生态环境学报 ›› 2023, Vol. 32 ›› Issue (11): 2030-2040.DOI: 10.16258/j.cnki.1674-5906.2023.11.013
刘安*(
), 吴昊, 何贝贝
收稿日期:2022-07-20
出版日期:2023-11-18
发布日期:2024-01-17
通讯作者:
*作者简介:刘安（1983年生），女，副教授，博士，主要从事城市环境污染治理及生态修复等研究。E-mail: liuan@szu.edu.cn
基金资助:
LIU An*(), WU Hao, HE Beibei
Received:2022-07-20
Online:2023-11-18
Published:2024-01-17
摘要：
塑料在自然环境中降解缓慢，塑料污染物的积累不可避免地成为人们关注的问题。尺寸微小的塑料被定义为纳米塑料（NPs）。虽然NPs的尺寸尚存在争议，但与其他工程纳米颗粒类似，NPs可造成多种不利的环境影响。NPs的存在和在生物体内的积累会对生物体产生一系列毒性效应，影响生物体的生长、繁殖和内分泌系统等。因此，NPs对包括人类在内的较多生物都构成威胁。尽管NPs污染已成为最令人关注的环境问题之一，但目前有关NPs对土壤环境及生物体的毒害效应等的研究仍然较少。旨在综述NPs本身的毒害效应（包括其中的添加剂）、降解产物和与其他环境污染物（有机污染物、无机污染物）耦合后的复合毒性以及NPs对陆生生态环境，包括植物、动物以及土壤产生的综合影响，并总结本领域内的研究现状和不足。主要的研究不足包括对经过降解等过程形成的次级NPs的毒性效应尚未深入开展，NPs对真实生物体的影响研究仍具有局限性，针对环境-NPs-生物-污染物的交互耦合机制对土壤环境的毒害效应仍需进一步探究。针对这些研究不足开展相应的科研探究工作能为全面科学地评价NPs的生态风险提供理论支撑。
中图分类号:
刘安, 吴昊, 何贝贝. 陆地环境中纳米塑料毒性效应的研究进展[J]. 生态环境学报, 2023, 32(11): 2030-2040.
LIU An, WU Hao, HE Beibei. Toxic Effects of Nanoplastics on Terrestrial Environment: A Review[J]. Ecology and Environment, 2023, 32(11): 2030-2040.
图1 NPs在环境中的分布及归趋
Figure 1 Distribution and fate of NPs
| 影响部位 | 影响效果 | 参考文献 |
|---|---|---|
| 血管 | NPs很可能通过血液转移至其他组织或器官，尺寸较大的NPs可能会聚集或沉积，从而堵塞毛细血管，影响血液运输氧气 | Lett et al., Leslie et al., |
| 睾丸 | NPs会使睾丸萎缩、精子上皮的蒸泡化、Sertoli细胞屏障（血睾丸屏障）的混乱/破坏或渗透性增加；诱使精子头畸形、无尾、小头、杂交体丢失、卷曲或精子肿胀；引发促炎症和促氧化事件，以及雄性和雌性动物性激素水平失衡 | Marcelino et al., |
| 免疫系统 | 碱性磷酸酶（ACP）、酸性磷酸酶（AKP）、苯并氧化酶（PO）等免疫相关酶的活性下降，NPs会抑制溶酶体释放ACP和AKP，并影响免疫防御。随着NPs浓度的增加，外部应激程度超过幼虾免疫防御系统的能力，免疫酶活性下降，免疫系统受损。ROS水平升高。高ROS水平会导致脂质过氧化和膜损伤，脂质过氧化会抑制抗氧化相关基因的表达，并破坏抗氧化防御系统 | Li et al., |
| 肝脏 | 造成肝细胞坏死、浸润和脂质飞沫，引起肝脏炎症和脂质积累；扰乱了肝脏的代谢组谱，改变脂质代谢和能量代谢过程，使体内胆碱、磷胆碱和胆固醇含量发生改变，从而影响动物的脂肪累积 | Lu et al., |
| 胎盘 | NPs可能会改变胎盘中的几种细胞调节途径，如怀孕期间的免疫机制、胚胎和子宫之间的信号传导，以及正常怀孕期间子宫树突状细胞、T细胞和巨噬细胞的转运。这些影响都可能导致不良妊娠结局，包括子痫前期和胎儿生长限制 | Ragusa et al., |
