Assessment of kinetics behavior of electrocoagulation process for the removal of suspended solids and metals from synthetic water

Article information

Environmental Engineering Research. 2017;22(2):141-148

Publication date (electronic) : 2016 October 19

doi : https://doi.org/10.4491/eer.2016.029

Department of Environmental Science and Engineering, Indian Institute of Technology (ISM) Dhanbad, Jharkhand 826004, India

^†Corresponding author: Email: bkmishra3@rediffmail.com, Tel: +91-947-1191704, Fax: +91-326-2296624

Received 2016 February 18; Accepted 2016 October 17.

Abstract

Globalization, industrialization, mining, and uncontrolled population growth have fostered a shortage of potable water. Therefore, it has become imperative to understand an effective and reasonable water purification technique. A renewed interest in electrocoagulation (EC) has been spurred by the search for reliable, cost-effective, water-treatment processes. This paper has elucidated a technical approach for getting rid of heavy metals and total suspended solids (TSS) from synthetic water using an aluminum electrode. The effect of operational parameters, such as current density, inter-electrode distance, operating time, and pH, were studied and evaluated for maximum efficiency. This study corroborates the correlation between current density and removal efficiency. Neutral pH and a low electrode gap have been found to aid the efficacy of the EC setup. The outcome indicates that a maximum TSS removal efficiency of 76.6% occurred at a current density of 5.3 mA/cm² during a contact time of 30 min. In the case of heavy metals remediation, 40 min of process time exhibited extremely reduced rates of 99%, 59.2%, and 82.1%, for Cu, Cr, and Zn, respectively. Moreover, kinetic study has also demonstrated that pollutants removal follows first-and second-order model with current density and EC time being dependent.

Keywords: Current density; Electro-coagulation; Heavy metals; Kinetic; Synthetic water

1. Introduction

The explosive population increase and expansion of urban areas have exacerbated adverse impacts on water resources [1, 2]. Nowadays, Mining and industries have been found to produce significant contributions in accelerating extent of contamination in the surroundings. Mine water and Industrial effluents are known antecedent of heavy metals. Doubtless, it has deteriorated water quality by incorporating a high absorption of toxic metals. The repercussions of metallic contaminants like Pb, Cr, Zn and Cu on the wide application of water have been scrutinized and it has been recommended to treat contaminated water before discharging. Thus, there is an exigency to develop effective and economical water purification technique to curtail its deleterious effects.

The right of all people to access suitable water supplies must thus be seen as a global challenge, the solution of which is dependent on the formulation and implementation of sustainable water management strategies. To resolve this problem, technical approaches such as ion exchange chromatography, ultrafiltration, reverse osmosis and chemical precipitation have been applied. But each treatment method comes with their respective pros and cons. For example, Ion exchange chromatography is highly effective in removing certain charged contaminants, but it requires costly resin regeneration. Ultra filtration and reverse osmosis are clean processes, merely they are prohibitively expensive. Chemical precipitation is a simple procedure; it does get a high volume of sludge.

Researchers have explored different innovative approaches to unfold eco-friendly heavy metals remediation. Studies have revealed electrocoagulation (EC) as one of the efficient and cost effective technique for the removal of heavy metals. This technique relies on the principal of segregating heavy metals in the presence of electric current using suitable electrodes [3–5]. In this process, Iron is the most widely used electrode followed by aluminum. When aluminum is used as anodes, it produces aluminum hydroxide, Al(OH)_3, upon oxidation in an electrolytic system [6].

Table 1 shows the values of EC parameters chosen by some authors [4, 7–10] for the removal of heavy metal using aluminum or iron electrodes. The parameters, whose values will be compared with this work (Table 1), are: Conductivity and electrolyte composition; initial pH; number of metals present in the medium and initial metal concentrations; the volume of the solution investigated; number of electrodes used; total electrode surface area and distance between electrodes; current density; operating time. As indicated in Table 1, EC is usually taken using high electrolyte conductivity (from 1.5 to 20 mS/cm). High conductivity can be obtained with the addition of salts like NaCl, NaNO₃ and Na₂SO₄ [7, 8]. The role of salt addition is to lower the electrolysis potential and, in the case of chloride ions, to enhance anodic dissolution of the electrodes.

