Introduction

The ever-increasing usage and disposal of pharmaceutically active substances as well as personal-care products are becoming a matter of concern worldwide. The chemical pollutants present in these products are progressively entering into various natural water resources such as lakes, rivers and groundwater. The dewatered municipal biosolids are frequently used in agricultural manure in order to improve physicochemical properties of soil and enrich soil fertility (Liu and Wong 2013; Moldovan 2006; Usman et al 2012). However, it could also lead to the release of persistent pharmaceutical pollutants in the ecosystem, including groundwater (Sabourin et al. 2011). The solicitation of dewatered municipal biosolids in soil profile has remarkable influence on depravity rate of various biodegradable substances and decreases their possible ecological hazard (Al‐Rajab et al. 2015). Since the recognition of small quantities of active pharmaceutical substances in the groundwater has been noticed, the alertness about their existence and hazards has increased (Ternes 1998). In the recent decades, these compounds have been detected in wastewater and subsequently reach into surface, ground and drinking water in North America, Australia and Europe (White et al. 2006).

Caffeine (1,3,7-trimethylpurine-2,6-dione) is a well-known central nervous system stimulant and excessive consumption for long time can produce adverse health effects such as anxiety, insomnia, nervousness and hypertension; may affect the quality and quantity of sleep, even at low concentration (Gokulakrishnan et al. 2005; Shilo et al. 2002; Waring et al. 2003). It can also produce harmful effects in patients with cardiac complications (James 1997). Caffeine is considered to be addictive compound which has more prominent effects in women than men, its withdrawal symptoms are reported to be fatigue, headache, drowsiness and apathy (Greenberg et al. 1999; Daly and Fredholm 1998; Landolt et al. 1995; Nehlig 1999). Moreover, its exposure to plants and animals have harmful impact (Pincheira et al. 2003; Meyer et al. 2004). The domestic wastes of caffeinated drinks, beverages and chocolates are the major sources of entry of caffeine in the environmental system. About 90% of the world adult population consume caffeine in one way or another with the highest average consumption of 440 mg/day/person in USA, followed by 300, 210 and 171 mg/day/person in Switzerland, UK and Brazil, respectively (Frary et al. 2005; Buerge et al. 2003; Standley et al. 2002; Monica and Camargo 1999). The global average consumption of caffeine varies in the range of 80–400 mg/day/person (Gokulakrishnan et al. 2005). Although caffeine is present naturally in coffee, tea, cocoa, kola nuts and added to beverages, its presence in environmental water is mainly attributed to the discharge of domestic wastewater or mediation moving through inefficient onsite wastewater treatment (Buerge et al. 2003; Seiler et al. 1999; Siegener and Chen 2002). Because of its high solubility (13.5 g/L), caffeine is largely expected to persist in water (Buerge et al. 2006; Chen et al. 2002). High concentrations of caffeine in wastewater were attributed from densely populated areas (Peeler et al. 2006; Rodriguez del Rey et al. 2012). It ranges from traces to enormously excessive concentrations (up to 192 µg L−1) in wastewaters (Gomez et al. 2007). Caffeine concentration reported in various water resources include, surface water (112–781 ng L−1) (Daneshvar et al. 2012), groundwater (0.23 µg L−1) (Seiler et al. 1999), effluent wastewater (0.07–126 µg L−1) (Weigel et al. 2004), coastal water (15–185 ng L−1) (Cantwell et al. 2016) and well water (1.7 µg L−1) (Reddy et al. 2006).

