1. Introduction
In the past few decades, the pressures of human population and patterns of economic development have led to the shrinking of available water resources worldwide, while water shortage has become a critical factor in the global water crisis. It is a challenge for water resource managers and planners to maintain sustainable development under situations of increasing population, developing economies and changing climate. Particularly in many semiarid and arid regions, water shortage and an unreliable water supply have been regarded as one major obstacle to regional sustainable development for watershed systems [
1,
2,
3,
4]. Water trading is useful for allocating water resources optimally, which increases the economic productivity of water by encouraging its movement from low to high valued use. Under the situation of limited water resources, markets can also provide incentives to adopt water saving policies [
5]. Water trading can balance limited water resources between the allocation for human use and the streamflow, especially in semi-arid and arid regions, such that several water trading programs have been established and are under development throughout the world [
6,
7,
8]. However, the uncertainties existing in practical water trading programs are often related to errors in the acquired data, variations in spatial and temporal units and the incompleteness or impreciseness of the observed information, which leads to difficulties in planning water trading scientifically [
9]. Consequently, the effective planning of water resource management under such uncertainties and complexities is important for facilitating sustainable socio-economic development for watershed systems [
10].
Two-stage stochastic programming (TSP) is effective in dealing with problems for which an analysis of policy scenarios is desired and the uncertainties can be expressed as probabilistic distributions [
11,
12]. In TSP, an initial decision must be made before the realization of random variables (first-stage decision), and then, a corrective action can be taken after random events have taken place (second-stage decision) [
13]. This implies that a second-stage decision can be used to minimize “penalties” that may appear, due to some infeasibility [
14]. TSP has been widely used for water resource management and planning over the past few decades. For example, Maqsood
et al. [
15] developed an interval-fuzzy two-stage stochastic programming method for planning water resource management systems associated with multiple uncertainties, in which interval fuzzy programming methods were introduced into a TSP framework. Kenneth
et al. [
16] developed a TSP method for tackling uncertainties expressed as probability density functions for water availability. Li
et al. [
17] proposed an interval-parameter two-stage stochastic nonlinear programming method for supporting decisions about water-resource allocation within a multi-reservoir system, where uncertainties expressed as both probability distributions and discrete intervals were reflected. Vidoli [
18] evaluated water resource services by integrating conditional, robust, nonparametric frontier and multivariate adaptive regression splines into a TSP framework. In general, TSP can provide an effective linkage between policies and the economic penalties, which has the advantages of reflecting the complexities of system uncertainties, as well as analyzing policy scenarios when the pre-regulated targets are violated. However, the major problem of TSP is that the increased data requirement for specifying the probability distributions of coefficients may affect their practical applicability [
19]. One potential approach to better account for more complex uncertainties is to introduce an interval-parameter programming (IPP) technique into the TSP framework. IPP is an alternative for handling uncertainties in the model’s left- and/or right-hand sides, as well as those that cannot be quantified as membership or distribution functions, since interval numbers are acceptable as its uncertain inputs. Moreover, in practical water resource management problems, uncertainties may be related to errors in the acquired data, variations in spatial and temporal units and the incompleteness or impreciseness of the observed information in water resource management [
10,
20]. Fuzzy programming (FP) is effective in handling ambiguous coefficients of objective functions and constraints caused by imprecision and vagueness, when the quality and quantity of uncertain information is often not satisfactory enough to be presented as a probabilistic distribution. Previously, a number of FP techniques, such as the fuzzy-stochastic [
21,
22], interactive fuzzy [
23] and robust methods [
24,
25], were developed to deal with uncertainties in decision making problems. Fuzzy credibility-constrained programming (FCP) is effective in reflecting the fuzziness inherited with parameters associated with subjective considerations, which would be useful in the presence of weaker sources of information. FCP can measure the confidence levels in a fuzzy water system to tackle uncertainties expressed as fuzzy sets, when detailed information is not able to be presented by interval or stochastic numbers [
26,
27,
28,
29]. However, few studies have been reported on the application of FCP techniques to water resource management and planning [
30,
31,
32]. Therefore, one potential approach to better account for multiple uncertainties and economic penalties is to introduce the IPP and FCP concepts into the TSP framework; this will lead to a two-stage inexact credibility-constrained programming (TICP) method.
The aim of this study is to develop such a TICP method for identifying a cost-effective water trading policy under multiple uncertainties. The TICP is an integrated optimization technique for tackling uncertainties expressed as discrete intervals, probability distributions and fuzzy sets. The TICP method will be applied to a real case study of water resource management in the Kaidu-kongque River Basin, which is one of the aridest regions in Northwest China. The degrees of satisfaction for the given constraints will be represented using interval credibility levels, which can provide scientific support for large-scale regional water-resource management under uncertainty conditions at the watershed level. A number of policy scenarios that are associated with different decreasing levels of the water permit and trading ratio will be analyzed, which can help in gaining insight into the tradeoff between water trading and economic objectives.
2. Methodology
When uncertainties of the right-hand side of the model are expressed as probability density functions (pdfs) and decisions need to be made periodically over time, the problem can be formulated as a two-stage stochastic programming (TSP) model [
33]. A general TSP linear model can be formulated as follows:
subject to:
where
x is the vector of the first-stage decision variables,
cTx is the first-stage benefits, ω is the random events after the first-stage decisions are made,
ph is the probability of an event, ω
h,
Q(
y, ω
h) is the recourse at the second-stage under the occurrence of the event, ω
h, and
is the expected value of the second-stage penalties [
12]. However, the parameter of a model may fluctuate within a certain interval, and it is difficult to state a meaningful probability distribution for this variation. Interval-parameter programming (IPP) can deal with uncertainties in objective function and system constraints, which can be expressed as intervals without distribution information. An interval number,
x±, can be defined as an interval with a known lower-bound and upper-bound, but unknown distribution information [
34,
35]. It can be expressed as [
x−,
x+], representing a number (or an interval), which can have a minimum value of
x− and a maximum one of
x+.
where
x− and
x+ are the lower and upper bounds of
x±, respectively. When
x− =
x+,
x+ becomes a deterministic number. When uncertainties presented as probabilities and intervals exist in water resource management systems, based on IPP and TSP techniques, an inexact TSP (ITSP) model can be formulated as follows [
17]:
subject to:
Let
be a fuzzy set of imprecise right-hand sides with possibility distributions. The triangular fuzzy membership function is the most popular possibility distribution, and it is adopted in this study, due to its computational efficiency. Accordingly, the credibility of the constraint
Ax ≤
could be defined as follows [
32]:
Thereby, a general credibility constrained problem can be formulated as follows:
subject to:
where λ is the credibility level. In the optimization process for management and planning, it is usually assumed that the credibility level should be no less than 0.5 [
32]. Thus, Equation (5b) can be rewritten as:
where it can be transformed into a deterministic constraint as follows:
Therefore, by incorporating the creditability constraints equation into the ITSP framework, a two-stage inexact credibility-constrained programming (TICP) model can be formulated as follows:
subject to:
Then, an interactive two-step solution algorithm is proposed for solving the TICP model, which is different from normal interval analysis and best/worst-case analysis [
12,
34,
35]. The TICP model can be transformed into two sets of deterministic submodels, which correspond to the lower and upper bounds of the desired objective function value. The resulting solutions can provide intervals for the objective function and decision variables with different levels of risk in violating the constraints. When the objective is
ƒ+, which corresponds to the upper bound of the objective function value, it can be formulated as follows:
subject to:
where
c+j (
j = 1,2,…,
q1) > 0;
c+j (
j =
q1 + 1,
q1 + 2,…,
n) < 0;
d+k (
j = 1,2,…,
q2) > 0;
d+k (
j =
q2 + 1,
q2 + 2,…,
m) < 0;
when
,
when
and λ
- = the lower bound of the credibility level value.
The optimal solution of Model (9), including
for
j = 1 to
q1, for
j = q1 + 1 to
n,
for
k = 1 to
q2 and
for
k = q2 + 1 to
m, can be obtained. Accordingly, the second submodel corresponding to the lower bound of the objective function value can be formulated as:
subject to:
Thereby, optimal solutions of Model (10) can be gained, including
for
j = 1 to
q1,
for
j = q1 + 1 to
n,
for
k = 1 to
q2 and
for
k = q2 + 1 to m. Therefore, by integrating the solutions of the two submodels, the solution of the TICP model can be generated.
The solution process of TICP can be summarized as follows:
Step 1: Formulate the TICP model.
Step 2: Transform the TICP model into two submodels, where the submodel corresponding to ƒ+ is desired first, since the objective is to maximize ƒ±.
Step 3: Obtain the optimal solutions by solving the ƒ+ submodel under each λ.
Step 4: Formulate and solve the ƒ- submodel by importing optimal solutions from the ƒ+ submodel into the ƒ-submodel under each λ.
Step 5: Obtain the optimal solution interval value under each λ.
3. Case Study
The Kaidu River and the Kongque River are the branches of the Tarim River formed from the middle of mountain Tian to Lake Bositeng and are about 610 km- and 785 km-long, respectively. The Kaidu-kongque River Basin is located in the middle reach of the Tarim River Basin, which is approximately 62 × 10
3 km
2 [
36] (as shown in
Figure 1). It is a typical arid region, due to an extremely dry climate and a low and uneven distribution of rainfall. For example, the climate in the basin is extremely dry, with the average rainfall being about 273 mm/year, which is more than 80% of the total annual precipitation fall from May to September and less than 20% of the total fall from November to the following April [
37]. The basin includes six counties (
i.e., Kuerle, Yanqi, Hejing, Heshuo, Bohu and Yuli) and has a population of more than one million [
36]. It is suitable for the growth of crops, such as wheat, corn, sugar beet, tomato and fruit, which have provided high-speed growth in agricultural product processing and manufacturing. Moreover, the rich mineral and oil resources of the basin form an industrial structure dominated by mining, the chemical industry and the fossil oil industry, while textiles, electric power, papermaking and transportation are keeping pace with the development of the mainstay industries. The water demands of four users (e.g., municipal, agricultural, industrial and ecological) in six districts rely on the river’s streamflow, which is mainly derived from upstream flow, snow melt and rainfall. Due to the dry climate, low-rainfall and high evaporation, the water supply capacity of the river is quite low, which presents difficulties in satisfying the water demands from the six counties. Particularly in recent years, the demand for water has reached the limits of what the natural system can provide, so that water shortage could become a major obstacle to social and economic development for this region. Unfortunately, in the study of the basin, there is a lack of effective tools for facilitating efficient, equitable and sustainable water resource management. Therefore, population growth, the food security challenge, industrial sector development and the potential threat of climate change elevate the attention given to efficient and sustainable water management [
38].
Water trading can solve conflicts caused by water shortage [
39,
40], not only improving the net benefit for the system, but also saving water, while respecting hydrological, environmental, food security, economic development, population growth and institutional constraints. Under an allocated water permit, trading can release surplus water to remedy the losses from water deficiency, achieving a higher profitability. However, a number of variations caused by factitious factors and natural factors exist in the trading system, which bring more complexities and uncertainties to the water trading system. For example, less observation and insufficient data create uncertainties in data inputting, and natural uncertainties generate many stochastic factors in the trading system, such as streamflow water, demand and water-allocation targets; fluctuations can be associated with the net benefit for the system. These complexities could become further compounded by not only interactions among the uncertain parameters, but also their economic implications [
2]. Therefore, the proposed TICP model can be used in water trading for optimally allocating limited water resources to facilitate regional sustainability with a maximized benefit for the system.
Figure 1.
The study area.
Figure 1.
The study area.
A manager (e.g., a valley authority or water resources bureau) is responsible for allocating water resources to multiple users (e.g., residential, industrial, agricultural and ecological) in the Kaidu-kongque River Basin and aims to create a plan to effectively allocate the uncertain supply of water to every user in order to satisfy the users’ demand and to maximize the overall benefit for the system. In order to recover the ecological system of the lower reach of the watershed, the manager has obligated water to maintain the water level of the river first. Water permits have been allocated to each user by a manager in the beginning of this year, which are based on the water utilization of last year. Nevertheless, allocations are made once per year, which will be adjusted by the water manager next year. When variations emerge in this year, system disruption risk attributable to the uncertainties may influence the benefits for the system and water supplies tremendously. This leads to a problem of recourse for planning water resource allocation with a maximized economic benefit and a minimized system failure risk.
