Fabrication and Response Surface Methodology for the Adsorption of Nickel Ferrite-Graphene Oxide Nanocomposite for the Removal of Methylene Blue from Water

Thy, Lu Thi Mong; Linh, Nguyen Thi Chi; Tram, Nguyen Thi Tuyet; Tu, Tran Hoang; Tai, Le Tan; Khang, Pham Tan; Nam, Hoang Minh; Hieu, Nguyen Huu; Phong, Mai Thanh

doi:https://doi.org/10.1155/2021/4636531

Journal of Nanomaterials

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Abstract Introduction Methods Results and Discussion Conclusions Data Availability Conflicts of Interest Acknowledgments References Copyright Related Articles

Research Article | Open Access

Volume 2021 | Article ID 4636531 | https://doi.org/10.1155/2021/4636531

Fabrication and Response Surface Methodology for the Adsorption of Nickel Ferrite-Graphene Oxide Nanocomposite for the Removal of Methylene Blue from Water

Lu Thi Mong Thy,^1,2,3Nguyen Thi Chi Linh,¹Nguyen Thi Tuyet Tram,¹Tran Hoang Tu,¹Le Tan Tai,^1,4Pham Tan Khang,^1,4Hoang Minh Nam,^2,4Nguyen Huu Hieu ,^1,2,4and Mai Thanh Phong^2,4

Academic Editor: Ester Vazquez

Received10 Jun 2020

Revised23 Nov 2020

Accepted25 Dec 2020

Published15 Jan 2021

Abstract

This study is aimed at studying the adsorption of methylene blue (MB) from aqueous solutions by nickel ferrite/graphene oxide (NGO) nanocomposite. The nanocomposite was characterized by Fourier transform infrared spectroscopy, X-ray diffraction, X-ray photoelectron spectroscopy, transmission electron microscopy, energy dispersive X-ray, Brunauer-Emmett-Teller-specific surface area, and vibrating sample magnetometer analyses. The interactive effects of critical variables including pH, initial concentration, and contact time on the adsorption capacity of NGO for MB were studied using response surface methodology (RSM) according to composite central design. In RSM models, the predicted values agreed well with verification experiments, with a high correlation coefficient of 0.9887. The adsorption process followed the pseudo-second-order kinetic and Langmuir isotherm models. The maximum capacity for adsorption of MB onto NGO was found to be 476.19 mg/g. Based on these results, NGO has the potential as an efficient adsorbent for the removal of MB from water.

1. Introduction

Recently, water pollution has been taken into account as an insurmountable problem by the rapid industrialization occurring in many parts of the world. The release of contaminants resulting from industrial activities into water reservoirs has negative impacts on people’s health as well as afflicting harmful damage to living organisms [1]. In other words, many industrial fields like textile, printing, painting, pesticides, or even fertilizers are common pollutants of wastewater. This poses a serious threat to ecosystems, especially with aquatic creatures, as well as human well-being like carcinogenic agents [2]. The most chemical dye found from water is methylene blue (MB) as a phenothiazine dye. Consequently, the removal of MB plays an essential role in protecting natural habitat and the preservation of human health [3].

To deal with the poisonous reasons for MB, various attempts were made to eliminate them including ultrafiltration, sedimentation, coagulation-flocculation, and biological processes. However, these methods still exist limitations about the capacity to remove toxic organic compounds into nondangerous compounds due to their complex structure [4, 5]. Besides, the adsorption method stands out as a durable process and an effective and promising way to solve aqueous solutions containing pollutants due to some advantages including economical concern, high flexibility, easy operation and manufacture, and high sensitivity to hazardous substances [6]. Therefore, the appearance of suitable and effective adsorbents for the development of adsorption of dyes from the aqueous environment has been paid attention around the world, especially with the application of nanoparticles as an adsorbent, possessing high efficiency of removal of contaminants in water [7].

