Pre-concentration and determination of tartrazine dye from aqueous solutions using modified cellulose nanosponges

Ecotoxicology and Environmental Safety 135 (2017) 123–129

Contents lists available at ScienceDirect

Ecotoxicology and Environmental Safety journal homepage: www.elsevier.com/locate/ecoenv

Pre-concentration and determination of tartrazine dye from aqueous solutions using modified cellulose nanosponges Roohollah Shiralipour a, Arash Larki b,n a

Food and Drug Safety Evaluation Research Center of Jundishapur University of Medical Sciences, Ahvaz, Iran Department of Marine Chemistry, Faculty of Marine Science & Marine Science Research Institute, Khorramshahr University of Marine Science and Technology, Khorramshahr, Iran

b

art ic l e i nf o

a b s t r a c t

Article history: Received 13 November 2015 Received in revised form 29 September 2016 Accepted 30 September 2016

In this study, a new absorbent based on cellulose nanosponges modified with methyltrioctylammonium chloride (aliquat 336) was prepared and used for pre-concentration, removal and determination of tartrazine dye, using UV–vis spectrophotometry. This adsorbent was fully characterized using various instrumental techniques such as SEM, FTIR and XRD spectra. The pre-concentration and removal procedures were studied in column and batch modes, respectively. The effects of parameters such as pH of the aqueous medium, methyltrioctylammounium chloride dose, adsorbent amount, desorbing conditions and interfering ions on the adsorption of tartrazine were investigated and optimized. The fitting experimental data with conventional isotherm models revealed that the adsorption followed the BrunauerEmmett-Teller (BET) model and the maximum adsorption capacity for tartrazine was 180 mg/g with modified nanosponges. Under the optimized conditions, the calibration curve was linear over the range of 2–300 ng/mL and the limit of detection was 0.15 ng/mL. The relative standard deviation (RSD) for 20 and 100 ng/mL of tartrazine were 3.1% and 1.5%, respectively. The proposed method was applied for preconcentration and determination of tartrazine dye in different water samples. & 2016 Elsevier Inc. All rights reserved.

Keywords: Tartrazine Cellulose nanosponges Aliquat 336 Methyltrioctylammounium chloride Brunauer-Emmett-Teller

1. Introduction Synthetic dyes have been used instead of natural colors because of their high stability to light, oxygen, heat and pH, color uniformity and relatively lower costs. Tartrazine (E102) is a synthetic lemon yellow azo dye which has been widely used as an additive in food, drinks, medicine and cosmetics. Tartrazine appears to cause the allergic and intolerance reactions, chiefly affecting individual’s allergy to aspirin (Gupta et al., 2011). Recently, studies show that this dye poses potential risks to human health, especially when consumed in excess, due to the significant adverse effects on neurobehavioral parameters. However, presence and content of this dye must be controlled due to its potential harmfulness to human beings (Abu Shawish et al., 2013). Several analytical techniques have been used for the determination of tartrazine dye, including spectrophotometry (Sahraei et al., 2013; Dinc et al., 2002), chromatography (Wu et al., 2013; Alves et al., 2008), electroanalytical methods (Gan et al., 2012; Ye et al., 2013) and capillary electrophoresis (Perez-Urquiza et al., 2000). However, most of these methods are expensive, long analysis n

Corresponding author. E-mail addresses: [email protected], [email protected] (A. Larki).

http://dx.doi.org/10.1016/j.ecoenv.2016.09.038 0147-6513/& 2016 Elsevier Inc. All rights reserved.

time and sometimes it is necessary to make sample pretreatments. On the other hand, the combination of simple methodologies, such as spectrophotometric methods with pre-concentration techniques, represents a rapid, simple and cheap strategy for the determination of dyes (Pourreza et al., 2008). According to the above-mentioned reasons, determination of tartrazine requires a fast, simple, low-cost and reliable method, which can be used routinely. Among the several techniques, solid phase extraction (SPE) has been generally used as a pre-concentration procedure for various target analytes. This widespread use of SPE is due to its wellknown advantages such as simplicity, high enrichment factor, good recovery, low consumption of organic solvents, suitability for combination with different detection techniques and relatively low cost (Herrero Latorre et al., 2013). The basic principle of SPE is the transfer of analytes from the sample solution phase to bind to the active site of the solid phase (Pourreza et al., 2014). Nanotechnology and nanoparticles are increasingly recognized for their potential applications in different branches of science. In the recent years, nanoparticles-based SPE offers great possibilities for development of new analytical methodology, because of their unique properties, such as their large surface areas and high adsorption capacity (Parham et al., 2012). Nanosponges (NSs) are a new class of tiny sponges which are made of microscopic particles with cavities a few nanometers wide, characterized by the capacity

124

R. Shiralipour, A. Larki / Ecotoxicology and Environmental Safety 135 (2017) 123–129

to encapsulate a large variety of substances that can be transported through aqueous media. NSs are highly efficient at entrapping different types of molecules (both organic and inorganic), and they can accomplish this by inclusion or non-inclusion complex formation (Lembo et al., 2013). These sorbents have been prepared by various chemical and physical techniques (Rojas et al., 2009; Watthanaphanit et al., 2010; Berry et al., 2006; Ma et al., 2005; Jiang et al., 2013; Wang et al., 2012; Mishra et al., 2011), and applied in drug therapy (Farooq et al., 2013; Bolmal et al., 2013; Naga et al., 2013; Rapolu et al., 2012), environmental studies (Mhlanga et al., 2007; Kozlowska et al., 2012–2013; Allabashi et al., 2007) and metal analysis (Yavuz et al., 2014). In the present work, we focus on the potential application of new cellulose acetate-based nanosponges (CNSs) as novel solid phase. The prepared CNSs were modified with methyltrioctylammonium chloride (aliquat 336) and used for the removal, pre-concentration and determination of tartrazine dye, with UV–vis spectrometer detection. The parameters which affect the adsorption and elution efficiency of tartrazine were studied in batch and column modes.

