- Research article
- Open Access
Determination of copper(II) by flame atomic absorption spectrometry after its perconcentration by a highly selective and environmentally friendly dispersive liquid–liquid microextraction technique
Journal of Analytical Science and Technologyvolume 10, Article number: 3 (2019)
A new, simple, rapid, selective, and environmentally friendly method is proposed for the determination of Cu(II) ions based on the formation of the complex between these ions and salophen as the ligand followed by the dispersive liquid–liquid microextraction of the neutral hydrophobic complex formed in the organic phase and flame atomic absorption spectrophotometric detection. Various factors including the pH of the sample solution, concentration of salophen as the complexing reagent, type and volume of the extraction and disperser solvents, and extraction time affecting the extraction efficiency of Cu(II) ions and its subsequent analytical signal were studied and optimized. Under the optimized experimental conditions, the detection limit (3σ) and the enrichment factor were obtained to be 0.60 μg L−1 and 49, respectively, for 10.0 mL of the sample solution. The consumptive index was 0.20 mL and the calibration graph was linear in the range of 3.0–120 μg L−1. The relative standard deviations for six replicate measurements of 5.0, 20.0, and 50.0 μg L−1 of Cu(II) ions were 4.1%, 1.5%, and 1.8%, respectively. The proposed method was also successfully applied for the extraction and determination of Cu(II) ions in different water and food samples with satisfactory results.
Copper is a significant heavy metal, required for the human body (Behbahani et al. 2014; Özzeybek et al. 2017). However, it can cause serious problems at excess amounts (Behbahani et al. 2014). Copper enters the environment via different human and natural activities (Özzeybek et al. 2017; Yin et al. 2016). The utilization of copper-polluted water with a dosage of more than the legal level (1.3 μg/mL (Yin et al. 2016)) causes risky problems like vomiting, nausea, blood cell damage, and kidney failure (Behbahani et al. 2014; Zhong et al. 2016). Thus determination of trace amounts of copper in different matrices is of great significance.
The most commonly used analytical techniques for determination of metals are graphite furnace atomic absorption spectrometry (GFAAS), flame atomic absorption spectrometry (FAAS), and inductively coupled plasma-optical emission spectrometry (ICP-OES). Nevertheless, because of the matrix interferences and/or the very low concentrations of metal ions, a direct determination of metal ions in water or food samples by the cited techniques is not always attainable (Fan et al. 2017). In order to solve these problems, a preconcentration and matrix elimination step is sometimes needed before applying the cited methods. Different separation and preconcentration techniques like the co-precipitation (Bader and Benkhayal 2014), liquid–liquid extraction (LLE) (Nishihama et al. 2001; Silvestre et al. 2009), and solid-phase extraction (Behbahani et al. 2014; Yin et al. 2016; Khalilian and Rezaee 2017) methods have been developed. However, the mentioned methods are laborious, time-consuming, and require a high volume of organic solvents (Khalilian and Rezaee 2016; Quigley et al. 2016). Recently, in order to solve such problems, the dispersive liquid–liquid microextraction (DLLME) technique has been developed by Assadi and co-workers (Rezaee et al. 2006). According to this method, a mixture of an extraction solvent (with a high density) and a disperser solvent (with a high miscibility) is rapidly injected via a syringe into the aqueous phase containing the analyte. During this injection, fine droplets of the extraction solvent dispersed throughout the aqueous sample are formed. At this stage, a cloudy solution is produced. Because of the formation of very small-sized droplets of the extraction solvent, a large surface area is formed between the extraction solvent and the aqueous phase, causing a very quick mass transfer of the analyte from the aqueous phase into the other phase; therefore, the extraction time is very short. The cloudy solution formed is subsequently centrifuged, as a result of which fine droplets are sedimented at the bottom of the conical test tube. Using a syringe, the sedimented phase is removed. The analytes in the enriched phase can then be determined by different analytical methods like GFAAS, FAAS, high-performance liquid chromatography (HPLC), and gas chromatography (GC) (Zhong et al. 2016; Rezaee et al. 2010; El-Shahawi and Al-Saidi 2013; Ming-Jie et al. 2015).
