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微塑料在水產養殖水域中的分布及在魚體內的富集和毒性效應

2025-04-24 00:00:00侯梅芳岳凝王恩鴻李丹陳麗婷嚴欣黃婷宋麗莉羅永巨
農業環境科學學報 2025年3期

摘要:研究發現,水產養殖水域中微塑料的豐度與經濟條件、流體動力學條件、人口密度等因素密切相關。微塑料在魚體內的累積順序為消化道、鰓gt;肝臟、腦gt;肌肉。腸道、鰓和肝臟中微塑料的主要存在形式分別為纖維、碎片和顆粒。具有吞咽攝食行為的魚類體內微塑料的豐度高于濾食性魚類,雜食性魚類體內微塑料的豐度高于草食性/肉食性魚類,底棲魚類體內微塑料的豐度高于中上層魚類。此外,本文對水產養殖領域微塑料研究的未來方向進行了展望,以期為評估微塑料對水產品質量安全的影響提供參考。

關鍵詞:微塑料;水產養殖水域;魚;生物蓄積;毒性效應

中圖分類號:X174;X714 文獻標志碼:A 文章編號:1672-2043(2025)03-0630-11 doi:10.11654/jaes.2024-1023

塑料因其優良的性能和低廉的價格而被廣泛應用于工業生產和日常生活。2019年塑料的年產量達4.6億t,同時也伴隨著大量塑料廢物的產生[1],2019—2050年將共產生120億t的塑料廢物[2]。濫用、處理不當和管理不善等原因導致大量塑料垃圾進入自然環境[3]。通常情況下塑料的分解非常緩慢,但當其暴露在紫外線(UV)下和持續磨損時,分解便會顯著加速[4]。在水生和陸地生態系統中的塑料經過破碎、紫外線輻射(光氧化)、微生物引起的生物降解等后,其粒徑會逐漸變小,成為微塑料,即粒徑小于5 mm的塑料[5],其通常以纖維、薄膜、泡沫、球體和顆粒的形式存在[6]。

目前在水環境中檢測到的微塑料主要有聚乙烯(PE)、聚丙烯(PP)、聚苯乙烯(PS)、聚氯乙烯(PVC)、聚對苯二甲酸乙二醇酯(PET)和聚酰胺(PA)等[7-8]。微塑料在水體中的分布取決于它們自身的密度、大小和形狀,PP和PE是典型的低密度塑料,容易漂浮在水體中,而PVC、PS、PET和PA是高密度塑料,容易下沉到沉積物中[9-10]。微塑料除本身含有毒單體和添加劑外,也是各種污染物、抗性基因和微生物的載體[11],因此會對意外攝入它們的水生生物產生健康威脅。微塑料顆粒的大小和形狀使其很容易被魚、蝦等水生生物誤食,并累積在體內影響其生長和繁殖,進而對漁業可持續發展產生巨大的影響[12-13]。

我國擁有世界上最大的水產養殖面積,2023 年全國水產養殖面積為762.46 萬hm2,產量為7 116.17萬t,是唯一一個水產養殖產量超過野生捕撈的國家[14-15]。我國的水產養殖場一般為封閉或半封閉的池塘,長期、高強度的水產養殖活動,可能會導致微塑料大量積累,進而影響水產品的質量安全。魚類種類繁多且食性和攝食方式各異,棲息活動在不同的水層,很容易接觸和攝入水環境中無處不在的微塑料并在體內蓄積,從而對其生長和健康造成損害[13]。魚體中的微塑料也可能通過食物鏈傳遞到人體中,進而對人體健康造成威脅。

本文就目前微塑料在水環境中的污染現狀,綜合闡述了水產養殖水域微塑料的分布特征、微塑料在魚體中的富集特征和微塑料對魚體的毒性效應機制,并對水產養殖領域微塑料未來的研究方向進行了展望。本研究結果將為保障漁業的可持續發展和水產品質量安全提供一定科學依據。

