Abstract
This work is related to removal of phenol from wastewaters by adsorption onto polymeric resins, a current alternative to activated carbon. A closed circuit, bench-scale liquid fluidized bed system was developed for this purpose. Phenol aqueous solutions with initial concentrations in the range of 0.084 to 0.451 kg/m³ were used to fluidize small permeable capsules of stainless steel screen containing a commercial resin at 308 K. Experiments were carried out using a fluidizing velocity 20% above that of the minimum fluidization of the capsules. Typically, 30 passages of the liquid volume circulating through the bed were required to reach a quasi-equilibrium concentration of phenol in the treated effluent. A simple batch adsorption model using the Freundlich isotherm successfully predicted final phenol concentrations. Suspended solids, often present in residual waters and a common cause of fixed bed clogging, were simulated with wood sawdust.
Phenol adsorption; Fluidized beds; Macroporous resins
ENVIRONMENTAL ENGINEERING
Development of a fluidized bed system for adsorption of phenol from aqueous solutions with commercial macroporous resins
R. A. CorrêaI, * * To whom correspondence should be addressed ; L. A. CalçadaII; R. P. PeçanhaIII
IInstituto de Engenharia Nuclear (DIQN / SETEQ), CNEN / MCT, Cidade Universitária, Ilha do Fundão, CEP: 21945 970, Rio de Janeiro - RJ, Brasil. E-mail: racorrea@ien.gov.br
IIDepartamento de Engenharia Química/UFRRJ. E-mail: calcada@ufrrj.br
IIIDepartamento de Engenharia Química, Escola de Química/UFRJ, Phone: +(55) (21) 2562 7633, Fax: +(55) (21) 25627 631. E-mail: pecanha@eq.ufrj.br
ABSTRACT
This work is related to removal of phenol from wastewaters by adsorption onto polymeric resins, a current alternative to activated carbon. A closed circuit, bench-scale liquid fluidized bed system was developed for this purpose. Phenol aqueous solutions with initial concentrations in the range of 0.084 to 0.451 kg/m3 were used to fluidize small permeable capsules of stainless steel screen containing a commercial resin at 308 K. Experiments were carried out using a fluidizing velocity 20% above that of the minimum fluidization of the capsules. Typically, 30 passages of the liquid volume circulating through the bed were required to reach a quasi-equilibrium concentration of phenol in the treated effluent. A simple batch adsorption model using the Freundlich isotherm successfully predicted final phenol concentrations. Suspended solids, often present in residual waters and a common cause of fixed bed clogging, were simulated with wood sawdust.
Keywords: Phenol adsorption; Fluidized beds; Macroporous resins.
INTRODUCTION
Phenols comprise a large category of organic compounds highly toxic for the vast majority of known forms of life, including humans. The toxicity of these substances is mainly related to the aromatic ring and to a lesser extent to their acid properties. The main chemical is phenol (C6H5OH, Ka = 1.0 ´ 10-10 at 25° C), present in the wastewater of many important industries, like those of dyes, explosives, adhesives, emulsifiers, pesticides, insecticides, detergents, etc. (Wagner and Schulz, 2001).
The solubility of phenol in water at 288 K is appreciable: 82 kg/m3. Consequently, without rigorous emission control, the phenol concentration in wastewaters will exceed legal limits quite easily.
The most important phenol recovery method is adsorption onto activated carbon or polymeric resins. Fixed beds are used for large-scale operation while mechanically agitated suspensions are preferred for medium/small-scale ones (Cooney, 1999). Regeneration and reutilization of adsorbent is a key economic factor in both cases (Wagner and Schulz, 2001; Zha et al., 1994).
The chemical nature of phenol adsorption on activated carbon makes its regeneration more costly than that of polymeric resins, where physical adsorption prevails. Also, activated carbon granules are easily friable, producing fine particles on handling, transportation and in shocks with mixer blades and chicanes. These can either be entrained from the system carrying adsorbed molecules to the receiving body or worse, in the case of fixed beds, migrate internally, clogging the porous structure of the bed. On the other hand, due to crosslinking, beads of polymer resins are strong and reasonably elastic. According to Paleos (1969), all aspects considered (including the marked difference between the unit costs of each material), the use of resins is economically more advantageous then the use of activated carbon.
