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Article

Seawater Mixed with One Part Alkali Activated Material: An Environmental and Cost Evaluation

by
Xiaoyu Li
1,2,
Huiyang Liu
1,2,
Jinxin Xing
1,2,
Min Gan
1,2,
Zhiyun Ji
1,2,
Xiaohui Fan
1,2 and
Zengqing Sun
1,2,*
1
School of Minerals Processing & Bioengineering, Central South University, Changsha 410083, China
2
Engineering Research Centre of Ministry of Education for Carbon Emission Reduction in Metal Resource Exploitation and Utilization, Changsha 410083, China
*
Author to whom correspondence should be addressed.
Materials 2024, 17(16), 4113; https://doi.org/10.3390/ma17164113
Submission received: 22 July 2024 / Revised: 9 August 2024 / Accepted: 10 August 2024 / Published: 20 August 2024
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Abstract

:
Concrete production is associated with extensive energy consumption and significant CO2 emissions. In addition, tremendous amounts of freshwater are used as a mixing agent. Urgency is increasing to develop sustainable cementitious materials and promote freshwater-saving strategies. An environmentally friendly alternative binder, seawater mixed with one part alkali activated material, is studied. In this work, a cradle-to-gate life cycle assessment was applied to study the equivalent CO2 emission and cost properties of the clinker-free binder. The seawater mixed mortar possesses comparable mechanical properties to Portland cement, with 3 d flexural and compressive strengths of 5.3 MPa and 25.2 MPa. In addition, the mortar developed in this work is of similar cost as commercial cement, but reduces CO2 emissions by 44.8%.

1. Introduction

Cement concrete is the second most used commodity and the most used construction material in the world [1]. Meanwhile, the concrete industry is suffering from increasing environmental and ecological burdens. For example, 8% of worldwide CO2 emissions are caused by the production of cement, which is the binding phase that provides strength to concrete [2]. Urgency is increasing to reduce the CO2 emissions of cement or develop alternative construction materials. Practices have been made in utilizing industrial by-products (fly ash (FA), ground granulated blast furnace slag (GGBS), silica fume (SF), etc.) as supplementary cementitious materials (SCMs). McLellan et al. [3] stated that a reduction in CO2 emissions from 1 t CO2/t to 760–860 kg CO2/t can be achieved by blending 15–30% SCMs. Limestone blended calcined clay cement (LC3) is another trend [4,5]. Low-grade clays are highly efficiently used in this process without capital modification to the existing cement plants. In addition, the LC3 can reduce CO2 emissions by up to 30% compared with ordinary Portland cement (OPC) [6].
Another choice is developing clinker-free binders, with alkali-activated materials (AAMs) as a representative. The most used solid materials for AAM production are FA, GGBS, metakaolin (MK), etc. and sodium hydroxide and sodium silicate are the most frequently used activators [2,7]. As documented, this history starts from the 1900s, when Kühl patented findings based on a mixture of alkaline components with GGBS. In the 1940s, Purdon conducted detailed investigation and commercialized the products in Belgium. Glukhovsky, former Soviet Union scientist, developed binders based on the alkali activation of low-calcium aluminosilicates [7]. The obtained binders were successfully used in infrastructure and domestic construction. In the 1970s, French scientist Joseph Davidovits patented several alkali-activated aluminosilicates with the terminology ‘Geopolymer’ [8]. Geopolymers are normally regarded as a subclass of AAMs, which refers to the low-calcium or calcium-free group [7]. Extensive work has been conducted on the reaction and properties of geopolymer. Studies have shown that AAMs possess excellent engineering properties, such as rapid hardening, high early and long-term strength, chemical resistance, dimensional stability in service, strong adhesion, etc. [9]. Moreover, AAM production is characterized as low CO2 emission because it does away with the high temperature calcination process [2,10]. A tremendous amount of CO2 is released during the calcination of carbonate feedstocks together with the grinding process. The equivalent CO2 emission is approximately 0.85 t for the production of 1 ton of cement. In comparison, AAMs are estimated to save up to 97% of CO2 emissions [2].
Benefiting from their superior properties, AAMs possess the possibility of being used in immobilizing hazardous/nuclear wastes and high-volume infrastructure construction. To date, success has been achieved in immobilizing artificial wastes comprising lead (Pb), zinc (Zn) and chromium (Cr(VI)) [11,12]. Chemical entrapment is supposed as one of the solidifying mechanisms. Studies have demonstrated that arsenic (As) is more likely to be associated with iron-rich areas from FA [13]. In addition, the small radius of copper (Cu) ions decreases the tendency of being trapped in nano-pore networks. Blackford et al. [14] reported that cesium (Cs) can be chemically bound in the geopolymer structure as a charge-balancing cation. Hence, better immobilization effects than OPC matrices have been found. Similar results were reported by Li et al. [15]. Apart from these laboratory-level investigations, actual nuclear waste immobilization using geopolymers has been accepted by the Slovak Nuclear Authority [16]. In addition to the aforementioned engineering practices of AAMs, a four-story building was constructed using geopolymer concrete floors in Queensland in 2013. Additionally, one year later, the Brisbane West Wellcamp Airport (BWWA) was opened for business, for which approximately 40,000 m3 of geopolymer concrete was used. All these demonstrate that AAMs, including geopolymers, are promising alternative binders.
Freshwater consumption is another problem associated with concrete production. Water withdrawal and consumption occur throughout every major production phase of concrete, including the manufacture of cement and additives, the quarrying and crushing of aggregates, mixing and batching, etc. [1]. According to Miller et al. [1], approximately 1.66 × 1010 m3 of water is consumed for concrete production every year. Water scarcity is one of the greatest risks all over the world. It is predicted that 75% of water demand from concrete production in 2050 will take place in regions that are most likely to suffer water shortage. Using seawater as a replacement for concrete mixing has been investigated. Although the high chloride content may enhance the corrosion potential of steel reinforcing, positive findings have been obtained from seawater-mixed concrete structures [17]. In addition, steel corrosion can be avoided when using non-corrosive fiber-reinforced polymer (FRP). The FRP-reinforced concrete is reported to possess properties of excellent durability under seawater exposure and significant long-term cost savings [18,19,20]. In our previous work, the micro- and macro-properties of seawater mixed with one part AAM were studied [21]. The obtained materials achieved excellent mechanical properties and only very slight corrosion traces were found on the surface of steel reinforcement after one year. Similarly, AAMs containing seawater and/or sea sand were produced by Yang [22] and Jun [23], respectively. The incorporation of seawater led to the intercalation of chloride ions with layered double hydroxides and the development of early strength [23]. A dense structure was detected with reduced dimensions and a reduced number of micro-cracks in the interfacial transition zone. All these increase confidence in the production of seawater-mixed AAM concrete.
The application of a new material is not only determined by its engineering properties, but also the cost and environment credits. As part of systematic study, this work is designed to characterize the environment and cost properties of seawater mixed with one part AAM mortar. An analysis was conducted using a cradle-to-gate (from resource extraction to products) life cycle assessment (LCA). Comparison with OPC mortar of the same compressive strength grade is included to evaluate whether the AAM possesses environmental and commercial advantages.

