Degradability of the three dimethyl phthalate isomer esters (DMPEs) by a Fusarium species isolated from mangrove sediment.
Degradability of the three dimethyl phthalate isomer esters (DMPEs) by a Fusarium species isolated from mangrove sediment.
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DOI：
10.1016/j.marpolbul.2009.03.005
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发表时间：
2009-05
影响因子：
5.8
通讯作者：
Zhuhua Luo;K. Pang;J. Gu;R. Chow;L. Vrijmoed
中科院分区：
文献类型：
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作者：
Zhuhua Luo;K. Pang;J. Gu;R. Chow;L. Vrijmoed
邻苯二甲酸二甲酯（DMPEs）是常用的增塑剂和添加剂，可提高塑料制品的柔韧性和柔软度（Cartwright et al., 2000; Wang et al., 2004; Xu et al., 2005）。三种二苯乙烯异构体，即邻苯二甲酸二甲酯(邻苯二甲酸二甲酯；两个羧基的邻苯二甲酸二甲酯（间-）和对苯二甲酸二甲酯（对-），具有不同的物理和化学性质，并用于不同的工业用途。DMP被用作纤维素酯基塑料的增塑剂（醋酸纤维素和丁酸纤维素；Staples等，1997年）。在以聚酯为基础的产品中，如录像机盒式磁带、合成纺织纤维等，DMI和DMT被用作合成的中间体（Lee et al., 1999; Wang and Gu, 2006a, b）。邻苯二甲酸酯（PAEs）普遍存在于水生和陆地环境中（Gu et al., 2005）以及食品中（Petersen and Breindahl, 2000）。由于PAEs不与树脂共价结合，从塑料材料中滤出和迁移到环境中是与这些化学品相关的潜在健康问题的主要关切。PAEs在极低浓度下可作为内分泌干扰物，影响人类和动物生殖系统的正常功能和发育（Jobling et al., 1995; Colón et al., 2000; Gu et al., 2005; Xu et al., 2005）。因此，包括DMP在内的六种PAEs被美国环境保护局列为优先污染物（Gu et al., 2005）。研究表明，环境中PAEs的完全降解是通过微生物矿化（Staples等人，1997；Gu等人，2005）。PAEs的降解已经在细菌中得到了充分的证明。已从活性污泥、红树林、土壤、河流和海洋环境中分离出多种pae降解细菌（Vega和Bastide, 2003； Chang等，2004；Gu等，2005；Li等，2005 5a, b； Xu等，2005；Wang和Gu 2006a， b； Fang等，2007）。革兰氏阳性菌和革兰氏阴性菌都通过不同的途径参与邻苯二甲酸（PA）的有氧降解（Chang and Zylstra, 1998; Stingley et al., 2004）。几个参与PA代谢的功能操纵子已经在keyseri节杆菌12B、vanbaaleni分枝杆菌PYR-1、伯克霍尔德氏菌DBO1等菌株中被鉴定和表征（Chang and Zylstra, 1998; Eaton, 2001; Stingley et al., 2004）。然而，真菌对PAEs的降解很少被发现。真菌已被证明是多种顽固性化合物的潜在降解者，包括多环芳烃（PAHs）、苯-甲苯-乙苯-二甲苯（BTEX）、氯酚、多氯联苯、弹药废物和农药（Tortella等，2005年）。然而，真菌对PAEs的降解仅在有限程度上研究了黑曲霉和罗氏菌核菌（Sivamurthy等人，1991；Ganji等人，1995；Pradeepkumar等人，2000）。真菌对PAEs的环境命运的作用在很大程度上仍然未知。沿海湿地，如红树林，通常是水生系统污染物的汇（Tam et al., 2001; Ke et al., 2005）。红树林微生物可能在水生环境中有机污染物的命运中发挥重要作用。从红树林沉积物中分离出了许多能够降解PAEs的细菌，如荧光假单胞菌、橡胶红球菌、多杀性帕斯德菌和少动藻单胞菌（Li et al., 2005; Xu et al., 2005; Li and Gu, 2006）。然而，没有关于红树林真菌降解PAEs的报道。
Dimethyl phthalate esters (DMPEs) are common plasticizers and additives to improve flexibility and softness of plastic products (Cartwright et al., 2000; Wang et al., 2004; Xu et al., 2005). Three DMPE-isomers, namely dimethyl phthalate (ortho-DMP; ortho-arrangement of the two carboxyl groups), dimethyl isophthalate (DMI; meta-) and dimethyl terephthalate (DMT; para-), display different physical and chemical properties and are used in different industrial applications. DMP is used as a plasticizer in cellulose ester-based plastics (cellulose acetate and cellulose butyrate; Staples et al., 1997). In polyester-based products, such as tape for VCR cassettes, synthetic textile fibers etc., DMI and DMT are used as intermediates for their synthesis (Lee et al., 1999; Wang and Gu, 2006a, b). Phthalate esters (PAEs) occur