- Citado por SciELO
versión On-line ISSN 0717-3458
Electron. J. Biotechnol. v.9 n.2 Valparaíso abr. 2006
Biosorption of uranium from aqueous solutions by nonliving biomass of marinealgae Cystoseira indica
Mohammad Hassan Khani*
Ali Reza Keshtkar
Mohammad Firouz Zarea
Financial support: Jaber Ibn Hayan research laboratories, Atomic Energy Organization of Iran.
Keywords: biosorption,Cystoseira indica, equilibrium, kinetic, marine algae, uranium.
Biosorption of heavy metals can be an effective process for the removal and recovery of heavy metal ions from aqueous solutions. In this paper uranium biosorption by protonated, Ca-pretreated and non-pretreated Cystoseira indica algae biomass was investigated in a batch system. The results of the kinetic studies showed that the sorption of uranium on protonated and non-pretreated biomass followed pseudo-second order kinetics. The effect of pH on the equilibrium uranium sorption capacity of Cystoseira indica exhibited that highest uptake occurred at pH 4 at a solution with 350 mg/l uranium concentration. At various initial uranium concentrations from 50 to 1000 mg/l, batch sorption equilibrium at 30ºC was reached within 3 hrs and the sorption isotherms were interpreted in terms of the Langmuir and Freundlich models. Equilibrium data fitted very well to Langmuir model for all studied forms of Cystoseira indica algae. The Freundlich isotherm cannot fit as well as the Langmuir model the equilibrium data of protonated and non-pretreated Cystoseira indica algae. The maximum uranium adsorption capacity on the Ca-pretreated, protonated and non-pretreated Cystoseira indica algae predicted by Langmuir isotherm at pH 4 and 30ºC was 454.5, 322.58 and 224.67 mg/g respectively.
Toxic heavy metal contamination of industrial water is a significant universal problem. They accumulate in living tissues throughout the food chain which has humans at its top. These toxic metals can cause accumulative poisoning, cancer and brain damage when found above the tolerance levels. Uranium is one of the most seriously threatening heavy metals because of its high toxicity and some radioactivity. Excessive amounts of uranium have found their ways into the environment through the activities associated with the nuclear industry. Uranium contamination poses a threat in some surface and groundwaters (Laul, 1992). There is a need for controlling the heavy metal especially uranium emissions into theenvironment. Conventional methods for removing heavy metals from industrial effluents (e.g. precipitation and sludge separation, chemical oxidation or reduction, ion exchange, reverse osmosis, membrane separation, electrochemical treatment and evaporation) are often ineffective and costly when applied to dilute and very dilute effluents (Aksu, 1998). Recently, biological removal processes has been attracting considerable attention for removing heavy metals from aqueous wastes and screening for microorganisms having higher potential for removing heavy metals from wastes has been promising so far (Volesky and Holan, 1995; Kratochvil et al. 1997; Kratochvil and Volesky, 1998; Pagnanelli et al. 2001; Singh et al. 2001; Kaewsarn, 2002; Nuhoglu et al. 2002; Pessoa de Franca et al. 2002; Tien, 2002; Axtell et al. 2003; Padmavathy et al. 2003). Microbial removal of heavy metals offers the advantages of low operating cost, minimizing secondary problems with metal-bearing sludge and high efficiency in detoxifying very dilute effluents. Metal uptake by microorganisms can occur actively (bioaccumulation) and/or passively (biosorption) (Ehrlich, 1997; Nies, 1999). Feasibility studies for large-scale applications demonstrated that the biosorptive processes are more applicable than the bio-accumulative processes because living systems often require the addition of nutrients and hence increase biological oxygen demand (BOD) or chemical oxygen demand (COD) in the effluent, maintenance of a healthy microbial population is difficult due to metal toxicity and other unsuitable environmental factors and mathematical modelling of an undefined system is difficult (Sternberg and Dorn, 2002; Chandra Sekhar et al. 2003).
Although the fact that marine algae are capable of biosorbing radionuclides such as radium, thorium and uranium has been known for a long time (Edgington et al. 1970), the biosorption of uranium by Cystoseira indica algae, a brown algae biomass which found vastly in Iran, has not been investigated. The aim of this paper is to determine the effect of the basic parameters such as pH, contact time and initial metal concentration on the uranium biosorption by Cystoseira indica algae and to compare between sorption on protonated, Ca-pretreated and non-pretreated algae biomass in a batch system.
