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Article

Effects of Application of Pig Manure on the Accumulation of Heavy Metals in Rice

by
Wenchong Lan
1,
Chunxia Yao
2,*,
Fan Luo
1,
Zhi Jin
1,
Siwen Lu
1,
Jun Li
1,
Xindong Wang
1 and
Xuefeng Hu
1,*
1
School of Environmental and Chemical Engineering, Shanghai University, Shanghai 200444, China
2
Laboratory of Quality and Safety Risk Assessment for Agro-Products (Shanghai), China Ministry of Agriculture, Institute for Agro-Food Standards and Testing Technology, Shanghai Academy of Agricultural Sciences, Shanghai 201403, China
*
Authors to whom correspondence should be addressed.
Plants 2022, 11(2), 207; https://doi.org/10.3390/plants11020207
Submission received: 12 December 2021 / Revised: 6 January 2022 / Accepted: 10 January 2022 / Published: 14 January 2022
(This article belongs to the Section Plant Response to Abiotic Stress and Climate Change)
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Versions Notes

Abstract

:
Pig manure (PM) is often highly enriched in heavy metals, such as Cu and Zn, due to the wide use of feed additives. To study the potential risks of heavy metal accumulation in the soil and rice grains by the application of PM and other organic manure, a four-year field experiment was conducted in the suburb of Shanghai, southeast China. The contents of Cu, Zn, Pb, and Cd in the soils and rice plants by the treatments of PM and fungal culturing residues (FCR) show a trend of annual increase. Those in the soils and rice by the PM treatment are raised even more significantly. Cu and Zn contents in the soil and rice roots by the PM are significantly higher than those by the non-fertilizer control (CK) during the four years, and Pb and Cd also significantly higher than CK in the latter two years. Heavy metals taken up by the rice plants are mostly retained in the roots. Cu and Zn contents in the rice plants are in the decreasing order of roots > grains > stems > leaves, and Pb and Cd in the order of roots > stems > leaves > grains. Cu, Zn, Pb, and Cd contents in the soils by the PM treatment increase by 73%, 32%, 106%, and 127% on annual average, and those in the brown rice by 104%, 98%, 275%, and 199%, respectively. The contents of Cu, Zn, Pb, and Cd in the brown rice of the treatments are significantly correlated with those in the soils and rice roots (p < 0.05), suggesting the heavy metals accumulated in the rice grains come from the application of PM and FCR. Though the contents of heavy metals in the brown rice during the four experimental years are still within the safe levels, the risks of their accumulative increments, especially by long-term application of PM, can never be neglected.

1. Introduction

Excessive application of chemical fertilizers often leads to agricultural diffuse pollution, causing the eutrophication of surface water and contamination of groundwater [1]. In recent decades, the replacement of chemical fertilizers by organic manure has been highly encouraged in China. The number of live pigs attained 680 million in China in 2016 [2]. PM is not only an important source of organic manure but also a link to the circulation of the livestock-soil-plant system [3]. Long-term application of PM significantly increases the contents of organic matter and nutrients in soils [4].
To prevent pigs from infecting intestinal pathogen and supplement nutrients, some trace elements such as Cu, Zn, Fe, and Mn are often added into livestock feed [5], thus causing the enrichment of heavy metals in the PM [6,7]. According to the investigations, the rates of livestock manures with Cd and Pb content exceeding the safe limits of organic fertilizers are 12.3% and 2.6%, and those with Cu and Zn exceeding the limits are 53.9% and 45.7%, respectively [8]. Long-term application of livestock manures hence often leads to the accumulation of heavy metals in agricultural soils [9,10]. PM is particularly highly enriched in Cu and Zn [11,12,13,14,15,16,17]. These in the PM released from an intensively raising farm in China attain as high as 1726 mg/kg and 1506 mg/kg, respectively [18]. The application of PM often causes the contamination of heavy metals and antibiotics in soils [19,20].
Rice is the staple food of nearly half of the world’s population [21]. The rice grain, however, is inclined to accumulate Cd and other toxic metals, even growing on Cd-low soils. Therefore, it never seldom occurs that Cd content in the rice in the market exceeds the safe limit (0.2 mg/kg) [22,23]. Whether long-term application of PM influences the contents of Cd and other toxic heavy metals in rice grains should be paid close attention to.
In this study, a field experiment of application of PM and two FCR are carried out in the suburb of Shanghai for four consecutive years from 2017 to 2020. The contents of Cu, Zn, Pb, and Cd in the soils, rice plants, and grains by the different fertilizer treatments are detected to study the effects of the application of PM and FCR on the accumulation of toxic heavy metals in rice grains and to evaluate its potential edible risks.

2. Results

2.1. Effects of Application of PM and FCR on Soil Nutrients

2.1.1. Organic Matter (OM) Content

The content of OM in the soils by the agaricusbisporus (AB), flammulinavelutipes (FV), and PM treatments shows a trend of annual increase (Figure 1). That in the AB, FV, and PM soils is significantly higher than CK (p < 0.05) in each experimental year, which increases by 38.0%, 34.2%, and 48.9% on annual average, respectively. Especially, OM content in the PM soil is significantly higher than that in AB, FV, and CK.

2.1.2. Total N (TN) and Alkaline Hydrolyzed N (AN) Contents

The contents of TN and AN in the AB, FV, and PM soils also increase annually (Figure 2). Compared with CK, these in the AB soil increase by 25.2% and 23.0% on annual average during the four experimental years; these in FV increase by 37.7% and 21.2%; these in PM increase by 36.8% and 33.8%, respectively. The contents of TN and AN in the PM soil in the fourth year are 1.1 and 1.9 times those in the first year and are higher than those in the AB and FV soils.

2.1.3. Total P (TP) and Available P (AP) Contents

The contents of TP and AP in the PM, AB, and FV soils also increase annually (Figure 3). Compared with CK, these in the AB soil increase by 121.6% and 135.0% on annual average during the four experimental years; these in the FV soil increase by 109.0% and 143.2%; these in the PM soil increase by 163.9% and 254.7%, respectively. TP and AP contents in the PM soil on the fourth year are 2.7 and 3.0 times those on the first year, respectively. The content of AP in the PM soil is significantly higher than that in the AB and FV soils (p < 0.05), and TP in the PM soil is also higher than in the AB and FV soils (p > 0.05) in the fourth year, suggesting that the PM application is more beneficial to P increase in the soil.

2.1.4. Total K (TK) and Available K (AK) Contents

The contents of TK and AK in the PM, AB, and FV soils also increase annually (Figure 4). During the four experimental years, the contents of TK and AK in the PM, AB, and FV soils are significantly higher than CK (p < 0.05). Compared with CK, moreover, these in the AB soil increase by 37.1% and 93.0% on annual average; these in the FV soil increase by 49.2% and 60.6%; these in the PM soil increase by 62.3% and 93.6%, respectively. TK and AK contents in the PM soil in the fourth year are 1.6 and 1.7 times those in the first year, respectively. The content of AK in the PM soil in the third and fourth years is significantly higher than that in the AB and FV soils (p < 0.05).

2.2. Effects of Application of PM and FCR on Rice Yield

During the four experimental years, the yield of rice grain by the AB, FV, and PM treatments increases by 40.0%, 45.1%, and 49.8% on annual average, respectively (Figure 5). The effect of yield increase by the PM treatment is significantly higher than that of AB and FV. The grain yield of the three fertilizer treatments in the second and third years is significantly higher than that of the first year (p < 0.05). That of the fourth year, however, is significantly reduced, possibly related to unsuitable climate and severer incidence of rice pests and diseases.

2.3. Effects of Application of PM and FCR on the Accumulation of Heavy Metals in the Soil Plant System

2.3.1. Heavy Metal Contents in the Soils

During the four experimental years, the contents of Cu, Zn, Pb, and Cd in the PM, AB, and FV soils also show a trend of annual increase, which are mostly higher than CK (Figure 6). Especially, the contents of Cu and Zn in the PM soil during the four years are significantly higher than CK (p < 0.05) (Figure 6a,b), and Pb and Cd in the latter two years are also significantly higher than CK (p < 0.05) (Figure 6c,d).
During the four years from 2017 to 2020, Cu content in the PM soils is 1.5, 1.4, 1.5, and 1.7 times higher than CK (Figure 6a), and Zn content is 1.2, 1.2, 1.2, and 1.3 times higher than CK (Figure 6b), respectively. Pb content in the PM soil in the latter two years is 1.9 and 2.1 times higher than CK (Figure 6c), and Cd content is 1.2 and 2.3 times higher than CK (Figure 6d), respectively.

