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Effects of Pig Slurry as Basal and Panicle Fertilizer on Trace Element Content and Grain Quality in Direct-Seeding Rice

Jiangsu Key Laboratory of Crop Genetics and Physiology/Co-Innovation Center for Modern Production Technology of Grain Crops, Yangzhou University, Yangzhou 225009, Jiangsu, China
Taicang Agro-Tech Extension Center, Taicang 215400, Jiangsu, China
Authors to whom correspondence should be addressed.
Academic Editor: Iain Gordon
Sustainability 2016, 8(8), 714;
Received: 2 May 2016 / Revised: 11 July 2016 / Accepted: 18 July 2016 / Published: 26 July 2016
(This article belongs to the Section Sustainable Agriculture)


Direct-seeding rice has grown in popularity in recent years and is widespread in China. This study focused on the effects of pig slurry (PS) on grain quality and safety in direct-seeding rice. Application of more than 210 m3·hm−2 increased rice yield and dry matter accumulation, compared with conventional chemical fertilizer treatment (CK2). At the heading and maturing stage, a high dosage of PS (T6, T8 and T9 treatments) promoted uptake of Pb, Cu, Zn, Fe and Mn by rice plants and grain, but retarded uptake of Cr, Co and Ni, indicating an ability to alleviate toxicity of some heavy metals. Compared with CK2, PS alleviated the transfer of Pb, Cr, Co, Ni and Cu from straw to grain, but enhanced the transport of Zn, Fe and Mn. Although PS application slightly diminished the processing quality, including brown rice, milled rice and head milled rice, it significantly decreased the amylose content, optimized the starch profile, and improved the overall quality. The results confirmed the feasibility and safety of PS application to direct-seeding rice, and determined that PS basal and panicle fertilizer could increase yield and improve the rice quality when applied between 210 and 240 m3·hm−2.
Keywords: pig slurry; trace elements; direct-seeding rice; rice quality pig slurry; trace elements; direct-seeding rice; rice quality

1. Introduction

As a traditional agricultural country, China is one of the largest producers of animal manure in the world, with an annual output of more than 3 billion tonnes [1]. Disposal of animal manure usually involves aerobic composting and anaerobic fermentation [2]. Pig slurry (PS) is primarily used as fertilizer in agricultural production to provide nutrients such as nitrogen (N), phosphorus (P), and potassium (K) to crops [3,4,5,6]. Tao et al. [7] found that applying PS at 60–120 m3·hm−2 instead of chemical fertilizer at 30–60 kg N·hm−2 during winter, at the panicle formation stage, could meet the high nitrogen demand utilization efficiency of wheat. Moreover, Gomez-Munoz et al. [8] demonstrated that acidification of PS increased N availability from separated solid fractions but did not affect N2O and CO2 emissions.
However, continual application of high doses of PS can result in high concentrations of heavy metals, especially copper (Cu) and Zinc (Zn), which could lead to secondary contamination in a PS-amended soil [9,10]. Concentrations of Cu and Cd in grain and straw were dependent on the available Cu and Cd in the soils, and soil available Cu and Cd were significantly affected by the soil pH [11]. Heavy metals in variable charge soil are highly bioavailable and easy to transfer into plants. The use of organic fertilizer such as biogas slurry in As-contaminated paddy soil can significantly alter the behaviour of As in a soil-rice system and enhance As accumulation in rice plants [12]. The As concentrations in polished grain were reported to be positively and significantly correlated with As root-grain translocation factor [13]. The Cu content in stems and leaves in anaerobically digested PS was reported be significantly higher (p < 0.05) than that in a chemical fertilizer treatment [14]. Although there is a potential risk of heavy metal pollution from PS, phytotoxicity caused by Cu and Zn did not occur, even after several years of PS application, because chemical species in soil tend to form complexes with dissolved organic carbon, and Cu and Zn in their free forms are only present at low levels [15]. Engineered cultivars and low-accumulating genotypes could mitigate CH4 emissions and reduce heavy metal accumulation in rice grown in pig biogas-fertilized fields [16,17]. It is essential to manage and utilize PS effectively in crop production, because it is not only a useful organic fertilizer, but also a potential risk to the environment.
Direct-seeding and transplanting are the most important rice cultivation methods [18]. Rice cultivation in Asia is undergoing significant changes in response to economic factors and technological innovation in farming practices. One such change has been a shift from transplanting to direct-seeding methods for rice establishment. Compared with transplanting, direct-seeding has both advantages and disadvantages. Advantages include water- and labour-saving, higher economic returns, a shorter crop cultivation period, higher abundance and diversity in paddy fields, and lower CH4 emissions [18,19,20,21]. In China, 83.2% of rice was grown by direct-seeding in Shanghai, as was 33.3% in Jiangsu province, and 39.7% in Zhejiang province in 2008 [22]. Direct-seeding is now spreading rapidly to farms around the middle and lower reaches of the Yangtze River. Some of the challenges of the direct-seeding method include weed management, yield loss, and poor and erratic emergence [23,24]. In contrast, transplanting produces taller plants, a greater number of grains per panicle, and a higher 1000-grain weight, and tiller number, fertile tillers, kernel and straw yield, and the harvest index is also higher than in direct-seeding [25,26].
Our group previously tested PS in the production of rice and wheat, and found it can reduce the use of chemical fertilizer and protect the environment [7,27,28,29]. In transplanting rice, PS from pig farming can replace 70% of the chemical fertilizer used, while increasing crop yield and enhancing the content of beneficial elements, as well as altering the levels of heavy metals such as Hg, Cd and Cr [28,29]. To our knowledge, application of PS to direct-seeding rice has not been reported. We predict that PS may act as a chemical fertilizer to improve yield if applied at the appropriate times and spread in the appropriate way. However, whether PS can be applied safely without inducing the accumulation of heavy metals in grains remains unknown, as do the potential effects on rice quality.
In this study, we tested various doses of PS as a basal and panicle fertilizer for growing direct-seeding rice, and measured the effect on rice yield, dry matter accumulation, and trace element uptake in straw and grain at different growth stages. Rice edibility and the rapid visco analyser (RVA) profile were also studied, as was processing quality. These results provide insight into the suitability of PS application for direct-seeding rice production.