Cystoseira indica, a brown alga, obtained from Persian gulf on the coast of Qeshm, Iran was extensively washed with distilled water and sun-dried on the beach and in an oven at 50ºC overnight. Dried biomass was ground in a laboratory blender and sorted by sieving using the standard test sieves. The batch of biomass with particle size 1.0-1.25 mm was selected for subsequent pre-treatment. Pre-treatment of the biomass was carried out as follows: A sample of 10 g of biomass was treated with 0.1 M CaCl2 solution (1000 ml) for 12 hrs under slow stirring. The solution pH was kept constant at pH 5.0 by using 0.01 M HCl or 0.01 M NaOH solution if deviations were observed. The calcium-treated biomass was washed several times with deionised water to remove excess calcium from the biomass. Also protonation of the biomass was carried out by using 0.1 N HCl (10 g biomass/L). After 12 hrs of contacting with acid, the biomass was rinsed with deionised water in the same volume many times until a stable wash solution pH 5.0 was reached. The Ca-pretreated and protonated biomasses were then dried in an oven at 50ºC overnight. The prepared biomasses was stored for later uses.
Uranium solutions were prepared by diluting 1000 mg uranium/lstock solution which was obtained by dissolving a weighed quantity of uranium in nitrate salt form, UO2(NO3)2.6H2O, analytical grade. Diluted solutions were prepared at room temperature in distilled and deionised water.
Dissolved uranium concentrations in solution were assessed by an inductively coupled plasma atomic emission spectrophotometer (ICP-AES, Thermo Jarrel Ash, Model TraceScan). The ICP analyses were conducted at wavelength of 409.014 nm.
In order to determine the contact time required for the sorption equilibrium experiments, the sorption dynamics experiments were conducted first. On a shaker incubator 0.2 gram of biomass was mixed with 100 mL of 350 mgU/l UO2(NO3)2 solution at 150 rpm and 30ºC. A series of 0.5 mL samples of solution were removed from the vessel at predefined time intervals. After appropriate dilution, the samples were analyzed by the ICP-AES for metal concentrations. After the equilibrium time was determined, a series of uranium nitrate solution with different concentrations (100 mL) were mixed with 0.2 g biomass and the sorption equilibrium experiments were conducted in the same way. The suspensions were brought to the desired pH by adding 0.05 N HCl or NaOH during the sorption process and the volume of HCl or NaOH added was recorded. After 3 hrs of contact (according to the preliminary sorption dynamics tests), equilibrium was reached and the solution was filtered. The supernatant was diluted for uranium concentration analyses by the ICP-AES.
The amount of uranium ions adsorbed per unit of empty sorbent was obtained by using the following expression:
q = (Ci- Ce) x V/M 
where q is the amount of uranium adsorbed onto the unit mass of the adsorbent (mg/g), Ci and Ce are the concentrations of the metal ions before and after biosorption (mg/l), V is the volume of the aqueous phase (l), and M is the amount of the adsorbent (g).
All sorption experiments were carried out in triplicate. Values used in calculations were the arithmetic averages of the experimental data.
Generally speaking, the uptake of heavy metal ions by microorganisms has often been observed to occur in two stages; an initial rapid uptake due to surface adsorption on the cell walls and a subsequent slow uptake due to membrane transport of the metal ions on the cytoplasm of the cells. Uranium biosorption by Cystoseira indica algae exhibited the same behaviour (Figure 1). As can be seen from Figure 1, the uranium ions adsorption rate by Cystoseira indica algae is high at the beginning but plateau values are reached in about 3 hrs. This result is typical for biosorption of metals involving no energy-mediated reactions, where metal removed from solution is due to purely physico/chemical interactions between the biomass and metal in solution. The fast dynamic behaviour of uranium uptake suggests a minimal residence time (or contact time) for a process based on these preparations. Figure 1 also shows that a larger amount of uranium removed by protonated biomass in the first 30 min of contact time so that the initial solution rate for protonated and non-pretreated biomass is 11.88 and 9.76 mg/g x min, respectively. The rapid kinetics has significant practical importance as it will facilitate smaller reactor volumes ensuring efficiency and economy.