2.3.2. Heavy Metal Contents in the Rice Roots

The contents of Cu, Zn, Pb, and Cd in the rice roots of the PM, AB, and FV treatments all show an annual increasing trend and attain maximum values in the fourth year (Figure 7).
Cu content in the rice roots of the PM, AB, and FV treatments in the fourth year is mostly significantly higher than that in the earlier three years (p < 0.05) (Figure 7a). Especially, that of PM on the fourth year attains 22.82 mg/kg, which is 2.9, 1.5, and 1.1 times higher than that of CK, AB, and FV in the same year, respectively. During the four experimental years, the Cu content of the PM roots is significantly higher than that of CK and AB (p < 0.05). Meanwhile, Zn content in the rice roots of the three treatments in the latter three years is significantly higher than that in the first year (p < 0.05) (Figure 7b). That in the PM roots in the latter two years is significantly higher than in the first two years (p < 0.05). Zn content in the PM roots is significantly higher than that in CK, AB, and FV (p < 0.05) during the four years. That on the fourth year attains as high as 62.84 mg/kg, which is 3.0, 1.6, and 1.6 times higher than in CK, AB, and FV, respectively. Pb content in the PM roots in the latter two years is significantly higher than that in CK and AB (p < 0.05) (Figure 7c). That on the fourth year attains 9.33 mg/kg, which is 2.0, 1.3, and 1.1 times higher than that of CK, AB, and FV, respectively. Cd content in the PM roots during the four experimental years is higher than that of CK, AB, and FV (Figure 7d). That on the fourth year attains 1.48 mg/kg, which is 2.7 times higher than CK and 3.5 times higher than in the first year.

2.3.3. Heavy Metal Content in the Rice Grains

The contents of Cu, Zn, Pb, and Cd in the brown rice of the three treatments also show a trend of annual increase, correlated with the annual increase in heavy metals in the soils and rice roots. Especially, these of PM during the four years are mostly significantly higher than CK (p < 0.05), and also mostly higher than these of AB and FV (Figure 8).
Cu content in the brown rice of PM is enhanced even more significantly and increases by 14.9%, 74.4%, 80.7%, and 103.6%annuallyduring the four years, compared with CK; that of AB increases by 7.5%, 20.6%, 77.3%, and 80.0%; that of FV increases by 11.3%, 51.4%, 71.2%, and 73.7%, respectively (Figure 8a).Zn content in the brown rice of PM increases by 12.9%, 37.8%, 46.1%, and 97.5%; that of the AB by 5.2%, 24.1%, 42.8%, and 45.3%; that of the FV by 3.6%, 25.5%, 30.2%, and 71.8%, respectively (Figure 8b).Pb content in the brown rice of the PM increases by 16.0%, 9.2%, 4.6%, and 274.9%; that of AB increases by 6.0%, 10.2%,14.0% and 128.3%; that of FV increases by 9.2%, 5.4%, 17.3%, and 134.3%, respectively (Figure 8c). Cd content of the brown rice of PM increases by 28.5%, 112.8%, 147.8%, and 198.9%; that of AB increases by 7.3%, 71.2%, 84.7%, and 155.4%; that of FV increases by 35.2%, 62.8%, 92.2%, and 140.7%, respectively (Figure 8d).

2.3.4. Distribution of Heavy Metals in the Rice Plants

The distribution of Cu, Zn, Pb, and Cd in the different tissues of rice plants by the three treatments on the fourth year shows a similar rule (Figure 9): Cu content in the rice roots is significantly higher than that in the rice stems, leaves and brown rice (p < 0.05) (Figure 9a). Especially, Cu in the rice roots of PM is 11.5, 15.1, and 7.7 times that in the rice stems, leaves, and brown rice, respectively. Moreover, Cu content in brown rice is higher than that in rice stems and leaves (p < 0.05). Zn content in the rice roots and brown rice is also higher than that in the stems and leaves (Figure 9b). Especially, that of PM attains 62.84 and 30.90 mg/kg, respectively, which is significantly higher than in the stems and leaves (p < 0.05).
Pb content in the rice roots is significantly higher than that in the stems, leaves, and brown rice (p < 0.05), while that in the stems is also significantly higher than in the leaves and rice (p < 0.05) (Figure 9c). Cd content in the different tissue of rice plants shares a similar distribution with Pb (Figure 9d).

3. Discussion

3.1. Enhancements of Soil Nutrients by Application of PM and FCR

Soil fertility is gradually improved after the application of PM and FCR. The content of OM in the soils of AB, FV and PM increases by 38.0%, 34.2%, and 48.9% on annual average during the four years; TN, 25.1%, 38.4%, and 37.1%; AN, 23.0%, 21.2%, and 33.8%; TP, 121.6%, 109.4%, and 163.9%; AP, 135.0%, 143.2%, and 254.7%; TK, 37.1%, 49.2%, and 62.3%; AK 93.0%, 60.6%, and 93.6%, respectively. During the four experimental years, the content of OM in the soils of PM is significantly higher than that of AB, FV, and CK (Figure 1). The application of PM and FCR increases the content of soil OM and improves soil quality significantly [24,25]. The effects of PM application on the improvement of soil fertility are even more significant [26]. The excessive application of PM, however, often causes the accumulation of P in soils (Figure 3) and increases the risk of agricultural diffuse pollution [27].
Correlating with the annual enhancement of soil nutrients, the yield of rice grain of AB, FV, and PM increases by 40.0%, 45.1%, and 49.8%, on annual average, respectively. There is a significant positive correlation between the content of OM in the soils and the yield of rice grains (r = 0.886, n = 12; p < 0.01), further suggesting that the application of organic manure has contributed to the yield increase. The effects of yield increase by PM are even more significant as PM contains high content of nutrients [28,29]. Moreover, higher content of Zn in PM may also contribute to yield increase [30,31]. Over the first three years, the grain yield by the AB, FV, and PM continuously increases, and that of PM is significantly higher than of AB and FV, which is consistent with the previous results [32,33,34]. In the fourth year, the yield of rice grain of the treatments, however, is significantly reduced (Figure 5), which may be related to the unsuitable climatic conditions and high incidences of rice pests and diseases this year.

3.2. Accumulation of Heavy Metals in the Soils Caused by Application of PM and FCR

Feed additives commonly used in pig breeding often contain a certain amount of heavy metals, such as Cu, Zn, Fe, and Mn, which are used to prevent diseases, supplement nutrients and improve the growth of pigs [35,36,37]. The heavy metals added into feed are finally mostly released with dung [37,38]. PM is thus often highly enriched in Cu and Zn [39,40] and sometimes even contains toxic metals or metalloids such as Cd and As [41,42]. Toxic heavy metals in organic fertilizers that are made from animal manures therefore often exceed the safe limits [43]. The contents of Cu and Zn in 117 samples of organic fertilizers in northern China are 75.2 mg/kg and 581.9 mg/kg on average, respectively [44]. Cu content in the PM used in this study is 5.5 and 20.8 times that of FV and AB, and Zn content 4.4 and 16.3 times that of FV and AB, respectively (Table 1. The contents of Pb and Cd in the PM are also significantly higher than those in the two FCR (p < 0.05) (Table 1).
The inputs of heavy metals into the soils through the application of PM and FCR are much higher than the outputs by the uptake of rice plants, resulting in the annual increase in Cu, Zn, Pb, and Cd contents in the soils for the consecutive four years (Figure 10). The contents of Cu and Zn in the PM soil are significantly higher than CK (p < 0.05) during the four years, and the contents of Pb and Cd in the PM soil are also significantly higher than CK (p < 0.05) in the latter two years. The contents of Zn and Pb in the AB and FV soils are significantly higher than CK (p < 0.05) in the latter two years, and Cd content in the AB and FV soils is also significantly higher than CK (p < 0.05) on the fourth years, which is, however, still much lower than in the PM soil (Figure 6). This suggests that the contents of heavy metals in the soils are significantly raised by the application of PM and FCR, and those by the application of PM are more significant. Cu content in the soils of PM annually increases by 8.3%, 9.3%, and 15.0%; Zn content by 2.6%, 1.4%, and 13.7%; Pb content by 3.5%, 96.5%, and 7.0%; Cd content by 0.4%, 14.4%, and 73.3%, respectively.
Pb and Cd are even more rapidly accumulated in the soils than Cu and Zn. The contents of Pb and Cd in the PM soil in the fourth year are 2.2 and 2.0 times that on the first year, while Cu and Zn in the fourth year are 1.4 and 1.2 times that on the first year (Figure 10). It may be because both Cu and Zn are nutrient elements and highly taken up by crops, while Cd and Pb are toxic to and less assimilated by crops and thus are mostly adsorbed by soil particles. Cd is easily accumulated in soil by fertilizer application [45]. Cd in the cultivated layers of soil is significantly raised after the application of PM for 10 years [42,46]. The high content of P in PM may also contribute to the accumulation of toxic metals in the soil as the combination of P with Cd and Pb [47,48].
The content of OM in the soils is significantly correlated with that of Cu, Zn, Pb, and Cd in the soils (r = 0.856, 0.803, 0.928, 0.973, n = 12; p < 0.01), further suggesting that the accumulation of heavy metals in the soils is mainly attributed to the application of organic manure. On the other hand, the high content of OM is beneficial to the accumulation of heavy metals due to the function of chelation [49,50,51,52]. The higher the content of OM in the soil is, the more Cd is accumulated in the soil [53].
The contents of Cu and Zn in the PM are over the safe limits of organic fertilizers; Pb and C dare below the safe limits (Cu < 100; Zn < 500; Cd < 3; Pb < 100) specified by the China national standards (NY-525-2012) [54]. The risks of heavy metal accumulation caused by the long-term application of PM and FCR can never be neglected. Long-term application of livestock manure, especially PM, is one of the important reasons for the accumulation of heavy metals in farmland [10,25,55,56]. The application of PM results in the enhancement of Cu, Zn, Pb, and Cd contents in soils [57,58,59]. In this study, the annual increments of Cu, Zn, Pb, and Cd in the soil are 2.33, 3.97, 4.80, and 0.024 mg/kg on annual average, respectively. According to the rates of increase, the contents of Cu, Zn, Pb, and Cd in the soil will exceed the safe limits (Cu ≤ 100 mg/kg; Zn ≤ 250 mg/kg; Pb ≤ 140 mg/kg; Cd ≤ 0.60 mg/kg) according to the China national standards (GB15618-2018) [60] after the application of PM for 35, 47, 27, and 22 years.

