New Insights into the Microbial Degradation of D-Cyphenothrin in Contaminated Water/Soil Environments.

Persistent use of the insecticide D-cyphenothrin has resulted in heavy environmental contamination and public concern. However, microbial degradation of D-cyphenothrin has never been investigated and the mechanism remains unknown. During this study, for the first time, an efficient D-cyphenothrin-degrading bacterial strain Staphylococcus succinus HLJ-10 was identified. Response surface methodology was successfully employed by using Box-Behnken design to optimize the culture conditions. At optimized conditions, over 90% degradation of D-cyphenothrin (50 mg·L-1) was achieved in a mineral salt medium within 7 d. Kinetics analysis revealed that its half-life was reduced by 61.2 d, in comparison with the uninoculated control. Eight intermediate metabolites were detected in the biodegradation pathway of D-cyphenothrin including cis-D-cyphenothrin, trans-D-cyphenothrin, 3-phenoxybenzaldehyde, α-hydroxy-3-phenoxy-benzeneacetonitrile, trans-2,2-dimethyl-3-propenyl-cyclopropanol, 2,2-dimethyl-3-propenyl-cyclopropionic acid, trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, and 1,2-benzenedicarboxylic acid, dipropyl ester. This is the first report about the degradation of D-cyphenothrin through cleavage of carboxylester linkage and diaryl bond. In addition to degradation of D-cyphenothrin, strain HLJ-10 effectively degraded a wide range of synthetic pyrethroids including permethrin, tetramethrin, bifenthrin, allethrin, and chlorempenthrin, which are also widely used insecticides with environmental contamination problems. Bioaugmentation of D-cyphenothrin-contaminated soils with strain HLJ-10 substantially enhanced its degradation and over 72% of D-phenothrin was removed from soils within 40 d. These findings unveil the biochemical basis of a highly efficient D-cyphenothrin-degrading bacterial isolate and provide potent agents for eliminating environmental residues of pyrethroids.


Isolation and Identification of D-Cyphenothrin-Degrading Bacterial Isolates
Pesticide activated sludge was collected from a farmland in Harbin, Heilongjiang Province, China. Five g of soil sample was added to a 250 mL Erlenmeyer flask containing 50 mL of sterilized MSM medium. Bacterial culture was enriched by adding D-cyphenothrin stock in the flask to make a final concentration of 50 mg·L −1 . Flask was incubated at 30 • C and 200 rpm in a rotary shaker. After 7 d, 5 mL culture was transferred into a new flask containing 50 mL fresh MSM medium at a concentration of 100 mg·L −1 . The same method was continuously repeated to prepare enrichment culture concentrations of 200, 400, and 800 mg·L −1 , respectively. Final enrichment culture (800 mg·L −1 ) was serially diluted and spread on MSM plates (1.5% agar) containing D-cyphenothrin (50 mg·L −1 ). Plates were incubated at 30 • C for 3 d to isolate individual colonies. Individual colonies were selected and purified by re-streaking three times, and preserved with 15% glycerol at −80 • C. D-cyphenothrin degradation potential of the isolate was determined by high-performance liquid chromatography (HPLC) (Waters, Milford, MA, USA).
Bacterial strain HLJ-10 was identified and characterized by morphology, physio-biochemical characteristics, and genetic analysis of 16S rDNA gene sequence. After two days of incubation at 30 • C and 200 rpm, morphological characteristic of strain HLJ-10 (size, color, surface, edge, and texture) were studied under light microscope (Olympus, Tokyo, Japan) and scanning electron microscope (XL-30 ESEM, Philips Optoelectronics Co., Ltd., Holland) [34]. Physio-biochemical assays were conducted with reference to previous literature [35]. The 16S rRNA gene was PCR-amplified with universal set of primer pairs (forward primer: 5 -TGACGAGTGGCGGACGGGTG-3 and reverse primer: 5 -CCATGGTGTGACGGGCGGTGTG-3 ) purchased from Genewiz, NJ, USA. The resulting sequence of PCR product (1136 bp) was compared in Basic Local Alignment Search Tool (BLAST) of National Center for Biotechnology Information (NCBI). Multiple alignment of 16S rRNA were performed in DNAMAN (version 6.0, LynnonBiosoft, San Ramon, CA, USA) and phylogenetic tree was constructed in MEGA 7.0 (Pennsylvania State University, University Park, PA, USA) by following the neighbor-joining method according to Tamura et al. [36].

Optimization of Conditions for D-Cyphenothrin Degradation
Stored culture (−80 • C) of strain HLJ-10 was thawed and activated by streaking on LB agar plates. Two days later, single colonies were inoculated into LB liquid medium for 24 h. After adjusting the OD (optical density) to 0.8, 1 mL of bacterial broth was taken in a 2 mL centrifuge tube and centrifuged (4000× g, 4 min) to collect the cells. The cells were washed twice with sterile normal saline and re-suspended. Re-suspended broth was transferred to 50 mL MSM medium containing D-cyphenothrin (50 mg·L −1 ) and incubated in the dark at 30 • C and 200 rpm. The experiment was set up in triplicate and uninoculated flasks served as controls. The growth OD of strain HLJ-10 was monitored with UV/visible spectrophotometer (Shimadzu UV-2410, Shimadzu, Japan) at 600 nm and residual amount of D-cyphenothrin was determined by HPLC.
Response surface methodology (RSM) designed by Box-Behnken was used to optimize the crucial factors and interactive influences of strain HLJ-10 degradation activity. According to the preliminary one-factor-at-a-time experiment results, three main factors (temperature, pH, and inoculum size) were selected as independent variables to achieve optimal conditions for D-cyphenothrin degradation. Range and center values of the three independent variables are shown in Table 1. Degradation of 50 mg·L −1 D-cyphenothrin in MSM after 7 d was considered as the dependent variable. Box-Behnken design with three-variables consisting of 17 experimental runs in triplicate at the midpoint was generated by Design Expert version 12.0 (Stat-Ease, MN, USA). Randomized block design was followed Microorganisms 2020, 8, 473 4 of 17 and experimental data were subjected to regression analysis. The data were analyzed by response surface regression program and fitted to the following quadratic polynomial equation: where Y i is the predicted response, X i and X j are variables, b 0 is the constant, b i is the linear coefficient, b ij is the interaction coefficient, and b ii is the quadratic coefficient. To confirm the effect of strain HLJ-10 on D-cyphenothrin degradation, a first-order kinetic model was followed to describe the biodegradation process: where C 0 is the initial concentration of D-cyphenothrin (mg·L −1 ), C t is the content of D-cyphenothrin at time t, k is the degradation constant (day −1 ), and t is the degradation time (days).
Equation (3) was used to calculate the theoretical half-life (t 1/2 ) of D-cyphenothrin: where ln (2) is the natural logarithm of 2 and k is the degradation constant.