1 微塑料在水產養殖水域的分布現狀

水產養殖水域中的微塑料主要來自遺棄的漁具、飼料、幼魚缸、網、繩索、管道、浮標和網箱等[8]。這些塑料經過物理、化學或生物降解等過程,逐漸破碎或分解,導致水產養殖環境中檢測出大量的微塑料(表1)。

研究發現華南珠江口南沙養殖池塘中的微塑料豐度為6.6~263.6 個·L-1 [21],廣西茅尾海水產養殖區水體中微塑料豐度范圍為1.2~10.1 個·L-1 [26]。上海稻魚共養系統[17]、馬鞍列島人工魚礁[20]和海南島水產養殖場[22]的水體中微塑料平均豐度分別比華南珠江口南沙養殖池[21]和廣西茅尾海水產養殖區[26]水體中的低了99.3%~99.7%、99.7%~99.9% 和99.6%~99.8%。自20世紀70年代后期以來,珠江三角洲已成為我國人口最多、經濟最活躍的地區。近幾十年來快速的經濟增長和城市發展造成的南沙區污水(主要來自工業、農業和日常生活)和廢物污染,致使珠江口附近的養殖場中微塑料的豐度較高[21]。池塘的水源很可能是受到微塑料污染的水體,導致華南地區水產養殖水體中微塑料豐度較高。微塑料污染水平的差異也可能是由于流體動力學條件的不同。上海稻魚共養系統的養殖稻田有山脊與天然水柱隔離,可以阻止微塑料進入[17]。廣東省佛山市草魚養殖池塘中微塑料豐度相對較高,可能是由于草魚養殖主要在土池中,土池是一個相對封閉的系統,具有較長的保水時間和較低的流速,有利于微塑料的沉積[28]。人口密度也是影響水中微塑料污染程度的重要因素之一,兩者之間存在正相關性[29]。馬鞍列島、海南島以及南海地區人口密度相對較低,相應受到微塑料污染的影響也較小。

上述結果表明,水產養殖水域中微塑料的豐度與經濟、流體動力學條件和人口密度等密切相關。

2 微塑料在魚體中的富集特征

水產養殖水體中的微塑料可能會被魚類誤食并在魚體內累積。本文以“microplastics”和“fish”為關鍵詞,在Web of Science數據庫中檢索出3 096篇相關文獻,經過篩選最終選取54篇文獻,對78種魚體內微塑料的分布特征進行了研究(表2)。結果表明,微塑料在魚體內的分布具有顯著的組織差異性、攝食差異性和棲息地差異性等特征。

2.1 組織差異性

微塑料主要通過直接接觸或食物鏈進入魚體,并累積在魚的不同組織中[65,81]。研究發現微塑料在魚類不同組織中的累積順序大致為消化道、鰓gt;肝臟、腦gt;肌肉(表2),說明消化道和鰓是微塑料在魚體內的直接累積器官。微塑料尺寸較小并且很多微塑料的形狀與浮游生物類似,因此容易被以浮游動物為食的魚類攝入并累積在消化道中[82]。作為與外界環境持續接觸的直接靶標以及濾食性魚類的攝食器官[83],魚鰓中微塑料的積累也較為顯著。研究表明,尺寸較小的微塑料通過上皮細胞的內吞作用內化,穿過生物屏障或通過循環系統轉移到其他組織,這可能是肝臟、腦和肌肉中也存在微塑料的原因[84]。例如,在暴露于20 μm PS的斑馬魚的肝臟中沒有發現微塑料,但在暴露于5 μm PS的斑馬魚肝臟中檢測到了微塑料[85]。

另外,魚類不同組織中的微塑料形狀也有所不同。魚的腸道內容物中纖維狀的微塑料豐度較高[86],鰓或皮膚上主要是薄膜和碎片狀微塑料[87],肝臟等組織中的微塑料以細小顆粒為主[85]。這可能是由于纖維形狀微塑料細長并且與浮游生物相似,容易被魚類誤食,而薄膜和碎片狀微塑料的較大表面積使它們容易被鰓和皮膚阻攔[87],肝組織中微塑料的累積高度依賴于顆粒的大小,較小的微塑料顆??梢赃M入循環系統并轉移到肝臟[85,88]。