2. Materials and Methods

2.1. Study Site

This study was conducted at the Shanghai farm in Dafeng County, Jiangsu province (33°21.736′N, 120°32.012′E) in 2014. This area has a subtropical seasonal climate and a rice-wheat crop rotation system, with an annual mean precipitation of 1040 mm, an annual mean temperature of 14 °C, a frost-free period of 213 days, and annual sunshine totalling 2255 h. The previous crop was wheat. The soil is sandy loam with 19.32 g·kg−1 organic matter, 1.00 g·kg−1 total nitrogen, 75.21 mg·kg−1 alkali hydrolysable N, 23.48 mg·kg−1 Olsen-P, 216.78 mg·kg−1 exchangeable K, 11.35 mg·g−1 Ca, 8.52 mg·g−1 Mg, 0.71 mg·g−1 Na, 23.53 mg·g−1 Fe, 0.10 mg·g−1 Cd, 2.84 mg·kg−1 Cu, 1.00 mg·kg−1 Pb, 6.71 mg·kg−1 Zn, 18.81 mg·kg−1 As, 22.23 mg·kg−1 Cr, and 0.17 mg·kg−1 Hg.
Topsoil (0–20 cm) samples were collected and air-dried, ground into powder and passed through a 2 mm sieve. Only soil <2 mm was used for analyses. Total organic matter in soil was determined by mass loss upon ignition of oven-dried soil in a muffle furnace at 550 °C for at least 6 h. Total N content was determined by micro Kjeldahl digestion. Alkali hydrolysable N was determined by the alkali solution diffusion method. Olsen-P was extracted by NaHCO3 and determined by the classic colorimetric method. Exchangeable K was extracted by ammonium acetate and determined by the flame photometric method. To extract the metal elements in soil, a 0.3 g soil sample was digested by a mixture of concentrated hydrochloric acid and nitric acid (3:1, v/v) using a CEM closed microwave system [30]. The concentrations of metal elements in the extract , namely, Ca, Mg, Na, Fe, Cd, Cu, Pb, Zn, As, Cr and Hg, were determined by an inductively coupled plasma mass spectrometer (ICP-MS, Thermo Fisher Corporation, Munich, Germany).

2.2. Study Materials

PS was obtained from a closed pig slurry collection system. Pig manure, urine and partial flushing water entered the pretreatment tank system through pipelines. After anaerobically fermenting for 6 months, this substance was used in this study. Treated PS contained the following trace elements: 0.246 mg·L−1 Cu, 0.577 mg·L−1 Zn, 0.041 mg·L−1 Pb, <5.0 × 10−4 mg·L−1 Cd, 0.063 mg·L−1 Cr, 0.0283 mg·L−1 As and <5 × 10−4 mg·L−1 Hg. The contents of trace elements in PS conform to the national standards of the irrigation water quality in China (GB5084-92) [28]. The total nitrogen, alkali hydrolysable N, total P2O5, total K2O and pH of PS were 1000 mg·L−1, 540 mg·L−1, 77.9 mg·L−1, 416 mg·L−1 and 7.92, respectively. The rice variety in all the treatments was Huaidao No. 5.

2.3. Field Experiment

The experiment included 11 treatments with three replicates of each treatment (Table 1), including one unfertilized control treatment (CK1), one local conventional fertilization treatment (CK2) consisting of 150 kg·hm−2 urea, 225 kg·hm−2 compound fertilizer (N: P2O5: K2O = 12:15:18) as base fertilizer, 112.5 kg·hm−2 urea as tillering fertilizer and 150 kg·hm−2 urea as panicle fertilizer [28]. Nine treatments (T1–9) involved the combined application of PS and nitrogen fertilizer, and a randomized block design was employed. For basal fertilizer application, PS was applied at a dose of 60, 90 and 120 m3·hm−2. At the panicle fertilizer stage, PS was applied at a dose of 60, 90 and 120 m3·hm−2. At the tillering stage, urea was applied at a dose of 225 kg·hm−2. The area of each block was 15.75 m2 (4.5 m long × 3.5 m wide). The direct sowing rate was 112.5 kg·hm2, and broadcast sowing was adopted. PS as basal fertiliser was applied on 16 June 2013 to allow soil to fully absorb nutrients ahead of seeding, and seeds were sown on 19 June 2013. The management of pests, diseases and weeds was performed using typical local procedures.

2.4. Determination of Trace Elements

A total of 10 rice plants were collected from each group at the jointing, heading and mature stages, and the dry weight of each component was determined by oven-drying at 70 °C to a constant weight. Oven-dried samples were then ground in a stainless steel grinder fitted with a 45-mesh sieve to determine the trace element content in the grain or other parts of the rice plant. Samples were digested using a CEM closed microwave system as follows: 0.48 g samples in nitric acid were digested for 5, 10 and 15 min at 100, 150 and 180 °C. The concentrations of trace elements in the extract, namely, Pb, Cr, Co, Ni, Cu, Zn, Fe, Mn, were measured using an inductively coupled plasma mass spectrometer (ICP-MS, Thermo Fisher Corporation, Munich, Germany).
For all elements tested, the average translocation factor (TF) from straw to grain was calculated as ratios between grain element levels and straw element levels [31].

2.5. Determination of Rice Yield and Grain Quality

Rice grain was harvested from an area of 2.25 m2 in each plot and adjusted to a moisture content of 14%. Aboveground biomass and yield were determined for plants sampled randomly from a 1-m2 area (excluding the border region) in each plot. Evaluation of rice quality was conducted according to the China national standard for grain quality measurements (GB/T 17891-1999; Supervising Department of Quality and Technology of China, 1999) [32], and all analyses were carried out in duplicate. Grains were dehulled to produce brown rice using a chaff removal machine (OHYA-25, Ohya Corporation, Tokyo, Japan) and the percentage of brown rice was determined. Brown rice was milled with a rice polishing machine (JMNJ-3/CPC 96-3, Hangzhou Qianjiang Instrument Corporation, Hangzhou, China) until a standard degree of milling was achieved (as estimated by the percentage of milled rice and head rice).
Milled rice samples were then oven-dried at 60 °C to a constant weight and ground with a stainless steel grinder (FW-100, Shanghai Chuding Instrument Corporation, Shanghai, China) fitted with a 100-mesh sieve to prepare samples for protein content, amylose content, gel consistency and starch viscosity analysis.
Amylose and protein contents were measured with an Infratec 1241 grain analyser (FOSS Tecator, Copenhagen, Denmark) and a near-infrared transmittance analyser, respectively, and calculated based on grain dry weight. Gel consistency was measured by the length of cold milled rice paste in a test tube in a horizontal position. Gelatinization temperature and starch viscosity were determined with a rapid visco analyser (RVA) (RVA-3D, Newport Scientific Inc., Warriewood, Australia) using procedures of the American Association of Cereal Chemists (AACC, 1995).