Another aspect to be considered is that wastewaters always contain suspended solids (e.g., fibers, waxes and gums) which clog fixed beds, requiring frequent backwashing or fluidization to dislodge the foreign material (Veeraraghavan et al., 1989).
Other problems typical of fixed beds are dead zones, gas/vapor pockets and channeling. Additionally, pressure drops in fixed beds are roughly proportional to the square of the superficial fluidizing velocity, causing relatively high pumping costs (Kunii and Levenspiel, 1969).
Table 1 compares fixed beds, mechanically agitated suspensions and fluidized beds as alternatives for contacting adsorbents and solutions.
Motivated by the above mentioned operational problems of fixed beds and mechanically agitated suspensions of activated carbon granules, this work is aimed at the development of a liquid fluidized bed system for adsorption of phenol from wastewaters using polymeric resins.
THEORY
Like other unit operations dependent on the mass transfer of individual species (e.g., distillation, absorption, stripping, etc.), the design of adsorption equipment relies on equilibrium data, represented by isotherms, as well as on transient mass balances for the adsorbate, represented by the so-called breakthrough curves (McCabe et al., 2001).
Isotherms and Models
In adsorption systems, adsorbate is continuously transferred from the carrier fluid to the adsorbent material. For this to happen, the actual concentration of adsorbate on the adsorbent (q) should be smaller than the equilibrium concentration (q*) for the same concentration of adsorbate in the fluid (C). Thus q* = f (C) represents equilibrium. Alternatively, equilibrium can be expressed as C* = g (q) where C* is the concentration of adsorbate in the fluid that would be in equilibrium with q.
In accordance with Ku and Lee (2000), Navarro and Mijangos (1995), Mijangos and Navarro (1995) and Gusler et al. (1993), adsorption equilibria were described in this work with the Freundlich isotherm:
where k and n are empirical constants. Notice that k units depend on q* and C units, while n is dimensionless.
Breakthrough Curves and Models
Breakthrough curves represent the time profile for saturation of a given amount of an adsorbent structured as a fixed bed with a given solution of an adsorbate forced through this bed at a constant rate and fixed temperature. In spite of being fully empirical and dependent on almost all variables involved, breakthrough curves serve two purposes: (a) to decide whether the adsorbent is efficient for the required separation and (b) to establish the break point (process interruption), based on some criterion, either technical, economic or legal (Knaebel, 1999).
Breakthrough curves can be developed based on the basis of transient mass balance for the adsorbate in an infinitesimal volume of adsorbent fixed bed continuously percolated by a fluid carrying the adsorbate. The following hypotheses are adopted:
-
temperature is constant: the adsorption heat, which increases the system temperature, is neglected. The lower the concentration of the adsorbate in the fluid in the feed stream, the smaller the temperature rise will be;
-
flow rate is constant: the lower the concentration of the adsorbate in the fluid in the feed stream, the smaller the effect of adsorption on the flow rate will be. Flow transients characteristic of large-scale plants are also prohibited;
-
interstitial velocity profile is plug flow: in addition to the previous hypothesis this one also requires a uniform bed porosity;
-
adsorbate is not involved in chemical reactions: this is equivalent to saying that the adsorbate fed is either adsorbed or leaves the system in the effluent;
-
adsorbate is not dispersed: all types of mixing effects (convective, diffusive and eddy) are prohibited within the fixed bed.
Under these idealized conditions, the adsorbate mass conservation in the system can be expressed by the following equation (Hines and Maddox, 1985):
where DZ is the effective axial diffusion coefficient of the adsorbate, z is axial distance, u is the interstitial fluid velocity, t is time, e is the bed porosity and Ca is the concentration of adsorbate on the adsorbent.
Equation (4) can be rewritten as
where ra is the density of the adsorbent material and q, defined previously, is the actual concentration of adsorbate in the adsorbent.
As a matter of fact ra(1-e) is the density of the adsorbent bed, symbolized simply by r. Thus equation (3) becomes
Since diffusion is generally a slow process compared to the bulk flow present in fixed bed adsorption systems, the first term in equation (4) can be neglected giving:
The initial and boundary conditions associated with equation (5) are
where H is the height of the adsorbent bed and CF is the concentration of adsorbate in the liquid in the bed feed stream.
