Document Type : Original Research Paper
Wood and Paper Science Department, Faculty of Natural Resources, Sari Agricultural Sciences and Natural Resource University, Sari, Iran
Industrial activities cause wastewater in large volume including hazardous inorganic (metals) or organic (microbes, dyes/ pigments) species. One of the visual remarkable pollution which is generated from paper and pulp, plastic, cosmetic, distilleries, textile and tanneries industries is dye contaminated wastewater . Dyes play a role as a main raw material in different kind of industries. However, their disposal in water bodies exhibits an adverse effect on the aquatic and human life by creating eutrophication, mutagenic, carcinogenic effects and dysfunction of the organs .
Dyes are classified to non-ionic-disperse, acid and reactive, cationic-basic and anionic direct dyes. the biggest and the most diverse group among synthetic dyes are constituted by Azo dyes containing one or more azo groups (-N=N-). Methylene blue’s (MB) name is 3,7-bis (dimethylamino)-phenothiazine-5-ium chloride. It is a fully synthetic chemical and was first used in the treatment of malaria [3,4]. In many applications which are related to medicine such as biomedical dyes applicable in cell staining, cancer phototherapy, antidepressant agents, cyanide, antimicrobial chemotherapy and poisoning by carbon oxide, Alzheimer’s disease treatment by methemoglobinemia, MB has been studied among others, since the first report in 1876 .
In the structure of the MB, the presence of the electrons which are delocalized from the joined p-bonds (chromophore group) is the main cause for its blue color at the times when it is in aqueous solution and it is also responsible for the red color that it has in toluene which has the same mole amount of hydroxide. Due to MB’s clear color, it can be applied as a dye and also for paper industry and staining in the textile [6-7].
Synthetic dyes can be lost at the time of manufacturing or it may be disposed to the environment among industrial wastewaters. The amount of its loss is estimated to be ca. 30% . Considering MB’s oral LD50 of 3500 mg kg-1 (in mice), it is not considered as a compound that is highly hazardous .
However, using doses of MB that are higher than 7.0 mg kg-1 can make abdominal pain and vomiting. It can also cause blood pressure to go high or nausea and mental disorder and other problems. Reports of chronic exposure to MB have indicated that it is mutagenic and causes reproductive disorder .
World health organization (WHO) prescribes a limit of 1mg L-1 of coloring substances in drinking water . Therefore, there is an urgent need for appropriate and functional devices in order to remove MB from wastewaters.
For removing dyes from effluents of industry, some biological and physical or chemical methods have been used such as flocculation, coagulation, precipitation, adsorption on activated carbon, filtration of the membrane, biosorption, electrochemical methods, oxidation/ozonation and anaerobic/aerobic treatments. Various techniques of dye removing from wastewaters have some advantages and disadvantages . Adsorption method was the only one considered to be best and superior among many other physicochemical methods which have been tested. Some of the advantages of this method in comparison with others are as follows: low-cost requirement, easily available, simple design, biodegradability, ease of operation, high efficiency and also the ability to treat dyes in forms that are more concentrated [13-15].
The principle of treatment using adsorption method is dyes entrapment by a solid compound. Generally, according to the various studies conducted by scientists, activated carbon is a good adsorbent element for treatment of discoloration but it makes high-cost problems and saturates quickly and after being used it should be removed . Then the research is lead to use adsorbents with low cost like agricultural wastes, these are very abundant in nature and effective and functional for dyes adsorption from aqueous solutions.
In recent years, different low cost biosorbents like date stones , Wheat straw , Arthrospira platensis , Sunflower seed hull , Penicillium YW 01 , Burkholderia vietnamiensis C09V , Bacillus catenulatus JB-022 strain , Saccharomyces cerevisiae spent , Symphoricarpus albus , Shrimp shell , and Algal spirogyra sp. , have been utilized for dyes removing from aqueous solutions.
The adsorption capacities of dyes by different natural adsorbent have been extensively reviewed by Lakayan et al. . For example, the adsorption percentage for methylene blue was 98.5 % into walnut sawdust coated with polypyrrole (PPy). Ansari et al. have synthesized PPy/SD for adsorption of methylene blue from aqueous solution . Kholghi et al. successfully used Azolla A. Filiculodes species for bio-sorption of Acid Red 14 (AR14) dye (64.5%) from aqueous solution . Asfaram et al. reported an adsorption capacity of 37.96 mgg−1 for Direct Red 12B removal using Garlic Peel .
