不同水分管理模式下坡缕石修复稻田土壤镉污染效果

李剑睿; 徐应明

doi:10.19336/j.cnki.trtb.2021122901

不同水分管理模式下坡缕石修复稻田土壤镉污染效果

doi: 10.19336/j.cnki.trtb.2021122901

李剑睿^1,,
徐应明²

1.
太原工业学院，山西太原 030008
2.
农业农村部环境保护科研监测所，天津 300191

基金项目: 国家自然科学基金（201107056）资助

详细信息

作者简介:
李剑睿（1981−），男，山西朔州，博士研究生，副教授，土壤生态与修复。E-mail: jianrui-419@163.com

中图分类号: X53
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- 被引次数: 0
出版历程
- 收稿日期: 2021-12-29
- 录用日期: 2022-02-25
- 修回日期: 2022-02-11
- 刊出日期: 2022-06-17

Use of Palygorskite to Remediate Cd polluted Paddy Soils under Different Water Managements

LI Jian-rui^1
,,
XU Ying-ming²

1.
Taiyuan Institute of Technology, Taiyuan 030008, China
2.
Agro-Environmental Protection Institute, Tianjin 300191, China

摘要

摘要: 目的探究在合理的水分管理模式下提高坡缕石钝化稻田土壤镉的效率，及坡缕石施加对土壤理化性质、环境质量和水稻抗氧化胁迫的影响。方法采用盆栽试验方法，试验设置长期淹水、传统灌溉和湿润灌溉3种水分管理措施，每一水分管理模式下设0%、0.5%、1.0%、1.5%、2.0%和2.5% 6个坡缕石施加浓度，共18个处理，通过测定土壤pH、zeta电位、有效态镉、稻米生物量、稻米镉含量、土壤酶和叶抗氧化酶活性，分析不同水分管理措施与坡缕石用量组合修复镉污染的效果。结果长期淹水、传统灌溉和湿润灌溉下，坡缕石处理土壤pH分别增加0.49 ~ 1.24、0.49 ~ 1.47和0.42 ~ 1.64个单位，0.025 mol L⁻¹ HCl提取态镉含量分别下降15.4% ~ 46.2%，11.5% ~ 39.7%和11.4% ~ 32.4%，毒性浸出法提取态镉最大降幅分别为47.4%、42.4%和40.2%（P < 0.05）。未施加坡缕石条件下，与传统灌溉比，长期淹水、湿润灌溉的稻米生物量降低11.2%和19.3%（P < 0.05）。3种水分管理模式下，坡缕石处理的稻米镉含量分别下降21.9% ~ 75.0%，17.8% ~ 70.2%和17.4% ~ 66.5%，土壤磷酸酶活性最大增幅分别为40.0%、57.1%和40.9%，叶超氧化物歧化酶活性最大增幅分别为33.9%、50.2%和37.4%（P < 0.05）。结论长期淹水下坡缕石钝化土壤镉的效率最高，1.0%坡缕石施加使稻米镉含量降至我国食品污染物含量限量标准0.20 mg kg⁻¹（GB 2762—2012）以下，长期淹水联合坡缕石施加组合为镉污染稻田土壤修复技术。
- 稻田土壤 /
- 镉 /
- 水分管理 /
- 坡缕石 /
- 修复
Abstract: Objective The water management model plays an important role in remediation of cadmium (Cd) polluted paddy soils. The reasonable water management regime is explored to promote the immobilization of Cd by palygorskite in contaminated paddy soils and investigate the effects of palygorskite addition on physicochemical property and environmental quality of soil and resistance of rice plant to Cd oxidative stress. Method There were totally 18 treatments in the pot experiment, which included 3 water managements of continuous flooding (5-7 cm surface water during the whole growth period of rice plant, with a scale line on the sidewall of pot), traditional irrigation (moist soil surface during the late tillering state and grain filling stage, and 5-7 cm surface water during the other growth stages of rice plant) and wetting irrigation (moist soil surface during the entire growth period of rice plant. The deionized water (2.3 kg) was added in the pot according to soil moisture content of 75% field water capacity and 8.0 kg of soil sample added in the pot) and six palygorskite treatments included the doses of 0, 0.5%, 1.0%, 1.5%, 2.0% and 2.5% in paddy soils. The effects of palygorskite addition on pH, zeta potential and contents of chemically extractable Cd (0.025 mol L⁻¹ HCl extractable Cd and Toxicity Characteristic Leaching Procedure, TCLP extractable Cd) were determined in paddy soils, and biomasses and concentrations of Cd in brown rice were tested in the pot experiment, as well as the activities of enzymes in soils and antioxidant enzymes in leaves of rice plant. Result After the palygorskite was added to paddy soils, the pH increased by 0.49-1.24 units under continuous flooding, 0.49-1.47 units under traditional irrigation, and 0.42-1.64 units under wetting irrigation (P < 0.05). The absolute values of zeta potential in amended soils rose significantly. The contents of chemically extractable Cd in treated soils declined significantly, with reductions of 15.4%-46.2%, 11.5%-39.7% and 11.4%-32.4% for the 0.025 mol L⁻¹ HCl extractable Cd and maximum decreases of 47.4%, 42.4% and 40.2% for the TCLP extractable Cd under 3 water managements (P < 0.05). In paddy soils untreated with palygorskite, the biomasses of brown rice reduced by 11.2% under continuous flooding and 19.3% under wetting irrigation in contrast to traditional irrigation (P < 0.05). The concentrations of Cd in brown rice in amended soils reduced by 21.9%-75.0% under continuous flooding, 17.8%-70.2% under traditional irrigation, and 17.4%-66.5% under wetting irrigation (P < 0.05). The activities of phosphatase in paddy soils amended with palygorskite under 3 water managements rose significantly with maximum increases of 40.0%, 57.1% and 40.9%, and the activities of superoxide dismutase (SOD) in leaves of rice plant upon palygorskite treatment increased by 33.9%, 50.2% and 37.4% maximally (P < 0.05). Conclusion The continuous flooding promotes the Cd immobilization by palygorskite in heavy metal contaminated paddy soils with a maximum reduction of content of chemically extractable Cd among 3 water managements. The 1.0% palygorskite treatment causes the concentration of Cd in brown rice lower than Chinese standard of 0.20 mg kg⁻¹ (GB 2762—2012, Maximum permissible concentration of contaminants in food in China). The palygorskite addition combined with continuous flooding management, could be recommended as a practical measure for immobilization remediation of Cd-polluted paddy soils.
- Paddy soil /
- Cadmium /
- Water management /
- Palygorskite /
- Remediation

