• Vol 8, No 1 (2017)
  • Chemical Engineering

A Modified Shrinking Core Model for Leaching of Aluminum from Sludge Solid Waste of Drinking Water Treatment

Agus Mirwan, Susianto , Renanto Handogo


Cite this article as:

Mirwan, A., & SusiantoHandogo, R., 2017. A Modified Shrinking Core Model for Leaching of Aluminum from Sludge Solid Waste of Drinking Water Treatment . International Journal of Technology. Volume 8(1), pp.19-26

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Agus Mirwan Department of Chemical Engineering, Faculty of Industrial Technology, Institut Teknologi Sepuluh Nopember, Surabaya 60111, Indonesia
Susianto Department of Chemical Engineering, Faculty of Industrial Technology, Institut Teknologi Sepuluh Nopember, Surabaya 60111, Indonesia
Renanto Handogo Department of Chemical Engineering, Faculty of Industrial Technology, Institut Teknologi Sepuluh Nopember, Surabaya 60111, Indonesia
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Abstract
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The kinetics of aluminum leaching from sludge solid waste (SSW) using hydrochloric acid at different leaching temperatures (30-90°C) was studied. A mathematical model was developed based on a shrinking core model by assuming first-order kinetics mechanisms for leaching and an equilibrium linear at the solid-liquid interface. The proposed model is suited to fit experimental data with three fitting parameters and to simulate the leaching of aluminum from SSW, which was validated with the mass transfer coefficient (kc, cm/s), diffusion coefficient (De, cm2/s), and reaction rate constants (k, cm/s). The evaluated kc, De, and k are expected to follow an increasing trend with increasing temperature. The correlation coefficient ? 0.9795, the root mean square error ? 0.399, the mean relative deviation modulus ? 6.415%, and the value of activation energy is 13.27 kJmol-1. The proposed model could describe the kinetics of aluminum leaching from the SSW DWT in accordance with test parameters and relevant statistical criteria. Valuable information on the results of this work can be given for the purposes of the simulation, optimization, scaling-up, and design of the leaching process.

Aluminum; Leaching; Recovery; Shrinking core model; Sludge solid waste

Introduction

Sludge solid waste of drinking water treatment (SSW DWT) is the waste by-product of the drinking water treatment processes produced daily and largely produced during clarification (e.g., coagulation-flocculation and solid-liquid separation with sedimentation process) while removing colloidal impurities from raw water (Nair & Ahammed, 2015; Zhou et al., 2015). It is a fundamental process that uses a large amount of general aluminum salt coagulants, such as commercial aluminum sulfate and polyaluminum chloride (Nair & Ahammed, 2015). A large amount of the coagulant used in DWT is proportional to the amount produced in SSW. Regarding the global production of SSW, approximately 10,000 tons are produced per day, of which European countries, such as Ireland, Germany, the Netherlands, the United Kingdom (UK), and Portugal, take up 10.38%, the United States 72.6%, and China and Taiwan 0.003% (Babatunde & Zhao, 2007). In Indonesia, especially Banjarmasin, South Kalimantan, more than 6.91 × 106 tons (70 wt.%) of SSW is produced every year. At present, the majority of SSW is still disposed in landfills, in sanitary sewers, and by land applications, such as land treatment facility and waste pile, assuming that the SSW is not poisonous (Babatunde & Zhao, 2007). Given the high demand for a high quantity of and high-quality drinking water, coupled with the increasing generation of SSW and environmental restrictions on their disposal up until recently,

various studies have been done in search of options for reusing coagulants (Zhou et al., 2015). The reduction and re-use of SSW have been considered and have provided varying achievement levels.

The main constituents of SSW-DWT are SiO2 and Al2O3; however, during the addition of aluminum salt in the water treatment process, aluminum hydroxide [Al(OH3)] precipitates have formed (Cheng et al., 2012; Nair & Ahammed, 2015). Aluminum extraction from SSW is performed mainly by hydrometallurgical methods, in which SSW is first leached by a hydrochloric acid solvent. During the leaching process, soluble aluminum hydroxides can form and stay in the solution. In the separation process, precipitates of aluminum hydroxides are transferred to the leaching filter cake.

Based on differential mass-balance, mass-transfer, and equilibrium relationships, a mathematical model has been proposed. The shrinking core (SC) model describes how irreversible desorption is followed by the diffusion process through pores inside a porous solid (Goto et al., 1996), which reacts with a solvent to leave a reacted layer around the  unreacted core. This model assumes that a solute is extracted around a shrinking core. The SC model has been widely used in hydrometallurgy for the leaching process to obtain metal or any other material that is valuable

Experimental Methods

2.1.   Material

SSW was collected from the sludge ponds of DWT Banjarmasin, Indonesia; washed and dried under direct sunlight for 24 hours; and then oven-dried at 105°C for 3 hours. It was milled in a grinder and then sieved to select particles that were 0.074-0.044 mm in width, with a particle size of 0.0585 mm, before the leaching process was carried out.