Caffeine is comprehensively found in nature because of its consistent disposal into the sewage framework by the transfer of unconsumed coffee, tea or beverages down the channels, and the flushing of coffee pots and mugs (Seiler et al. 1999). Several techniques, such as photo-electrolysis, ozonation, activated charcoal adsorption, electro-chemical oxidation, photo-oxidation, biodegradation and dielectric barrier discharge (DBD) plasma, have been investigated for caffeine removal from wastewater (Kim et al. 2008; Lin et al. 2010; Yu et al. 2014). In recent years, DBD plasma technique has been utilized as an effective system for removal of pharmaceutical contaminants in wastewater treatment plants (Magureanu, et al. 2015). In DBD plasma technique, discharge electrode plates separated by dielectric barrier, generally made up of quartz are used (Reddy et al. 2014a). Electric discharge in water leads in the production of UV radiation, high electric fields and overpressure shock waves and generation of active species such as hydroxyl radicals(˙OH), ozone (O3), atomic oxygen (O), hydrogen peroxide (H2O2), and hydroperoxyl radicals (˙HO2) resulting in oxidative degradation of organic contaminants in water (Al-Rajab et al. 2018; Lin et al. 2010; Reddy et al. 2014a, b; Wang et al. 2017). Buerge et al. (2003) have reported 81–99.9% removal of caffeine from wastewater containing low concentrations of caffeine (7–73 µg/L) at Swiss wastewater processing plants, they have also analyzed the suitability of caffeine as chemical marker for surface water pollution from domestic discharge. Sui et al. (2010) have investigated the removal of 13 pharmaceuticals including caffeine from wastewater at four different wastewater treatment plants in Beijing, China, and reported about 12–100% elimination rate of micro-pollutants using ozonation and microfiltration/reverse osmosis techniques. In another publication, 94% caffeine removal from aqueous solution (50 mg/L) by using a DBD plasma treatment technique coupled with goethite catalysis was reported in 24 min treatment (Wang et al. 2017). In addition, several methods based on biodegradation of caffeine by different bacterial and fungal strains have also been described (Edwards et al. 2015; Gokulakrishnan et al. 2005). However, most of the available methods for caffeine removal from wastewater suffered one or more drawbacks of being expensive, time consuming, low caffeine removal rate, incomplete degradation, high-energy consumption, usage of catalysts, expensive gases and toxic organic solvents and complicated procedure such as solvent and supercritical fluid extraction. Therefore, to remove the potential organic contaminants from water resources, and hence to improve the quality of life, a technically and economically balanced method is still needed. As a consequence, in the present work, we attempted to develop a cost-effective method based on DBD plasma technique with faster caffeine removal from water system. Furthermore, the DBD system utilized in this investigation was operated at atmospheric pressure in open air without application of any catalyst, expensive gases and organic solvents. The concentration of caffeine in treated water samples was monitored by validated high-performance liquid chromatography (HPLC) method.

Materials and methods

Materials

Caffeine (99.0%) was purchased from Sigma Aldrich, Germany, and used without further purification. Ammonium acetate, acetic acid, ammonium hydroxide and acetonitrile (HPLC grade) were procured from Sigma Aldrich, Germany. All the reagents used in this experiment were of analytical grade or were specified. HPLC grade water was produced in-house using Milli-Q water purification system (Millipore, Molsheim, France).

Instrumentation and optimization of experimental parameters

A laboratory scale dielectric barrier discharge (DBD) system, as described in our previous experiment, used for the removal of acetaminophen from water samples (A-Rajab et al. 2018) with little modification was utilized in this study. The major component of the plasma system consisted of plasma reactor; a high voltage current generator developed by Nanjing Suman Electronics, China and an oscilloscope (Lecroy, WaveSurfer 24x-A) to measure the discharge voltage and current generated. A schematic diagram of plasma DBD system used in this experiment is represented in Fig. 1. The plasma reactor comprised of two stainless steel electrodes organized in a parallel plate arrangement. 20 mL of sample solution was put in a glass petri-dish on the lower electrode, and the upper electrode was enclosed by means of 1 mm thick quartz plate. The distance between the quartz plate and petri-dish (two dielectric) was 7 mm, while the gap between sample surface and quartz plate was approximately 5 mm. In the current study, all the solutions were subjected to 60 W power, 10 kHz frequency at atmospheric pressure and room temperature (20 °C) for 4 min. The total input plasma power (P), averaged over the alternating voltage period (T) in the DBD system was calculated by using the following Eq. (1):

Fig. 1
figure 1

Schematic diagram of dielectric barrier discharge (DBD) system used in this experiment. Operated at atmospheric pressure in ambient air and room temperature (20 ºC); 20 mL sample volume and 60 W input power

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$$P=\frac{1}{T}{\int }_{0}^{T}V\left(t\right)\times i\left(t\right)\times dt$$
(1)

where V(t) and i(t) represent measured instantaneous voltage and current at time t, respectively (Pipa and Brandenburg 2019; Wang et al. 2016). The samples were analyzed at a time interval of 30 s. The content of caffeine and solution pH was determined after each plasma treatment. The experiment was performed in triplicate and the energy density (ED) was calculated using the following formula:

$$Energy\, Density=\frac{Plasma\,power\,\times\,Treatment\,time}{Volume\,of\,the\,solution\,in\,the\,reactor}$$
(2)

The experimental parameters including, initial concentration of caffeine solution, initial pH of the solutions and treatment time were investigated to optimize the degradation process. In order to study the effect of initial concentration on degradation process, different concentrations viz., 1, 25, 50, 75 and 100 ppm were processed, whereas, to optimize the treatment time, the DBD process was carried out at room temperature (20° C) and the samples were evaluated from the reactor at different time intervals viz., 0, 0.5, 1, 2, 3 and 4 min. To find out the optimum pH of the initial caffeine sample, several trials were processed at acidic, neutral and basic pH values.