2.6. Statistical Analysis

Analysis of variance was performed using the SAS/STAT statistical analysis package (version 6.12, SAS Institute, Cary, NC, USA). Data from each sampling date were analyzed separately and met all requirements for analysis of variance. Differences between means were tested using the least significant difference test at the 0.05 probability level.

3. Results

3.1. Effects of Pig Slurry on Direct-Seeding Rice Biomass

After application of varying amounts of PS as basal and heading fertilizer, the yield and dry matter accumulation of straw at the maturing stage were highest with the highest PS dosage (T9 treatment). When applying a low dose of PS (60 m3·hm−2) as basal fertilizer (T1, T2 and T3), the yield decreased by 15.1%, 9.4% and 2.9%, respectively, compared with the control CK2 treatment (Table 2). Application of a medium dosage (90 m3·hm−2) as basal fertilizer, combined with a low (T4) and medium (T5) dosage as panicle fertilizer decreased the yield by only 9.8% and 4.8%, respectively. However, application of a high dosage of PS (120 m3·hm−2) as basal fertilizer, combined with a medium (T8) and high (T9) dosage as panicle fertilizer resulted in a yield that was 0.3% and 6.6% higher, respectively, than that achieved in CK2. Application of PS at 210 m3·hm−2 or more during the heading stage (T6, T8 and T9) therefore increased grain yield in direct-seeding rice. Effects of PS on dry matter accumulation of rice straw at the maturing stage displayed a similar pattern. When applied with the same dosage of PS as basal fertilizer, dry matter accumulation of rice straw also increased with the dosage of PS as panicle fertilizer.

3.2. Effects of Pig Slurry on Trace Element Accumulation in Rice at Different Growth Stages

The Cr, Co, Ni, Cu, Zn, Fe and Mn contents in rice plants decreased gradually from the jointing stage to maturing stage, as the reproductive period advanced, whereas Pb showed the opposite trend (Figure 1 and Figure 2). Pb, Cu, Zn, Fe and Mn were lowest in the CK1 treatment and highest in the T9 treatment. At the jointing, heading and maturing stages, Pb was 84.9%, 121.4% and 61.3% higher in T9 than in CK1, respectively, while Cu was increased by 41%, 65.7% and 86.6%, Zn was increased by 59.6%, 97.2% and 64.0%, Fe was increased by 79.9%, 59.4% and 55.2%, and Mn was increased 60.71%, 76.57% and 41.20%. At the jointing, heading and maturing stages, when comparing T9 with CK2, the Pb content was increased by 26.1%, 39.1% and 17.5%, respectively, Cu was increased by 0.81%, 12.8% and 28.2%, Zn was increased by 0.7%, 13.8% and 9.9%, Fe was increased by 0.38%, 12.5% and 14.4%, whereas Mn was decreased by 3.83%, 8.33% and 4.96%. The amount of these elements increased with increasing application of PS as basal fertiliser during the heading stage, and levels were significantly higher in T6, T8 and T9 than in CK2. In contrast, Cr, Co, Ni were highest in CK2, followed by CK1, and levels of these elements decreased with increasing PS application. In conclusion, the uptake evolution differentiates the micronutrients (Cu, Zn, Fe and Mn) from the non-essential elements (Cr, Co, Ni) with the exception of Pb, which “acts” as a micronutrient.

3.3. Trace Element Content and Translocation in Grains

Under these experimental conditions, CK1 had the lowest levels of all elements tested, but trace elements were all within the acceptable range for food security prescribed by the government. T9 treatment had the highest levels of Pb, Cu, Zn and Fe, followed by T6 and T8 (Table 3). These results indicate that there is a risk of these elements rising to high levels when PS is applied at over 210 m3·hm−2. The highest Cr, Co, Ni and Mn contents in grain occurred with conventional fertilizer treatment, and levels in PS treatments were 4.1%–32.7%, 4.2%–141.0%, 34.0%–186.2% and 2.0%–26.6% lower, respectively, than those in the CK2 treatment. The results showed that PS can alleviate the toxicity of some heavy metals. Specifically, Cr, Co and Ni contents decreased with increasing application of PS at the heading stage, whereas Mn levels increased.
Linear regression analysis was carried out on the total amount of PS applied and the content of each metal element in rice for all nine PS treatments. The results showed a significant positive correlation between the contents of Pb, Cu, Zn, Fe and Mn and the amount of PS applied (r = 0.945**, 0.945**, 0.834**, 0.954**, 0.962**). Conversely, there was a significant negative correlation between the contents of Cr, Co and Ni and the amount of PS applied (r = 0.968**, 0.927**, 0.951**).
For all elements tested, the average transfer factor (TF) in PS treatments was 0.475, 0.441, 0.379 and 0.339, respectively (Table 4). The TFs of Pb, Zn, Cr and Cu from straw to grain were highest, followed by Co, Fe and Ni, and the lowest was Mn with an average TF of only 0.018. These trace elements, especially Mn, therefore accumulated in straw instead of grain, and the TF values were significantly different in PS treatments, except for Mn. The TF of Cr and Zn increased with increasing PS application at the heading stage, while other elements showed the opposite trend. The highest TFs of Pb, Cr, Co, Ni and Cu from straw to grain were reached in CK2, followed by PS treatments, and TF values were lowest in CK1. In contrast, the highest TFs of Zn, Fe and Mn were observed in CK1, followed by PS treatments and then CK2. These results suggest PS could alleviate the transfer of Pb, Cr, Co, Ni and Cu from straw to grain and enhance the transport of Zn, Fe and Mn to rice grain, compared with the CK2 treatment.

3.4. Processing, Eating and Cooking Quality of Grain

In direct-seeding rice, processing quality parameters including brown rice, milled rice and head milled rice all tended to be highest in CK2, intermediate in PS treatments, and lowest in CK1 (Table 5). Brown rice in PS treatments was not significantly different from CK2, but milled and head milled rice increased with increasing PS application for all treatments except T9, and the difference compared to CK2 was significant.
The highest amylose content was observed in CK1, followed by CK2, and differences from most PS treatments were significant (Table 5). The amylose content decreased with increasing PS application at the heading stage when PS was also used as basal fertilizer. The gel consistency was significantly lower in CK1 than in other treatments, and highest in T9, which was 19.2% and 0.7% higher than in CK1 and CK2, respectively, and 0.7%–11.7% higher than in other PS treatments.
The protein content was lowest in CK1 but the difference with most PS treatments was not significant (Table 5), while the highest protein content in grains was reached in T9 (8.5% and 1.4% higher than CK1 and CK2, respectively), followed by T6. The protein content increased with increasing PS application at the heading stage when PS was also used as basal fertilizer. When applying a low dosage of PS as basal fertilizer, the protein content did not differ significantly no matter how much PS was applied at the heading stage, but when a medium or high dosage of PS was applied as basal fertilizer, a high or medium dosage of PS as panicle fertilizer resulted in a significant increase in protein content.