The advantages of the DLLME method are the simplicity of the operation, a short extraction time, a low volume of the organic solvent, a high enhancement factor, low-cost apparatus, and a green method because of the minimizing of consumption of harmful solvents (Özzeybek et al. 2017; Khalilian and Rezaee 2016; Jalbani and Soylak 2015; Reclo et al. 2017; Bahadir et al. 2018; Pouyan et al. 2016). The most significant advantage of these methods is that almost all of the total volume of the extraction phase can be introduced into the detection system, while only a limited volume of the extraction solvent is introduced in the conventional preconcentration and extraction methods (Yilmaz and Soylak 2016).
Thus in the present work, by considering the cited advantages, a new environmentally friendly procedure was developed for the pre-concentration and determination of trace amounts of copper. The method is based on the formation of a complex between Cu(II) ions and salophen molecules. The complex formed is then transferred into the organic phase using the DLLME technique, and is finally subjected to FAAS detection. Based on our literature survey, up to the present time, no report has been given for the separation and pre-concentration of trace amounts of copper using salophen as the chelating agent.
A Shimadzu flame atomic absorption spectrophotometer (model 760AA) equipped with an air-acetylene flame was used for absorbance measurements at a wavelength of 324.8 nm. The instrumental parameters were adjusted according to the manufacturer’s recommendations. A Metrohm (model 744) digital pH-meter equipped with a combined glass electrode-calomel (3 M KCl) was used for the pH adjustments. A Shimadzu UV-visible spectrophotometer (model UV-160) was used to record the absorption spectra.
Reagents and materials
2-Hydroxybenzaldehyde (salicylaldehyde) (≥ 99.0), 1,2-diaminobenzene (1,2-phenylenediamine) (≥ 99.0), carbon tetrachloride (≥ 99.0), chloroform (≥ 99.0), dichloromethane (≥ 99.0), acetone (≥ 99.5), methanol (≥ 99.5), ethanol (≥ 99.5), acetonitrile (≥ 99.5), and potassium nitrate (≥ 99.0) were supplied from Merck (Darmstadt, Germany), and they were used as received. Doubly distilled water was used throughout the work.
A stock standard solution of Cu(II) ions at a concentration of 1000 μg mL−1 was prepared from copper(II) sulfate anhydrous (≥ 99.0) (Merck), and the working standard solutions were obtained daily by stepwise dilutions of the stock solution with doubly distilled water.
Synthesis of salophen
N,N′-bis (salycilidene)-1,2-phenylenediamine (salophen) was synthesized (Mirkhani et al. 2007) and purified in ethanol as what follows.
Salicylaldehyde (2.44 g) and 1,2-phenylenediamine (1.08 g) were dissolved separately in 25 mL of ethanol. The salicylaldehyde solution was added dropwise to the solution of 1,2-phenylenediamine, and the mixture was refluxed for 3 h. The reaction mixture was then cooled down, and the resulting bright yellow precipitate was separated by filtration. For purification of salophen, the precipitate was dried and recrystallized twice in ethanol. The resulting product (salophen) was characterized by an FT-IR spectrometer, and it had a melting point range of 164–166 °C. A solution of 0.010 M salophen was prepared by dissolution of 0.0790 g of salophen in acetonitrile and it was diluted in a 25-mL volumetric flask with acetonitrile.
