Next Article in Journal
Molecular Characterization of the Chicken Parvovirus Based on VP1 Gene Circulating in Brazilian Chicken Flocks
Previous Article in Journal
Performance of Halo-Alkali-Tolerant Endophytic Bacteria on Hybrid Pennisetum and Bacterial Community under Varying Soil Conditions
Previous Article in Special Issue
Characterization of the 3,4-Dichloroaniline Degradation Gene Cluster in Acinetobacter soli GFJ2
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Microorganisms
Volume 12
Issue 6
10.3390/microorganisms12061063
microorganisms-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Efficient Biodegradation of the Neonicotinoid Insecticide Flonicamid by Pseudaminobacter salicylatoxidans CGMCC 1.17248: Kinetics, Pathways, and Enzyme Properties

by
Yun-Xiu Zhao
1,†,
Jing Yuan
2,†,
Ke-Wei Song
1,
Chi-Jie Yin
1,
Li-Wen Chen
3,
Kun-Yan Yang
3,
Ju Yang
3,* and
Yi-Jun Dai
2,*
1
Jiangsu Key Laboratory for Bioresources of Saline Soils, Jiangsu Synthetic Innovation Center for Coastal Bio-Agriculture, School of Wetlands, Yancheng Teachers University, Yancheng 224007, China
2
Jiangsu Key Laboratory for Microbes and Functional Genomics, Jiangsu Engineering and Technology Research Center for Industrialization of Microbial Resources, College of Life Science, Nanjing Normal University, Nanjing 210023, China
3
College of Marine and Biological Engineering, Yancheng Teachers University, Yancheng 224002, China
*
Authors to whom correspondence should be addressed.
†
These authors contributed equally to this work.
Microorganisms 2024, 12(6), 1063; https://doi.org/10.3390/microorganisms12061063
Submission received: 15 April 2024 / Revised: 21 May 2024 / Accepted: 22 May 2024 / Published: 24 May 2024
(This article belongs to the Special Issue Microbial Biocatalysis and Biodegradation 2.0)
Browse Figures
Versions Notes

Abstract

:
Nitrile-containing insecticides can be converted into their amide derivatives by Pseudaminobacter salicylatoxidans. N-(4-trifluoromethylnicotinoyl) glycinamide (TFNG-AM) is converted to 4-(trifluoromethyl) nicotinoyl glycine (TFNG) using nitrile hydratase/amidase. However, the amidase that catalyzes this bioconversion has not yet been fully elucidated. In this study, it was discovered that flonicamid (FLO) is degraded by P. salicylatoxidans into the acid metabolite TFNG via the intermediate TFNG-AM. A half-life of 18.7 h was observed for P. salicylatoxidans resting cells, which transformed 82.8% of the available FLO in 48 h. The resulting amide metabolite, TFNG-AM, was almost all converted to TFNG within 19 d. A novel amidase-encoding gene was cloned and overexpressed in Escherichia coli. The enzyme, PmsiA, hydrolyzed TFNG-AM to TFNG. Despite being categorized as a member of the amidase signature enzyme superfamily, PsmiA only shares 20–30% identity with the 14 previously identified members of this family, indicating that PsmiA represents a novel class of enzyme. Homology structural modeling and molecular docking analyses suggested that key residues Glu247 and Met242 may significantly impact the catalytic activity of PsmiA. This study contributes to our understanding of the biodegradation process of nitrile-containing insecticides and the relationship between the structure and function of metabolic enzymes.

1. Introduction

The insecticide flonicamid (N-cyanomethyl-4-trifluoromethylnicotinamide, FLO) is a new systemic insecticide with selective action that is widely used for the treatment of aphids and whiteflies [1]. In harvested crops (e.g., cabbage, bell peppers, dried hops, cucumbers, and oranges) and water sources, the main metabolites of FLO, N-(4-trifluoromethylnicotinoyl) glycinamide (TFNG-AM), 4-(trifluoromethyl) nicotinoyl glycine (TFNG), and 5-trifluoromethylnicotinic acid (TFNA) have been detected [2,3,4,5]. In addition to this, traces of FLO have been found in human urine and serum samples [6,7]. The mouse genome can be significantly damaged by high doses of FLO [8]. FLO and its metabolites are highly soluble in water and persistent in the environment, which allow them to accumulate in humans [8,9]. Some scholars have attempted photo-oxidation-based remediation methods to address the residues of FLO in the environment. For example, when adding persulfate to test wastewater, the removal effect of FLO is not ideal. Although adding ZnO- and TiO2-coated magnetic particles to the system can significantly improve the degradation rate of FLO, it is not economically feasible [10,11,12]. With the increasing use of FLO and the increasing possibility of accumulation of FLO and its metabolites in the environment, adequate attention is needed.
Microbial remediation is a cost-effective, environmentally friendly technique that may remove residual pesticides or insecticides from soil and water [13,14]. Two degradation pathways—via nitrile hydratase (NHase)/amidase and nitrilase, respectively—are used by microbes to break down FLO [15]. According to our earlier research, the N2-fixing bacteria Variovorax boronicumulans CGMCC 4969, Microvirga flocculans CGMCC 1.16731, Aminobacter sp. CGMCC 1.17253, Ensifer meliloti CGMCC 7333, and E. adhaerens CGMCC 6315 efficiently convert FLO to TFNG-AM using NHases [16,17,18,19,20]. V. boronicumulans CGMCC 4969 and M. flocculans CGMCC 1.16731 hydrolyze TFNG-AM to TFNG using amidases but do not hydrolyze TFNA-AM, another intermediate of FLO. Pseudomonas stutzeri CGMCC 22915 effectively degraded TFNA-AM to 5-trifluoromethylnicotinic acid (TFNA) by using the amidase PsAmiA, but it could not degrade TFNG-AM [21]. Yang et al. [22] reported that a bifunctional nitrilase from Alcaligenes faecalis CGMCC 17553 degraded FLO into its amide products (TFNG-AM) and acids (TFNG). However, the enzymes responsible for this degradation are still unknown.
Nitrile-converting bacteria usually possess nitrilase and NHase/amidase systems [23]. The NHases (EC 4.2.1.84) are metalloenzymes that catalyze nitrile compounds into the corresponding amides. They are widely used as biocatalysts in the synthesis of fine chemicals, amino acids, and derivatives, and they play a crucial role in the degradation of toxic nitrile compounds [24,25]. As a class of hydrolases, amideases (EC 3.5.1.4) play a vital role in the biosynthesis of amide products and the elimination of toxic environmental pollutants, primarily by breaking the C–N bond of amides and catalyzing their hydrolysis to the corresponding carboxylic acid and ammonia [26]. The substrate spectrum of amidase signature family amidases has been widely studied, and all of them showed broad substrate specificity [27]. Amidases and NHases are co-expressed in the same gene cluster in wild-type microorganisms, and hence nitrile-containing compounds are ultimately metabolized to carboxylic acids [26,28]. Variovorax boronicumulans, Agrobacterium, Rhizobium, Ensifer, and Bradyrhizobium convert indole-3-acetonitrile (IAN) to indole-3-acetamide (IAM) via NHase and then IAM to indole-3-acetic acid (IAA) via amidase [29,30,31]. The NHase/amidase cascade enzymatic system can degrade nitrile compounds into less toxic acids [32].
In this study, we demonstrate that Pseudaminobacter salicylatoxidans CGMCC 1.17248 degrades FLO via the NHase/amidase enzymatic cascade system to produce TFNG-AM and TFNG. An investigation of the kinetics of TFNG-AM degradation by P. salicylatoxidans CGMCC 1.17248 was performed, and the amidase gene responsible for the conversion was cloned, overexpressed, and purified. This research improves our comprehension of the mechanisms of microbial FLO degradation. P. salicylatoxidans CGMCC 1.17248 has the potential to remediate nitrile-containing pesticide contamination.

