Research Article  Open Access
Biosorption Behavior of Basic Red 46 and Violet 3 by Dead Pleurotus mutilus from Single and Multicomponent Systems
Abstract
The performance of nonviable P. mutilus for removal of Crystal Violet (CV) and Basic Red 46 (BR46) was investigated in single and binary systems. Batch kinetic studies were carried out as a function of pH, temperature, biomass amount, and dye concentration to determine the decolorization efficiency of biosorbent. In single system, the biosorption capacities of P. M. reached 166 and 76.92 mg/g for CV and BR46, respectively. A comparison of kinetic models applied to the adsorption of basic dyes onto P. Mutilus was evaluated for the pseudosecondorder and intraparticle diffusion kinetics models. The experimental data fitted very well the pseudosecondorder kinetic model, whereas diffusion is not only the ratecontrolling step. The thermodynamic study indicates that the adsorption of dyes is spontaneous and endothermic process. In binary system, the biosorption capacities of P. Mutilus for both dyes decreased significantly compared to that in single system. Competitive coefficients calculated on a concentration basis using SheindorfRebhunSheintuch (SRS) equation were useful for describing the degree of competitive interaction in P. M.
1. Introduction
The release of synthetic dyestuffs into the aquatic ecosystems through the wastewater of textile industries is a global environmental concern [1]. The immense volume of aromatic structures present in dye molecules makes wastewater treatment through a biological process ineffective. As a result, the removal of dyes from wastewater is important for the environmental protection and human health. To avoid the ecological health problems, many methods were developed for removing dyes.
Biosorption is one of the popular and attractive technologies for the removal of color contaminants from aqueous effluents. Biosorption is a process that utilizes inexpensive dead biomass to sequester inorganic [2–9] and organic ions [10–13]. It has retained a great attention for the last decades as an alternative to conventional processes (such as membrane processes, ion exchange, etc.) for the removal of dye from aqueous solutions, therefore, a wide variety of microorganisms including bacteria, fungi, and yeasts are used for the biosorption of a broad range of dyes [14–16]. Much of the work on the biosorption of dyes by various kinds of biosorbents has focused on the uptake of single dyes [17–21] but fewer studies were conducted to investigate adsorption behavior of biosorbent for dyes in multicomponent systems. In practice, most industrial effluents contain a mixture of several dyes, thus, it is necessary to study the simultaneous biosorption of two or more dyes from aqueous solutions.
A variety of biomasses is used by the SAIDAL antibiotic complex at Medea, (Algeria) among which the basidomycete Pleurotus mutilus from which an antibiotic (pleuromutilin) for veterinary use, is isolated. Our previous study [22] explored the feasibility of utilizing Pleurotus mutilus as biosorbent for Basic Blue 41 removal from aqueous solution in single system. At present, this study aims: (i) to investigate the biosorption of basic violet 3 and Basic Red 46, currently used in Algeria onto dead Pleurotus mutilus in single and bicomponent systems in different concentration ratios, and to (ii) model the experimental results using the SRS equation. In doing so, the biosorption of basic dyes on this waste material from aqueous solutions was evaluated in batch experiments. The adsorption isotherms, kinetics, and temperature effect were studied.
2. Materials and Methods
2.1. Dyes and Analysis
The sorbates used in the experiments were Basic red 46 (BR46) and Crystal violet (CV) or genetian violet which are used in textile processing Industry of Algier (Algeria). These dyes are suitable for dyeing of acrylic substrates, some polyamide and polyester types, viscose, cotton, and wool. CV is also used as an active ingredient in Gram’s stain and as a bacteriostatic agent in animal husbandry and veterinary practice [23, 24]. The chemical structures of these dyes are shown in Figure S1 (Supplementary data available online at doi:10.1155/2013/965041). A stock of aqueous solution of the dyes was prepared in deionised water in the concentration of 1000 mg/L.
Batch kinetic biosorption studies were conducted in a temperaturecontrolled stirrer using 1000 mL of adsorbate solution. Samples were withdrawn at suitable intervals and were separated from the sorbent by centrifugation for 20 min at 5000 rpm and then analyzed using a UV spectrophotometer.