In this paper, Spruce sawdust (SD) as an agricultural waste, low-cost adsorbent and eco-friendly has been explored as the adsorbent for removing the MB in the batch system from aqueous solution.
Using materials like zinc oxide and magnesium oxide nanoparticles as a powerful sorbent on the surface of other adsorbents (e.g. AC) has a lot of advantages [32, 33]. The increase in the sorption active sites numbers onto the adsorbent can be caused by this process. The problems relevant to the separation of nanoparticles from the solution can also be solved by this process . In this investigation, in order to enhance SD’s capacity for the adsorption of MB dye, magnesium oxide nanoparticles (MgO) were ﬁxed onto SD.
For empirical design, creating an experimental model and also analyzing the models that are built and using a group of numerical and statistical methods is needed and therefore the Response Surface Methodology (RSM) is applied. RSM is based on a polynomial equation ﬁtting to the experimental data, in order to describe the relationship between the response of interest and several variables with the objective of the effects evaluation of independent variables, their interaction effects, and also obtaining optimum conditions for the desirable responses .
Box-Behnken design (BBD) is usually utilized by the RSM. It was propounded by Box and Wilson . The aim of using such a design is to diminish the number of experiments for the particular optimization process. Moreover, it also makes this opportunity for the chemist to investigating the effects of inter-variable that would not be possible with one traditional variable in a time technique. Therefore, BBD is a meticulous method to design the experiment and also to avoid the data redundancy . Analysis of variance (ANOVA) is a statistical technique that is widely employed to assess the significance of various variables into the adsorption process.
Investigating the condition which is optimum for maximum adsorption of MB dye on synthesized Spruce sawdust coated with Magnesium oxide nanoparticles (SD/MgO) was the objective of this study. The BBD model was used for precisely figuring out the role of individual process parameters and also optimization of process variables. Moreover, synthesized SD/MgO nano-biocomposite was characterized by using FTIR, FE-SEM, XRD, and BET in order to determine desirable modification.
MATERIALS AND METHODS
Chemicals and materials
Sawdust samples (SD) were prepared from Spruce wood (Pterocarpus indicus) and were obtained from a local carpentry workshop (north of Iran). In order to remove the adhering dirt and foreign particles, the SD was washed first. The SD which was cleaned, dried using the light of the sun but the oven was made dry by keeping it at 60 OC in one night. The dried materials were crushed and then sieved through 180 µm mesh size.
MB is a dye having the empirical formula C16H18N3S, λ (665nm) and a molecular mass M=319.86 g Mol-1; the molecular structure is represented in Fig. 1. This organic dye is applied to examine the adsorption capacity of adsorbent. By dissolving of 0.5 g of dye in 1 liter of distilled water, a stock solution was made, and dilution was done due to gain the demanded concentrations . Methylene blue dyes utilize in this study was provided by Samchun Chemicals Ltd.
A trans instruments pH meter (model HP3040) with a combined double junction glass electrode was used for measuring pH. All the grade chemicals needed for analysis were from Merck (Germany) and Sigma– Aldrich Chemical Co. (USA).
Preparation and modification of the adsorbent
In a chemical modification, 5.0 g SD with the given characteristics (180 µm mesh size, 10% humidity) was treated with 0.3MMagnesium sulfate heptahydrate (MgSO4.7H2O) and then, NaOH was added dropwise to the mixture under stirring at room temperature until the precipitation was completed. Then the modified SD was washed with double distilled water and filtered. The modified SD were dried in an oven at 90 OC for 6 h . The desired absorbent means nanoparticles MgO coated on SD was prepared (Fig. 2 a). This heating causes the conversion of magnesium hydroxide deposits formed by the reaction to magnesium oxide.
Characterization of adsorbent
The surface images the adsorbents of was captured before adsorption process by applying a Mira 3-XMU (TESCAN, Czech Republic) field emission scanning electron microscope (FE-SEM).
The surface functional groups of adsorbent were analyzed by FTIR spectroscopy (Agilent, Cary 630 2017). The spectra were recorded from 600 to 4000 cm-1 with a number of scans 45.
