“微塑料(MPs)”是指＜5 mm 的微型塑料碎片[1],20 世纪70—80年代已有科学家关注塑料碎屑在环境中的变化及其对环境的影响[2],但直到2004年题为“Lost at sea: Where is all the plastic?”的文章[3]在Science 杂志上发表后微塑料才开始引起科学家们的广泛关注。 之前的报告指出,全球塑料垃圾产生量和处置量呈指数增长趋势[4]。 有文献统计发现,目前全球主要的淡水生态系统均受到不同程度的微塑料污染,微塑料浓度为100 ~3 500个·L-1[5]。 另有研究估算,每年大约有200 万 t 不同来源的微塑料纤维被释放到海洋中[6]。 塑料污染已成为一个全球性问题,特别是对全球水环境的污染及水生生物多样性的影响[7]。 有学者通过文献计量学综述了全球微塑料的研究情况,发现MPs 与freshwater(淡水)、marine debris(海洋碎片)、fish(鱼)都存在大量共现关系(co-occurrence)[8],说明越来越多的研究关注微塑料与鱼类的相互关系。
鱼类作为水生生态系统的重要组成部分,对生态系统稳定具有重要意义。 同时,鱼类为人类提供大量蛋白质,特别是海洋鱼类,它们为世界上2/3 的人口提供了40%的蛋白质[9]。 历史数据显示,自20世纪70—80年代,随着捕捞技术的进步、捕捞强度的增大,海洋渔业资源开始衰退[10]。 有学者通过计算渔业捕捞的主要鱼种的营养级变化,在印度[11]与巴西[12]都发现自20 世纪70—80年代以来,主要鱼获的营养级呈下降趋势,这表明,高营养级鱼类无法通过自然补充满足人类对鱼类的需求,低营养级鱼种面临逐渐增加的捕捞压力。 微塑料具有持久性、疏水性等特点,且大小与各种浮游生物相似,很容易被滤食性水生生物误食,这增加了微塑料在食物网中积累及营养转移的潜在风险[13]。 已有大量研究关注水生生物与微塑料之间的相互关系,而且越来越多的证据表明微塑料可能对暴露的生命体产生重大的健康影响[14]。 有研究通过微塑料为主的关键检索词在Google Scholar 数据库中进行检索,发现47%的文章是关于微塑料对生物的影响[15]。 就鱼类而言,它们既可以直接摄入水中的微塑料也可以通过捕食其他生物获得微塑料,因此鱼类面临很大的暴露风险。 目前以微塑料及鱼类为研究内容开展的研究有很多,我们基于Web of Science 核心数据库,利用布尔运算符“TS=Microplastic and TS=fish”检索后,统计全球以微塑料及鱼类为研究对象的主要国家,发现目前在全球范围内,不同国家对微塑料与鱼类相互关系的关注度差别很大,研究内容主要集中在野外调查鱼类摄取微塑料的情况和微塑料对鱼类的影响,特别是微塑料对鱼类的毒性效应。 目前,关于微塑料对鱼类产生毒性效应的文献有很多,目前的研究大致可以概括为:研究人员使用不同特征(类型、大小、形状、浓度)的微塑料,采用不同暴露途径(食物相、水相),开展了不同暴露时间(短期/急性、长期/慢性)、不同暴露形式(单一暴露、联合暴露)的多项研究。 这些研究主要关注了微塑料对鱼类的生理活动(生殖、免疫、生长、代谢、行为等)、组织器官(肝脏、肠道、鳃等)的影响及鱼体中微塑料的归趋(排泄、转移、传递)等。 由于相关研究中涉及的要素很多,因此缺乏关于微塑料对鱼类影响的全面概述。
虽然已有文献分别综述了淡水、海洋中鱼类对微塑料摄取情况[16-17],但关于全球水生生态系统中鱼类受到微塑料污染现状的全面概括尚未见报道。综上,本文基于Web of Science 文摘数据库,利用Endnote 文献管理软件及BibExcel 文献计量学分析软件,就微塑料与鱼类之间的几个主要方面进行概述,主要从鱼类受到微塑料污染现状、微塑料对鱼类产生毒性效应的相关要素(暴露方式、微塑料特征、鱼类的生理变化、受影响的器官和微塑料的归趋)、存在的问题与展望等进行了概述。
1 鱼类受到的微塑料污染现状(Contamination posed by MPs on fish)
本研究基于Web of Science 中的核心合集数据库以布尔运算符“TS=Microplastic and TS=Fish”检索文献后将其导入EndNote 软件中,利用EndNote智能分组功能筛选标题中含有“distribution”或“occurrence”或“present”或“ingest”或“uptake”不包含“shellfish”的文章,然后查找文章中研究区域的地理位置(坐标),将研究区域按国家、地区和海域归类统计研究频次。 使用ArcGIS 软件展示全球水生生态系统中鱼类受到微塑料污染情况及其被关注度(图1)。
如图1 所示,研究海洋鱼类最多的地区是地中海及其沿岸,其次是大西洋及其沿岸、里海及其沿岸、中国海域及近海岸。 研究淡水生态系统中鱼类受到微塑料污染的主要地区是非洲、中国、美国和印度。 在全球尺度上,鱼类受到的微塑料污染情况存在地域差异。 与海洋环境相比,微塑料在淡水鱼类中的研究相对较少。 而海洋中的大部分塑料都是先进入淡水环境后通过河流进入海洋,因此关于微塑料对淡水环境中鱼类影响的研究有待加强。 就目前的研究情况来看,对淡水微塑料的研究主要集中在发达国家,在发展中国家的研究较少。 由于在多数发展中国家的国内生产总值(GDP)中渔业占很大比重,这些国家的淡水河流受塑料污染最严重[18]。 除受污染的分布区域外,受污染的个体比例与微塑料在鱼体内富集程度也是反映鱼类受污染情况的重要指标。 由于环境中的微塑料污染存在动态变化,为展示不同研究区域的最新数据。 将图1 中各研究区域的相关文章按发表时间排序,选择近5年(2016—2020年)调查数据,筛选出样本量30 及以上的文章,以这些文章的数据分析相应区域鱼类受到的微塑料污染现状。 表1 汇总了不同区域鱼类体内检测到的微塑料的相关信息。 如表1 所示,不同研究区域鱼类受污染个体的比例(1.68% ~100%)存在一定差异,但所有调查区域的鱼类均受到不同程度的微塑料污染,其中,中国沿海的鱼类受到微塑料污染的个体比例(96.9% ~100%)比全球其他区域更高。 之前有文献综述也得到类似结果[19],该文献基于全球鱼类调查数据分析了鱼类受污染比例(图2)。 在所有调查区域中,大部分地区50%及以上的鱼类受到微塑料污染,只有欧洲北部和一些深海海域的鱼类受污染较轻。 如表1 所示,不同区域鱼类个体检测到的微塑料的富集浓度范围为每个个体0 ~247个。其中,在中国珠江流域的罗非鱼肠道内检测到了高达每个个体247个的个体富集浓度。 另外,鱼体内检测到最多的微塑料种类为聚乙烯(PE),最常见的微塑料形态为纤维状。
图1 全球研究监测鱼类摄入微塑料的主要地区
Fig.1 Major areas where fish ingesting microplastics (MP) were investigated all over the world