ubiquitously in both aquatic and terrestrial environments (Gu et al., 2005), and foods (Petersen and Breindahl, 2000). Because they do not bond covalently with the resin, leaching and migration of PAEs from plastic materials into the environment are of major concern for the potential health problems associated with these chemicals. PAEs may act as endocrine disruptors affecting the normal function of the reproductive system and development of humans and animals at very low concentrations (Jobling et al., 1995; Colón et al., 2000; Gu et al., 2005; Xu et al., 2005). As a result, six PAEs including DMP are listed as priority pollutants by the United States Environmental Protection Agency (Gu et al., 2005). It is suggested that complete degradation of PAEs in the environment is via microbial mineralization (Staples et al., 1997; Gu et al., 2005). Degradation of PAEs has been well documented in bacteria. Various PAE-degrading bacteria have been isolated from activated sludge, mangroves, soils, rivers, and the marine environment (Vega and Bastide, 2003; Chang et al., 2004; Gu et al., 2005; Li et al., 2005a, b; Xu et al., 2005; Wang and Gu 2006a, b; Fang et al., 2007). Both Gram-positive and Gram-negative bacteria are responsible for the aerobic degradation of phthalic acid (PA) via different pathways (Chang and Zylstra, 1998; Stingley et al., 2004). Several functional operons involved in the metabolism of PA have been identified and characterized in Arthrobacter keyseri 12B, Mycobacterium vanbaalenii PYR-1, Burkholderia cepacia DBO1 and other bacterial strains (Chang and Zylstra, 1998; Eaton, 2001; Stingley et al., 2004). However, degradation of PAEs by fungi has rarely been shown. Fungi have been demonstrated to be potential degraders of a wide range of recalcitrant compounds, including polycyclic aromatic hydrocarbons (PAHs), benzene–toluene–ethylbenzene–xylenes (BTEX), chlorophenols, polychlorinated biphenyl, munitions waste, and pesticides (Tortella et al., 2005). Nevertheless, degradation of PAEs by fungi has been studied only to a limited extent with Aspergillus niger and Sclerotium rolfsii (Sivamurthy et al., 1991; Ganji et al., 1995; Pradeepkumar et al., 2000). The role of fungi on the environmental fate of PAEs remains largely unknown. Coastal wetlands, such as mangroves, are usually sinks of pollutants from the aquatic system (Tam et al., 2001; Ke et al., 2005). Mangrove microorganisms may play an important role in the fate of organic pollutants in aquatic environments. A number of bacterial species capable of degrading PAEs have been isolated from mangrove sediments, such as Pseudomonas fluorescens, Rhodococcus ruber, Pasturella multocida, and Sphingomonas paucimobilis (Li et al., 2005a, b; Xu et al., 2005; Li and Gu, 2006). However, there are no reports concerned with the degradation of PAEs by mangrove fungi …