Graphene oxide (GO) can be mentioned as another popular adsorbent with high surface area as well as containing oxygenated functionalities including hydroxyl (–OH), carbonyl (–C=O), carboxylic (–COOH), and epoxide (–O–) groups, which lead to the fact that GO has hydrophilicity and high negative charge density [8, 9]. Because GO is well dispersed in water, the ability to separate and recover the material is not high, which significantly limits its applications [10]. Thus, it is necessary to combine GO with another agent such as metal oxide to increase the selectivity and the recoverability of the adsorbent. The study of a literature survey of graphene-based composites such as Fe₃O₄/GO, Mn₃O₄/GO, and MnFe₂O₄/GO for the removal of pollutants from water has been prepared. Among the available oxides, nickel spinel ferrite (NiFe₂O₄) was chosen due to an inverse spinel structure with Ni²⁺ ions located at octahedral lattices which leads to the low saturated magnetization and high electrical resistivity of NiFe₂O₄. The nickel spinel ferrites (NF) is one of the soft ferrites, possessing a comparatively narrow bandgap which is attracting attention to scientists in the field of waste-water treatment as their exceptional magnetic response and chemical stabilities like magnetoconductivity and low hysteresis loss [11, 12]. This oxide is chosen as a promising base metal oxide nanocomposite due to characteristic properties of Ni²⁺ such as high catalytic efficiency with great ability of high transferring charge [10]. The nickel ferrite/graphene oxide (NGO) is proposed as an adsorbent for the removal of pollutants, especially for MB.

Besides, the optimization process which is built to improve the performance has received much attention from researchers [13]. To enhance the efficient removal of contaminants from aqueous solution and to boost adsorption productivity, it is necessary to investigate the optimization [14]. In this context, the response surface methodology (RSM) involving central composite design (CCD) is employed as the optimization study to investigate the effect of input parameters. In particular, the RSM involving mathematical and statistical procedures depended on the interaction of empirical models to the experimental data achieved from the construction of experiments, which has been considered as the most suitable technique applied to analytical optimization in processing multivariable [15]. An attractive advantage of this method is to reduce the number of experiments, so it can benefit the time and finance problem of the adsorption [14]. Among the RSM designs, CCD is one of the most popular methods due to its simplicity in structure and high achievement for efficiency. CCD brings several advantages including the decrease in the number of experiments and effective predictions in investigating the interaction factors [16]. Besides, CCD illustrates a 2-dimensional surface response graph and finds out the interaction of any two parameters and their effect on the response via polynomial equations [17]. Furthermore, two prominent approaches to study and conduct the optimization of the effect of input variables, including RSM with CCD, are also adopted.

In the present study, the NGO was synthesized by the coprecipitation method to adsorb MB from water. The structure and morphology of the nanocomposite were characterized by Fourier transform infrared spectroscopy (FTIR), X-ray diffraction (XRD), X-ray photoelectron spectroscopy (XPS), transmission electron microscopy (TEM), energy dispersive X-ray (EDX), Brunauer-Emmett-Teller-specific surface area (BET), and vibrating sample magnetometry (VSM). The interactive effects of critical variables on the adsorption capacity of NGO for MB were studied according to RSM. The experiment data were analyzed to study the kinetic and isotherm models and mechanisms. Besides, the regeneration experiments of material were also constructed.

2. Material and Methods

2.1. Material

Graphite powder (20 μm) was purchased from Sigma-Aldrich (Germany). All analytical grade chemicals, including H₂SO₄ (98 wt.%), H₃PO₄ (85 wt.%), HCl (36 wt.%), FeCl₃.6H₂O (99 wt.%), NiCl₂.4H₂O (99 wt.%), H₂O₂ (30 wt.%), and MB (C₁₆H₁₈ClN₃S, >99 wt.%), were purchased from Xilong Chemical (China). KMnO₄ (99 wt.%), NaOH (99 wt.%), and C₂H₅OH (99 wt.%) were obtained from Vina Chemsol (Vietnam).

2.2. Methods

2.2.1. Preparation of NGO

GO was fabricated by improved Hummer’s method [18]; NF particles were synthesized by the coprecipitation method [19]. The NGO composite was synthesized by coprecipitation [20], with the weight of NiFe₂O₄ in NGO was 30%. Briefly, 0.5426 g NiCl₂.6H₂O and 1.2349 g FeCl₃.6H₂O were mixed in 250 mL GO suspension (5 g/L). Then, 2 M of NaOH solution was added drop by drop to the mixture until pH 12 was reached. The mixture was heated at 80°C under stirring for an hour before cooled to room temperature. The black precipitate was separated by an external magnetic field, washed with water, ethanol, and finally dried at 50°C.