参Reference献文考[20][21]颜色主Main color色白White主Main shape要ent片料Ps detected 状征形Sheet要、碎特维纤Characteristics of M ifferent locations片薄塑微Fiber and fragm到的m m小Size测大检1.8 m0.3 ~＞5 m性特ET料P,塑类Type种, PA, PPE-P PE ples from d微的PE P, P到etected in fish sam测塑s·-individual 1)s·individual concentration -1)检内 量体 含料3247类0 ~3 ~鱼 微区MP地/(item/(item同Ps d不 体球f M个/%inated/%.7全染例污比Ratio of fish 2550 1受contam表aracteristics o目数ple 35 Ch个Number体of sam 279 Table 1hina eservoir, C hina区Region orges R江域Three G 珠国iver, C中库Pearl R ater fish 水峡三国中类F reshw种分Classification鱼水淡[22][23]、色、红等色色黑粉Pink, red, black, etc.维维纤Fiber、纤沫、泡片碎Fragments, foam and fibers m m＞1 m 4.85 m0.89 ~E ,)P, P BT, PET ylon(N PE T, P PP, P 龙尼5.30.3 ~100 26 217123 hinaast C湖口 德河海纳ake, India巴沿 姆东 维华Coast and estuary area of E度印Vembanad L[24][25][26][27][28][29][30][31][32][33][34]白White 色色Gray, blue色色色Blue White蓝、灰、蓝 色 黑Black色白黑Black, gray色灰片ents片ents片Fiber Fiber维Fiber Fiber碎Fragments维Fragments维纤Fiber Fragments维维Fragments、碎 、碎纤片纤 片纤纤片维 维碎碎碎纤Fiber, fragm纤Fiber, fragm m m m m m＜5 m m＜5 m m＜5 m m＜5 m .35 m 12m m 5 m 0.18 ~＜5 m＞1 m 0.5 ~4.75 m 0.5 ~5 m 1 ~ET P ET U, P , PA, P, PA T, P ET PE PE VC, P , P E, PA, P PE PE PP, P 24.5.0 1 ~17 1.5 ~2.45.34.64.93 1 ~17 1.0 ~0.1 ~0.2 ~0.43 ~80 4 ~2045.7 2683.8871100.9 9610043.5667.7 51 40436172483235641009311187 anzania SA hina ake, T asin, U ustralia岸razil razil razil ea南河uangdong, C湖ea多ictoria L iver B特iver, B arbor, A亚iver, B Pajeú R Brazos R Xingu R iver, B埃hina S湾利与eixe R佩南aspian S部 根罗ay, Iran维河South C Sydney H海 格亚 域 河特 海Southeast coast of India里 朗尼 流河鲁铁 南 海港 伊Gorgan B桑 河古帕西iver and P国Estuarine areas of G沿尼Southern C坦Southern shore of V斯欣 悉索西西巴 中海南亚拉巴巴 沿东利布Tietê R东度大国广印澳美Marine fish国中种鱼洋海[35]纤Fiber维m2.5 m0.1 ~, IRPS351 ~581 337ea海海aters of the M editerranean S领其耳土 中地Turkish territorial w
参Reference献文考[36][37][38][39][40][41][42][43][44][45][46][47][48][49][50]主Main color色色颜色色Blue Blue色要Transparent黑Black黑Black色色色Blue蓝 、绿色白White明蓝蓝透白White, green料Ps detected 状 片ents征形维Fiber维Fiber维Fiber Fiber维 、碎 维Fiber维维片特 主Main shape要 纤Fiber维纤Fiber维纤Fiber维维Fragments纤Fiber纤Fiber维纤Fiber纤Fiber碎纤纤纤纤 球小片纤Fragments塑微Pellets, fragm碎的m到m m m m m m m测m .6 cm m m检Characteristics of M小Size 5 m 200 μm~6.6 m 1.8 m 63 μm~3.1 m大＜5 m 1 100 μm 0.10 ~4.8 m 2.2 m 225 m 2 m 0.6 ~1 nm~0.38 ~20 m 2.44 m 50 ~0.1 ~.5 ~205 ~0.1 ~0.031 ~EA ayon),P, PAN类Type(R P ylon)(N E种T, P , P PE PE T, P PA PE维龙PE 纤PP, P造人PE T, 尼塑s·-individual 1)s·individual concentration -1)量含41414640料31 ~4.89 3.20.8 0.4 ~.7 ~4 1 ~110423 1 ~微0.25 ~1.6 ~1.4 ~32 ~/(item MP/(item 2.47 ~0.6 ~0.2 ~251.8 ~体个/%inated/%.3.8.8.541 9污比染例fish 2316466817382.95.552 26 ~991.68 10021受Ratio of contam个Number目数ple体of sam 229125884337212120347290174155 2 233 284 1 010 30133 ea )海editerranean S ea 区地pain ea tates ortugal海中岸hannel(地altic S razil iver, P frica reece coastal areas nited S anada ea岸editerranean S 沿ica Balearic Islands, S口海岸沿海 地editerranean coasts岛olynesia洋中nglish C领沿班河沿editerranean S ea and B Mondego R阿港区Region 利瓜iver E德沿arbour, S rance, Italy and G hana岸 河Western E North S outh A岛 平osta R stuary, B太 雷域与大希瓜的 海 兰 的 莫rench P和纳意亚岛洋aters of the M tlantic and M利腊oast of the U海芬foundland, C加海加 曼 纽ew 黎 西中群西大Western M河马大Italy territorial w尼达of the M部、意 里 大地阿牙 古海峡海非Coast of G西East C拿利斯Spanish A西国岸德加的南Durban H利班波巴海中、法 蒙巴西 利罗 哥Pacific coast of C班Spain, F 吉波 海牙Island of N近Moorea Island, F地牙 牙 英与Mamanguape R东班萄葡西海北国西西美1表续类分Classification酸[51]甲二苯对烯乙聚示表;P ET酯stands for ethylene propylene co-二Fiber 丁E-PP酸二维 苯纤对聚示S stands for polystyrene.m;PB T 表0.5 m0.2 ~物stands for polypropylene;P聚共PP烯丙烯乙示stands for polyvinyl chloride; P P 表VC;PE-P烯A stands for polyacrylate;丙PE聚示;PP 表 酯酸烯U stands for polyurethane; P丙2.8聚示E stands for polyethylene;;PE A 表 烯72乙聚示;PE 表。