An additional simplification regards the third term in equation (5), the adsorption rate of adsorbate. It can be expressed in terms of an overall liquid phase mass transfer coefficient, KL; the interfacial mass transfer area per unit volume of bed, a; and the deviation from equilibrium concentration in the fluid, as follows (Sherwood et al., 1975):
Following the approach of Chern and Chien (2002), which is based on the nonlinear wave propagation theory, the concept of adjusted time,t, is introduced as follows:
where uw is the adsorbate concentration wave velocity. According to this theory the shape of the concentration wave is constant as it travels through the adsorbent bed.
Substituting equation (9) into equation (5) results in:
which is clearly independent of t.
The following boundary condition holds:
where is the concentration of adsorbate on the solid that would be in equilibrium with CF.
Equation (10) can then be integrated to give
In terms of the adjusted time, equation (8) becomes
Since C* = g (q) and with q given by equation (12) and assuming further that KL a is constant, equation (13) can be integrated between suitable limits to give
where t1/2 is the time required for the concentration of adsorbate in the bed effluent to rise to CF/2.
If the Freundlich isotherm, equation (1), represents the equilibrium data, equation (14) becomes
where x is the normalized, or relative, concentration of adsorbate in the bed effluent, defined as x=C/CF.
Equation (15) represents a model of breakthrough curve using the Freundlich isotherm. The parameter t1/2 is obtained directly from the experimental data, while KL a is determined from the known slope of the tangent to the curve x versus t at x=0.5, as follows. The integral in equation (15) is solved, giving an expression for x as a function of t, whose derivative in relation to t is the general curve slope. Since the slope at x=0.5 is known from experiments, KL a can be computed:
The breakthrough curve predicted by equation (15) will be checked against our own experimental data.
EXPERIMENTAL AND MODELING
From here on, when the specificity of the text allows, we prefer to use the words "phenol," "resin" and "aqueous solution" instead of, respectively, "adsorbate," "adsorbent" and "fluid," which are generic.
Adsorbent
The literature survey showed that the commercial resin Amberlite XADTM4 (Rohm and Haas Co.), was the best adsorbent for phenol from aqueous solutions. According to Fox (1978) the resin, which is a copolymer of styrene and divinylbenzene, has been tested for up to 1300 cycles (or two years) of adsorption and regeneration, with negligible loss of adsorptive capacity. Table 2 shows the relevant characteristics of the XADTM4 resin used in this work.
Since fluidization was our main concern, the resin density, size distribution and particle shape were the first characterizations made.
Mean density was quantified with an ordinary density bottle. Since the resin absorbs water, prior to measurement of density, samples were soaked in water so as to give its real density in the fluidized bed. Next, the resin was quickly dried and only then measurements were made.
The resin particle size distribution was determined with a set of standard sieves. Since resin particles could swell upon absorbing water, samples were initially soaked in water and then wet sieved. The resin was characterized by the Sauter mean particle size (DS).
Figure 1 is illustrative of a typical sample of XADTM4 resin. Notice the spherical shape of particles and the variable size.
Isotherms
Isotherms were established at 308 K using a thermostatic agitated bath (Dubnoff, Mod. 304, Nova Ética), with various initial concentrations of phenol tested simultaneously. Phenol P.A. (Vetec Química) was dissolved in distilled and deionized water to give a solution with a concentration around 41.36 kg/m3. The solution served as a supplier batch for further dilution as required. Conical flasks of 2.5 ´ 10-4 m3 containing 5.0 ´ 10-4 kg of resin and 5.0 ´ 10-5 m3 of aqueous phenol solution at various initial concentrations were shaken during 14 days. The equilibrium concentration of phenol on the solid phase, q*, was calculated with the equation:
where Ci and C* are respectively the initial and the equilibrium concentration of phenol in the liquid, Vliq is the initial volume of liquid and M is the initial mass of resin. Notice that equation (17) is approximate, since the volume of adsorbed phenol was negligible in relation to Vliq. Lower values of Ci and M, improve this approximation. Values of C* were determined using a UV spectrophotometer (GBC Scientific Equipment, mod. 918 UV) at a wavelength of 2.693 ´ 10-7 m.