For the single system, the dye concentrations were determinated by measuring the absorbance at wavelength of maximum absorbance of CV (594 nm), and BR46 (530 nm) and then calculated according to the calibration curves, respectively.
For components of a binary system, the concentrations of each dye in mixture solutions can be computed using (1) [29] where 1 and 2 represent components in a binary system. , and are the calibration constants for components 1 and 2 at and , respectively, and are the optical densities at and , respectively.
2.2. Biomass Preparation
Waste P. mutilus biomass was collected at the SAIDAL antibiotic production complex at Medea (Algeria). The collected samples were washed repeatedly with deionised water to remove extraneous materials and salts and dried for 24 h at 50°C in an oven. The dried biomass was ground manually in a mortar and sieved into particle size ranges: 110–215 μm.
2.3. Sorption Isotherms
Adsorption experiments were carried out by adding a fixed amount of adsorbent (0.6 and 0.7 g/L for CV and BR46, resp.) to a series of conical flasks filled with 100 mL diluted solutions (10–120 mg/L). The conical flasks were placed in a thermostatic shaker at 10, 15, 20, and 30° at pH 7.5. The removal efficiency (E) of dye on P. M. and sorption capacity, (q) were calculated from (2):
3. Results and Discussion
3.1. Biosorption in Single Dye
3.1.1. Effect of Initial Dye Concentration and Contact Time
Experiments were undertaken to study the effect of varying initial concentration (10–120 mg/L) at 30°C on dye removal by dead P. mutilus. Figures 1 and 2 represent the effect of initial dye concentration on the biosorption on P. M. for CV and BR46 at pH 7.5 and 8.1, respectively. The rate of dye uptake is found to be very rapid during the initial 5 min, and thereafter, the rate of dye ions uptake decreases considerably. No significant change in dye uptake is observed after about 25 min. Initially, the surface of P. M. was vacant, and the biosorption rate was fast.
After a lapse of some time, the remaining vacant surface sites are difficult to be occupied due to repulsive forces between the adsorbate on the P. M. surface and in the bulk phase. An increase in initial dye concentration led to an increase in the biosorption capacity of dye on P. M., and longer time was required to reach equilibrium. The data showed that as the initial concentration of the dye increased from 10 to 120 mg/L the biosorption capacity increased from 10.76 to 49.89 mg/L for BR46 and from 15.94 to 134.53 mg/L for CV. This showed that biosorption capacity was highly concentration dependent. Also, it was found that the values of for CV were greater than that for BR46 at any .
3.1.2. Effect of Biosorbent Concentration
The sorbent concentration is another factor that influences the sorption equilibrium. In order to examine the effect of the sorbent dosage on the removal efficiency dye, adsorption experiments were set up with various amounts of dried P. M. (0.2, 0.4, 0.6, 0.7, and 0.8 g/L) and dye concentrations (10 mg/L). During the adsorption, the temperature of system was kept constant at 30°C. The effect of sorbent dosages on the percentage removal of both dyes is shown in Figure 3.
It followed the predicted pattern of increasing percentage sorption as the dosage was increased and reaches a saturation level at high doses, 0.6 and 0.7 g/L of biosorbent were observed to be the upper limit for the removal of CV and BR46 respectively. This is probably because of the resistance to mass transfer of dye from bulk liquid to the surface of the solid, which becomes important at highadsorbent loading in the conical flask in which the experiment was conducted.
3.1.3. Effect of pH
Adsorption equilibrium studies were conducted at initial dye concentration of 50 mg/L by adding a fixed amount of adsorbent (0.6 g and 0.7 g for CV and BR46, resp.) into a series of conical flasks each filled with 1000 mL of dye solution. Batch sorption experiments were performed at various aqueous phase pH (4.7, 5.8, 6.5, 7.5, 8.1, and 8.6). During the adsorption, the temperature of system was kept constant at 30°C.
The pH of the dye solution plays an important role in the whole biosorption process and particularly in the adsorption capacity, influencing the surface charge of the biosorbent, the degree of ionization of the dye present in the solution and the dissociation of functional groups on the active sites of biosorbent, and the solution dye chemistries. The fungal cell wall contains a high amount of polysaccharides and some of them are associated with proteins and other components. These macromolecules have several functional groups, and the biosorption phenomenon depends on the protonation or unprotonation of these functional groups on the surface of the cell wall [30]. Figure 4 indicates the removal of dye by dead P. mutilus at various initial pH values ranging from 4.7 to 8.6 in 10 mg/L of dye solution. Evidently pH significantly affected the extent of adsorption of dye.