General procedure for analysis
A 10.0-mL sample solution containing 3.0–120 μg L−1 of Cu(II) ions at pH = 2.0 was transferred into a glass test tube with a conical bottom, and 20.0 μL of a salophen solution in acetonitrile (0.010 M), used as the chelating agent, was added. Then 1.80 mL of a mixture of acetone (as the disperser solvent; 1.68 mL) and chloroform (as the extraction solvent; 120 μL) was rapidly injected into the sample solution using a syringe, and a stable cloudy solution (water, acetone, and chloroform) was obtained. The resulting Cu–salophen complex was extracted into the fine droplets of chloroform. The mixture was subsequently centrifuged for 5 min at 5000 rpm, and therefore, the extraction solvent (chloroform) containing the analyte was sedimented at the bottom of the conical test tube. The sediment phase (70 ± 3 μL) was then removed using a sampler, transferred into a vial, and diluted with 130 μL of ethanol. This solution was subsequently directly introduced into the flame atomic absorption spectrophotometer, and the absorbance of the sample solution was measured against the blank solution. The difference between the absorbance of the sample and blank solutions (∆A = As − Ab) at 324.8 nm was used as an analytical signal. A calibration curve was constructed by plotting the analytical signal versus the Cu(II) concentration in a series of working standard solutions.
Procedure for obtaining extraction efficiency
Absorbance of the standard solutions of Cu(II), prepared in the range of 1.0–10.0 μg mL−1, was measured by direct aspiration into the flame atomic absorption spectrometer. The calibration curve was then drawn. Using the analytical signal obtained for each sample after dilution with 130 μL ethanol and the calibration curve, the concentration of Cu(II) ions was determined, and then the mass of copper after DLLME was calculated. The extraction efficiency was then determined in 10.0 mL of an aqueous solution using the mass of copper before and after DLLME.
To indicate that the analytical signal for the standard solutions in water and that in the chloroform-ethanol mixture were equal, an investigation was carried out. For this purpose, a series of working solutions were prepared, as follows: 20 μL of the standard solutions of Cu(II) ions in the concentration range of 10.0–100.0 μg mL−1 was added to a mixture of 60 μL of chloroform and 120 μL of ethanol. Then the absorbance of these solutions was measured by FAAS. The signals obtained for the standard solutions in the chloroform-ethanol mixture were the same as those obtained for the standard solutions in water.
Results and discussion
Cu(II) ions reacted with salophen, and a complex was formed between them under the experimental conditions (Fig. 1) (Zeeb et al. 2011). The Cu-salophen complex in an acidic medium was extracted into the organic solvent. To reach a high analytical signal and enrichment factor, the effects of different parameters such as the solution pH, type and volume of the extraction solvent, type and volume of the disperser solvent, and concentration of the chelating agent were optimized. For optimization of the above-mentioned parameters, the univariate optimization strategy was used.
Effect of pH
The pH value plays an important role in the formation of the Cu-salophen complex and the subsequent extraction. For this reason, a series of experiments were carried out by adjusting the pH value from 1.5 to 7.0. The results obtained (Fig. 2) show that the analytical signal for copper is nearly constant in the pH range of 1.5–4. Thus based upon the results obtained and to obtain a high selectivity, pH = 2.0 was chosen as the optimum pH.
Selection of extraction solvent
The type of the extraction solvent has a significant effect on the extraction efficiency. The extraction solvent must have a low solubility in water, its density should be higher than water, and the solvent should have the ability to extract the compounds of interest (Naseri et al. 2008). In this regard, the efficiencies of different solvents such as carbon tetrachloride, chloroform, and dichloromethane were investigated. Since the solubility of the extraction solvents in water are different, it was necessary to add an excess amount of the extraction solvent in order to recover a constant volume of the sedimented phase (60 ± 3 μL). Therefore, 80, 110, and 140 μL of carbon tetrachloride, chloroform, and dichloromethane with 1.30 mL of acetone (as the disperser solvent) were separately injected into 10.0 mL of the sample solutions to achieve a total volume of 60 μL of the sedimented phase. The results obtained (Fig. 3) showed that the extraction efficiencies of carbon tetrachloride, chloroform, and dichloromethane were 58%, 94%, and 51%, respectively. Consequently, chloroform was selected as the best extraction solvent.
