191), 25-norhopanes (m/z 177) and steranes (m/z 217) the temperature program was: 70°C (2 min) to 190°C at 30°C/min, to 250°C at 1.5°C/min and at 2°C/min to 300°C (hold 20 min). All samples were analyzed in duplicate using 5α-cholestan-3-one, 0.02 μg/mL, as internal standard for the quantitative analyses of biomarker biodegradation. The instrument response was regularly checked by injecting a mixture of n-alkanes.
Biomarker biodegradation ratios were calculated using peak areas from the m/z 191 and m/z 217 ion chromatograms. The quantitative analyses were carried out following the methodology previously described by da Cruz et al. (2008).
Gas aliquots were removed every 30 days and the headspace composition was analyzed using gas chromatography-mass spectrometry (GC-MS). The amount of dissolved oxygen (DO) was measured during 60 days each 10 days using a galvanic DO probe from Fisher Scientific (the observed range was 8.2-8.7 mg/L ± 1.5%, temperature 22-24.5°C). The anaerobic assays used resazurin as redox indicator, which remained colorless during the experiment indicating an E' of < -0.11 V. By using the Nernst equation, this redox potential was calculated to correspond to a theoretical oxygen concentration of < 1 pmol/L O2 (Zeyer et al. 1986). The oxygen in solution was rapidly measured after opening the flasks at room temperature and atmosphere.
DNA extraction and 16S rRNA gene libraries
One 16S rRNA gene library was constructed for each of the aerobic (Co_Aer), anaerobic (Co_Ana) and mixed (Co_mix) microbial consortium. Samples for DNA extraction were taken at the end of the biodegradation assay and replicates of each microbial consortium were pooled before molecular biology procedures. DNA extraction of the bacterial consortia was carried out using a protocol based on Groβkopf et al. (1998) and Neria-Gonzáles et al. (2006), with modifications, as follows: the microbial pellets retrieved from enrichments (20 mL-aliquots) were suspended in 600 μL PBS buffer, homogenized by vortex and adding lisozyme to a final concentration of 17 mg/mL. After incubation at 37°C for 1 h, proteinase K and SDS were added (final concentration of 0.7 mg/mL and 2%, respectively) and the solution was incubated at 60°C for 30 min. The tubes were subjected to 3 freeze-thaw cycles (2 min in liquid nitrogen followed by 2 min at 65°C). The solution was extracted once with an equal volume of saturated phenol (pH 8.0) and once with an equal volume of chloroform:isoamylic alcohol (24:1). For DNA precipitation, 10% NaCl and 2 volumes of cold ethanol were added to the solution. The pellet was washed once with 70% ethanol, dried and suspended in Milli-Q water. For 16S rRNA gene library construction, amplification was performed from total community DNA by using the bacterial primer set 27f and 1100r (Lane 1991). Fifty microliters of the reaction mixtures contained 50 ng of total DNA, 2 U of Taq polymerase (GE Healthcare), 0.2 mmol/L-1 of dNTP mix, and 0.4 μmol/L-1 of each primer, in 1× Taq buffer. PCR amplifications were done using 10 cycles of 1 min at 94°C, 30 s at 60°C, decreasing 0.5°C each cycle, and 3 min at 72°C, followed by additional 10 cycles of 1 min at 94°C, 30 s at 56°C and 3 min at 72°C. Amplicons were pooled from five reactions (~500 ng), purified using GFX™ PCR-DNA and gel band purification kit (GE Healthcare) and cloned using the pGEM-T cloning vector kit, according to the manufacturer's instructions (Promega, Madison, WI). All the insert-containing clones were submitted to amplified ribosomal DNA restriction analysis (ARDRA) by digesting M13 amplicons with the enzymes Hae III, Hha I and Msp I, at 37°C for 2 h 30 min. Clones representing distinct ribotypes were selected for DNA sequencing and phylogenetic analysis. The 16S rRNA gene sequences were determined by direct amplification of the inserts from overnight grown-clone cultures with M13 forward and reverse primers and sequencing with the DYEnamic ET Dye Terminator Cycle Sequencing Kit for the automated MegaBace 500 system (GE Healthcare), according to the manufacturer's recommendations.