3.5. Starch Pasting Properties

The starch pasting properties of ground grains strongly influences the texture and stickiness of cooked rice, and can be characterized using RVA profiles [32]. Peak viscosity, hot viscosity, cool viscosity, pasting temperature and breakdown were highest in the T9 treatment, as the setback was lowest (Table 6). These parameters all increased with increasing PS application at the heading stage when PS was also used as basal fertilizer, and differences compared with CK2 were significant.

4. Discussion

Previous studies indicate that yield, heavy metal content and crop quality are all significantly affected by application of PS during crop production [12,33,34,35]. Li et al. [11] found that pig manure increased the grain yield between 0.3- and 15.3-fold. In this research, we demonstrated that, when combined with 225 kg·hm−2 urea at the tillering stage, the yield of high dosage of PS application treatment, T8 and T9, can reach or even exceed the yield of conventional chemical treatment (CK2). In each PS treatment, the chemical N applied was only 41.4 percent of that in CK2, saving 58.6 percent chemical N fertilizer. However, it is worthy to point out that, when the total PS application was 150 m3·hm2, the total N input was 253.5 kg·hm2, equal to the CK2 treatment (250 kg·hm2). Thus, when the dosage of PS application was 180, 210 and 240 m3·hm−2, the total load of N exceeded CK2 by 13.4%, 25.4% and 37.4%. Therefore, we caution that when applying PS as fertilizer in rice production, other measures should be taken to avoid ammonia volatilization to the air, and nitrate loss in the water should be altered and avoided.
Successive pig slurry applications may increase soil Cu and Zn concentrations and change the proportions of free chemical species in solution when combined with plant cultivation [13]. Additionally, organic fertilization, especially farmyard manure and straw, significantly reduced the cadmium content in selected vegetables [36]. However, when soils were amended with biogas slurry, Bian et al. [37] measured mean concentrations of Cr of 0.43 and 0.46 mg·kg−1 in rice and wheat, respectively, which are close to the standard limit (0.5 mg·kg−1), and mean concentrations of Zn, Pb, and Cd exceeded the maximum permissible levels by 1.8-, 20.7-, and 2.6-fold, respectively. The reason for the apparent contradiction may be due to differences in heavy metal contents in the PS and biogas slurries applied, or differences in soil characteristics between experiments. In the present study, levels of Ni were highest in both plant material and grain in the CK2 treatment, followed by CK1, and lowest in the nine PS treatments. Cr and Co were highest in CK2, intermediate in PS treatments, and lowest in CK1, suggesting PS can alleviate toxicity of some heavy metals in direct-seeding rice. The Cr, Co and Ni contents decreased with increasing PS, whereas Pb showed the opposite trend. Even though the Pb content in grain was lower than the maximum allowed level, it is still important to be mindful of Pb pollution during long-term PS utilization.
Microelements such as Cu, Zn, Fe and Mn are indispensable for plant growth [11,35]. When Cu and Zn are used as pig feed additives, they can also be found in high concentrations in some animal manures and may be retained in the soil [15,17]. It has been shown that Fe, Mn, Cu and Zn in rapeseed increases with increasing biogas slurry application [38]. Levels of Zn and Cu in stems and leaves were significantly higher in all anaerobically digested slurry treatments than in the control chemical fertilizer treatment, whereas comparable concentrations of Zn and Cu were observed in the rice grain among the treatments [14]. In our study, Cu, Zn, and Fe increased with increasing PS application, consistent with a previous report [38]. Cu, Zn and Fe decreased gradually from the jointing stage to the maturing stage, with the advancement of the reproductive period, and levels were higher than in the CK1 and CK2 treatments when PS was applied in combination with nitrogen fertilizer. Considering the total load of TE, the input quantities of Cu and Zn accompanied by PS were 112.7- and 39.5-fold higher in the T9 treatment when compared with CK2. Therefore, it is reasonable to interpret that contents of Cu and Zn were 9.08% and 30.7% higher than in the CK2 grains. These results indicate that PS can increase the content of some micronutrient elements in direct-seeding rice, but levels remained below the maximum allowed limits. However, concentrations of these elements in soil should continue to be monitored to avoid environmental pollution.
In previous rice research, less attention has been paid to the effects of PS on processing and eating quality. Liu et al. [39] reported that biogas manure is an effective nutrient source for high-quality vegetable production, based on synergistic effects and its ability to enhance yield and improve quality, and to suppress nitrate accumulation. In the present study, application of PS combined with nitrogen fertilizer decreased the processing quality of direct-seeding rice only slightly, but in our previous study, Gao et al. [28] found that application of PS to machine-transplanted rice enhanced brown, milled and head milled rice. Differences in the effects on processing quality may be attributed to different ways nutrients are absorbed under different cultivation methods. Indeed, Zhang et al. [40] found that, compared with machine-transplanted rice, the nutrient absorption pattern of direct-seeding rice is stronger during the early growth stage and weaker during the late growth stage. The underlying mechanisms, however, are not fully understood. Even so, application of PS consistently decreased the amylase content and optimized the RVA profile in both cultivation methods, and therefore improved the overall rice grain quality.

5. Conclusions

In conclusion, with a total PS dosage of between 210 and 240 m3·hm−2 as basal and panicle fertilizer, the yield of direct-seeding rice reached or even exceeded that of regular chemical fertilizer. The Pb content increased gradually from the jointing stage to the maturing stage, but levels of many other metal elements decreased following PS application. Specifically, PS mitigated the accumulation of Cr, Co, Ni and Mn, but levels of Pb, Cu, Zn and Fe increased with increasing PS dosage, reaching a peak in treatment T9 (240 m3·hm−2) that remained below the maximum contaminants allowed in food (GB2762-2005) [29]. Additionally, PS decreased the transfer of Pb, Cr, Co, Ni and Cu from vegetative plant parts to grain, but increased the transfer of Zn, Fe and Mn. Furthermore, PS had only a slight negative effect on grain processing quality, and significantly decreased the amylose content, enhanced gel consistency, and optimized the RVA profile, and improved the overall quality of direct-seeding rice.


This study was supported by the National Natural Science Foundation of China (No. 31201154 and 31571596), Three New Agriculture Project of Jiangsu Province (SXGC[2016]212 and SXGC[2015]089), the Open Project Program of Key Laboratory of Crop Physiology (No. K12008) and the Priority Academic Program Development of Jiangsu Higher Education Institutions.