2. Experimental 2.1. Apparatus A Hach DR5000 UV–Visible Spectrophotometer (USA) was used for recording the spectra and the absorbance measurements of tartrazine, with 1.0 cm cell. The scanning electron microscope (SEM, Leo, 1455 VP, Germany) was performed to study the morphology of synthesized modified cellulose acetate nanosponges. The infrared spectra were obtained using a FTIR (BRAIC WQF-510, China) to identify the functional groups and chemical bonding of the modified materials. An IKA Works KS 130 Orbital Shaker (IKA Works Basic Model), a Jenway stirrer model 1000 (UK) and a Metrohm pH meter model 827 (Switzerland) were used during the experiments.

(at 500 X), resulting in the formation of the CNSs. The prepared CNSs were filtered through a filter paper (Whatman No. 41) and rinsed with water for several times to remove the excess of the acetic acid. The washed CNSs were poured in the 200 mL of 5 M of KOH solution, and then the mixture was stirred for 24 h, filtered and afterward washed with excess water. In the next step, the obtained alkalized CNSs were added to the methyltrioctylammounium chloride solution (containing 0.5 g methyltrioctylammounium chloride in 200 mL water) and the mixture was stirred for 15 h. After this period, filtering-washing procedure was repeated on the modified-cellulose nanosponges (m-CNSs) to remove the extra of the methyltrioctylammounium chloride. The resulting M-CNSs were dispersed in 20 mL of water, so one milliliter of this solution contained almost 1 mg of M-CNSs. 2.5. Adsorption procedure The adsorption of tartrazine by M-CNSs was performed by a batch procedure at room temperature. A beaker containing 50 mL solution of tartrazine 5.0 mg/L (pH 1.5), was shaken (400 X) with 5.0 mg of M-CNSs for 100 min. After this time the initial yellow colored solution became colorless; the nanosponges were collected using passed through a filter paper. Then, the residual concentration of the tartrazine in the supernatant solution was determined by UUV–Visspectrophotometer at 427 nm. The removal efficiency of tartrazine by the M-CNSs adsorbent was calculated according to the following equation:

R% =

C0 − Ct × 100 C0

Where R is the removal efficiency of the tartrazine, C0 is the initial concentration of tartrazine (mg/L), and Ct is the concentration of tartrazine (mg/L) remaining in the solution. 2.6. Pre-concentration and recovery procedure

All chemicals were of analytical grade were purchased from Merck (Merck, Darmstadt, Germany) and double distilled water was used throughout. A stock solution of 500 mg/L of tartrazine was prepared by dissolving 0.050 g of the tartrazine dye in water and diluting to 100 mL in a volumetric flask. More diluted solutions were prepared daily using this stock solution. Alkyl dimethyl benzyl ammonium chloride (ADBAC), methyltrioctylammonium chloride (aliquat 336), Acetic acid (glacial) 100% and potassium hydroxide were used. The cellulose acetate was obtained from waste photographic film tapes. In all materials, reporting of genetic description was not observed.

This procedure was carried out using a polyethylene tube (5 cm length and 1 cm inner diameter) with a very fine bore. The outlet of the column was fitted with the glass wool, and then filled with the 5.0 mg of the M-CNSs solution (equivalent to 5.0 mL). To perform pre-concentration, 200 mL of tartrazine solutions (containing 2– 300 ng/mL) which has been equilibrated at pH 1.5 were passed through the column, at a flow rate 3.0 mL/min. Then, the column was washed with 4.0 mL of ADBAC solution (8% w/w) to release the dye retained in the column and its absorbance determined by UUV– Visspectrophotometer. A blank solution was also prepared under the same analytical conditions without adding any tartrazine dye. The recovery of tartrazine adsorbed on the M-CNSs was calculated from its amount in the starting sample and eluted from the column.

2.3. Preparation of cellulose acetate solution

2.7. Sampling

The cellulose acetate was treated by sodium hypochlorite solution (5%) in order to remove colored gelatinous layers. The transparent films were fragmented and washed by detergent solution and water several times. The cleaned discolored cellulose acetate films were dried in oven at 50 °C for 1 h. Finally, 0.5 g of fragmented cellulose acetate films was dissolved in 500 mL glacial acetic acid and then kept in an appropriate container prior to use.

The proposed method was applied to different water samples including, Karoon River water (Khuzestan Province, Ahvaz, Iran), Caspian Sea (northern Iran) and waste water of beverage factory (Khuzestan Province, Ahvaz, Iran). All water samples were filtered through a 0.45 mm cellulose acetate membrane filter and the pre-concentration procedure was performed on the samples as described above.