Breakthrough Curves
A sketch of the equipment used to establish the breakthrough curves is shown in Figure 2.
The resin was packed in a vertical glass tube with an internal diameter of 1.3 ´ 10-2 m, supported on a porous sintered glass plate fixed to the tube walls. Phenol solution from the supplier batch was diluted to 0.470 kg/m3, forming the bed feed. The solution was forced downward through the fixed bed by means of a positive displacement pump with a controllable flow rate (Milton-Roy, mod. LMI). After suitable dilutions, the phenol concentration in the bed effluent was determined by UV spectrophotometry, as already mentioned. The working temperature was 299 K.
The main operational variable of adsorption equipment is the flow rate. Its effects on the breakthrough curves were studied in this work by changing the pump set points of stroke volume and pitch.
Resin Structured Particles
Early experiments with the resin XADTM4 showed that after soaking in water, the density of the beads was just above that of water, resulting in very small values for the minimum fluidizing velocity. This fact posed a serious limitation to the fluidization of the resin with water, restricting fluidizing velocities to figures slightly higher than the minimum fluidizing velocity so as to avoid elutriation of the finer resin beads present.
Considering that typical chemical industries produce high wastewater flow rates, the transversal area required to process them in such fluidized beds would be correspondingly large and in most cases probably unviable economically.
To circumvent this limitation a series of ideas were tested, all of them based on fixation or encapsulation of resin particles on a denser support so as to increase the minimum fluidizing velocity. After many attempts it was found that resin could be confined inside small cylindrical capsules (diameter = 0.008 m, length = 0.010 m) of stainless steel screen, 42 mesh (opening = 3.54 ´ 10-4 m). The original resin was sieved to remove particles smaller than 42 mesh, guaranteeing that none would escape from the capsules during fluidization. Figure 3 illustrates a fully assembled capsule.
The amount of resin in a single capsule was approximately 1.00 ´ 10-4 kg, resulting in a relatively loose bed occupying roughly half of the capsule volume. This would allow the resin particles to move around inside the capsule during fluidization, improving the mass transfer of adsorbate towards them. A total of 406 capsules were handcrafted for the tests.
Fluidized Bed
Fluidization experiments were carried out in the bench-scale equipment shown in Figure 4.
The bed was contained in a vertical glass tube (ID = 0.065 m). The distributor was a 0.013 m thick fixed bed of polypropylene pellets (mean size = 0.003 m), tightly secured between two stainless steel screens, mesh 42, adapted to the tube by means of flanges. To avoid jetting through the distributor passages, the plenum was packed with glass spheres (mean diameter = 0.002 m), which worked as a calming section. The equipment was provided with a single deposit for the fluidizing liquid, which was continuously recycled through the system by means of a centrifugal pump (DANCOR, 372.85 W). We shall call the above-described system a closed circuit fluidized bed (CCFB), not to be confused with the well-known circulating fluidized bed (CFB), mainly used for the combustion of low-grade coals. Flow rates were measured by a calibrated rotameter on the bed feed line. A needle valve on the rotameter feed line allowed good control over the operational flow rate.
The minimum fluidization velocity of the bed of capsules, Umf, was determined via the classic plot of bed height (H) versus superficial velocity (v0) for decreasing flow rates of water at 308 K.
Seven initial concentrations of phenol in water were tested: 8.4 ´ 10-5, 1.72 ´ 10-4, 2.24 ´ 10-4, 2.84 ´ 10-4, 3.56 ´ 10-4, 4.37 ´ 10-4 and 4.51 ´ 10-4 kg/m3, for a constant flow rate of 4.2 ´ 10-4 m3/s. All experiments were carried out at 308 K using a fluidizing velocity equal to 1.20 Umf. The circulating volume of phenol aqueous solution was approximately 0.010 m3. Liquid samples were taken from the tank at five minute intervals and phenol concentration, C, was measured using UV spectrophotometry as before. The profile C versus t for each run showed that a near equilibrium condition was reached after around 20 minutes. To get closer to equilibrium, runs were stopped after 40 minutes. This corresponded roughly to 100 passages of the liquid through the fluidized bed.