2. Materials and Methods

2.1. Chemicals and Media

FLO and TFNG were obtained from Hubei Nuona Technology Co. (Wuhan, China) and Sigma-Aldrich (St. Louis, MI, USA), respectively. FLO had a purity of 95% and TFNG had a purity of 99%. TFNG-AM (purity 99%) was synthesized following the protocol laid out by Yang et al. [22]. A gradient-grade acetonitrile for high-performance liquid chromatography (HPLC) analysis was supplied by Honeywell (Burdick and Jackson, Shanghai, China). Sinopharm Chemical Reagent Co. (Shanghai, China) supplied all additional reagents of analytical grade.
Luria-Bertani (LB) medium containing 5 g/L yeast extract, 10 g/L tryptone, and 10 g/L NaCl (pH 7.2) was used to cultivate all Escherichia coli strains and P. salicylatoxidans CGMCC 1.17248.

2.2. Strains and Plasmids

As previously reported [33], our laboratory isolated and preserved P. salicylatoxidans CGMCC 1.17248. The protein expression was achieved using Novagen Rosetta (DE3) pLysS cells and a pET28a(+) expression vector from Merck (Kenilworth, New Jersey, USA). E. coli Rosetta strains that overexpress P. salicylatoxidans CGMCC 1.17248 NHase genes (anhA or anhB) had already been constructed by our laboratory [33].

2.3. Kinetics of FLO Degradation by P. salicylatoxidans CGMCC 1.17248 Resting Cells

P. salicylatoxidans CGMCC 1.17248 resting cells were tested for their capacity to degrade FLO. The bacterium was inoculated into 100 mL flasks containing 30 mL of LB medium and incubated for 36 h at 30 °C with shaking at 220 rpm. Following incubation, 3 mL of this culture was inoculated into a 500 mL flask containing 150 mL of LB medium, and a final concentration of 0.1 mmol/L CoCl2 was added. The culture was incubated for 24 h in the same conditions. Centrifugation at 8000× g for 8 min, followed by two washes with sterilized 50 mmol/L phosphate-buffered saline (PBS, pH 7.5), was used to harvest bacterial cells. After harvesting cells, cell pellets were resuspended in the same buffer containing 0.99 mmol/L FLO, and the optical density of 600 nm was measured and adjusted to 5. HPLC was used to measure residual FLO and its metabolites after samples were collected at the required time intervals.

2.4. HPLC and Liquid Chromatography–Tandem Mass Spectrometry (LC–MS)

The concentrations of FLO and its metabolites were measured using a Thermo Scientific UltiMate 3000 (Waltham, USA) Rapid Separation HPLC system outfitted with a Corona charged aerosol detector. The HPLC column and pre-column were, respectively, Agilent reverse-phase HC-C18 columns (4.6 × 250 mm) and reverse-phase C18 pre-columns (4.6 × 20 mm). The mobile phase consisted of a mixture of acetonitrile and deionized water containing 0.01% acetic acid (acetonitrile:water, 30:70 v/v). At a flow rate of 1 mL/min, the elution was monitored at 265 nm [19]. LC–MS analysis was performed using the method outlined in the Supplementary Materials.

2.5. Substrate FLO Testing of AnhA and AnhB

To investigate the FLO transformation ability of E. coli pET28a-AnhA and E. coli pET28a-AnhB resting cells, as well as of a control E. coli strain containing pET28a, bacteria were inoculated into 20 mL of LB medium at 37 °C (220 rpm). Following an initial incubation period of 12 h, 1 mL of this seed culture was added to 100 mL of LB medium, which was then incubated for a further 2.5 h (until the OD600 value reached 0.6). Isopropyl β-D-1-thiogalactopyranoside (IPTG) was added to a final concentration of 0.2 mmol/L. After further incubation for 6 h, samples were collected by centrifugation at 8500× g for 5 min. The resulting cell sediments were then washed in PBS. The cells were resuspended at OD600 = 5 in 5 mL of the PBS buffer with 0.99 mmol/L FLO. Samples were collected after 12 h and centrifuged at 10,000× g for 10 min to eliminate any remaining cells. The supernatant was then filtered and diluted to a volume suitable for HPLC analysis of substrates and metabolites.

2.6. Cloning of Amidase Genes from P. salicylatoxidans CGMCC 1.17248

The amidases potentially responsible for the transformation of TFNG-AM to TFNG were identified using a protein homology analysis strategy. The genome of P. salicylatoxidans CGMCC 1.17248 was sequenced and all annotated proteins were screened as possible amidases. Because the amidases AmiA and AmiB of the N2-fixing bacterium M. flocculans CGMCC 1.16731 were previously demonstrated to convert TFNG-AM to TFNG, all putative amidase protein sequences were aligned with AmiA and AmiB. A phylogenetic tree was constructed for potential amidases based on sequence similarity using the neighbor-joining algorithm in MEGA 8.0 software (Figure S1). Then, amidase sequences with high homology to the amidases AmiA and AmiB of M. flocculans were chosen for gene cloning.
The above-selected amidase-encoding genes were cloned using primers synthesized by Springen Biotechnology Co., Ltd. (Nanjing, China) (Table 1). A Sangon Bacterial Genomic DNA Extraction Kit (Shanghai, China) was used to extract genomic DNA from P. salicylatoxidans CGMCC 1.17248. For DNA amplification operations, PrimeSTAR Max DNA Polymerase Premix (Takara, Dalian, China) was employed. The DNAMAN software version 8.0 was used to analyze protein sequence similarity. The PsmiA and PsmiB sequences characterized in the present study have been submitted to GenBank under the indicated accession numbers WHP70861 and WHP70862, respectively.

2.7. Gene Expression and Metabolism of Substrate TFNG-AM

Genes encoding amidases were amplified by using the gene-specific primers described in Table 1 and the genomic DNA of P. salicylatoxidans CGMCC 1.17248 as the template. After being gel-purified, target fragments were ligated into expression vector pET28a, and recombinant plasmids were transformed into electrocompetent E. coli Rosetta (DE3) pLysS cells. The recombinant strains were then induced with IPTG for expression of the amidases.
SDS-PAGE and Coomassie Brilliant Blue R-250 were used to evaluate protein expression. TFNG-AM degradation was achieved using resting cells containing recombinant amidase via the resting cell transformation method as described in the Supplementary Materials.

