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Team:Bielefeld-Germany/Project/Background/BPA
From 2011.igem.org
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Bisphenol A
The organic compound bisphenol A (abbreviated BPA) is a key monomer in the production of polycarbonate plastics and epoxy resins. Polycarbonate is clear, heat stable and nearly shatter-proof and therefore used in a lot of common products like baby and water bottles, electronics, CDs and DVDs or eyeglass lenses. Epoxy resins are used as coatings on the inside of almost all food and beverage cans. Unpolymerized BPA monomers are leaking in small doses into aqueous solutions from BPA containing plastics leading to a daily exposure to BPA. Due to safety concerns, BPA is forbidden in the production of baby bottles in the European Union and in Canada.
Bisphenol A and its effects on mammals
The exposure of BPA to heat under acidic or basic conditions causes the ester-bonds of its monomers to hydrolyse. Subsequently, the BPA is released and may therefore be absorbed by humans or eventually contaminate the environment ([1]). The exposure to already low doses of BPA during development has persistent effects([2]). Bisphenol A accounts as endocrine disruptor, because it mimics the natural hormone estrogen and may thus induce negative health effects. It can bind to in vivo and in vitro estrogen receptors (ER) which lead to alteration in several levels of tissues and cells. The consequences are changes in estrogen-targeted cells like brain, mammary gland and others. In addition, BPA acts on non-classical targets like bone, cardiovascular tissue, pancreas, adipose tissue and the immune system ([3]). There is also evidence indicating an anti-tyroid hormone effect ([4]). A study of the urine concentration of BPA shows a significant relationship to cardiovascular disease, type 2 diabetes, and liver-enzyme abnormalities in adults (Lang,2008). Another estrogenic effect of BPA is the disruption of pancreas ß-cells, resulting in an insulin resistance. Furthermore, it leads to an increase in glucose transporter GLUT4 and so to glucose uptake into cells ([5]). BPA has also an effect on the immune system, which is dependent on the timing of exposure, because the estrogen receptor that is expressed by a lymphocyte is dependent upon age and gender ([6]). Moreover, studies show evidence that points to an effect on male and female reproductive tracts. In males it has an impact on the sperm production, the testosterone secretion and on reproductive structures (e.g. the prostate). These consequences are already found under admission of low BPA doses. So the effect on the adult male reproductive tract has adverse consequences for the testicular function. In the long run, this can lead to infertility. In case of females, alterations in the development of the mammary glands and their structure could be observed, which might be a reason for developing cancer ([7]).
Bisphenol A degradation
There exist a lot of bacteria in nature that can degrade xenobiotic substances such as phenolic compounds or endocrine disruptors. In a lot of soil samples that were taken from contaminated soil to find organisms that degrade these substances, sphingomonads were extraordinarily often isolated (Stolz, 2009). In 2005, Sasaki et al. isolated a soil bacterium from the Sphingomonas genus which is able to degrade the endocrine disruptor bisphenol A (BPA) with a unique rate and efficiency compared to other BPA degrading organisms. This strain, called Sphingomonas bisphenolicum AO1, is able to completely decompose 120 mg BPA L-1 in about 6 hours while other strains need days of cultivation (e.g. Sphingomonas strain BP-7 isolated by Sakai et al. (2007)).
The full bisphenol A degradation pathway which is found in nature is shown in figure 1 (taken from KEGG database). BPA is metabolized to 4-Hydroxybenzaldehyde, 4'-Hydroxyacetophenone and 4-Hydroxybenzoate which can be used by some bacteria as carbon source. These and other metabolites of the BPA degradation pathway can be found in the supernatant of BPA containing cultivations of S. bisphenolicum AO1. They can grow on BPA as the only carbon source, too (Sasaki et al., 2005a).
Bisphenol A is mainly hydroxylated into the products 1,2-Bis(4-hydroxyphenyl)-2-propanol and 2,2-Bis(4-hydroxyphenyl)-1-propanol by some kind of oxidoreductase acting with NADH or NADPH. In S. bisphenolicum AO1, a total of three genes were identified that are responsible for this BPA hydroxylation: a cytochrome P450 (CYP, bisdB), a ferredoxin (Fd, bisdA) and a ferredoxin-NAD+ oxidoreductase (FNR) (Sasaki et al., 2005b). Common class I electron transport systems for bacterial cytochrome P450 consist of these three enzymes mentioned above, mostly using a ferredoxin with [2Fe-2S] iron-sulfur cluster (Hannemann et al., 2007). In addition, class V electron transport systems were found in bacteria, composed of a ferredoxin-cytochrome P450 fusion protein and a NAD(P)H-ferredoxin oxidoreductase. In these systems, the ferredoxin is fused to the N-terminus of the cytochrome P450 via a linker region (Hannemann et al., 2007). The three proteins mentioned above were isolated separately from S. bisphenolicum AO1 (Sasaki et al., 2005), so the CYPbisd electron transport system is a bacterial class I system.
