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Optimization of photochemical decomposition acetamiprid pesticide from aqueous solutions and effluent toxicity assessment by Pseudomonas aeruginosa BCRC using response surface methodology


Contamination of water resources by acetamiprid pesticide is considered one of the main environmental problems. The aim of this study was the optimization of acetamiprid removal from aqueous solutions by TiO2/Fe3O4/SiO2 nanocomposite using the response surface methodology (RSM) with toxicity assessment by Pseudomonas aeruginosa BCRC. To obtain the optimum condition for acetamiprid degradation using RSM and central composite design (CCD). The magnetic TiO2/Fe3O4/SiO2 nanocomposite was synthesized using co-precipitation and sol–gel methods. The surface morphology of the nanocomposite and magnetic properties of the as-synthesized Fe3O4 nanoparticles were characterised by scanning electron microscope and vibrating sample magnetometer, respectively. In this study, toxicity assessment tests have been carried out by determining the activity of dehydrogenase enzyme reducing Resazurin (RR) and colony forming unit (CFU) methods. According to CCD, quadratic optimal model with R2 = 0.99 was used. By analysis of variance, the most effective values of each factor were determined in each experiment. According to the results, the most optimal conditions for removal efficiency of acetamiprid (pH = 7.5, contact time = 65 min, and dose of nanoparticle 550 mg/L) was obtained at 76.55%. Effect concentration (EC50) for RR and CFU test were 1.950 and 2.050 mg/L, respectively. Based on the results obtained from the model, predicted response values showed high congruence with actual response values. And, the model was suitable for the experiment’s design conditions.


Due to the ever-increasing growth of population and increased need for agricultural crops, food and fight with pathogenic carriers, use of pesticides has also grown in various sectors. Contamination of water with pesticides is usually caused by agricultural runoffs and the wastewater of toxin-producing industries. The flow of surface water owing to rainfall or irrigation of farmlands carries these materials and introduces them to rivulets and rivers (Samadi et al. 2010; Akhlaghian and Sohrabi 2015; Hossain et al. 2015; Ryberg and Gilliomb 2015; Stehle and Schulz 2015). Today, different pesticides are used for fighting vectors. Acetamiprid is a systemic, contact, and digestive insecticide, belonging to a new class of neonicotinoid insecticides, which is considered one of the most important micro-contaminants. Its solubility in water is 4250 mg/L at 25 °C and has a half-life of 5–15 days in the environment (Fasnabi et al. 2012; Carra et al. 2015). Acetamiprid is widely used in controlling pests of agricultural crops (John et al. 2016). However, most of the time due to unfamiliarity of chemical toxins, consumers are unaware about the damaging effects of these toxins and correct fighting principles. Due to high solubility, stability and presence of some resistant compounds in the structure of acetamiprid, conventional water and wastewater treatment technologies are not effective in its removal (Miguel et al. 2012; Mutsee 2013; Shanping et al. 2014; Sahithya and Das 2015; Jafari et al. 2014).

Some studies have been conducted for removing acetamiprid pesticide. John et al. (2016) in Kerala by coagulation and flocculation process (John et al. 2016). Wang (2013) in China used biological processes for removing acetamiprid (Wang et al. 2013). Similarly, Shanping (2014) and Fasnabi (2012) employed low-temperature heat plasma and ozonation process, respectively for removal of acetamiprid (Fasnabi et al. 2012; Shanping et al. 2014).

Recently, advanced oxidation processes (AOP) have attracted a great deal of attention, thanks to chemical stability, recoverability, low costs, and processing routes for detoxifying contaminants. They can be a potential substitute for physical, chemical, and biological methods of toxin removal (Ahmed et al. 2011; Moussavi et al. 2014).

TiO2 nanoparticles along with UV radiation are considered a suitable method in water and wastewater treatment (Mohammadi and Sabbaghi 2014; Sivashankar et al. 2014). However, as the distance of energy balances of TiO2 is lower than 3.2 eV, thus it receives only a small part of the ray spectrum and uses it for photocatalytic activity. Accordingly, to enhance optimal response, some changes should be made in its structure. With this aim in mind, for full employment of UV radiation and improving photocatalytic activity, doping of TiO2 nanoparticles with magnet, silica, carbon, and silver-containing materials can be of benefit (Samadi et al. 2010; Liu 2012; Wang et al. 2012; Cao et al. 2013).

Therefore, in the current study, SiO2 and Fe3O4 were introduced to the reaction. Introduction of magnetic nanoparticles into the TiO2 matrices resulted in prevention of accumulation of nanoparticles, catalyst durability, diminished cavity among nanoparticles, increased surface of the catalyst, and recoverability. Since silica particles are hydrophilic, due to presence of silanol group, activity of the surface of nanoparticles increased (Wu et al. 2009; Miguel et al. 2012; Shi et al. 2012; Wang et al. 2012; Cao et al. 2013).