The results of percentage of dye removal versus equilibrium pH increased with increasing pH. Further the variation in pH (7.5–8.6) did not cause any disintegration of the biosorbent, and the extent of adsorption was observed to become nearly constant at pH values greater than 7.5. As the initial pH of the dye solution decreased, the number of negatively charged adsorbent sites decreased and positively charged sites increased which did not favor the adsorption of positively charged dye cation due to electrostatic repulsion [31].
The lower uptake of dye adsorption at acidic pH is also due to the presence of excess of H^{+} ions competing with dye cation for the adsorption sites. Therefore, ionic exchange, electrostatic repulsion, structural properties of the dye and pleurotus Mutilus biomass could play a vital role in dye adsorption processes using fungal biomass.
All the two dyes found to follow the similar trend with low percentage of removal at low pH (pH = 4.7). At pH 7.5 and 8.1, the maximum adsorption onto P. M. for 10 mg/L initial dye concentration was 96.48% for CV and 69.4% for BR46 respectively.
There were many factors responsible for this difference in dye uptake, such as their structure, molecular size, and functional groups.
3.1.4. Effect of Temperature
The effect of temperature on BR46 and CV uptake capacity () of P. M. was studied. From Figures 5 and 6, it was observed that the BR46 and CV uptake capacity () of P. M.increased with increasing temperature up to 30°C, indicating that the adsorption of BR46 and CV ions was favored at higher temperatures. Increase of with increasing temperature might be due to the increase of kinetic energy of the dye in solution, which increased the collision rate with the surface of the adsorbent [32]. Also the increase in adsorption with temperature may be attributed to either increase in the number of active surface sites available for adsorption on the P. M.or the decrease in the thickness of the boundary layer surrounding the P. M. It means that the sorption of BR46 and CV is endothermic.
3.2. Modelling of the Sorption Equilibrium Depending Temperature
In order to optimize the design of a sorption system to remove dyes from aqueous solutions, it is important to establish the most appropriate correlation for the equilibrium curves. The isotherms data were analyzed using two of the most commonly used equilibrium models, Langmuir [33] and Freundlich [34]. The mathematical expressions are given by (3), respectively, as follows: where (mg/g), is the maximum amount of sorbate per unit weight of adsorbent, to form a complete monolayer on the surface bound at high and b (L/mg) is a constant related to the affinity of the binding sites. and can be determined from the linear plot of versus . and are the Freundlich constants characteristics of the system (dimensionless; ()). Equation (6) can be linearized in logarithmic form and the Freundlich constants can then be determined.
The effects of temperature on biosorption were studied at initial dye concentration (10 mg/L), fixed initial pH (7.5 and 8.1 for CV and BR46, resp.) and biomass concentration (0.6 and 0.7 g/L for CV and BR46, resp.) for 90 min. Adsorption isotherms in singlecomponent systems are presented in Figures 7, 8, 9, and 10. With increasing temperature from 10 to 30°C, increases from 71.43 to 166.66 mg/g and from 62.5 to 76.92 mg/g for CV and BR46, respectively. The bestfit values of the model parameters estimated from (3) and (6) by linear regression analyses are listed in Table 1. Also shown are the correlation coefficients (), which provide measure of model fitness. A comparison of the experimental isotherms with the adsorption isotherm models showed that the Langmuir equation represented the poorest fit of experimental data as compared to the Freundlich isotherm. The equilibrium adsorption data for CV and BR46 biosorption on P. M. can be represented appropriately by Freundlich model in the studied concentration and temperature range. It is found from Table 1 that the P. M. shows greater heterogeneity for CV than that for BR46 ions. Since ; both the dye ions are favourably adsorbed by P. M. The values indicate the higher uptake of CV ( = 22.35 mg g^{−1} at T = 30°C) than that of BR46 ions ( = 10.91 mg g^{−1} at T = 30°C) by P. M.