3.3. Distribution of Heavy Metals in Rice Plants

Roots are the passageway of heavy metals from the soil into crops. The contents of Cu, Zn, Pb, and Cd in the rice roots are significantly positively correlated with those in the soils in each experimental year (r = 0.723, 0.707, 0.983, 0.944, n = 12; p < 0.05), also suggesting that the enhancement of heavy metals in the rice roots is caused by their accumulation in the soils. The contents of Cu, Zn, Pb, and Cd in the rice roots of the three treatments show an annual cumulative trend (Figure 9). The contents of Cu and Zn in the rice roots of PM are significantly higher than CK (p < 0.05) during the four years, the content of Pb in the PM rice roots is significantly higher than CK (p < 0.05) in the latter two years, and Cd in the PM rice roots is significantly higher than CK (p < 0.05) in the latter three years. Cu content in the AB rice roots is significantly higher than CK (p < 0.05) in the fourth year, and that in the FV rice roots is significantly higher than CK (p < 0.05) in the latter two years. The content of Zn in the rice roots of AB and FV is significantly higher than CK (p < 0.05) in the latter three years, Pb content in the rice roots of AB and FV is significantly higher than CK (p < 0.05) in the latter two years, and Cd in the AB and FV roots is also significantly higher than CK (p < 0.05) in the latter two years (see Figure 7). The contents of heavy metals in the roots of AB and FV, however, are still much lower than those of PM, also suggesting that the application of PM and FCR have made heavy metals accumulate in the rice roots, and the accumulation by the PM is even more significant. Cu content in the rice roots of PM annually increases by 3.8%, 47.9% and 6.7% from 2018 to 2020; Zn by 62.3%, 16.2%, and 4.0%; Pb by 16.3%, 17.4% and 30.4%; Cd by 153.1%, 31.4% and 5.2%, respectively (Figure 7). Especially, Cd content in the rice roots of PM on the fourth year attains as high as 1.48 mg/kg, which is 3.5 times that on the first year and also one order magnitude that in the soils. This suggests that Cd can be actively taken up by the rice roots from the soils.
Heavy metals taken up by the rice roots are partially translocated to the aerial parts. The contents of Cu, Zn, Pb, and Cd in the aerial parts of the rice plants of PM in the fourth year are 22.0%, 50.5%, 8.9%, and 42.2% of the total, respectively. Both Cu and Zn are essential elements for crops and are inclined to be translocated to the rice shoots, thus showing higher rates in the aerial part. Cd and Pb are not only non-essential but also toxic to crops and thus are mostly trapped in the crop roots.
Cu and Zn contents in the different tissues of rice plants are in the decreasing order of roots > grains > stems > leaves and Pb and Cd in the decreasing order of roots > stems > leaves > grains, which are consistent with many previous studies [23,61]. Cu and Zn are mostly accumulated in the roots, reduced in the stems and leaves, and again raised in the rice grains. This indicates that both Cu and Zn, as nutrient elements, can be actively taken up by rice seeds, while Pb and Cd are mainly retained in the rice roots and stems (Figure 9). Only a small amount of Pb is translocated into rice grains, and a relatively higher amount of Cd is translocated into rice grains (Figure 9), which coincides with many previous studies [62,63]. Cd content in the roots and brown rice of PM on the fourth year attains 1.48 mg/kg and 0.066 mg/kg, and Pb content 9.33 mg/kg and 0.078 mg/kg, respectively. The ratio of Cd content in the roots, stems, leaves, and brown rice is 24:16:2:1, compared with that of Pb being 152: 12: 2: 1. This also suggests that Pb is mostly retained in the roots, and Cd is relatively easily translocated into the rice grain.

3.4. Risk of Heavy Metal Contamination in Rice Grain Caused by Application of PM and FCR

The contents of Cu, Zn, Pb and Cd in the brown rice of the fertilizer treatments in each experimental year are positively correlated with those in the soils (r = 0.836, 0.745, 0.874, 0.949; n = 12; p < 0.01) and rice roots (r = 0.843, 0.930, 0.926, 0.968, n = 12; p < 0.01). The contents of Cu and Zn in the brown rice of PM, FV, and AB in the latter two years are significantly higher than CK (p < 0.05) (Figure 8). Moreover, Cu content in the brown rice of PM, FV, and AB in the latter two years is significantly higher than that in the first two years (p < 0.05). Pb content in the brown rice of PM, AB, and FV in the fourth year is significantly higher than CK (p < 0.05), and Cd content in the brown rice of PM and FV in the four years is significantly higher than CK (p < 0.05). Likewise, the contents of Cu, Zn, Pb, and Cd in the brown rice of AB and FV are much lower than those of PM. Heavy metals in the brown rice of the PM treatment are annually raised more significantly than those of AB and FV (p < 0.05) (Figure 8). For example, Cu content in the brown rice of PM attains 2.94 mg/kg in the fourth year, which is 2.0, 1.1, and 1.2 times that of CK, AB, and FV, respectively. This also suggests that the application of PM and FCR has already posed a risk of heavy metal accumulation in brown rice, and the risk caused by the application of PM is much higher.
A root/rice ratio of Cd content in the PM rice plants is 22.1, and that of Pb is 119.7, suggesting that Cd is more easily translocated into the rice grains and Pb is mostly retained in the rice roots, which is consistent with many previous studies [64,65,66]. It was also reported that 10% of rice samples randomly collected in the market in China exceed the safe limit of Cd content (Cd ≤ 0.2 mg/kg) specified by the China national standards [67]. Cd accumulation in soil has posed a threat to human health through the food chain [68,69].
The contents of heavy metals in the brown rice of the treatments for the consecutive four years are still below the safe limits, specified by the China national standards (GB 2762-2017, NY861-2004) [70,71]. Zn in rice grains inhibits the further uptake of Cd by grains to protect itself from toxicity [72,73]. The high contents of Cu and Zn in rice grains reduce the mobility of Pb and Cd in rice plants [74].
However, Cu content in the brown rice of PM increases by 35.5%, 16.7%, and 12.7% annually from 2018 to 2020; Zn increases by 15.7%, 11.5%, and 39.2%; Pb increases by 4.4%, 18.8% and 141.9%; Cd increases by 48.0%, 21.3%, and 12.0%, respectively (Figure 10). The amount of annual increase in Cu, Zn, Pb, and Cd in the brown rice of PM is 0.43, 4.56, 0.019, and 0.011 mg/kg on average, respectively. If continuously increasing at the rates, the contents of Cu, Zn, Pb, and Cd in the rice grains will exceed the safe limits (NY861-2004, Cu ≤ 10 mg/kg; Zn ≤ 50 mg/kg; Pb ≤ 0.40 mg/kg; Cd ≤ 0.20 mg/kg) [71] after 20, 8, 21 and 16 years of the application of pig manure, respectively. Long-term application of PM to paddy fields raises the risk of Cd contamination of rice [75]. The risk of heavy metal accumulation in rice grains by long-term application of PM and FCR, therefore, can never be neglected.
The bioaccumulation coefficients (BAC) in rice, brown rice/soils ratios of heavy metals were calculated. Cd is much mobile in grain plants and can be actively taken up by grain [76,77,78]. The BAC of Cd in the rice grains is the highest (Figure 11). Cu and Zn are two essential elements for plants and can also be easily taken up and transferred to rice grain. Thus, the BAC of Cu and Zn in the grains is also high. Pb is mostly retained in the roots, and its BAC is the lowest. The BAC of heavy metals for the AB, FV, and PM treatments are mostly significantly higher than CK (p < 0.05), suggesting that the applications of PM and FCR increase the risk of heavy metal accumulation in rice grains. Moreover, the BAC of Pb in the PM grains is significantly higher than that in CK, AB, and FV (p < 0.05), the BAC of Zn in the PM and FV grains significantly higher than that in CK and AB, and the BAC of Cd in the PM and AB grains significantly higher than that in CK and FV (p < 0.05), further suggesting that the application of PM more easily leads to the accumulation of heavy metals in rice grains.

