Next Article in Journal
Next Article in Special Issue
Previous Article in Journal
Previous Article in Special Issue

Water 2014, 6(5), 1172-1186; doi:10.3390/w6051172

Establishment of the Underlying Rationale and Description of a Cheap Nanofiltration-Based Method for Supplementing Desalinated Water with Magnesium Ions
Liat Birnhack *, Oded Nir and Ori Lahav
Faculty of Civil and Environmental Engineering, Technion-Israel Institute of Technology, Haifa 32000, Israel; E-Mails: (O.N.); (O.L.)
Author to whom correspondence should be addressed; E-Mail:; Tel.: +972-4-8292627; Fax: +972-4-8295696.
Received: 14 March 2014; in revised form: 15 April 2014 / Accepted: 16 April 2014 /
Published: 5 May 2014


: The importance of supplying drinking water with a balanced mineral composition, including a minimal concentration of Mg(II) ions, has been recently acknowledged by many publications, as well as in official WHO guidelines. The issue is relevant to naturally occurring soft waters and lately to the rapidly increasing volume of supplied desalinated water. This paper presents an enhancement of a recently developed nanofiltration-based method for the selective separation of soluble Mg(II) species from seawater. The generated rich-Mg(II) brine is demonstrated to be suitable for supplementing soft waters with magnesium ions. The brine, generated using a commercial membrane (DS-5 DL, Osmonics) at various operational conditions is characterized by high Mg(II) concentrations (~8.5 g/L) and low Cl:Mg and Na:Mg molar concentration ratios (1.6 and 0.6, respectively, at 28-bar operation). A food-grade antiscalant is dosed to the feed seawater to prevent scaling; however, since the Mg(II) concentration in the brine is high, for attaining 10 mg Mg/L of desalinated water, the dilution ratio with the desalinated water is ~1:850, resulting in maximal additional concentrations of 0.024 antiscalant, 34.9 Cl(−I), 12.9 Na(I), 0.05 Sr(II) and 0.003 B (all concentrations in mg/L). The overall cost of 1 kg of Mg(II) separated by the presented process amounts to between $0.05 and $0.07, i.e., much cheaper than the estimated costs of alternative processes for Mg(II) addition to desalinated water.
nanofiltration; post-treatment; desalination; magnesium ion; drinking water; cost assessment; water quality

1. Introduction

1.1. Health Risks Associated with Low Mg(II) Concentrations in Drinking Water

Throughout the years, epidemiologic studies have implied that low concentrations of magnesium ions (Mg(II)) in drinking water may be associated with several significant health risks (e.g., type 2 diabetes, metabolic syndrome, hypertension, sudden cardiac death, several cancer types, and more [1,2]). However, an unambiguous linkage has not been established, and the protective mechanism of Mg(II) ions has not been identified. Despite this, in 2009, the World Health Organization (WHO) concluded in an official document that “there is growing consensus among epidemiologists that the epidemiological evidence, along with clinical and nutritional evidence, is already strong enough to suggest that new guidance should be issued” [1]. In view of this statement, the WHO thus recommended maintaining a minimum Mg(II) concentration of 10 mg/L in all drinking waters [1].

Desalinated water is a rising water source in which the Mg(II) concentration is usually close to zero, even after the re-mineralization step, which typically aims at replenishing calcium ions (Ca(II)) and carbonate alkalinity to the water. Following the WHO recommendation, the Israeli Ministry of Health decided in 2011 on the addition of Mg(II) to desalinated water to a level of 20–30 mg Mg/L [3]; however, Mg(II) addition has not, do-date, been implemented in Israel. Following the 2009 WHO recommendation, several epidemiological studies were published, which supported the request for replenishing Mg(II) in desalinated water: For example, Chiu et al. (2010) [4] conducted matched cancer case-control studies to investigate the relationship between the risk of cancer occurrence and drinking water quality, including Mg(II) content; the study showed that the risk of pancreatic cancer associated with high tri-halo-methane (THM) levels was elevated among cases with lower Mg(II) intake from drinking water. The authors suggested that Mg(II) may act similarly to folate, which has already been proven mechanistically to have a protective effect against cancer. Correspondingly, it was shown that Mg(II) levels in drinking water modified the effects of THM on the risk of colon cancer development [5]. Moreover, drinking water Mg(II) intake apparently modifies the effect of exposure to nitrate in drinking water and the associated increased risk of mortality attributed to esophageal cancer [6]. Ca(II) and Mg(II) intake from drinking water may reduce the risk of gastric cancer occurrence related to the exposure of a high concentration of nitrate in drinking water [7]. A clear trend of a decreased risk of lung cancer in women with elevated Mg(II) levels was also observed [8].