Author Contributions

Lifen Huang and Hengyang Zhuang conceived and designed the experiments; Wei Gao performed the experiments; Jie Yang and Lifen Huang analyzed the data; Jie Yang contributed reagents/materials/analysis tools; Lifen Huang wrote the paper; Weikang Yang and Xiaoyi Cui revised the paper. All authors read and approved the final manuscript.

Conflicts of Interest

The authors declare no conflict of interest.


  1. Zhang, F.S.; Ma, W.Q.; Cen, X.P. Research and Application of Nutrient Resources Integrated Management Technology; China Agricultural University Press: Beijing, China, 2006. [Google Scholar]
  2. Marcato, C.E.; Pinelli, E.; Pouech, P.; Winterton, P.; Guiresse, M. Particle size and metal distributions in anaerobically digested pig slurry. Bioresour. Technol. 2008, 99, 2340–2348. [Google Scholar] [CrossRef] [PubMed][Green Version]
  3. Brunetto, G.; Comin, J.J.; Schmitt, D.E.; Guardini, R.; Mezzari, C.P.; Oliveira, B.S.; Moraes, M.P.; Gatiboni, L.C.; Lovato, P.E.; Ceretta, C.A. Changes in soil acidity and organic carbon in a sandy typic hapludalf after medium-term pig-slurry and deep-litter application. Rev. Bras. Ciênc. Solo 2012, 36, 1620–1628. [Google Scholar] [CrossRef]
  4. Couto, R.R.; Santos, M.; Comin, J.J.; Pittol Martini, L.C.; Gatiboni, L.C.; Martins, S.R.; Filho, B.P.; Brunetto, G. Environmental vulnerability and phosphorus fractions of areas with pig slurry applied to the soil. J. Environ. Qual. 2015, 44, 162–173. [Google Scholar] [CrossRef] [PubMed]
  5. Guardini, R.; Comin, J.J.; Rheinheimer, D.S.; Gatiboni, L.C.; Tiecher, T.; Schmitt, D.E.; Bender, M.A.; Filho, P.B.; Oliveira, P.A.V.; Brunetto, G. Phosphorus accumulation and pollution potential in a Hapludult fertilized with pig manure. Rev. Bras. Ciênc. Solo 2012, 36, 1333–1342. [Google Scholar] [CrossRef]
  6. Scherer, E.E.; Nesi, C.N.; Massotti, Z. Long-term swine manure fertilization and its effects on soil chemical properties in Santa Catarina, southern Brazil. Rev. Bras. Ciênc. Solo 2010, 34, 1375–1383. [Google Scholar] [CrossRef]
  7. Tao, X.T.; Zhu, Z.J.; Gao, W.; Miao, C.Y.; Wang, Y.L.; Huang, L.F.; Zhuang, H.Y.; Lu, J.F. Nitrogen uptake and utilization in wheat as influenced by pig slurry from large-scale pig farm. J. Agro-Environ. Sci. 2014, 33, 555–561. (In Chinese) [Google Scholar]
  8. Gomez-Munoz, B.; Case, S.D.C.; Jensen, L.S. Pig slurry acidification and separation techniques affect soil N and C turnover and N2O emissions from solid, liquid and biochar fractions. J. Environ. Manag. 2016, 168, 236–244. [Google Scholar] [CrossRef] [PubMed]
  9. Legros, S.; Doelsch, B.; Feder, F.; Moussard, G.; Sansoulet, J.; Gaudet, J.P.; Rigaud, S.; Basile Doelsch, I.; Saint Macary, H.; Bottero, J.Y. Fate and behaviour of Cu and Zn from pig slurry spreading in a tropical water–soil–plant system. Agric. Ecosyst. Environ. 2013, 164, 70–79. [Google Scholar] [CrossRef]
  10. Mallmann, F.J.K.; Rheinheimer, D.S.; Ceretta, C.A.; Cella, C.; Minella, J.P.G.; Guma, R.L.; Filipovié, V.; Oort, F.V.; Simunek, J. Soil tillage to reduce surface metal contamination model development and simulations of zinc and copper concentration profiles in a pig slurry-amended soil. Agric. Ecosyst. Environ. 2014, 196, 59–68. [Google Scholar] [CrossRef]
  11. Li, P.; Wang, X.X.; Zhang, T.L.; Zhou, D.M.; He, Y.Q. Effects of several amendments on rice growth and uptake of copper and cadmium from a contaminated soil. J. Environ. Sci. 2008, 20, 449–455. [Google Scholar] [CrossRef]
  12. Jia, Y.; Sun, G.X.; Huang, H.; Zhu, Y.G. Biogas slurry application elevated arsenic accumulation in rice plant through increased arsenic release and methylation in paddy soil. Plant Soil 2013, 365, 387–396. [Google Scholar] [CrossRef]
  13. Ye, X.X.; Sun, B.; Yin, Y.L. Variation of As concentration between soil types and rice genotypes and the selection of cultivars for reducing as in the diet. Chemosphere 2012, 87, 384–389. [Google Scholar] [CrossRef] [PubMed]
  14. Sasada, Y.; Win, K.T.; Nonaka, R.; Win, A.T.; Toyota, K.; Motobayashi, T.; Hosomi, M.; Chen, D.J.; Lu, J. Methane and N2O emissions, nitrate concentrations of drainage water, and zinc and copper uptake by rice fertilized with anaerobically digested cattle or pig slurry. Biol. Fertil. Soils 2011, 47, 949–956. [Google Scholar] [CrossRef]
  15. De Conti, L.; Ceretta, C.A.; Ferreira, P.A.A.; Lourenzi, C.R.; Girotto, E.; Lorensini, F.; Tiecher, T.L.; Marchezan, C.; Anchieta, M.G.; Brunetto, G. Soil solution concentrations and chemical species of copper and zinc in a soil with a history of pig slurry application and plant cultivation. Agric. Ecosyst. Environ. 2016, 216, 374–386. [Google Scholar] [CrossRef]