2.8. Half-Life Calculation

Determination of the half-life of FLO was in accordance with the approach described by Zhang et al. [34] (see Supplementary Materials).

2.9. Homology Modeling of Amidases

Structural models of amidases PsmiA and PsmiB were constructed based on the crystal structures of Rhodococcus sp. N-771 amidase (fold library id: 3a1i.1.A) and Candida albicans fatty acid amide hydrolase (fold library id: 6kvr.1.A), respectively. The homology models of these amidases were built and evaluated using the SWISS-MODEL workspace (https://swissmodel.expasy.org/interactive) (accessed on 6 September 2023) and I-TASSER (Iterative Threading ASSEmbly Refinement, http://zhanglab.ccmb.med.umich.edu/I-TASSER/) (accessed on 7 September 2023) [35]. The reliability of the models was assessed using the Global Model Quality Estimation and Quantitative Model Energy Analysis methods [36,37]. PyMOL version 2.4 was employed to further examine the structures and templates of the amidases [38].

2.10. Molecular Docking of PsmiA and TFNG-AM

The molecule TFNG-AM was drawn with a 2D structure by using ChemDraw 19.0. The predicted structure of PsmiA was obtained by homology modeling as described in Section 2.9. Using MOE (Molecular Operating Environment) software (version 2022.02 package), the ligand–protein interaction behaviors of TFNG-AM and PsmiA were estimated. Docking was performed by using the Triangle Matcher docking algorithm and London dG scoring function. Calculations of root mean square displacement (RMSD) are critical in comparing different conformers of the same ligand. Docking software generates different ligand conformations, the quality of which is usually assessed by RMSD values [39,40,41]. The 2D interactions of ligands with PsmiA were visualized by the MOE protein–ligand interaction tool.

3. Results and Discussion

3.1. Degradation of FLO by Resting Cells of P. salicylatoxidans CGMCC 1.17248 and Metabolite Identification

P. salicylatoxidans CGMCC 1.17248 was found to convert FLO into two polar metabolites, as determined by HPLC analysis (Figure 1A,B). The retention times of these metabolites were approximately 2.8 and 3.2 min, which matched the retention times of the standard compounds TFNG and TFNG-AM, respectively, in LC–MS analysis. No detectable peaks corresponding to metabolites of FLO were observed in the substrate or bacterial control samples (Figure 1C,D). Mass spectrometry analysis in positive ion mode revealed that metabolite P1 exhibited peaks at m/z = 249, 271, and 287, corresponding to [M + H]+, [M + Na]+, and [M + K]+ ions, respectively (Figure 1E,F). Metabolite P2 displayed peaks at m/z = 248 and 270, corresponding to [M + H]+ and [M + Na]+ ions (Figure 1G,H). These findings are consistent with the results reported by Zhao et al. [19]. Consequently, metabolites P1 and P2 were identified as TFNG and TFNG-AM, respectively.
Interestingly, the concentration of TFNG-AM increased rapidly during the initial 48 h of incubation, followed by a rapid decrease in concentration. Concurrently, the concentration of TFNG increased. According to the previous study, nitrile hydratase may initially play a catalytic role in the metabolism of FLO to TFNG-AM by P. salicylatoxidans CGMCC 1.17248 [19]. With the extension of conversion time, the action of amidases slowly began to take effect, so the concentration of TFNG increased. Based on these results, one or more metabolic enzymes may be involved in the conversion of TFNG-AM to TFNG by P. salicylatoxidans CGMCC 1.17248. The findings indicate that P. salicylatoxidans CGMCC 1.17248 is capable of metabolizing FLO into TFNG-AM, which is subsequently transformed into TFNG.

3.2. Time Course of FLO Degradation by Resting Cells of P. salicylatoxidans CGMCC 1.17248 and Degradation Pathway Analysis

As shown in Figure 2A, resting cells of P. salicylatoxidans CGMCC 1.17248 exhibited a high degradation activity toward FLO, with 61.6% degradation occurring within 24 h. The initial concentration of FLO decreased from 0.99 mmol/L to 0.38 mmol/L during this period. Simultaneously, 0.59 mmol/L of TFNG-AM was generated (a molar conversion rate of 96.7%). The half-life of FLO was found to be 18.7 h. The degradation ability was significantly lower than the values reported for other FLO-degrading bacteria such as the N2-fixing Ensifer adhaerens CGMCC 6315 (24 h, degradation rate 92%) and M. flocculans CGMCC 1.16731 (48 h, degradation rate 94.2%) [19,20], but higher than that of Variovorax boronicumulans CGMCC 4969 (48 h, degradation rate 50.9%) [18].
Various species within the genus Pseudaminobacter have exhibited proficiency in the degradation of environmental pollutants. For instance, Kim et al. [42] observed that Pseudaminobacter sp. SP1a, derived from agricultural soil, contributed to the breakdown of the N-methylcarbamate insecticide prothiocarbamate. Zhang et al. [43] proved the capacity of Pseudaminobacter sp., isolated from soil suffering from long-term contamination from methyl parathion, to remediate environmental contamination resulting from pesticide usage. The degradation ability of P. salicylatoxidans CGMCC 1.17248 suggests its potential as an effective agent for the microbial remediation of FLO.
Nitrile-converting bacteria typically possess nitrilase and NHase/amidase systems. Previous studies revealed that Alcaligenes faecalis CGMCC 17553 has a bifunctional nitrilase (named NitA) that transformed FLO into both TFNG and TFNG-AM (Figure 2B). However, no nitrilase gene was identified in the genome of P. salicylatoxidans CGMCC 1.17248 or M. flocculans CGMCC 1.16731. As a result, amidases are probably involved in the formation of TFNG by these bacteria. M. flocculans CGMCC 1.16731 and V. boronicumulans CGMCC 4969 could further metabolize the FLO intermediate TFNG-AM to TFNG [18,20]. As a result of these findings, a complete metabolic pathway for FLO degradation can be proposed for P. salicylatoxidans CGMCC 1.17248.
This pathway starts with the degradation of FLO into TFNG-AM by enzymes AnhA and AnhB, followed by the hydrolysis of TFNG-AM to TFNG by amidase (Figure 2B).

3.3. FLO Degradation by Recombinant Strains

Resting cells of E. coli pET28a-AnhA and E. coli pET28a-AnhB completely converted FLO to TFNG-AM within 12 h, whereas controls exhibited no degradation activity. Previous studies have shown that AnhA and AnhB exhibited catalytic activity against some neonicotinoid insecticides such as sulfoxaflor and acetamiprid, because nitrile hydratases could hydrolyze the CN group of these nitrile compounds, and the same is true for FLO [33,44]. These results suggest that these two NHases (AnhA and AnhB) are responsible for converting FLO to TFNG-AM.