Caffeine analysis

The concentration of caffeine was measured by high-performance liquid chromatographic system (Waters Breeze 1525, Netherland). The system was equipped with auto-sampler (Waters 2707), binary pump (Waters 1525) and UV–Visible detector (Waters 2489). Data were monitored by using Waters Breeze 2 LC solution software. The caffeine solutions were injected into Symmetry C-18 analytical column (75 mm × 4.6 mm id., particle size 3.5 µm). Ammonium acetate buffer (10 mM, pH 4.0) and acetonitrile in the ratio of 90:10 v/v were used as mobile phase, which was monitored at a flow rate of 1 mL/min, throughout the experiment. The injection volume was 20 µL and UV detection wavelength was 220 nm. Linearity of the method was evaluated by analyzing a range of caffeine working standard solutions at concentrations between 1 to 128 µg/mL. Calibration curve was constructed by plotting peak area against respective concertation. The accuracy of the method was demonstrated by estimating the recovery of caffeine at three concentration levels (2, 64 and 128 µg/mL).

Caffeine and its degradation products were identified by direct injection of samples to the mass spectrometry system containing LCQ fleet Max ion trap (Thermo Fischer Scientific, Inc., USA) equipped with electrospray interface (ESI) source operated in positive ion mode with optimum operating parameters viz., spray voltage 5 kV, ion-transfer capillary temperature 275 °C, capillary voltage 10 V. The collision gas pressure was 0.25 by argon and nebulizer and sheath gas flow rate were maintained at 35 arbitrary unit loaded by nitrogen gas. The mass spectra in the m/z range from 100 to 500 were recorded in ion scan mode. The sample solutions were injected directly into the ion trap MS without chromatographic separation at a flow rate of 10 µL/min by using 500 µL syringe.

Preparation of solutions

Standard stock solution for plasma treatment was prepared by dissolving 100 mg of caffeine into 100 mL Milli Q water. The stock solution was diluted to obtain a working solution of 100 µg/mL concentration, which was used as initial caffeine concentration. Caffeine working standard solutions of concentrations, 1, 2, 4, 8, 16, 32, 64 and 128 µg/mL were prepared by diluting the standard stock solution with mobile phase to obtain calibration curve.

Results and discussion

Increasing usage and disposal of pharmaceuticals as well as personal-care products are becoming a matter of concern as pollutants, which progressively contaminating various water resources including lakes, rivers and groundwater. Caffeine is generally found in considerably high concentrations in water streams, which can be easily estimated. Hence, it can be proposed as a probable wastewater tracer which will indicate the occurrence and level of pollution in water samples, in addition, to differentiate between wastewater and water from other environmental resources. In the present experiment, efficiency of a laboratory scale dielectric barrier discharge plasma technology has been investigated with regards to the removal of caffeine, a potential pollutant, from water samples. The aqueous caffeine solution (20 mL) was exposed to plasma treatments and the degradation of caffeine was assessed at different times. The DBD system used in this study has shown fast and effective removal efficiency, as a degradation of 72.55% of caffeine in water (100 µg/mL initial concentration, pH 7) was achieved in a short time period (4 min) of plasma treatment at atmospheric pressure in open air. The energy efficiency of the system was excellent. Moreover, the method was also considered to be cost-effective and safe, as no gas, catalyst and organic solvents were utilized. Concentration of caffeine in the sample solution before and after plasma treatment was measured by HPLC analysis.

In the HPLC method development process, chromatographic parameters were optimized by various trials and symmetric peak of caffeine was obtained at a mobile phase composition of 90:10 v/v of ammonium acetate buffer (10 mM, pH 4) and acetonitrile. The analytical elution of caffeine was achieved by using symmetry C-18 analytical column at mobile phase flow rate of 1 mL/min, and the retention time of the analyte peak was observed at 4.96 min. The method was linear in the concentration range of 1–128 µg/mL (R2 ˃0.999). Precision of the method was demonstrated by analyzing quality control sample at three concentrations, 2, 64 and 128 µg/mL (LQC, MQC and HQC, respectively), and relative standard deviation (RSD) of peak area of caffeine for six replicate injections was ˂1%. Recovery of the analyte at all three concentration levels was within 100 ± 2%. The representative chromatogram of caffeine working standard solution is shown in Fig. 2.

