Residue Monitoring of Propiconazole in the Rice–Crab Co-Culture Field and its Toxicity and Bioaccumulation to Eriocheir sinensis

Abstract

Rice–crab co-culture is a high-benefit eco-breeding pattern that has been extensively developed in many regions of China. However, little attention has been paid to the safety of pesticides used to control rice pests in the crab–rice co-culture system. This study monitored the actual residue levels of propiconazole in water and soil of rice–crab co-culture fields and evaluated the acute toxicity, subchronic toxicity, and bioaccumulation of propiconazole to Eriocheir sinensis. We observed that the residue level of propiconazole in paddy soil was higher than that in paddy water within 42-day field monitoring. Propiconazole demonstrated a low acute toxicity (96 h-LC₅₀ > 100 mg/L) to E. sinensis and exhibited no obvious adverse impact on the growth of E. sinensis after exposure to 500 μg/L, which was 10 times the actual residual concentration of propiconazole in the crab–rice co-culture field. The highest bioaccumulation of propiconazole was obtained from gills, followed by the hepatopancreas and meat. These results will contribute to the guidance of scientific utilization of pesticides in the crab–rice co-culture field.

Introduction

Food shortage has become an urgent problem to be solved because of the rapid growth of population and limited water and soil resources (Bashir et al., 2020; Xu et al., 2021; Zhang et al., 2021). As one of the important staple foods, rice (Oryza sativa L.) feeds roughly half of the global population (Fageria, 2007; Liu et al., 2018). However, rice production systems have been identified as a major sector wasting available water resources, consuming up to 90 percent of irrigation water in Asia. Thus, improving the utilization of land and water resources in the rice production system is still a lacking demand (Bashir et al., 2020).

The co-culture of rice and aquatic animals has a history of more than 2,000 years in China (Wang et al., 2021). It has been considered a strategy to improve the utilization of land and water resources in paddy fields to provide both grains and aquatic animal protein products to humans (Zhang et al., 2021). The Chinese mitten crab (Eriocheir sinensis) is native to the coastal rivers and estuaries of the Yellow Sea. It is an important freshwater aquaculture species in China because of its rapid growth, strong fertility, and high nutritional values (Shen et al., 2017; Hong et al., 2019), with an annual output of over 770,000 tons (BFMA, 2020). Driven by huge economic benefits, E. sinensis has been developing rapidly in China in recent years and contains a variety of farming models. Rice–crab co-culture is a high-benefit eco-breeding pattern that has been extensively developed in many regions of China, especially in Liaoning Province (Yan et al., 2014). Panjin city, Liaoning Province, a representative area for cultivating crabs in paddy fields, has a rice–crab co-culture area of about 45,300 ha, accounting for 43.27% of the city’s rice-planting area.

However, there are still some problems to be solved in the rice–crab co-culture system, especially the safety issues of pesticides to biological resources, for e.g., E. sinensis, when they were applied to control rice diseases, pests, and weeds. Although the crabs could eliminate some weeds and pests in the field to achieve the effect of biological pest control, there is no evidence that crabs can effectively control rice diseases. Therefore, in order to avoid rice yield reduction caused by diseases, fungicides have to be used to control rice diseases in rice–crab co-culture fields. Propiconazole was first registered in 1981 by the United States Environmental Protection Agency (EPA) in applications against a broad range of fungal diseases (Souders et al., 2019). The fungicide acts via demethylation of the C14 in ergosterol biosynthesis, an event that disrupts fungal cell wall integrity, effectively impeding further fungal growth (Johansen et al., 2007). Propiconazole is widely used in China to control rice diseases, and more than 150 formulations containing propiconazole have been registered for the control of rice diseases by the Ministry of Agriculture and Rural Affairs of China. However, propiconazole is frequently detected in the aquatic environment. Battaglin et al. detected propiconazole residues in 13% of 29 rivers in 13 states of the United States with a maximum concentration of 1.15 μg/L (Battaglin et al., 2010). Similarly, in Belgium, propiconazole was detected in surface water samples collected from 16 locations and ranged from 1.9 to 178.3 ng/L in effluent from waste water treatment plants (Van De Steene et al., 2010). Propiconazole has been found to have potential effects on aquatic invertebrate crabs, such as Mysidopsis bahia (28 days reproduction NOEC = 0.114 mg/L) (European Food Safety Authority, 2017). In addition, the long half-life (DT50) of propiconazole in the environment makes it more vital to investigate the long-term influence on the related biological resources and environment. Edwards et al. reported that propiconazole showed a DT50 value of 99–116 days in agricultural practices (Edwards et al., 2016). DT50 of propiconazole in the water/sediment system was 561 days according to the European Food Safety Authority (European Food Safety Authority, 2017). Therefore, it is necessary to study whether propiconazole has potential adverse effects on E. sinensis in the rice–crab co-culture system. Although propiconazole belongs to medium bioaccumulation chemicals, indicated by the bioconcentration factor (BCF) of 180 in fish (European Food Safety Authority, 2017), whether or not propiconazole can accumulate in E. sinensis, enter, and affect human health through the food chain is still unknown.