In order to modelling the sorption rate of uranium on Cystoseira indica algae suspension in a well-agitated batch system, pseudo-second order rate equation was applied (Ho and Mckay, 1999). Assuming the sorption capacity of uranium on the biomass is proportional to the number of active sites occupied on the sorbent, then the pseudo-second order equation is given by:
t = 0 , qt = 0 
Where k is the equilibrium rate constant of pseudo-second order sorption kinetics (g/mg x min), qt the amount of sorbate on sorbent at time t (mg/g), and qeq the equilibrium uptake (mg/g). Equation  can be integrated and rearranged in to:
Figure 2 shows a plot of t/qt versus t, for the sorption of uranium on the biomass at 350 mg/l initial concentration and 30ºC. The values of the parameters, qeq and k are calculated from the slops and the intercepts of the straight lines shown in Figure 2 and tabulated in Table 1. The values of the theoretical qeq for both sorbents are in good agreement with those found experimentally. Also the correlation coefficients for both sorbents are greater than 0.999. These results indicate that the sorption of uranium on the sorbents investigated in this study follows a pseudo-second order kinetics.
Earlier studies on heavy metal biosorption have shows that pH is an important parameter effecting the biosorption process. The effect of initial pH on uranium ion biosorption capacity of Cystoseira indica algae was studied at 350 mg/l initial uranium concentration and at 30ºC. As seen from Figure 3 the biosorption of uranium for both protonated and non-pretreated algae increased with pH up to 4 and then declined with further increase in pH. The maximum equilibrium uptake value was found at pH 4.
The metal ion binding in biosorption could be attributed to several mechanisms such as ion exchange, complexation, electrostatic attraction and micro precipitation. For algae biomass, ion exchange has been considered as a main mechanism responsible for metal sequestering (Crist et al. 1988). The ion exchange mechanism for uranyl ions binding to the biomass is complicated by the fact that the uranium cation UO22+ is hydrolyzed in aqueous solutions within the range of the sorption system pH. Portioning of the hydrolysed uranium species depends on the solution pH and on the total uranium concentration in the solution. In the range of acidic to near neutral pH values, four major hydrolysed complex ions, UO22+, (UO2)2(OH)22+, UO2OH+, (UO2)3(OH)5+ and a dissolved solid schoepite (4UO3.H2O), a hydrous uranium oxide, exist in the solution (Baes and Mesmer, 1976). The hydrolysis equilibrium constants are pK = 5.8 for UO2OH+, pK = 5.62 for (UO2)2(OH)22+ and pK = 15.63 for (UO2)3(OH)5+ (Baes and Mesmer, 1976). At pH 4 and uranium concentration 350 mg/l all hydrolyzed ions exist in the solution.
According to Collins and Stotzky (Collins and Stotzky, 1992), the hydrolyzed species can obviously be sorbed better than the free hydrated ions. Particularly the monovalent, compared with the divalent hydrolyzed ions, have even higher affinity to the biomass in ion exchange with protons because they could replace single protons on separate binding sites in the biomass.
The percentage of UO22+ in the solution increases with decreasing the pH of system. The lower pH suppresses the enhancement of uranium biosorption occurring normally because of the hydrolyzed ions. When the pH becomes low enough, for example at pH 2.6, the divalent free UO22+ becomes the dominant ion form in the solution for a wide uranium concentration range from 0.3 to 1000 mg/l. In addition, since the UO22+ is divalent, it can only replace two protons on the adjacent binding sites of the biomass but cannot react with those sites which are farther apart from each other. In other words, at low pH some binding sites are not available to the divalent UO22+. On the other hand, the non-ion dissolved solid schoepite starts appearing in the solution when the pH is too high. The uranium sorption may be hindered by the decrease in ion concentration in this situation.
The initial concentration provides an important driving force to overcome all mass transfer resistance of uranium between the aqueous and solid phases. Hence a higher initial concentration of uranium will enhance the adsorption process. Such an effect is clearly demonstrated in Figure 4 where the experimental data of qeq versus initial concentration of uranium have been illustrated for protonated, non-pretreated and Ca-pretreated algae biomass at pH 4 and 30ºC. As can be seen from Figure 4, at low initial uranium concentration, the equilibrium sorption capacity of the all sorbents is directly proportional to the initial uranium concentration in the solution and in the high initial uranium concentration range, the equilibrium sorption capacity of the all forms of the algae biomass go to a constant value. Also the results show that the pre-treatment of the algae biomass considerably influences the equilibrium sorption capacity of the sorbent. Figure 4 shows that the Ca-pretreated Cystoseira indica algae is better than protonated and non-pretreated Cystoseira indica algae and the protonated algae is better than non-pretreated algae in the all range of initial uranium concentration. The pre-treatment process enhances biomass surface ions. Since the biosorption of uranium is largely ion exchange process, the processed samples of the biomass have higher sorption capacity in comparison with raw. Also the Ca-treatment is more effective than the protonation, because the Ca2+ ions are divalent and can replace with two monovalent uranium ions. Proton, nevertheless, can replace with only one. In this paper, the characteristics of the surface groups on Cystoseira indica algae were not determined. Acidic sites, carboxylic and phosphatic types or amino-type sites are more likely to take part in ion exchange. It is supposed to be determined by potentiometric titration.