3.4. Cloning and Overexpression of Amidases in E. coli Rosetta (DE3) and TFNG-AM Degradation by the Recombinant Strains

In E. coli Rosetta cells, pET28a-based plasmids containing psmiA and psmiB were successfully introduced, respectively. The expressed target protein PsmiB exhibited good solubility as observed in SDS-PAGE analyses (Figure 3A). However, recombinant PsmiA formed insoluble inclusion bodies, which presumably may result from incorrect folding of the protein. We were not able to improve the soluble expression of PsmiA despite attempts to optimize the conditions. The molecular weights of PsmiA and PsmiB were consistent with their predicted sizes.
The degradation activity of TFNG-AM by the recombinant strains was investigated. Within the first 48 h of incubation, E. coli-PsmiA resting cells transformed the available TFNG-AM into TFNG. In contrast, control E. coli cells containing the empty pET28a vector and E. coli-PsmiB did not exhibit any measurable degradation of TFNG-AM (Figure 3B). These findings strongly suggest that PsmiA is responsible for the metabolic conversion of TFNG-AM to TFNG in P. salicylatoxidans CGMCC 1.17248.

3.5. Bioinformatic Analyses

The lengths of psmiA and psmiB were determined to be 1308 and 1545 base pairs, respectively, corresponding to proteins PsmiA and PsmiB with 435 and 514 amino acid residues, respectively. The G+C contents of the genes were 68.12 mol% and 62.78 mol%, respectively. The molecular weights of PsmiA and PsmiB were predicted to be approximately 45.5 kDa and 55.0 kDa, respectively. The isoelectric points of PsmiA and PsmiB were predicted to be 5.16 and 5.46, respectively. Through protein homology analysis, it was found that these amidases clustered with the amidases AmiA and AmiB from M. flocculans CGMCC 1.16731. Further analysis using the Protein Basic Local Alignment Search Tool revealed that PsmiA shared 62.76% and 27.46% amino acid sequence identity with M. flocculans CGMCC 1.16731 AmiA and AmiB, respectively. PsmiB showed only 25.82% and 20.54% identity with AmiA and AmiB. Additionally, PsmiA and PsmiB showed 24.62% and 23.67% similarity, respectively, to the amidase PsAmiA from Pseudomonas stutzeri CGMCC 22915 (GenBank accession no. UOU03443.1).
There is a conserved serine- and glycine-rich sequence (GGSSSG) shared by PsmiA and PsmiB, which were identified as members of the amidase family of proteins [27,45]. According to a sequence comparison analysis, both proteins contain the conserved triad of residues Ser161-Ser137-Lys61 and Ser241-Ser217-Lys142, which is characteristic of amidase family members (Figure 4A). Thus, PsmiA and PsmiB belong to the signature amidase family. Based on phylogenetic analysis, PsmiA and PsmiB appear to be closely related to amidases from N2-fixing bacteria. Interestingly, however, PsmiB and the two amidases from M. flocculans CGMCC 1.16731 (AmiA and AmiB) were located on separate branches of the tree (Figure 4B).
In terms of evolutionary branching, PsmiB is closer to M. flocculans CGMCC 1.16731 AmiB (QNH86249) than PsmiA and AmiA, and PsmiB shares only 28.30% amino acid sequence identity with PsmiA. Zhao et al. [19] previously discovered that AmiB could degrade TFNG-AM, but in this investigation, we found that PsmiB does not degrade TFNG-AM, whereas PsmiA does. PsmiA is significantly different from other known signature amidases, with <30% amino acid sequence identity, suggesting that PsmiA is a novel amidase. Interestingly, PsmiA and PsmiB were on different branches of a phylogenetic tree (Figure S1), indicating evolutionary divergence between them. Recently, Jiang et al. [21] identified an amidase (UOU03443) in S. stutzeri CGMCC 22915 that catalyzes the formation of TFNA-AM from FLO, another intermediate of FLO. However, it is unable to catalyze the conversion of TFNG and shares only 24.71% amino acid sequence similarity with PsmiA. This finding suggests that amidases belonging to the same family may exhibit strict substrate specificity.

3.6. Predicted Structures of PsmiA and PsmiB

Figure 5A and Figure S2A show that PsmiA and PsmiB have 27.27% and 31.18% amino acid sequence similarity to Rhodococcus sp. N-771 amidase and C. albicans fatty acid amide hydrolase, respectively. As illustrated in Figure 5B, PsmiA was predicted by homology modelling to consist of 19 helices and 10 strands. There is a predicted catalytic site, within the substrate-binding pocket, that contains the Ser16–Ser137–Lys61 catalytic motif. Active site residues Ser138, Thr158, Gly159, and Gly160 are also present in the catalytic pocket (Figure 5C). As predicted (Figure S2B), PsmiB consists of 20 helices and nine strands. Ser241–Ser217–Lys142, the catalytic motif, is incorporated into the predicted substrate-binding cleft, while active site residues Ser218, Thr238, and Gly240 are positioned at a distance from the catalytic pocket (Figure S2C).
There may be a spatial difference between major active sites and the catalytic pocket that affects substrate binding efficiency, thus explaining the observed variation in PsmiA and PsmB activity. Previous studies have confirmed that when the catalytic triad of PsAmiA (residues K98A, S173A, and S197) was mutated, the protein still showed good solubility but it lost TFNA-AM degradation activity. These results indicate that these specific amino acid residues are crucial for the degradation of the substrate [21].
Among signature-type amidases, Asp191 and Ser195 are highly conserved active site residues, and substitution of these residues completely inhibits enzyme activity in Rhodococcus [30]. Interestingly, PsmiA has a phenylalanine residue at position 191 instead of asparagine, while PsmiB contains a threonine at position 195 in place of serine. We hypothesize that these substitutions of these crucial residues may impede the catalytic activity of the amidases toward TFNG-AM; this warrants further investigation.

3.7. Structure–Function Relationship of PsmiA

Calculations from molecular docking experiments of the structural model TFNG-AM of PsmiA with ligand TFNG-AM are shown in Table S1. The list has been ordered by how well the ligand binds, with the docking score and the “S” column serving as the primary reference criteria: a lower value indicates that the ligand is more strongly bound to the receptor. Compound TFNG-AM exhibited the highest binding affinity and RMSD (value 3.3902 Å) to PsmiA, as summarized in Table S1. The S value for it was −5.0515, and it strongly interacted with the binding site by forming two H-bonds, with residues Glu247 and Met242 (Figure 6A). In the catalytic pocket, the pyridine ring and trifluoromethyl group of TFNG-AM formed hydrophobic interactions with hydrophobic amino acids Leu239, Pro244, Pro356, and Ile378 (Figure 6A). These hydrophobic interactions stabilized the conformation of TFNG-AM in the catalytic pocket and ensured the nucleophilic attack of Ser161 on TFNG-AM. Based on the different interaction modes of the ligand with the hydrophilic amino acid backbone in the PsmiA binding site (Figure 6B), we postulate that the hydrophilic fragments in residues Glu243, Glu247, Arg240, and Asp241 play important roles in the binding of molecules to PsmiA.