Other studies showed the positive effect of drinking water Mg(II) with respect to additional health related aspects: for example, Mg(II) may have a positive role against hip fractures, according to the inverse association between drinking water magnesium concentration and the risk of hip fracture in both genders observed in Norway [9]. It may have a positive effect on blood pressure, as reflected by the comparison of individuals from some Serbian municipalities having different drinking water Mg(II) concentrations. This comparison showed that diastolic blood pressure was the lowest in subjects from the district with the highest drinking water Mg(II) concentration (42 mg/L, compared to 11 mg/L) [10]. Low levels of magnesium in drinking water can aggravate liver damage from alcohol [11]. In addition, results supporting the theory of a link between soft water and the pathogenesis of osteoporosis were presented [11]. Consumption of low-mineral bottled water (TDS of 1.2–10.9 mg/L and hardness of 2.3–0.8 mg/L as CaCO3) is associated with higher levels of CVD biomarkers, serious pathological lesions of the heart and aortic arch in rabbits (following 12 month of low mineral water consumption) and an increased level of Hcy and a deteriorated lipid profile in young men (after 30 days of low mineral water consumption) [12].

In addition to these health related findings, it should be recognized that a low concentration of Mg(II) in drinking water has a significant inverse impact on the overall Mg(II) intake, as demonstrated by Spungen et al. [13], who compared the total Mg(II) and Ca(II) intake (i.e., the intake from both food and drinking) of individuals living in areas in which different water sources were supplied, including an area supplied by desalinated water. According to their results, the Mg(II) and Ca(II) intakes may be significantly lower among individuals consuming desalinated water than among individuals consuming water from conventional or mixed sources. The latter results corroborate the recommendation to replenish desalinated water with Mg(II) and Ca(II).

To conclude, there are publications that imply that magnesium intake does not necessarily protect against cardiovascular disease and coronary heart disease. However, the majority of relevant studies, including some endorsed by the WHO, show evidence of statistically significant inverse association between Mg2+ concentrations in drinking water and cardiovascular mortality.

1.2. Other Aspects Associated with Low Mg(II) Levels in Irrigation Water

A valuable water source allocated for agricultural irrigation should include a minimum Mg(II) concentration, required in order to minimize the need for the application of fertilizers, particularly in case the local soil is low in minerals [14] and no other water sources containing these components are continuously available. Yermiyahu et al. (2007) [15] stated that even if such water sources are available (i.e., high mineral water sources) and are planned to be mixed with the desalinated water, to minimize fluctuations in the quality of the supplied water, the mineral content of the desalinated water should approach the content of the other sources. Otherwise, the farmer will have to install and operate sophisticated and expensive control systems to flatten fluctuations. The addition of adequate concentrations of these minerals to the desalinated water in the desalination plant may circumvent the need for adding them through fertilizers.

With respect to the health impact of irrigating with water low in Mg(II), it has been noted that the decreasing mineral content in high-yield grains, as observed since the Green Revolution, has coincided in time with rising global mortality rates from cardiovascular diseases. This suggests that irrigating with low Mg(II) waters results in low Mg(II) intake from cultivated crops, which, in turn, may be associated with elevated cardiovascular mortality over the past 50 years [16]. Finally, it is noted that in arid areas of the world, such as Israel and parts of Spain and Australia, a considerable portion of treated wastewater is reused for agricultural irrigation. Thus, low Mg(II) concentration in drinking water eventually leads to low Mg(II) concentration in irrigation water [17].

1.3. Description of a Cheap and Very Simple Process for Enriching Desalinated Water with Mg(II) (As Well As Ca(II) and SO4(−II)) Through the Dosage of Seawater Nanofiltration Retentate

This paper describes new results of a recently developed method [18] for separating Mg(II) ions from seawater in a fashion that maximizes the Mg(II) concentration in the target solution, while at the same time minimizes the addition of the unwelcome seawater species (Cl, Na+, B, Br, etc.) to the receiving desalinated or soft water. The process is schematically depicted in Figure 1. The Mg(II) separation method is based on passing seawater through suitable nanofiltration (NF) membranes in a way that: (1) enhances the separation between divalent and monovalent ions, i.e., rejects the divalent ions, while allowing monovalent ions to pass the membrane; and (2) generates brine with the highest Mg(II) concentration possible. Since the solution dosed to the desalinated water is the brine of the NF step, pathogens initially present in seawater will remain in the seawater NF brine. Thus, in order to prevent the contamination of the desalinated water, the NF brine is passed through an ultrafiltration membrane, prior to its introduction to the desalinated water. Note that the bacteria and protozoa retention of ultrafiltration (UF) membranes is very high (6-log attenuation [19]), while virus retention is moderate (it can reach 6-log removal, but often a removal below 1-log is reported [19]). Therefore, it can be assumed that the brine dosed to the desalinated water contains no bacteria and protozoa, but it may contain viruses. However, since disinfection is normally applied to the product water prior to distribution, the viruses that might have passed the UF membrane would be removed by the disinfection step.

