Research progress of antibiotic resistance genes in wastewater treatment plants
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摘要:
抗生素抗性基因（ARGs）是一类对自然环境及人体健康造成极大威胁的新型污染物，城市污水处理厂是ARGs的重要源和汇，具有重大潜在生态风险。系统梳理了污水处理过程中不同类型ARGs的组成变化特征和转移机制，提出β-内酰胺类、大环内酯类、四环素类、磺胺类、氨基糖苷类等类型ARGs广泛存在于全球污水处理厂中，但不同类型ARGs的丰度随污水处理过程的变化特征各异，且不同处理单元中的高丰度ARGs存在差异，水平转移是ARGs的主要转移机制。总结了环境条件、进水水质、操作参数等常见因素对ARGs丰度和分布的影响。在此基础上提出，识别具有指示作用的ARGs及其关键影响因素，定量分析各类因素对ARGs丰度、种类及水平转移机制的影响，以及建立ARGs风险评价标准体系是城市污水处理厂监测与控制ARGs潜在生态风险的未来发展方向。
Abstract:Antibiotic resistance genes (ARGs) are emerging contaminants which pose a great threat to the environment and human health. As an important source and sink of ARGs, wastewater treatment plants (WWTPs) have great potential ecological risks. Therefore, the diversity, composition as well as transfer mechanism of ARGs in the wastewater treatment processes were systematically introduced. ARGs of beta-lactam, macrolide, tetracycline, sulfonamide and aminoglycoside were widely detected in global WWTPs. However, the abundance of different types of ARGs along treatment processes and dominant ARGs detected in each process were different. Horizontal transfer was the main transfer mechanism of ARGs. The effects of common factors such as environmental conditions, influent wastewater quality and operational parameters on the abundance and distribution of ARGs were also summarized. It was proposed that the focus of future research was identifying the representative ARGs and the most influencing factors, quantifying the effects of various factors on the abundance, compositions and horizontal transfer mechanisms of ARGs, and establishing a standard system for evaluating the risks of ARGs for monitoring and controlling the potential ecological risks of ARGs in WWTPs.
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图 1 2006—2021年国内外有关污水处理厂ARGs的发文统计
Figure 1. Statistical charts of publications on ARGs in WWTPs at home and abroad from 2006 to 2021
图 2 污水处理厂中ARGs沿程变化模式
注：图中ARGs的个数对应大致丰度。
Figure 2. Conceptual map of ARGs changes along the process in a WWTP
表 1 不同地区污水处理厂中不同种类ARGs在进水、出水、污泥中的丰度变化
Table 1. Variations of abundance of different kinds of ARGs in influent, effluent and sludge in various WWTPs
抗性
基因
种类所在地区 抗性基因
亚型名称进水中丰度/
(拷贝/L)出水中丰度/
(拷贝/L)污泥中丰度/
(拷贝/g)去除
效果
(lg C)1）处理工艺 β-内酰胺类 中国北京[20] bl2d_oxa10、bl3_imp等51种 1.25×1010 4.73×107 1.47×1010 2.42 MBR工艺 美国加利福尼
亚州[21]blaM-1 2.23×108 2.82×106 1.9 活性污泥法+氯消毒 中国河北[22] blaPSE-1 106 2.46×104 107 2.64 A2/O工艺+氯消毒 美国马萨
诸塞州[21]blaTEM-uni 1.41×109 4.73×108 0.47 活性污泥法+氯消毒 瑞典哥德堡[20] mecA 5.01×104 5.01×103 1 活性污泥法+生物滤池 大环内酯类 中国北京[20] ermF、Inua等46种 1.17×1010 1.89×107 0.75×1010 2.79 MBR工艺 中国华北[23] erm 2种 (7.0±12)×107 (1.2±0.9)×1010 活性污泥法+氯消毒 中国河北[23] ermB 3×108 5.30×105 4×108 2.77 A2/O工艺+氯消毒 以色列夏夫丹[21] ermB 3.02×1010 2×105~3.02×107 3~4 活性污泥法 ermF 6.02×1010 3.02×106~2×108 2~4 四环素类 中国北京[20] tetG、tetM等