2.2. Reagents

2.8. PZC experiment 2.4. Preparation of modified cellulose nanosponges The cellulose acetate nanosponges (CNSs) were prepared according to immersion-precipitation method (Reuvers et al., 1987). In order to achieve 20 mg CNSs, 20 mL of the prepared cellulose acetate solution (in previous section) was rapidly injected into 300 mL stirring water

To obtain more information about the surface of the M-CNSs, an experiment to obtain its PZC was performed. In such experiment, 5.0 mg of this material were shaken up with 10.0 mL of the solutions whose pH varied from 1 to 10. The pH of the solutions was adjusted by the addition of HCl and NaOH solutions, and the

R. Shiralipour, A. Larki / Ecotoxicology and Environmental Safety 135 (2017) 123–129

125

material samples were shaken up for 24 h before measuring the final pH (Pourreza et al., 2010; Wondracek et al., 2016).

3. Results and discussion 3.1. Characterization of M-CNSs The FT-IR spectrum of cellulose acetate (Fig. 1A) exhibits the characteristic vibrational peaks including, stretching of C–O at 1040 and 1237 cm
1 (for alkoxy and acyl group), stretching of C ¼O at 1756 cm
1and bending C–H sp3 at 1377 cm
1. It is found that desertification of cellulose acetate with KOH removes the acetate groups of cellulose acetate and converted this structure to cellulose, so elimination of these peaks at 1237 and 1756 cm
1 of Fig. 1B is an evidence of this conversion. Afterward, the alkalized cellulose acetate was stirred in the presence of methyltrioctylammounium chloride and it snapped on the surface of cellulose, due to electrostatic interaction of nitrogen group of methyltrioctylammounium chloride and hydroxyl group of cellulose. Appearance of the peaks at 1470 cm
1 (for C–H scissoring) and three peaks in range of 2800–3000 cm
1 (for C–H stretching at alkanes) demonstrate the modification of surface of cellulose by methyltrioctylammounium chloride (Fig. 1C). The crystalline phase of nanosponges was characterized by powder X-ray diffraction (XRD) using a diffractometer. The X-ray diffractograms of CNs (before modification) and M-CNSs (after modification) are shown in Fig. 2a and b. CNSs displayed a diffraction spectrum with no sharp peak because of any crystallinity of cellulose acetate nanosponges. But M-CNSs revealed a different crystalline structure in the X-ray diffractogram and composed of two overlapped peaks at 20.1° and 22.4°, ascribed to cellulose reflection (Arkas and Tsiourvas, 2009). Perhaps the crystallinity of CNSs was increased after modification by methyltrioctylammonium chloride. The morphology of the synthesized M-CNSs was also examined by scanning electron microscopy (SEM). As shown in the Fig. 2c, M-CNSs have sponges structure with different sizes of nano cavities and particle pores lower than 100 nm. Finally, before the application of the modified material in adsorption experiments, an investigation to determine its PZC was performed. Depending on the pH of the medium, the surface can be positively, negatively, or even neutrally charged. As the pH of the medium increases above pHPZC (pH 4pHPZC), the surface of the materialattains a negative charge mainly due to phenomena such as deprotonation of surficial groups and/or adsorption of hydroxyl species. On the contrary, when the pH of the medium is below pHPZC (pH opHPZC), the surface of the material will be positively charged,

Fig. 2. X-ray diffraction of cellulose acetate nanosponges (a) before (b) and after modification with methyltrioctylammounium chloride, (c) the SEM image of modified cellulose acetate nanosponges.

which is due to the protonation of such surficial groups (Wondracek et al., 2016; Pourreza et al., 2010). From obtained results presented in Fig. 3a, the pHPZC was calculated as the average of the final pH values measured in the range in which such values remained almost constant. Therefore, the pHPZC of the M-CNSs was 4.0. 3.2. Effect of pH The pH of the loading solution plays an important role in the adsorption process of the dye on the adsorbent and this parameter should be investigated. Thus, the effect of pH on the adsorption of tartrazine on the M-CNSs was studied in the range of 1.0–9.0, by the addition of diluted nitric acid and sodium hydroxide solutions. The obtained results revealed that, the highest adsorption of tartrazine was achieved in an acidic medium. It is well known that, the sulfonate groups of tartrazine will not be changes at low pH and they will remain in their anionic form. So, anionic form of tartrazine dye via electrostatic attraction can be absorbed on the surface of adsorbent. To identify a suitable acidic medium, the effect of different concentrations of nitric acid was investigated in the range of 0.0– 0.05 M. The achieved results show, the absorbance increased by increasing nitric acid concentration up to 0.02 M and it was almost constant after this value. Thus, this concentration of HNO3 in the final solution selected as the optimum value for further studies. 3.3. Effect of M-CNSs amount as adsorbent

Fig. 1. FT-IR specta of (A) cellulose acetate nanosponges, (B) alkalized cellulose acetate nanosponges and (C) modified cellulose nanosponges with Methyltrioctylammounium chloride.