4. Materials and Methods

4.1. Study Area

Located in front of the Yangtze River Delta, Shanghai is surrounded by water on three sides. The land area of Shanghai was initially created by the combined action of the Yangtze River and the East China Sea, with an elevation of 3.2 m on average. Shanghai has a subtropical humid monsoon climate with a mean annual temperature of 17.1 °C and a mean annual rainfall of 1223.4 mm. An experimental field is situated at Professor’s Farm (31 07′ N, 120 53′ E) of Qingpu District in the western suburb of Shanghai. The soils in the experimental site are mostly derived from the sediments of lakes and rivers, with clayey loam texture, and are mostly classified as entisols. Some physical-chemical properties of the experimental soil are indicated in Table 2.

4.2. Field Experiment

Field experiments were carried out for four consecutive years from 2017 to 2020. In each experimental year, the same four fertilizer treatments were arranged, which included the applications of PM, residues of AB and FV as well as non-fertilizer control (CK). Each treatment is triplicated, and the number of experimental plots is 12 in total, with each plot being 2.5 m × 10 m in area and an interval of 50 cm between the two plots.
Rice seedlings were cultivated on seedbed in late May and then transplanted to the experimental fields in middle June. Rice grains were harvested in late October. The whole period of rice growth in the experimental years is about 120 days. A local variety of rice, Jiahe 218, suitable to the climate in Shanghai, was selected for the experiment.
PM, taken from a local pig farm, was composted for several months before being applied to the plots as an experimental treatment. Likewise, the composed culturing residues of AB and FV fetched from the two companies of edible fungi production were also applied as experimental treatments. The culture medium of FV is originally composed of corncob, hull of cottonseeds, rice bran, and husk of wheat, and that of AB composed of straw, chicken manure, rapeseed cake, hull of cottonseeds, and soybean pulp. The contents of nutrients and heavy metals in the two FCR are indicated in Table 1.
Each experimental treatment included basal and topdressing fertilizations, which were applied before seedling transplanting in early June, and during seedling jointing in early July, respectively. The amount of fertilizer application for each treatment is calculated based on the equivalent N content applied by conventional rice farming during the whole rice-growing season, as shown in Table 3.

4.3. Investigation and Sampling

The growth of rice plants was investigated each week during the whole rice-growing season. The rice grains of each plot were harvested and weighed independently to calculate the actual yield of rice grains.
Six rice plants in each plot were randomly collected in each experimental plot after it was matured. The plant samples were immediately carried to the laboratory, cleaned with deionized water, and divided into the subsamples of roots, stems, leaves, and rice grains, which were oven-dried at 90 °C for 30 min and then continuously dried at 70 °C for 12 h. The dried plant samples were ground into powder for chemical analyses.
The cultivated layers of the soils (0–20 cm) in each plot were sampled in the different periods of the rice-growing season. The samples were crushed, ground, and then passed through 2 mm- and 0.149 mm-sized nylon sieves successively for chemical analyses.

4.4. Sample Analyses

The content of OM in the soils was determined by the potassium dichromate-sulfuric acid method; TN by the Kjeldahl method; AN by the alkaline diffusion method; TP by the acid digestion-phosphomolybdate colorimetric method; AP by the NaHCO3 solution extraction-phosphomolybdate colorimetric method; TK content by the acid dissolution method; AK by ammonium acetate extraction method [79].
0.2 g soil sample (<0.149 mm) was put into Teflon crucible and digested with the three mixed acids (HNO3-HClO4-HF). All the reagents are guaranteed. The contents of Cu and Zn in the solution were determined by the inductively coupled plasma-atomic emission spectrometry (ICP-AES, Mason, OH, USA) of Leeman Prodigy produced by American Leeman Instrument Co. Ltd., with the error being 1.52–3.43%, and the relative standard deviation being less than 3%. The minimum detection limits for Cu and Zn are 0.002 µg/mL. The contents of Cd and Pb were determined by the graphite furnace atomic absorption spectrophotometer (GF-AAS, Jena, Germany) (Zee nit 600/650) produced by Jena Company, Germany, with the error being 2.31–4.13% and the relative standard deviation being less than 5%. The minimum detection limits for Pb and Cd are 0.06 µg/L and 0.008 µg/L.
The samples of rice plants, PM, and FCR were put into beakers and digested with the mixed acids (HNO3 + HCl + HClO4). The contents of Cu, Zn, Cd, and Pb in the solution were determined by the GF-AAS.
The bioavailability of heavy metals in soils was evaluated by BAC. The BAC (%) of a heavy metal element in rice grains reflects the transfer and bioaccumulation of the element from soil to grain [80].
BAC ( % ) = C rice C x × 100
Crice: Heavy metal content in rice grains; Cx: heavy metal content in soil.

4.5. Statistical Analysis

All the experimental data were firstly treated by Microsoft Excel 2016 (Microsoft, Redmond, WA, USA). The data were commonly expressed as the mean ± standard deviation (SD), and the statistical difference was checked by the Duncan test, with the significance level set to p < 0.05. The significances of differences among the data and Pearson correlations between the two groups of data were analyzed by IBM SPSS Statistics 24.0 (IBM, New York, NY, USA). All the graphs were drawn using Origin 9.1 (OriginLab, Northampton, MA, USA).

5. Conclusions

The applications of PM and FCR to the paddy fields raise the contents of OM and nutrients in the soils significantly and increase grain yield effectively. However, both lead to an annual accumulative increase in heavy metals in the soils. Especially, the risk of heavy metal accumulation by the application of PM is more significant. Cu and Zn contents in the soil of the PM treatment are significantly raised during the four years, and Pb and Cd are also significantly raised in the latter two years.
Heavy metals in the rice plants by the application of PM and FCR also increase annually. These taken up by plants are mostly retained in the roots. Cu and Zn contents in the rice roots of PM are significantly higher than CK during the four experimental years, and Pb and Cd are also significantly higher than CK in the latter two years. Cu and Zn contents in the rice plants are in the decreasing order of roots > rice grains > stems > leaves, and Pb and Cd in the decreasing order of roots > stems > leaves > rice grains.
The contents of Cu, Zn, Pb, and Cd in the brown rice by the PM, FV, and AB treatments increase annually, which are positively significantly correlated with those in the soils and rice roots (p < 0.05). This suggests that the heavy metals accumulated in the brown rice are caused by the applications of PM and FCR. The risk of heavy metals by the application of PM is even more significant. Though the contents of heavy metals in the brown rice are still within the safe levels during the experimental years, the risks of their accumulative increments, especially by long-term application of PM, can never be neglected.

Author Contributions

Conceptualization, X.H. and C.Y.; methodology, F.L. and J.L.; investigation, S.L.; X.W. and Z.J.; data curation, W.L.; writing—original draft preparation, W.L.; writing—review and editing, X.H.; funding acquisition, C.Y. All authors have read and agreed to the published version of the manuscript.

Funding

The authors acknowledge financial support from the Shanghai Agriculture Applied Technology Development Program, Shanghai Agricultural Commission, China (grant no. G20190301), the National Natural Science Foundation of China (no. 40877005), and the project from Shanghai Science and Technology Commission (grant no. 20392002200).