| 心肌细胞 | NPs对心肌细胞的兴奋-收缩偶联、血浆膜和线粒体功能有不利影响；NPs会显著降低细胞内钙水平、线粒体膜电位、细胞代谢和心肌细胞的收缩力，这最终可能导致体内致命的心力衰竭；PS-NPs会吸附到心肌细胞的血浆膜上，干扰Ca2+转移，影响细胞内外Ca2+平衡，从而影响心机收缩能力；PS-NPs破坏糖酵解稳态，使基底氧消耗率和ATP生产能力明显降低。此外，低线粒体膜电位可能会降低肌质网（SR）Ca2+-ATP酶活性，这可能导致SR内部Ca2+含量和心脏收缩性降低 | Roshanzadeh et al., |
| 神经系统 | NPs分散在小鼠大脑中，包括皮层、海马体、SNC和纹状体；PS-NPs会使神经元细胞繁殖能力下降，甚至凋亡；诱发神经元线粒体功能障碍和能量代谢障碍 | Jung et al., Liang et al., |
表1 NPs的易位及对各个器官的毒理效应
Table 1 Translocation of NPs and toxic effects on organs
| 影响部位 | 影响效果 | 参考文献 |
|---|---|---|
| 血管 | NPs很可能通过血液转移至其他组织或器官，尺寸较大的NPs可能会聚集或沉积，从而堵塞毛细血管，影响血液运输氧气 | Lett et al., Leslie et al., |
| 睾丸 | NPs会使睾丸萎缩、精子上皮的蒸泡化、Sertoli细胞屏障（血睾丸屏障）的混乱/破坏或渗透性增加；诱使精子头畸形、无尾、小头、杂交体丢失、卷曲或精子肿胀；引发促炎症和促氧化事件，以及雄性和雌性动物性激素水平失衡 | Marcelino et al., |
| 免疫系统 | 碱性磷酸酶（ACP）、酸性磷酸酶（AKP）、苯并氧化酶（PO）等免疫相关酶的活性下降，NPs会抑制溶酶体释放ACP和AKP，并影响免疫防御。随着NPs浓度的增加，外部应激程度超过幼虾免疫防御系统的能力，免疫酶活性下降，免疫系统受损。ROS水平升高。高ROS水平会导致脂质过氧化和膜损伤，脂质过氧化会抑制抗氧化相关基因的表达，并破坏抗氧化防御系统 | Li et al., |
| 肝脏 | 造成肝细胞坏死、浸润和脂质飞沫，引起肝脏炎症和脂质积累；扰乱了肝脏的代谢组谱，改变脂质代谢和能量代谢过程，使体内胆碱、磷胆碱和胆固醇含量发生改变，从而影响动物的脂肪累积 | Lu et al., |
| 胎盘 | NPs可能会改变胎盘中的几种细胞调节途径，如怀孕期间的免疫机制、胚胎和子宫之间的信号传导，以及正常怀孕期间子宫树突状细胞、T细胞和巨噬细胞的转运。这些影响都可能导致不良妊娠结局，包括子痫前期和胎儿生长限制 | Ragusa et al., |
| 心肌细胞 | NPs对心肌细胞的兴奋-收缩偶联、血浆膜和线粒体功能有不利影响；NPs会显著降低细胞内钙水平、线粒体膜电位、细胞代谢和心肌细胞的收缩力，这最终可能导致体内致命的心力衰竭；PS-NPs会吸附到心肌细胞的血浆膜上，干扰Ca2+转移，影响细胞内外Ca2+平衡，从而影响心机收缩能力；PS-NPs破坏糖酵解稳态，使基底氧消耗率和ATP生产能力明显降低。此外，低线粒体膜电位可能会降低肌质网（SR）Ca2+-ATP酶活性，这可能导致SR内部Ca2+含量和心脏收缩性降低 | Roshanzadeh et al., |
| 神经系统 | NPs分散在小鼠大脑中，包括皮层、海马体、SNC和纹状体；PS-NPs会使神经元细胞繁殖能力下降，甚至凋亡；诱发神经元线粒体功能障碍和能量代谢障碍 | Jung et al., Liang et al., |
| 植物 | 塑料类型 | 塑料尺寸/nm | 影响效果 | 参考文献 |
|---|---|---|---|---|
| 绿豆 | PS | 28 | 叶子质量降低；平均根直径降低 | Chae et al., |
| 大白菜 | PS | 50‒100 | 光合作用色素含量（叶绿素a、叶绿素b和胡萝卜素）降低； | Zhang et al., |
| 水稻 | PS | 20‒200 | 种子萌发率降低；随着NPs浓度的增加，根长逐渐显著减少；染色体断裂、粘稠，染色质受损 | Spano et al., |
| PS | 80 <1000 | 损伤植物的运输系统，影响水稻对营养物的吸收和转运作用 | Liu et al., | |