The influence of adsorbent dosage for effective adsorption of tartrazine was investigated in the range of 1.0–10.0 mg. The results shown in Fig. 3b indicated that the recovery of the eluted dye is almost constant when the amount of the adsorbent is greater than 5.0 mg. Therefore, in this procedure 5.0 mg of adsorbent was

126

R. Shiralipour, A. Larki / Ecotoxicology and Environmental Safety 135 (2017) 123–129

solution containing 100 ng/mL of tartrazine was passed through the column with the flow rate adjusted in the range 1–6 mL/min. The results (Fig. 3c) revealed that the recovery did not change up to 2.0 mL/min and decreased at higher flow rates, because there is not sufficient contact time between the sample solution and adsorbent. Therefore a flow rate of 2 mL/min was used for following experiments. 3.6. The effect of sample volume In the pre-concentration procedure, it is desired to request high breakthrough volume and also high pre-concentration factor so that lower concentrations can be analyzed. For this aim, recommended procedure was carried out for sample volumes of 50–250 mL containing the same amounts of tartrazine. The recovery of the eluted solution from the column was constant for sample volumes up to 200 mL and decreased after this value. Hence, 200 mL was chosen as the largest applicable sample volume and, by using 4.0 mL of elution solution, a pre-concentration factor of 50 was achieved. 3.7. Reusability of the M-CNSs In SPE procedures, the ability of the adsorbents to be used in several successive adsorption and desorption processes should also be investigated. Therefore, after passing the tartrazine solution through the column and regeneration by ADBAC solution, the above procedure was repeated many times. The obtained results showed that the modified cellulose nanosponges can be reused for three times (99%, 96.5% 92.7% and 87.1%) without a considerable loss in their recoveries. 3.8. Study of interferences

Fig. 3. (a) The pH of PZC for M-CNSs, (b) The effect of adsorbent amount on the recovery of tartrazine and (c) Effect of sample flue rate on the pre-concentration and determination of tartrazine.

selected as the optimum. It is possible to use higher amounts of the adsorbent, which would be capable of retaining efficiently both low and high concentrations of the analyte, however higher adsorbent amount would also affect the loading flow rate. 3.4. Effect of desorption conditions In order to desorb of tartrazine from M-CNSs, same volume of different reagents such as EDTA, isopropanol, ADBAC solution and triton X-100 (4% v/v) were tested. The desorption efficiency for EDTA, isopropanol and triton X-100 after passing through the column was found to be lower than 70%, but for ADBAC solution was higher than 90%. Thus, ADBAC solution, as a most effective eluent, was used for desorption of tartrazine dye from M-CNSs. Thereafter, various volumes and concentrations of ADBAC solution [0.5 to 10.0% (w/v)] in the range of 1.0–6.0 mL were used. The results showed that the maximum recovery of tartrazine was obtained when concentration of 8.0% (w/v) applied. According to the obtained results and for attaining high pre-concentration factor and recovery, 4.0 mL of ADBAC solution (8% w/v) was selected for subsequent measurements. 3.5. Effect of sample flue rate The retention of the tartrazine depends upon the flow rate of the sample solution and so the effect of this parameter was examined by applying the recommended procedure and using a pump. The 200 mL

The optimum experimental conditions which have been described were used to study the interfering effect of some ions and four dyes (amaranth, aniline blue, methylene blue and neutral red) on the pre-concentration and determination processes of tartrazine. A constant concentration of tartrazine (100 ng/mL) was taken with different concentrations of interfering reagent and the general procedure was followed. The tolerance limit was defined as the maximum concentration of potentially interfering reagent causing an error of 75% in the determination of tartrazine. It was proved that, Na þ , SO42-, CO32-, K þ , Mg2 þ , Ca2 þ , NO3-, K þ were tolerated up to 1000 mg/L, Cu2 þ , Mg2 þ , Fe3 þ , Zn2 þ , Co2 þ tolerated up to 600 mg/L, NH4 þ , Ag þ , Al3 þ , Mn2 þ , HCO3-, I- tolerated up to 300 mg/L, PO43-, Ni2 þ , Hg2 þ tolerated up to 200 mg/L and Cd2 þ , Pb2 þ , F-, Br- tolerated up to 100 mg/L. Also, some common dyes such as methylene blue, aniline blue, neutral red and amaranth were examined it was found that they did not interfere at concentrations at least 50, 20, 10 and 2 mg/L, respectively. 3.9. Analytical parameters and applications Under the optimum experimental conditions, the proposed analytical method was validated by calculated precision (RSD), linear dynamic range and limit of detection (LOD). The calibration graph was linear in the range 2–300 ng/mL for a 200 mL sample. The limit of detection (LOD), defined as LOD ¼3 Sb/m, where Sb and m are the standard deviation of the blank and the slope of the calibration graph, respectively, was 0.15 ng/mL. The relative standard deviation (RSD) for six replicate measurements of 20 ng/mL and 100 ng/mL of tartrazine were 3.1% and 1.5%, respectively. As the amount of tartrazine in 200 mL of the solution was concentrated to 4 mL, maximum pre-concentration factor of the method is 50. In order to evaluate the analytical applicability of the proposed method, it was applied to the determination of tartrazine in different water and wastewater samples. In addition, known amounts

