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Revista Ambiente & Água

On-line version ISSN 1980-993X

Rev. Ambient. Água vol.10 no.3 Taubaté July/Sept. 2015

http://dx.doi.org/10.4136/ambi-agua.1577 

Articles

Metals uptake by live yeast and heat-modified yeast residue

Sorção de metais por levedura viva e resíduo de levedura modificado por processos de aquecimento

Geórgia Labuto 1   * 

Bianca Trama 2  

Geison Castro da Silveira Gueller 3  

Bruna de Souza Guarnieri 4  

Fernando Vitorino da Silva 5  

Roberta Collazo 6  

1Universidade Federal de São Paulo(Unifesp), Diadema, SP, Brasil, Instituto de Ciências Ambientais Químicas e Farmacêuticas, e-mail: geolabuto@gmail.com

2Universidade Federal de São Paulo (Unifesp), Diadema, SP, Brasil, Instituto de Ciências Ambientais Químicas e Farmacêuticas, e-mail: btrama@gmail.com

3Universidade de São Paulo (USP), São Paulo, SP, Brasil, Instituto de Biociências, e-mail: g3ison@gmail.com

4Universidade de São Paulo (USP), São Paulo, SP, Brasil, Escola de Artes, Ciências e Humanidades, e-mail: brunasguarnieri@gmail.com

5Universidade Federal de São Paulo (Unifesp), Diadema, SP, Brasil, Instituto de Ciências Ambientais Químicas e Farmacêuticas, e-mail: fernando_vitorino@terra.com.br

6Universidade Federal de São Paulo (Unifesp), Diadema, SP, Brasil, Instituto de Ciências Ambientais Químicas e Farmacêuticas, e-mail: roberta_collazo@yahoo.com.br

ABSTRACT

This study evaluated the biosorption of Cd2+, Cr3+, Pb2+ and Cu2+ at pHs 3, 4, 5 and 6 for Saccharomyces cerevisiae both alive and biologically inactivated by different heating procedures (oven, autoclave or spray dry technique originated from alcohol industry). The material inactivated by autoclave (IA, at 120°C, 30 min) had the best performance for metals uptake: 1.88 ± 0.07 (Cu2+), 2.22 ± 0.02 (Cr3+) and 1.57 ± 0.08 g kg-1 (Pb2+). For Cd2+; while the material inactivated by spray dry (RY) presented the higher sorption capacity, 2.30 ± 0.08 g kg-1. The sorption studies showed that the biosorbent materials presented different sorption capacities and an ideal sorption pH. The sorption sites were investigated by potentiometric titration and FT-IR and showed that different heating processes used to inactivate biological samples produce materials with different characteristics and with a diverse sorption capacity due to modification of the available sorption sites. This suggests that inactivation by heating can be an alternative to improve the performance of biosorbents. The main sorption sites for each material were phenolic for live yeast (LY) and carboxylic for yeast inactivated by heating in an autoclave (IA).

Key words: biosorption; metals sorption; modification of the biosorbent; sorption sites

RESUMO

Saccharomyces cerevisiae viva e biologicamente inativada por diferentes processos de aquecimento (forno, autoclave ou spray dry) foram empregadas para biossorção de Cd2+, Cr3+, Pb2+ e Cu2+ em pHs 3, 4, 5 e 6. O material inativado por autoclave (IA, a 120°C, 30 min) teve o melhor desempenho para a sorção de metais: 1,88 ± 0,07 (Cu2+), 2,22 ± 0,02 (Cr3+) e 1,57 ± 0,08 g kg-1 (Pb2+). Para Cd2 + o material inativado por spray dry (RY) apresentou a maior capacidade de sorção, 2,30 ± 0,08 g kg-1. Os estudos de sorção mostraram que os materiais biossorvente apresentaram diferentes capacidades de sorção e pH ideal de sorção. Os sítios de sorção foram investigados por titulação potenciométrica e FT-IR e denotam que diferentes processos de aquecimento empregados para inativação biológica produzem materiais com características diversas e com capacidade de sorção distintos devido a modificação dos sítios de sorção disponíveis. Isto sugere que a inativação por aquecimento pode ser uma alternativa para melhorar o comportamento de biossorventes. Os principais sítios de sorção para cada material foram grupos fenólicos para a levedura viva (LY) e grupos carboxílicos para levedura inativada em autoclave (IA).

