摘要
本文通过水培苗期毒性试验,研究了23种常见作物幼苗对砷、镉毒害敏感性的差异,筛选了砷、镉高敏感作物。以高敏感植物为毒性生态受体,通过土培方式研究了砷、镉的植物毒害临界值及其土壤学的影响因素,建立了土壤砷、镉毒害临界值与关键土壤因素间的标准化关系,提出了土壤砷、镉的植物毒害临界值,为区域性土壤重金属植物毒害临界值研究提供科学依据。主要结果如下：
1、培养液中低浓度的砷、镉能促进作物的生长,尤以砷更为明显。高浓度的砷、镉会对作物产生毒害,毒害效应随砷、镉浓度的升高和处理时间的延长而加剧。水稻对砷的毒性响应比蔬菜类敏感,主要表现为新叶黄白化,沿叶脉有条纹状锈斑。镉对植物的主要毒害症状是生长受抑,新叶黄化,侧根须根增生,严重时根发褐发黑甚至腐烂。
2、综合23种作物砷、镉毒害敏感性的分类结果与作物地上部鲜重减少20%的效应浓度(EC20),确定水稻、黄瓜、红豇豆、苋菜、辣椒、茄子为砷毒害敏感作物,大白菜、油白菜、油麦菜、芥菜、小白菜为镉毒害敏感植物,这些作物可以作为进一步确定土壤和植物中砷、镉的毒害临界值的毒性生态受体以及土壤砷、镉污染的监测植物。而黄瓜则确定为镉抗性较强植物。
3、通过水稻的土培毒性测试试验,分别以稻谷产量降低10%和20%作为依据,推算出福建酸性潴育型水稻土有效砷(0.5 mol·L-1 NaH2PO4)基的植物毒害临界值EC10、EC20分别为1.42 mg·kg~(-1)和(?)3.00 mg·kg~(-1)。根据前期野外采集的水稻土全砷与0.5mol·L-1 NaH2PO4提取砷含量的回归方程,进一步推导出福建省水稻土相应的全砷植物毒害临界值EC10、EC20分别为14.07 mg·kg~(-1)和30.51 mg·kg~(-1)。以芥菜地上部减产10%和20%为依据,推算出土壤有效镉(0.1mol·L-1 CaCl2)的植物毒害临界值EC10、EC20分别为0.15 mg·kg~(-1)和0.32 mg·kg~(-1)。依据前期野外采集的福建省菜地土壤全镉与0.1 mol·L-1 CaCl2提取镉含量的回归方程推算出相应的土壤全镉的植物毒害临界值EC10、EC20分别为0.40 mg·kg~(-1)和0.70 mg·kg~(-1)。
4、通过盆栽水稻幼苗的砷毒性测试,研究了9种土壤有效砷(0.5 mol·L-1 NaH2PO4)的植物毒害效应的差异。水稻地上部鲜重和株高的EC10的变化区间为3.22～27.96 mg·kg~(-1)和3.72～29.11 mg·kg~(-1),分别代表了不同土壤间8.68倍和7.83倍的差异。水稻地上部鲜重和株高的EC20的变化区间为5.83～38.87 mg·kg~(-1)和7.12～45.60 mg·kg~(-1),表明土壤间存在6.67倍和6.40倍的差异。通过盆栽蕹菜幼苗的镉毒性测试,土壤有效镉(0.1 mol·L-1 CaCl2)基的蕹菜地上部鲜重和株高EC1o的变化区间分别为0.14～0.52 mg·kg~(-1)、0.21～0.63 mg·kg~(-1),代表了不同类型土壤间3.71倍和3倍的变异。而蕹菜地上部鲜重和株高EC20的变化区间分别为0.18～2.46 mg·kg~(-1)、0.44～3.25 mg·kg~(-1),反应出土壤间13.67倍和7.39倍的变异。
5、土壤7种理化性质与ECX的逐步回归分析表明土壤游离氧化铁是影响土壤有效砷植物毒害临界值的主要土壤学因素,土壤有效砷(0.5 mol·L-1 NaH2PO4)基植物毒害临界值ECX(株高)的修正模型如下：[EC10]=-1.451+1.160[游离氧化铁] (R2=0.718,P=0.004,n=9)[EC20]=1.659+1.791[游离氧化铁] (R2=0.764,P=0.002,n=9)[EC50]=16.367+2.715[游离氧化铁] (R2=0.827,P<0.001,n=9)土壤7种理化性质与ECX的逐步回归分析表明土壤pH是引起土壤有效镉(0.1 mol·L-1 CaCl2)ECX值变异的最重要的参数,土壤有效镉(0.1 mol·L-1 CaCl2)基植物毒害临界值ECX(地上部鲜重)的修正模型如下：[EC10]=-0.650+0.180 [pH] (R2= 0.791, P= 0.001, n=9) [EC20]=-4.072+0.954 [pH] (R2= 0.877, P< 0.001, n=9) [EC50]=-463.488+100.680 [pH] (R2= 0.747, P= 0.003, n=9)
6、依据90%的土壤受保护的原则和福建省农业土壤中pH值和游离氧化铁的调查数据,分别推算出福建省农业土壤校正后的有效砷(0.5 mol·L-1 NaH2PO4)植物毒害临界值(株高)EC10、EC20分别为5.1 mg·kg~(-1)、10.1 mg·kg~(-1),土壤有效镉(0.1 mol·L-1 CaCl2)植物毒害临界值(地上部鲜重)EC10、EC20、分别为0.19 mg·kg~(-1)、0.36 mg·kg~(-1)。
Sensitive disparity of 23 vegetable species that commonly cultivated in Fujian Province to As and Cd was studied by water culture. The most As- and Cd- sensitive species were selected and used in soil culture to study the threshold values of As and Cd phyto-toxicity, respectively. The influence of soil properties on As and Cd toxicity to plants were investigated using 9 soils. The threshold values of As and Cd phyto-toxicity were modified by the normalization relationships between the threshold values and soil properties, which will provide scientific basis for studies on the regional threshold values of soil heavy metals phyto-toxicity. The results were as follows:
1. Low concentrations of As and Cd in the culture solutions had hormesis effects to same vegetable species under water culture. However, when the concentrations of As and Cd increased, the toxicitys to the crops appeared. Rice was more sensitive than vegetables to As toxicity. The typical symptoms of As toxicity were chlorosis in new leaves, rust along leaf margins. Similarly, the typical symptoms of Cd toxicity were growth inhibition, chlorosis in new leaves, hyperplasia in fibrous roots, and black root.