Response surface methodology has been found to be a useful tool to study the interactions of two or more variables. RSM is a collection of mathematical and statistical techniques which are used considering several affecting factors in an optimum manner, even in the presence of complex interactions. It also gives a lot of information from a small number of experiments compared to conventional methods (Sahoo and Gupta 2012; Salman 2014; Mansouriieh et al. 2015; Yousefi et al. 2015). In this study, the photo catalytic experiments were designed based on CCD model for variables such as contact time, initial concentration of acetamiprid, dose of nanoparticles and pH.

However, very little information is available about the optimization of photochemical decomposition acetamiprid illuminated with TiO2/Fe3O4/SiO2 composite. Therefore, in the current study, applicability of TiO2/Fe3O4/SiO2 nanocomposite as an efficient photo catalyst for the degradation of acetamiprid and a novel test for effluent toxicity assessment using Pseudomonas aeruginosa were evaluated.

Materials and methods

Chemicals and media

Analytical acetamiprid toxin was purchased from Sigma-Aldrich Co. with a purity of 98.5%, while its technical form was purchased from Ariashimi Co, Zahedan with a purity of 97%. Acetic acid, ethanol 99.9%, FeCl3, FeCl2, tetra ethyl ortho silicate 95%, tetra-n-butyl lorthotitanate, ammonium solution, Resazurin powder, agar muller hinton, broth nutrient, KH2PO4, K2HPO4, glucose, sodium acetate, dimethyl sulfur oxide (DMSO), n-amyl alcohol, HCl–phthalate buffer, and sodium bicarbonate were purchased from Sigma-Aldrich Co.


Pseudomonas aeruginosa BCRC 11864 strain (ATCC™ 27853) was purchased from Microbiology Laboratory, Islamic Azad University Qom.Iran. In order to prepare a fresh culture and activate the bacteria, Agar Muller–Hinton culture medium (34 g/L) was employed.

Synthesis of Fe3O4 nanoparticles

To synthesize magnetic nanoparticles Fe3O4 using co-precipitation method. Firstly, 11.68 g of FeCl3·6H2O and 4.31 g of FeCl2·6H2O were dissolved in 200 mL of distilled water for 30 min and stirred at 85 °C. Next, the solution obtained was added to 1.8 L of distilled water and was stirred for at 85 °C for 24 h. In order to prevent oxidation, concurrent magnetic injection of nitrogen gas and bubbling was performed. Thereafter, 20 mL of ammonium solution with 30% W/V was added drop-wise to the solution. Its supernatant was removed by a separator funnel (decanter) and following four washes with distilled water and ethanol, the final magnetic product was obtained (Lopez et al. 2010; Hakami et al. 2012; Zhang et al. 2013; Tian et al. 2014).

Synthesis of Fe3O4/SiO2/TiO2 nanoparticles

Synthesis of Fe3O4/SiO2/TiO2 nanocomposite (NPs) was done using sol–gel methods. Before synthesis of titanium dioxide with Fe3O4, an internal layer (SiO2) was used between the TiO2 coating, while magnetic compounds were applied for better TiO2 coating and preventing iron dissolution. For this purpose, Fe3O4 nanoparticles were dispersed in 200 mL distilled water containing TEOS under ultrasonic conditions for 20 min. After that, for separation of nanoparticles from each other, there were four washing stages by water and ethanol. For coating Fe3O4/SiO2 nanoparticles with TiO2, first 30 mL of acetic acid was added to an iron and silica containing reactor and stirred. Next, a mixture of tetra-n-butyl lorthotitanate solution (volume of 15 mL), acetic acid 30 mL, and ethanol 30 mL was prepared. The compound obtained was added to the reactor drop-wise very slowly. The resulting solution underwent ultrasound for 30 min, after which it was kept still for 2 h. In order to dry the nanoparticles, calcination was performed using an electric furnace at 800 °C for 2 h (Wang et al. 2010; Hakami et al. 2012; Shi et al. 2012; Zhan et al. 2014).

Characteristics of nanocomposite

The surface morphology of the fabricated core–shell Fe3O4/SiO2/TiO2 was characterised by SEM (Vega/Tescan-Lmu) analysis after the samples were coated with a thin layer of gold to prevent charge problems and to enhance the resolution. Vibrating Sample Magnetometer studies (VSM) were carried out to study the effect of phase transformations on the magnetic properties of the nanoparticles. The variation of magnetization versus the applied magnetic field for the nanoparticles measured at room temperature.

Experimental design and statistical analysis

In this study, response surface methodology has been used for the modelling (Sahoo and Gupta 2012; Lee and Hamid 2015; Mansouriieh et al. 2015) of the acetamiprid degradation. The photocatalytic experiments were designed based on CCD model for variables such as; contact time (10–120 min), acetamiprid initial concentration (1–40 mg/L), dose of nanoparticles (0.1–1 g/L), and pH (3–12), Table 1. For data analysis, Design Expert. Ver 7 was used.