腈烯stands for polyacrylonitrile;P烯乙stands for polyethylene terephthalate; P丙苯ET cean 聚聚示示Arctic O;PA;PS N 表表烯洋 胺乙冰酰氯stands for polyamide;PAN北 聚聚示示PA;PA 表烯;PV C 表二酯戊氨异聚stands for polybutylene terephthalate; P示示BT:IR表表;PU注酯Note: IR stands for isoprene;polymer; P
图2 体内含有微塑料的鱼的占比[19]
Fig.2 Percentage of fish containing microplastics[19]
2 微塑料对鱼类产生的毒性效应的相关要素(Main elements of toxic effect of MPs on fish)
为全面分析微塑料对鱼类的影响,将以微塑料及鱼类为研究内容的检索结果导入BibExcel 软件,利用共现词分析(Co-occurrence Analysis)功能找到在文献标题中出现的高频词汇,再根据暴露相关(暴露方式、发育阶段、微塑料参数)、效应相关(生理活动、组织器官)、归趋、研究目标(塑料种类、常用鱼类)进行分类整理,进一步统计相关词汇出现频次。 最终得到微塑料对鱼类影响涉及的主要高频词汇及频次(图3)。 本部分内容基于图3 分析结果就微塑料对鱼类影响相关的几个主要方面(暴露方式、微塑料特征、生理活动、组织器官、微塑料归趋)进行了概述。
2.1 实验暴露方式
结合图3 结果通过精读相关文献发现,与实验暴露方式相关的主要高频词汇为“rapid, chronic/long-term, single, combine”。 根据暴露时间长短可以将暴露实验分为急性/短期暴露与慢性/长期暴露,根据暴露形式可以分为单一暴露与联合暴露。 从暴露时间角度来看,不同暴露时间下微塑料对鱼类的毒性效应存在较大差别。 之前,有综述论文汇总分析了一些以斑马鱼为研究对象的短期或中期暴露(最多42 d)试验结果,发现在效应类型和效应程度方面存在不同的结果[52]。 作者通过概括分析发现,在出现毒性效应的研究中,急性暴露实验的主要特点是暴露时间短、污染物浓度较高、受试生物敏感,以幼鱼[53-54]居多;慢性或长期暴露实验的特点是暴露时间长、污染物浓度较低或接近环境浓度、受试生物敏感性低,以成鱼[55-57]为主。
图3 微塑料对鱼类影响涉及的主要高频词汇及频次(频次＞5)
Fig.3 High-frequency words (＞5) appeared in the literatures on the influence of microplastics on fish
除暴露时间上的差异外,不同研究采用的暴露形式也有较大差别。 就单一暴露而言,通常选择人工合成的单一成分纯净微塑料,主要关注微塑料对鱼类的毒理学效应,如研究不同粒径微塑料对鱼的毒理学效应[58-59],较少关注其环境或生态毒性,且通常以高于环境浓度进行暴露。 有研究者汇总了多项研究结果发现,在淡水环境(包括自然水体、自来水、瓶装水)中微塑料的浓度范围为1×10-2 ~1×108个·m-3,平均浓度为 5×102个·m-3[60]。 而大部分单一暴露实验使用的浓度均高于该平均值(表2)。 环境中的微塑料通常不是单一化合物,而是由聚合物和添加剂组成的混合物,这些聚合物和添加剂可以吸收周围环境中的其他物质,包括有生命的物质、营养物质和污染物[61]等。 因此,在研究微塑料对鱼类影响的研究中有一些实验是研究多种污染物联合暴露或塑料添加剂对鱼类的影响。 联合暴露实验主要是关注微塑料及其吸附污染物的联合效应,其中包括微塑料与重金属(金[62]、镉[63]、银[64]、铅[65]和铜[66]等)或微塑料与有机污染物(多环芳烃[67]、卤代污染物[68]和芘[69]等)对鱼类的联合毒性。 多数联合暴露实验结果显示联合暴露的毒性效应大于单一暴露[70-72]。 但也有研究发现联合暴露下的毒性效应并未增强,Yan 等[65]以聚乙烯(PS)微塑料与重金属(镉、铅和锌)联合暴露海水青鳉(Oryzias melastigma),结果发现联合暴露并没有增加海水青鳉的生殖腺发育的风险。随着全球海洋塑料垃圾污染日益严重,增塑剂、阻燃剂等塑料添加剂对海洋动物的潜在影响也开始引起人们的关注[73]。 早在十几年前,已有学者研究塑料添加剂对鱼类的影响。 如Cuq 等[74]研究了亲水性增塑剂对沙丁鱼(Sardina pilchardus)肌原纤维蛋白基膜功能特性的影响。
2.2 微塑料特征与毒性效应之间的关系
由于不同研究团队关注微塑料对鱼类毒性效应的研究目的不同,前期大量实验在使用微塑料暴露鱼类时使用的微塑料的相关参数(塑料种类、形状、大小、浓度等)也存在差异。 本研究通过略读摘要筛选出微塑料对鱼类进行暴露的相关研究,通过精读文献的“材料与方法(material and methods)”汇总文献中涉及的鱼的种类、微塑料的特征(种类、形状、大小、浓度)数据及其关注的微塑料对鱼类产生的主要影响,结果见表2。
如表2 所示,受试生物中,淡水鱼类中的关于斑马鱼的研究最多,海洋鱼类中的海水青鳉研究较多。不同实验中所使用的微塑料种类、大小、形状、浓度存在一定差异。 暴露实验中使用最多的是PS,其次是PE。 大部分实验使用的微塑料是人工合成的单一成分的微塑料,只有少量实验使用塑料制品制作的微塑料或环境中收集的微塑料。 由于受试生物、暴露浓度、暴露时间、研究目的的不同,上述微塑料特征与其对鱼类的影响之间尚无明确结论。 就微塑料种类而言,有研究人员比较了不同种类微塑料(PS、PE 和 PET)对褐鳟(Salmo trutta)幼鱼的内分泌、遗传和细胞毒性的影响,发现不同聚合物对海鳟鱼幼鱼的遗传毒性大小顺序为:PS＞PET＞PE [115]。 而另有研究认为微塑料对鱼的影响主要与微塑料浓度有关,与微塑料种类无关[117]。 微塑料大小对鱼类的影响的研究结果也不尽相同,Yang 等[59]比较了纳米级(70 nm)与微米级(5 μm)PS 微塑料对鲫鱼(Carassius auratus)幼鱼的影响,他们发现高浓度的纳米微塑料和微米微塑料都可能对幼鱼造成损害,纳米微塑料潜在的危险性更大。 而Batel 等[118]的研究认为4 ~6 μm 和 125 ~500 μm 的 PE 微塑料对鱼类产生的影响没有差异。 除种类、大小外,还有研究人员比较了不同形状微塑料对鱼的影响,发现不规则形状PE 微塑料对鱼类游泳行为影响较球形微塑料更明显[84]。 而 Qiao 等[97]研究不同形状 PS 微塑料(纤维、碎片和圆球)对斑马鱼的影响时发现纤维微塑料导致的肠道毒性大于碎片微塑料和球形微塑料。 微塑料的暴露浓度也是影响其被鱼类摄入的重要因素之一。 通常认为鱼类摄入微塑料的量与微塑料浓度成正比,但Mbedzi 等[119]开发并应用了一种功能响应方法,以量化鱼类对不同浓度的微塑料的摄取情况,发现斯氏罗非鱼(Tilapia sparrmanii)在环境浓度相对较低的情况下依然会摄取PE 微塑料,当浓度升高时,摄取量增加但不具有统计显著性。 综上,微塑料的各特征参数与其对鱼类产生的毒性效应都存在一定关系,但由于缺乏多物种、多微塑料参数的综合实验,当前阶段的研究结果尚无关于微塑料特征与其对鱼类产生的毒性效应关系的明确结论。