Table 1

Comparisons of Treatment Performances of Different Wastewater with Process Conditions and Variables in the EC Process

Metals and total suspended solids (TSS) removal through the EC process is well known, but optimization of the EC process with reference to energy requirement and percentage removal has not yet been studied in detail. The aim of the present study was to understand the various factors affecting removal efficiency of metals and TSS by EC process with reference to energy requirement to understand the feasibility of EC process.

2. Materials and Methods

2.1. Reagents and Solutions

Reagents were prepared using distilled demineralized water from the Mili-Q water system. Titrisol Merck standard solutions of 1,000 mg/L of copper, chromium, and zinc were used and solutions of different concentrations were obtained by adequate dilutions. The pH of the solution was adjusted by 0.1 N HCl and 0.1 N NaOH solutions prepared from AR grade Merck chemicals.

CuSO₄·5H₂O, K₂Cr₂O₇, and ZnO were used in the present study for preparing of Cu, Cr and Zn based synthetic water. A measured quantity of 1 L of freshly prepared synthetic solution of Cu, Cr and Zn using tap water was taken in EC process.

2.2. Experimental Setup and Procedure

A Perspex made reactor (Table 2) having specific dimension 250 mm × 250 mm × 300 mm was used to carry out remediation of heavy metals as a batch type to conduct the experiments. Good quality metal sheets of aluminum used as electrodes of 150 mm × 250 mm × 2 mm size for EC. The sufficient gap between the anode and cathode was varied as per requirement. The reactor is constructed in such a style; it could be adjusted horizontally as well as vertically as needed.

Table 2

Reactor and Electrodes Characteristics

The experimental setup is shown in Fig. 1 for the EC experiments, Aluminum (Al) plates with 2 mm thickness were used, and the surface area in contact with the electrolyte was in each case 113 cm² per side. In each experiment, two plates were used in the electrochemical reactor and the distance (d) between plates was varied from 2–4 cm. The electrodes were placed using a monopolar configuration with a total anodic or cathodic surface area (S) of 450 cm².

Fig. 1

Schematic diagram of electro chemical cell for removal of metals and TSS.

The current values were selected from 150 mA to 600 mA corresponding to a current density from 1.3 mA/cm² to 5.3 mA/cm² using a precision DC power supply (Microtech agencies Dhanbad, India) characterized by the ranges 0–2 A for current and 0–30 V for voltage. Before each experiment, the electrodes were polished with abrasive paper to get rid of any oxide film and then thoroughly rinsed.

To pursue the progress during treatment, 10 mL samples were periodically taken from the container at predetermined time intervals (10 to 40 min) and were filtered using Whatman filter paper of grade 42 (GE Healthcare UK Limited) to sort out the sludge from the solution to be dissected. The residual concentrations of metal ions were determined using an atomic absorption spectrophotometer (FAAS-GBC Avanta, Australia) according to APHA standard 2012 [11]. The pH was continuously measured in the 18-L container and was not adjusted during the treatment. All experiments were performed at room temperature.

2.3. Calculations

The amount of electrical energy used is an important economical parameter in the EC process [10]. This parameter is computed by Eq. (1):

(1) E=UITV

E is the electrical energy used (in kWh/m³), U is the voltage applied (in V), I is the current (in A), T is the coagulation time in hours. V is the volumes in liters. The amount of sacrificed electrode use is determined by measuring the initial and eventual weight of the electrodes.

The percentage removal efficiency of EC process was computed as a function of operating time by Eq. (2):

Removal efficiency, %

(2) RE=C0-CtC0×100

Where C₀ and C_t are heavy metal concentrations for each heavy metal and TSS at times 0 and t.

For kinetic study, first order and second order kinetic model were considered to describe for the removal rate [12]. The EC batch process, the mass conservation of pollutants ion is:

(3) -dCdt=-rD

Where (r_D) is the removal rate in ppm/min and t is EC time in min. With the first-order model (r_D = k₁C), the integration of Eq. (3) at the initial concentration C(0) = C_0, gives

(4) C(t)=C0e-k1t

Where k₁ is the first-order rate constant in min⁻¹. For the second order model (−r_D = k₂C²), the time-dependent concentration is obtained as:

(5) 1C(t)=1C0+k2t

Where k₂ is the second-order rate constant in ppm⁻¹min⁻¹.