Table 1 The levels and ranges of variables central composite statistical experiment design

Preparation of reactor

Photocatalytic experiments were performed in a glass reactor with a reflective wall with a volume of 3 L (height 27 cm, width of 10.53 cm) equipped with UV lamp within the range of 251–257 nm, with the peak of 254 nm and a power of 125 W. In each stage of the experiment, 2 L of the solution of the toxin and the nanoparticles synthesized with concentrations of interest was poured into the reactor. Thereafter, the resulting mixture was stirred by a mechanical stirrer.

Analytical methods

Over the course of the experiment, sampling was conducted according to the design. Once samples were taken from the reactor, centrifugation was conducted at 1000g for 5 min to separate the nanoparticles from the solution better. Next, using a magnet with an intensity of 8 T, nanoparticles inside the samples were precipitated and samples filtered using a syringe equipped with a 0.22 μm filter. The concentration of acetamiprid was measured using HPLC (model Agilent Technologies 1260 Infinity) equipped with UV lamp detector and the following specifications were used: C18 column, length and diameter of the column were 4.6 mm × 250 mm, wavelength was 260 nm, mobile phase containing a mixture of deionized water and methanol had a volume ratio of (50/50), the matrix inside the bed column contained pure spherical particles of silica gel, the ambient temperature during the measurement was 25 ± 2 °C, and the volume of injection sample = 20 µL. pH, temperature, and ORP were obtained using a multiparametric probe (HQ40d). The degree of mineralization of the Acetamiprid was ascertained by measuring the chemical oxygen demand (COD) according to standard methods (Ensano et al. 2017). Also, the by-products resulting from decomposition of acetamiprid were analyzed by gas chromatography–mass (GC–MS) (Wang and Shih 2016).

Measurement of UV lamp intensity

In order to measure the intensity of UV lamp (125 W) with average pressure in the reactor, radiometer device Hanger ECL-X, specifically designed for measuring the intensity of UV-C radiation range lamps, was used. In order to compare the intensity of lamp in a typical reactor and reflective wall reactor, it was controlled and measured at a distance half of the reactor length within different time intervals. The intensity of UV radiation was determined using Eq. 1

$${\text{Intensity of UV radiation }}\;({\text{w}}/{\text{cm}}^{2} ) = {\text{T}}\; \times \;{\text{L}}$$

where: T = time (s), \({\text{L}} = {\text{light intensity}}\;({\text{w}}/{\text{s}}\,{\text{cm}}^{2} )\)

Toxicity assessment test based on RR methods

In order to determine the extent of reduction of Resazurin dye using dehydrogenase enzyme, first broth nutrient culture medium with a concentration of 1.6 g/L was enriched with KH2PO4 (1.64 g/L), K2HPO4 (2.64 g/L), glucose (0.2 g/L), and sodium acetate (0.2 g/L). Next, 2750 µL of the enriched broth nutrient culture medium was poured into a test tube. A total of 250 µL DMSO, 1000 µL of bacterial suspension, and 1000 µL of Resazurin solution (100 mg/L) were added to the solution.

In the next stage, 1000 µL of the toxin containing solution was added with specific concentrations (diluted with distilled water). Thereafter, it was incubated in darkness at 28 °C. Following 30 min of contact time, 10 mL of n-amyl alcohol solution and 1 mL of HCl–phthalate 0.05 M buffer were added to each test tube. Following the mixing and centrifugation (1000g in 5 min), the top alcohol layer was transferred to a sink of microplate containing 2–3 g sodium bicarbonate. Once these materials were stirred slowly, the extent of Resazurin reduction was determined through the extent of absorption at the wavelength of 610 nm using UV/Vis spectrophotometer device.

In the presence of active and alive bacteria, the activity of dehydrogenase enzyme caused reduction of Resazurin and its conversion to Resorufin, whereby the color of the solution changed from blue to pink. Inactive bacteria do not develop any changes in Resazurin and its color remains blue (Liu 2006; Tizzard et al. 2006; Zare et al. 2015). The percentage of reduction in the growth was obtained using Eq. 2.

$${\text{Diminished activity of dehydrogenase enzyme in Resazurin conversion}}\;\% = {{\left( {{\text{A}} - {\text{B}}} \right)} \mathord{\left/ {\vphantom {{\left( {{\text{A}} - {\text{B}}} \right)} {{\text{A}} \times 1 0 0}}} \right. \kern-0pt} {{\text{A}} \times 1 0 0}}$$

where: A, the extent of activity of dehydrogenase enzyme in the control sampleand B, the extent of activity of dehydrogenase enzyme in the main sample.