Substrate Range of Strain HLJ-10 and Concentration Range of D-Cyphenothrin
The degradation potential of strain HLJ-10 was studied against various SPs (permethrin, bifenthrin, tetramethrin, allethrin, and chlorempenthrin) and different concentrations of D-cyphenothrin. Various SPs were added to the 50 mL of MSM medium at a final concentration of 50 mg·L −1 , respectively. D-cyphenothrin was added to the 50 mL MSM medium to make a final concentration of 25, 50, 100, 200, 400, and 800 mg·L −1 , respectively. The experiments were performed in triplicate with uninoculated flasks as controls. After 7 d of shaking in dark at 30 • C and 200 rpm, the samples were extracted and analyzed by HPLC.

Identification of Intermediate Metabolites of D-Cyphenothrin
To study the metabolic pathway of strain HLJ-10 during D-cyphenothrin degradation, samples were collected from MSM on day 1, 3, 5, and 7, respectively. Metabolites were detected by gas chromatography-mass spectrometry (GC/MS) (Agilent 6890N/5975, Santa Clara, CA, USA) and results were matched with standard compounds in the National Institute of Standards and Technology (NIST) library database.

Biodegradation of D-Cyphenothrin in Soils
To analyze the effect of strain HLJ-10 in soil, an experiment with sterile and nonsterile soil was planned. Soil samples for this experiment were collected from the top 5-20 cm layer of a field located in South China Agricultural University, Guangdong Province, China where D-cyphenothrin had never been applied. Physicochemical parameters for the soil were characterized as (g/kg of dry weight): organic matter, 10.5; total N, 0.5; total P, 0.4; total K, 18.2; and pH, 6.9. Soil consisted of sand, 65.0%; silt, 28.0%; and clay, 7.0%. Soil samples were naturally air dried indoors and sieved (2 mm) for bioremediation studies [18].
Soil was autoclaved at 121 • C for 1 h to completely remove indigenous microbial communities. Then, 250 g sterile and nonsterile soil samples were placed in a 500 mL Erlenmeyer flask, respectively. D-cyphenothrin solution was added to a final concentration of 50 mg·kg −1 in each flask. Soil moisture content was adjusted to 40%-50% with sterile deionized water. Approximately 6.0 × 10 8 CFU·mL −1 bacterial cell suspension was inoculated to sterile and nonsterile soils, respectively, whereas uninoculated samples served as the control. After complete mixing, soil remediation experiments were carried out in the dark at 30 • C. Then, 10 g soil samples were collected on 5th, 10th, 15th, 25th, and 40th day for extraction.

Extraction method of D-Cyphenothrin
To extract D-cyphenothrin from MSM medium, a 50 mL centrifuge tube was used instead of the traditional separatory funnel. Then, 10 mL of the collected sample was added to a 50 mL centrifuge tube and 10 mL acetone was added. Tubes were vortexed for 10 s followed by ultrasonication for 20 min. Then, 15 mL ethyl acetate was added to the tube and vortexed for 1 min. Tubes were kept at room temperature until the aqueous and organic phases were clearly layered. Upper organic phase was transferred to a new 50 mL centrifuge tube, 15 mL ethyl acetate was re-added, and the same procedure was repeated. Organic phases were combined in the new tube and original tubes were discarded. About 10 g of anhydrous sodium sulfate was added to the tube containing organic phase, vortexed for 30 s, and kept for 20 min. Subsequently, the organic phase was transferred to a 100 mL flat-bottom flask and dried by vacuum evaporation. D-cyphenothrin residues and metabolites were recovered by chromatographic acetonitrile. Recovered samples were further collected by using 1 mL injector and 0.22 µm filter membrane and stored in brown bottles at 4 • C before HPLC detection.

Analytical Methods
D-cyphenothrin was quantified with Waters 2690 HPLC system equipped with a Phenomenex C 18 reverse phase column (250 nm × 4.60 mm, 5 µm) and UV detector. Mobile phase was composed of acetonitrile and deionized water (75:25) at a flow rate of 1.0 mL·min −1 . Injection volume and detection wavelength were 10 µL and 253 nm, respectively. Retention times of D-cyphenothrin, permethrin, bifenthrin, tetramethrin, allethrin, and chlorempenthrin remained as 8.97, 14.04, 20.99, 6.78, 7.22, and 10.78 min, respectively. D-cyphenothrin metabolites were identified in Agilent 6890N/5975 GC/MS system equipped with auto-sampler, an on-column, split/splitless capillary injection system, and HP-5MS capillary column (30.0 m × 250 µm × 0.25 µm) with array detector. Helium was used as carrier gas at a flow rate of 1.5 mL·min −1 . Analytical mode was scanned from 30-500 nm. The column temperature was first held at 90 • C for 2 min, raised at 6 • C·min −1 to 150 • C for 1 min, 10 • C·min −1 to 180 • C for 4 min, and finally 20 • C·min −1 to keep at 260 • C for 10 min. Temperatures corresponding to transfer line and ion source were 280 and 230 • C, respectively. The column outlet was directly inserted into electron ionization source block at 70 eV. The injection volume was 1.0 µL with splitless sampling at 250 • C [37].