2.2.2. Characterization

The functional groups on the surface of materials were studied with the FTIR spectrum (Tensor 27, Bruker). The crystal structure of the materials was analyzed via the D8 ADVANCE Bruker powder diffractometer with a Cu-K_α excitation source. The morphologies of the materials were identified by TEM (JEM 2100, Jeol, Japan) with a 200 kV accelerating voltage source. EDX spectra (Jeol-JMS 6490, Japan) was applied to determine the elemental compositions of materials. Valence states were analyzed using XPS (AXIS Supra, Kratos) with a monochromatized Al-K_α X-ray source (1486.6 eV). The specific surface areas of the material were measured through the BET method (Nova 3200e, Quantachrome). Lastly, the saturation magnetization value of the nanocomposite was recorded using VSM–7400 (MicroSense Easy VSM v. 9.13 L).

2.2.3. Experimental Design

The experiments were set up by adding 0.02 g of NGO into 20 mL MB solution. After the adsorption process, the MB concentration was determined by ultraviolet-visible spectroscopy (UV-Vis, Horiba Dual FL, Japan). The adsorption capacity (, mg/g) of NGO was calculated according to equation (1). where and (ppm) are the initial and equilibrium concentrations of MB, respectively, (mL) is the volume of MB solution, and (mg) is the mass of the adsorbent [21].

RSM with CCD model was applied to investigate the simultaneous effects of factors on adsorption ability, including that of pH, initial MB concentration (ppm), and contact time (min). Table 1 shows the range of independent variables in the experimental design.

According to the CCD model, with the number of survey elements and the number of experiments at the center , the total number of experiments () was calculated according to equation (2):

The quadratic response surface model was fitted to the following equation (3): where is the response (adsorption performance); are the variables of the survey elements; is a constant coefficient; are the first-order coefficients; are the second-order coefficients; and are the interactive coefficients. The statistical parameters were assessed using an analysis of variances (ANOVA) via the Design Expert 10 software.

3. Results and Discussion

3.1. Characterization

The FTIR spectra were utilized to elaborate the functional groups on GO and NGO as shown in Figure 1. GO exhibited a strong absorption band at 3414.01 cm^-1, which corresponds to a characteristic band of –OH. The absorption band at about 1721.06 cm^-1 is assigned to the C=O (carbonyl) groups, while the absorption bands at 1601.03, 1382.55, and 1041.02 cm^-1 are C=C (aromatic), C–O (epoxide), and C–O (alkoxy), respectively. In the NGO and NiFe₂O₄ spectrum, the absorption bands were attributed to Ni–O (O–M_tet) and Fe–O (O–M_oct) linkages, which appeared at 624.33 and 434.78 cm^-1. The results indicated that NiFe₂O₄ nanoparticles have been linked on GO sheets [22].

The XRD patterns of GO, NiFe₂O₄, and NGO are displayed in Figure 2. The unique peak of the bare GO appeared at , indicating successful oxidation and exfoliation of GO [23]. The peaks of NGO appeared at , corresponding to those of NiFe₂O₄ including (111), (220), (311), (222), (400), (511), and (440) planes. The diffraction peak of GO did not exist as shown in Figure 2(b) due to the high diffraction intensities of NiFe₂O₄ particles overwhelming the weak GO peak. These results also indicate that the order of crystal structures in GO remained after the attachment with NF nanoparticles [24, 25].

(a)

(b)

The XPS spectrum of GO and NGO is shown in Figure 3. As shown in C 1s, the spectrum of GO and NGO shows the presence of oxygen-functional groups associated with the carbon structures including C-C (285.8, 284.9 eV), C-O (288.1, 287.8 eV), and O=C-O (289.1, 290.8 eV), respectively. However, the signal strength of the C=O groups in the displacement NGO compared with GO was explained by the Ni²⁺ and Fe³⁺ ions linked with the oxygen-containing functional groups of GO. In the O1s spectrum (Figure 3(e)), the peaks at 528.9, 530.1, and 534.1 eV correspond to the presence of O^2-, O-H bond, and adsorbed H₂O, respectively. The presence of the O^2- bond in the NGO determines the Fe or Ni-O-C bond formation [26, 27]. The XPS spectrum of Ni 2p (Figure 3(f)) is divided into two regions of Ni 2p3/2 (the peak of 855.9, 861.87 eV) and Ni 2p1/2 (the peak of approximately 873.1, 881.3 eV), indicating the presence of Ni²⁺ in the NGO. Two characteristic peaks in Figure 3(g) was centered at binding energies of 711.8 and 725.1 eV due to Fe 2p3/2 and Fe 2p1/2, respectively. In addition, another peak at 719.2 eV also created the presence of Fe³⁺ in the XPS analysis of NiFe₂O₄ following XRD and FTIR [28, 29].