Toxicity assessment test based on CFU methods

Firstly, one loop of P. aeruginosa was added to 25 mL of broth culture medium to prepare bacterial suspension. The turbidity developed in the suspension had a density of about 3 × 108 cells/mL. Thereafter, dilution was performed until its optical density was equal to a solution 1 McFarland by this culture medium. After that, its turbidity was measured by a spectrophotometer device at wavelength of 625 nm (Toolabi et al. 2011). In the next stage, 100 µL of bacteria containing suspension was inoculated on a plate containing the culture medium and acetamiprid toxin at different concentrations. Finally, using Eq. 3, the growth inhibition percentage was determined.

$$\% {\text{Growth inhibition}}\;{ = }\;{{{\text{A}} - {\text{B}}} \mathord{\left/ {\vphantom {{{\text{A}} - {\text{B}}} {\text{A}}}} \right. \kern-0pt} {\text{A}}} \times 100$$

where: A, the number of colonies of the control sample and B, the number of colonies of the inoculated sample.


Scanning electron microscopy

Figure 1 shows the SEM images at higher magnification and the size distributions of particles were in the range of 100–200 nm, also it gave clear idea about the particle separation, we can see that the particles are separated smoothly and not highly affected by agglomeration.

Fig. 1

SEM images of a, b Fe3O4, c, d Fe3O4/SiO2/TiO2

Vibrating sample magnetometer

VSM was used to evaluate magnetization of the NPs as a function of an applied external magnetic field (H) between −8 and 8 T with a resolution of 10−4 emu. Based on the obtained VSM curve at room temperature, magnetic behaviours of the NPs can be analyzed. The zero magnetic remanence (when H is zero) and the hysteretic loop feature indicates that the NPs are super paramagnetic. The dependences of magnetic momentum of NPs on magnetic field are shown Fig. 2.

Fig. 2

VSM result of naked Fe3O4/SiO2/TiO2

The effect of variables

In this study, three-dimensional response and contour plot in removal of acetamiprid with interactions among factors such as pH, contact time, concentrations of acetamiprid and dose of nanoparticles were studied Fig. 3 and Table 2. It was observed that maximum removal efficiency of acetamiprid is (greater than 73%) when pH is near 6.5, contact time is between 65 and 73 min, initial concentrations of acetamiprid and dose of nanoparticles were 20.55 and 550 mg/L, respectively.

Fig. 3

Three-dimensional response removal of acetamiprid with interactions between factors. a The effect of dose of nanoparticles (mg/L) and concentrations of acetamiprid (mg/L). b The effect of concentrations of acetamiprid (mg/L) and pH. c The effect of contact time (min) and pH. d The effect of contact time (min) and concentrations of acetamiprid (mg/L). e The effect of contact time (min) and dose of nanoparticles (mg/L). f The effect of dose of nanoparticles (mg/L) and pH

Table 2 Results of the experimental runs designed according to the CCD


According to various models (linear, two-factor interaction, quadratic and cubic) and their subsequent ANOVA, the acetamiprid removal suitably illustrated by the quadratic model (R2 = 0.9939). The predicted values of the response obtained from the model were sufficiently correlated to the observed values. The following quadratic equation describes the acetamiprid removal efficiency as a function of the variables in terms of cod factors, Eq. 4.

$$\begin{aligned} \;{\text{Y}}\,=\,& 7 2. 6 3 \; - 3. 4 3 2\; \times \; {\text{A}} - 0. 2 5 50 \; \times \; {\text{B }} - 3. 7 5 9 \; \times \; {\text{C 3}}. 1 3 6 \; \times \; {\text{D}}\; - 0. 5 7 3 7 \; \times \;{\text{A}}\; \times \; {\text{B}}\; - 0. 1 3 7 5 \\ & \times \;{\text{A}}\; - 0.0 2 3 7 5 \; \times \; {\text{A}} \times {\text{D}} - 0. 2 100 \; \times \; {\text{B}}\; \times \;{\text{C}}\; - 0. 8 3 6 3\; \times \; {\text{B}}\; \times \; {\text{D}}\; - 0. 40 7 5\; \times \; {\text{C}}\; \times \; {\text{D}}\; - 4. 4 3 9 \\ & \times \;{\text{A}}^{ 2} - 2. 8 8 7\; \times \; {\text{B}}^{ 2} - 0. 90 1 7\; \times \; {\text{C}}^{ 2} - 1. 7 20 \; \times \; {\text{D}}^{ 2} \\ \end{aligned}$$

where: Y represent acetamiprid removal (%) A, B, C and D are the coded values of pH, contact time, initials concentration of acetamiprid and dose of nanoparticles, respectively. The experimental data for acetamiprid removal were statistically analyzed by analysis of variance.

By-products formation

According to the results, 24 compounds with a detection quality of over 50% were detected based on molecular weight. By-products with molecular weight from 98.11 to 444.113 atomic mass unit (AMU) were detected within different retention times of 2.232 until 28.113 min. The clearest peaks were related to Nonadecane, Octadecane, Cyclohexasiloxane–dodecamethyl, Cyclotrisiloxane–hexamethyl, and Heptane compounds, whose detection quality was over 90%. The major peak at the time of 19.334 min was related to Pentasiloxane–dodecamethyl compound, whose detection quality was obtained to be 47%.