Partial 16S rRNA gene sequences obtained from clones using forward and reverse primers were assembled in a contiguous sequence using the phred/Phrap/CONSED program (Godon et al. 1997; Ewing et al. 1998). Identification was achieved by comparing the contiguous 16S rRNA gene sequences with 16S rRNA sequence data from reference and type strains, as well as environmental clones, available at the public databases Genbank and the RDP (Ribosomal Database Project, Wiscosin, USA) by using BLASTn and RDP sequence match routines. Sequences were aligned using the CLUSTAL X program (Thompson et al. 1997) and analyzed with MEGA software Version 4.0 (Tamura et al. 2007). The evolutionary distances were derived from the sequence-pair dissimilarities, calculated as implemented in MEGA using the DNA substitution model reported by Kimura (1980). The phylogenetic reconstruction was done using the neighbour-joining (NJ) algorithm (Saitou and Nei 1987), with bootstrap values calculated from 1000 replicate runs, using the routines included in MEGA software. The nucleotide sequences determined in this study were deposited at the Genbank database under the accession numbers: FJ493061 to FJ493071.
For diversity analysis of the 16S rRNA libraries, Operational Taxonomic Units (OTU) were defined as distinct ARDRA profiles obtained and total richness as the number of observed OTUs. Coverage values were calculated for each 16S rRNA library using the formula of Good (1953). Rarefaction curves based on ARDRA data were performed using the independent sampling algorithm, implemented in the EcoSim program (Gotelli and Entsminger 2003).
Biodegradation (%) for n-alkanes and isoprenoids by aerobic, anaerobic and mixed consortium.
96 ± 0.9
48 ± 1.6
> 99 ± 1.60
68 ± 1.5
51 ± 1.4
98 ± 2.4
63 ± 1.3
33 ± 1.1
> 99 ± 1.1
50 ± 0.9
50 ± 0.8
> 99 ± 0.6
45 ± 0.5
46 ± 0.6
> 99 ± 0.8
54 ± 2.1
42 ± 2.8
98 ± 2.7
39 ± 1.2
39 ± 1.8
> 99 ± 1.7
55 ± 0.6
57 ± 0.9
> 99 ± 2.0
45 ± 2.2
42 ± 1.2
> 99 ± 1.2
69 ± 1.5
62 ± 1.8
> 99 ± 1.6
49 ± 0.9
47 ± 0.7
> 99 ± 2.7
60 ± 0.8
60 ± 0.9
> 99 ± 1.3
65 ± 1.3
51 ± 1.5
> 99 ± 0.9
60 ± 1.8
59 ± 1.6
> 99 ± 0.8
64 ± 0.6
44 ± 0.9
> 99 ± 2.8
68 ± 1.6
64 ± 1.8
> 99 ± 2.6
63 ± 1.0
41 ± 2.0
> 99 ± 0.6
69 ± 2.0
67 ± 1.0
> 99 ± 1.5
44 ± 1.1
42 ± 1.3
> 99 ± 1.2
49 ± 1.6
59 ± 1.9
> 99 ± 1.1
50 ± 1.1
42 ± 1.8
Biomarker ratios for different microbial consortium from laboratory degraded oil and from Pampo Sul field (P2).
C 28 TT/C 35 H a
C 29 TT/C 35 H a
C 35 H/C 30 H b
C 28 TT/C 35 H
C 29 TT/C 35 H
C 35 H/C 30 H
C 28 TT/C 35 H
C 29 TT/C 35 H
C 35 H/C 30 H
Coverage values and composition of bacterial 16S rRNA gene clone libraries from the aerobic (A), anaerobic (B) and mixed (C) consortium.