2. Materials and Methods

2.1. Materials

The solid precursors used in this work are FA and GGBS; both are commercially available. Portland cement, CEM I 42.5 N, was selected as a reference. The chemical compositions of FA and GGBS were characterized using X-ray fluorescence (XRF). As shown in Table 1, the FA is mainly composed of SiO2 and Al2O3, with the CaO content being 4.85%. The densities of FA and GGBS are 2.03 g/cm3 and 2.94 g/cm3, respectively. The surface area was detected using a Blaine air permeability test, which is 3250 cm2/g for fly ash and 4127 cm2/g for GGBS.
Though not shown here, the mineralogical compositions of source materials were documented using powder X-ray diffraction (XRD) and the results were quantitatively analyzed. GGBS and FA comprise mainly amorphous phases, with the amounts being 73.0% and 94.9%, respectively.
Alkaline activators for AAM synthesis are sodium hydroxide, sodium silicate and sodium carbonate, all solid phase. Sodium silicate possesses an original SiO2/Na2O molar ratio of 3.5. The mix proportion of each component is listed in Table 2. The mixture was determined based on extensive pre-tests. The seawater used was from Zhoushan, East China Sea. The content of major elements is shown in Table 3. A water-to-binder ratio of 0.45 was applied for the AAM and OPC mixture.

2.2. Sample Preparation

Mortar samples were prepared using AAM and OPC, respectively. For the AAM, solid precursors and activators were weighted and mixed in a planet mixer for 3 min. The seawater was then added into the mixer and mixed for 2 min. Standard sand was adopted for mortar production. The mass ratio of sand-to-binder is 3 for all mixtures. After adding sand, another 3 min of mixing was conducted to obtain homogeneous mortar. The fresh mortar was then casted into 40 × 40 × 160 mm3 molds and vibrated for 2 min to remove air bubbles. The molds together with casted mortar were covered with a glass plate and stored in a curing box. The temperature and relative humidity (RH) inside the curing box were 20 °C and 100%. Samples were demolded after 24 h, wrapped with PE foil and then further cured at 20 °C, 65% RH until measurement.

2.3. Strength Measurement

The compressive and flexural strengths of seawater mixed with one part AAM and reference OPC mortars were documented. Strength measurement was conducted after 3, 7, 14 and 28 days of curing. The tested sample was first visually checked to make sure it was unbroken. The flexural strength measurement was performed using the three-point loading method, with the distance between two supports being 100 mm. A load was applied at the mid span at a rate of 0.05 kN/s. For the flexural strength, three samples were tested. The resultant six halves were used for the compressive strength measurement. The force rate for compressive strength measurement was 2.4 kN/s.