Palavras-Chave: biossorção; modificação do biosorvente; sítios de sorção; sorção de metais

1. Introduction

Biological materials alive or dead have been used successfully as biosorbent for metals or organic compounds since 80's (Madrid and Cámara, 1997). The main disadvantages of using living organisms - which have led to a search for using inactivated organisms - are: a) they are unable to regenerate for reuse; b) the pathogenic feature of the material; c) the need to know and control the best growing conditions in the presence of the analyte; and d) the toxicity of such analytes may affect the biological material leading to the inhibition of its development or even its death, stopping the sorption process (Vegliò and Beolchini, 1997). On the other hand, the mechanisms not dependent on metabolism are faster, without major influences of temperature in the range of 30 to 40ºC, and are directly related to the pH of the medium (Vegliò and Beolchini, 1997). The pH dependence favors the use of inactivated biological materials. Thermal inactivation is frequently mentioned as a way to interrupt the metabolism of biological materials employed in studies of biosorption (Arica et al., 2003; Bayramoğlu and Arica, 2008).

While the mechanisms of change related to macromolecular cell death during heat treatment are not fully known, we know that thermal inactivation creates a new material, once it has caused the irreversible denaturation of the cell wall (which is composed of lipids, phospholipids, polysaccharides and proteins), membranes, ribosomes, and nucleic acids (Lee and Kaletunç, 2002). Thermal inactivation is employed to interrupt the metabolism for biosorption and also has been used to improve their sorption capacity (Arica et al., 2005; Gürişik et al., 2004; Bayramoğlu and Arica, 2008). However, such items do not discuss how biological inactivation by heating processes affects the sorption sites of biosorbents, contributing to the improvement of sorption capacity.

This work reports the influence of heating inactivation (HI) of Saccharomyces cerevisiae from the alcohol industry on metals uptake and available sorption sites. S. cerevisiae is a cost-effective biosorbent because it is largely obtainable as a residue from the ethanol industry (c.a. 420,000 tons/year only in Brazil) and is nonpathogenic. The cell wall is composed of glucans, mannans, chitin, protein and lipid, all rich in organic functional groups with high potential for metals uptake (Volesky, 2004).

2. Material and Methods

2.1. Yeast origin and heating inactivation procedures

All experiments were conducted with the same initial biomasses that originated from the first ethanol fermentation which was stored frozen until ready for use (except for the biomass inactivated by spray dry). After thawing, the biomass was filtered with Filter Pro 0.45 µm, 33 DM (Aprolab, Brasil) then washed with distilled deionized water. The laboratory inactivation of yeast was conducted immediately after filtering.

Saccharomyces cerevisiae provided from ethanol industry was employed in four forms: i) live yeast (LY); ii) inactivated by heating in an oven (IO): 120°C, 2 h; iii) inactivated by heating in an autoclave (IA): 30 min, 120°C, afterward dried in oven at 60°C until constant weight; and iv) inactivated by the spray dry technique (RY) by the ethanol industry.

To verify that the material had been inactivated, the inoculations of living matter and materials were submitted to the inactivation procedures in Petri dishes containing culture medium for yeast (20 g L-1) YPD agar (Sigma-Aldrich). The inocula were incubated in a microbiological chamber at 30°C for 24 hours. After that, the absence of growth in the plates containing yeast submitted to the inactivation procedures was confirmed by comparison with the inocula of live yeast obtained from the alcohol industry. The whole procedure of preparation of the suspension and inoculation was performed under sterile conditions within a laminar flow hood, and disinfected with 70% alcohol and submission to UV radiation for five minutes. All solutions and materials used to prepare the suspension for the inoculation and were autoclaved for 30 minutes at 120°C.

2.2. Characterization of biosorbent materials

Potentiometric titration of sorption sites: Three aliquots of 50 mg of each type of biosorbent were suspended in 50 mL of 0.1 mol L-1 KNO3 and the initial pH was determined. The sorption sites were potentiometrically titrated up to pH 2.0 with standardized HNO3 solutions, according to (Araújo et al., 2007). Other 3 aliquots were titrated until pH 12.0 with standardized KOH solutions.