Isolation and Characterization of Strain HLJ-10
Activated sludge collected from Harbin, Heilongjiang Province, had a large number of isolates with various characteristics. Isolates were obtained in MSM agar plates containing 50 mg·L −1 D-cyphenothrin. One of the isolates utilized D-cyphenothrin as a carbon and energy source to grow and was designated as HLJ-10. Gram staining characterized this isolate as Gram-positive strain. Scanning electron microscope (SEM) revealed that strain HLJ-10 was nearly ball-shaped having a diameter of approximately 0.7-1 µm. Strain HLJ-10 colonies appeared light yellow, smooth, moist, opaque, and with irregular edges, on LB plates. Detailed appearance and scanning electron micrograph of the strain HLJ-10 are shown in Figure S1. The optimum degradation temperature and pH were found to be about 32 • C and 8.0 respectively, and could grow with NaCl (up to 15%) in LB broth. Strain HLJ-10 exhibited significant degradation potential in the pH range of 5-11 but failed to grow at pH 3. Physiological and biochemical tests showed positive results in Gram-staining, starch hydrolysis, gelatin liquefaction, and urease tests, whereas negative results were noted in esculin hydrolysis, sorbierite, and raffinose (Table S1). Turbid growth was observed in LB broth medium after 24 h of incubation in shaker at 30 • C and 200 rpm.
Phylogenetic analysis of 16 S rDNA gene sequence indicated that strain HLJ-10 belongs to the genus Staphylococcus and shares high similarity with S. succinus subsp. AMG-D1 (GenBank accession number NR028667) (Figure 1). Partial 16S rDNA gene sequence of strain HLJ-10 was submitted to the GenBank under the accession number MN396450. Based on the 16S rRNA analysis and morphology, the strain HLJ-10 was identified as Staphylococcus succinus. S. succinus is a widespread bacterium in various natural habitats and possesses catabolic capabilities. Several potent microbial genera have been reported for SPs biodegradation including Micrococcus, Ochrobactrum, Raoultella, Klebsiella, Brevibacterium, Candida, Bacillus, and Pseudomonas [19,[38][39][40][41]. However, degradation of xenobiotic compounds by genus Staphylococcus has not received the attention it deserves and this study for the first time presented SPs degradation by S. succinus. approximately 0.7-1 μm. Strain HLJ-10 colonies appeared light yellow, smooth, moist, opaque, and with irregular edges, on LB plates. Detailed appearance and scanning electron micrograph of the strain HLJ-10 are shown in Figure S1. The optimum degradation temperature and pH were found to be about 32 °C and 8.0 respectively, and could grow with NaCl (up to 15%) in LB broth. Strain HLJ-10 exhibited significant degradation potential in the pH range of 5-11 but failed to grow at pH 3. Physiological and biochemical tests showed positive results in Gram-staining, starch hydrolysis, gelatin liquefaction, and urease tests, whereas negative results were noted in esculin hydrolysis, sorbierite, and raffinose (Table S1). Turbid growth was observed in LB broth medium after 24 h of incubation in shaker at 30 °C and 200 rpm. Phylogenetic analysis of 16 S rDNA gene sequence indicated that strain HLJ-10 belongs to the genus Staphylococcus and shares high similarity with S. succinus subsp. AMG-D1 (GenBank accession number NR028667) (Figure 1). Partial 16S rDNA gene sequence of strain HLJ-10 was submitted to the GenBank under the accession number MN396450. Based on the 16S rRNA analysis and morphology, the strain HLJ-10 was identified as Staphylococcus succinus. S. succinus is a widespread bacterium in various natural habitats and possesses catabolic capabilities. Several potent microbial genera have been reported for SPs biodegradation including Micrococcus, Ochrobactrum, Raoultella, Klebsiella, Brevibacterium, Candida, Bacillus, and Pseudomonas [19,[38][39][40][41]. However, degradation of xenobiotic compounds by genus Staphylococcus has not received the attention it deserves and this study for the first time presented SPs degradation by S. succinus.

Growth of Isolate and Kinetic Analysis of Degradation Process
Degradation kinetics of D-cyphenothrin and growth of strain HLJ-10 were simultaneously investigated in MSM medium with 50 mg·L −1 D-cyphenothrin. As shown in Figure 2, there was no lag phase during the growth of strain HLJ-10, indicating that it effectively utilized D-cyphenothrin as a growth substance by degrading 75.8% in 72 h. D-cyphenothrin degradation was correlated with bacterial cell density and biodegradation of D-cyphenothrin rapidly increased during exponential phase (72 h), whereas it slowed down in stationary phase. Approximately 92.8% of D-cyphentorhrin was degraded on the 7th day in the dark. HPLC analysis of D-cyphenothrin degradation by strain HLJ-10 over time is shown in Figure S2. At the same time, no significant change in D-cyphenothrin concentration was observed in the control flasks without bacterial inoculum.