As the brine is produced, food-grade antiscalant (e.g., Genesys CAS, manufactured by Genesys International, [20]) is dosed to the feed water in order to prevent CaCO3 and CaSO4 precipitation and subsequent chemical fouling of the membrane. Previous studies [18,21] showed that operating the NF step at high recovery ratios was beneficial in the sense that it reduced the ratio between the unwanted ions (namely Cl(−I) and Na(I)) and the desired ions (namely Mg(II)) in the brine. The produced NF Mg(II)-rich brine is ultimately used as the Mg(II) ion source at the post-treatment stage in the desalination plant. Naturally, such a supplementary step can be combined with any conventional post-treatment process and is not limited to calcite dissolution, which was arbitrarily shown as the Ca(II) and alkalinity addition technique in Figure 1. Moreover, the investigated NF-based Mg(II) addition process can be integrated also into the treatment of other soft water types, and not exclusively to reverse osmosis (RO) desalinated water. As compared with previous methods suggested for Mg(II) addition to desalinated waters at the post treatment stage [22,23,24,25], the current approach is less selective in the sense that the Mg(II) supplied to the water is accompanied by a certain (not very high) concentration of (mainly) Na+ and Cl, but on the other hand, it is simpler in operation and (as shown at the end of this paper) much cheaper than any other (reasonable) alternative.

2. Experimental Section

2.1. Experimental Apparatus

NF experiments were carried out using a pilot-scale seawater desalination unit comprising one 4″ spiral wound NF module. The experimental system included two pumps, a booster pump (centrifugal) and a high pressure pump (positive displacement), as well as a titanium heat exchanger and a chiller for maintaining a constant temperature of 25 ± 1 °C. In addition, the system includes flow meters for the permeate and the brine streams, a 25-micron filter to protect the high-pressure pump, pressure and temperature gauges and a pressure regulator spring valve. All tubing, fittings and wetted parts in the equipment are stainless steel made. In the experimental setup, the concentrate stream was continuously recycled back to the feed tank, which initially consisted of ~200 L of typical Mediterranean seawater. The permeate stream was collected in a different tank, which was placed on a scale for the purpose of accurately determining the recovery ratio at any given time during the run. Once a desired recovery ratio was attained, the permeate stream was directed to the feed tank, and the system was allowed to stabilize in a full recirculation mode for a minimum of 20 min. Samples were then collected from the feed tank (representing the cumulative brine concentrations), the permeate tank (representing the accumulative permeate concentrations) and from the brine and permeate pipes, representing the momentary brine and permeate concentrations, respectively.

Water 06 01172 g001 1024
Figure 1. Schematic representation of the Mg(II) enrichment process, based on seawater nanofiltration (NF) separation.

Click here to enlarge figure

Figure 1. Schematic representation of the Mg(II) enrichment process, based on seawater nanofiltration (NF) separation.
Water 06 01172 g001 1024

2.2. Calculations

Two types of solute rejection values (denoted r) are presented and discussed in this paper: (1) the “overall rejections” (that is, the rejection values calculated based on the initial feed concentration of the solute (CFeed) and its accumulative permeate concentration (CP accu)): r = 1 – CP accumulate/CFeed; and (2) the “momentary rejection” (that is, the solute rejection at a specific time, or specific recovery, calculated based on the momentary permeate solute concentration (CP t) and the solute concentration on the feed side of the membrane at the specific time).

In the next sections, unless otherwise specified, the overall rejections are presented and discussed.

2.3. Analyses

The samples were characterized by Inductively Coupled Plasma—Atomic Emission Spectroscopy (ICP-AES) (1CAP6300 Duo, Thermo Scientific) for the determination of the following ion concentrations: Ca2+, Mg2+, Na+, SO42−, K+, B, Sr2+. In addition, chloride concentrations were determined using the argentometric method, according to standard methods [26].

3. Results and Discussion

3.1. Resultant Water Quality

Dosing NF brine for enriching desalinated water with Mg(II) unavoidably introduces other components to the product water. Thus, the composition of the produced brine was analyzed under various conditions in order to identify the most advantageous NF process operational conditions, from the desalinated water quality standpoint. Figure 2 presents the Mg(II) rejections (overall rejections) recorded with three applied pressures and a wide range of recovery ratios. As observed from Figure 2, considerably higher rejection values were achieved when the applied pressure was increased from 10 to 18 bar, while only slight improvement was apparent in the rejection values when the pressure was further increased to 28 bar. Consequently, at the higher pressure values, a smaller volume of seawater is required in order to separate the required Mg(II) mass. Moreover, the dilution effect when dosing the brine to the desalinated water is reduced when the pressure is increased, because the brine’s Mg(II) concentrations are elevated: 7.707, 7.892 and 8.520 g Mg/L at 10, 18 and 28 bar, respectively (at a recovery of 85%). From the quality aspect of the product desalinated water, another important factor is the concentration ratios between unwanted seawater ions (mainly Cl(−I) and Na(I)) and the target ion (Mg(II)), which are shown in Figure 3. From Figure 3, it can be concluded that decreasing the pressure from 28 bar to 10 bar had a negligible effect on the Na(I) to Mg(II) and on the Cl(−I) to Mg(II) molar concentration ratios. Note that for technical reasons, the recovery ratio in the experiments was not increased beyond 90%. Therefore, only the Na(I) and Cl(−I) to Mg(II) concentration ratios presented in Figure 3 at recovery ratios below 90% are calculated based on the concentrations measured in the brines, while the points representing the concentration ratios at 95% recovery are theoretically shown, by way of extrapolation. The 95% recovery ratio points (full symbols) were derived from the approximate linear slopes of the measured points (empty symbols). Thus, these points are merely estimations, which still need to be proven. The theoretically calculated points suggest that such an elevation of the recovery ratio would reduce the Cl(−I) to Mg(II) molar ratio to 1.80, 1.67 and 1.57 at 10, 18 and 28 bar, respectively; that is, below the Cl(−I) additions resulting from pure MgCl2 dosage. With respect to the Na(I) to Mg(II) ratio, it would be reduced to 0.65 0.74 and 0.67, at the 10, 18 and 28 bar scenarios, respectively.