R. Shiralipour, A. Larki / Ecotoxicology and Environmental Safety 135 (2017) 123–129

3.11. Adsorption kinetics

Table 1 Results for the determination of tartrazine in different water samples. Sample

Added (ng/mL)

Founda (ng/mL)

Recovery (%)

Karoon river

0 20 0 20 0 20

– 19.0 7 0.2 – 19.6 7 0.2 – 20.2 7 0.3

– 95.0 – 98.0 – 101.0

Caspian sea Karoon river

a

In order to predict adsorption kinetic models of tartrazine solutions, pseudo-first order and pseudo-second-order kinetic models were applied to the data. The Lagergren pseudo-first order model is shown by the equation (Hashemian and Salimi., 2012);

(

)

log qe − qt = logqe −

Mean 7 standard deviation (n¼ 3)

of tartrazine were spiked to different samples for the recovery tests. The results are given in Table 1, as can be seen good recoveries are obtained by the proposed method, which indicate there is no serious interference in such water samples. 3.10. Adsorption isotherm

K1t 2.303

(1)

Where qe and qt are the amounts of dye adsorbed onto M-CNSs (mg g
1) at equilibrium and at time t, respectively and k1 (min
1) is first order rate constant for adsorption. The rate constant, k1, can be calculated from the plots of log (qe
qt) versus t. The following equation stands for the linear form of the pseudo-second order model (Yola et al., 2014);

1 t t = + q2 qt k2q22

(2)
1

Adsorption isotherm models are basis to describing the interactive behavior between of adsorbate and adsorbent, and are also significant for investigating mechanisms of adsorption. In this study, different concentrations of tartrazine dye in the range of 2– 30 mg/L (at pH 1.5) were loaded on the adsorbent at 100 min times and the concentration of tartrazine in the solution at equilibrium (Ce) was determined by UUV–visspectrophotometer. Afterward, equilibrium data were analyzed using the Langmuir, Freundlich and Brunauer-Emmett-Teller (BET) isotherms. The Langmuir isotherm is referred to monolayer adsorption on homogenous surface of an adsorbent, while Freundlich and BET isotherms are mentioned by multilayer adsorption on heterogeneous surfaces via chemisorption and physisorption processes, respectively (Brunauer et al., 1938). The results showed that the adsorption of tartrazine was correlated well with the BET model equation (R2 ¼ 0.9994) compared to the Langmuir (R2 ¼0.9671) and Freundlich (R2 ¼ 0.9539) models in the studied concentrations. The BET isotherm equation has been applied to explain the correlation between the quantity of tartrazine molecules adsorbed and their equilibrium concentration in solutions (Foo and Hameed, 2010):

Ce (C −1) C 1 = + BET × e qe(CS − C ) qS CBET qS CBET CS Where, CBET, Cs, qs and qe are the BET adsorption isotherm (L/mg), adsorbate monolayer saturation concentration (mg/L), theoretical isotherm saturation capacity (mg/g) and equilibrium adsorption vs. capacity (mg/g), respectively. The equation from plot the Ce qe(CS −C )

Ce CS

127

is y¼0.0055 x þ3  10
5, which from it CBET and qs were cal-

culated 184 and 180, respectively. The obtained results of the Langmuir, Freundlich and BET isotherms are given in Table 2.

where qe is the maximum adsorption capacity (mg g ); qt is the amount of dye adsorbed per unit mass of the adsorbent (mg g
1); k2 is the rate constant of the pseudo-second order equation (g mg
1 min
1). In pseudo-first order model; the kinetic parameter of qe and k1 were calculated 51.76 and 0.049, respectively. Whereas, this parameter in pseudo-second order kinetic model (containing qe and k2) were 89.28 and 0.001. The correlation coefficient of the pseudo-first order model (0.973) is lower than that of the pseudo-second order kinetic model (0.998), indicating that the adsorption process on M-CNSs is pseudo- second order.

4. Conclusion In summary, we have presented and successfully employed a simple, cost-effective and environment-friendly nanosponge as solid phase for the pre-concentration and following determination of tartrazine dye, in addition to its removal from aqueous solutions. To the best of our knowledge, this is the first paper on the use of modified cellulose nanosponges (m-CNSs) as a green adsorbent for separation, pre-concentration and consequent determination of tartrazine dye. The BET isotherm gave best fit for the adsorption data than Langmuir and Freundlich isotherm that this fact may be attributed to physisorption of tartrazine to the adsorbent. The results indicated that the adsorption of tartrazine data follow pseudo-second order kinetics. The proposed method has advantages of good accuracy, high pre-concentration factor, simple procedure which uses a very small amount of adsorbent and gives low detection limit. Some characteristics of previously reported methods such as limit of detection and linearity were summarized in Table 3 for the comparison. As it can be seen, the suggested pre-concentration method in this work showed an appropriate linearity in comparison to the previous methods and had relative low limit of detection for the pre-concentration of

Table 2 The results of adsorption isotherms(Langmuir, Freundlich and BET). Initial conc. (mg/L)

20 50 100 150 200 250 300

C (mg/L)

0.055 9.526 42.156 79.25 117.37 157.24 199.57

q (mg /g adsorbent)