The effect of reactor type on intensity of UV radiation

UV radiation was generated both inside the reactor with a reflective wall and a reactor with an aluminum wall. According to the results obtained, the extent of intensities of radiation emitted in the reflective reactor and aluminum reactor were 180 and 125 W/cm2, respectively. This difference had been due to greater reflection of radiation from the reactor walls, which was 1.44 times more than the one observed in the aluminum reactor under similar conditions. Therefore, removal efficiency of acetamiprid was observed due to greater presence of radiation, causing rapid electron excitation off the catalyst surface by UV radiation. Other properties of these reactors include generation of less heat in the solution and being economical, such that when the reflective reactor was used. The maximum measured temperature of the solution was 32 °C, and under the same conditions, the temperature observed in the aluminum reactor was above 43 °C.

Effect concentration of acetamiprid in RR and CFU

In order to determine the inactive rate of P. aeruginosa BCRC 11864, effective concentration (EC) parameter was used. Accordingly, inhibition level of 10–100% was investigated, Table 3. EC50 (mg/L) related to RR and CFU methods were 1.950 and 2.050, respectively. Furthermore, 100% mortality (mg/L) using the two methods stood at 4.180 and 4.280, respectively.

Table 3 The result of acetamiprid effect concentration in Resazurin reduction and colony forming unit


The Fe3O4/SiO2/TiO2 nanoparticles were successfully synthesized by sol–gel methods. The SEM image clearly indicates that the as-synthesized Fe3O4/SiO2/TiO2 nanoparticles are composed of spheres having uniform features. According to the results in the current study, The ANOVA of the second order quadratic polynomial model for the responses show that the models are significant. The Model F-value of 175.85 implies the model is significant, Table 4. There is only a 0.01% chance that a model F value this large could occur due to noise. Values of Prob > F less than 0.0500 indicate model terms are significant (Lee and Hamid 2015; Dong and Sartaj 2016). In their study, It was observed that maximum removal efficiency was when pH near 6.5 and contact time between 65 and 73 min. Minimum removal efficiency when pH near 9. It was also observed that at lower pH values, the removal of acetamiprid was more than alkaline state. As a result, more hydrolysis of acetamiprid occurred at solutions containing hydrogen. According to the results Fig. 3 contact time was an effective parameter in decomposition of acetamiprid toxin, such that with the increase in contact time from 10 to 65 min, the extent of acetamiprid decomposition grew from 38 to 75%. After this, the removal efficiency saw only minor changes, but at contact time of 70 min, it became constant. This is due to greater electron excitation off the catalyst’s surface, production of more active radicals, and the possibility of greater physical collision of the catalyst’s active agents with acetamiprid, providing enough time for collision and decomposition of acetamiprid.

Table 4 ANOVA for response surface quadratic model: analysis of variance table (partial sum of squares—Type III)

According to the results Fig. 3 and through plotting the single-factor curve, it was found that with increase in the concentration of acetamiprid toxin, removal efficiency declined, such that with increase in the concentration from 1 to 40 mg/L, under the same experimental conditions, the removal efficiency decreased from 76.5 to 61.5%. This difference is due to the fact that when acetamiprid is decomposed, the higher its initial concentration, the greater the number of molecules and hydrolyzed particles in the solution. Furthermore, high-energy electrons of the catalyst and the free radicals remained at a certain level of the solution and could not reach all acetamiprid molecules to decompose them.

According to the results from plotting single-factor curve in CCD, with the increase in concentration of TiO2/Fe3O4/SiO2 in the experimental environment, removal efficiency of acetamiprid and COD increased. However, at the concentration of 325 mg/L of nanoparticles, their removal level was 61 and 79% respectively. When the concentration of the nanoparticles increased to 550 mg/L, their removal level reached 76 and 95%, respectively. This is due to the fact that when the concentration of nanoparticles increases in the solution of the experiment and is accompanied by UV radiation, the extent of excitation of e and generation of h+ increases in the catalyst surface. When in contact with water molecules, h+ produces hydroxyl radicals and H+ ions, and e gets into the reaction with dissolved oxygen for formation of superoxide ions (O2·). Next, its reaction with water molecules cause generation of hydroxide ions and peroxide radicals (OOH·). These peroxide radicals are mixed with H+ ions and produce OH·. These hydroxyl radicals collide with acetamiprid and decompose it (Cao et al. 2013; Rodriguez et al. 2013; Verma and Sillanpaa 2015).

According to the results in the current study, the toxicity of acetamiprid is evident at low concentrations for P. aeruginosa BCRC 11864 bacteria. Furthermore, there is a direct and positive relationship between the inhibition percentage of the activity of dehydrogenase enzyme of the bacteria and inhibition percentage of the colonies that formed (R2 = 0.987). In the study by Zare et al. (2016), RR method and its comparison with CFU of Pseudomonas, Enterobacter, and Bacillus bacteria were evaluated in determining the toxicity of wastewater containing heavy metals. In their study, it was found that there is a linear and direct relationship between the bacterial enzymatic activity and colony count in determination of toxicity. Therefore, the results of this study were in line with the conducted study.