In our assays the aerobic consortium selectively degraded n-alkanes and isoprenoids (biodegradation rates of 36 to 99% in 60 days), with decreasing ratios of pristane (Pr)/phytane (Ph), increasing ratios of Pr/n C17 and Ph/n C18, and an even-to-odd predominance over all the biodegradation process. The anaerobic (micro) consortium showed a slower depletion rate of n-alkanes and isoprenoids (39 to 69% in 180 days) and an odd-to-even predominance. The mixed aerobic/anaerobic consortia alternated n-alkane biodegradation preferences (33 to 64% in 180 days) and the even-to-odd or odd-to-even preferences with lower biodegradation rates than with the pure aerobic consortium (Table 2). It is commonly accepted that odd number n-alkane preference is associated with low oil thermal maturity; however these experimental data reveal that the alkane carbon number predominance can change with the type of biodegradation and should be interpreted with caution.
Headspace monitoring for 270 days (every 10 days) of the anaerobic and mixed consortia detected acetic acid (Heuer et al. 2010, 120 days of biodegradation) and CO2 (270 days of biodegradation) but no methane, indicating the presence of acetogenic bacteria and the absence of methanogenic archaea in the microbiota Zengler et al. (1999) showed that the process of CH4 formation is very slow, taking about 150 days to obtain detectable amounts of CH4.
Biodegradation with the aerobic consortia increased the ratios of tricyclic terpane (TT) [C28 (TT)/C35 17α,21β-homohopane (C35H), C29 tricyclic terpane (TT)/C35 17α,21β-homohopane (C35H)] with increasing biodegradation time, revealing a preferencial depletion of (R+S) C35 hopane (> 82% depletion) in relation to tricyclic terpane (22 and 17% depletion of C28 and C29 TT, respectively) (Table 3). These assays confirmed the selective biodegradation of 22R homohopane isomers. The anaerobic experiment revealed that these ratios decreased, suggesting a preferential depletion of tricyclic terpane (40 and 38% depletion for C28 and C29 TT, respectively) relative to C35 hopane (36% depletion). The aerobic consortia degraded 0 to 22% C23-C31 TT, whereas the anaerobic consortia degraded 19 to 40% of such compounds. This effect reveals that oils with lower tricyclic/17α-hopane ratios, usually interpreted as more mature oils, could, in fact, be the consequence of an anaerobic microbiota biodegradation operating at higher temperatures.
The homohopane index decreased for aerobic consortium, showing that C35 is more biodegradable than C31-C34 homohopanes, with preferential biodegradation of the higher molar-mass 22R epimers C35 > C34 > C33 > C32 > C31 extended hopanes. Our data are similar to the results of the laboratory culture experiments made by Goodwin et al. (1983) but opposite to the laboratory studies conducted by Bost et al. (2001). These apparent conflicting results indicate that experiments with different consortia produce different biomarker parameters. Therefore the coherence in biodegradation parameters applied to petroleum analyses for the last 60 years indicate that the microbiota in most reservoirs are consistent. The homohopane index increased during the anaerobic biodegradation and indicates a preferential biodegradation of the lower molar mass homohopane 22R C31 > C32 > C33 > C34 > C35, suggesting that C35 is more resistant to the biodegradation process. The bioresistance of higher-hopane homologs has been reported in different oils (Moldowan and McCaffrey 1995; Peters and Moldowan 1991).