105.7249 214.5455 306.6207 375.0331 438.0069 491.7042 532.3615

Langmuir

Freundlich

BET

C/q

Ln C

Ln q

C/C0

C/q (C0
C)

0.00052 0.044401 0.137486 0.211315 0.267964 0.319786 0.374877


2.90042 2.254025 3.741377 4.372607 4.765331 5.057773 5.296165

4.66084 5.368522 5.725612 5.927014 6.082235 6.197877 6.277323

0.00275 0.19052 0.42156 0.528333 0.58685 0.62896 0.665233

2.60826 E
05 0.001097021 0.002376838 0.00298678 0.003242936 0.003447453 0.003732718

128

R. Shiralipour, A. Larki / Ecotoxicology and Environmental Safety 135 (2017) 123–129

Table 3 Comparison of the published methods with the proposed method in the determination of tartrazine. Type of method

L.O.D (ng/mL)

Linear range (ng/mL)

Ref.

AgNPs-based Spect. UUV– Vis IL-DLLME- UUV–Visa Modified GC-RDEb Boron-doped diamond electrode HPLC-UV

0.3

0.7–360

Sahraei et al., 2013

0.15 6.5 1300

0.5–2000 25–10000 2600–32000

40

50–20000

4.0

16–2600

Wu et al., 2013 Ye et al., 2013 Medeiros et al., 2012 Yoshioka and Ichihashi, 2008 Zhao et al., 2014

3.2 0.05 0.15

10–1100 0.61–2000 2–300

Gan et al. 2013 Sha et al., 2015 This work

MIP–MWNTs-IL@PtNPs/ GCEc Electrochemical sensor IL-LLEd-HPLC M-CNSs SPE- spect. UUV– Vis a

Ionic liquid dispersive liquid phase microextraction. Glassy carbon-rotating disk electrode. Molecular imprinted polymer – multiwalled carbon nanotubes - ionic liquid supported Pt nanoparticles composite film coated glassy carbon electrode. d Ionic liquid liquid–liquid microextraction. b c

Table 4 Comparison of the published methods with the proposed method in the removal of. Adsorbents

Maximum adsorption capacity (mg/g)

adsorbent dose (g)

time

Ref.

Activated carbon Commercial activated carbon Chitin Chitosan Amberlite IRA910 Chitosan coated bentonite Hen feather M-CNSs This work

90.90

0.2

30 min

121.3

1.0

24 h

30 350 49.96

0.25 0.25 0.25

30 min 30 min 30 min

294.1

0.01

80 min

Kumar Gautam et al., 2015 Monser and Adhoum, 2009 Dotto et al., 2012 Dotto et al., 2012 Wawrzkiewicz and Hubicki, 2009 Ngah et al., 2010

64.1 180

0.01 0.005

24 h

Mittal et al., 2007 100 min

tartrazine. In addition to, for investigation of usability of M-CNSs adsorbent in the removal of tartrazine from aqueous solutions, a comparison between the proposed method and reported methods are given in Table 4. According to several studies listed, the maximum adsorption capacity of M-CNSs is a similar or better compared to other adsorbents. Finally, the proposed method was applied for determination of tartrazine in different water samples.

Acknowledgement The authors are sincerely grateful to Food and Drug Safety Evaluation Research Center of Jundishapur University of Medical Sciences and Khorramshahr University of Marine Science and Technology for providing research facility for this project.

References Abu Shawish, H.M., Abu Ghalwa, N., M. Saadeh, S., El Harazeen, H., 2013. Development of novel potentiometric sensors for determination of tartrazine dye concentration in foodstuff products. Food Chem. 138, 126–132. Allabashi, R., Arkas, M., Hörmann, G., Tsiourvas, D., 2007. Removal of some organic pollutants in water employing ceramic membranes impregnated with crosslinked silylated dendritic and cyclodextrin polymers. Water Res. 41, 476–486.