参Reference献文考[75][76]响影Ps 制抑要长 降主塑Main effects on fish by M、生 下的留 率活生产滞内类道 、存慢鱼化对消 缓在 长料料 生塑微ere trapped in intestine and growth inhibited Microplastics w th slower and survival rate reduced Grow微表总-1-1汇0.083,g·L响度g·L影浓0.055,要Concentration 0.1 m主ith different characteristics on fish species 0.025,0.1769 m类鱼对Ps w料f M塑微小m征Ps 大2 m 1 000 μm特Particle size同 征250 ~2 不ain influences o特料塑表ary table of m 微Characteristics of M球状 粒形Particle shape颗Pellets、小片碎Summ Fragments, pellets Table 2塑Particle type 物类合种T 混料PE料塑生原Mixture of virgin plastic鱼鲷类边鳃种光is polyacanthus双鱼Fish species棘刺 氏多Acanthochrom杜bassis dussumieri Am[77][71][59][78][79][80]低降化as changed 率效制化抑同长 留的bined exposure滞 伤激联Assimilation efficiency of fish to polychlorinated应苯biphenyls decreased under com、生道变伤 内在ere trapped in the intestine脏损化为 联氯损、肝行官 消Ingestive behavior w、氧化食多 器 激性摄对 应毒类、多 料 化 经,鱼 激ultiple organ injury and growth inhibited塑 氧神下应 微露化Oxidative stress and liver injury Neurotoxic and oxidative stress暴氧合Oxidative stress, m Microplastics w-1,g·L -1of diet 2 m ,20%g·L 1.5,0.4,1 m .5,3.0%.2,,15%% of diet.1,%,,025,0icrobeads or 50 1.50 0.04,10%diets at 0 3.0 percentage 5%0.01 50 m microfibers per diet%,) μm 0.50 212 μm 5 μm ) μm(95.41 ± 4 500 μm 70 nm,,500 μm),beads (200 μm).23(95.41 ± 4.23 180 ~100 ~F ibers (50珠球 球 球 、微icroplastic末 片微Microspheres微Microspheres微Microspheres维纤beads粉 碎微Microfibers, m Powdered form Fragments PE PE PS Mixture C PV C PV眼phiprion ocellaris鱼锯鲶 鲶双鱼鱼鱼胡胡斑鲫鲫鲫齿齿Carassius auratus Carassius auratus Carassius auratus尖 尖Am Clarias gariepinus Clarias gariepinus[81]获’t have genetic adaptation性应适传遗得 未代子Larval fish don-1 30 particles·m L7.5,m90 m球微Microspheres P S鲑白唇突Coregonus lavaretus[82][83]应une response反激疫应、免 化扰、氧干制泌抑分长内Endocrine disruption and imm生th inhibited and oxidative stress Grow,-1 g·L 0.0911-1 g·L0.25 m 0.00555,0.13665 m 200 μm100 ~球球微Microspheres微Microspheres乳体料护塑或微C奶的PV面中ost popular brands洗Be isolated from one of the m of a face and body scrub鱼鱼鲤Cyprinus carpio鲤Cyprinus carpio
参Reference献文考[84]加影响Ps塑Main effects on fish by M as increased主增要的量含氧生产性活类鱼道化对料消微R eactive oxygen in digestive tract w-1g·L Concentration,250 m浓度50180 μm,350 μm Ps Particle size Characteristics of M征6 ~大150 ~小塑特料 微形球或P article shape不Irregularly shaped状状形则形规and spherical料类塑Particle type种PE鳉2 鱼类种色表杂续Fish species Cyprinodon variegatus[57][85]伤性 损毒 学胎 理胚bryotoxicity Em 病无No histopathological changes occurred-1g·L2.52 m of food2%20 μm5,10 ~5 μm,220 μm 1 ~1 ~120 ~球 球微Microspheres微Microspheres PE PE鱼 鱼马 马斑Danio rerio斑Danio rerio[86][87]炎matory response 性毒经应反 、神症 常异Inflam 为行泳游ming behavior changed, neurotoxicity imSw-1g·L -1 20 m g·L 2 m106,45 μm ,90 ~600 μm 53 10 ~,45 ~500 ~22250,10 ~212 ~片 片碎Fragments碎Fragments PE PE鱼 鱼马 马斑Danio rerio斑Danio rerio[64]率用降Absorption and utilization rate of m etal利收吸的物染污属金内体鱼pollutants in fish decreased低-1,1 000 particles·m L,10010106 μm10 ~球微Microspheres P E鱼马斑Danio rerio[88]化as