Water 06 01172 g002 1024
Figure 2. Mg(II) rejection values at 10, 18 and 28 bar (∆, ○ and +, respectively) as a function of the recovery ratio.

Click here to enlarge figure

Figure 2. Mg(II) rejection values at 10, 18 and 28 bar (∆, ○ and +, respectively) as a function of the recovery ratio.
Water 06 01172 g002 1024

Figure 2 shows that the rejection of Mg(II) by the NF membrane deteriorated with the recovery value, as expected. The same trend was observed for all other ions, i.e., the reduction in rejection as the recovery ratio was increased. However, the results shown in Figure 3 are a consequence of differences in the extent of the reduction of the rejection with the recovery, for both Mg(II) and the monovalent ions (Cl(−I) and Na(I)). In other words, at high concentrations (i.e., high recovery ratios), the rejection values for all ions decrease. However, the rejection of Mg(II) is reduced in a moderate manner, while the rejections of the monovalent ions (Cl(−I) and Na(I)) decrease more steeply. This phenomenon (which has already been observed in previous studies, e.g., [18]) implies that the governing filtration mechanism is such that the momentary rejection of Mg(II) declines in a lesser fashion as a result of the increase in concentration in the feed side of the membrane. It is apparent that the rejections of K(I) and Na(I) deteriorated more sharply (from rejections of around 4% to negative rejection below −5% for Na(I) and K(I), values varying significantly from experiment to experiment, i.e., 10, 18 and 28 bar) than the rejection of Mg(II) (which was reduced from 97.0% to 94.4% in the 28 bar experiment, for example). The decrease in the total rejection of Mg(II) may be completely attributed to increased Mg(II) concentration in the retentate side and the decreased flux, which is more prominent at low trans-membrane pressure, explaining the steeper decrease observed in the 10-bar experiment. The negative rejection of Na(I), on the other hand, was ascribed to increased electro-migration of Na(I), resulting from local electrical fields, which arise when ions of different diffusivities move through NF/RO membranes. Overall, the trend of the rejection results (as a function of the recovery ratio) is in accordance with the diffusivity rate expected from these ions, i.e., the diffusion coefficients (in 10−6 cm2∙s−1) of K(I) and Na(I) (19.57 and 13.34, respectively [27]) are higher than the diffusion coefficients of Mg(II) (7.06 [27]). The diffusion coefficient of Ca(II) is also low (7.92 × 10−6 cm2∙s−1 [27]), and its rejection was also only moderately reduced with recovery.

Water 06 01172 g003 1024
Figure 3. Molar concentration ratios of Na(I) to Mg(II) (a) and Cl(−I) to Mg(II) (b) in brines generated at 10, 18 and 28 bar (∆, ○ and □, respectively), as a function of the recovery ratio. The 95% recovery ratio points (filled bars) are estimations based on linear extrapolation, while all other points are the measured results.

Click here to enlarge figure

Figure 3. Molar concentration ratios of Na(I) to Mg(II) (a) and Cl(−I) to Mg(II) (b) in brines generated at 10, 18 and 28 bar (∆, ○ and □, respectively), as a function of the recovery ratio. The 95% recovery ratio points (filled bars) are estimations based on linear extrapolation, while all other points are the measured results.
Water 06 01172 g003 1024