The patterns of powder X-ray diffraction (XRD) were recorded in step scanning on a Philips PW3050 X-ray diffractometer by applying Cu Kα radiation (k=1.5406 Å) operating at 40 kV and 40 mA. XRD patterns were recorded in the range of 0–70O (2θ).
Nitrogen adsorption-desorption measurement was carried out on a BELSORP-max analyzer (BEL, JAPAN) at –196 OC after the sample was degassed at 120 OC in an N2 flow.
The removal of MB dye was carried out by batch adsorption process. It was done under these effects: optimized adsorbent’s amount, concentration and time and RSM which was based on BBD were adopted for this task.
The initial pH of dye solutions was adjusted using 0.1 N NaOH and 0.1 N HCl. The MB dye contents before and after adsorption processes were analyzed by UV/VIS spectrophotometer (Cary- Eclipse). The results obtained after equilibrium was reached, were fitted to various adsorption isotherms.
Equilibrium experiments were accomplished by putting some measured amount of sawdust in 250-mL flasks which contained 100 mL of dye solution of various initial amounts of dye (50–160 mg L-1). The mixture was vibrated in an orbital shaker at 150 rpm while maintaining a constant temperature (25 OC). The solid phase was then separated by centrifugation (6000 rpm) through the liquid. Then, the dye concentration was measured at 664 nm maximum methylene blue wavelength using a UV-visible spectrophotometer. The adsorption isotherm models which are used more frequently than others were used in the present research and they are Freundlich , the Langmuir , Redlich–Peterson  and Temkin .
Kinetics experiments were done in 250 mL flasks which contain 100 mL of the dye solutions applying a 0.35 g of SD/MgO nano-biocomposite. The flasks were agitated for various time intervals (30–300 min) on the orbital shaker at 150 rpm while the temperature remained constant (25 OC). The kinetic data was analyzed using pseudo-first order, pseudo-second order  and intraparticle diffusion  and elovich kinetic models .
The picture of dye solution before and after the adsorption process for removing the MB dye by using SD/MgO nano-biocomposite is given in Fig. 3.
In order to get values from the samples, the measurement from all of the samples was taken in triplicates and then the mean values were calculated and were used for further analysis. The following equations were used to determine the capacity of the equilibrium adsorption and dye removal%:
qe (mg g-1) represents the capacity of the equilibrium adsorption while Co and Ce are the initial and equilibrium dye concentrations (mg L-1), respectively. V is the volume of the dye solution (L) and W is the dry weight of the adsorbent (g).
BBD presents some advantages of other RSM like full factorial and central designs of composite due to its fewest points of design. Also, BBD offered treatment combinations at the edge’s midpoint and the center of the process. But then, BBD avoidance of the experimental points which are extreme (corner and star points) led to a more efficient estimation of the coefficients. [46-47]. In this research, three factors with three BBD levels were applied to study the effects of variables; MB concentration, adsorbent dosage, and pH on the response factor; on removing of MB. The three levels of each variable; low, middle and high were encoded as −1, 0 and 1, respectively as in Table 1. 15 designed experimental BBD run with the independent variable arrangement; three response factors have been displayed in Table 2. Three responses of the central point were considered to estimate the pure error.
To correlate the MB removal, a quadratic polynomial equation was developed as a function of independent variables and their interactions. The correlation’s general form is as follows:
Y stands for the response factor (i.e., the removing of MB), X is input variable and β0, βj, βjj, βij are the intercept, the linear effect, the square effect, and the interaction effect, respectively. K is the quantity of input variables (3 in the current study) and ɛ is the unanticipated error . The analyzing and optimization procedures and all the tables and figures were implemented using the Design-Expert 7.06 trial (Stat Ease, Inc. Minneapolis, USA).
RESULTS AND DISCUSSION
Characterization of nanobiocomposite SD/MgO
The physical properties of SD and SD/MgO nano-biocomposite samples were analyzed by low-temperature N2 adsorption-desorption and the results are listed in Table 2. According to Table 1, the SD/MgO nano-biocomposite exhibits a high total surface area (0.873 m2 g–1) and lower pore diameter (6.858 nm). The results demonstrate that the presence of MgO nanoparticles enhances the total surface area and decreases the pore diameter.