4. Conclusions

This study provides evidence that P. salicylatoxidans CGMCC 1.17248 possesses the ability to effectively break down the systemic insecticide FLO into TFNG-AM and TFNG using an NHase/amidase pathway. A previously unknown amidase, which belongs to a unique signature family, has been identified as playing a role in the degradation of TFNG-AM. PsmiA holds promise for applications in environmental remediation and the synthesis of novel amides. The predicted key amino acids may have an impact on the activity of amidase, and this study provides a perspective for understanding the structure–function relationship of amidase and the microbial remediation of FLO.

Supplementary Materials

The following supporting information can be downloaded at: https://www.mdpi.com/article/10.3390/microorganisms12061063/s1. Liquid chromatography-mass spectrometry (LC-MS) analyses; Resting cell transformation method; Half-life of FLO; Table S1: Simulated molecular docking energies (kcal/mol) of the tested ligands; Figure S1: Phylogenetic tree showing the relationships among amidases from P. salicylatoxidans CGMCC 1.17248; Figure S2: Homology modeling analysis of PsmiB.

Author Contributions

Y.-X.Z.: Conceptualization, Investigation, Supervision, Writing—Original draft, Writing—Review & Editing, Funding acquisition; J.Y. (Jing Yuan): Investigation, Supervision, Writing—Original draft; K.-W.S.: Writing—review & editing; C.-J.Y.: Writing—review & editing; L.-W.C.: Writing—review & editing; K.-Y.Y.: Writing—review & editing; J.Y. (Ju Yang): Investigation, Supervision, Funding acquisition; Y.-J.D.: Supervision, Funding acquisition, Writing–Review & Editing. All authors reviewed the manuscript. All authors have read and agreed to the published version of the manuscript.

Funding

This study was supported by the National Natural Science Foundation of China (grant no. 31970094), the Natural Science Foundation of the Jiangsu Higher Education Institutions of China (grant no. 23KJB180027), and the Yancheng City Basic Research Program (grant no. YCBK2023057 and YCBK2023058).

Data Availability Statement

The original contributions presented in the study are included in the article/Supplementary Materials, further inquiries can be directed to the corresponding authors.

Acknowledgments

We thank James Allen for editing the English text of a draft of this manuscript.

Conflicts of Interest

The authors declare no conflicts of interest.