The effect of dosing the NF brine to desalinated water was studied assuming nine different scenarios: filtration at 10, 18 and 28 bar and three different dosages of brine for achieving final Mg2+ concentration of 5, 10 and 20 mg/L of desalinated water. These three concentrations were chosen in order to simulate three scenarios: (1) the intended Mg2+ concentration (5 mg/L) addition at the Thames desalinated post treated water [28], which is apparently achieved by MgSO4 dosage [29]; (2) the minimum concentration recommended by the WHO, i.e., 10 mg/L; and (3) the minimum concentration recommended by the Israeli Ministry of Health, i.e., 20 mg/L. All nine scenarios were calculated according to the results obtained at 85% recovery. On top of sodium and chloride ions, the addition of all major ions and of the antiscalant due to the NF brine dosage was calculated for the nine scenarios. The results are shown in Table 1, which shows that the overall quality of the desalinated water is hardly damaged by the addition of the brine. With respect to chloride and sodium ions, it can be concluded that their additions are not high (< 79 and < 23 mg/L, respectively, in the 20 mg Mg/L case scenario) compared to background concentrations in conventional drinking water sources and compared to the addition of chlorides through the most practical technique for magnesium addition (i.e., dosage of MgCl2). Note that the WHO did not set a health-based guideline to chloride and sodium ions, but rather mentions a taste threshold in the range 200–300 mg/L and ~200 mg/L (chloride and sodium, respectively) [30]. The addition of potassium to drinking water is generally welcome, as it is an essential element for both humans and plants [30]. The recommended daily requirement of K+ is greater than 3000 mg [30]. Thus, the addition of less than 1.2 mg/L through the dosage of the NF brine (Table 1) is not a health concern. In addition, Table 1 presents the calculated addition of the injected food grade antiscalant, which was lower than 53 g/L for all the considered cases. This figure was calculated based on the assumptions that 3 mg/L of antiscalant are dosed to the feed stream and are totally rejected by the membrane. With respect to boron, the WHO increased the guidelines for B concentration in drinking water from 0.5 to 2.4 mg/L [30]. Therefore, the addition of <0.011 mg/L should have no harmful effect, even in the case that the water is used for the irrigation of sensitive crops. With respect to bromide, its seawater concentration is around 80 mg/L. Considering its rejection is similar to the rejection of Cl, it can be calculated that its maximum addition would be ~0.3 mg/L (assuming 20 mg Mg/L target). The concentration of bromide in natural drinking water can be around 0.5 mg/L and in desalinated water ~0.4 mg/L (prior to NF brine dosage, assuming 99.5% rejection in a typical SWRO step). However, a 1 mg/L concentration in desalinated water is not uncommon [30]. The only health related problem that might rise from the presence of such low bromide concentration in drinking water is the possible formation of bromates upon ozonation (the current WHO guideline is 0.01 mg/L [30]). However, the formation of bromate can be reduced by controlling the disinfection conditions. To conclude, the presence of low bromide concentration should be taken into account when choosing the applied disinfection method [30].

Regarding the addition of Ca(II), it is evident that its addition is minor compared to the background Ca(II) concentration, which is usually on the order of several tens of mg/L. For example, the Israeli minimal Ca(II) concentration requirement is 32 mg/L [31].

The addition of other trace metals as a consequence of dosing NF brine was assumed to be negligible, based on the following calculation: although the concentration of strontium in seawater is relatively high (~8 mg/L), its measured concentrations in the brines were 23.6, 23.26 and 24.76 mg/L at 10, 18 and 28 bar, respectively. As a result, even for the highest brine dosage scenario (i.e., 20 mg/L Mg(II) addition) the strontium addition is negligible (Table 1). Thus, it can be safely concluded that the addition of other trace metals is also negligible.

Table Table 1. The addition of ions (Cl, Na+, K+, Ca2+, Sr2+ and B) and antiscalant agent to the desalinated water in the nine examined scenarios and the addition of Cl for the alternative of MgCl2 dosage.

Click here to display table

Table 1. The addition of ions (Cl, Na+, K+, Ca2+, Sr2+ and B) and antiscalant agent to the desalinated water in the nine examined scenarios and the addition of Cl for the alternative of MgCl2 dosage.
Mg2+ additionApplied pressurevia MgCl2 dosage
mg/L10 bar18 bar28 bar
Chloride ion addition (mg/L); WHO taste threshold: 200–300 mg/L [30]
Sodium ion addition (mg/L); WHO taste threshold: 200 mg/L [30]
Potassium ion addition (mg/L);
Calcium ion addition (mg/L)
Strontium ion addition (µg/L)
Boron addition (µg/L); WHO health threshold: 2.4 mg/L [30]
Antiscalant addition (µg/L)

3.2. Comparison with Water Qualities Attained in Alternative Mg(II) Addition Processes

To date, only three practical methods are available for enriching soft and desalinated water with magnesium ions: the direct dosage of magnesium-salts (either MgSO4 or MgCl2), as practiced, for example, in Cyprus [32] and England; dolomite (CaMg(CO3)2) dissolution followed by calcite dissolution [24]; and the exchange of calcium ions with magnesium ions by means of an ion-exchanger [22]. Considering these methods solely from the water quality point of view, the following conclusions can be drawn:

  • Direct dosage can bring the concentration of Mg(II) to any required value. However, this results in a counter-ion addition ratio (relative to Mg(II) ion addition) of 1:1 (Cl(−I) or SO4(−II) to Mg(II), in equivalent units). Thus, the dosage of MgSO4 can be regarded as favorable. The addition of MgCl2 is only slightly superior over the suggested method, in case the recovery ratio is below 90%. In case of a 95% recovery ratio, the addition of Cl(−I) is smaller in the suggested process. In any event, the addition of Cl(−I) is small, relative to chloride concentrations in natural fresh water sources.

  • Dissolution of dolomite is very limited from the resultant water quality aspect [24], since its dissolution kinetics is practical only at low pH values, and the addition of magnesium is accompanied with calcium addition (at ~1 : 1 ratio). Thus, the addition of 20 mg Mg/L is impossible in the case that the water should also comply with other water quality standards, such as a minimum alkalinity threshold of 80 mg/L as CaCO3 and a dissolved calcium maximum threshold of 120 mg/L as CaCO3 [31].

  • The enrichment of water with Mg(II) originating from seawater by means of an ion-exchanger is a relatively flexible method [22,23,25]; however, since in this method, magnesium is exchanged with calcium, the product water quality is also somewhat limited. For example, achieving high Mg(II) concentrations (e.g., 20 mg/L) will most likely be coupled with high calcium concentrations.

3.3. Assessment of Process Cost

From the water quality point of view, it is beneficial to operate the NF process at high pressures (i.e., 28 bars). Moreover, at low pressures, permeate and brine fluxes are reduced, and Mg(II) rejections deteriorate; therefore, a larger NF plant will be required, resulting in increased capital costs. Capital costs are a significant cost component in the suggested process (Table 2). On the other hand, the operation of the plant at low pressures results in lower operational costs. Thus, in order to decide upon the most cost-effective pressure, the optimization of the cost assessment should be conducted. Since this was out of the scope of the current work, the cost assessment is given here only for operation at the two higher pressures (i.e., 18 and 28 bar), while the cost of operating at 10 bar is not shown, since from the water quality aspect, there was no incentive to decreasing the pressure to this value. Moreover, the permeate flux attained at high recovery in the 10 bar operation case was impractically low (<10−6 m∙s−1).

The main component of the cost of the presented process is the energy required in the NF step. However, in the cost assessment, the addition of antiscalant, the UF step (Figure 1) and the capital expenses (CAPEX) were also calculated (Table 2). The following assumptions were used in the cost assessment procedure: electricity price of 0.068 $/(kW∙h); electricity consumption of 40 W∙h per bar per pumping per m3 of feed; antiscalant price $2,000 per ton; antiscalant dosage of 3 mg/L to the feed; 85% recovery. The cost of the UF step was calculated based on the average UF filtrate cost of $0.8 cent per m3 of the filtrate [33]. Capital expenses (CAPEX) were calculated assuming 5% interest and a 20-year serviceable lifetime; a cost of $2,500 m−3 feed h (regardless of the pressure); and a desalination plant capacity of 100 Mm3 per year. Note that in the assessment of the CAPEX, the enlargement of the NF plant (i.e., number of membranes) required due to the reduced flux at the lower pressure scenario was neglected. Instead, Table 2 presents that in the case that the CAPEX of the 18-bar operation is twice the CAPEX of the 28-bar one (values given in brackets in the last two rows), the total costs of the 18-bar scenarios are practically the same as those of the 28-bar scenarios.

The costs of separating 1 kg of Mg(II) by the process in the 18- and 28-bar scenarios are $0.053 and $0.070, respectively, while in the case that the CAPEX of the 18-bar scenarios are doubled; the total cost of 1 kg Mg(II) becomes $0.074. Note that the figures in Table 2 are almost proportional to the mass of Mg(II) added to the desalinated water, for a given pressure. Nevertheless, there are small differences between the calculated costs, but since these differences are of the order of ~10−4 cents, they are not noticeable in the Table.

As mentioned before, the energy required for the NF stage is the main cost component, comprising 50.7% and 61.5% of the overall cost in the 18-bar and 28-bar scenarios, respectively. The second main component is the CAPEX, which constitutes 39.2% and 30.6% of the overall cost, in the 18- and 28-bar cases, respectively.

Table Table 2. Estimation of the operational cost components and capital costs (cents per m3 of desalinated water) associated with the presented process, for six different case studies.

Click here to display table

Table 2. Estimation of the operational cost components and capital costs (cents per m3 of desalinated water) associated with the presented process, for six different case studies.
Pressure18 bar28 bar
Mg(II) addition (mg/L)5102051020
Antiscalant2.2 × 10−34.5 × 10−39.0 × 10−32.3 × 10−34.6 × 10−39.3 × 10−3
NF energy0.0130.0270.0540.0220.0430.086
UF energy4.5 × 10−48.9 × 10−41.8 × 10−34.6 × 10−49.3 × 10−41.9 × 10−3
Total OPEX0.0160.0320.0640.0240.0490.098
CAPEX a0.010
Total cost b0.026

Notes: a values in brackets represent the elevated CAPEX due to the required enlargement of the NF plant in the low pressure (i.e., low flux) scenarios; b values in brackets represent the elevated total costs due to the doubled CAPEX in the low pressure scenarios.

The cost of adding Mg(II) to desalinated water by means of dosing NF brine is approximately one order of magnitude lower than any other available Mg(II) enrichment method. However, it should be recognized that the water quality attained in each process is different (see Section 3.2); therefore, straightforward comparison of the cost does not reveal the complete picture. The prices of the Mg salts, MgCl2 and MgSO4∙7H2O, are ~$300 and ~$275 per ton chemical, respectively [18]. Thus, enriching the water with 10 mg Mg/L, through direct dosage of MgCl2 or MgSO4∙7H2O, will cost 1.18 and 2.06 cents per m3 desalinated water, respectively. The costs associated with the other two alternatives, i.e., the dolomite-calcite dissolution process and the ion exchange dissolution process, could not be easily distinguished from the cost of the overall post-treatment processes; thus, the following figures are merely an assessment of the overall cost of adding 12.15 mg Mg/L in the dolomite and the ion exchange processes: 0.53 and 0.51 cents per m3 of product water, respectively [18], i.e., one order of magnitude higher than the addition of 10 mg Mg/L by the suggested process.

4. Conclusions

The enhancement of a method for enriching desalinated and soft water with Mg(II) ions is presented. The method is based on passing seawater through an NF membrane (DS DL5) and the dosage of the Mg(II)-rich brine in the desalinated water.

The new results show that elevating the pressure from 10 to 18 bar significantly affected the Mg(II) rejection values. However, further elevation of the pressure to 28 bar improved the rejection values only slightly. The NF brine was characterized by high Mg(II) concentrations of 7.707, 7.829 and 8.520 g/L applying 85% recovery at 10, 18 and 28 bar, respectively. The Mg(II):Na(I) concentration ratios were significantly reduced when the recovery ratios were elevated, while they were hardly affected by the applied pressure. Therefore, in areas in which stringent upper thresholds for Na(I) and Cl(−I) are forced, the brine generated at higher recovery ratios is considered more adequate for enriching soft waters with Mg(II).

The cost of the process was found to be approximately one order of magnitude lower than the cost of replenishing Mg(II) by alternative methods.


This project was funded by the Israel Science Foundation (#504/10) and the Joint German-Israeli Water Technology Research Program (BMBF/MOST) (research #2018807).

Author Contributions

The three authors contributed evenly to the execution of the experiments and the writing of this paper.

Conflicts of Interest

The authors declare no conflict of interest.