Field Emission Scanning Electron Microscopy (FE-SEM)
Scanning Electron Microscopy is one of the most widely employed technique to obtain the information regarding the surface and morphology of the nanomaterials. The morphological information of the SD/MgO nano-biocomposite was obtained by FE-SEM.
The FE-SEM images of the SD and SD/MgO nano biocomposite are represented in Fig. 4. It is evident that sawdust is a smooth and layered material without any pores (Fig. 4a). This structure would account for its weak BET surface area. In contrast, the surface of the chemically modiﬁed sawdust has a large amount of MgO particles within the range of 40-60 nm (Fig. 4b).
Moreover, it also represents that most of the particles are quite homogeneous, have spherical-like shapes and are distributed on the SD surface, uniformly. This is obvious that the present material has high surface area and is therefore capable of adsorption of objective constituents.
X-ray diffraction studies
XRD analysis obtained from SD and SD/MgO nano-biocomposite samples (Fig. 5) reveals that both adsorbents are completely amorphous. However, peaks emerge at 2θ= 26, 38, 50, 59, 64 and 69, suggesting the appearance of MgO crystals in SD/MgO .
The crystallite sizes (nm) were calculated by the Scherrer equation . The mean nanocrystal size of the prepared SD/MgO has estimated about 5.2 nm. using the Debye-Scherrer formula on the basis of the full width at half maximum (FWHM) of the 2θ=38O peak.
The various groups present in adsorbent which are the potential sites to bin dye ion on the adsorbent surface are detected by the FTIR spectroscopy technique.
The spectra of SD/MgO before adsorption of MB and after that were analyzed within the amounts between 600-4000 cm-1 (Fig. 6). The FTIR spectrum of SD/MgO before MB adsorption displayed a number of peaks at various wavenumbers retaining to different functional groups. The appearance of the O-H group (phenols, carboxylic acids, and alcohols) on the adsorbent’s surface as it happens in cellulose has been indicated by the presence of broad bands in the region of 3300 cm-1, pectin and lignin [50,51].
The peak’s presence in the area of 2900 cm-1 attributed to aliphatic C-H asymmetric stretching present in present in biomass structure (cellulose, hemicellulose, lignin) [50,52]. The peak at 1735 cm-1 is a correspondence to C=O stretching vibration of carboxylic acids groups [53,54]. C=C aromatic stretching of lignin assigns the bands in the region 1595 cm-1 and 1504 cm-1 to itself .
The bands at 1230 cm-1 and 1025 cm-1 corresponds to C-O stretching vibration of carboxylic acids and alcohols [-56, -57]. The bending vibration of C-H can cause the band at 896 cm-1 [-58]. After adsorption of MB, we note that the peaks intensity of O-H (3300 cm-1), C=O (1735 cm-1) and C-O (1230 cm-1, 1025 cm-1) decreased, these shifts indicate that an interaction occurred between MB and these groups. These results showed that the SD/MgO nanocomposite contains several functional groups responsible for the MB adsorption such as O-H, C=O, and C-O. Some new peaks have been detected on the SD/MgO spectrum after adsorption at 1330 and 1247 cm-1 for aromatic nitro compound and S=O stretching, respectively, attributed to the MB molecules presence on the surface of adsorbent .
Three factors with three levels of Box–Behnken response surface design (BBD) have been applied to investigate the dependent variables’ features. These factors were used to optimize and study the process variables’ effect on the response (MB Removing). The variables design matrix of not coded and coded units by the BBD; along with the values of the response which are experimental and predicted, is presented in Table 3. Each experiment was carried out three times and the average results of the MB Removal evaluation over the SD/MgO nano-biocomposites and their corresponding standard deviation values were reported. After that, the values of their related standard deviation were given. By reviewing the following table data, it is clear that the range of the values related to the deviation of the results was between 0.0 and 0.3 %, thus they were relatively low. Moreover, the values related to the relative standard deviation of the results were about ±2.3% and therefore they also were low, which approves that the experiments have good accuracy and reproducibility.
The values of MB removal which are measured in different batches presented wide variation (i.e., the range of values was from a minimum of 31.20 to a maximum of 93.36). The fact that the value of MB removal is highly affected by the variables selected for the study is clearly shown in the results.