3.3. Biosorption Kinetics
3.3.1. Kinetic Models
The studies of adsorption equilibrium are important in determining the effectiveness of adsorption; however, it is also necessary to identify the types of adsorption mechanism in a given system.
The kinetic of biosorption of CV and BR46 had been modeled using (4)–(7) given below. Pseudosecond order see [25].Intraparticle diffusion see [26, 27].Pore diffusion coefficient see [28], where and are adsorption capacities (mg/g) at any time, t (min) and equilibrium, respectively; (g·/mg/min), h (mg/g.min), (g/mg·min^{0.5}), Di (cm^{2}/s), _{1/2}(s) and r(cm), the rate constant of pseudosecondorder adsorption, initial adsorption rate, intraparticle diffusion rate constants, diffusion coefficient, time for halfadsorption of dye, and the average radius of the adsorbent particle, respectively. The value of r (average radius) was calculated as 67 × 10^{−4} cm. In these calculations, it has been assumed that the solid phase consists of spherical particles.
Pseudo Second Order. The application of the linear form of pseudosecondorder kinetic model on our experimental results is presented in Figures (S2–S5) (Supplementary data). Both constants and were calculated from the intercept and slope of the line obtained by plotting t/ versus . It can be seen from Table 2 that the kinetics of BR46 and CV adsorption onto P. M. follow this model with correlation coefficients higher than 0.999 and the equilibrium adsorption capacity, , increases as the initial dye concentration, , increases from 10 to 120 mg/L. Further, it was found that the variations of the rate constant, , seem to have a decreasing trend with increasing initial dye concentration for both dyes. The variations of t/ versus at various temperatures of the dye solution under the initial concentration of 10 mg/L still confirmed to fit the pseudosecondorder model. The values of model parameters (, h,and ) for different temperatures have been calculated from (4) and (5), and the results are given in Table 2, revealing that the fitted adsorption capacity of both dyes on P. M. at equilibrium, , increased with increasing temperature. Thus, on increasing the solution temperature from 10 to 30°C, the value of increased from 13.89 to 16.13 mg/g and from 11.36 to 12.05 mg/g for CV and BR46, respectively Also, from Table 2, it was noticed that the initial adsorption rate, h, increases with increasing temperature. These results imply that chemisorption mechanism may play an important role.

Intraparticle Diffusion Model. The pseudosecondorder model could not identify the diffusion mechanism, and the kinetic results were then analyzed by using the intraparticle diffusion model. In the model developed by Weber and Morris [26], McKay and Poots [27], the initial rate of intraparticle diffusion is calculated by linearization of (6).
According to this model, the plot of uptake, , versus the square root of time (_{1/2}) should be linear if intraparticle diffusion is involved in the adsorption process and if these lines pass through the origin then intraparticle diffusion is the ratecontrolling step [35]. When the plots do not pass through the origin, this is indicative of some degree of boundary layer control and this further shows that the intraparticle diffusion is not the only ratelimiting step, but also other kinetic models may control the rate of adsorption, all of which may be operating simultaneously [36]. From Figures (S6–S9), it can be observed that the straight lines did not pass through the origin and this further indicates that the intraparticle diffusion is not the only ratecontrolling step. The intraparticle diffusion, , values were obtained from the slope of the straight line portions of plot of versus _{1/2} for various dye concentrations and solutions temperature (Figures S6–S9). The correlation coefficients () of the intraparticle diffusion model are given in Table 2; they are lower than that of the pseudosecondorder kinetic model. This suggests that the BR46 and CV biosorption process appears to be controlled by the chemical reaction. It was observed that intraparticle rate constant values () increased with initial dye concentration. The observed increase in values with increasing initial dye concentration can be explained by the growing effect of driving force resulted in reducing the diffusion of dye in the boundary layer and enhancing the diffusion in the solid. Also, as shown in Table 2, increasing the temperature promoted the pore diffusion in sorbent particles and resulted in an enhancement in the intraparticle diffusion rate [37]. The corresponding values of intraparticle diffusion rate constant, , for the various concentrations of CV and BR46 (10–120 mg/L) varied from 0.522 to 4.31 mg/g min^{1/2} and from 0.453 to 3.35 mg/g min^{1/2}, respectively (Table 2). It is found from Table 2 that the rate parameters of CV are greatly bigger than BR46 and that may be due to the difference in the molecule structures of both dyes.