References

  1. Wang, S.S.; Jin, F.; Cao, X.L.; Shao, Y.; Wang, J.; She, Y.X.; Qi, Y.; Zhang, C.; Li, H.; Jin, M.J.; et al. Residue behaviors and risk assessment of fonicamid and its metabolites in the cabbage feld ecosystem. Ecotoxicol. Environ. Saf. 2018, 16, 420–4299. [Google Scholar] [CrossRef] [PubMed]
  2. López-Ruiz, R.; Romero-González, R.; Vidal, J.L.M.; Frenich, A.G. Determination of flonicamid and its metabolites in bell pepper using ultra-high-performance liquid chromatography coupled to high-resolution mass spectrometry (Orbitrap). Food Addit. Contam. Part A 2016, 33, 1685–1692. [Google Scholar] [CrossRef] [PubMed]
  3. Abdel-Ghany, M.F.; Hussein, L.A.; El Azab, N.F. Multiresidue analysis of five neonicotinoid insecticides and their primary metabolite in cucumbers and soil using high-performance liquid chromatography with diode-array detection. J. AOAC Int. 2017, 100, 176–188. [Google Scholar] [CrossRef]
  4. Metcalfe, C.D.; Helm, P.; Paterson, G.; Kaltenecker, G.; Murray, C.; Nowierski, M.; Sultana, T. Pesticides related to land use in watersheds of the Great Lakes basin. Sci. Total Environ. 2019, 648, 681–692. [Google Scholar] [CrossRef] [PubMed]
  5. Sabry, A.K.H.; Salem, L.M.; Ali, N.I.; Ahmed, S.S.E. Genotoxic effect of flonicamid and etofenprox on mice. Biosci. Res. 2018, 15, 2295–2303. [Google Scholar]
  6. Zhou, W.L.; Yue, M.; Liu, Q.; Wang, F.; Liu, L.Y.; Wang, L.; Liu, X.Q.; Zheng, M.L.; Xiao, H.; Bai, Q.H.; et al. Measuring urinary concentrations of neonicotinoid insecticides by modified solid-phase extraction-ultrahigh performance liquid chromatography-tandem mass spectrometry: Application to human exposure and risk assessment. Chemosphere 2021, 273, 129714. [Google Scholar] [CrossRef] [PubMed]
  7. APVMA. Public Release Summary on the Evaluation of the New Active Fonicamid in the Product Mainman 500 WG Insecticide. 2014. Available online: https://apvma.gov.au/sites/default/files/publication/13721-prs-flonicamid.pdf (accessed on 18 May 2024).
  8. Yamamuro, T.; Ohta, H.; Aoyama, M.; Watanabe, D. Simultaneous determination of neonicotinoid insecticides in human serum and urine using diatomaceous earth-assisted extraction and liquid chromatography-tandem mass spectrometry. J. Chromatogr. B 2014, 969, 85–94. [Google Scholar] [CrossRef]
  9. Masiá, A.; Suarez-Varela, M.M.; Llopis-Gonzalez, A.; Picó, Y. Determination of pesticides and veterinary drug residues in food by liquid chromatography-mass spectrometry: A review. Anal. Chim. Acta 2016, 936, 40–61. [Google Scholar] [CrossRef]
  10. Vela, N.; Fenoll, J.; Garrido, I.; Perez-Lucas, G.; Flores, P.; Hellín, P.; Navarro, S. Reclamation of agro-wastewater polluted with pesticide residues using sunlight activated persulfate for agricultural reuse. Sci. Total Environ. 2019, 660, 923–930. [Google Scholar] [CrossRef] [PubMed]
  11. Garrido, I.; Pastor-Belda, M.; Campillo, N.; Viñas, P.; Yañez, M.J.; Vela, N.; Navarro, S.; Fenoll, J. Photooxidation of insecticide residues by ZnO and TiO2 coated magnetic nanoparticles under natural sunlight. J. Photochem. Photobiol. A 2019, 372, 245–253. [Google Scholar] [CrossRef]
  12. Liu, Z.; Dai, Y.; Huang, G.; Gu, Y.; Ni, J.; Wei, H.; Yuan, S. Soil microbial degradation of neonicotinoid insecticides imidacloprid, acetamiprid, thiacloprid and imidaclothiz and its effect on the persistence of bioefficacy against horsebean aphid Aphis craccivora Koch after soil application. Pest Manag. Sci. 2011, 67, 1245–1252. [Google Scholar] [CrossRef] [PubMed]
  13. Fan, X.X.; Song, F.Q. Bioremediation of atrazine: Recent advances and promises. J. Soils Sediments 2014, 14, 1727–1737. [Google Scholar] [CrossRef]
  14. Xiong, H.F.; Dong, S.S.; Zhang, J.; Zhou, D.D.; Rittmann, B.E. Roles of an easily biodegradable co-substrate in enhancing tetracycline treatment in an intimately coupled photocatalytic-biological reactor. Water Res. 2018, 136, 75–83. [Google Scholar] [CrossRef]
  15. Sakashita, T.; Hashimoto, Y.; Oinuma, K.I.; Kobayashi, M. Transcriptional regulation of the nitrile hydratase gene cluster in Pseudomonas chlororaphis B23. J. Bacteriol. 2008, 190, 4210–4217. [Google Scholar] [CrossRef]
  16. Yang, W.L.; Dai, Z.L.; Cheng, X.; Fan, Z.X.; Jiang, H.Y.; Dai, Y.J. Biotransformation of insecticide flonicamid by Aminobacter sp. CGMCC 1.17253 via nitrile hydratase catalysed hydration pathway. J. Appl. Microbiol. 2020, 130, 1571–1581. [Google Scholar] [CrossRef] [PubMed]
  17. Yang, W.L.; Fan, Z.X.; Jiang, H.Y.; Zhao, Y.X.; Guo, L.; Dai, Y.J. Biotransformation of flonicamid and sulfoxaflor by multifunctional bacterium Ensifer meliloti CGMCC 7333. J. Environ. Sci. Health Part B 2021, 56, 122–131. [Google Scholar] [CrossRef] [PubMed]
  18. Jiang, H.Y.; Jiang, N.D.; Wang, L.; Guo, J.J.; Chen, K.X.; Dai, Y.J. Characterization of nitrilases from Variovorax boronicumulans that functions in insecticide flonicamid degradation and β-cyano-L-alanine detoxification. J. Appl. Microbiol. 2022, 133, 311–322. [Google Scholar] [CrossRef]
  19. Zhao, Y.X.; Guo, L.; Wang, L.; Jiang, N.D.; Chen, K.X.; Dai, Y.J. Biodegradation of the pyridinecarboxamide insecticide flonicamid by Microvirga flocculans and characterization of two novel amidases involved. Ecotoxicol. Environ. Saf. 2021, 220, 112384. [Google Scholar] [CrossRef]
  20. Zhao, Y.X.; Wang, L.; Chen, K.X.; Jiang, N.D.; Sun, S.L.; Ge, F.; Dai, Y.J. Biodegradation of flonicamid by Ensifer adhaerens CGMCC 6315 and enzymatic characterization of the nitrile hydratases involved. Microb. Cell Fact. 2021, 20, 133. [Google Scholar] [CrossRef]
  21. Jiang, H.Y.; Yuan, P.P.; Ding, J.J.; Wu, H.K.; Wang, L.; Chen, K.X.; Jiang, N.D.; Dai, Y.J. Novel biodegradation pathway of insecticide flonicamid mediated by an amidase and its unusual substrate spectrum. J. Hazard. Mater. 2023, 441, 129952. [Google Scholar] [CrossRef]
  22. Yang, W.L.; Guo, L.L.; Dai, Z.L.; Qin, R.C.; Zhao, Y.X.; Dai, Y.J. Biodegradation of the insecticide flonicamid by Alcaligenes faecalis CGMCC 17553 via hydrolysis and hydration pathways mediated by nitrilase. J. Agric. Food Chem. 2019, 67, 10032–10041. [Google Scholar] [CrossRef] [PubMed]
  23. Sun, S.L.; Zhou, J.S.; Jiang, J.H.; Dai, Y.J.; Sheng, M.M. Nitrile hydratases: From industrial application to acetamiprid and thiacloprid degradation. J. Agric. Food Chem. 2021, 69, 10440–10449. [Google Scholar] [CrossRef] [PubMed]
  24. Supreetha, K.; Rao, S.N.; Srividya, D.; Anil, H.S.; Kiran, S. Advances in cloning, structural and bioremediation aspects of nitrile hydratases. Mol. Biol. Rep. 2019, 46, 4661–4673. [Google Scholar] [CrossRef] [PubMed]
  25. Ma, D.; Cheng, Z.Y.; Peplowski, L.; Han, L.C.; Xia, Y.Y.; Hou, X.D.; Guo, J.L.; Yin, D.J.; Rao, Y.J.; Zhou, Z.M. Insight into the broadened substrate scope of nitrile hydratase by static and dynamic structure analysis. Chem. Sci. 2022, 13, 8417–8428. [Google Scholar] [CrossRef] [PubMed]
  26. Wu, Z.M.; Liu, C.F.; Zhang, Z.Y.; Zheng, R.C.; Zheng, Y.G. Amidase as a versatile tool in amide-bond cleavage: From molecular features to biotechnological applications. Biotechnol. Adv. 2020, 43, 107574. [Google Scholar] [CrossRef] [PubMed]
  27. Sharma, M.; Sharma, N.N.; Bhalla, T.C. Amidases: Versatile enzymes in nature. Rev. Environ. Sci. Biotechnol. 2009, 8, 343–366. [Google Scholar] [CrossRef]
  28. Varshavsky, A. N-degron and C-degron pathways of protein degradation. Proc. Natl. Acad. Sci. USA 2019, 116, 358–366. [Google Scholar] [CrossRef] [PubMed]
  29. Sun, S.L.; Yang, W.L.; Fang, W.W.; Zhao, Y.X.; Guo, L.; Dai, Y.J. The plant growth-promoting rhizobacterium Variovorax boronicumulans CGMCC 4969 regulates the level of indole-3-acetic acid synthesized from indole-3-acetonitrile. Appl. Environ. Microbiol. 2018, 84, e00298-18. [Google Scholar] [CrossRef] [PubMed]
  30. Kobayashi, M.; Suzuki, T.; Fujita, T.; Masuda, M.; Shimizu, S. Occurrence of enzymes involved in biosynthesis of indole-3-acetic acid from indole-3-acetonitrile in plant-associated bacteria, Agrobacterium and Rhizobium. Proc. Natl. Acad. Sci. USA 1995, 92, 714–718. [Google Scholar] [CrossRef]
  31. Feng, Y.S.; Chen, P.C.; Wen, F.S.; Hsiao, W.Y.; Lee, C.M. Nitrile hydratase from Mesorhizobium sp. F28 and its potential for nitrile biotransformation. Process Biochem. 2008, 43, 1391–1397. [Google Scholar] [CrossRef]
  32. Pasquarelli, F.; Spera, A.; Cantarella, L.; Cantarella, M. Biodegradation of bromoxynil using the cascade enzymatic system nitrile hydratase/amidase from Microbacterium imperiale CBS 498-74. Comparison between free enzymes and resting cells. RSC Adv. 2015, 5, 36913–36923. [Google Scholar] [CrossRef]
  33. Guo, L.L.; Yang, W.L.; Cheng, X.; Fan, Z.X.; Chen, X.M.; Ge, F.; Dai, Y.J. Degradation of neonicotinoid insecticide acetamiprid by two different nitrile hydratases of Pseudaminobacter salicylatoxidans CGMCC 1.17248. Int. Biodeterior. Biodegrad. 2021, 157, 105141. [Google Scholar] [CrossRef]
  34. Zhang, H.J.; Zhou, Q.W.; Zhou, G.C.; Cao, Y.M.; Dai, Y.J.; Ji, W.W.; Shang, G.D.; Yuan, S. Biotransformation of the neonicotinoid insecticide thiacloprid by the bacterium Variovorax boronicumulans strain J1 and mediation of the major metabolic pathway by nitrile hydratase. J. Agric. Food Chem. 2012, 60, 153–159. [Google Scholar] [CrossRef]
  35. Zheng, W.; Zhang, C.X.; Li, Y.; Pearce, R.; Bell, E.W.; Zhang, Y. Folding non-homology proteins by coupling deep-learning contact maps with I-TASSER assembly simulations. Cell Rep. Methods 2021, 1, 100014. [Google Scholar] [CrossRef] [PubMed]