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

All data are provided in the manuscript.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Uphoff, N.; Dazzo, F.B. Making Rice Production More Environmentally-Friendly. Environments 2016, 3, 12. [Google Scholar] [CrossRef] [Green Version]
  2. Qian, X.; Wang, Z.; Shen, G.; Chen, X.; Tang, Z.; Guo, C.; Gu, H.; Fu, K. Heavy metals accumulation in soil after 4 years of continuous land application of swine manure: A field-scale monitoring and modeling estimation. Chemosphere 2018, 210, 1029–1034. [Google Scholar] [CrossRef]
  3. Onwosi, C.O.; Igbokwe, V.C.; Odimba, J.N.; Eke, I.E.; Nwankwoala, M.O.; Iroh, I.N.; Ezeogu, L.I. Composting technology in waste stabilization: On the methods, challenges and future prospects. J. Environ. Manag. 2017, 190, 140–157. [Google Scholar] [CrossRef]
  4. Cai, A.; Xu, M.; Wang, B.; Zhang, W.; Liang, G.; Hou, E.; Luo, Y. Manure acts as a better fertilizer for increasing crop yields than synthetic fertilizer does by improving soil fertility. Soil Tillage Res. 2019, 189, 168–175. [Google Scholar] [CrossRef]
  5. Stroppa, N.; Onelli, E.; Hejna, M.; Rossi, L.; Gagliardi, A.; Bini, L.; Baldi, A.; Moscatelli, A. Typha latifolia and Thelypteris palustris behavior in a pilot system for the refinement of livestock wastewaters: A case of study. Chemosphere 2020, 240, 14. [Google Scholar] [CrossRef]
  6. Jin, H.; Chang, Z. Distribution of heavy metal contents and chemical fractions in anaerobically digested manure slurry. Appl. Biochem. Biotechnol. 2011, 164, 268–282. [Google Scholar] [CrossRef]
  7. Huang, H.; Li, B.; Li, J.; Zhang, P.; Yu, W.; Zhao, N.; Guo, G.; Young, B. Influence of process parameters on the heavy metal (Zn(2+), Cu(2+) and Cr(3+)) content of struvite obtained from synthetic swine wastewater. Environ. Pollut. 2019, 245, 658–665. [Google Scholar] [CrossRef] [PubMed]
  8. Mu, H.Y.; Zhuang, Z.; Li, Y.M.; Qiao, Y.H.; Chen, Q.; Xiong, J.; Guo, L.L.; Jiang, R.F.; Li, H.-F. Heavy Metal Contents in Animal Manure in China and the Related Soil Accumulation Risks. Huan Jing Ke Xue 2020, 41, 986–996. [Google Scholar] [CrossRef] [PubMed]
  9. Franco, A.; Schuhmacher, M.; Roca, E.; Luis, D.J. Application of cattle manure as fertilizer in pastureland: Estimating the incremental risk due to metal accumulation employing a multicompartment model. Environ. Int. 2006, 32, 724–732. [Google Scholar] [CrossRef] [PubMed]
  10. Yang, X.; Li, Q.; Tang, Z.; Zhang, W.; Yu, G.; Shen, Q.; Zhao, F.J. Heavy metal concentrations and arsenic speciation in animal manure composts in China. Waste Manag. 2017, 64, 333–339. [Google Scholar] [CrossRef] [PubMed]
  11. Sager, M. Trace and nutrient elements in manure, dung and compost samples in Austria. Soil Biol. Biochem. 2007, 39, 1383–1390. [Google Scholar] [CrossRef]
  12. Shi, J.; Yu, X.; Zhang, M.; Lu, S.; Wu, W.; Wu, J.; Xu, J. Potential Risks of Copper, Zinc, and Cadmium Pollution due to Pig Manure Application in a Soil-Rice System under Intensive Farming: A Case Study of Nanhu, China. J. Environ. Qual. 2011, 40, 1695–1704. [Google Scholar] [CrossRef] [PubMed]
  13. Zhang, F.; Li, Y.; Yang, M.; Li, W. Content of Heavy Metals in Animal Feeds and Manures from Farms of Different Scales in Northeast China. Int. J. Environ. Res. Public Health 2012, 9, 2658–2668. [Google Scholar] [CrossRef] [Green Version]
  14. Xu, Y.; Yu, W.; Ma, Q.; Zhou, H. Accumulation of copper and zinc in soil and plant within ten-year application of different pig manure rates. Plant. Soil Environ. 2013, 59, 492–499. [Google Scholar] [CrossRef] [Green Version]
  15. Zhao, Y.; Yan, Z.; Qin, J.; Xiao, Z. Effects of long-term cattle manure application on soil properties and soil heavy metals in corn seed production in Northwest China. Environ. Sci. Pollut. Res. 2014, 21, 7586–7595. [Google Scholar] [CrossRef] [PubMed]
  16. Liang, X.; Jin, Y.; He, M.; Liu, Y.; Hua, G.; Wang, S.; Tian, G. Composition of phosphorus species and phosphatase activities in a paddy soil treated with manure at varying rates. Agric. Ecosyst. Environ. 2017, 237, 173–180. [Google Scholar] [CrossRef]
  17. Liang, Y.G.; Li, X.J.; Zhang, J.; Zhang, L.G.; Cheng, B. Effect of microscale ZVI/magnetite on methane production and bioavailability of heavy metals during anaerobic digestion of diluted pig manure. Environ. Sci. Pollut. Res. 2017, 24, 12328–12337. [Google Scholar] [CrossRef]
  18. Cang, L.; Wang, Y.J.; Zhou, D.M.; Dong, Y.H. Heavy metals pollution in poultry and livestock feeds and manures under intensive farming in Jiangsu Province, China. J. Environ. Sci. 2004, 16, 371–374. [Google Scholar]
  19. Peng, S.; Wang, Y.; Zhou, B.; Lin, X. Long-term application of fresh and composted manure increase tetracycline resistance in the arable soil of eastern China. Sci. Total Environ. 2015, 506–507, 279–286. [Google Scholar] [CrossRef]
  20. Meng, J.; Liang, S.; Tao, M.; Liu, X.; Brookes, P.C.; Xu, J. Chemical speciation and risk assessment of Cu and Zn in biochars derived from co-pyrolysis of pig manure with rice straw. Chemosphere 2018, 200, 344–350. [Google Scholar] [CrossRef]
  21. Muthayya, S.; Sugimoto, J.D.; Montgomery, S.; Maberly, G.F. An overview of global rice production, supply, trade, and consumption. Ann. N. Y. Acad. Sci. 2014, 1324, 7–14. [Google Scholar] [CrossRef] [PubMed]
  22. Gu, J.F.; Zhou, H.; Tang, H.L.; Yang, W.T.; Zeng, M.; Liu, Z.M.; Peng, P.Q.; Liao, B.H. Cadmium and arsenic accumulation during the rice growth period under in situ remediation. Ecotoxicol. Environ. Saf. 2019, 171, 451–459. [Google Scholar] [CrossRef]
  23. Zhou, H.; Zhu, W.; Yang, W.T.; Gu, J.F.; Gao, Z.X.; Chen, L.W.; Du, W.Q.; Zhang, P.; Peng, P.Q.; Liao, B.H. Cadmium uptake, accumulation, and remobilization in iron plaque and rice tissues at different growth stages. Ecotoxicol. Environ. Saf. 2018, 152, 91–97. [Google Scholar] [CrossRef] [PubMed]
  24. Shan, H.; Su, S.; Liu, R.; Li, S. Cadmium availability and uptake by radish (Raphanus sativus) grown in soils applied with wheat straw or composted pig manure. Environ. Sci. Pollut. Res. 2016, 23, 15208–15217. [Google Scholar] [CrossRef]
  25. Qian, X.; Shen, G.; Wang, Z.; Zhang, X.; Hong, Z. Effect of swine liquid manure application in paddy field on water quality, soil fertility and crop yields. Paddy Water Environ. 2018, 16, 15–22. [Google Scholar] [CrossRef]
  26. Demelash, N.; Bayu, W.; Tesfaye, S.; Ziadat, F.; Sommer, R. Current and residual effects of compost and inorganic fertilizer on wheat and soil chemical properties. Nutr. Cycl. Agroecosyst. 2014, 100, 357–367. [Google Scholar] [CrossRef]
  27. Carpenter, S.R.; Caraco, N.F.; Correll, D.L.; Howarth, R.W.; Sharpley, A.N.; Smith, V.H. Nonpoint pollution of surface waters with phosphorus and nitrogen. Ecol. Appl. 1998, 8, 559–568. [Google Scholar] [CrossRef]
  28. Li, F.; Li, Z.; Mao, P.; Li, Y.; Li, Y.; McBride, M.B.; Wu, J.; Zhuang, P. Heavy metal availability, bioaccessibility, and leachability in contaminated soil: Effects of pig manure and earthworms. Environ. Sci. Pollut. Res. 2019, 26, 20030–20039. [Google Scholar] [CrossRef]
  29. Antonious, G.F.; Kochhar, T.S.; Coolong, T. Yield, quality, and concentration of seven heavy metals in cabbage and broccoli grown in sewage sludge and chicken manure amended soil. J. Environ. Sci. Health Part A—Toxic/Hazard. Subst. Environ. Eng. 2012, 47, 1955–1965. [Google Scholar] [CrossRef]
  30. Liu, D.Y.; Zhang, W.; Pang, L.L.; Zhang, Y.Q.; Wang, X.Z.; Liu, Y.M.; Chen, X.P.; Zhang, F.S.; Zou, C.Q. Effects of zinc application rate and zinc distribution relative to root distribution on grain yield and grain Zn concentration in wheat. Plant Soil 2017, 411, 167–178. [Google Scholar] [CrossRef]
