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Braz. J. Microbiol. vol.37 no.3 São Paulo July/Sept. 2006
Caracterização química e microbiológica de sedimentos de manguezal após um grande derramamento de óleo na Baia de Guanabara, RJ, Brasil
Maria do Carmo Maciel-SouzaI; Andrew MacraeI; Antonia Garcia Torres VolponII; Patrícia Silva FerreiraI; Leda Cristina Mendonça-HaglerI,*
ICentro de Ciências da Saúde, Instituto de Microbiologia Prof. Paulo de Góes, Universidade Federal do Rio de Janeiro, Rio de Janeiro, RJ, Brasil
IICentro de Pesquisas da Petrobrás, Rio de Janeiro, RJ, Brasil
Seventeen months after a 1,3 million L oil spill into Guanabara Bay, analyses of mangrove sediments showed that the three sites closest to the spill remain highly polluted (>10 µg-g-1 polyaromatic hydrocarbons). A fourth site was less polluted, from which most hydrocarbon degrading bacteria were isolated.
Key words: mangrove, PAH, bioprospecting, bioremediation, oil spill, polyaromatic hydrocarbons
Dezessete meses após um derramamento de 1,3 milhões de litros de óleo na Baía de Guanabara, análises de sedimento do manguezal mostraram que os três pontos de amostragem mais próximos do local do acidente permanecem altamente poluídos (>10 µg-g-1 hidrocarbonetos poliaromáticos). Do quarto ponto de amostragem, o menos poluído, foi isolada a maioria das bactérias degradadoras de hidrocarbonetos.
Palavras-chave: manguezal, HPA, bioprospecção, biorremediação, derramamento de óleo, hidrocarbonetos poliaromáticos
Mangroves are biologically important and productive ecosystems along subtropical and tropical coastlines, lagoons and estuaries. Undisturbed mangroves provide habitats for a wide variety of plants, animals and microorganisms. They have an important role in shore protection and are frequently associated with commercial fishing (11).They are at risk from acute/point pollution caused by freak accidents and from chronic pollution when associated with ports and petrochemical industries where repeated spills are common. In January 2000, more than 1,3 million L of heavy oil leaked from a refinery pipeline with visible pollution seen along 5 km of the Guanabara Bay coastline in Rio de Janeiro, oil covered sediments at points S1-S4 (Fig. 1) (9,17). This was not the first spill from the Duque de Caxias refinery but the largest in recent history. Although some of the effects of oil spills on mangrove ecosystems have been reported (3,8,10-12,16,20), little is known about chronic spill sites and the oil-degrading bacteria in such mangrove systems. Here we report on the physicochemical and microbiological state of four polluted Guanabara mangrove sites 17 months after being covered by oil and we compare that data with a nearby pristine mangrove. The chemical data is presented in the context of legal standards, the microbial data in colony forming unit (CFU) counts for heterotrophic bacteria (HB) and most probable number (MPN) for oil degrading bacteria. Oil degrading bacteria (DB) with biotechnological potential were isolated and identified from the rhizospheres of two mangrove plants: Rhizophora mangle and Laguncularia racemosa.
Bacterial counts and polyaromatic hydrocarbons (PAH) analyses were investigated from water, sediment and rhizosphere samples from the mangrove ecosystems in Guanabara Bay and Sepetiba Bay, Rio de Janeiro, Brazil. In Guanabara Bay, four contaminated sites were chosen. Sites S1 (22º 44' 06S; 043º 14' 21W), S2 (22º 44' 13S; 043º 14' 12W) and S3 (22º 58' 29S; 043° 13' 33W) are a transect extending from the spill site (S1) at the edge of the refinery mangrove along to the inner edge of Guanabara Bay (S3) on land belonging to the refinery. Site 4 (22º 41' 46S; 043º 06' 58W) is a more distant site that was also covered by oil as a result of the spill (Fig. 1). Site 5 samples (not shown in Fig. 1) were collected from the mangrove at Marambaia Restinga, Sepetiba Bay, Rio de Janeiro, (23º 02' 30S; 043º 35' 44W), and represent a pristine mangrove and a reference to which analyses were compared.