Growth of Isolate and Kinetic Analysis of Degradation Process
Degradation kinetics of D-cyphenothrin and growth of strain HLJ-10 were simultaneously investigated in MSM medium with 50 mg·L −1 D-cyphenothrin. As shown in Figure 2, there was no lag phase during the growth of strain HLJ-10, indicating that it effectively utilized D-cyphenothrin as a growth substance by degrading 75.8% in 72 h. D-cyphenothrin degradation was correlated with bacterial cell density and biodegradation of D-cyphenothrin rapidly increased during exponential phase (72 h), whereas it slowed down in stationary phase. Approximately 92.8% of D-cyphentorhrin was degraded on the 7th day in the dark. HPLC analysis of D-cyphenothrin degradation by strain HLJ-10 over time is shown in Figure S2. At the same time, no significant change in D-cyphenothrin concentration was observed in the control flasks without bacterial inoculum. Kinetic parameters of D-cyphenothrin degradation by strain HLJ-10 are shown in Table 2, which reveal that the degradation process of D-cyphenothrin followed a first-order kinetic model (Equation (2)). Degradation constant (k) of strain HLJ-10 and control were noted as 0.3896 and 0.011, respectively. Theoretical t1/2 value of the treatments with strain HLJ-10 and controls were calculated by Equation (3). Determination coefficients (R 2 ) of strain HLJ-10 and control were found as 0.9659 and 0.983, respectively, indicating that degradation data were well fitted with first-order kinetic model. The t1/2 of the D-cyphenothrin degradation by strain HLJ-10 was determined as 1.8 d, which is significantly shorter than 63.0 d of control. These results further illustrated efficiency of strain HLJ-10 in D-cyphenothrin degradation. Note: k refers to degradation constant (day −1 ); t1/2 refers to half-time (days); R 2 refers to determination coefficient.
To date, there are only few reports about microbial degradation of D-cyphenothrin. Suzuki et al. recently reported the metabolic behavior of D-cyphenothrin in aqueous environments but Dcyphenothrin-degrading microorganisms were not specified [31]. It is noteworthy that most of pyrethroid-degrading microbes isolated could not grow in the absence of extra carbon sources [42]. Strain HLJ-10 directly utilized D-cyphenothrin as the sole carbon and energy source for its growth that exhibited its promising potential for the bioremediation of pyrethroid-contaminated environments.

Optimization of D-Cyphenothrin Degradation Conditions
Experimental design variables corresponding to D-cyphenothrin degradation are presented in Table 3. Data were analyzed by response surface regression in Design Expert 12.0. Experimental Kinetic parameters of D-cyphenothrin degradation by strain HLJ-10 are shown in Table 2, which reveal that the degradation process of D-cyphenothrin followed a first-order kinetic model (Equation (2)). Degradation constant (k) of strain HLJ-10 and control were noted as 0.3896 and 0.011, respectively. Theoretical t 1/2 value of the treatments with strain HLJ-10 and controls were calculated by Equation (3). Determination coefficients (R 2 ) of strain HLJ-10 and control were found as 0.9659 and 0.983, respectively, indicating that degradation data were well fitted with first-order kinetic model. The t 1/2 of the D-cyphenothrin degradation by strain HLJ-10 was determined as 1.8 d, which is significantly shorter than 63.0 d of control. These results further illustrated efficiency of strain HLJ-10 in D-cyphenothrin degradation. Table 2. Kinetic parameters of D-cyphenothrin degradation with Staphylococcus succinus HLJ-10 in mineral salt medium (MSM).

Treatments
Regression Equation Note: k refers to degradation constant (day −1 ); t 1/2 refers to half-time (days); R 2 refers to determination coefficient.
To date, there are only few reports about microbial degradation of D-cyphenothrin. Suzuki et al. recently reported the metabolic behavior of D-cyphenothrin in aqueous environments but D-cyphenothrin-degrading microorganisms were not specified [31]. It is noteworthy that most of pyrethroid-degrading microbes isolated could not grow in the absence of extra carbon sources [42]. Strain HLJ-10 directly utilized D-cyphenothrin as the sole carbon and energy source for its growth that exhibited its promising potential for the bioremediation of pyrethroid-contaminated environments.

Optimization of D-Cyphenothrin Degradation Conditions
Experimental design variables corresponding to D-cyphenothrin degradation are presented in Table 3. Data were analyzed by response surface regression in Design Expert 12.0. Experimental values of D-cyphenothrin residues were fitted to the following quadratic polynomial model equations (Equation (4): Table 3. Box-Behnken experimental design matrix and response of dependent variable for D-cyphenothrin degradation.
Note: X 1 = Temperature; X 2 = pH; X 3 = Inoculum size; Y 1 = Degradation (%). Table 4 presents analysis of variance (ANOVA) to fit a quadratic polynomial model. Significant p value (0.0277) of the model term indicates that the equation reliably predicted D-cyphenothrin degradation. A low coefficient of variation (CV = 5.41%) also suggested that the model is accurate and reliable. Results of regression analysis revealed that linear and square terms of temperature (X 1 ) and pH (X 2 ) had significant (p < 0.05) effect on D-cyphenothrin degradation by strain HLJ-10, whereas the linear term of inoculum size (X 3 ) and interaction terms were insignificant (p > 0.05). These results were similar to the previous report of Chen et al. [37], who degraded cypermethrin by a co-culture of Bacillus cereus ZH-3 and Streptomyces aureus HP-S-01.
The inoculum size was fixed at OD 0.8 (6.98 × 10 8 CFU/mL) and a three-dimensional response surface was drawn to visually present the effect of temperature and pH on D-cyphenothrin degradation by strain HLJ-10. As shown in Figure 3, the plot of D-cyphenothrin degradation had a maximum theoretical value of 90.7% at a stationary point, whereas optimal levels of three variables X 1 , X 2 , and X 3 were noted as 2.3, 1.9, and −0.06 at coded levels. The optimum temperature, pH, and inoculum size at the unencoded levels were found as 31.6 • C, 7.9, and 6.05 × 10 8 CFU·mL −1 , respectively. Strain HLJ-10 was capable of rapidly degrading D-cyphenothrin without a lag phase over a wide range of temperature (25-35 • C) and pH (5)(6)(7)(8)(9). This is a very important feature of an organism for bioremediation of variable environments [30]. Results demonstrated that degradation tends to occur under alkaline conditions which is consistent with SPs characteristic of easy hydrolyzation under alkaline conditions [43]. On the other side, acidity attenuated the activity of S. succinus HLJ-10, which resulted in decreased D-cyphenothrin degradation.