changed变为行食摄Ingestive behavior w g·L-1,50 m25300 μm250 ~球微Microspheres P E鱼马斑Danio rerio[89]毒ent toxicity性 育发D evelopm-1g·L20 m 45 μm10 ~片碎Fragments P E鱼马斑Danio rerio[90]性毒胎胚bryotoxicityEm-1g·L,100 m1013 μm11 ~球微Microspheres P E鱼马斑Danio rerio[91]性as changed效有物生的icroplastics w铅的出放释中料塑微变改-1Bioavailability of lead released from m g·L250,500 m125,0,200 μm片碎F ragm ents V C, PET, PPE鱼马斑Danio rerio[92]age伤损化、氧性毒殖、生伤损经神age, reproductive toxicity and oxidative dam N erve dam-1g·L5 m1.5,0.5,70 nm球微Microspheres P S鱼马斑Danio rerio[93]代etabolism w as changed化变谢脏、肝激应化氧O xidative stress and liver m-1g·L2 m.2,,00.0220 μm5 μm,70 nm,球微Microspheres P S鱼马斑Danio rerio
参Reference献文考[94]性影响Ps塑Main effects on fish by M要主的生产毒传遗类鱼Genetic toxicity微对料-1g·L C oncentration度浓1 m.1,,00.01 Particle size Characteristics of M Ps 1 μm特 塑大微小料征状 球Particle shape微形Microspheres塑Particle type类种料PS鱼2 鱼类种马表斑续Fish species Danio rerio[95][56]降as inhibited 应反症生炎as changed,下发ation力 道能 、肠position w生 成再 组鳍 物尾Caudal fin regeneration w微icrobial com生intestinal inflamm道肠变改Intestinal m-1g·L g·L-1 10 m1,1 m 0.1,0.1,,500 nm 50 μm 500.5,球 球微Microspheres微Microspheres PS PS鱼 鱼马 马斑Danio rerio斑Danio rerio[96][97][70][68][98][99]icrobiota激ation as changed 应Intestinal lesions and influenced the gut m 化 反物as increased, oxidative stress应应激生 、氧 疫 反 应微 积 症化为ming behavior w 道 蓄 、炎、免激、氧行肠 内 应une response缓 症ation and oxidative stress泳响道化减游 、影 、肠 长 、炎变脏、氧、生 应改 伤损肝 谢 高反, growth slower and inflamm在升道etabolism affected, oxidative intestines w 疫im代化 子 率脏免Sw 消增Accumulation of copper ions in the liver and离肝亡 天铜响stress and innate imm死 先加影Liver m Mortality increased une response, inflamm Innate imm-1-1 g·L-12%ass 20 m -1 g·L g·L 的量icrobeads 0.001 ~20 m 0.2 m 质of food m-1(diet)物食2%100 m 10 ~·mg 103,104,105 mg·L Fibers (25 μm), fragm ents 5 μm 10 μm), beads (15 μm)20 μm0.1 μm,250 μm125 ~45 μm10 ~150 μm40 ~(＜ents,子、珠球片 球 末球末微Microspheres、碎纤Fibers , fragm beads微粉 微粉维Microspheres Powders Microspheres Powders PS PS PS PE PE VC, PPE Danio rerio Danio rerio Dicentrarchus labrax鲈 鲈鱼 鱼Dicentrarchus labrax鱼齿鲈齿 齿马马马舌 舌舌斑Danio rerio斑斑洲 洲洲欧 欧欧Dicentrarchus labrax[72]变as changed改为行泳游m ing behavior wimSw-1g·L.69 m,00.265 μm1 ~球微Microspheres P S鲈齿舌洲欧Dicentrarchus labrax[53]化as changed变为行食摄Ingestive behavior w-3 4 241 particles·m 1 000 μm500 ~片碎Fragments,P S鲷白Diplodus sargus][100乱as disturbed紊脂etabolism w谢代质 脏肝L iver lipid m-1(dry feed)g·g20 m2.0,100 μm20 ~球微Microbeads PS鱼oara斑石纹云Epinephelus m
参Reference献文][101响考影Ps塑Main effects on fish by M要主滞中的留、鳃道生产ere retained in在类肠鱼对料塑fish intestine and gill料微微Microplastics w-1 Concentration 100 000 particles·L浓度P sCharacteristics of M征小Particle size大32 μm)icrofibers (500 μm)料特Microbeads (27 ~, m塑微Particle shape状维纤、微珠形微Microbeads,microfibers种类塑Particle type料PE鱼2 鱼类种刺表三续Fish species Gasterosteus aculeatus][102伤损道肠Intestinal lesions-10.01 g·d0.001,8 μm球微Microspheres P S鱾光Girella laevifrons][103化as changed变为行食摄Ingestive behavior w-1 100 particles·L 97 μm片碎Fragments P S鲈吻尖Lates calcarifer][104肝Liver injury伤损脏-1g·L50 m＜10 μm CPV鳅泥Misgurnus anguillicaudatus][105][106[67][58]][107[55]险风的谢内as increased代化体as affected脏变鱼谢 肝 为入 代 性 响 、行as changed伤进质毒as affected降损物 脂 因 、影下、鳃染 响etabolism