Water collection for microbial sampling was done using 500 mL sterilized flasks. Sediment samples (0-5 cm depth) were collected using a sterile stainless steel spatula. Three replicate samples were randomly collected from each site to make a composite sample and this was used for all subsequent analyses. Two mangrove tree species, R. mangle and L. racemosa, were selected for this study. To obtain sufficient rhizosphere sediment for microbial counts, 5 samples of sediment that adhered to the roots of five mangrove plants of similar size (~80 cm) were pooled to form one composite sample. This process was repeated six times to provide six different samples for analyses. All samples were transported on ice to the laboratory where they were stored at 4ºC until be analyzed. Temperature, pH, salinity, oxygen, biochemical oxygen demand (BOD), phosphorous and nitrogen were analyzed from water samples using standard methods (2). Extraction of n-alkanes and PAHs from sediment samples followed the USEPA (21) standard protocol 8260 and 827ºC. The concentrations of n-alkanes and PAH compounds were analyzed from six replicate samples from each site using a gas chromatograph Varian (GC/MS) at the Innolab Laboratory, Harburg, Germany. Heterotrophic bacteria (HB) colony forming unit (CFU) counts from water, sediment and rhizosphere samples were carried out using the spread-plate technique on Marine Agar (Difco). Rhizosphere samples, 5 g of sediment, were suspended in 45 mL of 0.1% sodium pyrophosphate (Merck) containing 0.1% Tween 80 in Erlenmeyer flasks with glass beads. After 30 min shaking at 200 rpm, serial dilutions were made with sterile saline solution (0.85%). Plates were prepared in triplicate and incubated at 29ºC for 48 hours. Hydrocarbon-degrading bacteria (DB) were estimated by serial dilution in tubes with 10 mL of mineral salts medium (MM) using the MPN method (2). The MM was prepared as follows: 0.05% K2HPO4; 0.05% KH2PO4; 0.02% MgSO4 .7 H2O; 0.01% CaCl2 .2 H2O; 0.01% NaCl; 0.0002% FeCl3 .6 H20; 0.05% NH4NO3; pH 7.0. Arabian Light crude oil was added, as the sole carbon source, to the sterilized media to a final concentration of 0.5% (vol/vol). The media was then inoculated and incubated for 7 days at 29ºC. After incubation, 50 mL aliquots from growth-positive tubes of rhizosphere samples were inoculated in MM plus crude oil and incubated for further 7 days at 29ºC. Sub-samples (1 mL) from the MPN tubes were taken and plated onto Tryptic Soy Agar (Difco). Isolates were described as petroleum degraders after growth in media with crude oil as the sole carbon source. Those bacteria that degraded the C15, C18 fractions and the Arabian Light crude oil at 0.5% (vol/vol) within 48 hours, resulting in an emulsion, were identified by 16S rDNA sequencing and stored for future biotechnological purposes. DNA was extracted from isolates using MoBio Ultra Clean DNA Isolation kit (Mo Bio Inc. Solana Beach - CA, USA) and 16S rDNA Polymerase Chain Reaction (PCR) amplified using primers U968f (5' AAC GCG AAG AAC CTT AC 3') and L1401r (5' GCG TGT GTA CAA GAC CC 3') (Interactiva, Germany) and protocols of Nubel et al. (15). Partial 16S rDNA sequences (250-400 base pairs) were obtained by automatic sequencing using an ABI 310 sequencer and the PRISM Big DyeTMTermination Cycle Sequencing kit. Sequences were compared with those on public databases using BLAST in order to identify the most efficient oil degrading bacteria (1).