2.2 攝食差異性

魚類進食方式、所處的營養級以及食性的差異都會導致微塑料在魚體內的累積程度不同(表2)。

魚類的覓食機制不同,其胃腸道中積累的微塑料數量也會有差異。吞咽進食的魚類如石斑魚,其腸道中微塑料的豐度達到23.91 個·條-1[30],而濾食性魚類沙丁魚體內微塑料的豐度僅為1.58 個·條-1[45]。濾食性魚類在通過鰓耙被動過濾水時偶爾會攝入微塑料[89],而不咀嚼直接吞食獵物的魚類會在很大程度上攝入更多的微塑料[90]。魚類的攝食習性也會影響微塑料的累積。雜食性魚類金鯧魚腸道中的微塑料高達546 個·條-1[36],顯著高于無須鱈魚、鯔魚、鯉魚等肉食性魚類[32,48,77]。這是由于雜食性魚類的食物種類繁多、來源廣泛,例如浮游生物、底棲生物以及動植物碎屑等[91],比肉食性和草食性魚類攝入的微塑料源更多,導致體內微塑料豐度較高[92]。洄游性魚類在不同季節生活在不同的水體中,具有更廣泛的營養生態位和餌料,會攝食不同環境介質(例如海水、沉積物)中的微塑料,導致微塑料在體內含量更高。如帶魚消化道中的微塑料為46 個·條-1 [45],鯉魚消化道內僅為4.2個·條-1[77]。此外,由于生物放大作用,微塑料會在較高營養級的魚類中富集。如前所述的石斑魚,其以底棲甲殼類、各種小型魚類和頭足類為食,在食物鏈中所處的營養級相對較高,體內微塑料豐度顯著高于低營養級魚類。

2.3 棲息地差異性

魚體內微塑料的蓄積在很大程度上受棲息地中微塑料的豐度和分布的影響,與水體中微塑料的豐度有關[93]。鯔魚主要棲息環境為沿岸沙泥底水域,以浮游動物、底棲生物等為食,其體內微塑料的豐度為10.00 個·條-1 [61],高于中上層魚類鳀魚的1.13 個·條-1 [46]。由于微塑料的蓄積和自然沉降,底層海水中微塑料的豐度一般高于上層和中層海水,從而增加了底棲魚類接觸微塑料的可能性,使得底棲魚類攝入更多的微塑料。海州灣沿海水域底層魚類攝入的微塑料數量也顯著高于中上層魚類[89]。但是在日本九州西海岸沿海地區,中上層魚類體內的微塑料含量要高于底層魚類[94],這可能是由于一些低密度的微塑料會長時間懸浮在地表水中,被中上層魚類攝入的概率較大[95]。另外,穴居生物的洞穴會導致沉積物局部下沉,形成小的“峽谷”,增加其表面積,是塑料碎片沉積的首選區域,此處微塑料的豐度大約是開闊斜坡、大陸架和平原環境的2倍[96]。因此,洞穴的存在也會增強下沉微塑料的保留,增加微塑料的豐度,進而增加微塑料被底棲魚類攝食的概率。

綜上所述,在自然條件下,微塑料在魚體內的分布特征具有組織差異性、攝食習慣差異性以及棲息地的差異性等。微塑料含量在魚體內累積的順序為消化道、鰓gt;肝臟、腦gt;肌肉。腸道、鰓和肝臟中微塑料的主要形狀分別為纖維狀、碎片狀和細小顆粒狀。吞咽式魚體比濾食性魚體內微塑料含量高,雜食性魚體內比植食性/肉食性魚體內微塑料含量高,底棲魚類比上層魚類體內的微塑料含量高。