  16. Win, A.T.; Koki, T.; DaisUKe, I.; Seiya, C.; Takashi, M.; NatsUKo, T.; Taiichiro, O.; Tadashi, H. Effect of two whole-crop rice (Oryza sativa L.) cultivars on methane emission and Cu and Zn uptake in a paddy field fertilized with biogas slurry. Soil Sci. Plant Nutr. 2016, 62, 99–105. [Google Scholar] [CrossRef]
  17. Duan, G.L.; Zhang, H.M.; Liu, Y.X.; Jia, Y.; Hu, Y.; Cheng, W.D. Long-term fertilization with pig-biogas residues results in heavy metal accumulation in paddy field and rice grains in Jiaxing of China. Soil Sci. Plant Nutr. 2012, 58, 637–646. [Google Scholar] [CrossRef]
  18. Rana, M.M.; Al Mamun, M.A.; Zahan, A.; Zahan, A.; Ahmed, M.N.; Jalil Mridha, M.A. Effect of planting methods on the yield and yield attributes of short duration Aman rice. Am. J. Plant Sci. 2014, 5, 251–255. [Google Scholar] [CrossRef]
  19. Watanabe, K.; Koji, S.; Hidaka, K.; Nakamura, K. Abundance, diversity, and seasonal population dynamics of aquatic Coleoptera and Heteroptera in rice fields: Effects of direct seeding management. Environ. Entomol. 2013, 42, 841–850. [Google Scholar] [CrossRef] [PubMed]
  20. Thakur, A.K.; Roychowdhury, S.; Kundu, D.K.; Singh, R. Evaluation of planting methods in irrigated rice. Arch. Agron. Soil Sci. 2004, 50, 631–640. [Google Scholar] [CrossRef]
  21. Ko, J.Y.; Kang, H.W. The effects of cultural practices on methane emission from rice fields. Nutr. Cycl. Agroecosyst. 2000, 58, 311–314. [Google Scholar] [CrossRef]
  22. Qiang, G. Research progress on cultivation technique of direct-seeding rice in the middle and lower reaches of the Yangtze River. South China Agric. 2015, 18, 36–37. (In Chinese) [Google Scholar]
  23. Balasubramanian, V.; Hill, J.E. Direct seeding of rice in Asia: Emerging issues and strategic research needs for the 21st century. In Direct Seeding: Research Strategies and Opportunities; Pandey, S., Mortimer, M., Wade, L.P., Lopez, K., Hardy, B., Eds.; International Rice Research Institute: Metro Manila, Philippines, 2002; pp. 15–39. [Google Scholar]
  24. Bhushan, L.; Ladha, J.K.; Gupta, R.K.; Singh, S.; Tirol-Padre, S.; Saharawat, Y.S.; Gathala, M.; Pathak, H. Saving of water and labor in a rice–wheat system with no-tillage and direct seeding technologies. Agron. J. 2007, 99, 1288–1296. [Google Scholar] [CrossRef]
  25. Farooq, M.; Basra, S.M.A.; Asad, S.A. ComParison of conventional puddling and dry tillage in rice–wheat system. Paddy Water Environ. 2008, 6, 397–404. [Google Scholar] [CrossRef]
  26. Mahmood, N.; Chatha, Z.A.; Akhtar, B.; Muhammad, S. Response of rice to different sowing methods. Asian J. Plant Sci. 2002, 1, 144–145. [Google Scholar]
  27. Huang, L.F.; Gao, W.; Zhu, Z.J.; Liu, X.C.; Quan, X.Y.; Xu, X.; Wang, Y.L.; Tao, X.T.; Zhuang, H.Y. The effects of different combinations of large-scale pig farm waste water and nitrogen fertilizer on wheat dry matter accumulation and yield formation. China Agric. Sci. Bull. 2012, 28, 165–170. (In Chinese) [Google Scholar]
  28. Gao, W.; Lu, D.M.; Miao, C.Y.; Wang, Y.L.; Quan, X.Y.; Zhuang, H.Y.; Lu, J.F. Effects of pig slurry form large-scale pig farm on rice yield formation and quality. J. Agro-Environ. Sci. 2012, 31, 2256–2264. (In Chinese) [Google Scholar]
  29. Gao, W.; Wang, Y.L.; Tao, X.T.; Shi, J.Q.; Xu, X.; Lu, J.F.; Zhuang, H.Y. Effects of pig slurry from large-scale pig farm on medium, micro-and heavy elements contents of rice. J. Agro-Environ. Sci. 2013, 32, 1639–1647. (In Chinese) [Google Scholar]
  30. Wu, Q.; Leung, J.Y.S.; Geng, X.; Chen, S.; Huang, X.; Li, H.; Huang, Z.; Zhu, L.; Chen, J.; Lu, Y. Heavy metal contamination of soil and water in the vicinity of an abandoned e-waste recycling site: Implications for dissemination of heavy metals. Sci. Total Environ. 2015, 506, 217–225. [Google Scholar] [CrossRef] [PubMed]
  31. Zhu, H.; Zhong, H.; Wu, J. Incorporating rice residues into paddy soils affects methylmercury accumulation in rice. Chemosphere 2016, 152, 259–264. [Google Scholar] [CrossRef] [PubMed]
  32. Supervising Department of Quality and Technology of China. Available online: (accessed on 10 September 2003). (In Chinese)
  33. Mantovi, P.; Baldoni, G.; Toderi, G. Reuse of liquid, dewatered, and composted sewage sludge on agricultural land: Effects of long-term application on soil and crop. Water Res. 2005, 39, 289–296. [Google Scholar] [CrossRef] [PubMed]
  34. Liu, W.K.; Du, L.F.; Yang, Q.C. Biogas slurry added amino acids decreased nitrate concentrations of lettuce in sand culture. Acta Agric. Scand. B Soil Plant Sci. 2009, 59, 260–264. [Google Scholar]