Effect of extraction solvent volume
The effect of the extraction solvent volume was also investigated by preparing mixtures of 1.30 mL of acetone and different volumes of chloroform. The results obtained are shown in Table 1. As it can be seen in this table, the analytical signal and the extraction efficiency were nearly constant in the volume range of 70–120 μL of chloroform, and then they gradually decreased. This is due to the fact that for an extraction solvent volume more than 120 μL, the resulting cloudy solution was not stable, and the size of chloroform droplets was large. Therefore, the surface area between the extraction solvent and the aqueous phase decreased, causing a decrease in the mass transfer and an efficient extraction of the Cu-salophen complex from the aqueous phase into chloroform. Thus to ensure an enough chloroform volume for extraction of a higher concentration of copper, 120 μL of chloroform was selected as the optimum volume, and the sedimented phase was 70 μL.
It should be noted that in studying the effect of the extracting solvent volume, since the volume of the sedimented phase was variable, the solutions were diluted up to 200 μL using different volumes of ethanol, as the diluting solvent. Therefore, it was necessary to investigate the effect of the volume of the diluting solvent on the analytical signal. In this regard, in a series of 10.0 mL water samples at pH = 2.0 containing 50.0 μg L−1 of Cu(II) ions, the Cu-salophen complex was extracted by injecting a mixture containing 1.30 mL of acetone and 120 μL of chloroform. After centrifugation, 50.0 μL of the sedimented phase was transferred into a vial, to which were added 0.0, 20, 40, 60, and 80 μL of chloroform. Then 150, 130, 110, 90, and 70 μL ethanol, respectively, were added to the above-mentioned solutions until the total volumes of 200 μL were reached. These solutions were aspirated to FAAS. The results obtained were the same (Table 2). Thus the changes in the ratio of volume of the sedimented phase to volume of ethanol had no effect on the analytical signal.
Selection of disperser solvent
In the DLLME method, the disperser solvent should be miscible with water and the extraction solvent. Therefore, the effect of miscible solvents such as acetone, methanol, ethanol, and acetonitrile on the analytical signal (extraction efficiency) of Cu(II) ions was investigated using mixtures of 1.30 mL of the above-mentioned solvents (as the disperser solvent) and 120.0 μL of CHCl3 (as the extraction solvent). The analytical signals (extraction efficiencies) obtained for acetone, methanol, ethanol, and acetonitrile were 0.140 (94%), 0.108 (72%), 0.118 (78%), and 0.098 (65%), respectively (Fig. 4). The maximum analytical signal (extraction efficiency) of Cu(II) ions was obtained using acetone, as the disperser solvent. Thus acetone was used as the disperser solvent in all the subsequent experiments.
Effect of disperser solvent volume
After selecting acetone as the disperser solvent, its volume is one of the important factors involved in DLLME that must be optimized. For this purpose, solutions with different volumes of acetone (0.88–1.88 mL) containing 120 μL of CHCl3 were prepared and subjected to the similar DLLME procedures. The results obtained (Fig. 5) showed that the analytical signal (extraction efficiency) increased with increase in the volume of acetone up to 1.50 mL, after which it remained constant. When a low volume of acetone was used, it could not disperse CHCl3 properly, and a stable cloudy solution was not formed. Consequently, the extraction efficiency was reduced. However, with a gradual increase in the disperser solvent volume, due to the formation of smaller droplets of chloroform, the surface area between the extraction solvent and the aqueous phase increased. This phenomenon led to an increase in the extraction efficiency. Therefore, based on the results obtained and in order to create a more stable cloudy solution, 1.68 mL of acetone was selected as the optimal volume.