According to the results in the current study, a strong relationship was seen between the extent of decomposition of acetamiprid and reduction of toxicity where greater the extent of acetamiprid decomposition, lower the extent of toxicity in both toxicity determination methods of RR and CFU. When the wastewater produced by the reactor was allowed to have contact for 150 min, the extent of growth inhibition of P. aeruginosa BCRC 11864 bacteria reached 2% using both the mentioned methods. These results suggest relatively good decomposition of acetamiprid in the solution by the TiO2/Fe3O4/SiO2/UV photocatalytic process and output of products whose toxicity is far lower than that of the acetamiprid. According to the results presented in Table 5, there is a significant relationship between the extent of absorption of Resazurin and oxidation reduction potential (ORP). In aerobic respiration, ORP level is positive, and typically an ORP above +50 mV represents aerobic conditions and bacterial activity. Lower the extent of absorption of Resazurin greater is the extent of conversion of Resazurin to Resorufin by P. aeruginosa BCRC 11864 bacteria, and the level of ORP is also higher.

Table 5 Results of the experimental ORP, COD and absorption of Resazurin

This is due to higher presence of P. aeruginosa aerobic bacteria in the culture environment containing acetamiprid toxin, which managed to remain alive and have enzymatic activity. Furthermore, there is an indirect and linear significant relationship (p < 0.05) between the extent of conversion of Resazurin to Resorufin and the level of residual chemical oxygen demand (CODr). The greater the extent of conversion of Resazurin to Resorufin by the bacteria, the higher is the extent of COD decomposition and lower the residue in the aqueous solutions.

Moreover, in the current study, a simple method, rapid, and economical based on the activity of dehydrogenase enzyme was optimized for determining the effluent toxicity assessment of aqueous solutions, so that the extent of reduction of Resazurin was in proportion to the extent of activity of P. aeruginosa BCRC 11864 bacteria. Also, a scientific and significant relationship was demonstrated between the oxidation reduction potential and colony forming unit with reduction of Resazurin. This had not been proven so far with regard to acetamiprid pesticide.



response surface methodology


central composite design


colony forming unit


Resazurin reduction


oxidation reduction potential


atomic mass unit


  1. Ahmed S, Rasul MG, Brawn R, Hashib MA (2011) Influence of parameters on the heterogeneous photocatalytic degradation of pesticides and phenolic contaminants in wastewater: a short review. J Environ Manag 92(3):311–330

    CAS  Article  Google Scholar 

  2. Akhlaghian F, Sohrabi S (2015) Fe/TiO2 catalyst for photo degradation of phenol in water. Int J Eng 28(4):499–506

    Google Scholar 

  3. Cao Q, Yu Q, Connell DW, Yu G (2013) Titania/carbon nanotube composite (TiO2/CNT) and its application for removal of organic pollutants. Clean Technol Environ Policy 15:871–880

    CAS  Article  Google Scholar 

  4. Carra I, Sirtori C, Robles LP, Sanchez JA, Malato S, Aguera A (2015) Degradation and monitoring of acetamiprid, thiabendazole and their transformation products in an agro-food industry effluent during solar photo–fenton treatment in a raceway pond reactor. Chemosphere 130:73–81

    CAS  Article  PubMed  Google Scholar 

  5. Dong S, Sartaj M (2016) Statistical analysis and optimization of ammonia removal from landfill leachate by sequential microwave/aeration process using factorial design and response surface methodology. J Environ Chem Eng 4:100–108

    CAS  Article  Google Scholar 

  6. Ensano B, Borea L, Naddeo V, Belgiorno V, Luna MDG, Ballesteros FC (2017) Removal of pharmaceuticals from wastewater by intermittent electrocoagulation. Water 85(9):1–15

    Google Scholar 

  7. Fasnabi P, Remya C, Madhu G (2012) Degradation of acetamiprid in wastewater by ozonation. Int J Eng Res Appl 2(6):1672–1675

    Google Scholar 

  8. Hakami O, Zhang Y, Banks CJ (2012) Thiol-functionalised mesoporous silica-coated magnetite nanoparticles for high efficiency removal and recovery of Hg from water. Water Res 46:3913–3922

    CAS  Article  PubMed  Google Scholar 

  9. Hossain M, Chowdhury M, Pramanik MD, Rahman MA, Fakhruddin ANM, Alam MK (2015) Determination of selected pesticides in water samples adjacent to agricultural fields and removal of organophosphorus insecticide chlorpyrifos using soil bacterial isolates. Appl Water Sci 5:171–179

    CAS  Article  Google Scholar 

  10. Jafari S, Moussavi G, Hossaini H (2014) Degradation and mineralization of diazinon pesticide in UVC and UVC/TiO2 process. Desalin Water Treat 57(8):3782–3790