  35. Galavi, M.; Yosefi, K.; Ramrodi, M. Effect of bio-phosphate and chemical phosphorus fertilizer accompanied with foliar application of micronutrients on yield, quality and phosphorus and zinc concentration of maize. J. Agric. Sci. 2011, 3, 22–29. [Google Scholar] [CrossRef]
  36. Zaniewicz-Bajkowska, A.; Rosa, R.; Franczuk, J.; Kostern, E. Direct and secondary effect of liming and organic fertilization on cadmium content in soil and in vegetables. Plant Soil Environ. 2007, 53, 473–481. [Google Scholar]
  37. Bian, B.; Wu, H.S.; Lv, L.; Fan, Y.M.; Lu, H.M. Health risk assessment of metals in food crops and related soils amended with biogas slurry in Taihu Basin: Perspective from field experiment. Environ. Sci. Pollut. Res. 2015, 22, 14358–14366. [Google Scholar] [CrossRef] [PubMed]
  38. Wu, J.; Yang, Q.; Yang, G.; Shen, F.; Zhang, X.H.; Zhang, Y.Z. Effects of biogas slurry on yield and quality of oil-seed rape. J. Plant Nutr. 2013, 36, 2084–2098. [Google Scholar] [CrossRef]
  39. Liu, W.K.; Yang, Q.C.; Du, L.F. Soilless cultivation for high-quality vegetables with biogas manure in China: Feasibility and benefit analysis. Renew. Agric. Food Syst. 2009, 24, 300–307. [Google Scholar] [CrossRef]
  40. Zhang, Z.J.; Xie, C.L.; Xie, R.K.; Lang, Y.Z.; Yang, L.; Zhang, J.F.; Zhu, Q.S. Population production capacity of direct-seeding rice in central Jiangsu Region and effects of nitrogen application. Acta Agron. Sin. 2011, 37, 677–685. (In Chinese) [Google Scholar] [CrossRef]
Figure 1. Pb, Cr, Co and Ni concentrations in plants after the application of PS at different growth stages. Different letters indicate significant differences between PS treatments at the 0.05 level; the bars are standard errors.
Figure 1. Pb, Cr, Co and Ni concentrations in plants after the application of PS at different growth stages. Different letters indicate significant differences between PS treatments at the 0.05 level; the bars are standard errors.
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Figure 2. Cu, Zn, Fe and Mn concentrations in plants after the application of PS at different growth stages. Different letters indicate significant differences between PS treatments at the 0.05 level; the bars are standard errors.
Figure 2. Cu, Zn, Fe and Mn concentrations in plants after the application of PS at different growth stages. Different letters indicate significant differences between PS treatments at the 0.05 level; the bars are standard errors.
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Table 1. Design of the field experiment.
Table 1. Design of the field experiment.
TreatmentPig Slurry as Basal Fertilizer (m3·hm−2)Pig Slurry as Panicle Fertilizer (m3·hm−2)Total Amount of Pig Slurry (m3·hm−2)
CK1 a000
CK2 b000
a Zero fertilizer and pig slurry treatment designated as CK1 for basic evaluation of soil fertility; b Conventional chemical fertilizer treatment designated as CK2 for field production control.
Table 2. Aboveground plant biomass production among pig slurry treatments (kg·hm−2).
Table 2. Aboveground plant biomass production among pig slurry treatments (kg·hm−2).
T17184.69 ± 188.27g6542.00 ± 201.22f
T27454.74 ± 261.03e6979.55 ± 239.57e
T37581.56 ± 212.89d7479.55 ± 267.31c
T47216.14 ± 181.15f6948.25 ± 236.19e
T57447.43 ± 281.67e7333.70 ± 287.34d
T67837.75 ± 260.56c7771.20 ± 314.73b
T77418.24 ± 377.64e7427.45 ± 287.45c
T88136.09 ± 253.35b7729.55 ± 290.82b
T98244.99 ± 391.41a8210.80 ± 342.61a
CK15847.55 ± 167.39h6510.75 ± 235.95f
CK27549.47 ± 260.62d7704.50 ± 276.17b
Different letters in a column indicate significant differences between PS treatments at the 0.05 level.
Table 3. Contents of trace element in grains under different PS treatments (mg·kg−1).
Table 3. Contents of trace element in grains under different PS treatments (mg·kg−1).
T10.0617 ± 0.0012b0.0632 ± 0.0018a0.0710 ± 0.0018a0.0927 ± 0.0029b0.2083 ± 0.0096a0.9646 ± 0.0401c33.8 ± 1.1cd4.383 ± 0.158c
T20.0662 ± 0.0013a0.0592 ± 0.0029c0.0606 ± 0.0016b0.0762 ± 0.0034bc0.2098 ± 0.0036a0.9925 ± 0.0257c34.4 ± 1.3c4.804 ± 0.203b
T30.0672 ± 0.0015a0.0532 ± 0.0024f0.0512 ± 0.0018c0.0677 ± 0.0029c0.2191 ± 0.0108a1.0337 ± 0.0224bc36.9 ± 0.4b5.003 ± 0.123b
T40.0643 ± 0.0031a0.0602 ± 0.0009b0.0707 ± 0.0024a0.0812 ± 0.0028bc0.2087 ± 0.0075a0.9691 ± 0.0256c33.9 ± 1.9d4.585 ± 0.094c
T50.0664 ± 0.0017a0.0562 ± 0.0024d0.0604 ± 0.0029b0.0668 ± 0.0032c0.2162 ± 0.0105a1.0050 ± 0.0283c35.8 ± 0.8c4.946 ± 0.195b
T60.0679 ± 0.0027a0.0506 ± 0.0006g0.0327 ± 0.0016c0.0441 ± 0.0015d0.2373 ± 0.0078a1.2883 ± 0.0568ab38.3 ± 1.5a5.110 ± 0.114b
T70.0669 ± 0.0028a0.0553 ± 0.0014e0.0569 ± 0.0011b0.0682 ± 0.0024c0.2178 ± 0.0047a1.0079 ± 0.0182c35.8 ± 0.5c4.960 ± 0.127c