Degradation Products and Degradation Pathway of D-Cyphenothrin
The degradation pathway of D-cyphenothrin by strain HLJ-10 was performed through GC/MS. Two significant peaks were detected at retention times of 27.975 and 28.050 min, showing a characteristic mass fragment [M + ] at m/z 375 with same major fragment ions at m/z 123 and were confirmed as two isomers of the same compound. The compound was designated as compound A having isomers 1 and 2. These two isomers of compound A were further characterized as cis-Dcyphenothrin and trans-D-cyphenothrin according to the fragment retention time (RT) and the similarity of molecular ions to corresponding authentic compounds in the National Institute of Standards and Technology (NIST, USA) library database. As the concentration of D-cyphenothrin was decreased, six new compounds B, C, D, E, F, and G were detected. Chemical structures, RTs, and characteristic ions of the mass spectra (m/z) are listed in Table 5

Degradation Products and Degradation Pathway of D-Cyphenothrin
The degradation pathway of D-cyphenothrin by strain HLJ-10 was performed through GC/MS. Two significant peaks were detected at retention times of 27.975 and 28.050 min, showing a characteristic mass fragment [M + ] at m/z 375 with same major fragment ions at m/z 123 and were confirmed as two isomers of the same compound. The compound was designated as compound A having isomers 1 and 2. These two isomers of compound A were further characterized as cis-D-cyphenothrin and trans-D-cyphenothrin according to the fragment retention time (RT) and the similarity of molecular ions to corresponding authentic compounds in the National Institute of Standards and Technology (NIST, USA) library database. As the concentration of D-cyphenothrin was decreased, six new compounds B, C, D, E, F, and G were detected. Chemical structures, RTs, and characteristic ions of the mass spectra (m/z) are listed in Table 5. RTs of compounds B, C, D, E, F, and G were noted as 23.16, 23.14, 23.39, 16.81, 16.76, and 26.63 min, respectively. Based on the similarity of fragment RTs and molecular ions to those of corresponding authentic compounds in the NIST library database, compounds B, C, D, E, F, and G were identified as trans-2,2-dimethyl-3-propenyl-cyclopropanol, 2,2-dimethyl-3-propenyl-cyclopropionic acid, trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, α-hydroxy-3-phenoxy-benzeneacetonitrile, 3-phenoxybenzaldehyde, and 1,2-benzenedicarboxylic acid and dipropyl ester, respectively ( Figure S3). Mass spectrum of the matched D-cyphenothrin metabolites in the NIST library database are shown in Figure S4.