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图 1 土壤zeta电位

Figure 1. The zeta potential in soils

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图 2 稻米生物量

Figure 2. The biomasses of brown rice

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图 3 稻米Cd含量

柱底不同字母表示同一水分管理下坡缕石处理间差异显著，柱顶不同字母表示同一坡缕石处理下水分管理间差异显著（P<0.05）。

Figure 3. The concentrations of Cd in brown rice

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表 1 土壤pH和有效态镉

Table 1. The pH and contents of available Cd in soils

水分管理 Water management	坡缕石用量（%） Palygorskite addition	pH	有效态镉 (mg kg⁻¹) Available Cd
水分管理 Water management	坡缕石用量（%） Palygorskite addition	pH	TCLP提取镉 TCLP extractable Cd	0.025 mol L⁻¹盐酸提取镉 0.025 mol L⁻¹ HCl extractable Cd
长期淹水	0	5.69 ± 0.18 de	0.78 ± 0.08 b	0.65 ± 0.09 cd
	0.5	6.18 ± 0.23 cd	0.69 ± 0.05 bc	0.55 ± 0.07 d
	1.0	6.73 ± 0.21 ab	0.56 ± 0.07 cd	0.48 ± 0.08 e
	1.5	6.88 ± 0.15 a	0.48 ± 0.06 d	0.43 ± 0.11 ef
	2.0	6.87 ± 0.21 a	0.41 ± 0.09 e	0.39 ± 0.15 f
	2.5	6.93 ± 0.13 a	0.43 ± 0.11 e	0.35 ± 0.11 f

传统灌溉	0	5.44 ± 0.18 e	0.85 ± 0.13 ab	0.78 ± 0.07 b
	0.5	5.93 ± 0.21 d	0.74 ± 0.07 b	0.69 ± 0.07 c
	1.0	6.59 ± 0.17 b	0.65 ± 0.11 bc	0.63 ± 0.08 cd
	1.5	6.81 ± 0.25 ab	0.58 ± 0.15 cd	0.58 ± 0.06 d
	2.0	6.91 ± 0.15 a	0.49 ± 0.13 d	0.47 ± 0.11 e
	2.5	6.90 ± 0.17 a	0.55 ± 0.11 cd	0.57 ± 0.08 d

湿润灌溉	0	5.25 ± 0.13 f	0.97 ± 0.07 a	1.05 ± 0.05 a
	0.5	5.67 ± 0.23 de	0.87 ± 0.08 ab	0.93 ± 0.08 ab
	1.0	6.33 ± 0.11 c	0.73 ± 0.07 b	0.82 ± 0.05 b
	1.5	6.55 ± 0.17 b	0.67 ± 0.06 bc	0.78 ± 0.06 b
	2.0	6.82 ± 0.21 ab	0.62 ± 0.08 c	0.71 ± 0.09 c
	2.5	6.89 ± 0.15 a	0.58 ± 0.06 cd	0.74 ± 0.13 bc
注：同列不同字母表示相同指标不同处理间差异显著（P < 0.05）。