2.4. XRD Measurement and Data Analysis

As aforementioned, the mineral composition of source materials was measured using the XRD method. The reaction products of seawater mixed with one part AAM were also characterized. AAM paste was produced and cured under the same procedure as mortar production. After 28 d, the paste was crushed to less than 1 mm. The obtained particles were immersed in isopropanol for 15 min. The mixture was then filtered, rinsed with diethyl ether, dried at 40 °C, and ground to <63 μm. More details can be found in [24,25].
The powder XRD measurement was conducted using an X’Pert Pro Diffractometer (Panalytical, Almelo, The Netherlands). Theta-theta geometry was adopted over the 2θ range of 5–60°. Tube operating conditions of 40 kV and 40 mA were applied to generate the CuKα X-rays. The measured data were analyzed using the software HighScore Plus. Details about the data analysis are reported in our previous work [24,25].

2.5. Equivalent CO2 Emission

LCA was applied in this work. The main steps are fully described as follows.

2.5.1. Goal and Scope

The investigation objective and designed implementation are covered in the ‘Goal and scope’ step, which describes the evaluated part, accuracy degree and functional unit. In this work, a cradle-to-gate study of seawater mixed with one part AAM was conducted. Apart from evaluating the potential environmental impacts of seawater mixed with one part AAM, a comprehensive comparison with OPC mortar of the same compressive strength grade was also conducted to quantify the pros and cons of AAM produced in this work.
Figure 1 depicts the system boundary of this study, which includes all the associated environmental footprints during the production of solid precursors and activators, production and transport of AAM mortars, etc. The physicochemical properties of solid precursors and mix design significantly influence the reaction kinetics and compressive strength development of the resultant product [26]. In many cases, elevated-temperature curing is necessary. Benefiting from a well-designed formula, excellent engineering properties can be achieved by AAM produced in this work even under ambient curing procedures. Therefore, thermal curing is not included in this work.
The functional unit of this work is 1 m3 AAM or OPC mortar, in which the solid binder, water and sand are included. As will be shown below, the excellent mechanical properties of AAM synthesized in this work make it suitable for multiple engineering applications, such as beams, columns, bridges, houses, etc. The work conducted here can not only be extended to the LCA of specific structural products but also to be compared with studies of other construction materials. In addition, the commercially available characteristics of all source materials used in this work make it easy adapt from a laboratory-scale study to industrial scale.

2.5.2. Inventory Analysis

An inventory analysis shows the inputs and outputs of a studied product or system, which are essential for the following impact assessment and interpretation phase [2,7,10]. The primary input data were collected from the Ecoinvent database and the literature [27,28,29,30]. These data have been widely accepted by various researchers and institutions. It is common sense that both GGBS and FA are industrial by-products rather than wastes and both are extensively used as SCMs in concrete production. For example, the yearly production of GGBS is fully used in several European countries. Thus, the allocation of each environmental impact parameter on both materials can be performed based on mass or market price. Studies were conducted to compare the influence of allocation process [27,29]. Results show that no specific allocation method is fully adequate. Generally, allocation based on economic values is more widely used since it represents the reality of industrial processes better. This was also the adopted allocation method of this work.
The alkaline activators used in this work, including sodium hydroxide, sodium silicate and sodium carbonate, were in solid form. The sodium hydroxide was electrolytically produced from chloride salts. Rock salt and sand are the main raw materials for the production of sodium silicate. Sodium carbonate is produced by the Solvay process from sodium chloride and limestone. The inventory data for alkaline activators have been well estimated [31,32,33]. In a conventional AAM production, alkali solutions are used. The alkaline solution is commercially purchased or produced by dissolving solid activator in water. In comparison, the one-part synthesis can avoid the impracticalities of transporting and dealing with large amounts of corrosive alkaline solutions. The contribution introduced by water is normally excluded due to its extremely low environmental footprint. Meanwhile, the effect of water was taken into consideration in this work for a more decent analysis. In the construction materials industry, the environmental inventory of Portland cement and standard sand have been extensively studied based on surveys and statistics [27,28,29,30,31,32].

2.5.3. Calculation and Interpretation

Based on the accumulated inventory data, the equivalent CO2 emission was calculated using the software Open LCA 2.0. The significant impacts and significant unit processes in the system were identified in interpretation. Conclusions based on the comparison of seawater mixed with one part AAM and Portland cement are given. The benefits of using seawater for the production of AAM with excellent corrosion resistance are included.

2.6. Cost Evaluation

The cradle-to-gate cost of seawater mixed with one part AAM was evaluated in a similar way as the equivalent CO2 emissions, except for the inventory data. The inventories of cost were based on a literature review of published values and preliminary marketing research [3]. Accumulated data are listed in Table 4.
The cost of a product to the end users is significantly influenced by the distance and mode of transport. Cement, fly ash, slag, chemicals, etc., are localized commodities due to the wide distribution of power plants, steelworks and chemical plants in China. Long-distance transport is rare. In addition, when focusing on a specific city, these factories are normally located in the same industrial park. All these indicate that the corresponding transport mode and distance of cement and AAM are similar. The cost of transport is then not considered in this work, and the most attention is paid to comparing the average cost of all ingredients for AAM and OPC mortars.