The mathematic model assumes that the material contains n binding sites of the main metal ions, and treats these sites as discrete monoprotic weak acids, HLn, the consumption of H+ by these sites can be expressed by the following Equação 1 (Wang et al., 1998):

where:

∆V = cumulative volume of acid/base added (mL);

V0 = initial volume of suspension solution (mL);

C = concentration of acid/base added (mol L-1); Cn = concentration of the acid site, Cn= [HLn\ + [Ln-\ (mol L-1);

Cc = total carbonate concentration (mol L-1);

Kan= acidity constant of HLn (mol L-1);

[OH-\0, [H+\0 = initial concentration of hydroxyl and ions H+ (mol L-1), respectively;

10-6,3 = first acidity constant (Ka1) of H2CO3;

10-16,6 = overall acidity constant (Ka1 × Ka2) of H2CO3

The first factor inside the parenthesis of equation 1 represents the consumption of hydrogen ions by the material, taking into account n complexation sites; the second factor represents the consumption by water; and the third factor represents the consumption by carbonate species. Thus, if pH is the unique dependent variable of the equation, a non-linear regression of the obtained data is run until fitting them to the equation will yield the constant values of acidity and the concentration of ligant sites as results (Lemos and Takiyama, 1999). The acid-base titration curves were used to estimate the constants of acidity and the concentrations of the acidic sites of the biosorbent material through the non-linear regression using the equation 1. The non-linear regression of the titration curves, performed with Sigma Plot 8.0 software (Statistical Solutions, USA), was used to infer the acid-base sorption site characteristics.

Changes in the main functional groups present in LY, IA, IO and RY biosorbent materials were investigated by use of a Fourier transform infrared spectrometer (Bomem MB 102, Austria). Portions of each material was added to KBr previously dried in an oven and pressed to produce tablets that had been analyzed to obtain infrared spectra.

2.3. Metals uptake by the yeast biosorbent materials

A quantity of 100.00 mg of LY, IA, IO and RY were conditioned in 15 mL of KNO3 0.5 mol L-1 and the pH was set to 3, 4, 5 or 6. The conditioned materials were centrifuged and re-suspended in 5 mL of individual metals solutions containing 50 mg L-1 of each metal Cd2+, Cr3+, Pb2+ or Cu2+ in KNO3 0.5 mol L-1 and pHs previously set to 3, 4, 5 or 6.

The suspensions were shacked (250 rpm, 10 min, 25°C), centrifuged (2 min, 3400 rpm) and the supernatants were transferred to different flasks to stop the contact with the metal solutions. The work solutions and supernatants of biosorption were analyzed using an ICP OES (Varian RD, USA) - spectral lines 226.502 nm Cd(II), 205.560 nm Cr(III), 213.598 nm Cu(II) and 182.143 nm Pb(II), 1.20 kW power, plasma flow 15 L min-1, auxiliary gas 1.50 L min-1, nebulizer flow 0.9 L min-1 and the quantification limits (LOQ) were 0.25; 0.5, 1.0 e 1.0 mg L-1, respectively.

The metals uptakes were determined by the difference between the metals concentration of individual solutions prepared in KNO3 0.5 mol L-1 in the four working pHs and the supernatants obtained after contact with these biosorbent solutions and these differences were used to calculate the mass of each metal biosorbed by the respective biomasses (LY, IA, IO and RY).

3. RESULTS AND DISCUSSION

3.1. Metals uptake by the yeast biosorbent materials

Changes in metals uptake are expected considering that the characterization of biosorbent materials denotes that HI results in different materials, with a diverse sorption sites distribution. Overall, all heating processes improved biosorbent capacity (Figure 1 and Table 1). This behavior is related in literature by different materials (Arica et al., 2005; Bayramoğlu and Arica, 2008).

The evaluation of the effectiveness of the inactivation methods employed was checked by the inoculation of all materials on YPD. The materials submitted to the inactivation processes were checked to ensure that they did not present metabolic action on observed sorption phenomena, depending only on the interaction of metals and sorption sites available on the surfaces of the modified materials.

