Estudo da produção de biopolímeros via enzimática através de inativação e lise celular e com células viáveis de Beijerinckia sp. 7070

Biopolímeros microbianos são polissacarídeos produzidos por microrganismos. A Beijerinckia sp. 7070 produz o biopolímero denominado clairana®. Biopolímeros microbianos podem ser produzidos utilizando enzimas purificadas (via enzimática). O objetivo desse trabalho foi avaliar a possibilidade de produzir o biopolímero clairana® via enzimática, verificar se a síntese e as enzimas envolvidas na síntese são intra e/ou extracelulares, se as enzimas permanecem ativas no meio e estudar a produção do biopolímero via enzimática, através de inativação e lise celular, e pelo processo convencional com células viáveis. As amostras foram cultivadas com a bactéria em meio líquido e submetidas à morte celular por inativação e lise celular após 30h, através de antibiótico e ultrasom, respectivamente. Amostras foram retiradas após 32, 46 e 54h de incubação, junto com amostras produzidas com células viáveis. O mesmo procedimento foi realizado em 46h e amostras foram coletadas após 48, 52 e 54h de incubação. Os polímeros foram recuperados, secos, pesados e analisados. Os resultados sugerem que é possível produzir o biopolímero clairanaâ via enzimática e que, provavelmente enzimas intra e extracelulares estão envolvidas, permanecendo ativas no meio e começando a atuar antes de 30h de fermentação. O processo via enzimática através de lise foi mais eficiente pois libera os polissacarídeos produzidos intracelularmente para o meio externo.

Caracterização de biopolímeros produzidos por Beijerinckia sp. 7070 em diferentes tempos de cultivo

Biopolímeros são polissacarídeos microbianos. O biopolímero produzido por Beijerinckia sp. 7070 possui comportamento pseudoplástico e apresenta alta viscosidade em baixas velocidades de deformação, conferindo ao polímero excelentes características de suspensão. O objetivo desse trabalho foi caracterizar o biopolímero produzido por Beijerinckia sp. 7070 em diferentes tempos de cultivo, quanto à produção total, produção de polímeros de fibra longa e curta, produtividade, viscosidade e composição química. Os polímeros produzidos em meio YM líquido foram recuperados em diferentes tempos de cultivo, secos e pesados para determinação da produção e produtividade. O tipo de fibra produzido durante o cultivo foi avaliado microscopicamente. Viscosidades aparentes de solução aquosa 1% foram determinadas a 6, 12, 30 e 60rpm, a 25º C, em um viscosímetro Brookfield. A composição do biopolímero foi determinada por cromatografia em camada delgada comparativa. As maiores produções totais encontradas foram em 30 e 72h, a maior produtividade em 48h e a maior viscosidade em 72h. Os polímeros de fibra longa apresentaram uma tendência de tornarem-se mais longos com o tempo. A viscosidade do polímero de fibra longa foi maior que a do de fibra curta. Todos os biopolímeros apresentaram os mesmos componentes (glucose, galactose, fucose e ácido glucurônico) mas em concentrações diferentes.

Diferencas fisiologicas e morfologicas entre tribus de bacterias do genero Beijerinckia isolados em solos brasileiros.

1956

Bactérias diazotróficas em solos sob seringueira

Diversos relatos evidenciam os benefícios de procariotos fixadores de nitrogênio atmosférico no crescimento e na nutrição de muitas espécies vegetais; entretanto, não há, até o momento, nenhum trabalho visando à prospecção desses microrganismos na rizosfera da seringueira (Hevea brasiliensis). Assim, os objetivos deste trabalho foram verificar a ocorrência de bactérias diazotróficas em solos sob plantio de seringueira, assim como em suas raízes, e isolar e caracterizar essas bactérias. Para essa finalidade, coletaram-se amostras de solo e de raízes finas de seringueiras cultivadas no Campus Experimental da Universidade Federal de Lavras (Lavras, MG) para inoculação em meios de cultura semissólidos sem N na forma combinada, de modo a favorecer o crescimento de algumas espécies de bactérias diazotróficas. Foram obtidos 19 isolados nas amostras de solo, e não houve crescimento de bactérias fixadoras de nitrogênio nas culturas com amostras de raízes. A caracterização celular e das colônias desses isolados indicou que 17 deles produzem grande quantidade de exopolissacarídeo elástico, algumas vezes cartilaginoso. Eles são todos Gram-negativos, com formato celular de bastonete, imóveis e com dois glóbulos de poli-β-hidroxibutirato (PBH), um em cada extremidade do bastonete. O sequenciamento do 16S rDNA e sua análise filogenética confirmaram que isolados representativos desse grupo pertencem ao gênero Beijerinckia (B. indica e B. derxii) e que os outros dois isolados Gram-positivos pertencem ao gênero Bacillus. A presença da nitrogenase - a enzima responsável pela fixação biológica do nitrogênio atmosférico (FBN) - foi confirmada por meio da técnica de redução do acetileno. Conclui-se que, no solo sob plantio de seringueira, houve predominância de diazotróficas de vida livre pertencentes ao gênero Beijerinckia (B. indica e B. derxii), não havendo indícios de bactérias endofiticas ou rizosféricas.