The experiment with mixed consortia, revealed an oscillating content of oxygen with periods of microaerobicity, at ~0.8 mg/L and aerobicity at ~6 mg/L of oxygen. These experiments were performed in closed vessels, therefore the oxygen was generated and consumed by the microbiota in alternated lifecycles (Figure 4). The biodegradation preference for all biomarkers was unusual, with aerobic characteristics (increasing C28TT from 30 to 90 days, Table 3) alternating with anaerobic ones (decreasing C28TT from 90 to 120 days, Table 3). The homohopane index decreased in the first 60 days and increased from then on until the assay was completed (180 days), with an unusual homohopane biodegradation preference C33 > C32 > C31 > C34 > C35 Munoz et al. (1997) showed 25% depletion of C35 pentakishomohopane and only 3% depletion of C31 homohopanes in soils exposed to an oil spill for eight years. Thus the controversial relative suceptibility of homohopanes to biodegradation, observed in the field and in laboratory experiments (Goodwin et al. 1983; Bost et al. 2001; Moldowan and McCaffrey 1995; Peters and Moldowan 1991; Munoz et al. 1997) might be assigned to different microbiota, aerobic, anerobic or both, when dealing with oils of equal origin and reservoir matrix. Consequently our experiments validate the C35 homohopane index traditionally used to evaluate the oxic or suboxic environment, linking this index to aerobic, anaerobic and mixed biodegradations (Obermajer et al. 2000).
The norhopanes 18α (H)-22,29,30-trisnorneohopane (Ts) and 17α(H)-22,29,30-trisnorhopane (Tm) remained almost unaltered throughout the experiment, with a small Ts/Tm ratio increase, indicating that Tm is more susceptible to biodegradation in all processes (aerobic, anaerobic and mixed).
During aerobic experiments the steranes (67% depletion) were less degraded than hopanes (87% depletion) and an increase of the sterane/hopane ratio was observed. Under anaerobic conditions sterane biodegradation (80% depetion) occured before that of hopane (67% depletion), decreasing the sterane/hopane ratio (Table 3). Mixed and aerobic consortium preferentially biodegraded steranes relative to hopanes (30 to 90 days) however this relative susceptibility was inverted over the next 60 days (120 to 180 days), which is consistent with anaerobic biodegradation. Sterane preferencial biodegradation was equal under both aerobic and anaerobic consortium, ααα 20R > > αββ 20R + αββ 20S ≥ ααα 20S > > diasteranes, and opposite for mixed consortia, αββ 20R + αββ 20S > ααα 20R > ααα 20S > > diasteranes with increasing carbon number C27 > C28 > C29 for all experiments. The relative susceptibility of these isomers varies considerably and depends on the microbiota involved, as shown by the present results. Therefore the 20S/(20S + 20R) ratio used as a thermal maturation parameter should be used with caution.
These controlled in vitro experiments (anaerobic, aerobic and both aerobic/microaerobicity conditions) provide a unique ensemble of data that were used in an attempt to explain controversial observations of in reservoir biodegradation and that attested to some biodegradation parameters. The evidence suggests that aerobic biodegradation is mainly responsible for the depletion of the linear hydrocarbons with an even-to-odd carbon preference, although switching to an anaerobic biodegradation, with odd-to-even carbon preference, was observed. The mixed (aerobic and anaerobic consortium) displayed periods of C-even preference and periods of C-odd preference, indicating the existence of alternating aerobic and anaerobic lifecycles. A comparative biodegradation of terpanes, hopanes and steranes under aerobic and anaerobic conditions, Table 3, indicate that some of the controversial biomarker parameters can be easily explained by taking into consideration the microbiota and oxygen content. These results represent an important step in understanding reservoir biodegradation, revealing that anaerobic and aerobic biodegradation can indeed occur without external input of oxygen.
This work was part of the multidisciplinary project BIOPETRO supported by FINEP and PETROBRAS. G. F. da Cruz was supported by grants from CAPES (Coordenação de Aperfeiçoamento de Pessoal de Nível Superior). S. P. Vasconcellos and C. F. F. Angolini were supported by grants from FAPESP (Fundação de Amparo à Pesquisa do Estado de São Paulo). We thank PETROBRAS for the authorization to publish this work. The authors are grateful to Prof. Carol Collins for revising this text.
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