A quadratic model with statistical significance from a combination of estimates for the variables and the ANOVA results can be produced. This model is given below:
Here, MB removal is the response and X1, X2 and X3 are the actual parameters. The coefficient’s sign and value in each correlation’ term show the effects of the parameters on the response increasing and decreasing.
From eq. (6) it can be concluded that the dosage of the adsorbent which has the coefficient of 28.42542, has the most positive linear impact among other ones and the interaction that is between the concentration of MB and the dosage of adsorbent which has a coefficient of 0.08625 has the most positive interaction impact on the removal of MB.
Table 4 shows the results of ANOVA test. It also shows the parameters which are based on statistics and are related to the suggested correlation which are quadratic. The F-Value (its other name is F-statistic) of a factor is something that is used to measure the assessment of the variance which is related to that factor and the residual variance. This value is calculated by dividing the mean square of the factor by the residual mean square. In most cases, in order to realize the configuration of interactions among the variables as the criteria, the ‘’Significance probability” (its other name is ‘’p-value”) and F-statistic can be applied. The corresponding variables being more significant is shown by a higher F-statistic and a lower P-value and if the factor with P-value is lower than 0.05, it is regarded as significant.
As Table 4 shows, all quadratic and linear terms are below 0.05 and therefore significant except the interaction term of ‘X2X3’. Nonetheless, because of the p-value (p < 0.0001) and F-statistic (F = 134.58), it can be concluded that this model is highly significant and it also approves the curvature’ presence in the surface of the response.
The determination’s coefficient of the proposed correlation is shown in Table 5. The definition of coefficient of variation (C.V) explains the standard deviation which is related to the mean and is also a statistical measure of dispersion.
Table 4 helps us approve that the regression model can portray the empirical data with a satisfying level of assurance (which is higher than 95%) by indicating that the low value of the coefficient of variation is 3.08% and the high value for determination coefficient is 0.9959 and adjusted determination coefficient is 0.9885.
Fig. 7 illustrates the empirical data points on the MB’s removal. These data points are also compared with the values that are predicted. The quantified response data which are for a specific run are actual values. The approximating functions were used to generate the predicted values which are evaluated from the model. Fig. 7 also proves that the empirical results have a fine agreement when they are compared to the values that are predicted.
Effect of process variables on MB removal
Fig. 8 displays the plots of the mean effect which are based on the data from Table 4. When there is a response which is as large as possible in these experiments, it is concluded that the system is optimized. It is observable that adsorbent dosage and pH have a positive impact on the MB removal and MB concentration has the negative impact. As the Table 4 shows, the adsorbent dosage is the highest effective degree of the individual factor on MB removal (F = 594.41, p < 0.0001).
In the case of adsorbent dosage, a clear increment in MB removal is seen by making the adsorbent dosage go from 1.5 to 3.5 g L-1. Furthermore, the MB removal was decreased by increasing the MB concentration. Considering the pH, MB removal was enhanced by increasing this factor. At the low level of X1 and high level of X2 with increasing pH to the upper level, MB removing went higher.
Effect of experimental parameters on MB removal
3D response surface plots for the measured responses have been constructed in order to reach the better understanding of the independent variables effects and their interactions on the dependent variable. When a circular 3D response of the surfaces was found, the interaction between the related variables was negligible. Moreover, the plot’s elliptical or saddle characters proves that the interaction between the related variables was significant .
Furthermore, parallel lines propose that no significant interaction has existed. In 3D response plots, the dependent variable is represented by the upper horizontal axis. Illustrating the response surfaces as three dimensional (3D) plots determined the importance of each three independent factors (MB concentration, adsorbent dosage, and pH) on the removal of MB. Three-dimensional plots for MB removal were obtained from Eq. (6) and given in Fig. 9.
Fig. 9 (a) showed 3D response surface plots for percentage removal of MB on SD/MgO nano biocomposite as a function of MB concentration and pH. In this removal percentage of MB increased with increasing pH of the solution (from pH 3 to 11). Curve portion in 3D plot Fig. 9 (a) suggested that significant removal of MB was found to have the almost good interactive influence of these two variables.