Effect of salophen concentration
The effect of the concentration of salophen, as the complexing agent, on the analytical signal in the extraction of Cu(II) ions by DLLME was studied in the concentration range of 5.0 × 10−6–3.0 × 10−5 M. The results obtained showed that the signal for Cu(II) ions increased with increase in the salophen concentration up to 1.5 × 10−5 M, and then it remained constant (Fig. 6). In this work, a salophen concentration of 2.0 × 10−5 M was chosen as the optimum concentration to prevent any interference.
Effect of reaction time for complex formation
The reaction time for the complex formation can be defined as the time spent between the addition of salophen solution to the sample solution and injection of the extraction solvent (chloroform) dissolved in the disperser solvent (acetone). This was studied in the time range of 0–15 min (Fig. 7). The results obtained showed that the reaction was fast, and so the reaction time did not have any effect on the analytical signal.
Effects of extraction time and centrifugation time
The extraction time is one of the most important factors involved in all the extraction procedures. In DLLME, the extraction time is defined as the interval time between the injection of the mixture of organic solvents (disperser and extraction solvents) and starting the centrifugation. The effect of the extraction time was evaluated in the range of 1–20 min under constant experimental conditions. The results obtained (Fig. 8) indicated that the extraction time had no significant influence on the analytical signal. These results showed that after formation of the cloudy solution, the surface area between the extraction solvent and the aqueous phase was infinitely large and that the resulting Cu(II)-salophen complex was transferred into the extraction solvent quickly. Therefore, the proposed DLLME method is time-independent, which can be one of its most important advantages.
The centrifugation time was also evaluated to be between 1 and 10 min at 5000 rpm. The results obtained showed that the analytical signal increased with increase in the centrifugation time up to 3 min, and then it remained constant, indicating a complete separation of chloroform to the bottom of the centrifuge tube. In order to ensure sedimentation (complete separation) of the extraction solvent, a time duration of 5 min was selected as the centrifugation time in all the further experiments. In the proposed method, the most time-consuming step was the centrifugation of the sample solution in the extraction procedure.
Effect of ionic strength
The influence of ionic strength on the extraction of the Cu-salophen complex was studied using potassium nitrate as a salting-out agent at the concentration range of 0–1.0 M. The results obtained showed that the salt concentration had no influence on the analytical signal (extraction efficiency). In all concentrations of KNO3, the extraction efficiency was 100% (Fig. 9). These results implied the possibility of applying the DLLME method for copper separation from salty solutions.
Study of interferences
The FAAS technique has a high selectivity but some species may interfere with the extraction step and change the extraction efficiency of copper. In order to investigate the effect of the potential interfering ions, solutions containing 50.0 μg L−1 of Cu(II) ions and different amounts of foreign ions were treated according to the recommended procedure. The tolerable concentration of foreign ions was considered, i.e., the concentration at which less than ± 5% deviation in the analytical signal was measured in comparison with the case in which the interfering ion was absent. The results obtained are summarized in Table 3. These results showed that most ions did not interfere even if they were present in amounts 1000-fold greater or more than copper.
The Hg2+, Sn2+, and Pb2+ ions reacted with the phosphate ions (i.e., the ion of buffer solution) and precipitated.
The analytical characteristics of the proposed method were calculated under the optimized conditions. For a sample volume of 10.0 mL, the calibration curve exhibited a linearity over the range of 3.0–120 μg L−1 under the optimum conditions. The regression equation for copper determination was ΔA = 2.9003C + 1.8 × 10−2, where ΔA is the analytical signal (the difference between the absorbance of the sample and blank solutions (∆A = As − Ab) at 324.8 nm) and C is the copper(II) ion concentration in solution (μg mL−1). The correlation coefficient (R2) of the calibration curve equation obtained was 0.9998, which indicated a good linearity in the mentioned concentration range. The limit of detection based on a signal-to-noise ratio of 3 (3σ) was 0.6 μg L−1. The equation obtained by direct aspiration in FAAS without the preconcentration procedure was ΔA = 0.059 C + 1.3 × 10−2 (R2 = 0.9997 and a linear range of 0.250–10.0 μg mL−1). The enrichment factor (EF), calculated as the ratio of the slope of calibration curve of the analytes after extraction to that before extraction (Şatıroğlu and Arpa 2008), was found to be 49 for 10.0 mL of the sample solution.