  31. Liu, D.Y.; Zhang, W.; Yan, P.; Chen, X.P.; Zhang, F.S.; Zou, C.Q. Soil application of zinc fertilizer could achieve high yield and high grain zinc concentration in maize. Plant Soil 2017, 411, 47–55. [Google Scholar] [CrossRef]
  32. Wei, W.; Yan, Y.; Cao, J.; Christie, P.; Zhang, F.; Fan, M. Effects of combined application of organic amendments and fertilizers on crop yield and soil organic matter: An integrated analysis of long-term experiments. Agric. Ecosyst. Environ. 2016, 225, 86–92. [Google Scholar] [CrossRef] [Green Version]
  33. Hu, N.; Wang, B.; Gu, Z.; Tao, B.; Zhang, Z.; Hu, S.; Zhu, L.; Meng, Y. Effects of different straw returning modes on greenhouse gas emissions and crop yields in a rice-wheat rotation system. Agric. Ecosyst. Environ. 2016, 223, 115–122. [Google Scholar] [CrossRef]
  34. Zhang, L.; Zheng, J.; Chen, L.; Shen, M.; Zhang, X.; Zhang, M.; Bian, X.; Zhang, J.; Zhang, W. Integrative effects of soil tillage and straw management on crop yields and greenhouse gas emissions in a rice-wheat cropping system. Eur. J. Agron. 2015, 63, 47–54. [Google Scholar] [CrossRef]
  35. Irshad, M.; Malik, A.H.; Shaukat, S.; Mushtaq, S.; Ashraf, M. Characterization of Heavy Metals in Livestock Manures. Pol. J. Environ. Stud. 2013, 22, 1257–1262. [Google Scholar]
  36. Li, Y.X.; Li, W.; Wu, J.; Xu, L.C.; Su, Q.H.; Xiong, X. Contribution of additives Cu to its accumulationin pig feces: Study in Beijing and Fuxin of China. J. Environ. Sci. 2007, 19, 610–615. [Google Scholar] [CrossRef]
  37. Dach, J.; Starmans, D. Heavy metals balance in Polish and Dutch agronomy: Actual state and previsions for the future. Agric. Ecosyst. Environ. 2005, 107, 309–316. [Google Scholar] [CrossRef]
  38. Tan, C.Y.; Wu, L.H.; Luo, Y.M.; Xu, J.M.; Han, X.Z.; Qiao, Y.F. Cadmium accumulation and its development tendency in black soil under long-term fertilization. J. Appl. Ecol. 2008, 19, 2738–2744. [Google Scholar]
  39. Karami, M.; Amini, M.; Afyuni, M.; Khoshgoftarmanesh, A.H.; Keller, A.; Abdi, A.; Schulin, R. Agricultural zinc fluxes into soils and crops of central Iran at regional scale. Arch. Agron. Soil Sci. 2014, 60, 437–456. [Google Scholar] [CrossRef]
  40. McBride, M.B.; Spiers, G. Trace element content of selected fertilizers and dairy manures as determined by ICP-MS. Commun. Soil Sci. Plant Anal. 2001, 32, 139–156. [Google Scholar] [CrossRef]
  41. Luo, L.; Ma, Y.; Zhang, S.; Wei, D.; Zhu, Y.G. An inventory of trace element inputs to agricultural soils in China. J. Environ. Manag. 2009, 90, 2524–2530. [Google Scholar] [CrossRef]
  42. Wu, L.; Tan, C.; Liu, L.; Zhu, P.; Peng, C.; Luo, Y.; Christie, P. Cadmium bioavailability in surface soils receiving long-term applications of inorganic fertilizers and pig manure. Geoderma 2012, 173, 224–230. [Google Scholar] [CrossRef]
  43. Dudka, S.; Miller, W.P. Accumulation of potentially toxic elements in plants and their transfer to human food chain. J. Environ. Sci. Health Part B Pestic. Food Contam. Agric. Wastes 1999, 34, 681–708. [Google Scholar] [CrossRef]
  44. Gong, Q.; Chen, P.; Shi, R.; Gao, Y.; Zheng, S.A.; Xu, Y.; Shao, C.; Zheng, X. Health Assessment of Trace Metal Concentrations in Organic Fertilizer in Northern China. Int. J. Environ. Res. Public Health 2019, 16, 1031. [Google Scholar] [CrossRef] [Green Version]
  45. Kirkham, M.B. Cadmium in plants on polluted soils: Effects of soil factors, hyperaccumulation, and amendments. Geoderma 2006, 137, 19–32. [Google Scholar] [CrossRef]
  46. Xu, Y.G.; Yu, W.T.; Ma, Q.; Zhou, H. Potential risk of cadmium in a soil-plant system as a result of long-term (10 years) pig manure application. Plant Soil Environ. 2015, 61, 352–357. [Google Scholar] [CrossRef] [Green Version]
  47. Guo, G.; Lei, M.; Chen, T.; Yang, J. Evaluation of different amendments and foliar fertilizer for immobilization of heavy metals in contaminated soils. J. Soils Sediments 2018, 18, 239–247. [Google Scholar] [CrossRef]
  48. Wang, X.; Zheng, G.; Chen, T.; Shi, X.; Wang, Y.; Nie, E.; Liu, J. Effect of phosphate amendments on improving the fertilizer efficiency and reducing the mobility of heavy metals during sewage sludge composting. J. Environ. Manag. 2019, 235, 124–132. [Google Scholar] [CrossRef] [PubMed]
  49. Guo, T.; Lou, C.; Zhai, W.; Tang, X.; Hashmi, M.Z.; Murtaza, R.; Li, Y.; Liu, X.; Xu, J. Increased occurrence of heavy metals, antibiotics and resistance genes in surface soil after long-term application of manure. Sci. Total Environ. 2018, 635, 995–1003. [Google Scholar] [CrossRef] [PubMed]
  50. Basar, H. Methods for Estimating Phytoavailable Metals in Soils. Commun. Soil Sci. Plant Anal. 2009, 40, 1087–1105. [Google Scholar] [CrossRef]
  51. Shaheen, S.M.; Rinklebe, J. Impact of emerging and low cost alternative amendments on the (im)mobilization and phytoavailability of Cd and Pb in a contaminated floodplain soil. Ecol. Eng. 2015, 74, 319–326. [Google Scholar] [CrossRef]
  52. Halim, M.A.; Majumder, R.K.; Zaman, M.N. Paddy soil heavy metal contamination and uptake in rice plants from the adjacent area of Barapukuria coal mine, northwest Bangladesh. Arab. J. Geosci. 2015, 8, 3391–3401. [Google Scholar] [CrossRef]
  53. Sprynskyy, M.; Kowalkowski, T.; Tutu, H.; Cozmuta, L.M.; Cukrowska, E.M.; Buszewski, B. The Adsorption Properties of Agricultural and Forest Soils Towards Heavy Metal Ions (Ni, Cu, Zn, and Cd). Soil Sediment Contam. 2011, 20, 12–29. [Google Scholar] [CrossRef]
  54. GB NY-525-(2012) Organic Manure Standard. Available online: https://img.antpedia.com/standard/files/pdfs_ora/CN-NY/30e/NY%20525-2012_2500.pdf (accessed on 9 January 2022).
  55. McLaughlin, M.J.; Parker, D.R.; Clarke, J.M. Metals and micronutrients—Food safety issues. Field Crops Res. 1999, 60, 143–163. [Google Scholar] [CrossRef]
  56. Xiong, X.; Li, Y.; Li, W.; Lin, C.; Han, W.; Yang, M. Copper content in animal manures and potential risk of soil copper pollution with animal manure use in agriculture. Resour. Conserv. Recycl. 2010, 54, 985–990. [Google Scholar] [CrossRef]
  57. Wan, Y.; Huang, Q.; Wang, Q.; Yu, Y.; Su, D.; Qiao, Y.; Li, H. Accumulation and bioavailability of heavy metals in an acid soil and their uptake by paddy rice under continuous application of chicken and swine manure. J. Hazard. Mater. 2020, 384, 121293. [Google Scholar] [CrossRef]
  58. Merrington, G.; Madden, C. Changes in cadmium and zinc phytoavailability in agricultural soil after amendment with papermill sludge and biosolids. Commun. Soil Sci. Plant Anal. 2000, 31, 759–776. [Google Scholar] [CrossRef]
  59. Weggler-Beaton, K.; McLaughlin, M.J.; Graham, R.D. Salinity increases cadmium uptake by wheat and Swiss chard from soil amended with biosolids. Aust. J. Soil Res. 2000, 38, 37–45. [Google Scholar] [CrossRef]
  60. GB 15618-(2018). Environmental Quality Standards for Soils. Part 7.2: Level 2 of Environmental Quality Standards for Soil Inorganic Matter. Available online: https://img.antpedia.com/standard/files/pdfs_ora/20200926/GB%2015618-2018.pdf (accessed on 9 January 2022).
  61. Ochoa, M.; Tierra, W.; Santiago Tupuna-Yerovi, D.; Guanoluisa, D.; Luis Otero, X.; Ruales, J. Assessment of cadmium and lead contamination in rice farming soils and rice (Oryza sativa L.) from Guayas province in Ecuador. Environ. Pollut. 2020, 260, 114050. [Google Scholar] [CrossRef]
  62. Bingham, F.T. Bioavailability of Cd to Food crops in relation to heavy metal content of sludge-amended soil. Environ. Health Perspect. 1979, 28, 39–43. [Google Scholar] [CrossRef]