(a)

(b)

(c)

(d)

(e)

(f)

(g)

The TEM images of GO, NiFe₂O₄, and NGO are shown in Figure 4. GO sheets were flat, which showed the highly oxidized and exfoliated attributes of GO; however, the wrinkles and folds of GO appeared, which showed the stacking of sheets. For NiFe₂O₄, the image was presented with many overlapped black dots forming several black portions, indicating the agglomeration of particles. For NGO, the NiFe₂O₄ nanoparticles were distributed uniformly on the GO surface, with an average size of 5-10 nm. These results can be explained by the effect of electrostatic interactions between GO and NF, which helped to prevent the agglomeration and stabilization of NiFe₂O₄ nanoparticles [30]. On a smaller scale, as shown in Figure 4(d), the HR-TEM image also showed the presence of one peak (111) with an interplanar spacing of 0.49 nm corresponding to a crystal plane of NiFe₂O₄ found on the GO sheets. This result is a good agreement with the results of XRD analysts. As a result, the comparison of the TEM and HR-TEM images between the bare GO and NGO revealed that NiFe₂O₄ nanoparticles were successfully decorated on the GO surface [28].

(a)

(b)

(c)

(d)

The element compositions of GO and NGO were determined through EDX data (Table 2). The element compositions of Ni and Fe were confirmed with Ni and Fe wt.% of 7.75 and 14.63%, respectively, which was consistent with the nominal loading molar ratio of Ni/Fe in the starting salt solution. Figure 5 illustrates the SEM image and the distribution of elements in NGO. The Fe and Ni were uniformly dispersed on the C and O base, presenting the attachment of NiFe₂O₄ on the GO surface as well the effective decline of agglomeration on the material.

(a)

(b)

The BET surface area of the NGO was 100.49 m²/g, while GO was 84.68 m²/g. The formation of NF nanoparticles on the GO substrate expanded the interlayer spacing between GO sheets, increasing the surface area of the nanocomposite [22]. This result was higher than that of other magnetic nanocomposite materials as shown in Table 3.

As shown in Figure 6, the magnetic properties of the fabricated NGO indicate that it can be removed after the adsorption process and recycled by applying an external magnetic field. The saturation magnetization value () was 29.4 emu/g, which is lower than that of NF in Table 4. The decrease in the value can be attributed to the smaller size of particles and the presence of nonmagnetic GO. The electron transfer from the nickel ferrite to GO reduces the magnetic moment, leading to the difference in the magnetic property of composite [32].

3.2. Influence of Factors on Adsorption Ability

RSM with CCD was employed to study the significance of the independent variables. In detail, pH (A), initial concentration (B), and contact time (C) were taken as input variables, and the adsorption capacity (Y) was taken as the response. Table 5 displays the experimental result of 20 runs, along with the experimental and predicted adsorption results for MB.

Based on the regression analysis, the estimated coefficients of the equation are shown in Table 6.

To analyze the relevance and significance of the model, it was assessed through ANOVA as shown in Table 7.

The regression coefficients were tested by the Fisher standard, with , suggesting that the regression coefficients are significant and that the model is a completely statistical analysis, with its reliability 99.99% (). Moreover, the value of and shows that the model is compatible with experiments. The adsorption capacity is correlated to the independent variables using the following second-order polynomial model that takes into account the individual, interactive, and quadratic terms as follows:

The appropriateness of the model with experiments was also based on the analytical values shown in Table 8. It shows the relevant and meaningful analysis of the model compared to the experiment. ANOVA analysis results show that the value of , which is close to 1; the coefficient of variation and correction factor show that the MB adsorption capacity of the NGO material is close to the model’s predicted value.

The MB adsorption capacity of NGO in experiments and simulations is shown in Figure 7. The experimental values compared with simulated data have high correlation coefficients, which confirms their compatibility. The regression model is shown to be suitable to predict MB adsorption, with defined conditions related to the effect of pH value, adsorption time, and initial concentration of MB.