3. Results and Discussion

3.1. Flexural and Compressive Strengths

Mechanical properties are among the primary factors for the design of cementitious structures. Figure 2 shows the flexural and compressive strength development of seawater mixed with one part AAM, as well as the reference OPC. The 28 d flexural and compressive strengths of AAM and OPC are of the same strength grade, demonstrating the selection of OPC is proper. The flexural and compressive strengths satisfy most structure application scenarios. Slightly higher flexural and compressive strengths of AAM than its OPC counterpart can be seen from Figure 1. In addition, the AAM possesses higher early age flexural and compressive strengths property, with the 3 d flexural and compressive strengths being 5.3 MPa and 25.2 MPa, respectively. This can be assigned to the extensive alkali activation process and the fast formation of flexural and compressive strengths giving phases [24,25]. The high early-age flexural and compressive property is essentially for cementitious materials. For example, when used for pavement construction, this contributes to minimizing traffic control and the early opening of traffic.
Numerous studies have been reported the flexural and compressive strengths of AAM with different mix designs [2,10]. The flexural and compressive strengths of AAM produced in this work are better than those in many of the reported studies, suggesting the advantage of proportion. It should also be mentioned that the AAM produced in this work is ambiently cured. This is not only energy saving because no heat treatment is required, but also user friendly, especially for in situ application.

3.2. Reaction Product

The reaction products of AAM were measured by XRD and the results are shown in Figure 3. Compared with the initial pattern of the binder, the reflection peaks of the activator disappeared. When coming into contact with water, the sodium hydroxide hydrolyses promptly and initiates alkaline conditions for the dissolution of sodium silicate. The network breakdown of solid source materials takes place simultaneously. Then the gelation and condensation processes of the dissolved ions are similar to conventional two-part AAMs. The mineral phases contained by solid precursors remain almost unchanged after 28 days, except the anhydrite. The dissolution of anhydrite during the alkali activation process has been reported in our previous studies [24,25].
New reflection peaks can be seen in Figure 3 indicating the formation of crystals. The humps around 25–35° 2θ can be assigned to the calcium (alumino)silicate hydrate type gel (C-A-S-H) [7,10]. The C-A-S-H is the main reaction product and responsible for the engineering properties of AAM. Regarded as aluminum-substituted C-S-H, the substations of aluminum mainly occur in the bridging tetrahedral sites. Puertas et al. [34] conducted experimental and computational studies on C-A-S-H gel; the findings show that it is much more densely packed than C-S-H.
Peaks around 14°, 19°, 24° and 27° 2θ can be assigned to the formation of cancrinite. Cancrinite is a zeolite belonging to the ABC-6 family. According to Oh et al. [35], the basic structure layer of cancrinite consists six member rings of Al- and Si-tetrahedra. The formation of cancrinite has been reported in several studies [24,35].
The reflection peaks of hydrocalumite were detected. Hydrocalumite, with an AFm-like structure, is typical double hydroxides (LDHs) in AAM [27,36]. Due to the substitution of divalent ions by trivalent ones, the LDHs is normally a positively charged layer structure [37]. Additionally, LDHs are capable of interlayer anion exchange. A closer check of the XRD pattern and comparison with the published literature indicates that the hydrocalumite formed in this work is chloride bearing. In the construction industry, ‘Friedel’s salt’ is a term applied to describe chloride-bearing AFm-like phases. Friedel’s salt is important for retaining chloride within a cementitious matrix [38,39]. The detection of chloride-bearing hydrocalumite suggests that the AAM possesses chloride-binding properties, which might be beneficial in protecting steel reinforcement from chloride corrosion.

3.3. Equivalent CO2 Emissions

The equivalent CO2 emissions of seawater mixed with one part AAM mortar are shown in Figure 4, compared with OPC mortar. As discussed above, both samples possess similar mechanical strength, indicating that the comparison of life cycle equivalent CO2 emissions is meaningful. The equivalent CO2 emissions of seawater mixed with one part AAM are 258.9 kg/m3. The main contributors are NaOH, GGBS, FA, sodium silicate and sodium carbonate, which account for 52.2%, 25.6%, 8.0%, 6.1% and 5.9% of total CO2 emissions, respectively. The high CO2 emissions generated from NaOH should be assigned to its production process. NaOH is generally produced by the electrolysis of sodium chloride solution via mercury cells, membrane cells or diaphragm cells. In 2018, sodium hydroxide production in China was over 34 million tons, over 85% of which was produced by the membrane cell technique. Some other obsolete technology is still used in China [31]. A life cycle assessment of NaOH production in China has been conducted by Hong et al. [31]. Electricity efficiency and raw material consumption, accounting for 72% and 19%, are the largest contributors to the overall environmental burdens of NaOH production. Compared with the best available technology in Europe, the NaOH production industry suffers from extensive energy consumption and CO2 emissions, high production costs and unbalanced development between NaOH and chlorine products.
The equivalent CO2 emissions of reference for OPC mortar are 469.3 kg/m3, of which over 90% is caused by the production of cement. It is well known that cement production is associated with high global warming potential. During cement production, raw materials, such as stone and clay, are calcined to generate clinker in a rotary kiln. Clinker is then ground to fine powder and mixed with gypsum. CO2 is released from both fossil fuel combustion (for electricity generation or directly used by cement rotary) and calcium carbonate conversion into oxide form during the calcination process. Though practices have been made in partially replacing clinker by supplementary cementitious materials, the reduction effect on CO2 emissions varies [40].
Comparing with the reference OPC mortar, equivalent CO2 emissions from seawater mixed with one part AAM are reduced by nearly 45%. This once again demonstrates the environmental benefits of AAM. In addition, the equivalent CO2 emissions of AAM synthesized in this work are lower than those of other AAMs reported in [3,41,42]. This is partially because of the well mix design and because no thermal treatment is required in this work.