Alves, S.P., Brum, D.M., de Andrade, E.C.B., Pereira Netto, A.D., 2008. Determination of synthetic dyes in selected foodstuffs by high performance liquid chromatography with UV-DAD detection. Food Chem. 107, 489–496. Arkas, M., Tsiourvas, D., 2009. Organic/inorganic hybrid nanospheres based on hyperbranchedpoly (ethylene imine) encapsulated into silica for the sorption of toxic metal ions and polycyclic aromatic hydrocarbons from water. J. Hazard. Mater. 170, 35–42. Berry, S.M., Harfenist, S.A., Cohn, R.W., Keynton, R.S., 2006. Characterization of micromanipulator–controlled dry spinning of micro- and sub-microscale polymer fibers. J. Micromech. Microeng. 16, 1825–1832. Brunauer, S., Emmett, P.H., Teller, E., 1938. Adsorption of gases in multimolecular layers. JACS 60, 309–319. Bolmal, U.B., Manvi, F.V., Rajkumar, K., Palla, S.S., Paladugu, A., Reddy, K.R., 2013. Recent advances in nanosponges as drug delivery system. Int. J. Pharm. Sci. Nanotechnol. 6, 1934–1944. Dinc, El, Baydan, E., Kanbur, M., Onur, F., 2002. Spectrophotometric multicomponent determination of sunset yellow, tartrazine and allura red in soft drink powder by double divisor-ratio spectra derivative, inverse least-squares and principal component regression methods. Talanta 58, 579–594. Dotto, G.L., Vieira, M.L.G., Pinto, L.A.A., 2012. Kinetics and mechanism of tartrazine adsorption onto chitin and chitosan. Ind. Eng. Chem. Res. 51, 6862–6868. Farooq, S.A., Saini, V., Singh, R., Kaur, K., 2013. Application of novel drug delivery system in the pharmacotherapy of hyperlipidemia. J. Chem. Pharm. Sci. 6, 138–146. Foo, K.Y., Hameed, B.H., 2010. Insights into the modeling of adsorption isotherm systems. Chem. Eng. J. 156, 2–10. Gan, T., Sun, J., Cao, Sh, Gao, F., Zhang, Y., Yang, Y., 2012. One-step electrochemical approach for the preparation of grapheme wrapped-phosphotungstic acid hybrid and its application for simultaneous determination of sunset yellow and tartrazine. Electrochim. Acta 74, 151–157. Gan, T., Sun, J., Meng, W., Song, L., Zhang, Y., 2013. Electrochemical sensor based on graphene and mesoporous TiO2 for the simultaneous determination of trace colourants in food. Food Chem. 141, 3731–3737. Gupta, V.K., Jain, R., Nayak, A., Agarwal, Sh, Shrivastav, M., 2011. Removal of the hazardous dye-Tartrazine by photodegradation on titanium dioxide surface. Mater. Sci. Eng. C. 31, 1062–1067. Hashemian, S., Salimi, M., 2012. Nano composite a potential low cost adsorbent for removal of cyanine acid. Chem. Eng. J. 188, 57–63. Herrero Latorre, C., Barciela Garcia, J., Garcia Martin, S., Pena Crecente, R.M., 2013. Solid phase extraction for the speciation and preconcentration of inorganic selenium in water samples: a review. Anal. Chim. Acta 804, 37–49. Jiang, P., Lin, L., Zhang, F., Dong, X., Ren, L., 2013. Changjian Lin, Electrochemical construction of micro-nanospongelike structure ontitanium substrate for enhancing corrosion resistance and bioactivity. Electrochim. Acta 107, 16–25. Kozlowska, J., Koldziejska, M., Moryn, S., Sliwa, W., 2012-2013. Selected applications of cyclodextrin polymers. Ars Sep. Acta 9–10, 37–54. Kumar Gautam, R., Kumar Gautam, P., Banerjee, S., Rawat, V., Soni, Sh, Sharma, S.K., Chattopadhyaya, M.Ch, 2015. Removal of tartrazine by activated carbon biosorbents of Lantana camara: kinetics, equilibrium modeling and spectroscopic analysis. J. E. C. E. 3, 79–88. Lembo, D., Swaminathan, Sh, Donalisio, M., Civra, A., Pastero, L., Aquilano, D., Vavia, P., Trotta, F., Cavalli, R., 2013. Encapsulation of Acyclovir in new carboxylated cyclodextrin-based nanosponges improves the agent's antiviral efficacy. Int. J. Pharm. 443, 262–272. Ma, Z., Kotaki, M., Ramakrishna, S., 2005. Electrospun cellulose nanofiber as affinity Membrane. J. Membr. Sci. 265, 115–123. Medeiros, R.A., Lourencao, B.C., Rocha-Filho, R.C., Fatibello-Filho, O., 2012. Flow injection simultaneous determination of synthetic colorants in food using multiple pulse amperometric detection with a boron-doped diamond electrode. Talanta 99, 883–889. Mhlanga, S.D., Mamba, B.B., Krause, R.W., Malefetse, T.J., 2007. Removal of organic contaminants from water using nanospongecyclodextrin polyurethanes. J. Chem. Technol. Biotechnol. 82, 382–388. Mishra, S.P., Thirree, J., Manent, A., Chabot, B., Daneault, C., 2011. Ultrasound-catalyzed tempo-mediated oxidation of native cellulose for the production of nanocellulose: effect of process variables. Bioresources 6, 121–143. Mittal, A., Kurup, L., Mittal, J., 2007. Freundlich and Langmuir adsorption isotherms and kinetics for the removal of Tartrazine from aqueous solutions using hen feathers. J. Hazard. Mater. 146, 243–248. Monser, L., Adhoum, N., 2009. Tartrazine modified activated carbon for the removal of Pb(II), Cd(II) and Cr(III). J. Hazard. Mater. 161, 263–269. Naga, S.J., Nissankararao, S., Bhimavarapu, R., Sravanthi, L.S., Vinusha, K., Renuka, K., 2013. Nanosponges: a versatile drug delivery system. Int. J. Pharm Life Sci. 4, 2920–2925. Ngah, W.S.W., Ariff, N.F.M., Hanafiah, M.A.K.M., 2010. Preparation, characterization, and environmental application of crosslinked chitosan-coated bentonite for tartrazine adsorption from aqueous solutions. Water Air Soil Pollut. 206, 225–236. Parham, H., Zargar, B., Shiralipour, R., 2012. Fast and efficient removal of mercury from water samples using magnetic iron oxide nanoparticles modified with 2-mercaptobenzothiazole. J. Hazard. Mater. 205–206, 94–100. Perez-Urquiza, M., Beltran, J.L., 2000. Determination of dyes in foodstuffs by capillary zone electrophoresis. J. Chromatogr. A 898, 271–275. Pourreza, N., Rastegarzadeh, S., Larki, A., 2014. Simultaneous preconcentration of Cd (II), Cu(II) and Pb(II) on Nano-TiO2 modified with 2-mercaptobenzothiazole prior to flame atomic absorption spectrometric determination. J. Ind. Eng.