3. Results and Discussion

3.1. Establishment of Metals Concentration and Other Water Characteristics

To evaluate the EC performance, synthetic water was prepared with initial concentration of TSS and heavy metals concentration which imparted a sufficient electrical conductivity, total dissolved solids (TDS), turbidity in water samples. The pH of the synthetic water drops down, which again adjusted as per experimental requirement during the establishment of physiochemical characteristics (Table 3). The pH of the solution was adjusted by adding either 0.1 N NaOH or 0.1 N HCl solution.

Table 3

Physiochemical Characteristics of Synthetic Water Used

3.2. TSS Removal

The relationship between the TSS removal efficiency and contact time for pH 7 at 30 min operating time of EC process is depicted in Fig. 3 in which maximum removal occurred at 2 cm electrode distance. The synthetic water of the initial value of TSS is 135 mg/L is used for experiments The Fig. 2 depicts that as the contact time increased from 10 min to 40 min removal efficiency increased from 62.1% to 76.6%. The removal efficiency, increased up to 30 min of contact time and beyond that no further significant increased was observed. Bukhari [13] also demonstrated same observation at current 0.2 A which has supported removal of TSS was significantly consistent after 30 min of process time [14]. The maximum removal of suspended solids removed in first 10 min after that suspended solids removed in smaller ratios are indicated in the Fig. 2, which was also reported by Aji et al. [4], for first 15 min after that removal was consistent and also similar results has been also reported by Chou et al. [15] for colour removal efficiency in 20 min of process time (at least 80%) and 53–99% of the initial concentration of zinc and copper decreased within 15–30 min of processing reported by Bazrafshan et al. [16]. The maximum removal efficiency of TSS was observed (> 76%) after 40 min of operating time at current density 5.3 mA/cm² from synthetic water in this study. The efficiency of TSS removal was increased with an increase in current density from 46.6% at 1.3 mA/cm² till it reaches 76.6% at 5.3 mA/cm². Beyond 5.3 mA/cm² no further TSS removal was observed. Such lower removal efficiency for suspended solids was bubble formation mechanism in the reactor [17] investigated that the bubbles formed by EC were not sufficient for a high removal efficiency of suspended solids. The reason that affects bubble size and generation is that the electrode surface, due to the passivation, has a rough surface, which provides larger adhering forces to bubbles than smooth surfaces, thus decreasing their generation.

Fig. 3

The relationship between TSS removal efficiency and current density at pH 7, different electrode distances, contact time 30 min.

Fig. 2

Removal of TSS along with contact time at different current density and at pH 7, electrode distance 2 cm.

3.3. Effect of pH

According to literature study, it was found that at neutral pH of 7, all the metals demonstrated optimal and consistent removal efficiency [18], so pH 7 was established in this study for experimentation. Duration of the process was 40 min and after every 10 min pH of the solution has been checked using a digital pH meter was found that pH changes from its initial value as indicated in Fig. 4. At the end of the process pH has been reached to a value of 7.34, 7.77 and 7.88, respectively, for different interelectrode distances (2–4 cm). In EC where the Al electrode is used, it has been observed that at passably basic ambience, Al(OH)₃ precipitation occurs and the sweep-flock mechanism dominates [19]. Maximum variation was observed at a lower interelectrode distance (2 cm) while at another distance pH of water had less variation. Chen et al. [15] advocated that in the presence of anions such as chloride or sulphate, aluminum hydroxide can exchange with these ions thus releasing hydroxyl ions and raising pH. The fact behind this mechanism that the generated metal hydroxides which act as the flocs and remove the pollutant by sedimentation get degraded by collision with each other due to high electrostatic attraction [20].

Fig. 4

Change in pH value during experiments at various electrode distances.

3.4. Effect of Current Density

In all EC processes, current density is the most important parameter for controlling the reaction rate within the electrochemical reactor and adjusts bubble production and its size and distribution. It has been found that as current density increases the removal rate of pollutants also increases [17, 21]. Higher metal removal efficiency accomplished by using electrocoagulation-flotation (ECF) with iron electrodes results from its capability of simultaneously inducing several processes (metal deposition on the cathode, precipitation, and co-precipitation of metals) and, more importantly, from the high sorption capacity of polymeric iron hydroxides generated by the anodic dissolution [14, 22]. The current density is expected to exhibit a strong effect on the removal efficiency [23–25] especially on the kinetics of heavy metals removal: the higher the current, the more efficient the ECF treatment. An increase in current density from 1.3 to 5.3 mA/cm² yields an increase in the efficiency of chromium, copper and zinc removal for aluminum electrode. At a high current density, the extent of anodic dissolution of aluminum increases, resulting in a greater amount of precipitate and removal of copper, zinc and nickel [26].

In this study it has likewise been noticed during a process that hydrogen bubble production was more and small in size that helps to accumulate the pollutants at upper surface at high current density. Flocs deposited on the surface of the water easily removed and sludge generated was less in quantity at the bottom of reactor as such condition.

3.5. Heavy Metals Removed

In this study the experiments conducted for 40 min contact time at different current density and electrode distances. Here chromium, copper and zinc removal percentages at different time and current density have been studied. Chromium, Copper and zinc initial concentration in water were 10 mg/L before the experiment.

The more current density was applied, the more Al³⁺ and OH⁻ were dosed into the ECF system and the faster the metal concentrations decreased. In addition, the rate of bubble generation increases and the bubble size decreases with the increase of current density. Both of these trends are benign in terms of high pollutant removal efficiency by H₂ flotation [9]. By observing the impact of EC operating time on the removal efficiency of metals from the waste synthetic water, it was observed that removal efficiency increases with the increase of electrolysis time, which is in accordance with the results of other authors [8, 27]. According to this work, the highest chromium removal efficiency (> 59%) was obtained after 40 min under the condition of 4 mA/cm² of current density (Fig. 5). Some authors found that the pH of the solution has a significant effect on the Cr(VI) removal efficiency [28–30]. The findings show that ions of chromium(VI) change into Cr³⁺ during the reaction that occurs around the cathode, and then the ions of Cr³⁺ are combined with the OH⁻ resulted from water hydrolysis and Cr(OH)₃ is produced. When pH is kept between 3 and 7, cations of Al³⁺ around the anode produce polymeric species such as Al₁₃O₄(OH)₂₄⁷⁺ that leads to the effective removal of ions of Cr³⁺ via a sweep coagulation process [29]. Zewail and Yousef [31] demonstrated the effect of pH on % removal of Cr³⁺ & Cr⁶⁺ and found maximum % removal of Cr³⁺ occurs at pH 8, whereas the maximum % removal of Cr⁶⁺ occurs at pH 4.5. The copper removal efficiency (> 99%) was obtained after 40 min by using an interelectrode distance of 3 cm and current density of 4 mA/cm². In the case of zinc, the removal efficiency (> 82%) at 5.3 mA/cm² for 3 cm was achieved after 40 min (Fig. 5). A shorter interelectrode distance is desirable, because the electrical resistance (IR drop) increases with the interelectrode distance increase [32]. By increasing the interelectrode distance, less interaction of heavy metals with hydroxide polymers of aluminum is expected [33]. According to the Cu-Pourbaix diagram, copper is solid in the form of Cu(OH)₂ at pH approximately > 4.5 until pH 14. The Zn-Pourbaix diagram shows that zinc is solid as ZnO at pH between 7 and 14 [4]. Removal of copper and zinc has been investigated higher as per Pourbaix diagrams indicates pH 7 suitable for such higher removal, but zinc pourbaix diagrams indicate stability of oxide of zinc due which zinc found in stable passive phase at temperature range reported in revised pourbaix diagrams of zinc [34].

Fig. 5

Variation of percentage removal efficiencies of heavy metals with current density after 40 min of EC process time of 7 L synthetic water (Inter electrode distance 3 cm, and pH 7).

The results can be explained by the flotation of hydrogen bubbles produced at the cathode, which produce more stable flocks when the interelectrode distance was 3.0 cm. The lowest interelectrode distances obstruct the adequate mass transport in the ECF cell, thus reducing removal efficiency rates. This behavior indicates the proportional importance of water movement and turbulence along the handling time and their great dependence on the interelectrode space.

3.6. Effect on Electrical Conductivity

Electrical conductivity is the ability of the solution to conduct electrical current between two electrodes. This electrical conductivity seems to affect more directly the voltage or the current intensity. During the EC process, it has been observed that the electrical conductivity of the solution in the reactor fluctuated in decreasing order due which TDS also changed. It had fluctuated 5–6% of its initial value. Decreasing the conductivity of the solution resulted in enhance of the cell voltage.