3.4. Cost Evaluation

As shown in Figure 5, the cost of seawater mixed with one part AAM is almost the same as that of the reference OPC mortar. The cost of OPC mortar is predominantly caused by OPC and sand, with the influence of water being extremely low. Sand makes a similar contribution in the seawater AAM mortar system, which accounts for 47% of the total cost, followed by NaOH, GGBS, sodium silicate, sodium carbonate and FA. The significant influence of sand is assigned to its large consumption amount. Alkali activators, NaOH, sodium silicate and sodium carbonate in total make up 27.5% of the cost.
According to McLellan et al. [3], the cost of AAM is in the range of 7% lower to 39% higher than that of OPC. The calculated results in this work are located in this cost range. It should also be mentioned that the cost is calculated under present pricing structures without taking carbon price into consideration. Nowadays, overall limits and taxes on CO2 emissions from energy-intensive industries (production of iron, aluminum, cement, paper, glass, etc.) have been set. These taxes seem to be enhanced by increasingly stringent environmental regulations [43]. As discussed above, AAM reduces CO2 emissions by 44.8% over OPC. Thus, when taking this into consideration, the cost of AAM mortar is promising and competitive.
Another benefit of the one-part AAM synthesized in this work is its potential freshwater saving characteristic. According to the United Nations World Water Development Report [44], global water demand will continue to rise at a rate of 20–30% above the current water usage level. The main driven force is the rising demand from industrial and domestic sectors. More seriously, more than 2 billion individuals live under high water stress and 4 billion individuals suffer from serious scarcity for at least one month a year. Concrete production is reported to be responsible for around 9% of the worldwide industrial water consumption [1]. In contrast, seawater covers over 70% of the Earth’s surface and is the most abundant aqueous material on the Earth. Considering the negative environmental impacts of current desalination and the scarcity of freshwater [1,45], studies about using seawater for concrete production are increasing. The influences of seawater on properties of concrete have been reported in [46,47]. In our previous work [21], the micro- and macro- properties of AAM mixed using seawater were studied. Our results favor the possibility of using seawater as an alternative mixing water for AAM concrete production.

4. Summary and Conclusions

The equivalent CO2 emissions and cost properties of seawater mixed with one part AAM are studied in this work using a cradle-to-gate life cycle assessment method. The AAM mortar possesses excellent mechanical properties. The 28 d flexural and compressive strengths are 7.5 MPa and 51.1 MPa, respectively. Chloride-bearing reaction product was detected in the seawater mixed with one part AAM, suggesting the AAM can contribute to retaining chloride within the matrix. Moreover, the cost of AAM studied in this work is similar to that of commercial Portland cement but reduces CO2 emissions by 44.8%. These results suggest that seawater mixed with one part AAM is sustainable and promising.
The authors are highly aware that though the environment and cost were evaluated, much work such as making life cycle inventory more readily available, scoping the assessment, updating impact indicators, etc., should be addressed. In addition, the durability of synthesized AAMs cannot be ignored, since weathering and corrosion will take place during service life. Further attention will be continuously paid to these aspects to promote the applicability of AAMs.

Author Contributions

X.L.: ideas, writing—original draft; H.L.: investigation, validation; J.X.: validation; M.G. and Z.J.: resources, writing—review and editing; X.F.: project administration, data curation; Z.S.: project administration, ideas, supervision. All authors have read and agreed to the published version of the manuscript.

Funding

This research received no external funding.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

The original contributions presented in the study are included in the article, further inquiries can be directed to the corresponding author.

Conflicts of Interest

The authors declare no conflicts of interest.