3 微塑料對魚體的毒性效應

3.1 氧化損傷

微塑料的存在會促進魚體不同組織中活性氧(ROS)的產生,從而引起抗氧化酶[超氧化物歧化酶(SOD)、過氧化氫酶(CAT)、谷胱甘肽過氧化物酶(GPx)等]的活性發生改變,誘導氧化應激[97]。鯉魚暴露于1.0 g·L-1和2.5 g·L-1 PP微塑料中,其鰓部丙二醛含量水平隨PP微塑料暴露濃度和暴露時間依賴性增加,CAT活性顯著降低[98]。鯉魚通過飲食暴露于不同濃度的PVC 微塑料60 d后,肝臟中的ROS水平表現出明顯的劑量依賴性上升趨勢,并誘發氧化應激,肝細胞中脂肪代謝的平衡被破壞,引起脂肪堆積,最終導致肝損傷[99]。

3.2 腸道影響

微塑料暴露可導致魚類腸道微生物群失調、攝食活性降低、腸道損傷及結構改變,進而抑制生長并引發腸道功能障礙。Jin 等[100]研究發現斑馬魚暴露于1 000 μg·L-1 PS微塑料14 d后腸道微生物群失調,擬桿菌門和變形菌門的豐度顯著降低,厚壁菌門的豐度顯著增加。微塑料在腸道中累積會顯著降低魚的攝食活性,使其生長被抑制,如海洋石斑魚暴露于106個·L-1 PS微塑料14 d后,其體質量和特定生長速率相對于未暴露組分別降低了65.4% 和65.9%[101]。斑馬魚暴露于50 μg·L-1 PS微塑料21 d后,腸道絨毛、上皮出現損傷,腸道通透性增加[102]。金魚幼魚暴露于100 μg·L-1 PS微塑料7 d后,出現腸道結構疏松、腸腔變大、腸外膜與肌層分離、腸黏膜結構破壞、線粒體細胞空泡化[103]。

3.3 免疫毒性

微塑料暴露會顯著影響魚類的免疫系統,導致與免疫相關的酶活性下降、炎癥反應加劇,并激活免疫信號通路,造成腸道和心血管等損傷,影響免疫功能。鯉魚通過飲食暴露于不同濃度的PVC 微塑料60 d后,腸道中的異性免疫酶——酸性磷酸酶(ACP)、堿性磷酸酶(AKP)及溶菌酶(LZM)的活性顯著下調,導致腸道絨毛受損、炎癥細胞浸潤[99]。羅非魚暴露于100 μg和500 μg PP微塑料30 d后,其血清中冬氨酸氨基轉移酶(AST)、丙氨酸轉氨酶(ALT)的活性和淋巴細胞、總白細胞以及血小板數量顯著增加,血管組織和心臟功能受到損害,誘發炎癥影響免疫[104]。斑馬魚胚胎被注射PS微塑料后,與免疫反應相關的信號通路被激活,補體替代途徑基因(CFHL3、CFHL4、CFb和C9)表達上調[105]。斑馬魚暴露于1 000 μg·L-1PE微塑料14 d后,腸道中IL1α、IL1β和IFN的蛋白水平顯著增加[100]。

3.4 生殖毒性

微塑料暴露對魚類的生殖發育造成嚴重影響,導致性腺發育延遲和繁殖力下降,卵巢和睪丸細胞凋亡率增加,引起卵巢組織炎癥及卵母細胞發育受損,最終影響魚類的繁殖。鯉魚幼魚通過飲食暴露于不同濃度的PVC微塑料60 d后,性腺體指標顯著降低,性腺發育延遲[106]。20 μg·L-1 PS微塑料可延遲海洋青鳉性腺成熟,從而降低雌魚的繁殖力[107]。暴露于1 000ng·L-1 PE 微塑料21 d 后,鯉魚卵巢中線粒體凋亡相關基因(bax、aif、cyt - c、caspase - 7、caspase - 9 和caspase-3)的表達升高,而抗凋亡基因(bcl-2 和bclxl)的表達較低,導致卵巢細胞凋亡率增加;PE還通過TRAF6/NF-kB通路激活p65 因子,導致卵巢中促炎因子il-6、il-1β 和tnf-a 的水平增加,誘導卵巢組織炎癥并損害卵母細胞發育[108]。雄性斑馬魚暴露于1 000μg·L-1 PS微塑料21 d后,睪丸細胞凋亡水平顯著增加,睪丸基底膜的厚度顯著降低[109]。