Fig. 2
figure 2

Representative chromatogram showing caffeine peak from standard working solution. Stationary phase: Symmetry C-18 column; Mobile phase: Ammonium acetate buffer (10 mM, pH 4.0): acetonitrile (90:10 v/v); Flow rate: 1 ml/min and detector wavelength: 220 nm

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In this study, the DBD system was operated in the ambient air at room temperature (20ºC), active species ˙OH, O3 and H2O2 may be produced, which resulted in the degradation of caffeine. The O2 was bombarded by high-energy electrons in the electric field and O˙ was generated through direct electron impact dissociation (Eq. 3) (Kogelschatz et al. 1988). This was followed by generation of ozone (O3) due to interaction of O˙ with molecular oxygen (O2) (Eq. 4) (Reddy et al. 2014a, b). The dissolved O˙ and O3 in the water may produce hydroxyl radical (˙OH), which is stronger oxidant than O3 itself and reported to participate in the degradation of organic compounds, in this case, caffeine (Eq. 5–8) (Kim et al., 2015; Wang et al 2016). In addition to that, in the system, strong oxidant, H2O2 was also produced, which was believed to be responsible for the degradation of the target molecule to some extent (Eq. 9–10) (Wang et al., 2017). The generation of active species in the present DBD conditions may be represented by the following series of reaction equations:

$${\mathrm{O}}_{2}+{\mathrm{ e}}^{-}\to {\mathrm{O}}^{.}+ {\mathrm{O}}^{.}+ {\mathrm{e}}^{-}$$
(3)
$${{\mathrm{O}}^{.}+\mathrm{O}}_{2}\to {\mathrm{O}}_{3}$$
(4)
$${{\mathrm{O}}^{.}+\mathrm{H}}_{2}\mathrm{O}\to 2\dot{}\mathrm{OH }$$
(5)
$${\mathrm{O}}_{3} + {\mathrm{OH}}^{-}\to {\mathrm{O}}_{2}^{- }+ {\mathrm{HO}}_{2}^{.}$$
(6)
$${\mathrm{O}}_{2}^{-}+ {\mathrm{O}}_{3}+ {\mathrm{H}}^{+} \to {\mathrm{O}}_{2}+ {\mathrm{HO}}_{3}^{.}$$
(7)
$${\mathrm{HO}}_{3}^{.} \to \dot{}\mathrm{OH}+ {\mathrm{O}}_{2}$$
(8)
$$2\dot{}\mathrm{OH }\to {\mathrm{H}}_{2}{\mathrm{O}}_{2 }+ {\mathrm{O}}_{2}$$
(9)
$${\mathrm{O}}_{3}+ {3\mathrm{H}}_{2}\mathrm{O }\to {3\mathrm{H}}_{2}{\mathrm{O}}_{2}$$
(10)
$$\mathrm{Active species }\left(\mathrm{O}\dot{}, {\mathrm{O}}_{3}, \dot{}\mathrm{OH and }{\mathrm{H}}_{2}{\mathrm{O}}_{2}\right)+\mathrm{Caffeine }\to \mathrm{ Degradants }$$
(11)

After DBD treatment, the caffeine degradation products were characterized by directly injecting the sample solution in the mass spectrometer. The full scan spectrum was recorded in the range of m/z 100–500 and major degradation products were identified as molecular ion m/z = 194.9 and fragment ions at m/z 168.8, 179.8, 142.8, 126.8, 101.8 and 59.8 (Fig. 3). The fragment ions at m/z 168.8 and 179.8 were due to removal of –C = N and –CH3 ions, respectively, whereas, the fragment ions at m/z 142.8 and 126.8 were formed by cleavage of one more –C = N ion and consequently a methyl group from m/z 168.8 fragment. Successive cleavage of the pyridine ring yielded fragment ions at m/z 101.8 and 59.8 by removal of –C = CH and –CON ions, respectively.