In general, IA was the best biosorbent for all analytes in all pHs, with the exception of Cd2+ (Figure 1) for which RY was the best biosorbent. Given that the sorption sites and species of metals in solution are Pearson's acids and bases, it is possible to infer about the probable sorption sites involved in metals uptake. The Cd2+ is the predominant species in all studied pHs (100%) (Baes and Mesmer, 1976), and this fact may explain the small variation of Cd uptake for these pHs independent of the evaluated material.

Thus, the variation of sorption may be related to three mechanisms: 1) complexation with sorption sites; 2) electrostatic attraction; and 3) metabolism dependence, which can be discarded since Cd2+ is very toxic to cells and promotes apoptosis (Gardarin et al., 2010). The order of Cd2+ uptake is RY>IA>IO>LY, where IA uptake is around 2.5 times that removed by IO (Table 1). Since RY has the higher possibilities of soft bases to complex Cd2+ (Pearson's soft acid) the superior analyte uptakes by RY could be related to the sorption sites hydroxyl which accounts for about 93.1% of the sites available for this material.

Figure 1. Metals removed at different pHs (n = 3). 

The Cu2+ is a free cation in pHs from 3 to 5. At pH 6, CuOH+ and Cu2(OH)22+ manifest (Baes and Mesmer, 1976), which could explain the decreased uptake of the analyte at this pH for all inactivated materials, since the probable interaction between them and this analyte is the electrostatic interaction. For all pHs the sorption sites of RY are protonated, suggesting that the mechanism is related to covalent bonds and not to an electrostatic attraction. Considering that Cu2+ is a Pearson's borderline acid, all sorption sites are able to complex with the analyte. While Cu2+ sorption increased at pH 6 for LY, the opposite behavior was observed for the inactivated materials. This behavior can be related to the fact that copper is an essential element for mitochondrial respiration, for carbon and nitrogen metabolism, for oxidative stress protection, besides being important for cell wall synthesis (Hänsch and Mendel, 2009). Furthermore, the best conditions for yeast development are between pH 5-6, which might have contributed to the higher sorption capacity presented by LY at this pH.

The Pb2+ is present as a free cation in solution for all pHs studied. Thus, the changes of sorption are related to the influence of pH on the available sorption sites. For Pb2+, the retention rate obtained for LY was 48.34% of available metal in work solutions at pH 4. For RY, the retention was around 55.74% at pH 5.0 and 59% for IO for all pHs from the initial available metals in solution, with the highest retention percentage for pH 6.0, on the order of 65.26%. For this metal RY, IA and LY presented similar sorption capacities (Table 1), which suggests that the uptake for this analyte is not metabolism-dependent even for the LY. In addition, the slight increasing of sorption observed for IO at pH 4 could be related to the deprotonation of carboxylic sites at this pH. This corroborates the hypothesis that these sorption sites are responsible for the retention of the analyte.

The Cr3+ is a Pearson's hard acid and produces six species in solutions with equilibrium varying with pH. The distribution of the Cr3+ species in diluted solution according to pH is: pH<3 = 100% Cr3+; pH 4= Cr3+ (72%) and Cr2(OH)24+ (28%); pH 5=Cr3+ (14%), CrOH2+ (30%), Cr3(OH)45+ (50%), Cr2(OH)24+(4%) and Cr(OH)4- (2%) Cr; pH 6=CrOH2+ (15%), Cr(OH)2+ (10%) and Cr3(OH)4+5 (75%) (Baes and Mesmer, 1976). The Cr3+ uptake was affected by pH increment for all materials, suggesting that the variation of chemical species can be affected by this parameter. Probably, the chromium species present in solution, which changes with pH, and their interactions with the available sorption sites are responsible for the sorption increasing with pH.

Inactivation provides a better performance of biosorbent due to the changes promoted by the different heating processes on available sorption sites. In general, the material inactivated by autoclave (IA) presented the best performance for metals uptakes. The yeast residue (RY) only presented a higher sorption for Cd. The solution of inactive materials has advantages, such as the need to control the conditions of microorganism growth which involves completely knowing its metabolism and life cycle, no danger of the toxicity of the analytes impeding biosorbent development, and the simplicity of storage and transportation of the biosorbent in the case of commercial uses.