2. Base on the apparent symptoms and the EC2o value (effective concentration causing a 20% reduction of shoot biomass) of each species, rice (Oryza sativa), cucumber (Cucumis sativus L.), cowpea(V. unquiculata ssp. unguioulata W.), three-coloured amaranth(Amaranthus mangostanus L), hot pepper(Capsicum annuum L), eggplant(Solanum melongena L.melongena L.) were screened as the most As sensitive vegetables, and Chinese cabbage (B. campestris L. ssp. Pekinensis (Lour.) Olsson), pakchoi (B. campestris L. ssp. Chinensis (L.)Makino), lettuce (Lactuca sativa L.) and leaf mustard(B. juncea Coss.) were screened as the most Cd sensitive vegetables. These vegetable species could be used as indicative plants in the following soil culture, which aimed at determining the threshold values of As and Cd toxicity to vegetables. Cucumber had a high resistance for Cd.
3. Based on the EC10 and EC20 of rice under soil culture, the threshold values of As toxicity were calculated to be 1.42 mg·kg~(-1) and 3.00 mg·kg~(-1) (as NaH2PO4-As), respectively. According to the regression between soil NaH2PO4-As and total As in the field, the corresponding thresholds of As toxicity (EC10 and EC20) were estimated as 14.07 mg·kg~(-1) and 30.51 mg·kg~(-1) (total As), respectively. Based on the EC10 and EC20 of leaf mustard under soil culture, the thresholds of Cd toxicity were calculated to be 0.15 mg·kg~(-1) and 0.32 mg·kg~(-1) (as CaCl2-Cd), respectively. According to the regression between soil CaCl2-Cd and total Cd in the field, the corresponding thresholds of Cd toxicity (EC 10 and EC20) were estimated as 0.40 mg·kg~(-1) and 0.70 mg·kg~(-1) (total Cd), respectively.
4. The disparity of soil As and Cd phyto-toxicity was studied by soil culture with 9 soils, using rice and water spinach as indicative plants, respectively. The EC10 (NaH2PO4-As) of rice shoot (fresh weight) and shoot height ranged from 3.22 to 27.96 mg·kg~(-1) and 3.72 to 29.11 mg·kg~(-1), representing 8.68 and 7.83-fold variations among soils respectively. The EC20 (NaH2PO4-As) of rice shoot (fresh weight) and shoot height varied between 5.83 and 38.87 mg·kg~(-1),7.12 and 45.60 mg·kg~(-1), representing 6.67 and 6.70-fold variations among soils respectively. The EC10 (CaCl2-Cd) of the shoot of water spinach (fresh weight) and shoot height ranged from 0.14 to 0.52 mg·kg~(-1) and 0.21 to 0.63 mg·kg~(-1), representing 3.71 and 3-fold variations among soils respectively. The EC20 (CaCl2-Cd) of the shoot of water spinach (fresh weight) and shoot height varied between 0.18 and 2.46 mg·kg~(-1),0.44 and 3.25 mg·kg~(-1), representing 13.67 and 7.39-fold variations among soils respectively.
5. Stepwise regression analysis identified that free iron was the main factors affected soil Asbioavailability. The modified prediction model of the ECX(plant height) of soil As phyto-toxicity as NaH2PO4-As was [EC10]=-1.451+1.160 [free iron] (R2= 0.718, P= 0.004, n=9) [EC20]= 1.659+1.791 [free iron] (R2= 0.764, P= 0.002, n=9) [EC50]= 16.367+2.715[free iron] (R2= 0.827, P< 0.001, n=9)
However, Soil pH was the main factors affected the availability of Cd in soil. The modified prediction model of the ECX (shoot fresh weight) of soil Cd phytoxicity based on CaCl2-Cd was [EC10]=-0.650+0.180 [pH] (R2= 0.791, P= 0.001, n=9) [EC20]=-4.072+0.954 [pH] (R2= 0.877, P< 0.001, n=9) [EC50]=-463.488+100.680 [pH] (R2= 0.747, P= 0.003, n=9)
6. In order to protect 90 percent of soils from As and Cd pollution, the thresholds of As and Cd phyto-toxicity of agriculture soils were calculated from soil pH and free iron of Fujian field survey. The As thresholds of EC10 and EC20 by rice shoot height were 5.1 mg·kg~(-1) and 10.1 mg·kg~(-1) (NaH2PO4-As), respectively, while the Cd thresholds of EC10 and EC20 by the water spinach shoot were 0.19 mg·kg~(-1) and 0.36 mg·kg~(-1) (CaCl2-Cd), respectively.
引文
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