Fig. 3
figure 3

Proposed degradation pathway of caffeine in mass spectrometric analysis

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Effect of time and initial concentration on caffeine degradation

The degradation rate of caffeine at 100 µg/mL initial concentration was found to be significantly increased with time. When the solution was treated by applying 60 W DBD plasma power, about 7.07% of caffeine was degraded in 30 s, followed by 13.4, 26.7, 34.48, and 72.55% in 1, 2, 3 and 4 min, respectively. This degradation pattern was considered to be significant. The removal efficiency of caffeine from water at 100 µg/mL initial concentration is represented in Fig. 4. To optimize the initial sample concentration, caffeine removal efficiency by DBD plasma was investigated by using samples solutions of 1, 25, 50, 75 and 100 µg/mL caffeine concentration. Results showed that the caffeine removal efficiency from water was significantly greater at lower initial concentrations, whereas at higher concentrations, lesser caffeine degradation was observed. This greater degradation of caffeine at lower concentration may be due to fast dissipation of caffeine from less saturated solution, whereas, at higher concentrations, the molecular caffeine, intermediate and fragment ions are more to compete with reactive species of DBD reactor which are constant for a particular experimental condition leading to reduced removal efficiency. The caffeine degradation rates in water were 19.31, 16.79, 9.12, 8.23 and 7.07, when the sample solution was treated by using 60 W plasma power for 30 s at 1, 25, 50, 75 and 100 µg/mL initial concentrations, respectively. The degradation rates were significantly enhanced to 96.59, 94.38, 81.6, 76.18 and 72.59%, respectively, when the treatment time was increased to 4 min, while keeping the other experimental parameters same. The removal efficiency of caffeine from water samples of above mentioned initial concentrations at different treatment times is depicted in Fig. 5.

Fig. 4
figure 4

Caffeine removal efficiency (%) from aqueous solution at 0.5, 1, 2, 3 and 4 min plasma treatment times. Initial caffeine concentration: 100 µg/mL; initial pH: 7 and input plasma power: 60 W

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Fig. 5
figure 5

Removal efficiency of caffeine from water with initial concentrations of 1, 25, 50, 50, 75 and 100 µg/mL at 0.5 and 4 min DBD plasma treatment. Initial pH: 7 and input plasma power: 60 W

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Effects of initial pH of sample solution

Usually, pH values of analytical solutions play an important role in the degradation of the pharmaceutical substances. It can alter the rate and pathway of a degradation reaction. The pH of aqueous solution might be vital factor in the generation and stability of oxidizing species such as ozone, hydrogen peroxide, hydroxyl and oxygen free radicals in water interphase. Consequently, in this study, caffeine degradation in aqueous solution (100 µg/mL initial concentration) at acidic, neutral and basic pH values, 4, 7 and 10, respectively, was evaluated and degradation efficiency was recorded after 0.5, 1, 2, 3 and 4 min DBD treatment at 60 W DBD plasma input power. The results showed that the initial pH value of caffeine aqueous solution had significant influence on the degradation of caffeine. Maximum degradation was recorded at pH 7, while no significant degradation of caffeine was observed in solution with pH 10. The degradation rate of caffeine at pH 7 were 7.07, 13.4, 26.7, 35.48 and 72.55% of initial caffeine content at 0.5, 1, 2, 3 and 4 min treatment time, respectively, whereas these values decreased to 1.42, 3.76, 8.48, 20.29 and 21.8%, respectively, in the same treatment times at pH 4. Only 3.15% of caffeine was degraded in 4 min DBD treatment in sample solution with initial pH 10. The Caffeine removal efficiency at pH 4, 7 and 10 with respect to time of DBD treatment is depicted in Fig. 6. DBD plasma treatment of the caffeine solution (100 µg/mL) has also resulted in drop of initial solution pH which was proportional to the time of treatment. The initial pH 7 was decreased to 3.3 in 30 s treatment, which then gradually declined to 2.5 in 3 min and reached 2.0 in 4 min treatment. The sample solution with pH 4 was found to be relatively less affected as in first 30 s treatment the pH reduced to 3.5, which remained unaffected up to 1 min, and finally reached to 3.0 in 4 min of DBD treatment. No significant reduction in pH values of the solution with pH 10 was observed as a result of DBD plasma treatment for similar time periods. The variation in initial pH values as a function of time DBD plasma treatment is shown in Fig. 7. Similar pattern of reduction in pH values after DBD plasma treatment of caffeine solution (initial pH 7) was observed at 1, 25, 50 and 75 µg/mL initial concentrations (Fig. 8).