    Article  Google Scholar 

  11. John S, Soloman P, Fasnabi PA (2016) Study on removal of acetamiprid from wastewater by electrocoagulation. Procedia Technol 24:619–630

    Article  Google Scholar 

  12. Lee K, Hamid S (2015) Simple response surface methodology: investigation on advance photocatalytic oxidation of 4-chlorophenoxyacetic acid using UV-active ZnO photocatalyst. Materials 8:339–354

    Article  PubMed Central  Google Scholar 

  13. Liu D (2006) rapid biochemical test for measuring chemical toxicity. Bull Environ Contam Toxicol 26:145–149

    CAS  Article  Google Scholar 

  14. Liu S (2012) Magnetic semiconductor nano-photocatalysts for the degradation of organic pollutants. Environ Chem Lett 10:209–216

    CAS  Article  Google Scholar 

  15. Lopez J, Gonzalez F, Bonilla AF, Zambrano G, Gomez ME (2010) Synthesis and characterization of Fe3O4 magnetic nanofluid. Materials 30(1):60–66

    Google Scholar 

  16. Mansouriieh N, Sohrabi MR, Khosravi M (2015) Optimization of profenofos organophosphorus pesticide degradation by zero-valent bimetallic nanoparticles using response surface methodology. Arab J Chem. doi:10.1016/j.arabjc.2015.04.009

  17. Miguel N, María P, Mosteo R, Ovelleiro JL (2012) Photocatalytic degradation of pesticides in natural water effect of hydrogen peroxide. Int J  Photoenergy 2012:1–11

    Article  Google Scholar 

  18. Mohammadi M, Sabbaghi S (2014) Photo-catalytic degradation of 2,4-DCP wastewater using MWCNT/TiO2 nano-composite activated by UV and solar light. Environ Nanotechnol Monit Manag 1–2:24–29

    Article  Google Scholar 

  19. Moussavi G, Hossaini H, Jafari SJ, Farokhi M (2014) Comparing the efficacy of UVC, UVC/ZnO and VUV processes for oxidation of organophosphate pesticides in water. Chem J Photochem Photobiol 290:86–93

    CAS  Article  Google Scholar 

  20. Mutsee T (2013) Photocatalytic degradation of pesticides using TiO2 nanoparticles. Nottingham, University of Nottingham. Ph.D. thesis 18–239

  21. Rodriguez E, Marqueza G, Leon EA, Alvarez PM, Amat AM, Beltran FJ (2013) Mechanism considerations for photocatalytic oxidation, ozonation and photocatalytic ozonation of some pharmaceutical compounds in water. J Environ Manag 127:114–124

    CAS  Article  Google Scholar 

  22. Ryberg R, Gilliomb R (2015) Trends in pesticide concentrations and use for major rivers of the United States. Sci Total Environ 538:431–444

    CAS  Article  PubMed  Google Scholar 

  23. Sahithya K, Das N (2015) Remediation of pesticides using nanomaterials: an overview. Int J ChemTech Res 8(8):86–91

    Google Scholar 

  24. Sahoo C, Gupta A (2012) Optimization of photocatalytic degradation of methyl blue using silver ion doped titanium dioxide by combination of experimental design and response surface approach. J Hazard Mater 215–216:302–310

    Article  PubMed  Google Scholar 

  25. Salman J (2014) Optimization of preparation conditions for activated carbon from palm oil fronds using response surface methodology on removal of pesticides from aqueous solution. Arab J Chem 7:101–108

    CAS  Article  Google Scholar 

  26. Samadi M, Khodadadi M, Rahmani AR (2010) Comparison of the efficiency of simultaneous application of UV/O3 for the removal of organophosphorus and carbamat pesticides in aqueous. Water Wastewater 21(1):69–75

    Google Scholar 

  27. Shanping L, Xiaolong M, Yanyan J, Xiaohong C (2014) Acetamiprid removal in wastewater by the low-temperature plasma using dielectric barrier discharge. Ecotoxicol Environ Saf 106:146–153

    Article  Google Scholar 

  28. Shi F, Li Y, Zhang Q, Wang H (2012) Synthesis of Fe3O4/C/TiO2 magnetic photocatalyst via vapor phase hydrolysis. Int J Photoenergy 1–8

  29. Sivashankar R, Sathya A, Vasantharaj K, Sivasubramanian V (2014) Magnetic composite an environmental super adsorbent for dye sequestration—a review. Environ Nanotechnol Monit Manag 1–2:36–49

    Article  Google Scholar 

  30. Stehle S, Schulz R (2015) Agricultural insecticides threaten surface waters at the global scale. PNAS 112(18):5750–5755

    CAS  Article  PubMed  PubMed Central  Google Scholar 

  31. Tian H, Liu F, He J (2014) Multifunctional Fe3O4/nSiO2/mSiO2–Fe core–shell microspheres for highly efficient removal of 1,1,1-trichloro-2,2-bis (4-chlorophenyl)ethane (DDT) from aqueous media. J Colloid Interface Sci 431:90–96