w激率高污 、影 性 应 活 升附伤毒化 率吸 损 胞 、氧etabolism w、存ent toxicity, survival rate卵可脏细性 性 产加肝 毒 毒增Cytotoxicity and genotoxicity liver m育料经Neurotoxicity, oxidative stress, and神发Developm declined and behavior w Increased spawning rate, gill injury塑微Risk of contaminants absorbed into fish w Liver injury and lipid m、基-1-1 1 000 particles·m L 2 411 2 226 ~-1·d g·L particles·fish -1-1 g·L % (m/m),1-1 700,50 m 0.1%in fish food,10 000 fibers·L 500 ~0.1 m%,1 000 0.01 106 μm 20 μm),60 μm)10 ~400 μm 100 ~220 nm 70 ~90 μm5,1 000 μm 0.3,0.1 ~(10 ~(50 ~PE PP球末珠 子 状微Microspheres粉Powders微Microbeads珠Beads线Thread料ental PE PS PS PS 塑环Environm P微, P境microplastics PE ykiss ykiss ykiss鳉 鳉鳟鳟鳟 鱼 青 青虹Oncorhynchus m虹Oncorhynchus m虹Oncorhynchus m非罗Oreochromis niloticus本 本日Oryzias latipes日Oryzias latipes][108扰干泌分内E ndocrine disruption-1g·L0.008 m m3 m微Pellets球P E鳉青本日Oryzias latipes][109][110 istake性食误Ingested by m 毒ent toxicity育发Developm-1 100 000 particles·L×106 particles·mL-1×103,110.1,10 μm .00 μm,6,0.500.05球 球微Microspheres微Microspheres PS PS青elastigm a a鳉青elastigm鳉水 水海Oryzias m海Oryzias m
参Reference献文][111[65]][112响考育发影Ps要塑Main effects on fish by M 腺 长生主的Reproductive toxicity响性 响性生、影毒 、影产变物eostasis and gonadal development类殖生改生微鱼为道影icrobiota hom对行肠 摄pact the foraging and growth料食响微Im Perturb gut m-1-1-1 g·L.2 m,0度浓0.02 Concentration g·L0.1 m 500 particles·L250 ~0.002,小Ps 10 μm Particle size 212 μm 2.5 μm 180 ~塑微特料状大Characteristics of M征球Particle shape球 球Microspheres微形微Microspheres微Microspheres料类塑Particle type PS种PS PE a a鲦鳉类Fish species口2 鱼鳉种青elastigm青elastigm软表水 水海海头续Oryzias m Oryzias m黑Pimephales promelas][113疫une response应反 免天先Innate im m-1 plasm ag·L0.1 m(41.0 nm),.7 nm)PS (158 PC S, PPC鲦口软头黑Pimephales promelas][114在ulated in the intestinal tract累积内道化消 并食摄被Ingested and accum,1 900 g·L-1 300,6 000 m 355 μm38 ~片碎F ragm ents粒颗胶橡胎轮T ire crum b rubber鲦口软头黑Pimephales promelas[69]性加Have greater effect than the pyrene毒的虎icrops鰕臀长眼小对atoschistus m芘om附吸可alone on P增,0.0184-1g·L 0,0.184 m 5 μm1 ~球微M icrospheres P E虎icrops鰕臀长眼小Pomatoschistus m[66]性毒加Have greater effect than the copper的鲤脂鲮纹条对子离rochilodus lineatus铜附吸可alone on P增-1g·L0.02 m 90 μm10 ~球微Microspheres P E鲤脂鲮纹条Prochilodus lineatus][115性毒传遗G enetic toxicity-1g·L2.8 m 3 000 μm球微Pellets S, PET, PPE褐鳟o trutta Salm][116料塑微色黑icroplastics,优Capture preferentially black m的粒颗物食ilar to food pellets于似类食摄which is sim先1 ∶6 (m/m)in fish food eter (1.0±0.1) m m,m Length (1.2±0.2) m Diam度径长直状管Tubular微icroplastics料塑 成合工人A rtificial m鲳鰤青紫Seriolella violacea][117[99]激应化影inent harm、氧应ation and oxidative stress响 反症无No imm、炎先une response, inflamm应反疫免天Innate imm-1-1-1·d0.1 g·kg 103,104,105 mg·L m＜2 m 150 μm40 ~形 末球Spherical pellets粉Powders V CS, PE, P VC, P, P PE PA鲷鲷头 头金Sparus aurata金Sparus aurata[63]P stands for poly-应une response反疫免天先和御stands for polyvinyl chloride; P防化VC氧抗Antioxidant defense and innate imm。烯丙聚示g·L-1,PP表S stands for polystyrene; P.5 m 烯,0乙0.05氯聚0,示,PV C 表 烯40 μm乙苯聚32 ~,PSET示stands for polyethylene terephthalate; P表 酯二乙酸甲球 二微Microspheres示E stands for polyethylene; P苯对聚,PE T 表 烯乙PS,P酯C stands for polycarbonate; P聚示E 表酸碳聚示鱼,PC Symphysodon aequifasciatus表丽盘棕龙黄:PA注N ote: PA stands for polyam ide; P尼示表propylene.