The percentage removal of dye increases with increase in an adsorbent dose of the solution. Curve portion in 3D plot Fig. 9 (b) suggested that significance removal of MB dye was found almost good interactive influence as the adsorbent dose was increased from 1.50 to 3.5 g L-1. At low doses (1.50 g L-1), because of the limited number of binding sites that are available, there is less opportunity among dye molecules, therefore removal process attained a low percentage. Because of the more adsorption sites which are available for dye uptake, an increase in adsorbent dose to 0.20 g L-1, would cause a corresponding increase in the percentage of removal [-61].
The F values for MB concentration, adsorbent dosage, and pH are 310.14, 594.41 and 233.97 according to Table 4, which affirms that adsorbent dosage has the highest important impact on MB removal.
Model validation for MB dye
The validation experiment was performed by several sets of different combination of variables (MB concentration, adsorbent dosage, and pH) each within their experimental ranges. The model predicted value, and the experimental value was used to define the validity of model (Table 6). These results affirm that the predicted conclusions satisfactorily match with the empirical values adequately.
On the basis of the best-fitted equation, the model optimization of variables was done to get the maximum removal percentage. 12 optimized results were obtained and it was found that the maximum optimized conditions for MB dye (MB concentration of 68.54 g L-1, the dose of adsorbent 3.45 g L-1 and pH 10.48) which showed 94.05% removal of MB.
In wastewater treatment, it is of great import to study the adsorption mechanism and steps of the potential rate controlling for design objectives. To describe the kinetics of adsorption, several kinetic models are available. Mostly applied models including the pseudo-first-order, pseudo-second-order, Elovich and intra-particle diffusion have been used for the empirical data to evaluate the adsorption kinetic of MB dye. The applicability of these kinetic models was appointed by measuring the correlation coefficients (R2).
Pseudo-first and second-order kinetics
Below the pseudo-first-order and pseudo-second-order kinetic models’ nonlinear equations are showed:
k1 stands for the pseudo-first-order rate constant (min-1) and k2 stands for the pseudo-second-order rate constant (g mg-1 min-1). The MB’ amount which is adsorbed at equilibrium is represented by qe (mg g-1). qt (mg g-1) stands for the MB’s amount that is adsorbed at time t. Fig. 10 shows the graph of log (qe - qt) against ‘t’ from which the pseudo-first-order kinetic rate constant was obtained.
The Fig. 10 shows the pseudo-second-order kinetic model. As can be seen in Table 7 a better R2 value was obtained (R2-0.875). The qe values which were obtained were highly in support of the data from the research experiments for the related kinetic model. The involvement of chemical adsorption process is suggested by the applicability of the pseudo-second-order kinetic equation.
The reactions that include the adsorption of chemicals and also Elovich model can be employed easily. In order to analyze the range of chemisorption, this can be an important model to use. Below is the mathematical representation of the model:
“a” is a constant. Because (qt/t) equals “a” at the time that the value of qt reaches 0, “a” is considered as the initial rate constant (mg g-1 min-1). “b” (g mg-1) represents the facade coverage’s level and activation energy. qt (mg g-1) represents the MB’s adsorption onto SD/MgO sorbent at time t. Plotting qt against t evaluates the constants. Fig. 10 points out the fact that MB dye and SD/MgO nano biocomposite is following this model very well (see Table 7).
Intra-particle diffusion model
An intra-particle diffusion model was applied to investigate the kinetics of adsorption for MB dye and SD/MgO nano-biocomposite system. Below is the mathematical representation of this model:
kid stands for the intra-particle diffusion (mg g-1) rate constant. C stands for the intercept (mg g-1) and its value shows the boundary layer’s thickness. Different parameters are being yielded from the plots of qt versus twhich describe that the process of batch adsorption involves more than one process. Furthermore, the Fig. 10 proposes that the intra-particle diffusion can be accepted as rate controlling step. The kinetic parameters and coefficients of the correlation are being shown in Table 7.
Equilibrium adsorption isotherm studies
The equilibrium isotherms are of great import elements for grasping the adsorption systems . Different models (e.i. Langmuir, Freundlich, Temkin, and Redlich–Peterson) have been selected in order to simulate the adsorption isotherm and therefore clarify interactions of dye adsorbent.