| 生菜 | PS | 45‒60 | PS使生菜干重、植株高度，叶面积和植物色素含量显著降低了；电解质泄漏率升高；总抗氧化能力降低；微量营养素和必需氨基酸的显著减少 | Lian et al., |
| 小麦 | PS-Cd | 100 | PS-NPs可以缓解小麦中Cd诱导的毒性；PS-NPs提高了碳水化合物和氨基酸代谢 | Lian et al., |
| PS | 79‒95 | 发芽率没有收到影响，但显著提高了小麦幼苗的生长。生长参数和叶绿素含量大大增加。PS-NPs降低了芽与根生物量比和微量营养素含量。PS-NPs改变了小麦叶片的代谢物含量 | Lian et al., | |
| PS | 70 | 小麦幼苗直径、根茎质量均有明显增大；提高了根的氮吸收能力和代谢水平 | Ren et al., | |
| 黄瓜 | PS | 100、300、 500、700 | PS-NPs的粒度会影响黄瓜植物的生物量和新陈代谢； PS-NPs影响黄瓜叶片的光合作用、抗氧化和糖代谢系统 | Li et al., |
| 玉米 | PS-NH2 或PS-COOH | 22‒24 | PS-COOH使幼苗叶质量降低；PS-NH2对植物生长具有更大的抑制作用；PS-NH2和PS-COOH均使植株叶绿素含量降低；PS-NH2激活了氧化防御机制，对叶片产生了氧化损伤 | Sun et al., |
| PS | 100、300、500 | 100 nm和300 nm的PS-NPs显著增加了玉米SOD和GSH-PX活性；500 nm PS-NPs显著提高了玉米CAT活性；300 nm和500 nm的PS-NPs使植物细胞壁受损；不同粒度的PS-NPs都诱导了植物根代谢的增加 | Zhang et al., | |
| 拟南芥 | PS-SO3H 或PS-NH2 | 55‒77 | NPs显著降低了植株的根系长度；阻止根毛的水分运输，从而降低植株鲜质量；过氧化产物产量提高；抗病基因下调 | Sun et al., |
表2 NPs对各类植物的毒理效应
Table 2 Toxic effects of NPs on plants
| 植物 | 塑料类型 | 塑料尺寸/nm | 影响效果 | 参考文献 |
|---|---|---|---|---|
| 绿豆 | PS | 28 | 叶子质量降低；平均根直径降低 | Chae et al., |
| 大白菜 | PS | 50‒100 | 光合作用色素含量（叶绿素a、叶绿素b和胡萝卜素）降低； | Zhang et al., |
| 水稻 | PS | 20‒200 | 种子萌发率降低；随着NPs浓度的增加，根长逐渐显著减少；染色体断裂、粘稠，染色质受损 | Spano et al., |
| PS | 80 <1000 | 损伤植物的运输系统，影响水稻对营养物的吸收和转运作用 | Liu et al., | |
| 生菜 | PS | 45‒60 | PS使生菜干重、植株高度，叶面积和植物色素含量显著降低了；电解质泄漏率升高；总抗氧化能力降低；微量营养素和必需氨基酸的显著减少 | Lian et al., |
| 小麦 | PS-Cd | 100 | PS-NPs可以缓解小麦中Cd诱导的毒性；PS-NPs提高了碳水化合物和氨基酸代谢 | Lian et al., |
| PS | 79‒95 | 发芽率没有收到影响，但显著提高了小麦幼苗的生长。生长参数和叶绿素含量大大增加。PS-NPs降低了芽与根生物量比和微量营养素含量。PS-NPs改变了小麦叶片的代谢物含量 | Lian et al., | |
| PS | 70 | 小麦幼苗直径、根茎质量均有明显增大；提高了根的氮吸收能力和代谢水平 | Ren et al., | |
| 黄瓜 | PS | 100、300、 500、700 | PS-NPs的粒度会影响黄瓜植物的生物量和新陈代谢； PS-NPs影响黄瓜叶片的光合作用、抗氧化和糖代谢系统 | Li et al., |
| 玉米 | PS-NH2 或PS-COOH | 22‒24 | PS-COOH使幼苗叶质量降低；PS-NH2对植物生长具有更大的抑制作用；PS-NH2和PS-COOH均使植株叶绿素含量降低；PS-NH2激活了氧化防御机制，对叶片产生了氧化损伤 | Sun et al., |