In applying the CCD model, the analytical adsorption capacity is compared with experimental results. This is shown in Table 9. Based on the model, the appropriate adsorption capacity is predicted to be 329.95 mg/g at pH 10, with an adsorption time of 150 minutes and an initial concentration of MB of 500 ppm. Based on the experiments, the adsorption capacity is 343.65 mg/g (less than 5% greater compared to the predicted results). This proves that the adsorption capacity of NGO for MB is congruent with the predictive model. Figure 8 shows the steepest curve C corresponding to the MB adsorption time; thus, the MB adsorption capacity of NGO is most prominently affected by adsorption time.

Three-dimensional curves were plotted to clarify the effects of process variables, with two factors for each graph shown in Figure 9. Figure 9(a) shows that the MB adsorption capacity of the material increases as pH and adsorption time increase. This shows that the higher the pH, the better the adsorbent material’s performance. Similar to Figure 9(b), the longer the adsorption time, the better the contact between the material and the MB solution, and the higher the MB adsorption capacity of the material. Results showed that during the first 60 minutes, the adsorption process took place quickly, and the amount of MB absorbed from the solution was higher. After 150 minutes, the adsorption capacity increased more slowly. In this case, the amount of NGO absorbed by MB is almost unchanged. For Figure 9(c), which indicates the relationship between pH and concentration, at concentrations greater than 400 ppm and pH greater than 9, the adsorption capacity of the material nearly reaches equilibrium, and the adsorption rate slows down greatly.

(a)

(b)

(c)

3.3. Adsorption Kinetic

As time increased, the adsorption capacity of NGO for MB was enhanced as shown in Figure 10(a). The values of constants for the kinetic models were calculated and summarized in Table 10. Higher values of correlation coefficient (²) show the fitness of the sorption data; it may be inferred that the pseudo-second-order model has higher ² compared to pseudo-first-order, and the interparticle diffusion kinetic models (Figure 10). In addition, based on the higher ² of the intraparticle diffusion, it is inferred that intraparticle diffusion plays a significant role in the adsorption of NGO for MB. The intraparticle diffusion process consisted of the following 3 steps: (1) film diffusion (from 0 to 60 minutes), (2) intraparticle or pore diffusion (from 60 to 150 minutes), and (3) sorption into interior sites (from 150 to 300 minutes). After 150 minutes, the active centers on the surface of the NGO were filled. The concentration of MB in the solution decreased, reducing the diffusion rate of MB into the material structure, so the adsorption capacity was little changed. Therefore, the appropriate MB adsorption time of the NGO is determined to be 150 [35].

(a)

(b)

(c)

(d)

3.4. Adsorption Isotherm

The Langmuir, Freundlich, and Temkin isotherm models were used to investigate the MB removal process of NGO [36]. Figure 11 and Table 11 present the linear plots and parameters of these models for MB adsorption.

(a)

(b)

(c)

Based on the experimental results, the adsorption process followed the Langmuir model with a correlation coefficient of nearly 1 (). Therefore, the operation resembles that of a single-layer adsorbent with a uniform adsorption surface, and the maximum MB adsorption capacity was .

The MB adsorption capacity of NGO is much higher than that of other adsorbent materials shown in Table 12. This result could be explained as follows: the attachment of NiFe₂O₄ nanoparticles on the GO surface increased the number of adsorption sites to link with MB. Besides, the process of transferring charged electrons from NiFe₂O₄ to the GO surface increases interaction with MB, improving the processing efficiency [22].

3.5. Adsorption Thermodynamics

The investigation of the effect of temperature on the adsorption process was conducted at three different temperatures of 304, 313, and 323 K with the initial concentration of MB of 34.30, 65.08, and 176.49 g/mL. According to the results as shown in Figure 12, the increase in adsorption capacity following the increase in temperature results from the rise in diffusion and drop in viscosity of the adsorbent.

The thermodynamic functions including adsorption free energy change (), standard enthalpy (), and entropy () are evaluated based on the Van’t Hoff equation: where is the thermodynamic equilibrium constant, is the universal gas constant (8.3145 J/mol·K), and is the temperature of the solution (). is the amount of the MB adsorbed per unit gram of the adsorbent (mmol/g), and is the equilibrium concentration of MB (mmol/mL).

The curve fitting and calculation results are listed in Figure 13 and Table 13. The negative value of confirms that the adsorption process is spontaneous (). When the above relations are used, the value of is positive in each case, confirming that the reaction is endothermic [38].