Data in Table 1 A, B, C demonstrate that concentrations of n-alkanes, total PAHs and individual PAH in surface sediments varied considerably among the Guanabara mangrove sites (S1-S4) and between Guanabara and Marambaia site (S5). The amounts of PAHs accumulated in Sites S1 to S3 sediments were much higher than S4. N-alkanes and PAH values were below detectable levels at the pristine reference site (S5). Data in Table 1C showed increased BOD with distance from the oil spill (S1 to S4) but did not reach the characteristically high BOD levels typical of mangrove sediments (S5). At Sites S1, S2 and S3 the ammonia levels were four to five times higher than the Brazilian National Environment Agency (IBAMA) guidelines (6). CFU counts of heterotrophic bacteria (HB) in the water samples were similar for all five sites (105 CFU mL-1). No impact on HB counts in water was apparent 17 months after the spill (Table 2). The counts for degrading bacteria (DB) were higher in water from the four polluted sites than at the pristine site S5. The sediment samples showed one order of magnitude increase in HB compared with the water samples at sites S1-S3 and a two order of magnitude increase for sites S4 and S5 (ranging from 104 - 107 MPN/100 mL-1). Counts of DB from sediments at S1 to S5 were an order of magnitude higher than their equivalents from water (Table 2). Counts of rhizosphere HB and DB remained relatively constant for R. mangle and L. racemosa during the study period. No rhizosphere effect on counts could be seen. The trend of a lower MPN for DB from rhizosphere sediments at the pristine site compared with rhizosphere sediments from polluted sites was again observed. Of the 400 degrading bacterial strains initially isolated from rhizosphere soils, 78 repeatedly grew under laboratory conditions and were tested for oil degradation potential. From the 78, eleven strains degraded oil within 48 hours and were selected for identification by partial 16S rDNA sequencing. Ten of the eleven strains sequenced were identified as Bacillus and the remaining strain as Acinetobacter. Three Bacillus strains (MC6, MC7, MC11) shared less than 95% 16S rDNA partial sequence similarity (~500 base pairs) compared with described type strains. These strains require further investigation to determine whether they merit new species status. The remaining strains had partial sequences (~500 base pairs) which were >97% similar to well described and known type strains.
Total PAH levels in surface sediments up to 20 µg-g-1 at S3 area were detected ten days after the spill in 2000 by Gabardo et al. (9). They importantly raised the issue that previous spills into Guanabara Bay from the same refinery made it difficult to determine whether their values recorded ten days after the large spill could be solely attributed to that particular spill. Seventeen months later, evidence of oil could still be seen on the trunks and roots of mangrove vegetation and sediments at all four Guanabara sites (S1-S4). Mean total PAHs for S1 and S2 were found to be 16.8 and 28.3 µg-g-1 respectively, which are similar to values reported by Gabardo et al. (9). Site 3 was lower at 11.5 µg-g-1 and S4 much lower at 1.23 µg-g-1 and as expected PAHs were not detected at S5. Placing these results in a global context, it is noted that the PAH levels in Guanabara Bay were between two and six times higher than the highest levels (6.19 µg-g-1) found from 20 sampling sites in four mangroves in Hong Kong (20). Moreover, Tam et al. (20) compared their data with further fourteen sites in Hong Kong, China, the Caribbean and Puerto Rico where the highest PAH level reported was 2.2 µg-g-1. Clearly the levels of PAHs reported here are very high by global comparison. In another study on PAHs (7) the important role of mangrove sediments as traps, or concentrating sites, for oil pollution was stressed. Medeiros et al. (17) reporting on an