  63. Song, W.E.; Chen, S.B.; Liu, J.F.; Chen, L.; Song, N.N.; Li, N.; Liu, B. Variation of Cd concentration in various rice cultivars and derivation of cadmium toxicity thresholds for paddy soil by species-sensitivity distribution. J. Integr. Agric. 2015, 14, 1845–1854. [Google Scholar] [CrossRef]
  64. Harris, N.S.; Taylor, G.J. Cadmium uptake and partitioning in durum wheat during grain filling. BMC Plant Biol. 2013, 13, 103. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  65. Yoneyama, T.; Gosho, T.; Kato, M.; Goto, S.; Hayashi, H. Xylem and phloem transport of Cd, Zn and Fe into the grains of rice plants (Oryza sativa L.) grown in continuously flooded Cd-contaminated soil. Soil Sci. Plant Nutr. 2010, 56, 445–453. [Google Scholar] [CrossRef]
  66. Ashraf, U.; Kanu, A.S.; Deng, Q.; Mo, Z.; Pan, S.; Tian, H.; Tang, X. Lead (Pb) Toxicity; Physio-Biochemical Mechanisms, Grain Yield, Quality, and Pb Distribution Proportions in Scented Rice. Front. Plant Sci. 2017, 8, 259. [Google Scholar] [CrossRef] [Green Version]
  67. Chen, H.; Tang, Z.; Wang, P.; Zhao, F.J. Geographical variations of cadmium and arsenic concentrations and arsenic speciation in Chinese rice. Environ. Pollut. 2018, 238, 482–490. [Google Scholar] [CrossRef]
  68. Jarup, L.; Akesson, A. Current status of cadmium as an environmental health problem. Toxicol. Appl. 2009, 238, 201–208. [Google Scholar] [CrossRef]
  69. Chen, Z.F.; Zhao, Y.; Zhu, Y.; Yang, X.; Qiao, J.; Tian, Q.; Zhang, Q. Health risks of heavy metals in sewage-irrigated soils and edible seeds in Langfang of Hebei province, China. J. Sci. Food Agric. 2010, 90, 314–320. [Google Scholar] [CrossRef] [PubMed]
  70. GB 2762-(2017). Limit of Contaminants in Food Safety of National Standards. Available online: https://kns.cnki.net/kcms/detail/detail.aspx?FileName=ZSPZ201803030&DbName=CJFQ2018. (accessed on 9 January 2022).
  71. GB NY-861-(2004). Limit Standard for Grain and Products. Available online: https://img.antpedia.com/standard/files/pdfs_ora/CN-NY/3f8/NY%20861-2004.pdf (accessed on 9 January 2022).
  72. Romkens, P.F.A.M.; Guo, H.Y.; Chu, C.L.; Liu, T.S.; Chiang, C.F.; Koopmans, G.F. Prediction of Cadmium uptake by brown rice and derivation of soil-plant transfer models to improve soil protection guidelines. Environ. Pollut. 2009, 157, 2435–2444. [Google Scholar] [CrossRef]
  73. Han, C.; Wu, L.; Tan, W.; Zhong, D.; Huang, Y.; Luo, Y.; Christie, P. Cadmium distribution in rice plants grown in three different soils after application of pig manure with added cadmium. Environ. Geochem. Health 2012, 34, 481–492. [Google Scholar] [CrossRef]
  74. Jalil, A.; Selles, F.; Clarke, J.M. Effect of cadmium on growth and the uptake of cadmium and other elements by durum wheat. J. Plant Nutr. 1994, 17, 1839–1858. [Google Scholar] [CrossRef]
  75. Wang, G.; Zhou, L. Application of Green Manure and Pig Manure to Cd-Contaminated Paddy Soil Increases the Risk of Cd Uptake by Rice and Cd Downward Migration into Groundwater: Field Micro-Plot Trials. Water Air Soil Pollut. 2017, 228, 29. [Google Scholar] [CrossRef]
  76. Fei, X.; Xiao, R.; Christakos, G.; Langousis, A.; Ren, Z.; Tian, Y.; Lv, X. Comprehensive assessment and source apportionment of heavy metals in Shanghai agricultural soils with different fertility levels. Ecol. Indic. 2019, 106, 105508. [Google Scholar] [CrossRef]
  77. Xiao, R.; Guo, D.; Ali, A.; Mi, S.S.; Liu, T.; Ren, C.Y.; Li, R.H.; Zhang, Z.Q. Accumulation, ecological-health risks assessment, and source apportionment of heavy metals in paddy soils: A case study in Hanzhong, Shaanxi, China. Environ. Pollut. 2019, 248, 349–357. [Google Scholar] [CrossRef] [PubMed]
  78. Qaswar, M.; Liu, Y.; Huang, J.; Liu, K.; Mudasir, M.; Lv, Z.; Hou, H.; Lan, X.; Ji, J.; Ahmed, W.; et al. Soil nutrients and heavy metal availability under long-term combined application of swine manure and synthetic fertilizers in acidic paddy soil. J. Soils Sediments 2020, 20, 2093–2106. [Google Scholar] [CrossRef]
  79. Zhang, G.L.; Gong, Z.T. Soil Survey Laboratory Methods; Science Press: Beijing, China, 2012; pp. 36–96. [Google Scholar]
  80. Xiao, R.; Wang, S.; Li, R.; Wang, J.J.; Zhang, Z. Soil heavy metal contamination and health risks associated with artisanal gold mining in Tongguan, Shaanxi, China. Ecotoxicol. Environ. Saf. 2017, 141, 17–24. [Google Scholar] [CrossRef] [PubMed]
Plants 11 00207 g001 550
Figure 1. Effects of the different fertilizer treatments on the content of OM in the soils. All the data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 1. Effects of the different fertilizer treatments on the content of OM in the soils. All the data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Plants 11 00207 g001
Plants 11 00207 g002 550
Figure 2. (a) Effects of the different fertilizer treatments on the content of TN in the soils; (b) Effects of the different fertilizer treatments on the content of AN in the soils. All the data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 2. (a) Effects of the different fertilizer treatments on the content of TN in the soils; (b) Effects of the different fertilizer treatments on the content of AN in the soils. All the data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Plants 11 00207 g002
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Figure 3. (a) Effects of the different fertilizer treatments on the content of TP in the soils; (b) Effects of the different fertilizer treatments on the content of AP in the soils. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 3. (a) Effects of the different fertilizer treatments on the content of TP in the soils; (b) Effects of the different fertilizer treatments on the content of AP in the soils. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
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Figure 4. (a) Effects of the different fertilizer treatments on the content of TK in the soils; (b) Effects of the different fertilizer treatments on the content of AK in the soils. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 4. (a) Effects of the different fertilizer treatments on the content of TK in the soils; (b) Effects of the different fertilizer treatments on the content of AK in the soils. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
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Figure 5. Yield of rice grains by the different fertilizer treatments during the four experimental years. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 5. Yield of rice grains by the different fertilizer treatments during the four experimental years. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
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Figure 6. (a) Cu content in the soils by the different fertilizer treatments during the four experimental years; (b) Zn content in the soils by the different fertilizer treatments during the four experimental years; (c) Pb content in the soils by the different fertilizer treatments during the four experimental years; (d) Cd content in the soils by the different fertilizer treatments during the four experimental years. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 6. (a) Cu content in the soils by the different fertilizer treatments during the four experimental years; (b) Zn content in the soils by the different fertilizer treatments during the four experimental years; (c) Pb content in the soils by the different fertilizer treatments during the four experimental years; (d) Cd content in the soils by the different fertilizer treatments during the four experimental years. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