Degradation Products and Degradation Pathway of D-Cyphenothrin
The degradation pathway of D-cyphenothrin by strain HLJ-10 was performed through GC/MS. Two significant peaks were detected at retention times of 27.975 and 28.050 min, showing a characteristic mass fragment [M + ] at m/z 375 with same major fragment ions at m/z 123 and were confirmed as two isomers of the same compound. The compound was designated as compound A having isomers 1 and 2. These two isomers of compound A were further characterized as cis-Dcyphenothrin and trans-D-cyphenothrin according to the fragment retention time (RT) and the similarity of molecular ions to corresponding authentic compounds in the National Institute of Standards and Technology (NIST, USA) library database. As the concentration of D-cyphenothrin was decreased, six new compounds B, C, D, E, F, and G were detected. Chemical structures, RTs, and characteristic ions of the mass spectra (m/z) are listed in Table 5. RTs of compounds B, C, D, E, F, and G were noted as 23.16, 23.14, 23.39, 16.81, 16.76, and 26.63 min, respectively. Based on the similarity of fragment RTs and molecular ions to those of corresponding authentic compounds in the NIST library database, compounds B, C, D, E, F, and G were identified as trans-2,2-dimethyl-3-propenylcyclopropanol, 2,2-dimethyl-3-propenyl-cyclopropionic acid, trans-2,2-dimethyl-3-propenylcyclopropionaldehyde, α-hydroxy-3-phenoxy-benzeneacetonitrile, 3-phenoxybenzaldehyde, and 1,2-benzenedicarboxylic acid and dipropyl ester, respectively ( Figure S3). Mass spectrum of the matched D-cyphenothrin metabolites in the NIST library database are shown in Figure S4. Based on the GC/MS results, the microbial degradation pathway of D-cyphenothrin was first time proposed (Figure 4). D-cyphenothrin was first hydrolyzed by the cleavage of carboxylester linkage to yield α-hydroxy-3-phenoxy-benzeneacetonitrile and trans-2,2-dimethyl-3-propenylcyclopropanol. Intermediate product α-hydroxy-3-phenoxy-benzeneacetonitrile was unstable in the environment and spontaneously converted to 3-phenoxybenzaldehyde. Subsequently, 3phenoxybenzaldehyde was further degraded through diaryl cleavage to form 1,2benzenedicarboxylic acid and dipropyl ester. Meanwhile, trans-2,2-dimethyl-3-propenylcyclopropanol was oxidized to form trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, which was transient and further oxidized to 2,2-dimethyl-3-propenyl-cyclopropionic acid. At the end of experiment, all these metabolites faded away without any non-cleavable metabolites. In the noninoculated controls with the same quantity of D-cyphenothrin, only D-cyphenothrin was detected after 7 d. Based on the GC/MS results, the microbial degradation pathway of D-cyphenothrin was first time proposed (Figure 4). D-cyphenothrin was first hydrolyzed by the cleavage of carboxylester linkage to yield α-hydroxy-3-phenoxy-benzeneacetonitrile and trans-2,2-dimethyl-3-propenylcyclopropanol. Intermediate product α-hydroxy-3-phenoxy-benzeneacetonitrile was unstable in the environment and spontaneously converted to 3-phenoxybenzaldehyde. Subsequently, 3phenoxybenzaldehyde was further degraded through diaryl cleavage to form 1,2benzenedicarboxylic acid and dipropyl ester. Meanwhile, trans-2,2-dimethyl-3-propenylcyclopropanol was oxidized to form trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, which was transient and further oxidized to 2,2-dimethyl-3-propenyl-cyclopropionic acid. At the end of experiment, all these metabolites faded away without any non-cleavable metabolites. In the noninoculated controls with the same quantity of D-cyphenothrin, only D-cyphenothrin was detected after 7 d. Based on the GC/MS results, the microbial degradation pathway of D-cyphenothrin was first time proposed (Figure 4). D-cyphenothrin was first hydrolyzed by the cleavage of carboxylester linkage to yield α-hydroxy-3-phenoxy-benzeneacetonitrile and trans-2,2-dimethyl-3-propenylcyclopropanol. Intermediate product α-hydroxy-3-phenoxy-benzeneacetonitrile was unstable in the environment and spontaneously converted to 3-phenoxybenzaldehyde. Subsequently, 3phenoxybenzaldehyde was further degraded through diaryl cleavage to form 1,2benzenedicarboxylic acid and dipropyl ester. Meanwhile, trans-2,2-dimethyl-3-propenylcyclopropanol was oxidized to form trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, which was transient and further oxidized to 2,2-dimethyl-3-propenyl-cyclopropionic acid. At the end of experiment, all these metabolites faded away without any non-cleavable metabolites. In the noninoculated controls with the same quantity of D-cyphenothrin, only D-cyphenothrin was detected after 7 d. Based on the GC/MS results, the microbial degradation pathway of D-cyphenothrin was first time proposed (Figure 4). D-cyphenothrin was first hydrolyzed by the cleavage of carboxylester linkage to yield α-hydroxy-3-phenoxy-benzeneacetonitrile and trans-2,2-dimethyl-3-propenylcyclopropanol. Intermediate product α-hydroxy-3-phenoxy-benzeneacetonitrile was unstable in the environment and spontaneously converted to 3-phenoxybenzaldehyde. Subsequently, 3phenoxybenzaldehyde was further degraded through diaryl cleavage to form 1,2benzenedicarboxylic acid and dipropyl ester. Meanwhile, trans-2,2-dimethyl-3-propenylcyclopropanol was oxidized to form trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, which was transient and further oxidized to 2,2-dimethyl-3-propenyl-cyclopropionic acid. At the end of experiment, all these metabolites faded away without any non-cleavable metabolites. In the noninoculated controls with the same quantity of D-cyphenothrin, only D-cyphenothrin was detected after 7 d. Based on the GC/MS results, the microbial degradation pathway of D-cyphenothrin was first time proposed (Figure 4). D-cyphenothrin was first hydrolyzed by the cleavage of carboxylester linkage to yield α-hydroxy-3-phenoxy-benzeneacetonitrile and trans-2,2-dimethyl-3-propenylcyclopropanol. Intermediate product α-hydroxy-3-phenoxy-benzeneacetonitrile was unstable in the environment and spontaneously converted to 3-phenoxybenzaldehyde. Subsequently, 3phenoxybenzaldehyde was further degraded through diaryl cleavage to form 1,2benzenedicarboxylic acid and dipropyl ester. Meanwhile, trans-2,2-dimethyl-3-propenylcyclopropanol was oxidized to form trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, which was transient and further oxidized to 2,2-dimethyl-3-propenyl-cyclopropionic acid. At the end of experiment, all these metabolites faded away without any non-cleavable metabolites. In the noninoculated controls with the same quantity of D-cyphenothrin, only D-cyphenothrin was detected after 7 d. Based on the GC/MS results, the microbial degradation pathway of D-cyphenothrin was first time proposed (Figure 4). D-cyphenothrin was first hydrolyzed by the cleavage of carboxylester linkage to yield α-hydroxy-3-phenoxy-benzeneacetonitrile and trans-2,2-dimethyl-3-propenylcyclopropanol. Intermediate product α-hydroxy-3-phenoxy-benzeneacetonitrile was unstable in the environment and spontaneously converted to 3-phenoxybenzaldehyde. Subsequently, 3phenoxybenzaldehyde was further degraded through diaryl cleavage to form 1,2benzenedicarboxylic acid and dipropyl ester. Meanwhile, trans-2,2-dimethyl-3-propenylcyclopropanol was oxidized to form trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, which was transient and further oxidized to 2,2-dimethyl-3-propenyl-cyclopropionic acid. At the end of experiment, all these metabolites faded away without any non-cleavable metabolites. In the noninoculated controls with the same quantity of D-cyphenothrin, only D-cyphenothrin was detected after 7 d. Based on the GC/MS results, the microbial degradation pathway of D-cyphenothrin was first time proposed (Figure 4). D-cyphenothrin was first hydrolyzed by the cleavage of carboxylester linkage to yield α-hydroxy-3-phenoxy-benzeneacetonitrile and trans-2,2-dimethyl-3-propenylcyclopropanol. Intermediate product α-hydroxy-3-phenoxy-benzeneacetonitrile was unstable in the environment and spontaneously converted to 3-phenoxybenzaldehyde. Subsequently, 3phenoxybenzaldehyde was further degraded through diaryl cleavage to form 1,2benzenedicarboxylic acid and dipropyl ester. Meanwhile, trans-2,2-dimethyl-3-propenylcyclopropanol was oxidized to form trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, which was transient and further oxidized to 2,2-dimethyl-3-propenyl-cyclopropionic acid. At the end of experiment, all these metabolites faded away without any non-cleavable metabolites. In the noninoculated controls with the same quantity of D-cyphenothrin, only D-cyphenothrin was detected after 7 d.