3.6. Reusability

After the MB adsorption process, NGO was regenerated by using various solvents namely ethanol, acetone, H₂O, HCl 0.01 M. The results showed that the efficiency of the desorption by ethanol was higher than that of other desorption solutions. Figure 14 shows the results from five cycles of experiments conducted in the batch mode and the ability to reuse adsorption of material via 5 cycles decreased from 89.27 to 38.86%.

3.7. Adsorption Mechanism

The significant change of adsorbent after the adsorption process was investigated by using SEM-EDX and FTIR analysis. The SEM image shows that the MB changed the morphology of the adsorbent; the surface of the adsorbent is rough, and the edges became fuzzy after adsorption as shown in Figure 15. The elemental compositions of NGO before and after adsorption are shown in Table 14. The increase of C and O contents in nanocomposite was compared to NGO. And, the attendance of the S and Cl element displays that the MB molecules were adsorbed on the NGO surface. These results indicate that the adsorption is a series of interactions produced by functional groups of NGO and MB.

Figure 16 shows the FTIR spectra of NGO before and after MB adsorption. The decrease in the intensity of –OH, –C=O, C=C, and –C-O peaks was reported; thus, the acidic protons of oxygen-containing groups existed on the NGO surface were interacted with MB. The removal behavior of NGO for MB could be explained through hydrophobic and electrostatic interactions as shown in Figure 17. The hydrophobic planes of the NGO interact with the aromatic rings of the dyes, leading to strong stacking interactions under neutral conditions. The electrostatic attraction between the positively charged MB-N⁺ and negatively charged NGO also provides a driving force for the adsorption [20]. These interactions between the dye molecules and adsorbent are responsible for the superior adsorption of the NGO nanocomposite [39, 40].

To evaluate the main adsorption mechanism of MB, the role of surface charge of adsorbent and adsorbate was discussed. Figure 18 shows the zeta potential of NGO, where the isoelectric point is at 5.14. The surface charge of NGO exists in cation at pH below 5.14 with the −OH and −COOH groups become positively charged −OH₂⁺ and −COOH₂⁺ groups. When pH is higher than 5.2, −OH and –COOH groups are ionized and NGO is negatively charged. Moreover MB is positively charged to MB⁺ forms in a wide pH and is a cation dye. To influence the pH on the adsorption capacity, the experiments were prepared in the range of pH from 3 to 9 as shown in Figure 19. Hence, the adsorption ability of NGO is slightly increased when pH increase; there is a fraction of electrostatic interaction between NGO and MB. However, in general, the removal ability of NGO has no great changes under almost pH conditions; thus, the hydrophobic interactions play a key force in the adsorption process [38].

Besides, the above explanation agrees well with the thermodynamic calculation results. The value of is generally between 20 kJ/mol and 0 kJ/mol; thus, the adsorption process of MB on NGO suggests physisorption [41]. The adsorption mechanism was contributed by hydrophobic interaction, electrostatic interaction, hydrogen bond, or Van der Waals interaction [42]. Based on the values of and , the domain interaction was identified in the adsorption process as shown in Table 15. The adsorption process had entropically favorable () and enthalpically unfavorable (), implying that the hydrophobic interaction was predominated.

4. Conclusions

NiFe₂O₄/GO nanocomposite was successfully synthesized by the coprecipitation method. The results of the characteristic analysis of NGO showed that NF nanoparticles were formed and linked on the surface of GO layers with sizes ranging from 10 to 20 nm. The saturation magnetism of NGO was 29.4 emu/g, and the specific surface area was 100.49 m²/g. The simultaneous effects of the above adsorption conditions on the adsorption capacity of NGO for MB were investigated by experimental design according to RSM with the CCD model. The adsorption capacity reached 343.98 mg/g at conditions pH 10, 150 minutes, and MB initial concentration of 500 ppm. The adsorption process followed the pseudo-second-order kinetics and Langmuir adsorption principle, which is hypothesized to be monolayer adsorption. Based on these results, NiFe₂O₄/GO nanocomposite has potential applications in the field of MB adsorption.

Data Availability

The data that support the findings of this study are available from the corresponding author upon reasonable request.

Conflicts of Interest

The authors declare that there is no conflict of interest.

Acknowledgments

This research is funded by Ho Chi Minh City University of Technology, VNU-HCM, under grant number BK-SDH-2020-1880319.

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Copyright © 2021 Lu Thi Mong Thy et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.

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