  36. Waterhouse, A.; Bertoni, M.; Bienert, S.; Studer, G.; Tauriello, G.; Gumienny, R.; Heer, F.T.; De Beer, T.A.P.; Rempfer, C.; Bordoli, L.; et al. SWISS-MODEL: Homology modelling of protein structures and complexes. Nucleic Acids Res. 2018, 46, W296–W303. [Google Scholar] [CrossRef] [PubMed]
  37. Benkert, P.; Biasini, M.; Schwede, T. Toward the estimation of the absolute quality of individual protein structure models. Bioinformatics 2011, 27, 343–350. [Google Scholar] [CrossRef] [PubMed]
  38. Seeliger, D.; de Groot, B.L. Ligand docking and binding site analysis with PyMOL and Autodock/Vina. J. Comput. Aided Mol. Des. 2010, 24, 417–422. [Google Scholar] [CrossRef]
  39. Amer, H.H.; Eldrehmy, E.H.; Abdel-Hafez, S.M.; Alghamdi, Y.S.; Hassan, M.Y.; Alotaibi, S.H. Antibacterial and molecular docking studies of newly synthesized nucleosides and Schiff bases derived from sulfadimidines. Sci. Rep. 2021, 11, 17953. [Google Scholar] [CrossRef]
  40. Lee, A.; Lee, K.; Kim, D. Using reverse docking for target identification and its applications for drug discovery. Expert. Opin. Drug Discov. 2016, 11, 707–715. [Google Scholar] [CrossRef]
  41. Xu, X.J.; Huang, M.; Zou, X.Q. Docking-based inverse virtual screening: Methods, applications, and challenges. Biophys. Rep. 2018, 4, 1–16. [Google Scholar] [CrossRef]
  42. Kim, H.; Kim, D.U.; Lee, H.; Yun, J.; Ka, J.O. Syntrophic biodegradation of propoxur by Pseudaminobacter sp. SP1a and Nocardioides sp. SP1b isolated from agricultural soil. Int. Biodeterior. Biodegrad. 2017, 118, 1–9. [Google Scholar] [CrossRef]
  43. Zhang, R.F.; Cui, Z.L.; Jiang, J.D.; He, J.; Gu, X.Y.; Li, S.P. Diversity of organophosphorus pesticide-degrading bacteria in a polluted soil and conservation of their organophosphorus hydrolase genes. Can. J. Microbiol. 2005, 51, 337–343. [Google Scholar] [CrossRef]
  44. Zhao, X.Y.; Chen, K.X.; Wang, L.; Yuan, P.P.; Dai, Y.J. Biodegradation of sulfoxaflor and photolysis of sulfoxaflor by ultraviolet radiation. Biodegradation 2023, 34, 341–355. [Google Scholar] [CrossRef]
  45. Fournand, D.; Arnaud, A. Aliphatic and enantioselective amidases: From hydrolysis to acyl transfer activity. J. Appl. Microbiol. 2001, 91, 381–393. [Google Scholar] [CrossRef]
Microorganisms 12 01063 g001
Figure 1. High-performance liquid chromatography and liquid chromatography–mass spectrometry analysis of flonicamid (FLO) and N-(4-trifluoromethylnicotinoyl) glycinamide (TFNG-AM) degradation by resting cells of Pseudaminobacter salicylatoxidans CGMCC 1.17248. (A) FLO degradation by resting cells of P. salicylatoxidans CGMCC 1.17248. (B) TFNG-AM degradation by P. salicylatoxidans CGMCC 1.17248. (C) Substrate-only control (FLO only). (D) Bacteria-only control. (E) Positive-ion electrospray ionization mass spectrum of metabolite P1. (F) Negative-ion electrospray ionization mass spectrum of metabolite P1. (G) Positive-ion electrospray ionization mass spectrum of metabolite P2. (H) Negative-ion electrospray ionization mass spectrum of metabolite P2.
Figure 1. High-performance liquid chromatography and liquid chromatography–mass spectrometry analysis of flonicamid (FLO) and N-(4-trifluoromethylnicotinoyl) glycinamide (TFNG-AM) degradation by resting cells of Pseudaminobacter salicylatoxidans CGMCC 1.17248. (A) FLO degradation by resting cells of P. salicylatoxidans CGMCC 1.17248. (B) TFNG-AM degradation by P. salicylatoxidans CGMCC 1.17248. (C) Substrate-only control (FLO only). (D) Bacteria-only control. (E) Positive-ion electrospray ionization mass spectrum of metabolite P1. (F) Negative-ion electrospray ionization mass spectrum of metabolite P1. (G) Positive-ion electrospray ionization mass spectrum of metabolite P2. (H) Negative-ion electrospray ionization mass spectrum of metabolite P2.
Microorganisms 12 01063 g001
Microorganisms 12 01063 g002
Figure 2. Time course of FLO degradation by resting cells of P. salicylatoxidans CGMCC 1.17248 and the proposed metabolic pathway. (A) FLO (initial concentration, 0.99 mmol/L) was degraded by resting cells of P. salicylatoxidans CGMCC 1.17248. Standard deviations were calculated from triplicate samples from three parallel cultures (n = 9). The density (OD600) of resting cell suspensions was adjusted to 5. (B) The metabolite pathways of FLO in microorganisms.
Figure 2. Time course of FLO degradation by resting cells of P. salicylatoxidans CGMCC 1.17248 and the proposed metabolic pathway. (A) FLO (initial concentration, 0.99 mmol/L) was degraded by resting cells of P. salicylatoxidans CGMCC 1.17248. Standard deviations were calculated from triplicate samples from three parallel cultures (n = 9). The density (OD600) of resting cell suspensions was adjusted to 5. (B) The metabolite pathways of FLO in microorganisms.
Microorganisms 12 01063 g002
Microorganisms 12 01063 g003
Figure 3. SDS-PAGE analysis of expression of PsmiA and PsmiB in Escherichia coli, and TFNG-AM biodegradation by resting recombinant E. coli cells. (A) Lane M, protein molecular weight markers (116, 66.2, 45, 35, 25, 18.4, and 14.4 kDa); Lane 1, total protein from E. coli cells expressing PsmiA; Lane 2, soluble protein from E. coli cells expressing PsmiA; Lane 3, total protein from E. coli cells expressing PsmiB; Lane 4, soluble protein from E. coli cells expressing PsmiB; Lane 5, total protein from wild-type E. coli (control); Lane 6, soluble protein from wild-type E. coli (control). (B) Resting cell transformation of TFNG-AM. Substrate control without TFNG-AM; E. coli control without TFNG-AM; TFNG-AM degradation by resting cells of E. coli-PsmiB; TFNG-AM degradation by resting cells of E. coli-PsmiA.
Figure 3. SDS-PAGE analysis of expression of PsmiA and PsmiB in Escherichia coli, and TFNG-AM biodegradation by resting recombinant E. coli cells. (A) Lane M, protein molecular weight markers (116, 66.2, 45, 35, 25, 18.4, and 14.4 kDa); Lane 1, total protein from E. coli cells expressing PsmiA; Lane 2, soluble protein from E. coli cells expressing PsmiA; Lane 3, total protein from E. coli cells expressing PsmiB; Lane 4, soluble protein from E. coli cells expressing PsmiB; Lane 5, total protein from wild-type E. coli (control); Lane 6, soluble protein from wild-type E. coli (control). (B) Resting cell transformation of TFNG-AM. Substrate control without TFNG-AM; E. coli control without TFNG-AM; TFNG-AM degradation by resting cells of E. coli-PsmiB; TFNG-AM degradation by resting cells of E. coli-PsmiA.
Microorganisms 12 01063 g003
Microorganisms 12 01063 g004
Figure 4. Alignment of partial amino acid sequences of PsmiA and PsmiB and phylogenetic analysis. (A) Red asterisks indicate residues belonging to the Ser–Ser–Lys catalytic triad. (B) Phylogenetic tree showing the relationships between PsmiA, PsmiB, and other amidases from signature family amidases, constructed using the neighbor-joining method. Bootstrap percentages are shown at the nodes from 1000 replicates.
Figure 4. Alignment of partial amino acid sequences of PsmiA and PsmiB and phylogenetic analysis. (A) Red asterisks indicate residues belonging to the Ser–Ser–Lys catalytic triad. (B) Phylogenetic tree showing the relationships between PsmiA, PsmiB, and other amidases from signature family amidases, constructed using the neighbor-joining method. Bootstrap percentages are shown at the nodes from 1000 replicates.
Microorganisms 12 01063 g004
Microorganisms 12 01063 g005
Figure 5. Homology modeling of PsmiA. (A) Sequence alignment of PsmiA and the selected amidase template, and analysis of key residues. (B) Homology model of the three-dimensional structure of PsmiA. (C) The predicted structure of PsmiA contains the Ser161–Ser137–Lys61 catalytic motif and other important active site residues. * indicated the amino acid residues of the catalytic triad.
Figure 5. Homology modeling of PsmiA. (A) Sequence alignment of PsmiA and the selected amidase template, and analysis of key residues. (B) Homology model of the three-dimensional structure of PsmiA. (C) The predicted structure of PsmiA contains the Ser161–Ser137–Lys61 catalytic motif and other important active site residues. * indicated the amino acid residues of the catalytic triad.
Microorganisms 12 01063 g005
Microorganisms 12 01063 g006
Figure 6. 2D (A) and 3D (B) binding modes of TFNG-AM in the active site of PsmiA. The active site residues of PsmiA are presented in the model. The ligands in the active site of PsmiA are shown as sticks, and hydrogen bonds are represented by dashed lines.
Figure 6. 2D (A) and 3D (B) binding modes of TFNG-AM in the active site of PsmiA. The active site residues of PsmiA are presented in the model. The ligands in the active site of PsmiA are shown as sticks, and hydrogen bonds are represented by dashed lines.
Microorganisms 12 01063 g006
Table 1. Primers used in this study.
Table 1. Primers used in this study.
TargetPrimerSequence (5’→3’) aAmplicon Size (bp)
psmiAF1ACAGCAAATGGGTCGCGGATCCGAATTCATGCAGTCCAGCCGCGAT1308
R1ATCTCAGTGGTGGTGGTGGTGGTGCTCGAGTCAACGCTCCGCCCTGGC
psmiBF2ACAGCAAATGGGTCGCGGATCCGAATTCATGCCGACGATGATCGATGC1545
R2ATCTCAGTGGTGGTGGTGGTGGTGCTCGAGTCAAAGTTCAGAGATGACTGCCTG
a Underlined bases indicate restriction enzyme cleavage sites for EcoRI (GAATTC) and XhoI (CTCGAG).
Disclaimer/Publisher’s Note: The statements, opinions and data contained in all publications are solely those of the individual author(s) and contributor(s) and not of MDPI and/or the editor(s). MDPI and/or the editor(s) disclaim responsibility for any injury to people or property resulting from any ideas, methods, instructions or products referred to in the content.