1,2-Benzenedicarboxylic acid, dipropyl ester
Based on the GC/MS results, the microbial degradation pathway of D-cyphenothrin was first time proposed (Figure 4). D-cyphenothrin was first hydrolyzed by the cleavage of carboxylester linkage to yield α-hydroxy-3-phenoxy-benzeneacetonitrile and trans-2,2-dimethyl-3-propenyl-cyclopropanol. Intermediate product α-hydroxy-3-phenoxy-benzeneacetonitrile was unstable in the environment and spontaneously converted to 3-phenoxybenzaldehyde. Subsequently, 3-phenoxybenzaldehyde was further degraded through diaryl cleavage to form 1,2-benzenedicarboxylic acid and dipropyl ester. Meanwhile, trans-2,2-dimethyl-3-propenyl-cyclopropanol was oxidized to form trans-2,2-dimethyl-3-propenyl-cyclopropionaldehyde, which was transient and further oxidized to 2,2-dimethyl-3-propenyl-cyclopropionic acid. At the end of experiment, all these metabolites faded away without any non-cleavable metabolites. In the non-inoculated controls with the same quantity of D-cyphenothrin, only D-cyphenothrin was detected after 7 d. Among these compounds, α-hydroxy-3-phenoxy-benzeneacetonitrile and 3phenoxybenzaldehyde have been frequently detected in SPs biodegradation [18,35]. These intermediates were transient with very low concentrations and easily transformed into smaller molecular compounds through oxidation and hydrolysis. Microbial degradation of pyrethroids mainly involves the hydrolysis of ester bonds and oxidation reaction [23]. Carboxylesterase enzyme is produced by the microorganism that specifically cleaves a carboxylate bond [44,45]. This cleavage transforms parent pesticide into the smaller molecular weight compound containing a carboxylic acid or alcohol that further oxidizes and dehydrogenates to yield less toxic or non-toxic compounds [46,47]. It is worth noting that the D-cyphenothrin degradation products are non-toxic to the environment.

Degradation of Various SPs and Different Concentrations of D-Cyphenothrin
In order to study the degradation potential of strain HLJ-10 under different environments, degradation experiments were carried out with different concentrations of D-cyphenothrin ( Figure  5A) and 50 mg·L −1 of various SPs ( Figure 5B). Initial concentrations of D-cyphenothrin were prepared as 25, 50, 100, 200, 400, and 800 mg·L −1 , respectively. The highest degradation (92.8%) was noted at 50 mg·L −1 . Unexpectedly, at 25 mg·L −1 , D-cyphenothrin was not completely degraded and maximum degradation reached 91.8%. Strain HLJ-10 rapidly degraded D-cyphenothrin at concentrations up to 800 mg·L −1 and utilized it as a sole carbon and energy source to grow without any lag period. At a Dcyphenothrin concentration of 800 mg·L −1 , maximum degradation reached 74.6% after 7 d. Previous studies revealed that the degradation activity of pyrethroid-degrading bacterial strains was substantially inhibited at high SPs concentrations [48,49]. This particular strain was found highly effective in degrading D-cyphenothrin up to the concentration as high as 800 mg·L −1 , indicating that strain HLJ-10 may be suitable for the bioremediation of various contaminated environments. Among these compounds, α-hydroxy-3-phenoxy-benzeneacetonitrile and 3-phenoxybenzaldehyde have been frequently detected in SPs biodegradation [18,35]. These intermediates were transient with very low concentrations and easily transformed into smaller molecular compounds through oxidation and hydrolysis. Microbial degradation of pyrethroids mainly involves the hydrolysis of ester bonds and oxidation reaction [23]. Carboxylesterase enzyme is produced by the microorganism that specifically cleaves a carboxylate bond [44,45]. This cleavage transforms parent pesticide into the smaller molecular weight compound containing a carboxylic acid or alcohol that further oxidizes and dehydrogenates to yield less toxic or non-toxic compounds [46,47]. It is worth noting that the D-cyphenothrin degradation products are non-toxic to the environment.

Degradation of Various SPs and Different Concentrations of D-Cyphenothrin
In order to study the degradation potential of strain HLJ-10 under different environments, degradation experiments were carried out with different concentrations of D-cyphenothrin ( Figure 5A) and 50 mg·L −1 of various SPs ( Figure 5B). Initial concentrations of D-cyphenothrin were prepared as 25, 50, 100, 200, 400, and 800 mg·L −1 , respectively. The highest degradation (92.8%) was noted at 50 mg·L −1 . Unexpectedly, at 25 mg·L −1 , D-cyphenothrin was not completely degraded and maximum degradation reached 91.8%. Strain HLJ-10 rapidly degraded D-cyphenothrin at concentrations up to 800 mg·L −1 and utilized it as a sole carbon and energy source to grow without any lag period. At a D-cyphenothrin concentration of 800 mg·L −1 , maximum degradation reached 74.6% after 7 d. Previous studies revealed that the degradation activity of pyrethroid-degrading bacterial strains was substantially inhibited at high SPs concentrations [48,49]. This particular strain was found highly effective in degrading D-cyphenothrin up to the concentration as high as 800 mg·L −1 , indicating that strain HLJ-10 may be suitable for the bioremediation of various contaminated environments. Generally, multiple SPs are used in rotation instead of repeating a single pyrethroid for a longer time. Therefore, residues of various SPs are found in terrestrial and aquatic environments [50,51]. Different SPs including tetramethrin, permethrin, bifenthrin, allethrin, and chlorempenthrin were separately added to the MSM medium at a final concentration of 50 mg·L −1 . Degradation of permethrin was found to be the highest (80.8%), followed by tetramethrin (62.5%). The lowest degradation occurred in allethrin and chlorempenthrin as 37.5% and 36.5%, respectively. Usually, the degraders only transform a single xenobiotic compound due to certain structural requirements [40]. Strain HLJ-10 was able to degrade a wide range of SPs, suggesting that the isolate possesses promising potential and advantages in removing pyrethroid residues from various environments.