Langmuir isotherm model
Langmuir isotherm model is studied for the surface which is covered by adsorbate monolayer. Langmuir isotherm describes the surface coverage of adsorbate monolayer (MB). Below is the mathematical representation of the nonlinear form of this model:
qo represents the maximum amount of the capacity of adsorption (mg g-1) and qe stands for the amount of analyte which is adsorbed per unit mass of the adsorbent at equilibrium condition (mg g-1). The values of respective constants of Langmuir are given in Table 8 and the graph plotted between qe and Ce as shown in Fig. 12.
The suitability of the model is estimated by separation parameter (RL) that can be evaluated by the following equation.
The RL values were plotted against Co to estimate the favourability of the adsorption of the process with respect to the initial concentration of the dye (Fig. 11). The fact that the nature of the isotherm is favorable (0<RL<1), reversible (RL = 0), linear (RL = 1) or unfavorable (RL > 1) is indicated by the values of the parameters of the separation. Value of RL in this study was in the between of 0–1 which reveals that adsorption of MB onto SD/MgO nano-biocomposite was a favorable process. For this system, the RL values approach towards zero as the initial concentration is increased.
Freundlich isotherm model
The isotherm model assumes heterogeneity in the adsorbent’ surface which arises cause of the fact that there are different functional groups at the adsorbent’s surface. Mathematically, a nonlinear form of this model is represented as.
where KF and n are Freundlich constants which represent Freundlich adsorption capacity (mg g-1) and its intensity. The values of respective constants of Freundlich are given in Table 8. The Freundlich isotherm is shown in Fig. 12.
Temkin isotherm is applied to survey the adsorption heat and indirect effect of the adsorbate interactions on adsorption. The model portrays the correlation of coverage with the adsorption energy and it takes no notice of the concentrations that are extreme. To Plot the amount of adsorbed qe against Ce concluded that the homogenous spreading of binding energies was done. Below is the nonlinear form of Temkin isotherm:
B = RT/b and T represents the absolute temperature (Kelvin), b stands for the Temkin constant and R represents the universal gas constant (8.314 J mol-1 K-1). A stand for the constant of the equilibrium binding and B represents the related heat of sorption. Table 8 presents the findings’ summary from the isotherm studies. If the experimental data fits better to the Temkin isotherm model, the high value of R2 (0.9537) will be achieved.
Redlich–Peterson isotherm model Redlich–Peterson equation included three adjustable parameters into an empirical isotherm. This equation is widely used as a compromise between Langmuir and Freundlich systems. The nonlinear form of Redlich–Peterson isotherm model is represented as.
WhereA, B, and g are the Redlich–Peterson isotherm constants, qe is the amount adsorbed at equilibrium (mg g-1) and Ce is the equilibrium concentration of adsorbate (mg L-1). When the value of g is equal to 1, the above equation is reduced to the Langmuir isotherm, while it reduced to a Freundlich isotherm, in case the value of the parameter BCeg is much bigger than 1. The ratio of A/B indicates the adsorption capacity. The higher R2 value (0.9846) for the three-parameter isotherms suggest the applicability of these models to represent the equilibrium adsorption of MB by SD/MgO nano-biocomposite. The values of the constants related to diverse isotherm models are presented in Table 8.
In this study, Spruce sawdust (SD) coated with MgO nanoparticles has been identiﬁed as effective adsorbent and this effective adsorbent is applied in a batch system for removing MB from aqueous solution. The synthesized SD/MgO nano-biocomposite was characterized by FTIR, FESEM, XRD, and BET. Further, RSM based BBD was carried out for optimization of variable parameters such as MB concentration, adsorbent dosage, and pH. R2 0.9959 showed the significance of applied model for removal of MB dye. The model F-value of 134.58 and a low probability value (Prob. >F < 0.0001) signify that model terms are symbolic. Based on optimized conditions through RSM, maximum percentage removal of dye was found to be 94.05 % for MB. Moreover, validation of the model was done for dye removal to determine the correlation between experimental and predicted value. Resultant, a good percentage removal of dye was found on the basis of optimized methodology. The Freundlich isotherm model and pseudo-second-order kinetic model described the data better than other isotherm and kinetic models.
CONFLICT OF INTEREST
The authors declare that there are no conflicts of interest regarding the publication of this manuscript.