To obtain a motion pattern for the capsules during fluidization, tests were filmed with a digital camera. Two spray-painted capsules, one red and one white, were used as tracers. It was found that the capsules circulated in the bed in a tumbling manner. The capsules tended to shoot up when very close to the bed walls and fall down when close to the center. Due to the up-and-down tumbling motion and liquid flow across the screens of the capsules, the resin beads inside them were most certainly under intense agitation. Figure 5 shows a photograph of the fluidized bed during test with the tracer particles.
Suspended solids, a common cause of fixed bed clogging, were simulated with wood sawdust with mesh sizes in the range of 16 to 28, suspended in water at a concentration of 1.3 kg/m3 . The smallest dust particle found was roughly 1.7 times coarser than the opening of the capsules'stainless steel screen (42 mesh).
The closed circuit fluidized bed (CCFB) was adequately modeled as stirred batch adsorption equipment. The intense pump recycling rate produces similar mixing effects as those of a mechanical device, which supports this strategy.
It is well established that adsorption rates are generally fast higher than other rates (e.g., diffusion of mass and heat) in such systems. Physical adsorption, the topic of this work, is particularly very fast. On this basis it will be assumed that at any time during adsorption, a condition close to equilibrium is established in the vicinity of the adsorbent surface. In this case, adsorption isotherms can be coupled to the overall mass balance of phenol, equation (17).
Notice that C in the Freundlich isotherm, equation (1), is the same as the equilibrium concentration represented by C* in equation (17). Eliminating q* between these two equations and retaining the starred symbol, a transcendental equation in C* is found, which requires a numerical method of solution:
where
and
Equations (18), (19) and (20) correspond to a model for the adsorption process whose predictive power will be tested against our own data.
RESULTS AND DISCUSSION
Adsorbent
Dry XADTM4 resin is less dense than water. However, due to its macro porous structure, the resin absorbs water becoming a little denser than water itself, a condition that prevailed in all tests with fixed or fluidized beds. Wet density measurements were made in triplicate. The average value was ra = 1060 kg/m3.
The resin particle size distribution was established with standard sieves, resulting in a monomodal pattern. The Sauter mean size was DS = 5.4 ´ 10-8 m, well within the particle size range ascribed to XADTM4 by Rohm and Haas Co. (2001).
Isotherms
Data on adsorption equilibrium at 308 K are shown in Figure 6, together with curves adjusted via the Freundlich isotherm model.
Clearly the Freundlich model fitted the data very satisfactorily, in full agreement with the findings of various researchers quoted previously.
The parameters of the Freundlich model were determined by nonlinear regressions of data at 308 K with the following results:, n = 0.59 and r2 = 0.975.
In addition to the finite bath experiments, blank tests, i.e., without the resin, were carried out to check for phenol photodegradation and/or evaporation. After fourteen days, no measurable variation in phenol concentration was detected.
Breakthrough curves
Figure 7 shows experimental data for the breakthrough phenomena at 308 K, together with predictions of equation (15), based on Chern and Chien´s (2002) constant-pattern concentration wave model and using the Freundlich isotherm. The effects of flow rate and bed depth were investigated.
Operational variables, physical properties and other parameters required by the breakthrough curve model, equation (15), are specified in Table 3.
As shown in Figure 7, model predictions are very good for the lower flow rates (3.1´10-8 and 5.2´10-8 m3/s). For higher flow rates (8.2´10-8 and 1.2´10-7 m3/s), predictions are also satisfactory, except for the early stages of adsorption where predicted curves failed to go through the origin as they should. However, notice that curves corresponding to higher flow rates are too steep for practical use: the time corresponding to the break point would be too short, making the process unviable economically. The first two breakthrough curves showed unequivocally that XADTM4 is a suitable adsorbent for removing phenol from water solutions.
Helfferrich and Carr (1993) proved that when the adsorption rate is controlled by the mobile phase (i.e., the mass transfer rate of adsorbate in the liquid is slow) the concentration wave front has a sharp tail. On the other hand, if adsorption rate is controlled by the stationary phase (i.e., adsorption rate by the adsorbent is slow), the concentration wave tail has a sharp front. The breakthrough curves shown in Figure 7 don't fit in either of these extreme cases, meaning that adsorption rate control in our experiments was shared by the mobile and stationary phases.