In the present study, the residue level of propiconazole in water and soil of rice–crab co-culture fields was monitored. In addition, the acute toxicity, subchronic toxicity, and bioaccumulation of propiconazole to E. sinensis were evaluated. The purpose was to quantify the potential adverse effects of propiconazole on the Chinese mitten crab based on the actual residual amount of propiconazole in the rice and crab co-culture fields and to provide guidance for the scientific use of propiconazole in the rice and crab co-culture system.

Materials and Methods

Chemical Material

95% propiconazole was purchased from Yunxin (Beijing) Agricultural Technology Co., Ltd. Stock solution of propiconazole exposure was prepared in dimethyl sulfoxide. The 25% propiconazole emulsifiable concentrate (EC) and propiconazole stock standard solutions of 100 mg/L in acetone were supplied by the College of Science, China Agricultural University. Dimethyl sulfoxide (purity 99.7%) and Tween 80 were purchased from J&K Scientific Ltd.

Field Experiment

One rice–crab co-culture field located in Panjin, China, was selected for this study. The experimental plots were 50 m² and consisted of a control site and propiconazole treatment site. Each treatment was conducted in three plots, with a 50-m² plot separating each site, acting as a buffer between locations. The map of the field experiment plot is shown in Figure 1.

FIGURE 1

25% propiconazole EC was sprayed evenly in the aforementioned experiment plots using a SeeSa SX-MD16E-2 backpack sprayer at an active ingredient dose of 45 g a. i/ha. The paddy water and soil samples were collected from each plot at 10 intervals up to 42 days after propiconazole application, i.e., 0 days (2 h), 1, 3, 5, 7, 10, 14, 21, 30, and 42 days. At each sampling date, at least 1 kg of soil (pooled sub-samples from randomly ten points) and 2000 ml of water (pooled sub-samples from 10 random locations) were taken and stored frozen (−20°C) until analysis.

Acute Toxicity

The acute toxicity of propiconazole to juvenile crabs was determined under static-renewal conditions. Crabs were exposed to a nominal concentration of 100 mg a. i./L for 96 h, alongside a dilution water control and solvent control (1.0 × 10⁻² mg/L dimethyl sulfoxide+1.0 × 10⁻⁴ mg/L Tween 80). Each test concentration was replicated three times. Glass fish tanks with a capacity of 60 L were used for the exposure operation. Each tank contained 50 L of exposure solutions and 10 crabs. The whole exposure solutions were replaced daily. Mortalities and visible abnormalities (individuals not dead but unresponsive to touching the periopods and eyestalk were considered abnormal) were recorded daily. During the acute toxicity experiment, crabs were not fed, and dead individuals were removed immediately from the tank.

Subchronic Toxicity

Juvenile crabs, after being weighed, were exposed to two sublethal concentrations (0.05 and 0.50 mg/L) of propiconazole dissolved in water under static-renewal conditions for 28 days. In total, ten crabs in each group without replicate were exposed to glass tanks containing 50 L blank control, solvent control (5.0 × 10⁻⁵mg/L dimethyl sulfoxide+5.0 × 10⁻⁷mg/L Tween 80), and propiconazole solution. The exposure solutions were prepared as described in the acute toxicity test. The control group was fed with excess feed as a reference to ensure that adequate nutrients were available. The whole test solutions were replaced daily. The crabs were examined daily during the test period. Any mortalities or the number of molting was recorded. At the end of the test, all surviving crabs were weighed as wet weights (blotted dry).

Bioaccumulation Test

In total, sixty crabs (ca. 35∼40 g) of each treatment group were exposed to 0.05 and 0.50 mg/L of propiconazole for 42 days. Solution preparation, exposure operation, and feeding patterns remained consistent with subchronic experiments. Uneaten food and feces were siphoned daily from the test chambers shortly after feeding (30 min to 1 hour).

In total, four crabs were sampled on each occasion, i.e., 0 days (2 h), 1, 2, 3, 5, 7, 10, 14, 21, 28, 35, and 42 days. The gill, meat, and hepatopancreas of each crab were collected and homogenized by steel balls and stored frozen (−20°C) until analysis.