Sorption site availability depends on other factors, such as the chemical function and quantity of sorption sites, accessibility, chemical state and affinity of the analyte (Hänsch and Mendel, 2009). In addition, the chemical neighborhood can differentiate the sites of the same chemical function, through withdrawing or donating groups that affect the electronic density of the sorption sites with the same theoretical uptakes capacity, making them more positive or negative (March, 1992).

Table 1. General data of metals uptake by different biological materials (100.00 mg of biological material, 50 mg L-1 of different metals in KNO3 0.5 mol L-1, n = 3). 

LY = live yeast; IO = inactivated by heating in an oven, 120°C, 2 h; IA = inactivated by heating in an autoclave, 30 min, 120°C, afterward dried in oven at 60°C until constant weight, and RY = inactivated by spray dry technique (RY).

3.2. Characterization of biosorbent materials

Potentiometric titration of acid sites: The cell wall of S. cerevisiae is composed by mannoproteins (30-50%), 1,6-β-Glucan (5-10%), 1,3- β-Glucan (30-45%) and chitin (1,5-6%) (Klis, 1994). According to other authors, the cell wall is also composed of c.a. 6% of lipids, 9% of glycoprotein, 25% of mannane and 43% of glycans (Avery and Tobin, 1993; Chaud and Sgarbieri, 2006).

These components present functional groups such as amine, amide, imidazol, thioethers, phosphate, carboxylic, thiol, phenolic and hydroxyl which present different affinities by metallic species (Shiewer and Volesky, 2000), pKa and acid-base classification according to Pearson theory (Pearson, 1968). Heating can cause loss of secondary or tertiary structure of cell wall proteins, which affects the sorption capacity of a biosorbent and its behavior by changes in functional groups' availability and exposure. Table 2 shows the differences found between S. cerevisiae inactivated by heat applied by different inactivation methods. According to the titration approach, the materials are chemically different and have not just different sorption sites but also presented a diverse percentual distribution when sorption sites of a same chemical function were present. Figure 2 presents the titration curves of sorption sites for the different materials and the best-fitting curve to predict the sorption sites.

The FT-IR spectra (Figure 3) of IA, IO, RY and LY present functional groups in the region between 3000-3750 cm-1 and 2940-2820 cm-1, which were attributed to OH. The peaks at 1730-1640 cm-1 can be related to carbonyl groups (C=O) or aromatic C C. The peaks at 1499 and1595 can be attributed to axial strain of aromatic C=C, and are more defined to LY, IA and IO, respectively. The band at 1260 and 1000 cm-1 was related to the axial strain of C-O bound from phenol and OH. It is worthy of mention that there are considerable differences between LY and the other bioabsorbents inactivated by heating, which confirms that the inactivation methods change the available sorption sites.

The diverse characteristics of sorption sites presented by the materials submitted to different biological inactivation processes could be related to the denaturation of protein and carbohydrate chains, disrupting the cell wall, which can expose different sites not previously accessible to the Biosorption (Halasz and Lasztity, 1991).

Figure 2. Titration curves of acidic sites for IA = Inactivated by Autoclave, IO = Inactivated by Oven, RY = Residue of Yeast from ethanol industry and LY = Live Yeast (n = 3). 

Table 2. Sorption sites (Sn) characterized by potentiometric titration for S. cerevisiae alive and inactivated by diverse processes. 

Figure 3. Fourier Infrared spectra presenting the main functional groups for A) LY = Live Yeast, B) IA = Inactivated by Autoclave, C) IO = Inactivates by Oven, D) RY = Residue of Yeast from ethanol industry. Resolution: 4 cm-1 at 20 scans min-1

4. Conclusions

Different kinds of heating have been used to inactivate biological material employed as biosorbent. The influence of the different kinds of heating should be monitored because these procedures can affect the sorption sites and their distribution on the biosorbents, modifying sorption capacities and the mathematical models that describe the biosorption phenomena. Overall, inactivation in an autoclave promotes the largest uptake of toxic metals.

5. ACKNOWLEDGEMENTS

The authors are gratefully to FAPESP (Proc. 2007/53860-6) and CNPq for students fellowships.

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Received: December 09, 2014; Accepted: April 16, 2015

* Autor correspondente: Geórgia Labuto, e-mail: geolabuto@gmail.com

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