Diffusion Coefficient. The diffusion coefficients for the intraparticle transport of CV and BR46 within the pores of P. M. particles have been calculated at different initial dye concentrations and temperatures by using (7). The values of diffusion coefficient for biosorption of CV and BR46 increase from 2.81 10^{−8} to 3.29 10^{−8 }cm^{2}/s and from 2.03 10^{−8} to 2.54 10^{−8} with change in temperature from 10 to 30°C. Based on Table 2, the results are comparable to those published in literature.
3.3.2. Thermodynamic Study
The thermodynamic parameters of the adsorption process were determined from the experimental data obtained using the following equations [38]: where is the distribution coefficient for the adsorption, and are the change of entropy, enthalpy and the Gibbs energy, T is the absolute temperature, R is the gas constant.
Figure 11 shows a linear relationship between the logarithm of rate constant and the reciprocal of temperature. The values of H°and S° were determined from the slope and intercept of the plot of ln versus 1/T (Figure 11). The H° and S° values are positive. Based on the results of intraparticle model, this study proposed that the adsorption involved intraparticle diffusion that was not the only ratecontrolling step and the other kinetic models might control the adsorption rate [39]. The positive value of entropy change (S°) reflects good affinity of both dyes towards the sorbent and the increasing randomness at the solidsolution interface during the adsorption process [37].
The value decreases from −5.10 to −9.62 kJ/mol and from −2.79 to −5.39 kJ/mol for CV and BR46, respectively, when the temperature increases from 10 to 30°C (Table 3), suggesting the more adsorbable of both dyes with increasing temperature. It was found from the values estimated for ° that the spontaneity of adsorption of CV was greater than that of BR46. The values of ° estimated for the adsorption of CV and BR46 were positive (Table 3). Thus, the adsorption reactions were endothermic, and that for the CV was greater than the BR46. The value of ° estimated was >40 kJ·/mol for CV (59.60 Kj/mol) biosorption with P. M, indicating chemisorption nature of the reactions.

3.4. Biosorption in Binary Systems
3.4.1. Biosorption Selectivity in Binary Systems
Figure 12 shows a comparison of CV and BR46 adsorption on P. M. in binary systems at 0.6 , 30°C and initial dye concentration of 10 . It is seen that CV and BR46 adsorption is reduced in binary system, which suggests a competitive adsorption. During the adsorption process, CV and BR46 adsorption are gradually increased and reached an equilibrium adsorption of 14 and 9,2 at 80 min, respectively, and compared with the adsorption rate in single system, CV and BR46 adsorption in binary system is slightly slower. The kinetics of CV and BR46 competitive adsorption in binary system was also studied using the above two models. Figures S10 and S11 illustrate the comparative results, and Table 2 lists the adsorption equilibrium and rate constants.
From Table 2, it is seen that the secondorder kinetic shows close approximation to the experimental data, and the regression coefficients are much closer to each other. Based on the adsorption equilibrium, the individual adsorption of CV and BR46 is reduced by 15 and 26%, respectively. However, the total adsorption of natural P. M. is higher than that of any CV and BR46 equilibrium adsorption in singlecomponent system. Table 2 shows that the diffusion coefficient is reduced by 24 and 74% for CV and BR46, respectively. The higher adsorption rate of CV than BR46 in binary system is due to the difference in structure and molecular size.
The relative adsorptions of CV and BR46 on P. M. in binary system were calculated from (9) [39] where and are the amount of adsorption of specific adsorbate in binary system and single system at time t, respectively. Also for the binary system, selectivity of adsorption on P. M. is defined as Figure 13 shows the variation of relative adsorption of CV and BR46 and the adsorption selectivity in binary system with time. It is seen that BR46 relative adsorption is gradually increased. This suggests that the presence of CV in solution does significantly influence the dynamic uptake process of BR46. The selectivity of adsorption shows a decreasing trend and approaches a constant value of 1.