The three gene products responsible for hydroxylating BPA act together to reduce BPA while oxidizing NADH + H+. The cytochrome P450 (BisdB) reduces the BPA and is oxidized during this reaction. BisdB in its oxidized status is reduced by the ferredoxin (BisdA) so it can reduce BPA again. The oxidized BisdA is reduced by a ferredoxin-NAD+ oxidoreductase consuming NADH + H+ so the BPA degradation can continue (Sasaki et al., 2005b). The bisdAB genes from S. bisphenolicum AO1 were isolated, transformed into and expressed in E. coli and enabled this bacterium to degrade BPA, too (Sasaki et al., 2008). In addition, the BisdAB proteins from S. bisphenolicum AO1 were able to degrade BPA in a cell-free system (enzyme assay) in which spinach reductase (EC 1.18.1.2) was added (Sasaki et al., 2005b).
In 2008, the iGEM team from the University of Alberta submitted the bisdAB genes from S. bisphenolicum AO1 to the registry of standard biological parts in the so called Freiburg BioBrick assembly standard (<partinfo>K123000</partinfo> and <partinfo>K123001</partinfo>). In order to degrade BPA in a cell-free system, a FNR BioBrick is also needed. As demonstrated, the BisdA and BisdB work together in a cell-free system with spinach reductase and they work intracellular in E. coli, it can be assumed that it is possible to produce all components necessary to degrade BPA in a cell free system in E. coli. To achieve this a ferredoxin-NADP+ oxidoreductase BioBrick, isolated from E. coli, is provided by the Bielefeld-Germany 2011 iGEM team (<partinfo>K525499</partinfo>).
The whole electron transport chain between the three enzymes involved in BPA degradation and the BioBricks needed to enable this reaction in vivo and in vitro are shown in the following figure (please have some patience, it's an animated .gif file):
Further applications of bisphenol A degrading BioBricks and enzymes
Beside the use in a biosensor, BPA degrading BioBricks could mainly be used in bioremediation approaches in BPA contaminated water or soil. If it was possible to determine and isolate the genes which are responsible for the complete degradation of BPA to substrates that can be used by bacteria as a carbon source, it would enable the bacterium carrying these BioBricks to grow on BPA. This device under the control of a BPA inducible promoter, transformed into bacteria living in a BPA contaminated environment, would be a selective advance making other selection markers such as antibiotic resistance unnecessary. For bioremediation approaches this would be an interesting advance because genes for antibiotic resistances are not released in the environment which could potentially be passed to other bacteria via bacterial conjugation. The release of antibiotic resistance genes always has the danger that these genes find a way into pathogenic bacteria strains creating multi-drug-resistant pathogens. A device which enabled bacteria to grow on BPA as the only carbon source would not present this risk in bacterial-based bioremediation approaches and therefore enhances the biosecurity of such approaches.
References
Lang IA, Galloway TS, Scarlett A, Henley WE, Depledge M, Wallace RB, Melzer D (2008) Association of Urinary Bisphenol A Concentration With Medical Disorders and Laboratory Abnormalities in Adults JAMA,Vol 300, No. 11.
Vandenberg LN, Maffini MV, Sonnenschein C, Rubin BS, Soto AM (2009) Bisphenol-A and the Great Divide: A Review of Controversies in the Field of Endocrine Disruption Endocrine Reviews 30(1):75–95.
Richter CA, Birnbaum LS, Farabollini F, Newbold RR, Rubin BS, Talsness CE, Vandenbergh JG, Walser-Kuntz DR, vom Saal FS (2007) In Vivo Effects of Bisphenol A in Laboratory Rodent Studies Reprod Toxicol. 24(2): 199–224.
Hannemann F, Bichet A, Ewen KM, Bernhardt R (2007) Cytochrome P450 systems—biological variations of electron transport chains, Biochimica et Biophysica Acta (BBA) - General Subjects 1770(3):330-344.
Sakai K, Yamanaka H, Moriyoshi K, Ohmoto T, Ohe T (2007) Biodegradation of Bisphenol A and Related Compounds by Sphingomonas sp. Strain BP-7 Isolated from Seawater, Bioscience, Biotechnology, and Biochemistry 71(1):51-57.
Sasaki M, Maki J, Oshiman K, Matsumura Y, Tsuchido T (2005a) Biodegradation of bisphenol A by cells and cell lysate from Sphingomonas sp. strain AO1, Biodegradation 16(5):449-459.
Sasaki M, Akahira A, Oshiman K, Tsuchido T, Matsumura Y (2005b) Purification of Cytochrome P450 and Ferredoxin, Involved in Bisphenol A Degradation, from Sphingomonas sp. Strain AO1, Appl Environ Microbiol 71(12):8024-8030.
Sasaki M, Tsuchido T, Matsumura Y (2008) Molecular cloning and characterization of cytochrome P450 and ferredoxin genes involved in bisphenol A degradation in Sphingomonas bisphenolicum strain AO1, J Appl Microbiol 105(4):1158-1169.
Stolz A (2009) Molecular characteristics of xenobiotic-degrading sphingomonads, Appl Microbiol Biotechnol 81:793-811.