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表 2 土壤酶和叶抗氧化酶活性

Table 2. The activities of enzymes in soils and antioxidant enzymes in leaves

水分管理 Water management	坡缕石用量（%） Palygorskite addition	土壤酶(mg g⁻¹ h⁻¹) Soil enzyme		抗氧化酶(U g⁻¹) Antioxidant enzyme
水分管理 Water management	坡缕石用量（%） Palygorskite addition	蔗糖酶 Sucrase	磷酸酶 Phosphatase	超氧化物歧化酶 Superoxide dismutase	过氧化物酶 Peroxidase
长期淹水	0	5.3 ± 0.31 d	1.5 ± 0.09 e	301 ± 17 c	431 ± 27 cd
	0.5	5.5 ± 0.28 cd	1.8 ± 0.11 d	331 ± 19 bc	457 ± 21 c
	1.0	5.2 ± 0.25 d	1.7 ± 0.08 de	382 ± 23 ab	528 ± 23 bc
	1.5	5.6 ± 0.33 c	1.9 ± 0.13 d	391 ± 18 a	583 ± 23 b
	2.0	5.7 ± 0.27 c	2.1 ± 0.17 cd	403 ± 25 a	607 ± 25 ab
	2.5	5.3 ± 0.35 d	2.1 ± 0.18 cd	372 ± 25 b	631 ± 28 a

传统灌溉	0	5.9 ± 0.21 bc	2.1 ± 0.25 cd	261 ± 17 d	373 ± 19 de
	0.5	6.1 ± 0.31 b	2.3 ± 0.41 c	303 ± 13 c	403 ± 18 d
	1.0	5.8 ± 0.37 bc	2.8 ± 0.25 b	356 ± 21 b	452 ± 17 c
	1.5	6.2 ± 0.37 b	3.0 ± 0.17 ab	368 ± 16 b	532 ± 23 bc
	2.0	6.0 ± 0.33 b	3.3 ± 0.13 a	383 ± 19 ab	558 ± 21 b
	2.5	6.2 ± 0.35 b	3.1 ± 0.21 ab	392 ± 23 a	579 ± 19 b

湿润灌溉	0	6.7 ± 0.31 ab	2.2 ± 0.23 c	198 ± 19 e	268 ± 15 g
	0.5	6.9 ± 0.33 a	2.3 ± 0.23 c	227 ± 13 de	292 ± 22 f
	1.0	6.6 ± 0.35 ab	2.7 ± 0.33 b	236 ± 15 de	323 ± 19 e
	1.5	6.8 ± 0.27 a	3.0 ± 0.28 ab	261 ± 13 d	405 ± 18 d
	2.0	7.0 ± 0.33 a	2.9 ± 0.35 b	251 ± 15 d	419 ± 17 cd
	2.5	6.8 ± 0.25 a	3.1 ± 0.43 ab	272 ± 21 cd	385 ± 23 de
注：同列不同字母表示相同指标不同处理间差异显著（P < 0.05）。

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参考文献(25)