Share and Cite

MDPI and ACS Style

Zhao, Y.-X.; Yuan, J.; Song, K.-W.; Yin, C.-J.; Chen, L.-W.; Yang, K.-Y.; Yang, J.; Dai, Y.-J. Efficient Biodegradation of the Neonicotinoid Insecticide Flonicamid by Pseudaminobacter salicylatoxidans CGMCC 1.17248: Kinetics, Pathways, and Enzyme Properties. Microorganisms 2024, 12, 1063. https://doi.org/10.3390/microorganisms12061063

AMA Style

Zhao Y-X, Yuan J, Song K-W, Yin C-J, Chen L-W, Yang K-Y, Yang J, Dai Y-J. Efficient Biodegradation of the Neonicotinoid Insecticide Flonicamid by Pseudaminobacter salicylatoxidans CGMCC 1.17248: Kinetics, Pathways, and Enzyme Properties. Microorganisms. 2024; 12(6):1063. https://doi.org/10.3390/microorganisms12061063

Chicago/Turabian Style

Zhao, Yun-Xiu, Jing Yuan, Ke-Wei Song, Chi-Jie Yin, Li-Wen Chen, Kun-Yan Yang, Ju Yang, and Yi-Jun Dai. 2024. "Efficient Biodegradation of the Neonicotinoid Insecticide Flonicamid by Pseudaminobacter salicylatoxidans CGMCC 1.17248: Kinetics, Pathways, and Enzyme Properties" Microorganisms 12, no. 6: 1063. https://doi.org/10.3390/microorganisms12061063

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop