Various United Nations, bilateral and local agencies have continued with their efforts to identify solutions for water scarcity and salinity problems in Gaza strip. Several studies have been undertaken and plans and reports have been produced for interventions to address the potable water requirements of the people in the Gaza Strip which is recorded as one of the most heavily populated areas in the world [1] .

At present the underground coastal aquifer represents the main source for water supply to the population of approximately 1.7 million living in Gaza. Minor volumes of fresh water (4.7 MCM/Year) are currently imported from Israel Mekorot Water Company in addition to other small amounts supplied from at least 13 existing (public) plants, for a total capacity of 7020 m³/day, and including 8 plants installed with UNI- CEF assistance [2] .

The latest registry and monitoring records showed that annual sustainable yield of the coastal aquifer within the geographical boundary of Gaza is estimated to be 55 Million Cubic Meters (MCM). Recent rates of pumping from the aquifer are estimated at 170 MCM/year for both domestic and agricultural needs. The abstraction rates have increased significantly over the last three decades, due to a combination of inadequate available water imports to Gaza, the expanding population within Gaza, and the drilling and use of unlicensed wells (especially to provide irrigation for agricultural activities). Figure 1 showed that the over-abstraction has caused saline intrusion i.e. the entry of sea water to the aquifer from the Mediterranean Sea to the west, and also due to the lowering of the water table from deep groundwater abstraction to the south-east of Gaza by Israel. Water quality has been deteriorating rapidly, and modeling data suggest that the deterioration will continue further, with time [1] [2] [3] .

Massive over-pumping has led to increased saline intrusion as seawater from the adjacent Mediterranean enters and contaminates the aquifer as shown in Figure 1 which shows chloride concentration in the groundwater aquifer in year 2015. Another quality problem is high concentration of nitrate in the agricultural areas in the north; the source of the nitrate ion in the groundwater chemical components has resulted from different sources i.e. intensive use of agricultural pesticides beside the existence of septic tanks to dispose the domestic wastewater in the areas where there is no wastewater collection system (Figure 2). The nitrate ion concentration reaches a very high range in different areas of the Gaza Strip, while the WHO standard recommended nitrate concentration less than 50 mg/L [1] .

At its present rate of deterioration, the United Nations estimates that the underlying portion of the coastal aquifer on which the Gaza Strip relies for all its water needs will be unusable by 2016, and irreversibly damaged by 2020 [4] [5] . The lack of adequate supply of safe drinking water is therefore exposing the lives the Palestinians in Gaza to high levels of health risks. It has now become crucially important to safeguard available fresh water supplies and provide new additional potable water supplies to protect the lives and public health of the people in Gaza. As such, both short term and long term solutions to address the water scarcity issues have been formulated with particular emphasis on reducing the dependency on fast deteriorating ground water aquifer sources, to seek new non-conventional water resource which in this case is limited to sea water desalination processes [6] [7] .

Short-Term Low Volume (STLV) Sea Water Desalination Plant of 6000 m³/d is being under construction in the middle area of Gaza Strip. The plant will provide desalinated water for 75,000 inhabitants in Khanyounis and Rafah (Southern Part of Gaza Strip). The plant consists of water intake (four beach wells), Reverse Osmoses (RO) desalination system, and brine outfall and carrier pipeline to transmit the desalinated water to the blending tanks.

The limited number of analytical solutions for variable density flow problems creates a heavy dependence on numerical codes for simulating seawater intrusion. Such computer models have become irreplaceable tools to gain insight in real-world seawater intrusion issues ranging from system understanding on local or regional scales to future projections of SI for management purposes. Most codes solve a coupled system of variable density flow and solute transport equations, which is numerically complicated and computationally demanding. The main difficulty lies in the accurate solution of the solute transport part, which requires a fine discretization of the aquifer. Common techniques such as the finite element or finite difference methods perform well for the solution of the flow equations. The most widely used codes are SEAWAT [8] . SEAWAT was specifically designed for the simulation of SI, although it has many other applications as well, notably the combined simulation of groundwater flow and heat transfer. SEAWAT uses MODFLOW (finite differences) to solve the flow system and MT3D with its many solution techniques to solve the solute transport equations. Most MOD- FLOW packages are available in SEAWAT to simulate different stresses and boundary conditions [9] .

This article will assess the impacts of water intake system on the aquifer. In case of negative impacts, mitigations measures will be addressed to minimize these negative consequences. The mean approach of this article is to use both MODFLOW and SEA- WAT will investigate the impact of the beach wells on the seawater intrusion in the middle area of Gaza Strip.

The STLV plant is located in Deir Al Balah Governorate, at the border with Khanyounis governorate, and will serve Rafah and Khanyounis governorates. 80 dunums have been allocated to this purpose from the Palestinian Land Authority (PLA) as shown in Figure 3. The feasibility study for the seawater intake option indicated that Beach Wells (BW) is the most feasible option for the STLV RO plant [10] . For this STLV plant with an intended capacity of 6000 m³/day, the expected pumping rate of the beach wells is between 13,500 to 14,000 m³/day. This number is calculated assuming a recovery rate of 48% and 3% for service water.

The number of beach wells was calculated based on the maximum quantity of water that can be pumped to serve the desalination plant which is a round 13,500 m³/day. The total number of wells is 3 wells in addition to one standby well. Each of the three beach wells should have a capacity of pumping equal to 200 m³/hour and should operate 24 hrs/day.

Based on the hydrogeological investigation carried out in the site the beach wells were allocated close to the shoreline to assure the pumping of seawater and not influence the groundwater aquifer. As shown in Figure 1 the four wells are located in one line parallel to the sea shoreline with a distance for 40 to 50 from the shoreline. The minimum distance between the wells is 40 m.

Well components such as the screen diameter and length, gravel pack, the location of

the screen, the location of pump, etc. were determined based on the preliminary design report and the hydrogeological investigation carried out by UG consultant. Figure 2 shows the description of the typical beach well that has the following characteristics:

1) The external diameter of the borehole is 20 inch.

2) The diameter of the screen is 14 inch, opening size is computed to retain 90% of the gravel pack, therefore, the opening size will range between 1 mm to 1.5 mm and the opening slot percentage is 35%.

3) The length of the screen is 15 m located in sand or coarse sand layer below the water table. Stainless steel screens are used. The screen is located below the water table with a distance equal to double the expected drawdown of the water table after pumping of 200 m³/hr. The shaft of the pump should be about between 8 m to 10 m below the groundwater table.

4) The total length of pump housing depends on the depth of the water table, the depth of permeable layers (sand aquifer) and the drawdown of the water table. The lithology indicates one layer of coarse sand (Kurkar) up to 45 m below the ground surface. The depth of the water level is 8 to 9 m below the ground surface. The beach wells screens are located inside the sand and kurkar layer. The exact depth of the screen will be designed considering maximum drawdown of the groundwater level. Figure 4 shows the location of the screen of the well which will be located between 30 m and 45 m depth below the ground surface.

In order to study the impacts of beach wells on the aquifer, a prediction model, starting from the year 2000 until year 2040, was used to investigate the impacts of pumping from beach wells on the aquifer. Figure 5 presents the domain as a part of the coastal

aquifer. Hence, the aquifer parameters were set as if they were in the transient model. The long term seasonal recharge rate for the summer and winter is considered to represent the seasonal differences in recharge through each year. In the projects area, the consultant does not find agricultural or monitoring wells which could be used a baseline for investigation the results of the model.

The modelling approach used in this study showed that the location and the distribution of the beach wells are appropriate for the small size desalination plant intake. The article presented that the current distribution of the beach wells will have positive impacts on the Gaza Strip aquifer. The beach well will form a barrier for the seawater intrusion to the aquifer. However, for another case where the design criteria of the desalination intake will be changed, the impacts will completely be different. The essential criteria are the number of the wells, the distance between the wells, the well abstraction, the distance of the beach wells from the sea shoreline and the groundwater aquifer characteristics. This small desalination plant is of great importance for Gaza Strip, to face the population increase and the lack of clean and drinkable water resources in Gaza Strip. On other hand, these small desalination plants can enhance the groundwater quality in terms of reducing the seawater intrusion in Gaza Strip aquifer. The modelling approach is recommended to be used in investigating the impacts of future small scale desalination plants in Gaza Strip.

Mogheir, Y. (2016) Assessing the Seawater Intrusion Due to Beach Wells in the Desalination Plant. Journal of Geoscience and Environment Protection, 4, 37-47. http://dx.doi.org/10.4236/gep.2016.412003