[1]	宋伟, 陈百明, 刘琳. 中国耕地土壤重金属污染概况[J]. 水土保持研究, 2013, 20(2): 293 − 298.
[2]	Rodríguez Martín J A, De Arana C, Ramos-Miras J J, et al. Impact of 70 years urban growth associated with heavy metal pollution[J]. Environmental Pollution, 2015, 196: 156 − 163. doi: 10.1016/j.envpol.2014.10.014
[3]	Song Y, Wang Y, Mao W F, et al. Dietary cadmium exposure assessment among the Chinese population[J]. Plos One, 2017, 12: e0177978. doi: 10.1371/journal.pone.0177978
[4]	汪鹏, 王静, 陈宏坪, 等. 我国稻田系统镉污染风险与阻控[J]. 农业环境科学学报, 2018, 37(7): 1409 − 1417. doi: 10.11654/jaes.2018-0453
[5]	韩君, 梁学峰, 徐应明, 等. 黏土矿物原位修复镉污染稻田及其对土壤氮磷和酶活性的影响[J]. 环境科学学报, 2014, 34(11): 2853 − 2860.
[6]	Sun Y B, Sun G H, Xu Y M, et al. Evaluation of the effectiveness of sepiolite, bentonite, and phosphate amendments on the stabilization remediation of cadmium-contaminated soils[J]. Journal of Environmental Management, 2016, 166: 204 − 210.
[7]	Liang X F, Xu Y, Xu Y M, et al. Two-year stability of immobilization effect of sepiolite on Cd contaminants in paddy soil[J]. Environmental Science and Pollution Research, 2016, 23: 12922 − 12931. doi: 10.1007/s11356-016-6466-y
[8]	Yin X L, Xu Y M, Huang R, et al. Remediation mechanisms for Cd-contaminated soil using natural sepiolite at the field scale[J]. Environmental Science:Processes & Impacts, 2017, 19: 1563 − 1570.
[9]	孙国红, 王鹏超, 徐应明, 等. 施用钾肥对稻田土镉污染钝化修复效应影响研究[J]. 灌溉排水学报, 2019, 38(5): 38 − 45.
[10]	Sun Y B, Sun G H, Xu Y M, et al. Assessment of sepiolite for immobilization of cadmium-contaminated soils[J]. Geoderma, 2013, 193-194: 149 − 155. doi: 10.1016/j.geoderma.2012.07.012
[11]	李园星露, 叶长城, 刘玉玲, 等. 生物炭耦合水分管理对稻田土壤As-Cd生物有效性及稻米累积的影响[J]. 农业环境科学学报, 2018, 37(4): 696 − 704. doi: 10.11654/jaes.2017-1505
[12]	王惠明, 林小兵, 黄欠如, 等. 不同灌溉模式对稻田土壤及糙米重金属积累的影响[J]. 生态科学, 2019, 38(3): 152 − 158.
[13]	鲁如坤. 土壤农业化学分析方法[M]. 北京: 中国农业科技出版社, 2000.
[14]	Liang X F, Han J, Xu Y M, et al. In situ field-scale remediation of Cd polluted paddy soil using sepiolite and palygorskite[J]. Geoderma, 2014, 235-236: 9 − 18. doi: 10.1016/j.geoderma.2014.06.029
[15]	孙叶芳, 谢正苗, 徐建明, 等. TCLP法评价矿区土壤重金属的生态环境风险[J]. 环境科学, 2005, 26(3): 152 − 156. doi: 10.3321/j.issn:0250-3301.2005.03.031
[16]	郭文燕, 田雄, 李尚锟, 等. 镉胁迫对抽穗期水稻生理生化特性的影响[J]. 安徽农业科学, 2018, 46(14): 37 − 43. doi: 10.3969/j.issn.0517-6611.2018.14.011
[17]	Chen H M, Zheng C R, Tu C, et al. Chemical methods and phytoremediation of soil contaminated with heavy metals[J]. Chemosphere, 2000, 41: 229 − 234. doi: 10.1016/S0045-6535(99)00415-4
[18]	Bradl H B. Adsorption of heavy metal ions on soils and soils constituents[J]. Journal of Colloid and Interface Science, 2004, 277: 1 − 18. doi: 10.1016/j.jcis.2004.04.005
[19]	于寿娜, 廖敏, 黄昌勇. 镉、汞复合污染对土壤脲酶和酸性磷酸酶活性的影响[J]. 应用生态学报, 2008, 19(8): 1841 − 1847.
[20]	刘善江, 夏雪, 陈桂梅, 等. 土壤酶的研究进展[J]. 中国农学通报, 2011, 27(21): 1 − 7.
[21]	Lombi E, Hamon R E, McGrath S P, et al. Lability of Cd, Cu, and Zn in polluted soils treated with lime, beringite, and red mud and identification of a non-labile colloidal fraction of metals using isotopic techniques[J]. Environmental Science and Technology, 2003, 37: 979 − 984. doi: 10.1021/es026083w
[22]	杜志敏, 郝建设, 周静, 等. 四种改良剂对Cu、Cd复合污染土壤中Cu、Cd形态和土壤酶活性的影响[J]. 生态环境学报, 2011, 20(10): 1507 − 1512. doi: 10.3969/j.issn.1674-5906.2011.10.020
[23]	杨叶萍, 简敏菲, 余厚平, 等. 镉胁迫对苎麻(Boehmeria nivea)根系及叶片抗氧化系统的影响[J]. 生态毒理学报, 2016, 11(4): 184 − 193.
[24]	张琼, 陆銮眉, 戴清霞, 等. 镉胁迫对水仙根系抗氧化系统的影响[J]. 福建农业学报, 2016, 31(6): 591 − 595.
[25]	Jiang J, Qin C X, Shu X Q, et al. Effects of copper on induction of thiol-compounds and antioxidant enzymes by the fruiting body of Oudemansiella radicata[J]. Ecotoxicology and Environmental Safety, 2015, 111: 60 − 65. doi: 10.1016/j.ecoenv.2014.09.014