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Figure 7. (a) Cu content in the rice roots by the different fertilizer treatments during the four experimental years; (b) Zn content in the rice roots by the different fertilizer treatments during the four experimental years; (c) Pb content in the rice roots by the different fertilizer treatments during the four experimental years; (d) Cd content in the rice roots by the different fertilizer treatments during the four experimental years. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 7. (a) Cu content in the rice roots by the different fertilizer treatments during the four experimental years; (b) Zn content in the rice roots by the different fertilizer treatments during the four experimental years; (c) Pb content in the rice roots by the different fertilizer treatments during the four experimental years; (d) Cd content in the rice roots by the different fertilizer treatments during the four experimental years. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
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Figure 8. (a) Cu content in the brown rice by the different fertilizer treatments during the four experimental years; (b) Zn content in the brown rice by the different fertilizer treatments during the four experimental years; (c) Pb content in the brown rice by the different fertilizer treatments during the four experimental years; (d) Cd content in the brown rice by the different fertilizer treatments during the four experimental years. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 8. (a) Cu content in the brown rice by the different fertilizer treatments during the four experimental years; (b) Zn content in the brown rice by the different fertilizer treatments during the four experimental years; (c) Pb content in the brown rice by the different fertilizer treatments during the four experimental years; (d) Cd content in the brown rice by the different fertilizer treatments during the four experimental years. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
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Figure 9. (a) Distribution of Cu content in the rice plants on the fourth experimental year; (b) distribution of Zn content in the rice plants on the fourth experimental year; (c) distribution of Pb content in the rice plants on the fourth experimental year; (d) distribution of Cd content in the rice plants on the fourth experimental year. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 9. (a) Distribution of Cu content in the rice plants on the fourth experimental year; (b) distribution of Zn content in the rice plants on the fourth experimental year; (c) distribution of Pb content in the rice plants on the fourth experimental year; (d) distribution of Cd content in the rice plants on the fourth experimental year. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
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Figure 10. (a) Annual increasing rates of Cu content in the soils, rice roots, and brown rice by the application of PM during the four experimental years; (b) annual increasing rates of Zn content in the soils, rice roots, and brown rice by the application of PM during the four experimental years; (c) annual increasing rates of Pb content in the soils, rice roots and brown rice by the application of PM during the four experimental years; (d) annual increasing rates of Cd content in the soils, rice roots, and brown rice by the application of PM during the four experimental years. Data are expressed as means ± SD; n = 3.
Figure 10. (a) Annual increasing rates of Cu content in the soils, rice roots, and brown rice by the application of PM during the four experimental years; (b) annual increasing rates of Zn content in the soils, rice roots, and brown rice by the application of PM during the four experimental years; (c) annual increasing rates of Pb content in the soils, rice roots and brown rice by the application of PM during the four experimental years; (d) annual increasing rates of Cd content in the soils, rice roots, and brown rice by the application of PM during the four experimental years. Data are expressed as means ± SD; n = 3.
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Figure 11. (a) BAC of Cu in the brown rice of the different treatments; (b) BAC of Zn in the brown rice of the different treatments; (c) BAC of Pb in the brown rice of the different treatments; (d) BAC of Cd in the brown rice of the different treatments. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
Figure 11. (a) BAC of Cu in the brown rice of the different treatments; (b) BAC of Zn in the brown rice of the different treatments; (c) BAC of Pb in the brown rice of the different treatments; (d) BAC of Cd in the brown rice of the different treatments. Data are expressed as means ± SD; n = 3. Different letters on data in the same group indicate a significant difference between them at p < 0.05 level.
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Table
Table 1. Nutrient and heavy metal content of PM and FCR in field experiments. Data are means ± SD, n = 3. Different letters indicate significant differences between treatments at p < 0.05 according to the Duncan test.
Table 1. Nutrient and heavy metal content of PM and FCR in field experiments. Data are means ± SD, n = 3. Different letters indicate significant differences between treatments at p < 0.05 according to the Duncan test.
Organic FertilizerpHOM (%)Water Content (%)TN (g/kg)TP (g/kg)TK (g/kg)Cu (mg/kg)Zn (mg/kg)Pb (mg/kg)Cd (mg/kg)
FV5.50 ± 0.1171.75 ± 0.8977.66 ± 0.1320.34 ± 0.2610.20 ± 0.093.07 ± 0.078.00 ± 0.81c33.46 ± 5.95c0.52 ± 0.16 c0.15 ± 0.05 c
AB5.85 ± 0.1636.49 ± 0.6375.63 ± 0.1219.24 ± 0.314.36 ± 0.052.65 ± 0.1530.09 ± 0.49b123.72 ± 6.52b1.71 ± 0.43 b0.30 ± 0.05 b
PM6.99 ± 0.1933.81 ± 0.5512.04 ± 0.1521.05 ± 0.1815.43 ± 0.163.76 ± 0.21166.76 ± 19.99a544.74 ± 75.48a3.20 ± 0.14 a0.43 ± 0.03 a
Table
Table 2. Background values of nutrients in the experimental soil in the suburb of Shanghai, Southeast China. Data are means ± SD, n = 3.
Table 2. Background values of nutrients in the experimental soil in the suburb of Shanghai, Southeast China. Data are means ± SD, n = 3.
pHOM (g/kg)TN (g/kg)TP (g/kg)TK (g/kg)AN (g/kg)AP (g/kg)AK (g/kg)
5.20 ± 0.1231.07 ± 0.281.41 ± 0.210.14 ± 0.0217.91 ± 0.480.11 ± 0.0050.006 ± 0.00040.044 ± 0.006
Table
Table 3. Quantities of base fertilizer and topdressing to the rice of the field experiment.
Table 3. Quantities of base fertilizer and topdressing to the rice of the field experiment.
Base Fertilizer (June 2017–June 2020) Topdressing (July 2017–July 2020)
TreatmentFertilization Amount TN (g/m−2)TPTK Fertilization AmountTNTPTK
(kg/m2)(g/m2)(g/m2)(g/m2) (kg/m2)(g/m2)(g/m2)(g/m2)
CK0.000.000.000.00CK0.000.000.000.00
AB1.339.502.150.65AB3.8027.610.885.84
FV0.579.503.361.14FV4.0427.613.754.91
PM0.489.505.521.15PM1.2127.616.993.03
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Lan, W.; Yao, C.; Luo, F.; Jin, Z.; Lu, S.; Li, J.; Wang, X.; Hu, X. Effects of Application of Pig Manure on the Accumulation of Heavy Metals in Rice. Plants 2022, 11, 207. https://doi.org/10.3390/plants11020207

AMA Style

Lan W, Yao C, Luo F, Jin Z, Lu S, Li J, Wang X, Hu X. Effects of Application of Pig Manure on the Accumulation of Heavy Metals in Rice. Plants. 2022; 11(2):207. https://doi.org/10.3390/plants11020207

Chicago/Turabian Style

Lan, Wenchong, Chunxia Yao, Fan Luo, Zhi Jin, Siwen Lu, Jun Li, Xindong Wang, and Xuefeng Hu. 2022. "Effects of Application of Pig Manure on the Accumulation of Heavy Metals in Rice" Plants 11, no. 2: 207. https://doi.org/10.3390/plants11020207

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