References

  1. Miller, S.A.; Horvath, A.; Monteiro, P.J.M. Impacts of booming concrete production on water resources worldwide. Nat. Sustain. 2018, 1, 69–76. [Google Scholar] [CrossRef]
  2. Provis, J.L.; Bernal, S.A. Geopolymers and related alkali-activated materials. Annu. Rev. Mater. Res. 2014, 44, 299–327. [Google Scholar] [CrossRef]
  3. Mclellan, B.C.; Williams, R.P.; Lay, J.; Riessen, A.V.; Corder, G.D. Costs and carbon emissions for geopolymer pastes in comparison to ordinary portland cement. J. Clean. Prod. 2011, 19, 1080–1090. [Google Scholar] [CrossRef]
  4. Avet, F.; Scrivener, K. Investigation of the calcined kaolinite content on the hydration of limestone calcined clay cement (LC3). Cem. Concr. Res. 2018, 107, 124–135. [Google Scholar] [CrossRef]
  5. Karen, S.; Fernando, M.; Shashank, B.; Soumen, M. Calcined clay limestone cements (LC3). Cem. Concr. Res. 2018, 114, 49–56. [Google Scholar]
  6. Berriel, S.S.; Favier, A.; Domínguez, E.R.; Machado, I.S.; Heierli, U.; Scrivener, K.; Hernández, F.M.; Habert, G. Assessing the environmental and economic potential of limestone calcined clay cement in cuba. J. Clean. Prod. 2016, 124, 361–369. [Google Scholar] [CrossRef]
  7. Provis, J.L.; van Deventer, J.S.J. Alkali-Activated Materials, State-of-the-Art Report; RILEM TC 224-AAM; Springer: Berlin, Germany, 2014. [Google Scholar]
  8. Davidovits, J. Mineral Polymers and Methods of Making Them. U.S. Patent US4349386A, 14 September 1982. [Google Scholar]
  9. Shi, C.; Roy, D.; Krivenko, P. Alkali-Activated Cements and Concretes, 1st ed.; CRC Press: Boca Raton, FL, USA, 2006. [Google Scholar]
  10. Bernal, S.A.; Provis, J.L.; Myers, R.J.; San Nicolas, R.; Van Deventer, J.S.J. Role of carbonates in the chemical evolution of sodium carbonate-activated slag binders. Mater. Struct. 2015, 48, 517–529. [Google Scholar] [CrossRef]
  11. Fernandez-Pereira, C.; Luna, Y.; Querol, X.; Antenucci, D.; Vale, J. Waste stabilization/solidification of an electric arc furnace dust using fly ash-based geopolymers. Fuel 2009, 88, 1185–1193. [Google Scholar] [CrossRef]
  12. Zhang, J.; Provis, J.L.; Feng, D.; Van Deventer, J.S.J. The role of sulfide in the immobilization of Cr(VI) in fly ash geopolymers. Cem. Concr. Res. 2008, 38, 681–688. [Google Scholar] [CrossRef]
  13. Fernández-Jiménez, A.; Palomo, A.; Macphee, D.E.; Lachowski, E.E. Fixing arsenic in alkali-activated cementitious matrices. J. Am. Ceram. Soc. 2005, 88, 1122–1126. [Google Scholar] [CrossRef]
  14. Blackford, M.G.; Hanna, J.V.; Pike, K.J.; Vance, E.R.; Perera, D.S. Transmission electron microscopy and nuclear magnetic resonance studies of geopolymers for radioactive waste immobilization. J. Am. Ceram. Soc. 2007, 90, 1193–1199. [Google Scholar] [CrossRef]
  15. Li, Q.; Sun, Z.; Tao, D.; Xu, Y.; Zhai, J. Immobilization of simulated radionuclide 133cs(+) by fly ash-based geopolymer. J. Hazard. Mater. 2013, 262C, 325–331. [Google Scholar] [CrossRef] [PubMed]
  16. Majersy, D.; Sekely, S.; Breza, M. Verified possibilities of specific and historical waste solidification. In Proceedings of the IAEA RCM on Behaviour of Cementitious Materials in Long Term Storage and Disposal of Radioactive Waste Meeting, Moscow, Russia, 10–14 September 2007. [Google Scholar]
  17. Witze, A. Rare mineral is the key to long-lasting ancient concrete. Nature 2017. [Google Scholar] [CrossRef]
  18. Eamon, C.; Jensen, E.; Grace, N.; Shi, X. Life-Cycle Cost Analysis of Alternative Reinforcement Materials for Bridge Superstructures Considering Cost and Maintenance Uncertainties. J. Mater. Civ. Eng. 2012, 24, 373–380. [Google Scholar] [CrossRef]
  19. El-Hassan, H.; El-Maaddawy, T.; Al-Sallamin, A.; Al-Saidy, A. Performance evaluation and microstructural characterization of gfrp bars in seawater-contaminated concrete. Constr. Build. Mater. 2017, 147, 66–78. [Google Scholar] [CrossRef]
  20. Robert, M.; Benmokrane, B. Combined effects of saline solution and moist concrete on long-term durability of gfrp reinforcing bars. Constr. Build. Mater. 2013, 38, 274–284. [Google Scholar] [CrossRef]
  21. Lv, W.; Sun, Z.; Su, Z. Production of seawater mixed one-part alkali activated material. Cem. Concr. Compos. 2019. under review. [Google Scholar]