Molecular characterization of the nitrifying bacterial consortia employed for the activation of bioreactors used in brackish and marine aquaculture systems

The addition of commercial nitrifying bacterial products has resulted in significant improvement of nitrification efficiency in recirculating aquaculture systems (RAS). We developed two nitrifying bacterial consortia (NBC) from marine and brackish water as start up cultures for immobilizing commercialized nitrifying bioreactors for RAS. In the present study, the community compositions of the NBC were analyzed by universal 16S rRNA gene and bacterial amoA gene sequencing and fluorescence in situ hybridization (FISH). This study demonstrated that both the consortia involved autotrophic nitrifiers, denitrifiers as well as heterotrophs. Abundant taxa of the brackish water heterotrophic bacterial isolates were Paenibacillus and Beijerinckia spp. whereas in the marine consortia they were Flavobacterium, Cytophaga and Gramella species. The bacterial amoA clones were clustered together with high similarity to Nitrosomonas sp. and uncultured beta Proteobacteria. FISH analysis detected ammonia oxidizers belonging to b subclass of proteobacteria and Nitrosospira sp. in both the consortia, and Nitrosococcus mobilis lineage only in the brackish water consortium and the halophilic Nitrosomonas sp. only in the marine consortium. However, nitrite oxidizers, Nitrobacter sp. and phylum Nitrospira were detected in both the consortia. The metabolites from nitrifiers might have been used by heterotrophs as carbon and energy sources making the consortia a stable biofilm.