3.7. Effect of EC Time and Kinetic Study

In this work, the kinetic study for the removal of pollutants was considered for various current densities at the ambient temperature and constant synthetic water volume. The squared-correlation coefficient, R², was used to measure the goodness of the kinetic model. The kinetic parameters of both first- and second-order models together with the R² values are given in Table 4. At current density of 5.3 mA/cm², the R² values that correspond to both kinetic models were found close to unity for all heavy metals and TSS. Only first-order kinetic model can describe the removal rate of chromium ions (Cr³⁺) at lower current density. The copper and zinc ions were the only heavy metal ions that their removal rate can be modeled by first- and second-order kinetics since the corresponding R² value at a lower current density was close to unity. In case of total suspended solids only for both kinetics modeled corresponding coefficient of determination, R² were close to unity at higher current density i.e. 5.3 mA/cm².

Table 4

Predicted Parameters of First- and Second-order Removal Rates of Heavy Metal Ions at Different Current Densities with Solution Volume = 7,000 mL, and pH = 7

3.8. Electrical Energy Consumption

The amount of energy consumed is an important economic parameter in the EC process. The majority of operating costs is also related to the amount of electrical energy used. Also in this study the amount of energy used for metals and TSS removal was evaluated as a function of time in different current densities and potential. When the current density increases from 1.3 mA/cm² to 5.3 mA/cm² (0.150–600 A), the energy consumption increased slightly. Results showed that increase in current leads to increase in energy consumption due to polarization and increase in the number of aluminum compounds, which elevate the efficiency of metals and TSS removal as well.

Therefore, in order to reach an optimum current density, it’s necessary to evaluate both the removal percent and the amount of electrical energy used [7, 8, 21, 26, 33] as depicted in Table 5.

Table 5

Consumption of Electrical Energy during Experiments at Different Time Conditions

The electrical energy, 0.459 kWh/m³ has been consumed to achieve 99%, 59.2% and 71.6% removal of Cu, Cr and Zn respectively for 30 min process time. Moreover, beyond 4.0 mA/cm² current density (0.450 A current) no significant removal was observed as shown in Fig. 3 and Fig. 5.

4. Conclusions

In this work, EC treatment using aluminum sacrificial electrodes for a synthetic water containing Cu, Cr, and Zn heavy metals were investigated. Effects of current density, operating time, and initial pH on the removal efficiency were examined in a parallel plate electrochemical reactor.

This study has concluded that experimentally as well as kinetic modeling has given high removal rate for all metals and TSS at higher current density except copper metals which give the same results at lower current density. During experiments, it was observed that pH of water increased more at lower current.

In this study concluded that current density required for efficient removal of heavy metals is lower at minimum time 30 min of process except zinc. Here it has been observed removal efficiency almost same for electrode distance 2 cm or 3 cm and operating time 30 min to 40 min.

In the context of sludge generated study shows that the sludge accumulates on the top layer of solution is more in comparison of the bottom of the reactor. Sludge generated is less at bottom at high current density. In the case of energy consumption, it was concluded that 0.459 kWh/m³ is sufficient for 99% Cu, 59% Cr and 71% of Zn up to 30 min of treatment time for which 0.450 A current is required.

Granting to the closing remarks, EC using monopolar aluminum electrodes is convenient and less power consumption for effective removal of heavy metals from synthetic water and achieves faster removal of pollutants in comparison to chemical coagulation, where several hours are needed.

Acknowledgements

We would wish to get hold of this chance to convey our sincere gratitude to TEQIP -II for funding this research study. We are immensely grateful to the Department of Environmental Science and Engineering, Indian School of Mines for their unconditional support and encouragement. We are indebted to all researchers who have guided us with their valuable data and info.

Nomenclature

C₀

Initial concentration of the heavy metals and TSS (mg/L)

C_t

Concentration of after t time in minute (mg/L)

Distance between electrodes (mm)

Electrical energy consumption (kWh/m³)

Faraday’ constant, 96,500 C/mol

Current used in EC process (ampere)

Amount of electrode (anode) metal dissociate in reactor, g M Molar mass, g/mol

R_E

Removal efficiency (%)

Anode surface area (cm²)

Time of EC process (h)

Cell voltage (V)

Volume of water in reactor (m³)