Biodegradation of D-Cyphenothrin in Soils
Soil remediation experiments were carried out under sterile and nonsterile conditions, whereas non-inoculated treatment served as the control ( Figure 6). After bioremediation with strain HLJ-10, approximately 77.2% and 72.8% of the initially added D-cyphenothrin was eliminated in nonsterile and sterile soils, respectively, within 40 d. Degradation parameters were characterized as k values of 0.0323 and 0.0283 day −1 and t1/2 values of 21.5 and 24.5 d, respectively. Specific kinetic parameters are shown in Table 6. In addition, no significant lag phase was observed during the experiment. In the controls with indigenous microbiota, 52.5% of D-cyphenothrin was removed, which is slightly higher than sterilized control (48.2%) and t1/2 values were noted as 46.2 and 55.5 d, respectively, indicating that indigenous microbiota play a role in the bioaugmentation of pyrethroid-contaminated sites. Similar results were observed by Zhan et al. [35]. Nonsterile soil contains natural microbial communities, which led to a higher degradation rate. Generally, multiple SPs are used in rotation instead of repeating a single pyrethroid for a longer time. Therefore, residues of various SPs are found in terrestrial and aquatic environments [50,51]. Different SPs including tetramethrin, permethrin, bifenthrin, allethrin, and chlorempenthrin were separately added to the MSM medium at a final concentration of 50 mg·L −1 . Degradation of permethrin was found to be the highest (80.8%), followed by tetramethrin (62.5%). The lowest degradation occurred in allethrin and chlorempenthrin as 37.5% and 36.5%, respectively. Usually, the degraders only transform a single xenobiotic compound due to certain structural requirements [40]. Strain HLJ-10 was able to degrade a wide range of SPs, suggesting that the isolate possesses promising potential and advantages in removing pyrethroid residues from various environments.

Biodegradation of D-Cyphenothrin in Soils
Soil remediation experiments were carried out under sterile and nonsterile conditions, whereas non-inoculated treatment served as the control ( Figure 6). After bioremediation with strain HLJ-10, approximately 77.2% and 72.8% of the initially added D-cyphenothrin was eliminated in nonsterile and sterile soils, respectively, within 40 d. Degradation parameters were characterized as k values of 0.0323 and 0.0283 day −1 and t 1/2 values of 21.5 and 24.5 d, respectively. Specific kinetic parameters are shown in Table 6. In addition, no significant lag phase was observed during the experiment. In the controls with indigenous microbiota, 52.5% of D-cyphenothrin was removed, which is slightly higher than sterilized control (48.2%) and t 1/2 values were noted as 46.2 and 55.5 d, respectively, indicating that indigenous microbiota play a role in the bioaugmentation of pyrethroid-contaminated sites. Similar results were observed by Zhan et al. [35]. Nonsterile soil contains natural microbial communities, which led to a higher degradation rate. Several pyrethroid-degrading microbes were reported and effectively removed pyrethroids under optimum conditions in liquid media, but few were subjected to soil remediation [33,40,42,52,53]. The degrading microbes isolated from the environment usually fail to degrade xenobiotics when used for bioremediation of contaminated soils; thus, additional treatments are needed to accelerate biodegradation [23,43,54]. In this work, bioaugmentation of D-cyphenothrincontaminated soils with strain HLJ-10 substantially enhanced the disappearance rate of Dcyphenothrin, and its t1/2 was reduced by 31.0 and 24.7 d in sterile and nonsterile soils, respectively, in comparison with soils without the strain HLJ-10. Unlike most bacterial isolates, strain HLJ-10 has an exceptional ability to adapt and thrive in different ecological niches, which makes it a potent strain for various applications. However, it is worth noting that the strain HLJ-10 exhibited a significant reduction in the ability to remediate soil compared with the liquid medium experiment. Microorganisms in the soil are more likely to be affected by factors such as pH, soil water content, organic matter content, soil porosity, heavy metals, and other organic contaminants than by liquid media [46,[55][56][57]. To improve the ability of strain HLJ-10 to remediate in soil, these issues should be fully considered.

Conclusions
In this study, we identified a novel bacterial isolate S. succinus HLJ-10 having superb Dcyphenothrin degradation activity. Strain HLJ-10 utilized D-cyphenothrin as the sole carbon source  Several pyrethroid-degrading microbes were reported and effectively removed pyrethroids under optimum conditions in liquid media, but few were subjected to soil remediation [33,40,42,52,53]. The degrading microbes isolated from the environment usually fail to degrade xenobiotics when used for bioremediation of contaminated soils; thus, additional treatments are needed to accelerate biodegradation [23,43,54]. In this work, bioaugmentation of D-cyphenothrin-contaminated soils with strain HLJ-10 substantially enhanced the disappearance rate of D-cyphenothrin, and its t 1/2 was reduced by 31.0 and 24.7 d in sterile and nonsterile soils, respectively, in comparison with soils without the strain HLJ-10. Unlike most bacterial isolates, strain HLJ-10 has an exceptional ability to adapt and thrive in different ecological niches, which makes it a potent strain for various applications.
However, it is worth noting that the strain HLJ-10 exhibited a significant reduction in the ability to remediate soil compared with the liquid medium experiment. Microorganisms in the soil are more likely to be affected by factors such as pH, soil water content, organic matter content, soil porosity, heavy metals, and other organic contaminants than by liquid media [46,[55][56][57]. To improve the ability of strain HLJ-10 to remediate in soil, these issues should be fully considered.

Conclusions
In this study, we identified a novel bacterial isolate S. succinus HLJ-10 having superb D-cyphenothrin degradation activity. Strain HLJ-10 utilized D-cyphenothrin as the sole carbon source for its growth over a wide range of temperature (25-35 • C) and pH (5)(6)(7)(8)(9), indicating that the strain has excellent working ability in adverse environments. This study proves that the bacterium harbors the metabolic pathway for complete detoxification and metabolism of D-cyphenothrin. This is the first report of the D-cyphenothrin degradation pathway that is of vital importance in the D-cyphenothrin biogeocycle. Further, this particular strain exhibited great advantages in bioremediation of D-cyphenothrin-contaminated soils because of its adaptability in different environments. Furthermore, this strain was capable of degrading a wide range of SPs, suggesting that strain HLJ-10 is a potent and effective candidate for the bioremediation of pyrethroid-contaminated terrestrial and aquatic environments. However, further studies, such as its interaction with environment, degradation enzymes, and genes that encode for key enzymes, are still needed before the application of this strain in the field-scale bioremediation.