estuarine lagoon in Southern Brazil found mean total PAHs at 11.8 µg-g-1 from sediments next to a petroleum distribution plant and 4.4 µg-g-1 from refinery sediments. These sites were 100 and 40 times more contaminated than a nearby lagoon and were described as sites of chronic/repeated pollution. From this preliminary study, we suggest that sites S1-S3, which continued to be highly PAH contaminated 17 months after the spill, are sites of repeated pollution (18,24). High levels of ammonium, a labile compound (Table 1C), are indicative of chronic industrial and sewage pollution, and were also found at sites S1-S3. This type of pollution has been independently reported by Paranhos et al. (21) in vicinity of S1-S3. The much lower PAH levels at S4 (1.23 µg-g-1)might indicate that this site is not repeatedly polluted and natural bioremediation is reducing PAH levels (15), however, to test this hypothesis new experiments are needed. Seventeen months after the spill, CFU counts did not reveal a disturbance in the numbers of heterotrophic bacteria in the water samples; however, they were lower in the polluted sediments than at the pristine site. Conversely, MPN numbers of degrading bacteria were higher from sites S1-S4 than S5. These findings are reasonable and are explained as an overall decrease in total HB bacteria as a result of the pollution and an enrichment of degrading bacteria in response to the enrichment of hydrocarbons spilled into the environment. A rhizosphere effect was not observed for R. mangle and L. racemosa which could reflect the difficulties in representative sampling from firstly the rhizosphere and secondly from tidal sediments (15). Seven of the best eleven petroleum-degrading strains were isolated from the rhizosphere of plants at S4, an interesting Site. The Site of intermediary pollution and possibly in recovery warrants further investigation to establish if there is a link between PAH concentration and biodegradation rates; similarly, is there an important difference between point versus chronic pollution sites for bioprospecting? Strains from the genera isolated in this study have frequently been reported as DB (6). Ten of the eleven most efficient petroleum degraders belonged to genus Bacillus, already recognized as a bacterial group of considerable practical importance for biotechnological applications. Several Bacillus strains from soils and mangrove sediments have already been reported as hydrocarbon degraders and emulsifier producers (10,13,23). Our results support those of Macrae et al. on soil (16), who found bacilli as dominant rhizosphere organisms and suggested that they should be targeted to provide microbial solutions which ameliorate polluted environments. Clearly, the desire to remediate pollution exists and our preliminary findings support the notion that it is in polluted sites that we are likely to find the microbes best adapted to carry out bioremediation.
The authors would like to thank CENPES-PETROBRAS and the Brazilian scientific research council CNPq for financial support; Dr Hugo Fortini, FEEMA, for his assistance with chemical analyses, José Olavo Nascimento for technical support and the Postgraduate Program in Microbiology, IMPPG, Federal University of Rio de Janeiro (UFRJ).
1. Altschul, S.F.; Madden, T.L.; Schaeffer, A.A.; Zhang, J.; Zhang, Z.; Miller, W. Gapped BLAST and PSI-BLAST: a new generation of protein database search programs. Nucleic Acids. Res., 25, 3389-3402, 1997. [ Links ]
2. American Public Health Association (APHA). Standard Methods for the Examination of Water and Wastewater. Ed. A.E. Greenberg; L.S. Clesceri; A.D. Eaton. APHA/AWWA/WEF. 1-10, 2000. [ Links ]
3. Böer, B. Anomalous pneumatophores and adventitious roots of Avicennia marina (Forssk.) Vierh. mangroves two years after the 1991 Gulf war oil spill in Saudi Arabia. Mar. Pollut. Bull., 27, 207-211, 1993. [ Links ]