    CAS  Article  PubMed  Google Scholar 

  32. Tizzard A, Bergsma J, Jones GL (2006) A resazurin-based biosensor for organic pollutants. Biosens Bioelectron 22:759–763

    CAS  Article  PubMed  Google Scholar 

  33. Toolabi A, Ahmadian M, Khanjani N, Javadi A, Hashemi M, Rajabizadeh R, Nadri F (2011) Cuo, Tio2 and Zno nanoparticles for disinfecting contaminated hospital surfaces. Word Appl Sci 13(8):1827–1832

    CAS  Google Scholar 

  34. Verma S, Sillanpaa M (2015) Degradation of anatoxin-a by UV-C LED and UV-C LED/H advanced oxidation processes. Chem Eng J 274:274–281

    CAS  Article  Google Scholar 

  35. Wang C, Shih Y (2016) Facilitated ultrasonic irradiation in the degradation of diazinon insecticide. Sustain Environ Res 26:110–116

    Article  Google Scholar 

  36. Wang J, Zheng S, Shao Y, Liu J, Xu Z, Zhu D (2010) Amino-functionalized Fe3O4/SiO2 core–shell magnetic nanomaterial as a novel adsorbent for aqueous heavy metals removal. J Colloid Interface Sci 349:293–299

    CAS  Article  PubMed  Google Scholar 

  37. Wang Z, Shen L, Zhu S (2012) Synthesis of core–shell Fe3O4/SiO2/TiO2 microspheres and their application as recyclable photocatalysts. Int J Photoenergy 2012:1–6

    Google Scholar 

  38. Wang G, Chen X, Yue W, Zhang H, Li F, Xiong M (2013) Microbial degradation of acetamiprid by Ochrobactrum sp. D-12 isolated from contaminated soil. PLoS ONE 8(12):1–9

    Article  Google Scholar 

  39. Wu R, Chen C, Chen MH, Lu CS (2009) Titanium dioxide-mediated heterogeneous photocatalytic degradation of terbufos: parameter study and reaction pathways. Hazard Mater 162(2–3):945–953

    CAS  Article  Google Scholar 

  40. Yousefi A, Tanaka H, Bagheri S, Elfghi F, Mahmood MR, Ikeda SH (2015) Vectorial crystal growth of oriented vertically aligned carbon nanotubes using statistical analysis. Cryst Growth Des 15(7):3457–3463

    CAS  Article  Google Scholar 

  41. Zare MR, Amin M, Nikaeen M, Bina B, Pourzamani H, Fatehizadeh A, Taheri E (2015) Resazurin reduction assay, a useful tool for assessment of heavy metal toxicity in acidic conditions. Environ Monit Assess 187(276):1–11

    Google Scholar 

  42. Zare MR, Amin M, Nikaeen M, Zare M, Bina B, Fatehizadeh A, Rahmani A, Ghasemian M (2016) Simplification and sensitivity study of Alamar Blue bioassay for toxicity assessment in liquid media. Desalin Water Treat 57:10934–10940

    CAS  Article  Google Scholar 

  43. Zhan J, Zhang H, Zhu G (2014) Magnetic photocatalysts of cenospheres coated with Fe3O4/TiO2 core/shell nanoparticles decorated with Ag nanoparticles. Ceram Int 40:8547–8559

    CAS  Article  Google Scholar 

  44. Zhang S, Zhang Y, Liu J, Xu Q, Xiao H, Wang X, Xu H, Zhou J (2013) Thiol modified Fe3O4@SiO2 as a robust, high effective, and recycling magnetic sorbent for mercury removal. Chem Eng J 226:30–38

    CAS  Article  Google Scholar 

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Authors’ contributions

AT, MM and MTG performed the experiments; AT and MT conceived and designed the experiments; AE and MA made a substantial contribution to the analysis and interpretation of the data presented; MHE and AT wrote the paper. MHE, AT, MM and MTG conceived and designed the experiments; AT performed the experiments; AE, AAS and MA made a substantial contribution to the analysis and interpretation of the data presented; MTG wrote the paper. All authors read and approved the final manuscript.


Authors Acknowledge the Zahedan Ariashimi Co, Iran University of Medical Science for providing the technical, experimental materials, synthesis of nanoparticle and analysis of samples.

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The authors declare that they have no competing interests.

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Correspondence to Mohammad Taghi Ghaneian.

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Toolabi, A., Malakootian, M., Ghaneian, M.T. et al. Optimization of photochemical decomposition acetamiprid pesticide from aqueous solutions and effluent toxicity assessment by Pseudomonas aeruginosa BCRC using response surface methodology. AMB Expr 7, 159 (2017).

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  • Photocatalytic decomposition
  • Acetamiprid
  • Toxicity assessment
  • Pseudomonas aeruginosa BCRC