Fig. 6
figure 6

Effect of initial pH on the removal efficiency (%) of caffeine from water samples in DBD plasma reactor. Initial caffeine concentration: 100 µg/mL; input power: 60 W; solution volume: 20 mL

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Fig. 7
figure 7

pH variation of caffeine aqueous solution with different initial pH on DBD plasma treatment. Initial caffeine concentration: 100 µg/mL; volume of sample: 20 mL and input power: 60 W

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Fig. 8
figure 8

pH variation of caffeine aqueous solutions with different caffeine concentrations on DBD plasma treatment. Initial pH of solutions: 7; volume of sample: 20 mL and input power: 60 W

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Effect of input power

The influence of input power on the removal efficiency of caffeine from aqueous solution was also investigated. The initial concentration of the test solution was 100 µg/mL and the initial pH was 7. It was observed that an increase in input power has increased the caffeine removal from solution. The caffeine degradation was 26.59% in 4 min after treatment at 40 W DBD plasma power, which was increased to 72.55%, when plasma power was increased to 60 W. The caffeine removal efficiency was reached to 77.36% and 87.55% in 4 min treatment at input power of 80 W and 100 W, respectively, in the DBD system (Fig. 9). Furthermore, the intensity of input power displayed similar effect to the pH of the caffeine solution after DBD treatment. The initial pH 7 was decreased to 3.3, 3.3, 2.9 and 2.7 in 0.5 min of treatment in the DBD system at 40, 60, 80 and 100 W input powers, respectively. The solution pH gradually decreased and finally reached to 2.5, 2.0, 1.9 and 1.8, respectively, after 4 min treatment. The relationship between input power and pH of the caffeine solution with treatment time is depicted in Fig. 10. Improved removal efficiency of caffeine from aqueous solution can be explained by generation of more active species at higher input power. The higher input power enhances the rate of electron participation, which generated stronger electric field and increased the intensity of particle collision in the system (Wang et al., 2017; Avramenko, 2013).

Fig. 9
figure 9

Effect of input plasma power on removal efficiency (%) of caffeine in water samples. Initial caffeine concentration: 100 µg/mL; solution volume: 20 mL and initial pH: 7

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Fig. 10
figure 10

Effect of input power in DBD plasma reactor on pH of the caffeine aqueous solution. Initial caffeine concentration: 100 µg/mL; volume of solution: 20 mL and initial pH: 7

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Energy efficiency

In this study, approximately 72.55% of caffeine from aqueous solution (100 µg/mL initial concentration) was removed in DBD plasma reactor operated in open air condition with an energy density of 7.2E05 JL−1. The energy efficiency in this study was better than that observed in our previous work (energy density 9.6E05 JL−1), in which removal of acetaminophen was investigated using similar DBD plasma system (Al-Rajab, et al, 2018). In another study, Liu et al., (3013) have reported more energy-efficient DBD system (1.5E05 JL−1) used in the removal of iopromide from water samples. The energy density may vary from one DBD system to another depending on the operating conditions and samples to be investigated. However, DBD plasma reactor used in this study is more cost-effective and safer because no carrier gas was used and the system was operated at atmospheric condition without using any organic solvent.

Conclusion

Caffeine has been considered to be one of the concerning contaminants in various surface and groundwater resources, and discharge of domestic wastes is the main source of contamination. In this study, a dielectric barrier discharge plasma system was investigated for removal of caffeine from water. After DBD plasma treatment, the caffeine concentration in the samples was estimated by HPLC and the degradation products were identified by directly injecting the sample to mass spectrometer. The influence of several experimental parameters on degradation efficiency of caffeine was evaluated. About 72.55% degradation of caffeine was achieved in a neutral sample (pH 7) after 4 min plasma treatment with an input power of 60 W. The caffeine removal was remarkably reduced at acidic (pH 4) and basic (pH 10) conditions. The removal efficiency was greater at lower initial concentrations and caffeine degradation was decreased from 96.59% to 72.55%, when the sample concentration was increased from 1 µg/mL to 100 µg/mL. Moreover, the caffeine (100 µg/mL) removal was increased from 26.59% to 87.88% after 4 min treatment, when the input power in the DBD system was enhanced from 40 to 100 W, respectively. The present DBD system was operated at atmospheric pressure in open air without use of any catalyst, expensive gases and organic solvent; therefore, it can be considered as efficient and economical. However, further efforts would be required to implement the method at large scale as well as to investigate the effluent toxicity.