4. Cerniglia, C.E. Biodegradation of polycyclic aromatic hydrocarbons. Curr. Opin. Biotechnol., 4, 331-338, 1993. [ Links ]
5. Colombo, J.C.; Barreda, A.; Bilos, C.; Cappelletti, N.; Demichelis, S.; Lombardi, P.; Migoya, M.C.; Skorupka C.; Suárez, G. Oil spill in Rio de la Plata estuary, Argentina: 1. Biogeochemical assessment of water, sediments, soils and biota. Environ. Pollut., 134, 277-289, 2005. [ Links ]
7. Díaz, M.P.; Grigson, S.J.W.; Pepita, C.J.; Burgess, J.G. Isolation and characterization of novel hydrocarbon-degrading euryhaline consortia from crude oil and mangrove sediments. Mar. Biotechnol., 2(6), 522-532, 2000. [ Links ]
8. Duke, N.C.; Watkinson, A.J. Chlorophyll-deficient propagules of A. marina and apparent longer term deterioration of mangroves fitness in oil-polluted sediments. Mar. Pollut. Bull., 44, 1269-1276, 2002. [ Links ]
9. Gabardo, I.T.; Meniconi, M.F.G.; Falcão, L.V.; Vital, N.A.A.; Pereira, R.C.L.; Carreira, R.S. Hydrocarbon and ecotoxicity in seawater and sediment samples of Guanabara Bay after the oil spill in january 2000. Proc. 2001 International Oil Spill Conference, American Petroleum Institute Publ., 2001, pp.941-950. [ Links ]
10. Holguin, G.; Vazquez, P.; Bashan, Y. The role of sediment microorganisms in the productivity, conservation, and rehabilitation of mangrove ecosystems: an overview. Biol. Fertil. Soils, 33, 265-278, 2001. [ Links ]
11. Lugo, A.E.; Snedaker, S.C. The ecology of mangroves. Annu. Rev. Ecol. Syst., 5, 39-64, 1974. [ Links ]
12. Mackey, A.P.; Hodgkinson, M. Assessment of the impact of naphthalene contamination on mangrove fauna using behavioral bioassays. Bull. Environ. Contam. Toxicol., 56(2), 279-286, 1996. [ Links ]
13. Macrae, A.; Lucon, C.M.M.; Rimmer, D.L.; O'Donnell, A.G. Sampling DNA from the rhizosphere of Brassica napus to investigate rhizobacterial community structure. Plant Soil, 233, 223-230, 2001. [ Links ]
14. Medeiros, P.M.; Bícego, M.C.; Castelao, R.M.; Del Rosso, C.; Fillmann, G.; Zamboni, A.J. Natural and anthropogenic hydrocarbons inputs to sediments to Patos Lagoon Estuary, Brazil. Environ. Int., 31, 77-87, 2005. [ Links ]
15. Nubel, U.; Engelen, B.; Fleske, A.; Snaidr, J.; Wieshuber, A.; Amann, R.I.; Ludwig, W.; Backhaus, H. Sequence heterogeneities of genes enconding 16S rRNA in Paenibacillus polymyxa detected by temperature gradient gel electrophoresis. J. Bacteriol., 178, 5636-5643, 1996. [ Links ]
16. Orge, M.D.R.; Porsche, I.J.; Costa, M.C.; Lima, J.S.; Soares, S.E.D.; Justino, R. Assessment of oil refinery waste on Rhizophora mangle L. seedling growth in mangroves of Todos os Santos Bay, Bahia, Brazil. Aquat. Ecosys. Health Manag., 3, 471-477, 2000. [ Links ]
17. Paranhos, R.; Ximenez, M.S. Verão negro no litoral carioca. Cienc. Hoje, 27(160), 48-49, 2000. [ Links ]
18. Paranhos, R.; Andrade, L.; Mendonça-Hagler, L.C.; Pfeiffer, W.C. Coupling bacterial abundance with production in a polluted tropical coastal bay. In: Faria, B.M.; Farjalla, V.F.; Esteves, F.A. (eds). Aquatic Microbial Ecology in Brazil. Series Oecologia brasiliensis, vol. IX. PPGE-UFRJ. Rio de Janeiro, Brazil, 2001, p.117-132. [ Links ]
19. Rojas, A.; Holguin, G.; Glick, B.R.; Bashan, Y. Synergism between Phyllobacterium sp. (N2-fixer) and Bacillus licheniformis (P-solubilizer), both from a semiarid mangrove rhizosphere. FEMS Microbiol. Ecol., 35, 181-187, 2001. [ Links ]
20. Tam, N.F.Y.; Ke, L.; Wang, X.H.; Wong, Y.S. Contamination of polycyclic aromatic hydrocarbons in surface sediments of mangrove swamps. Environ. Pollut., 114, 255-263, 2001. [ Links ]
Submitted: January 03, 2005; Approved: June 14, 2006
* Corresponding author. Mailing address: Centro de Ciências da Saúde, Bloco I, Instituto de Microbiologia Prof. Paulo de Góes. Universidade Federal do Rio de Janeiro, Ilha do Fundão, Cidade Universitária. 21949-900, Rio de Janeiro, RJ, Brasil. Tel.: (+5521) 2562-6739 / Fax: (+5521) 2260-8344 E-mail: email@example.com