3.5 神經毒性

微塑料暴露會對魚類神經系統產生毒性作用。斑馬魚暴露于5 mg·L-1 PE微塑料14 d后,參與神經元功能、神經元分化和軸突發生以及視覺相關(opsin6 和rhodopsin)的基因表達下調[110]。0.1~100 μg·L-1的老化PS微塑料顯著增加了斑馬魚的多巴胺(DA)、5-羥色胺(5-HT)、γ-氨基丁酸(GABA)和乙酰膽堿(Ach)水平[111]。乙酰膽堿酯酶(AchE)對維持神經肌肉系統的正常功能具有重要作用。暴露于0.26 mg·L-1和0.69 mg·L-1微塑料96 h后,鱸魚腦中AchE的活性受到抑制[112]。ROS的過量產生導致潛在的神經和神經肌肉功能障礙,誘發肌肉損傷并影響新陳代謝,從而影響魚的運動[103]。

此外,微塑料還干擾魚體內的新陳代謝。暴露于PE 微塑料后,斑馬魚體內參與糖酵解途徑、嘌呤代謝、氧化代謝和賴氨酸代謝的基因豐度降低,能量應激和代謝途徑受到影響[110]。微塑料暴露增加了鱸魚大腦和肌肉中的脂質氧化(LPO),能量相關酶[乳酸脫氫酶(LDH)和異檸檬酸脫氫酶(IDH)]的活性受到抑制[112]。綜上所述,微塑料會引起魚類組織病變,改變腸道微生物豐度,產生免疫毒性、生殖毒性、神經毒性等,并干擾相關代謝通路,對魚類健康造成嚴重危害(圖1)。

4 展望

雖然關于微塑料在水環境中的分布特征及其對魚類的效應研究取得了很大的進展,但尚有大量工作需要深入開展。例如,目前關于微塑料在我國水產養殖水域中的分布特征僅有10余篇研究報道,但我國擁有世界上最大的水產養殖面積,應該加強對我國不同類型水產養殖水域中微塑料分布情況的調查,尤其是一些缺乏有效管理措施的小型水產養殖場。微塑料在這種封閉、交換能力差、水動力較弱的環境中很容易大量積累,進而對漁業生物尤其是魚類的質量安全產生巨大的威脅。

微塑料對魚類毒性效應的研究主要集中在腸道、鰓等組織中,而魚類嗅覺器官和味覺器官也是水體中的微塑料與魚體直接接觸的部位。在水生環境中嗅覺和味覺感受器都用于檢測食物,決定魚類的攝食行為。微塑料對魚類嗅覺系統和味覺系統的影響機制如何,還需進一步研究。魚體中的微塑料與人體健康密切相關,但目前關于食用含有微塑料的魚對人體的影響機制研究較少。因此,檢測魚類中的微塑料并確定食用含微塑料的魚對人體健康的不利影響顯得至關重要。

我國水產漁業的發展具有重要的經濟和社會意義。為了更好地保障水產養殖生物健康生長和水產品質量安全,需要徹底了解水產養殖中的微塑料污染來源并采取措施減少塑料進入水生環境,減輕微塑料對水產養殖的影響。我國大多數水產養殖場屬于封閉型養殖場,傳統上經營規模較小并缺乏有效的管理措施。因此需要加強水產養殖管理,制定相應的法規限制和管控水產養殖過程中塑料制品的使用和塑料垃圾的排放,從源頭上遏制微塑料污染。此外,還需要加強對水產養殖環境中微塑料污染的檢測和水生生物微塑料攝入情況的研究。微塑料對水體的污染是一個長期、動態的過程,可運用遙感技術動態監測養殖環境中的微塑料[113]。同時,推動養殖塑料制品相關技術研發,如回收塑料制品、提高漁具的耐磨性、使用環境友好材料制作的漁具代替塑料漁具等[114],以期選用合適的水產養殖微塑料污染控制措施,促進水產養殖業的健康可持續發展。

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(責任編輯:李丹)

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