2.3 鱼类受微塑料影响的生理活动
根据标题共现词分析结果(图3),目前微塑料对鱼类生理活动的影响主要涉及生殖、免疫、生长、代谢、行为等方面。 之前,有文章综述了微塑料对水生生物(贝壳类、鱼类等)的生殖影响,发现微塑料暴露对水生生物生殖的影响因物种而异,但多数研究结果表明,微塑料暴露后水生生物的生殖细胞和卵母细胞质量、繁殖能力、精子游动速度和后代质量等显著降低[120]。 其中,关于鱼类的研究中,主要关注微塑料对鱼类性腺的影响。 其中有微塑料对性腺的直接作用,Sarasamma 等[92]以纳米微塑料暴露斑马鱼发现纳米微塑料会在斑马鱼性腺中积累;也有微塑料对性腺的间接作用,Wang 等[111]以不同浓度的10 μm PS 微塑料暴露海水青鳉,发现微塑料可以影响下丘脑-垂体-性腺轴,延缓了雌性海水青鳉鱼性腺的成熟。
微塑料对鱼类免疫的影响主要是从基因、酶或蛋白、细胞水平开展研究。 在基因水平上,微塑料主要影响鱼类炎症反应及细胞免疫的相关基因的表达。 Chen 等[110]以PS 微塑料暴露海水青鳉,发现参与炎症反应及免疫相关的基因:络氨酸激酶(Janus kinase)、趋化因子配体 11 (C-C motif chemokine 11)、白细胞介素6 (interleukin 6)表达均发生显著变化。在酶或蛋白水平上,微塑料主要影响鱼类免疫蛋白及与免疫调节相关的酶的变化。 Banaee 等[82]以微塑料与镉联合暴露鲤鱼(Cyprinus carpio),发现联合暴露下鲤鱼的总免疫球蛋白水平发生显著变化。 但Espinosa 等[121]以PVC 微塑料通过食物相暴露金头鲷发现PVC 微塑料对金头鲷的免疫球蛋白水平影响不大。 在细胞水平上,研究人员主要关注微塑料对免疫细胞的影响。 Greven 等[113]以 PS、PC 的微米级与纳米级塑料暴露黑头软口鲦(Pimephales promelas)后发现中性粒细胞吞噬PS 纳米颗粒,他们推测这将影响黑头软口鲦的免疫响应。
鱼类生长相关的直接生理指标是体质量、体长变化。 关于微塑料对鱼类生长影响的研究结论主要是生长抑制,但抑制程度不同。 Naidoo 和 Glassom[76]在环境中收集经微塑料长期暴露(95 d)后的金鱼,发现暴露组中金鱼的体质量、体长增加量较对照组都有所下降。 Xia 等[83]研究了不同浓度、不同暴露时间下,PVC 微塑料对鲤鱼(Cyprinus carpio var.)的影响,发现随浓度增加,鲤鱼体质量增加量降低,对体长影响不明显。 而Cedervall 等[122]研究纳米PS 微塑料经三级食物链传递后对鲫鱼(Carassius carassius)的影响,发现鲫鱼体质量下降。 上述研究认为微塑料暴露后体质量增长变慢的可能原因有:微塑料暴露引起鱼类的消化道堵塞或消化道损伤或发生炎症反应,影响食物摄入和消化道对营养物质的吸收;引起肝脏损伤,影响鱼类肝脏的脂质代谢功能,进而导致体质量增加变慢。 也有一些研究发现微塑料对鱼类生长影响不明显。 Critchell 和Hoogenboom[75]研究PET 微塑料对多刺棘光鳃鲷(Acanthochromis polyacanthus)的影响,发现暴露组与对照组相比,鱼的体质量、体长变化均无差异。 研究人员推测出现上述结果的原因是:鱼类可将微塑料排出体外,从而减小微塑料对消化道的损伤;鱼类对微塑料有一定识别能力,可以避免误食。
通过汇总分析发现,研究鱼类代谢的相关文献主要是关注鱼类的脂类、能量代谢。 目前,研究微塑料对鱼类代谢影响的方法之一是利用代谢组学技术研究代谢物的变化。 Zhao 等[123]从代谢组学角度研究发现丁基羟基苯甲醚和微塑料联合暴露下斑马鱼幼鱼发育异常的原因是2 种物质干扰了花生四烯酸、甘油磷脂和脂类的代谢。 还有研究人员关注代谢过程中一些蛋白和酶的变化。 Cedervall 等[122]研究了纳米微塑料经三级食物链传递后对鲫鱼(Carassius carassius)影响,发现鲫鱼的脂肪代谢发生变化,其主要原因是纳米颗粒结合了血清中的载脂蛋白(apolipoprotein A~I),抑制载脂蛋白利用体内储备的脂肪。 Wen 等[124]对比了微塑料与温度变化对黄棕盘丽鱼(Symphysodon aequifasciatus)代谢的影响,发现微塑料对能量代谢相关的酶(乙酰胆碱酯酶、碱性磷酸酶乳酸脱氢酶、柠檬酸合酶和细胞色素c 氧化酶)的活性有影响,干扰了鱼的能量代谢。
鱼类的行为变化也是研究环境毒物对鱼类影响的重要指标。 研究微塑料对鱼类行为影响的文献中涉及的主要行为包括游泳行为、摄食行为、攻击性等。 目前,微塑料暴露后鱼类的游泳行为变化尚无一致结论。 Barboza 等[72]研究了微塑料与汞对欧洲舌齿鲈鱼的联合毒性,发现在单一或联合暴露下欧洲鲈鱼的游泳速度均下降。 而Chen 等[96]以多种浓度的PS 微塑料暴露斑马鱼成鱼,发现微塑料暴露后斑马鱼变得极度活跃,其游泳距离比对照组增加了1.3 倍~2.4 倍。 微塑料对鱼类摄食方面影响的研究主要集中在摄食量与微塑料浓度的关系[119]及鱼类是否可以辨识微塑料。 通常的暴露实验认为鱼类不能辨识微塑料,但也有学者发现鱼类可以辨识微塑料。 Kim 等[88]发现斑马鱼在摄入 PE 微塑料(247.5 μm)后表现出喷吐行为,说明斑马鱼对微塑料有一定的识别能力。 McCormick 等[125]在研究野外环境中微塑料对革狗母鱼(Synodus dermatogenys)的行为影响时也得到相似的结果。 也有研究认为微塑料暴露不会影响鱼类的行为。 Critchell 和Hoogenboom[75]在研究PET 微塑料对一种岩礁鱼的影响时发现微塑料对其游泳、摄食及攻击性均没有影响。