Chemical Analysis of Propiconazole in Soil, Water, and Crab Tissues

Preparation of the Water Sample

For preparation of the water sample, 10 ml of the water sample was transferred into a 50-ml centrifuge tube, and 10 ml acetonitrile and 3 g sodium chloride were added. The solution was vortexed for 5 min and subsequently centrifuged at 3800 r/min for 5 min. The organic layer was transferred to a 1-ml EP tube containing 30 mg of PSA and 100 mg of anhydrous magnesium sulfate. After vortex and centrifugation, the supernatant was filtered through a 0.22-μm membrane filter into an autosampling vial and analyzed by LC–MS/MS.

Preparation of the Soil Sample

An additional 10 ml of water was added during sample extraction, with further preparation of samples following the same procedures as described for water sample analysis.

Preparation of Crab Tissues

For preparation of crab tissues, 1.0 g of thawed gills was added to a 15-ml stoppered centrifuge tube, followed by 5 ml of acetonitrile and 3 g of sodium chloride. It was shaken vigorously for 5 min and then centrifuged at 3,800 rpm for 5 min, and one milliliter of the supernatant was added to an EP tube containing 50 mg C18 and 100 mg anhydrous magnesium sulfate. After vortex and centrifugation, the supernatant was tested by passing through a 0.22-µm filter membrane. The samples of crab meat and hepatopancreas were processed as for crab gills.

Apparatus

All samples were detected by LC–MS/MS of Shimadzu. The ion source was electrospray ionization (ESI), and Agilent Poroshell 120EC-C₁₈ (2.7 μm × 2.1 mm × 50 mm) was employed at room temperature. The flow rate of acetonitrile/H₂O (0.1%HCOOH) = 70/30 (V/V) was 0.2 ml min⁻¹. MRM was selected as the detection mode in triple-quadrupole mass spectrometry. The relevant parameters and the limit of detection of this method are listed in Table 1.

Data Analysis

Statistical analyses were conducted using SPSS software (Version 20.0, SPSS Inc., Chicago, IL, United States). Data normality and homogeneity of variance were validated using the Kolmogorov–Smirnov and Levene’s tests, respectively. Significant differences between the control and exposure groups were evaluated using Dunnett’s one-way analysis of variance (ANOVA) with a statistical significance threshold of p < 0.05.

Results

Residues of Propiconazole in Water and Soil

As shown in Figure 2, the concentrations of propiconazole in paddy water decreased significantly during the initial 10 days of application. The peak concentration was approximately 0.005 mg/L for propiconazole, and they then remained relatively constant from 10 to 42 days.

FIGURE 2

The measured concentrations of propiconazole in soil were presented in Figure 3. The levels of soil residues of propiconazole peaks on the third day (∼0.05 mg/kg) after application, then reduced and fluctuated around 0.01 mg/kg during the rest of the test period.

FIGURE 3

Toxicity Results

No mortality or abnormal behaviors of juvenile crabs were observed after exposed to propiconazole (100 mg/L) for 96 h, indicating that the acute toxicity of propiconazole to E. sinensis is low.

The growth effect on juvenile crabs by propiconazole at concentrations of 0.05 and 0.50 mg/L was also evaluated. For a 28-day exposure, no mortality or molting was observed among the test organisms. The average weight growth rates for the 0–28 days period range from 13.7 to 15.7% (Figure 4), and there was no significantly statistical difference between the treatment groups and the control ones.

FIGURE 4

Bioconcentration in Crab Tissues

The highest bioaccumulation of propiconazole was detected in gills, followed by the hepatopancreas and muscle (Figures 5–7). The bioconcentration of propiconazole in the gills showed a time-dependent increase but did not reach a steady state during the 42-day test period (Figure 5). When crabs were exposed to propiconazole for 14 days, the bioaccumulation in the muscles reached a peak and then decreased to a steady state (Figure 6). The bioconcentration of propiconazole in the hepatopancreas fluctuated during the 42-day exposure period (Figure 7).

FIGURE 5

FIGURE 6

FIGURE 7

Discussion

It is reported that the effective utilization rate of pesticides was only about 40% in China (Shuqin and Fang, 2018), which means that about 60% of propiconazole will enter the paddy water and soil after it is used in paddy fields. Considering the long half-life of propiconazole in water and sediments, E. sinensis raised in rice fields may be exposed to high doses of propiconazole in long terms, which may harm the health of E. sinensis and cause economic losses. Therefore, this study first monitored the dissipation of propiconazole in the rice–crab co-culture field. The dissipation dynamics of propiconazole in the rice–crab co-culture field in Panjin City, Liaoning Province, was consistent with that of triazole fungicide difenoconazole in rice fields in Guangxi and Hubei reported by Wang et al. (2012).