T80.0679 ± 0.0022a0.0521 ± 0.0008f0.0455 ± 0.0014c0.0629 ± 0.0023cd0.2369 ± 0.0041a1.0675 ± 0.0238bc38.1 ± 1.8a5.058 ± 0.232b
T90.0723 ± 0.0012a0.0496 ± 0.0023g0.0307 ± 0.0009c0.0434 ± 0.0007d0.2463 ± 0.0038a1.3632 ± 0.0271a38.7 ± 0.5a5.442 ± 0.188a
CK10.0565 ± 0.0021b0.0646 ± 0.0017a0.0738 ± 0.0012a0.0952 ± 0.0026b0.1616 ± 0.0079b0.9196 ± 0.0236c33.4 ± 0.9d4.267 ± 0.071d
CK20.0677 ± 0.0008a0.0658 ± 0.0028a0.0740 ± 0.0029a0.1242 ± 0.0045a0.2258 ± 0.0049a1.0427 ± 0.0468bc37.2 ± 0.7b5.550 ± 0.215a
Different letters in a column indicate significant differences between PS treatments at the 0.05 level.
Table 4. Translocation factors (TFs) of trace elements from straw to grain.
Table 4. Translocation factors (TFs) of trace elements from straw to grain.
T10.512 ± 0.014b0.361 ± 0.013c0.244 ± 0.002b0.128 ± 0.002b0.406 ± 0.003a0.420 ± 0.017e0.142 ± 0.007b0.019 ± 0.001a
T20.502 ± 0.018c0.383 ± 0.011b0.214 ± 0.006d0.116 ± 0.007c0.374 ± 0.012b0.452 ± 0.005d0.123 ± 0.004c0.018 ± 0.001a
T30.464 ± 0.022d0.400 ± 0.017a0.209 ± 0.001e0.116 ± 0.003c0.338 ± 0.014c0.506 ± 0.002b0.120 ± 0.001c0.017 ± 0.001a
T40.518 ± 0.005b0.372 ± 0.012bc0.248 ± 0.005b0.121 ± 0.003b0.377 ± 0.009b0.423 ± 0.018e0.126 ± 0.001c0.019 ± 0.001a
T50.497 ± 0.012c0.379 ± 0.014b0.222 ± 0.004c0.104 ± 0.004e0.348 ± 0.009c0.448 ± 0.006d0.123 ± 0.005c0.019 ± 0.001a
T60.437 ± 0.013f0.388 ± 0.013b0.182 ± 0.003f0.082 ± 0.004f0.275 ± 0.007f0.453 ± 0.002d0.121 ± 0.001c0.017 ± 0.001a
T70.463 ± 0.017d0.361 ± 0.004c0.223 ± 0.003c0.113 ± 0.004cd0.341 ± 0.014c0.377 ± 0.012g0.122 ± 0.006c0.018 ± 0.001a
T80.458 ± 0.015e0.369 ± 0.016c0.213 ± 0.006d0.111 ± 0.004d0.314 ± 0.019e0.416 ± 0.004e0.121 ± 0.002c0.017 ± 0.001a
T90.425 ± 0.024f0.398 ± 0.017a0.178 ± 0.007f0.092 ± 0.003f0.279 ± 0.013f0.473 ± 0.001c0.110 ± 0.004d0.017 ± 0.001a
CK10.468 ± 0.017d0.395 ± 0.009a0.207 ± 0.006e0.125 ± 0.002b0.327 ± 0.015d0.523 ± 0.015a0.148 ± 0.001a0.020 ± 0.001a
CK20.536 ± 0.009a0.403 ± 0.008a0.254 ± 0.002a0.149 ± 0.005a0.341 ± 0.005c0.397 ± 0.007f0.119 ± 0.002c0.016 ± 0.001a
Different letters in a column indicate significant differences between PS treatments at the 0.05 level.
Table 5. Processing, cooking and eating quality of rice grains under different PS treatments.
Table 5. Processing, cooking and eating quality of rice grains under different PS treatments.
TreatmentsBrown RiceMilled RiceHead Milled RiceProtein ContentAmylose ContentGel Consistency
T185.3 ± 2.2b79.5 ± 1.5c75.1 ± 3.2cd8.8 ± 0.4c18.4 ± 0.3ab64.0 ± 1.2b
T285.4 ± 1.4ab81.0 ± 2.4c76.1 ± 1.9cd9.0 ± 0.2abc18.1 ± 0.9abc64.5 ± 2.7b
T385.4 ± 4.0ab85.6 ± 3.5bc78.5 ± 3.9bc9.1 ± 0.3abc17.3 ± 0.7bcd66.0 ± 2.7b
T485.4 ± 2.2ab79.9 ± 3.4c75.8 ± 3.6cd8.9 ± 0.4bc17.7 ± 0.4abcd64.5 ± 1.3b
T585.4 ± 1.6ab82.6 ± 2.5bc78.3 ± 2.5bcd9.0 ± 0.1abc17.5 ± 0.8abcd64.0 ± 3.2b
T685.6 ± 2.1ab87.1 ± 1.8bc81.8 ± 3.4b9.3 ± 0.2ab17.3 ± 0.6bcd70.0 ± 1.5a
T785.4 ± 1.7ab82.9 ± 3.3bc78.4 ± 1.9bcd9.0 ± 0.4abc17.4 ± 0.8bcd64.5 ± 1.4b
T885.5 ± 3.2ab86.0 ± 3.7bc79.4 ± 1.2bc9.1 ± 0.4abc16.8 ± 0.7cd71.0 ± 1.0a
T985.9 ± 3.1ab88.3 ± 4.2ab82.9 ± 2.2b9.4 ± 0.4a16.8 ± 0.2d71.5 ± 2.6a
CK184.5 ± 3.8c79.5 ± 1.4c74.0 ± 2.3d8.7 ± 0.3c18.6 ± 0.5a60.0 ± 2.2c
CK286.1 ± 0.9a88.7 ± 4.1a83.0 ± 1.2a9.2 ± 0.4ab18.5 ± 0.4a71.0 ± 1.5a
Different letters in a column indicate significant differences between PS treatments at the 0.05 level.
Table 6. RVA profile characteristics for evaluating starch pasting properties of rice grains under different PS treatments.
Table 6. RVA profile characteristics for evaluating starch pasting properties of rice grains under different PS treatments.
TreatmentsPeak ViscosityHot ViscosityCool ViscosityPasting TemperatureBreakdownSetback
T12045.3 ± 23.1c1319.7 ± 34.9b2325.7 ± 34.7bc69.7 ± 3.3b675.0 ± 16.1e292.0 ± 5.1a
T22085.0 ± 24.4bc1339.0 ± 53.5b2336.7 ± 82.1bc70.0 ± 2.1b720.0 ± 15.8c266.0 ± 7.7b
T32156.7 ± 43.5bc1390.0 ± 55.6b2369.3 ± 111.8bc70.2 ± 0.8b766.5 ± 36.4b249.0 ± 6.3c
T42084.7 ± 47.6bc1327.0 ± 41.4b2331.0 ± 60.4bc69.7 ± 2.7b710.5 ± 29.9d274.5 ± 3.5b
T52098.7 ± 70.7bc1344.0 ± 36.2b2344.5 ± 104.0bc70.0 ± 2.8b733.0 ± 9.2c257.5 ± 3.4b
T62204.3 ± 95.1ab1438.7 ± 43.5ab2444.0 ± 42.3ab70.5 ± 3.3b772.0 ± 35.2ab226.0 ± 4.8e
T72110.7 ± 87.3bc1364.3 ± 21.3b2353.3 ± 92.5bc70.2 ± 1.2b758.0 ± 25.9b255.5 ± 7.8b
T82163.3 ± 23.6bc1391.0 ± 32.7b2374.0 ± 102.2bc70.3 ± 2.6b770.0 ± 24.8ab231.0 ± 8.6d
T92317.3 ± 89.8a1562.3 ± 69.8a2558.3 ± 64.3a78.3 ± 3.6a791.5 ± 23.6a199.5 ± 4.5f
CK12039.0 ± 75.4c1310.3 ± 20.4b2312.3 ± 98.2c69.7 ± 0.8b663.0 ± 26.7e259.5 ± 11.2b
CK22109.7 ± 42.1bc1346.7 ± 33.9b2352.0 ± 87.1bc70.2 ± 3.9b753.5 ± 21.1b292.0 ± 8.1a
Different letters in a column indicate significant differences between PS treatments at the 0.05 level.
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