  22. Yang, Z.; Zhan, X.; Zhu, H.; Zhang, B.; Feng, P.; Li, H.; Kua, H.W. Performance-based alkali-activated seawater sea-sand concrete: Mixture optimization for mechanical, environmental, and economical objectives. Constr. Build. Mater. 2023, 409, 134156. [Google Scholar] [CrossRef]
  23. Jun, Y.; Han, S.H.; Bae, Y.H.; Kim, J.H. Seawater-mixed alkali-activated materials: A comparative investigation of metal slag suitability. J. Sustain. Cem.-Based Mater. 2023, 12, 907–923. [Google Scholar] [CrossRef]
  24. Sun, Z.; Vollpracht, A. Isothermal calorimetry and in-situ XRD study of the NaOH activated fly ash, metakaolin and slag. Cem. Concr. Res. 2018, 103, 110–122. [Google Scholar] [CrossRef]
  25. Sun, Z.; Vollpracht, A. One year geopolymerisation of sodium silicate activated fly ash and metakaolin geopolymers. Cem. Concr. Compos. 2019, 95, 98–110. [Google Scholar] [CrossRef]
  26. Chen, C.; Habert, G.; Bouzidi, Y.; Jullien, A. Environmental impact of cement production: Detail of the different processes and cement plant variability evaluation. J. Clean. Prod. 2010, 18, 478–485. [Google Scholar] [CrossRef]
  27. Feiz, R.; Ammenberg, J.; Baas, L.; Eklund, M.; Helgstrand, A.; Marshall, R. Improving the CO2 performance of cement, part I: Utilizing life-cycle assessment and key performance indicators to assess development within the cement industry. J. Clean. Prod. 2015, 98, 272–281. [Google Scholar] [CrossRef]
  28. Habert, G. 1–environmental impact of portland cement production. In Eco-Efficient Concrete; Woodhead Publishing: Sawston, UK, 2013; Volume 179, pp. 3–25. [Google Scholar]
  29. Li, C.; Nie, Z.; Cui, S.; Gong, X.; Wang, Z.; Meng, X. The life cycle inventory study of cement manufacture in China. J. Clean. Prod. 2014, 72, 204–211. [Google Scholar] [CrossRef]
  30. Hong, J.; Chen, W.; Wang, Y.; Xu, C.; Xu, X. Life cycle assessment of caustic soda production: A case study in China. J. Clean. Prod. 2014, 66, 113–120. [Google Scholar] [CrossRef]
  31. European Commission. Integrated Pollution Prevention and Control Reference Document on Best Available Techniques for the Manufacture of Large Volume Inorganic Chemicals—Solids and Others Industry; European Commission: Brussels, Belgium, 2007. [Google Scholar]
  32. European Commission. Integrated Pollution Prevention and Control Reference Document on Best Available Techniques Reference Document for the Production of Chlor-Alkali; European Commission: Brussels, Belgium, 2014. [Google Scholar]
  33. Puertas, F.; Palacios, M.; Manzano, H.; Dolado, J.S.; Rico, A.; Rodríguez, J. A model for the C-A-S-H gel formed in alkali-activated slag cements. J. Eur. Ceram. Soc. 2011, 31, 2043–2056. [Google Scholar] [CrossRef]
  34. Oh, J.E.; Monteiro, P.J.M.; Jun, S.S.; Choi, S.; Clark, S.M. The evolution of strength and crystalline phases for alkali-activated ground blast furnace slag and fly ash-based geopolymers. Cem. Concr. Res. 2010, 40, 189–196. [Google Scholar] [CrossRef]
  35. Myers, R.J.; Bernal, S.A.; San Nicolas, R.; Provis, J.L. Generalized structural description of calcium–sodium aluminosilicate hydrate gels: The cross-linked substituted tobermorite model. Langmuir 2013, 29, 5294–5306. [Google Scholar] [CrossRef]
  36. Haha, M.B.; Lothenbach, B.; Saout, G.L.; Winnefeld, F. Influence of slag chemistry on the hydration of alkali-activated blast-furnace slag—Part ii: Effect of Al2O3. Cem. Concr. Res. 2012, 42, 74–83. [Google Scholar] [CrossRef]
  37. Dong, L.; Zhang, H.; Fujita, T.; Ohnishi, S.; Li, H.; Fujii, M.; Dong, H. Environmental and economic gains of industrial symbiosis for Chinese iron/steel industry: Kawasaki’s experience and practice in liuzhou and jinan. J. Clean. Prod. 2013, 59, 226–238. [Google Scholar] [CrossRef]
  38. Ke, X.; Bernal, S.A.; Provis, J.L. Uptake of chloride and carbonate by Mg-Al and Ca-Al layered double hydroxides in simulated pore solutions of alkali-activated slag cement. Cem. Concr. Res. 2017, 100, 1–13. [Google Scholar] [CrossRef]
  39. Lee, Y.; Kim, M.; Chen, Z.; Lee, H.; Lim, S. Chloride-Binding Capacity of Portland Cement Paste Blended with Synthesized CA2 (CaO·2Al2O3). Adv. Mater. Sci. Eng. 2018, 2018, 5418930. [Google Scholar] [CrossRef]
  40. Heede, P.V.D.; Belie, N.D. Environmental impact and life cycle assessment (lca) of traditional and ‘green’ concretes: Literature review and theoretical calculations. Cem. Concr. Compos. 2012, 34, 431–442. [Google Scholar] [CrossRef]