The studies on the acute toxicity of pesticides to E. sinensis are currently mostly focused on the evaluation of the toxicity of insecticides, while there are relatively few studies on the toxicity of fungicides and herbicides. It has been reported that the organophosphorus insecticides phoxim, chlorpyrifos, triazophos, and organochlorine insecticide endosulfan were highly toxic to E. sinensis, while insecticides such as imidacloprid and avermectin were less toxic to E. sinensis (Li et al., 2013; Chen et al., 2014; Lu et al., 2020). Different formulations of diafenthiuron have also been found to have different toxicity to E. sinensis. The 96 h-LC₅₀ of diafenthiuron suspension concentrate (SC) was 42.55 mg/L, while the toxicity of emulsifiable concentrate (EC) is relatively higher due to the adjuvant, 96 h-LC₅₀, was 24.66 mg/L (Gao et al., 2010). Compared with insecticides, fungicides have relatively low toxicity to E. sinensis. Our results demonstrated that propiconazole is a low-toxic chemical to E. sinensis. Similar results were also reported by Zhang (Zhang et al., 2014). Considering that the residual level of propiconazole in the field is unlikely to reach 100 mg/L, there is no risk of acute lethality to E. sinensis after propiconazole is applied in the rice–crab co-cultivation field.

Since propiconazole has a long half-life in the environment, evaluating its acute toxicity alone is not enough to predict its safety to E. sinensis. It has been reported that some environmental pollutants have an impact on the growth and development of E. sinensis. For example, E. sinensis was exposed to chronic copper solution for 21 days, which significantly affects the weight gain of E. sinensis (Bu et al., 2022). A similar growth inhibition result of mercury chloride on E. sinensis has also been reported (Zhao et al., 2009). Our subchronic toxicity test results found that when E. sinensis was exposed to two doses of the highest residue in the field and 10 times the highest residue, propiconazole did not affect the growth of E. sinensis. However, whether propiconazole has adverse effects on the biochemical indicators of E. sinensis needs further study. Previous studies have shown that the antioxidant enzyme activities of rainbow trout were induced after long-term exposure to propiconazole (Li et al., 2010). In addition, propiconazole can also induce hypopigmentation, disrupt mitochondrial bioenergetics, and can alter locomotor activity in zebrafish (Souders et al., 2019). Therefore, more biochemical and genetic studies are needed to clarify the potential harm of propiconazole to E. sinensis.

The pesticides absorbed by organisms from the surrounding environment may accumulate in the body to amplify its biological effects and may also be transmitted through the food chain, thereby adversely affecting high-level organisms. Triazole fungicides have been reported to have the risk of bioaccumulation in organisms. For instance, tebuconazole, hexaconazole, and myclobutanil have been demonstrated to accumulate in zebrafish (Andreu-Sanchez et al., 2012; Wang et al., 2015; Liu et al., 2016; Pang et al., 2020). Rainbow trout can be accumulated with a variety of triazole fungicides including bromuconazole, cyproconazole, metconazole, myclobutanil, penconazole, propiconazole, tebuconazole, tetraconazole, and triadimefon (Konwick et al., 2006). The present bioconcentration study showed that the gill and hepatopancreas of E. sinensis could be the most susceptible parts where propiconazole accumulated in. E. sinensis is one of the most popular seasonal autumn foods in China. Thus, the potential health risk induced by consuming E. sinensis should be concerned. No maximum residue levels (MRLs) of propiconazole have been applied to fish, fish products, and any other marine and freshwater food products. Therefore, MRLs which applied to products of amphibians and reptiles were referred to, i.e., 0.01 mg/kg for propiconazole [Reg (EU) 2021/155]. Measured residues of propiconazole in the gill and hepatopancreas rather than meat in the laboratory study exceeded the EU MRLs. The gill tissues of E. sinensis were inedible, but the hepatopancreas was the most favorable tissues to be consumed. In regard to health risk, the reference values of acceptable daily intake (ADI) and acute reference dose (ARfD) were established by the European Commission for propiconazole [ADI 0.04 mg/kg bw/d, ARfD 0.1 mg/kg bw; Reg (EU) 2018/1865]. Considering the limited intake of the hepatopancreas and meat during a specific season, the possibility that adverse health effects occurred to consumers due to propiconazole residues was very low.

In conclusion, it was safe for E. sinensis in the rice–crab co-culture field to apply propiconazole based on normal agronomic practices. However, due to the persistence of propiconazole in the environment and its bioaccumulation in crab tissues, excessive use of propiconazole in the rice–crab co-culture field system should be avoided. In addition, the mechanism of differential bioaccumulation of propiconazole in different tissues of E. sinensis needed further investigations.

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