2.2.   Leaching Procedure

About 5 g (measured exactly) of grinded and classified SSW was extracted with 250 ml of 4 M hydrochloric acid (HCl) (prepared from Sigma-Aldrich with a purity of ? 32%) in an Iwaki Pyrex boiling flask. The flask had one neck for a thermometer and for the inlet or withdrawal of samples at regular time intervals (3-60 minutes). The reaction mixture was stirred at 300 r.min-1 using a magnetic stirrer and was heated (Dragon Lab, MS-H-Pro, People's Republic of China) indirectly through a water bath at different temperatures (30, 50, 70, and 90ºC). At selected time intervals (5, 10, 20, 30, 40, 50, and 60 minutes), all samples were collected using a syringe and filtered for analysis to determine the aluminum content in the solution using an inductively coupled plasma cluster optical emission spectrometer (ICP-OES) (9060-D Teledyne Leeman Labs. the USA). Each analysis was repeated three times and deputized with average values.

The total amount of aluminum can be leached out in the acid condition and calculated based on standard methods (Cheng et al., 2012). SSW was added in nitric acid with a ratio of 1:1 and filtered. The filtrate was analyzed using ICP-OES to determine the amount of soluble aluminum. The result indicated that approximately 61.8 mg of aluminum ions can leach from 1 g of WTS, and the aluminum leaching recovery (x) can be stated as , where X0 denotes the total aluminum obtained through the acid leaching process, and X is the amount of aluminum obtained at different conditions (mg/g).

2.3.   Model Development

According to Cheng et al. (2012), a lower pH between 1 and 3 in aluminum dissolution can be obtained with a higher aluminum recovery ratio of approximately 70-90%. Furthermore, at normal temperatures, Al2O3 cannot react with acid so that the solid-phase amorphous aluminum hydroxide contained in sludge can be leached out by the acidification process. Chemical reactions that occur in SSW and hydrochloric acid are stated as follows:


Al(OH)3 (s) + 3HCl (aq) ? AlCl3 (aq) + 3H2O

(1)



Figure 1 Schematic drawing of the SC model


2.4.   Mathematical Modeling of Leaching Kinetics

SC model assumptions are as follows: SSW has spherical particles; the particles are completely mixed so that their spherical shape can be maintained; the temperature is fixed during the leaching process; other substances in the SSW do not have a significant effect on the kinetics (Safari et al., 2009).

The total mass balance equation for leaching is as follows:

    (2)

Variations in time from the solid phase (aluminum concentration in a particle of SSW) are related to the mass transfer rate of solute as follows:




References

Baba, A.A., Adekola, F.A., 2012. A Study of Dissolution Kinetics of a Nigerian Galena Ore in Hydrochloric Acid. J. Saudi Chem. Soc., Volume 16(4), pp. 377-386

Babatunde, A.O., Zhao, Y.Q., 2007. Constructive Approaches Toward Water Treatment Works Sludge Management: An International Review of Beneficial Reuses. Crit. Rev. Environ. Sci. Technol., Volume 37(2), pp. 129-164

Buci?-Koji?, A., Sovová, H., Planini?, M., Tomas, S., 2013. Temperature-dependent Kinetics of Grape Seed Phenolic Compounds Extraction: Experiment and Model. Food Chem., Volume 136(3), pp. 1136-1140

Cheng, W.P., Fu, C.H., Chen, P.H., Yu, R.F., 2012. Dynamics of Aluminum Leaching from Water Purification Sludge. J. Hazard. Mater., Volume 217?218, pp. 149-155

Geankoplis, C.J., 1993. Transport Processes and Unit Operations. PTR Prentice Hall, City, State, Country

Goto, M., Roy, B.C., Hirose, T., 1996. Shrinking-core Leaching Model for Supercritical-fluid Extraction. J. Supercrit. Fluids, Volume 9(2), pp. 128-133

Levenspiel, O., 1998. Chemical Reaction Engineering, 3rd Edition. Wiley, City, New York, USA

Nair, A.T., Ahammed, M.M., 2015. The Reuse of Water Treatment Sludge as a Coagulant for Post-treatment of UASB Reactor Treating Urban Wastewater. J. Clean. Prod., Integrating Cleaner Production into Sustainability Strategies, Volume 96, pp. 272-281

Safari, V., Arzpeyma, G., Rashchi, F., Mostoufi, N., 2009. A Shrinking Particle—Shrinking Core Model for Leaching of a Zinc Ore Containing Silica.

Int. J. Miner. Process., Volume 93(1), pp. 79-83

Zhou, Z., Yang, Y., Li, X., Zhang, Y., Guo, X., 2015. Characterization of Drinking Water Treatment Sludge After Ultrasound Treatment, Ultrason. Sonochem., Volume 24, pp. 19-26