通过分析鱼类受到微塑料影响的生理活动的相关内容,发现在细胞或分子水平上产生这些毒性效应的机制主要包括:氧化应激、炎症反应、免疫细胞应答、脂质过氧化、DNA 断裂、细胞膜稳定性变化、细胞坏死、代谢或解毒相关通路的激活等。
2.4 鱼体中受微塑料影响的器官
从器官角度分析,大部分研究关注微塑料对鱼类的肝脏和消化道(肠道微生物)及鳃的影响。 肝脏是鱼类脂质代谢的主要器官,脂质代谢是鱼类的主要能量来源[126],所以研究人员关注微塑料对鱼类肝脏脂质代谢功能的影响。 且多数研究发现微塑料暴露会造成肝脏损伤[70]、氧化应激[93]或影响肝脏的代谢功能,特别是脂质代谢[100]等。 消化道作为鱼类摄入微塑料后微塑料存在的主要器官,其是否受到微塑料影响也是很多学者关注的问题之一。 微塑料对鱼类消化道的最直接影响肠道损伤[97,127],有研究发现不同部位损伤程度不同,与肠道前端、中部相比,末端肠道损伤最严重[127]。 其次是影响消化道对营养物质[76]或有毒物质(如铜[66]、银[105])的吸收,多项研究发现微塑料存在降低了鱼肠道对重金属的吸收。有学者认为肠道微生物是生物体的“特殊器官”[128],与生物体的健康息息相关,因此也有学者关注微塑料对鱼肠道微生物的影响。 目前研究认为微塑料对鱼类肠道微生物的影响主要是影响其肠道微生物组成[129]、多样性和丰度[65]及功能[130]。 微塑料的密度与水接近,因此会悬浮在水中,鳃作为鱼类呼吸和废物交换的关键部位[131],在鱼类呼吸的同时会过滤水中的悬浮物,所以鳃也是鱼类直接接触微塑料的主要器官之一。 已有研究证实野外环境中捕获的鱼的鳃丝中有微塑料存在[132],这可能会影响鳃发挥其正常功能。 另外,在实验室暴露实验中也发现微塑料会在鳃中大量积累[57]。
2.5 鱼体内微塑料的归趋
由于微塑料具有持久性、难降解等特点,进入鱼体内的微塑料很可能在鱼体内富集。 之前有基于文献计量学分析的综述文章认为,未来的研究应重点关注微塑料在食物链中的迁移、积累和影响[133]。 因此,明确鱼体内微塑料的归趋对研究其毒性效应、生物富集和食物链传递都具有重要意义。 目前,鱼体内微塑料的归趋途径主要包括:排泄、器官间转移和食物链传递。 有暴露实验在鱼排出的粪便中检测到了微塑料[134],说明微塑料有重新进入环境造成二次污染或持久污染的潜在风险。 另有研究人员关注微塑料在鱼体内的转移,即进入鱼体内的微塑料从消化道进入鱼的其他组织器官,发现5 μm 的PS 微塑料可以进入斑马鱼的肝脏[93]。 这说明粒径在5 μm以下的微塑料可以从消化道进入其他内脏器官。 研究人员还关注了微塑料在食物链中的传递。 Cedervall 等[122]发现纳米级PS 微塑料颗粒可以通过捕食关系从藻类转移到浮游动物再转移到鱼类体内。Zhang 等[135]研究了微塑料在中国东海野生鱼类和甲壳类动物之间的食物网转移,发现微塑料很可能在海洋食物网的高营养级鱼类中富集。 由于微塑料既能在鱼体内富集,又可以沿食物链传递,加之其对生命体存在一定的毒性效应,微塑料最终可能通过食物链传递威胁人类健康。
3 存在的问题与展望(Problems and prospective)
首先,通过文献计量学分析发现,与海洋鱼类相比微塑料在淡水鱼类中的调查数据相对较少。 而海洋中的大部分塑料都是先进入淡水环境后通过河流进入海洋,因此关于微塑料对淡水环境中鱼类污染情况的研究有待加强。 前期野外调查研究的检测方法参差不齐,后续对环境中的微塑料的检测时需要规范统一的环境分析方法。 第二,目前的统计结果显示,无论急性暴露还是长期暴露实验所使用的微塑料浓度多高于环境水体中的浓度。 早在2016年就有研究人员提出,微塑料暴露研究应该符合环境实际[136]。 以后关于微塑料的毒理学研究中如果只研究微塑料的毒性效应可以以高于环境的浓度进行暴露实验,但是如果是研究微塑料对鱼类的生态效应时必须以环境浓度为参考。 而且除环境水体中检测到的浓度外,野外捕获鱼类体内检测到的浓度也具有重要参考价值。 第三,由于微塑料形状、大小、密度存在差异,颗粒浓度与质量浓度之间无法换算,因此以后的研究中应采用统一的浓度单位,以便对不同研究结果进行比较分析。 而且需要将毒性测试方法标准化,尤其是如何配制稳定的实验溶液。 如果出现沉淀或团聚,则实验周期内的测量浓度会随时间降低。 已有的多数暴露实验使用球形塑料,而实际环境中微塑料形状不规则。 因此在以后的暴露实验中可考虑使用野外收集的微塑料进行暴露,以更好地模拟实际环境中的微塑料污染风险。 但使用原生微塑料进行试验时如何避免微塑料毒性测试中塑料添加剂溶出产生的影响也是目前科研人员必须考虑的一个重要问题。 第四,研究认为微塑料可以通过排泄重新进入环境,目前缺乏关于排泄物中的微塑料是否继续影响环境中生物的研究。 加强相关研究可以更好地了解微塑料的环境行为。 另外,加强对野外鱼类体内的微塑料污染情况监测对生态系统健康具有重要意义,特别是利用鱼类受污染的数据进行生态风险评估[137]。
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