Fluidized Bed
Figure 8 shows the classic plot of bed height (H) versus superficial velocity (U) for both increasing and decreasing flow rates of water. According to established convention, minimum fluidization velocity is defined by the intercept of the horizontal line representing the fixed bed height for a bed that has just been defluidized and the extension of the inclined line corresponding to the fall in fluidized bed height for decreasing flow rates.
The minimum fluidization velocity (Umf ) can be read directly from the above diagram, which gives Umf@ 0.1 m/s.
As already mentioned, adsorption tests with the fluidized bed were carried out using a fluidizing velocity (Uf ) arbitrarily specified as 1.20 Umf . In practice the fluidizing velocity is chosen to expand the bed to a large enough extent to avoid bed clogging. Both concentration and particle size distribution of the incoming suspended solids affect this choice.
One single clogging test was made using water to fluidize the capsules and wood sawdust to simulate solid suspended materials. After running for one hour in closed circuit at 1.20 Umf, a number of capsules were examined. To the naked eye, no dust particle was found blocking screen openings.
Figure 9 shows the time profile of phenol concentration in the circulating liquid of the closed circuit fluidized bed (CCFB) adsorption system developed in this work.
Notice that phenol concentration after around 1200 s (20 min) practically didn't change, suggesting that a condition near adsorption equilibrium was achieved in the system. Notice also that initial phenol concentration had a minor effect on the time required to achieve this condition.
Table 4 allows comparing phenol concentrations in the liquid after a number of passages through the fluidized bed, with the values predicted by the model, i.e., equations (18), (19) and (20).
Data shown in Table 4 corroborate the conclusions already drawn from Figure 9: after a number of passages between 25 and 38, a quasi-equilibrium condition was attained with little influence of the initial phenol concentration. In all instances, the model underpredicted equilibrium concentrations. At the high initial phenol concentration levels, where uncertainties in chemical analysis are small, model predictions were considered very satisfactory (deviations in the range of 3.4 5.4 %). For mid and low concentrations, model predictions were considered just reasonable (deviations in the range of 8.7 16.6 %). However, it is important to remember that the model is very simple and reliable: it is based on a straight forward material balance of phenol and on the accuracy of the Freundlich isotherm in representing adsorption equilibrium. Errors, human and instrumental, are introduced mainly via measurements.
CONCLUSIONS
Based on developments made and experimental evaluations carried out in this work, the following conclusions are drawn:
Liquid permeable capsules containing XADTM4 resin were developed and successfully tested for adsorption of phenol from water solutions in a closed circuit fluidized bed operating at 308 K.
Within uncertainties of spectrophotometric analyses, a condition of quasi-adsorption equilibrium was achieved after 25 to 38 passages of the circulating liquid through the capsules' fluidized bed. The initial concentrations of phenol tested had a small effect on the number of passages required to attain this condition.
After concluding the experiments, one capsule was opened. Resin particles were then examined under an estereoscope. No breakage or surface wear was observed.
Suspended solids, a common cause of fixed bed clogging, were simulated with wood sawdust with typical particle size range and concentration. Under examination with the naked eye, capsules didn't show any blockage of screen openings.
The adsorption process was modeled using the Freundlich isotherm, producing a transcendental equation for the phenol equilibrium concentration whose values were slightly underpredicted by the model.
Chern and Chien´s (2002) constant pattern concentration wave model coupled to the Freundlich isotherm successfully described the experimental breakthrough curves for XADTM4 resin. The effectiveness of XADTM4 for adsorption of phenol from aqueous solutions was fully confirmed by our data.
ACKNOWLEDGMENTS
R. A. Corrêa acknowledges the Instituto de Engenharia Nuclear CNEN/MCT for its support of this research, with special thanks to José Waldemar S. D. Cunha and Glória R. W. Silva.