Based on the organic phase volume (200 μL) and the sample volume (10.0 mL), a preconcentration factor of 50 was determined. The equality of the preconcentration factor and the enrichment factor indicates the completion of the quantitative extraction.
Since in the reported methods different volumes of the sample solution were used, the enrichment factors obtained in these methods are not compared. Therefore, the consumption factor is preferred on the enrichment factor. The consumptive index (CI) is defined as the aqueous sample volume (in mL) consumed to reach a unit of EF: CI = Vs/EF, where Vs is the aqueous sample volume (Lemos et al. 2007). For the proposed method, this parameter was obtained to be 0.20 mL. A low value for this parameter indicates a favorable efficiency of the method.
In order to investigate the reproducibility of the proposed method, six replicate measurements of 5.0, 20.0, and 50.0 μg L−1 of Cu(II) ions gave the relative standard deviations of 4.1%, 1.5%, and 1.8%, respectively.
A summary of the analytical characteristics of the DLLME method for copper determination is presented in Table 4.
Analysis of real samples
Analysis of water samples
The proposed method was applied to determine Cu(II) ions in samples of tap water (Shahrood and Jajarm, Iran) and spring water (Ali spring in Damghan, Iran) by the standard addition technique. The recoveries of copper from the water samples spiked with Cu(II) ions were also studied. The results obtained are shown in Table 5. Satisfactory recoveries were obtained for the spiked copper(II) ions, confirming the accuracy and applicability of the proposed DLLME-FAAS method for copper determination in water samples.
Analysis of a rice sample
In order to evaluate the applicability of the proposed method for determination of copper in food samples, a type of rice from the north of Iran was selected and analyzed. For this purpose, 10.00 g of the rice was dissolved according to the procedure reported by Zeeb et al. 2011 and transferred into a 100-mL volumetric flask. Then, 20.0 mL of the prepared rice sample solution, 1.25 mL of the phosphate buffer solution (pH = 2.0), and 50 μL of the salophen solution (0.010 M) were transferred into a 25-mL volumetric flask and diluted to the mark with doubly distilled water. The concentration of copper in 10.0 mL of this solution was determined by the proposed method using the standard curve technique. The results of the recovery experiments for different amounts of Cu are summarized in Table 6. These results indicate that the recoveries in the range of 96–105% are reasonably well for trace analysis, and the calculated t values are less than the t-critical values at the 95% confidence level. The results obtained confirm the validity of the developed method.
In the present work, the performance of an environmentally friendly method for the preconcentration and determination of ultra-trace amounts of Cu(II) ions has been investigated. This method is based upon the formation of complex between Cu(II) ions with salophen as a ligand, followed by DLLME of the neutral hydrophobic complex formed in the organic phase and flame atomic absorption spectrophotometric detection. The main advantages of the proposed method are its high selectivity, simplicity, low consumption of organic solvent, and rapidity. A comparison between the analytical figures of merit for the developed method and some of the other preconcentration methods combined with flame atomic absorption spectrometry used for the determination of copper ions is summarized in Table 7. The developed method has a high efficiency factor, a low limit of detection (LOD), and a consumptive index (with some exceptions). Therefore, the developed method is comparable with or even better than those reported by the other researchers and its performance in the determination of Cu(II) ions in the water and food samples was excellent.
Dispersive liquid–liquid microextraction
Fame atomic absorption spectrometry
Graphite furnace atomic absorption spectrometry
High-performance liquid chromatography
Inductively coupled plasma-optical emission spectrometry
Limit of detection
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The authors are thankful to the Shahrood University of Technology Research Council for the support of this work.
This work has been financially supported by the Shahrood University of Technology.
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