  1. Calcium and Magnesium in Drinking Water: Public Health Significance, 1st ed.; Cotruvo, J., Bartram, J., Eds.; World Health Organization Press: Geneva, Switzerland, 2009. Chapters 5–10.
  2. Rosanoff, A.; Weaver, C.M.; Rude, R.K. Suboptimal Magnesium Status in the United States: Are the Health Consequences Underestimated? Nutr. Rev. 2012, 70, 153–164. [Google Scholar] [CrossRef]
  3. Sinclair, M.; Hayes, P. Desalination Decision for Israel. Health Stream, 2011, 61, pp. 4–6. Available online: (accessed on 24 April 2014). [Google Scholar]
  4. Chiu, H.; Tsai, S.; Wu, T.; Yang, C. Effect Modification of the Association between Trihalomethanes and Pancreatic Cancer by Drinking Water Hardness: Evidence from an Ecological Study. Environ. Res. 2010, 110, 513–518. [Google Scholar] [CrossRef]
  5. Kuo, H.; Peng, C.; Feng, A.; Wu, T.; Yang, C. Magnesium in Drinking Water Modifies the Association between Trihalomethanes and the Risk of Death from Colon Cancer. J. Toxicol. Env. Health Part A Curr. Issues 2011, 74, 392–403. [Google Scholar] [CrossRef]
  6. Liao, Y.; Chen, P.; Chiu, H.; Yang, C. Magnesium in Drinking Water Modifies the Association between Nitrate Ingestion and Risk of Death from Esophageal Cancer. J. Toxicol. Env. Health Part A Curr. Issues 2013, 76, 192–200. [Google Scholar]
  7. Chiu, H.; Kuo, C.; Tsai, S.; Chen, C.; Wu, D.; Wu, T.; Yang, C. Effect Modification by Drinking Water Hardness of the Association between Nitrate Levels and Gastric Cancer: Evidence from an Ecological Study. J. Toxicol. Env. Health Part A Curr. Issues 2012, 75, 684–693. [Google Scholar] [CrossRef]
  8. Cheng, M.; Chiu, H.; Tsai, S.; Chen, C.; Yang, C. Calcium and Magnesium in Drinking-Water and Risk of Death from Lung Cancer in Women. Magnes. Res. 2012, 25, 112–119. [Google Scholar]
  9. Dahl, C.; Søgaard, A.J.; Tell, G.S.; Flaten, T.P.; Hongve, D.; Omsland, T.K.; Holvik, K.; Meyer, H.E.; Aamodt, G. Nationwide Data on Municipal Drinking Water and Hip Fracture: Could Calcium and Magnesium be Protective? A NOREPOS Study. Bone 2013, 57, 84–91. [Google Scholar] [CrossRef]
  10. Rasic-Milutinovic, Z.; Perunicic-Pekovic, G.; Jovanovic, D.; Gluvic, Z.; Cankovic-Kadijevic, M. Association of Blood Pressure and Metabolic Syndrome Components with Magnesium Levels in Drinking Water in some Serbian Municipalities. J. Water Health 2012, 10, 161–169. [Google Scholar] [CrossRef]
  11. Howarth, M.; Riva, A.; Marks, P.; Williams, R. Association of Water Softness and Heavy Alcohol Consumption with Higher Hospital Admission Rates for Alcoholic Liver Disease. Alcohol Alcohol. 2012, 47, 688–696. [Google Scholar] [CrossRef]
  12. Luo, J.; Zhao, Q.; Zhang, L.; Qiu, Z.; Liu, L.; Chen, J.; Zeng, H.; Huang, Y.; Tan, Y.; Yang, L.; et al. The Consumption of Low-Mineral Bottled Water Increases the Risk of Cardiovascular Disease: An Experimental Study of Rabbits and Young Men. Int. J. Cardiol. 2013, 168, 4454–4456. [Google Scholar] [CrossRef]
  13. Spungen, J.H.; Goldsmith, R.; Stahl, Z.; Reifen, R. Desalination of Water: Nutritional Considerations. Isr. Med. Assoc. J. 2013, 15, 230–234. [Google Scholar]
  14. Ben-Gal, A.; Yermiyahu, U.; Cohen, S. Fertilization and Blending Alternatives for Irrigation with Desalinated Water. J. Environ. Qual. 2009, 38, 529–536. [Google Scholar] [CrossRef]
  15. Yermiyahu, U.; Tal, A.; Ben-Gal, A.; Bar-Tal, A.; Tarchitzky, J.; Lahav, O. Environmental Science—Rethinking Desalinated Water Quality and Agriculture. Science 2007, 318, 920–921. [Google Scholar] [CrossRef]
  16. Rosanoff, A. Changing Crop Magnesium Concentrations: Impact on Human Health. Plant Soil 2013, 368, 139–153. [Google Scholar] [CrossRef]
  17. Lahav, O.; Kochva, M.; Tarchitzky, J. Potential Drawbacks Associated with Agricultural Irrigation with Treated Wastewaters from Desalinated Water Origin and Possible Remedies. Water Sci. Technol. 2010, 61, 2451–2460. [Google Scholar] [CrossRef]
  18. Telzhensky, M.; Birnhack, L.; Lehmann, O.; Windler, E.; Lahav, O. Selective Separation of Seawater Mg2+ Ions for use in Downstream Water Treatment Processes. Chem. Eng. J. 2011, 175, 136–143. [Google Scholar] [CrossRef]
  19. Arkhangelsky, E.; Gitis, V. Effect of Transmembrane Pressure on Rejection of Viruses by Ultrafiltration Membranes. Sep. Purif. Technol. 2008, 62, 619–628. [Google Scholar] [CrossRef]
  20. Genesys International. Available online: http://www.Genesysro.Com/Index.Php (accessed on 24 April 2014).
  21. Lahav, O.; Telzhensky, M.; Zewuhn, A.; Gendel, Y.; Gerth, J.; Calmano, W.; Birnhack, L. Struvite Recovery from Municipal-Wastewater Sludge Centrifuge Supernatant using Seawater NF Concentrate as a Cheap mg(II) Source. Sep. Purif. Technol. 2013, 108, 103–110. [Google Scholar] [CrossRef]
  22. Birnhack, L.; Lahav, O. A New Post-Treatment Process for Attaining Ca2+, Mg2+SO42− and Alkalinity Criteria in Desalinated Water. Water Res. 2007, 41, 3989–3997. [Google Scholar] [CrossRef]
  23. Birnhack, L.; Shlesinger, N.; Lahav, O. A Cost Effective Method for Improving the Quality of Inland Desalinated Brackish Water Destined for Agricultural Irrigation. Desalination 2010, 262, 152–160. [Google Scholar] [CrossRef]
  24. Birnhack, L.; Fridman, N.; Lahav, O. Potential Applications of Quarry Dolomite for Post Treatment of Desalinated Water. Desalination Water Treat. 2009, 1, 58–67. [Google Scholar] [CrossRef]
  25. Birnhack, L.; Oren, S.; Lehmann, O.; Lahav, O. Development of an Additional Step to Current CO2-Based CaCO3(s) Dissolution Post-Treatment Processes for Cost-Effective Mg2+ Supply to Desalinated Water. Chem. Eng. J. 2010, 160, 48–56. [Google Scholar] [CrossRef]
  26. Clesceri, L.S. Standard Methods for the Examination of Water and Wastewater, 20th ed.; Clesceri, L.S., Eaton, A.D., Greenberg, A.E., Eds.; American Public Health Association: Washington, DC, USA, 1998; p. 874. [Google Scholar]
  27. Vanysek, P. Ionic conductivity and diffusion at infinite dilution. In CRC Handbook of Chemistry and Physics, 94th ed.; Haynes, W.M., Ed.; CRC Press/Taylor and Francis: Boca Raton, FL, USA, 2013; pp. 5–77. [Google Scholar]
  28. Thames Gateway Water Treatment Works—An Engineering Solution. Available online: (accessed on 24 April 2014).
  29. Acciona-Aqua. Available online: (accessed on 24 April 2014).
  30. Guidelines for Drinking Water-Quality, 4th ed.; Sheffer, M., Ed.; World Health Organization (WHO): Geneva, Switzerland, 2011; p. 564.
  31. Lahav, O.; Birnhack, L. Quality Criteria for Desalinated Water Following Post-Treatment. Desalination 2007, 207, 286–303. [Google Scholar] [CrossRef]
  32. Marangou, V.; Savvides, K. First Desalination Plant in Cyprus-Product Water Aggresivity and Corrosion Control. Desalination 2001, 138, 251–258. [Google Scholar] [CrossRef]
  33. Bu-Rashid, K.A.; Czolkoss, W. Pilot Tests of Multibore UF Membrane at Addur SWRO Desalination Plant, Bahrain. Desalination 2007, 203, 229–242. [Google Scholar] [CrossRef]
Water EISSN 2073-4441 Published by MDPI AG, Basel, Switzerland RSS E-Mail Table of Contents Alert