| PS | 100、300、500 | 100 nm和300 nm的PS-NPs显著增加了玉米SOD和GSH-PX活性；500 nm PS-NPs显著提高了玉米CAT活性；300 nm和500 nm的PS-NPs使植物细胞壁受损；不同粒度的PS-NPs都诱导了植物根代谢的增加 | Zhang et al., | |
| 拟南芥 | PS-SO3H 或PS-NH2 | 55‒77 | NPs显著降低了植株的根系长度；阻止根毛的水分运输，从而降低植株鲜质量；过氧化产物产量提高；抗病基因下调 | Sun et al., |
| 研究课题 | 研究现状 | 研究不足 |
|---|---|---|
| NPs对植物的毒害效应 | NPs对植物生长量（植株高度、根茎直径、叶子质量）的影响；NPs对植物体产生氧化应激效应，植物体内的ROS含量和抗氧化酶活性的变化，反映出植物氧化受损的情况；NPs叶绿素、植物激素、微量营养素和必需氨基酸等植物生长指标含量的影响；NPs在植物体内的内化、运输和积累 | 降解过程及环境中与其他污染物的是否存在协同毒性?降解后的NPs在实际环境中对植物的毒害效应有何差异?考虑NPs对土壤的污染，从而对植物产生的间接毒害作用，研究NPs对土壤环境-陆生植物体系的综合效应而非单独地研究NPs对植物体的影响。针对更多的NPs种类，如聚氯乙烯（PVC）、聚乙烯（PE）等以评定各类NPs的毒理效应 |
| NPs对陆生动物的毒害效应 | NPs进入动物体内的途径；NPs在体内的累积；NPS的易位及对相应部位的毒理效应；NPs对细胞产生氧化损伤的程度 | NPs如何对各组织和器官造成毒害影响的机理?NPs在各组织和器官累积量的多少?对NPs如何引发生物的应激反应?NPs通过何种途径在生物体内运输的过程均未被探明? |
| NPs对土壤环境的影响 | NPs对土壤物理性质的影响；NPs对土壤中微生物活性、无机盐含量与比例的影响；NPs对土壤性能的短期影响 | 在实际土壤环境中，NPs的浓度是多少?NPs对土壤性能的长期影响有何区别?在研究NPs对土壤毒害效应时，没有考虑NPs、植物体、土壤、土壤中的微生物、土壤中的污染物的协同作用。开发准确的方法进行土壤样本中的NPs定量和定性分析。揭示NPs在土壤中的移动和累积机制。探索NPs与环境污染物的吸附机理等 |
表3 NPs领域的研究现状和不足
Table 3 Current research trends and knowledge gaps of NPs
| 研究课题 | 研究现状 | 研究不足 |
|---|---|---|
| NPs对植物的毒害效应 | NPs对植物生长量（植株高度、根茎直径、叶子质量）的影响；NPs对植物体产生氧化应激效应，植物体内的ROS含量和抗氧化酶活性的变化，反映出植物氧化受损的情况；NPs叶绿素、植物激素、微量营养素和必需氨基酸等植物生长指标含量的影响；NPs在植物体内的内化、运输和积累 | 降解过程及环境中与其他污染物的是否存在协同毒性?降解后的NPs在实际环境中对植物的毒害效应有何差异?考虑NPs对土壤的污染，从而对植物产生的间接毒害作用，研究NPs对土壤环境-陆生植物体系的综合效应而非单独地研究NPs对植物体的影响。针对更多的NPs种类，如聚氯乙烯（PVC）、聚乙烯（PE）等以评定各类NPs的毒理效应 |
| NPs对陆生动物的毒害效应 | NPs进入动物体内的途径；NPs在体内的累积；NPS的易位及对相应部位的毒理效应；NPs对细胞产生氧化损伤的程度 | NPs如何对各组织和器官造成毒害影响的机理?NPs在各组织和器官累积量的多少?对NPs如何引发生物的应激反应?NPs通过何种途径在生物体内运输的过程均未被探明? |
| NPs对土壤环境的影响 | NPs对土壤物理性质的影响；NPs对土壤中微生物活性、无机盐含量与比例的影响；NPs对土壤性能的短期影响 | 在实际土壤环境中，NPs的浓度是多少?NPs对土壤性能的长期影响有何区别?在研究NPs对土壤毒害效应时，没有考虑NPs、植物体、土壤、土壤中的微生物、土壤中的污染物的协同作用。开发准确的方法进行土壤样本中的NPs定量和定性分析。揭示NPs在土壤中的移动和累积机制。探索NPs与环境污染物的吸附机理等 |
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