The equilibrium established between adsorbed metal ion on the biosorbent and unabsorbed metal ion in solution can be represented by adsorption isotherms. Two isotherm equations have been tested in the present study, namely, the Langmuir, Freundlich (Aksu, 1998; Gin et al. 2002; Nuhoglu et al. 2002; Donat et al. 2005; Kumar Meena et al. 2005; Xiangliang et al. 2005).
The Langmuir equation which is valid for monolayer sorption onto a surface with a finite number of identical sites which are homogeneously distributed over the sorbent surface is given by Equation .
where qeq is the amount of metal ion bound to per gram of dried biomass at equilibrium and Ceq is the residual (equilibrium) metal ion concentration left in solution after binding, respectively. Q0 is the maximum amount of metal ion per unit weight of sorbent to form a complete monolayer on the surface bound at high Ceq, and b is a constant related to the affinity of the binding sites. Q0 and b can be determined from Ceq/qeq versus Ceq plot which gives a straight line of slope 1/Q0 and intercept 1/bQ0.
The empirical Freundlich equation based on sorption on a heterogeneous surface is given by Equation .
where kF and n are the Freundlich constants related to the sorption capacity and sorption intensity of the sorbent, respectively. Equation  can be linearized in logarithmic form and Freundlich constants can be determined. Both models were developed for a single-layer adsorption, but the Freundlich isotherm provides no information on the monolayer adsorption capacity, in contrast to the Langmuir model.
The Langmuir and Freundlich adsorption parameters with the correlation coefficients (R2) for the biosorption of uranium on the biosorbent are listed in Table 2. High regression correlation coefficients (>0.9887) for the Langmuir model show that the adsorption process of uranium by Cystoseira indica algae can be well defined by this model. As can be seen from Table 2, the Freundlich isotherm is only suitable for describing the biosorption equilibrium of uranium by Ca-pretreated and non-pretreated algae and it can not fit reasonably the biosorption equilibrium of uranium by protonated algae. While the Freundlich model does not describe the saturation behaviour of the biosorbent, Q0, the Langmuir constant represents the monolayer saturation of equilibrium. The maximum capacity, Q0 determined from the Langmuir isotherm defines the total capacity of the biosorbent for uranium. From Table 2 the maximum adsorption capacity for uranium on the Ca-pretreated, protonated and non-pretreated Cystoseira indica algae is 454.5, 322.58 and 224.67 mg/g, respectively. The Langmuir isotherm with the experimental data of qeq versus Ceq are shown in Figure 5.
The study indicated that the biomass of the Cystoseira indica algae particularly its Ca-pretreated form could be used as an efficient biosorbent material for the treatment of uranium ions-bearing waste water streams. The kinetics of adsorption by this biomass was rapid with 90% of the total adsorption occurring within first 30 min. Also the uranium biosorption on the biomass was found to follow pseudo-second order kinetics. The adsorption capacities were solution pH dependent and maximum adsorption capacities of Ca-pretreated, protonated and non-pretreated Cystoseira indica algae was determined to be 454.5, 322.58, 224.67 mg/g respectively at a solution pH of 4. The Langmuir and Freundlich adsorption models were used for the mathematical description ofthe biosorption equilibrium of uranium ions to Cystoseira indica algae andthe obtained results showed that the adsorption equilibrium data fitted very well tothe Langmuir model in the studied concentrationrange for all investigated biomass forms. Assumingthe batch biosorption as a single-staged equilibrium operation, the separation process can bemathematically defined using these isotherm constants to estimate the residual concentration ofmetal ions or amount of biosorbent for desiredpurification.
Special thanks to Dr. M. Ghannadi Maragheh, Dr. S.J. Safdari and Dr. A. Khanchi for their help to accomplish this work.
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