This suggests that P. M. has a higher affinity to CV biosorption in binary system, and the biosorption favors to the CV at initial stage. When the adsorption approaches the equilibrium, the adsorption selectivity will be the same for CV and BR46, the adsorption results suggest that the presence of CV has significant influence on BR46 adsorption capacity, while CV adsorption including capacity and kinetics is affected by the presence of BR46.
3.4.2. Effect of Initial Dye Concentration on the Biosorption of BR46 and CV in Binary System
To investigate the effect of initial dye concentration on binary biosorption, experiments were divided into two stages. In the first part, was changed from 10 to 30 mg/L while was at 10, 15, and 20 mg/L at pH value of 7.5 and biosorbent dosage of 0.6 g/L. In the second part, was changed and was held at the same concentration range.
Biosorption Isotherm Models and Competitive Analysis in Binary Systems. Figure 14 shows the biosorption isotherm of BR46 by P. M. with varied concentration of CV. It is seen that the adsorption capacity of BR46 decreased with increasing concentration of CV. The biosorption of CV also reduced in the presence of BR46 (Figure 15); however, the degree of suppression was less than that of CV in BR46.
Various researchers have developed models in binary systems. In this study, the model chosen refers to theories developed by Sheindrof at al. (1981) derived a Freundlichtype multicomponent adsorption isotherm. The sheindorfRebhunSheintuch (SRS) equation was based on assumption that there is an exponential distribution of adsorption energies available for each solute [40]. A general SRS equation can be written as where is the amount of solute I adsorbed per unit weight of adsorbent in the presence of solute j. is the singlecomponent Freundlich constant for solute i. is the Freundlich exponential term for solute i. and are the equilibrium concentrations of solute I and j, respectively and is the competitive coefficient. The bicomponent isotherm can be written [41, 42] as followas: In order to represent the batch isothermal data, the following linear forms of the SRS equation for binary solute system are used: with If both concentrations vary during the experiments, then plotting versus yields a straight lineofunity slope and the competition coefficients ( and ) could be determined from the intercept (Figures 16(a) and 16(b)). The values of competitive coefficients and are 0.151 and 6.13, respectively. The magnitude of CV competition on BR46 adsorption by P. M. was significant. Parametric value of competition coefficient for BR46 was 40 times higher than that observed for CV. The correlation coefficients () were found to be in the range of 0.951–0.983, which indicate a good relationship with the experimental data.
(a)
(b)
4. Conclusion
The present study shows that the P. Mutilus is an effective biosorbent for the removal of Crystal violet (CV) and Basic Red 46 (BR46) ions from aqueous solution. Maximum biosorption for CV and BR46 was found to occur at pH 7.5 and 8.1, respectively. The adsorption uptake of both dyes was very fast during the initial sorption period of about 5 min. Large adsorption capacity is registered for CV ( =166.66 mg/g), confirming its higher affinity for the biosorbent.
In single system, the Freundlich isotherm model yielded the concentration range. Batch studies show that a simple model of pseudosecondorder kinetic equation can adequately predict the adsorption of BR46 and CV on dead P. mutilus and the values of , h, and all increased with the temperature, suggesting that increasing the temperature increased the adsorption capacity and the adsorption rate. These results imply that chemisorption mechanism may play an important role for the adsorption of BR46 and CV on the dead P. mutilus. Also, it was observed that the intraparticle diffusion was not the only rate controlling step. The kinetic parameter values obtained (Di) are of the same order of magnitude as those measured by other authors [43]. The thermodynamic study indicates that the adsorption of CV and BR46 onto P. mutilus is spontaneous and endothermic process.
In this study, the ability of P. mutilus to bind two basic dyes, BR46 and CV simultaneously in solution was investigated and the results were compared. The combined effects of two dyes on a biosorbent may be antagonistic. Since the initial biosorption rates and equilibrium dye removal decreased with increasing concentration of the other dye. In the binary dye mixtures, the affinity of the P. Mutilis for CV was greater than that for BR46. The proposed SRS equation is successfully employed to describe competitive adsorption data in the range of concentrations studied.
Supplementary Materials
Biosorption behavior of Basic Red 46 and Violet 3 by dead pleurotus mutilus from single and multicomponent systems
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Copyright © 2013 N. Yeddou Mezenner 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.