Bioremediation of PAHs - Limitations and soultions

Introduction 1.1 Occurrence of polycyclic aromatic hydrocarbons (PAH) in the environment Worldwide industrial and agricultural developments have released a large number of natural and synthetic hazardous compounds into the environment due to careless waste disposal, illegal waste dumping and accidental spills. As a result, there are numerous sites in the world that require cleanup of soils and groundwater. Polycyclic aromatic hydrocarbons (PAHs) are one of the major groups of these contaminants (Da Silva et al., 2003). PAHs constitute a diverse class of organic compounds consisting of two or more aromatic rings with various structural configurations (Prabhu and Phale, 2003). Being a derivative of benzene, PAHs are thermodynamically stable. In addition, these chemicals tend to adhere to particle surfaces, such as soils, because of their low water solubility and strong hydrophobicity, and this results in greater persistence under natural conditions. This persistence coupled with their potential carcinogenicity makes PAHs problematic environmental contaminants (Cerniglia, 1992; Sutherland, 1992). PAHs are widely found in high concentrations at many industrial sites, particularly those associated with petroleum, gas production and wood preserving industries (Wilson and Jones, 1993). 1.2 Remediation technologies Conventional techniques used for the remediation of soil polluted with organic contaminants include excavation of the contaminated soil and disposal to a landfill or capping - containment - of the contaminated areas of a site. These methods have some drawbacks. The first method simply moves the contamination elsewhere and may create significant risks in the excavation, handling and transport of hazardous material. Additionally, it is very difficult and increasingly expensive to find new landfill sites for the final disposal of the material. The cap and containment method is only an interim solution since the contamination remains on site, requiring monitoring and maintenance of the isolation barriers long into the future, with all the associated costs and potential liability. A better approach than these traditional methods is to completely destroy the pollutants, if possible, or transform them into harmless substances. Some technologies that have been used are high-temperature incineration and various types of chemical decomposition (for example, base-catalyzed dechlorination, UV oxidation). However, these methods have significant disadvantages, principally their technological complexity, high cost , and the lack of public acceptance. Bioremediation, on the contrast, is a promising option for the complete removal and destruction of contaminants. 1.3 Bioremediation of PAH contaminated soil & groundwater Bioremediation is the use of living organisms, primarily microorganisms, to degrade or detoxify hazardous wastes into harmless substances such as carbon dioxide, water and cell biomass Most PAHs are biodegradable unter natural conditions (Da Silva et al., 2003; Meysami and Baheri, 2003) and bioremediation for cleanup of PAH wastes has been extensively studied at both laboratory and commercial levels- It has been implemented at a number of contaminated sites, including the cleanup of the Exxon Valdez oil spill in Prince William Sound, Alaska in 1989, the Mega Borg spill off the Texas coast in 1990 and the Burgan Oil Field, Kuwait in 1994 (Purwaningsih, 2002). Different strategies for PAH bioremediation, such as in situ , ex situ or on site bioremediation were developed in recent years. In situ bioremediation is a technique that is applied to soil and groundwater at the site without removing the contaminated soil or groundwater, based on the provision of optimum conditions for microbiological contaminant breakdown.. Ex situ bioremediation of PAHs, on the other hand, is a technique applied to soil and groundwater which has been removed from the site via excavation (soil) or pumping (water). Hazardous contaminants are converted in controlled bioreactors into harmless compounds in an efficient manner. 1.4 Bioavailability of PAH in the subsurface Frequently, PAH contamination in the environment is occurs as contaminants that are sorbed onto soilparticles rather than in phase (NAPL, non aqueous phase liquids). It is known that the biodegradation rate of most PAHs sorbed onto soil is far lower than rates measured in solution cultures of microorganisms with pure solid pollutants (Alexander and Scow, 1989; Hamaker, 1972). It is generally believed that only that fraction of PAHs dissolved in the solution can be metabolized by microorganisms in soil. The amount of contaminant that can be readily taken up and degraded by microorganisms is defined as bioavailability (Bosma et al., 1997; Maier, 2000). Two phenomena have been suggested to cause the low bioavailability of PAHs in soil (Danielsson, 2000). The first one is strong adsorption of the contaminants to the soil constituents which then leads to very slow release rates of contaminants to the aqueous phase. Sorption is often well correlated with soil organic matter content (Means, 1980) and significantly reduces biodegradation (Manilal and Alexander, 1991). The second phenomenon is slow mass transfer of pollutants, such as pore diffusion in the soil aggregates or diffusion in the organic matter in the soil. The complex set of these physical, chemical and biological processes is schematically illustrated in Figure 1. As shown in Figure 1, biodegradation processes are taking place in the soil solution while diffusion processes occur in the narrow pores in and between soil aggregates (Danielsson, 2000). Seemingly contradictory studies can be found in the literature that indicate the rate and final extent of metabolism may be either lower or higher for sorbed PAHs by soil than those for pure PAHs (Van Loosdrecht et al., 1990). These contrasting results demonstrate that the bioavailability of organic contaminants sorbed onto soil is far from being well understood. Besides bioavailability, there are several other factors influencing the rate and extent of biodegradation of PAHs in soil including microbial population characteristics, physical and chemical properties of PAHs and environmental factors (temperature, moisture, pH, degree of contamination). Figure 1: Schematic diagram showing possible rate-limiting processes during bioremediation of hydrophobic organic contaminants in a contaminated soil-water system (not to scale) (Danielsson, 2000). 1.5 Increasing the bioavailability of PAH in soil Attempts to improve the biodegradation of PAHs in soil by increasing their bioavailability include the use of surfactants , solvents or solubility enhancers.. However, introduction of synthetic surfactant may result in the addition of one more pollutant. (Wang and Brusseau, 1993).A study conducted by Mulder et al. showed that the introduction of hydropropyl-ß-cyclodextrin (HPCD), a well-known PAH solubility enhancer, significantly increased the solubilization of PAHs although it did not improve the biodegradation rate of PAHs (Mulder et al., 1998), indicating that further research is required in order to develop a feasible and efficient remediation method. Enhancing the extent of PAHs mass transfer from the soil phase to the liquid might prove an efficient and environmentally low-risk alternative way of addressing the problem of slow PAH biodegradation in soil.