39 种1.39×1010 5.14×107 2.5×1010 2.43 MBR工艺 中国华北[22] tet 15种 (8.4±2.4)×107 (1.3±1.6)×1010 活性污泥法+氯消毒 中国香港[21] tetA 1010.78~1011.2 ND~107.33 3~4 活性污泥法+氯消毒 tetC 1011.13~1011.3 ND~107.12 4~5 中国南京[21] tetA 5.01×1010 1.41×109 1.55 活性污泥法 tetC 8.13×1010 1.38×109 1.77 中国河北[23] tetC 8×108 4. 13×106 2.23 A2/O工艺+氯消毒 美国威斯
康星州[21]tetG 109.4~1010.8 107.2~108.9 1~4 活性污泥法+紫外/氯消毒 tetQ 1010.2~1012 106.9~109.2 1~6 中国合肥[24] tetQ 2.03×1011 2×107 1.11×1010 4.01 SBR工艺+氯消毒 以色列夏夫丹[21] tetO 2×1010 ND~106 4.3 活性污泥法 美国密歇根州[25] tetO 5.13×109 9.12×106 1.78×109 2.75 活性污泥法+氯消毒 tetW 5.13×109 5.13×106 5.62×108 3 中国合肥[24] tetO 2×109 106 2×109 3.3 SBR+氯消毒 tetW 2×109 2×106 2×109 3 磺胺类 中国北京[20] dfrA1等7种 2.8×109 4.3×107 2.5×1010 1.81 MBR 中国浙江[26] dfrA1 1.3×107 2×105 9.38 ×105 1.9 A2/O dfrA13 8×106 1.2×105 5.93×104 1.8 中国华北[22] sul 3种 (6.7±7.2)×108 (2.2±2.8)×1011 活性污泥法+氯消毒 美国密歇根州[25] sul1 1.82×109 1.05×107 1.00×108 2.24 活性污泥法+氯消毒 美国密歇根州[21] sul1 108.46~1010.54 107.37~109.75 1~3 活性污泥法/氧化沟/生物转盘/MBR+紫外/氯消毒 中国合肥[24] sul1 3.88×1010 1.5×107 9.06×1010 3.41 SBR+氯消毒 sul2 3×109 4×106 109 2.88 以色列夏夫丹[21] sul1 1011 107.78~108.48 3~4 活性污泥法 sul2 1011 106.48~107.88 3~5 中国河北[22] sul2 2×108 5. 58×106 1010 1.7 A2/O+氯消毒 氨基糖苷类 中国北京[20] ant2ia、ant3ia等35种 3.26×1010 2.06×108 4.38×1010 2.2 MBR 氟喹诺酮-喹诺酮-氟苯尼考-氯霉素和安非霉素类 中国北京[20] cml_e3、catb3等9种 3.26×1010 0.84×107 1.67×1010 3.59 MBR 中国浙江[26] floR 1.2×107 2.1×105 1.59 × 105 1.8 A2/O 中国华北[22] qnr 3种 (7.3±9.6)×106 (1.5±2.3)×109 活性污泥法+氯消毒 多药类 中国北京[20] qacEdelta1、qacH等51种 1.39×1010 1.5×108 3.75×1010 1.97 MBR 中国哈尔滨[27] mexF 7.09×107 3×106 1.37 A/O 万古霉素类 比利时托里勒[21] vanA ND ND 活性污泥法+膜滤 中国哈尔滨[27] vanCO3 3.50×105 ND 5.54 A/O vanXD 1.08×104 4×103 0.43 1）C为丰度。注：ND表示未检出。 
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表 2 污水处理厂中ARGs分布和转移的主要影响因素
Table 2. Main influencing factors of ARGs distribution and transfer in WWTPs
影响因素 对ARGs的影响 文献来源 抗生素 磺胺类药物与sul1、四环素与tetX具有强相关性 [47-48] 选择作用具有交叉性，氯霉素与氨基糖苷类ARGs共现 [8,49] 氨苄青霉素造成大肠杆菌内多种非β-内酰胺类ARGs共现 [50] 高浓度的环丙沙星未造成特定耐药基因的富集，或存在滞后性与共选择 [51-52] 杀菌抗生素对ARGs的富集效果比抑菌抗生素更强 [53] 不同浓度的四环素影响ARGs的HGT [54] 重金属 水中抗生素抗性检出频率随重金属暴露浓度的升高而升高 [55] ARGs的丰度与钒等重金属浓度的相关性强于抗生素，湖泊重金属污染增强了细菌的耐药性 [60] 部分HMRGs与intI1基因具有相关性，影响ARGs的HGT [62] 其他有机物 甲苯、乙苯、PNP、PAP等芳香族化合物浓度影响ARGs [63] 苯乙烯、孔雀绿染料等能提升RP4质粒的转移效率 [60] 卡马西平等有机物通过增加活性氧（ROS）等机制促进ARGs的HGT [57] 纳米颗粒可能促进ARGs的富集传播，抑或去除ARGs [64-65] 微塑料促进污水处理厂中ARGs的富集与传播 [66-67] 微塑料对eARGs的吸附作用及促进HGT作用强于iARGs [68] 微塑料对二沉池出水ARGs的富集能力显著高于进水与污泥 [69] 环境因素及
水质条件温度与污水处理厂ARGs丰度显著相关，其中与bla、mcr丰度成反比，与ermB、sul2丰度成正比 [70-73] 温度影响ARGs的转移，夏季有利于VGT，冬季有利于HGT [28] 氨氮浓度与tetC、ermB等ARGs丰度呈正相关 [23] 高COD促进耐药菌繁殖，提高转化几率 [74] 盐度增加到1%以上会大大降低ARGs的总体丰度 [75] 操作参数及
处理工艺ARGs丰度与HRT呈正相关，与MLSS浓度、DO浓度、SRT呈负相关 [18] 高MLSS浓度、长SRT、低污泥负荷可降低ARGs丰度和多样性 [26,66-67,76] 厌氧与好氧工艺对ARGs影响较大 [77] 膜滤、电化学消毒、微生物燃料电池能显著降低ARGs [53,78-79] 氯消毒等后续处理对ARGs去除效果不一 [25,81-83] 氯及UV消毒会促进宿主繁殖，导致eARGs增多 [80] UV与氯消毒联用比单独氯消毒工艺效果好 [84] UV-AOPs自由基能够极大去除ARGs [86] AOPs中Fenton有关技术对ARGs去除效果优于生物处理及其他AOPs [85,87] 需调节改进工艺以保证ARB与ARGs的去除效果 [88-89]
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