  41. Turner, L.K.; Collins, F.G. Carbon dioxide equivalent (CO2-e) emissions: A comparison between geopolymer and opc cement concrete. Constr. Build. Mater. 2013, 43, 125–130. [Google Scholar] [CrossRef]
  42. Teh, S.H.; Wiedmann, T.; Castel, A.; De Burgh, J. Hybrid life cycle assessment of greenhouse gas emissions from cement, concrete and geopolymer concrete in Australia. J. Clean. Prod. 2017, 152, 312–320. [Google Scholar] [CrossRef]
  43. Lin, B.; Li, X. The effect of carbon tax on per capita CO2 emissions. Energy Policy 2011, 39, 5137–5146. [Google Scholar] [CrossRef]
  44. United Nations. World Water Development Report 2019. Available online: https://www.unwater.org/publications/world-water-development-report-2019/ (accessed on 7 December 2023).
  45. Mekonnen, M.M.; Hoekstra, A.Y. Four billion people facing severe water scarcity. Sci. Adv. 2016, 2, 1500323. [Google Scholar] [CrossRef]
  46. Xiao, J.; Qiang, C.; Nanni, A.; Zhang, K. Use of sea-sand and seawater in concrete construction: Current status and future opportunities. Constr. Build. Mater. 2017, 155, 1101–1111. [Google Scholar] [CrossRef]
  47. Younis, A.; Ebead, U.; Suraneni, P.; Nanni, A. Fresh and hardened properties of seawater-mixed concrete. Constr. Build. Mater. 2018, 190, 276–286. [Google Scholar] [CrossRef]
Materials 17 04113 g001
Figure 1. Schematic boundary of this work.
Figure 1. Schematic boundary of this work.
Materials 17 04113 g001
Materials 17 04113 g002
Figure 2. Flexural and compressive strengths of seawater mixed with one part AAM mortar.
Figure 2. Flexural and compressive strengths of seawater mixed with one part AAM mortar.
Materials 17 04113 g002
Materials 17 04113 g003
Figure 3. XRD pattern of seawater mixed with one part AAM after 28 d.
Figure 3. XRD pattern of seawater mixed with one part AAM after 28 d.
Materials 17 04113 g003
Materials 17 04113 g004
Figure 4. Equivalent CO2 emissions of seawater mixed with one part AAM in comparison with OPC mortar.
Figure 4. Equivalent CO2 emissions of seawater mixed with one part AAM in comparison with OPC mortar.
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Materials 17 04113 g005
Figure 5. Cost evaluation of seawater mixed with one part AAM and OPC mortar.
Figure 5. Cost evaluation of seawater mixed with one part AAM and OPC mortar.
Materials 17 04113 g005
Table 1. Chemical composition of FA and GGBS.
Table 1. Chemical composition of FA and GGBS.
Parameter/CompoundFAGGBS
wt.%wt.%
Al2O321.6710.53
SiO252.7240.28
CaO4.8534.54
Fe2O39.550.39
MgO1.898.63
P2O50.480.15
TiO20.900.40
MnO0.081.14
Na2O1.110.59
K2O2.271.62
Table 2. Calculated chemical composition of the seawater mixed with one part AAM paste.
Table 2. Calculated chemical composition of the seawater mixed with one part AAM paste.
CompoundAl2O3SiO2CaOFe2O3MgONa2OK2O
Content (wt.%)21.6752.724.859.551.891.112.27
Table 3. Composition of the seawater used in this work, given in g/L.
Table 3. Composition of the seawater used in this work, given in g/L.
Na+K+Ca2+Mg2+Cl−SO42−Br−HCO3−
Seawater11.870.380.391.3320.952.970.110.14
Table 4. Market price of raw materials used in this work.
Table 4. Market price of raw materials used in this work.
MaterialMarket Price (USD/t)
FA7.3–21.8
GGBS30.2–35.1
NaOH421.4–501.7
Sodium silicate316.1–372.7
Sodium carbonate206.3–247.1
OPC56.4–71.6
Sand14.3–22.9
Water0.52–1.01
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MDPI and ACS Style

Li, X.; Liu, H.; Xing, J.; Gan, M.; Ji, Z.; Fan, X.; Sun, Z. Seawater Mixed with One Part Alkali Activated Material: An Environmental and Cost Evaluation. Materials 2024, 17, 4113. https://doi.org/10.3390/ma17164113

AMA Style

Li X, Liu H, Xing J, Gan M, Ji Z, Fan X, Sun Z. Seawater Mixed with One Part Alkali Activated Material: An Environmental and Cost Evaluation. Materials. 2024; 17(16):4113. https://doi.org/10.3390/ma17164113

Chicago/Turabian Style

Li, Xiaoyu, Huiyang Liu, Jinxin Xing, Min Gan, Zhiyun Ji, Xiaohui Fan, and Zengqing Sun. 2024. "Seawater Mixed with One Part Alkali Activated Material: An Environmental and Cost Evaluation" Materials 17, no. 16: 4113. https://doi.org/10.3390/ma17164113

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