R. Shiralipour, A. Larki / Ecotoxicology and Environmental Safety 135 (2017) 123–129

Chem. 20, 2680–2686. Pourreza, N., Rastegarzadeh, S., Larki, A., 2008. Micelle-mediated cloud point extraction and spectrophotometric determination of rhodamine B using Triton X-100. Talanta 77, 733–736. Pourreza, N., Zolgharnein, J., Kiasat, A.R., Dastyar, T., 2010. Silica gel–polyethylene glycol as a new adsorbent for solid phase extraction of cobalt and nickel and determination by flame atomic absorption spectrometry. Talanta 81, 773–777. Rapolu, K., Aatipamula, V., Reddy, K.J., Voruganti, S., 2012. Cyclodextrins: nanocarriers for novel drug delivery. Int. J. Pharm. 2, 109–116. Reuvers, A.J., Smolders, C.A., 1987. Formation of membranes by means of immersion precipitation. J. Membr. Sci. 34, 67–86. Rojas, O.J., Montero, G.A., Habibi, Y., 2009. Electrospun nanocomposites from polystyrene loaded with cellulose nanowhiskers. J. Appl. Polym. Sci. 113, 927–935. Sahraei, R., Farmany, A., Mortazavi, S.S., 2013. A nanosilver-based spectrophotometry method for sensitive determination of tartrazine in food samples. Food Chem. 138, 1239–1242. Sha, O., Zhu, X., Feng, Y., Ma, W., 2015. Aqueous two-phase based on ionic liquid liquid–liquid microextraction for simultaneous determination of five synthetic food colourants in different food samples by high-performance liquid chromatography. Food Chem. 174, 380–386. Wang, Q.Q., Zhu, J.Y., Gleisner, R., Kuster, T.A., Baxa, U., McNeil, S.E., 2012. Morphological development of cellulose fibrils of a bleached eucalyptus pulp by mechanical fibrillation. Cellulose 19, 1631–1643. Watthanaphanit, A., Supaphol, P., Tamura, H., Tokura, S., Rujiravanit, R., 2010. Wet– spun alginate/chitosan whiskers nanocomposite fibers: preparation, characterization and release characteristic of the whiskers. Carbohydr. Polym. 79, 738–746. Wawrzkiewicz, M., Hubicki, Z., 2009. Removal of tartrazine from aqueous solutions by strongly basic polystyrene anion exchange resins. J. Hazard. Mater. 164,

129

502–509. Wondracek, M.H.P., Jorgetto, A.O., Silva, A.C.P., Ivassechen, J.R., Schneider, J.F., Saeki, M.J., Pedrosa, V.A., Yoshito, W.K., Colauto, F., Ortiz, W.A., Castro, G.R., 2016. Synthesis of mesoporous silica-coated magnetic nanoparticles modified with 4-amino-3-hydrazino-5-mercapto-1,2,4-triazole and its application as Cu(II) adsorbent from aqueous samples. Appl. Surf. Res. 367, 533–541. Wu, H., Guo, J., Du, L., Tian, H., Hao, Ch, Wang, Zh, Wang, J., 2013. A rapid shakingbased ionic liquid dispersive liquid phase microextraction for the simultaneous determination of six synthetic food colourants in soft drinks, sugar- and gelatin-based confectionery by high-performance liquid chromatography. Food Chem. 141, 182–186. Yavuz, E., Tokalıoğlu, Ş., Şahan, H., Patat, Ş., 2014. Nano sponge Mn2O3 as a new adsorbent for the preconcentration of Pd(II) and Rh(III) ions in sea water, wastewater, rock, street sediment and catalytic converter samples prior to FAAS determinations. Talanta 128, 31–37. Ye, X., Du, Y., Lu, D., Wang, Ch, 2013. Fabrication of β-cyclodextrin-coated poly (diallyldimethylammoniumchloride)-functionalized graphene composite film modified glassy carbon-rotating disk electrode and its application for simultaneous electrochemical determination colorants of sunset yellow and tartrazine. Anal. Chim. Acta 779, 22–34. Yola, M.L., Eren, T., Atar, N., Wang, Sh, 2014. Adsorptive and photocatalytic removal of reactive dyes by silver nanoparticle-colemanite ore waste. Chem. Eng. J. 242, 333–340. Yoshioka, N., Ichihashi, K., 2008. Determination of 40 synthetic food colors in drinks and candies by high-performance liquid chromatography using a short column with photodiode array detection. Talanta 74, 1408–1413. Zhao, L., Zeng, B., Zhao, F., 2014. Electrochemical determination of tartrazine using a molecularly imprinted polymer- multiwalled carbon nanotubes- ionic liquid supported Pt nanoparticles composite film coated electrode. Electrochim. Acta 146, 611–617.