NOMENCLATURE
Latin Letters
![](https://minio.scielo.br/documentstore/1678-4383/XrJNZx96dPtWXknrGdMP7Tb/14506ec8e6b0b06fa3ff8ea8ab2515393e003a1d.gif)
![](https://minio.scielo.br/documentstore/1678-4383/XrJNZx96dPtWXknrGdMP7Tb/134615815fb4ea0a4419f3b69a65582f0212432e.gif)
Greek Letters
![](https://minio.scielo.br/documentstore/1678-4383/XrJNZx96dPtWXknrGdMP7Tb/4e9d4f6e7dd02639f49cd26c95e79c88e350bc20.gif)
![](https://minio.scielo.br/documentstore/1678-4383/XrJNZx96dPtWXknrGdMP7Tb/9c8b6ea6101231462c1c78f1d51aaad3a845e555.gif)
Subscripts
Note
A patent application for the encapsulation of light particulate materials for the purpose of contacting fluids and solids in fluidized beds is pending at INPI Ministério do Desenvolvimento, Indústria e Comércio Exterior, Brazil.
(Received: May 16, 2006 ; Accepted: October 30, 2006)
- Chern, J.M. and Chien, Y.W., Adsorption of nitrophenol onto activated carbon: Isotherms and breakthrough curves, Water Research, 36, 647-655 (2002).
- Cooney, D.O., Adsorption Design for Wastewater Treatment, Lewis Publishers, Boca Raton (1999).
- Fox, C.R., Plant uses prove phenol recovery with resins, Hydrocarbon Processing, November, 269-273 (1978).
- Gusler, G.M., Browne, T.E. and Cohen, Y., Sorption of organics from aqueous solutions onto polymeric resins, Ind. Eng. Chem. Res., 32, 2727-2735 (1993).
- Helfferrich, F.G. and Carr, P.W., Non-linear waves in chromatography I waves, shocks and shapes, Journal of Chromatography, 629, 97-122 (1993).
- Hines, A.L. and Maddox, R.N., Mass Transfer Fundamentals and Applications, Prentice-Hall, Englewood Cliffs, N.J. (1985).
- Knaebel, K., The basics of adsorbers design, Chemical Engineering, April, 92-101 (1999).
- Ku, Y. and Lee, K.C., Removal of phenols from aqueous solution by XAD-4 Resin, Journal of Hazardous Materials, B80, 59-68 (2000).
- Kunii, D. and Levenspiel, O., Fluidization Engineering, John Wiley and Sons, Inc., New York (1969).
- McCabe, W.L., Smith, J.C. and Harriott, P., Unit Operations of Chemical Engineering, 6th ed., McGraw-Hill, Inc., New York (2001).
- Mijangos, F. and Navarro, A., Parametric analysis of phenol adsorption onto polymeric adsorbents, J. Chem. Eng. Data, 40, 875-879 (1995).
- Navarro, A. and Mijangos, F., Análisis de la adsorción de fenoloes sobre una resina polimérica no polar, AFINIDAD LII, Noviembre - Diciembre, 387-392 (1995).
- Paleos, J., Adsorption from aqueous and non aqueous solutions on hydrophobic and hydrophilic high surface area copolymers, Journal of Colloid and Interface Science, 31, 1, 7-18 (1969).
- Rohm and Haas Company, Product Data Sheet 0556 A, June (2001).
- Sherwood, T.K., Pigford, R.L. and Wilke, C.R., Mass Transfer, McGraw-Hill, Inc., New York (1975).
- Veeraraghavan, S., Fan, L.T. and Mathews, A.P., Modeling adsorption in liquid-solid fluidized beds, Chemical Engineering Science, 44, 10, 2333-2344 (1989).
- Wagner, K. and Schulz, S., Adsorption of phenol, chlorophenols, and dihydroxybenzens onto unfunctionalized polymeric resins at temperatures from 294.15 K to 318.15 K, J. Chem. Eng. Data, 46, 322-330 (2001).
- Zha, F.F., Fane, A.G. and Fell, C.J.D., Phenol removal by supported liquid membrane, Separation Science and Technology, 29, 17, 2317-2343 (1994).
Publication Dates
-
Publication in this collection
31 May 2007 -
Date of issue
Mar 2007
History
-
Accepted
30 Oct 2006 -
Received
16 May 2006