Electrode with aluminum anode/cathode

Electrode with iron anode/cathode

Electro-coagulation

ECF

Electrocoagulation-Flotation

TSS

Total suspended solids, mg/L

TDS

Total dissolved solids, mg/L

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Reference	[7]	[8]	[9]	[4]	[10]	This study conditions
Kind of water	Synth. Water	Synth. Water	Metal plating wastewater	Synth. Water	Grenhole ground water	Synth. Water
Conductivity (mS/cm)	20	1.7–2.9	2	1.47	0.35	0.62 (21.3°C)
Initial pH	4.5–7.5	4.9	3	3; 5.68; 8.95	7.7	3.2 (7 after addition of NaOH)
Metal concentration (ppm)	Cu²⁺ 50–250 Zn²⁺ 50–5000 Ni²⁺ 50–250 Cr(VI) 10–50 Ag⁺ 5–50	Cu²⁺ 59 Zn²⁺ 67 Ni²⁺ 67	Cu²⁺ 45 Cr(VI) 44.5 Ni²⁺ 394	Cu²⁺ 50–250 Zn²⁺ 50–250 Ni²⁺ 50–250 Mn²⁺ 50–250	Cu²⁺ 12 Zn²⁺ 20 Ni²⁺ 20	Cu²⁺ 10 Cr⁶⁺ 10 Zn²⁺ 10
Treated volume (L)	1.2	0.9	0.65	0.5	15	7
Number of electrode used	4	2	6	6	4	2
Electrode material	Al	Al	Al or Fe	Fe	Al or Fe	Al
Interelectrode Distance d (mm)	5	40	10	3	15	30
Anodic surface area S (cm²)	300	54	200	100	720	113
Ratio d/S cm⁻¹	0.002	0.074	0.005	0.003	0.002	0.017
Current I (A)	0.3–3	0.27–1.08	0.5–2	0.2–2.5	0.5–1	0.15–0.6
Current density (A/m²)	16–98	50–200	25–100	20–250	7–14	13–53
Voltage U (V)	-	7–22	-	11.75	4–10.5	6.3–16.6
Treatment time t (min)	0–140	0–80	0–60	0–50	0–180	0–40
Energy consumption U.I.T/V (kW h m⁻³)	-	45 (calculated from the data at I = 1 A and t = 60 min)	2 (at I = 1A and t = 15 min)	49 (at I = 2.5 A and t = 50 min)	0.6 and 0.59 (at I = 1A and t = 60 min with Fe respectively Al electrodes)	0.459 (at I = 0.450 A and time 30 min)

Reactor Characteristics	Specification
Material	Plexiglass
Size	250 mm × 250 mm × 300 mm
Reactor mode	Batch
Reactor Volume	18 L
Working volume	7 L
DC power supply
Voltage range (V)	0–30
Current range (A)	0–2
Electrode
Material	Aluminum
Size	300 mm × 150 mm × 2 mm
Anode surface area	113 m²
Connection arrangement	Parallel type

Pollutants	Current density (mA/cm²)	First order kinetic, dC/dt = k₁C, K₁(min⁻¹)	Coeff. of Determination (R²)	Second order kinetic, – dC/dt = k₂ C², k₂ (ppm⁻¹ min⁻¹)	Coeff. of Determination (R²)
Cr	1.3	0.015	0.7802	0.0022	0.6748
	2.6	0.016	0.8606	0.0022	0.0001
	4	0.022	0.8491	0.0036	0.8260
	5.3	0.015	0.8528	0.0021	0.8301

Cu	1.3	0.08	0.7724	0.0632	0.3267
	2.6	0.081	0.1488	0.063	0.8253
	4	0.115	0.6740	0.247	0.6435
	5.3	0.115	0.7456	0.247	0.1089

Zn	1.3	0.009	0.5538	0.0011	0.5400
	2.6	0.017	0.7684	0.0017	0.8813
	4	0.031	0.3768	0.0063	0.1255
	5.3	0.043	0.8824	0.0114	0.3218

TSS	1.3	0.0156	0.2909	0.00016	0.0076
	2.6	0.019	0.7529	0.00021	0.6112
	4	0.033	0.8869	0.00053	0.0751
	5.3	0.036	0.9560	0.00059	0.9998

Voltage, (Volt)	Current, (Amp)	Electrical energy consumption (kW h/m³)

		10 min	20 min	30 min	40 min
6.3	0.150	0.0216	0.0445	0.067	0.089
8.6	0.300	0.058	0.121	0.184	0.243
14.3	0.450	0.141	0.303	0.459	0.606
16.6	0.600	0.227	0.469	0.711	0.939