On the basis of the local management policy, water availability is allocated to users for consumption by the percentage of the water permits, which leads to water surpluses and water shortages, but not to trading, when water is not tradable. The benefits for the system denote the profit of the economic production in proportion to the pre-regulated economic targets, while the system’s recourse penalties denote the loss for a shortage. With the purpose of obtaining a more effective water allocation, a water trading program can be established, in which water permits being traded at a higher value substitute for the allocation to each user proportionally. When water is tradable, water permits being allocated to users by cubic meters, water shortages and surpluses emerge, due to the difference between water targets, permits and availability. Therefore, retributions for water permits would be acquired, with which water shortages and surpluses could join in the water market for trading based on the law of value. Since the water market can provide an equal and effective manner of allocating water, water shortages and surpluses reallocated by water trading led to water permits being reattributed. Under such a situation, the manager can reduce the water permits to release appropriate water permits for trade in the water market according to the actual water requirements, which achieves a maximized benefit for the system, while considering the trading costs (the trading cost is smaller than the loss of the shortage). Moreover, multiple uncertainties may exist in water allocation and trading processes (e.g., uncertain data and the probability distribution of water availability), which affect water resource management planning. Thus, the manager will formulate a TICP model for water trading to maximize the entire benefit for the system, which can satisfy the goal of water use reduction and allow for reflection on complex uncertainties. When water is tradable, the TICP model can be formulated as follows:
Subject to the:
- (1)
Constraints of water permit:
- (2)
Constraints of water shortage:
- (3)
Constraints of water surplus:
- (4)
Constraints of water trading:
- (5)
Constraints of technical:
where
i denotes the type of user (
i = 1, 2, 3, 4),
j denotes name of the district (
j = 1, 2,…,6),
h denotes the probability level of random water availability (
h = 1, 2, 3),
presents the net benefit of the entire system with trading (US$),
is net benefit to user
i in district
j per volume of water being delivered (US$/10
3 m
3),
is the water demand target for user
i in district
j (10
6 m
3),
is the total water availability of the entire system under probability
Ph (10
6 m
3),
Ph denotes the probability of random water availability
under level h (%),
is the economic loss to user
i in district
j per volume of water not being delivered (US$/10
3 m
3),
is the water deficiency for user
i in district
j when demand
is not met (10
6 m
3),
is the allocated allowable water permit to user
i in district
j (10
6 m
3), λ is the credibility level, which measures the degrees of satisfaction of the constraints,
d is the percentage of the reduced total allowable water allocation,
is the water released to user
i in district
j when the total water availability exceeds the allowable water reallocation with trading scheme (10
6 m
3),
is the trading fixed cost to user
i in district
j with trading scheme (US$/10
3 m
3),
is the variable trading cost to user
i in district
j with trading scheme (US$/10
3 m
3),
is the amount of water trading from other water sources to user
i in district
j with trading scheme (10
6 m
3) and
tʹijh /
tijh is the ratio of water trading from other water sources to user
i in district
j with the trading scheme.
Table 1 shows basic economic data and trading costs, which are estimated indirectly based on the statistical yearbook of the Xinjiang Uygur Autonomous Region in the Uygur Autonomous Region, 2005–2010, and the water price for the Xinjiang Autonomous Region. Values of
and
are estimated according to different users’ gross national product in different counties indirectly, the upper bound values of which are estimated as the highest from the yearbook (2005–2010) and the lower bound values of which are the opposite. For example, the net benefit (
) for the agricultural user in Hejing County is estimated by the gross amount of crops (
i.e., wheat, corn, tomato, cotton and fruit) and the total water demand (net benefit = gross amount of crops/total water demand). From 2005 to 2010, the highest net benefit was 1860 US$/10
3 m
3 in 2008, which was estimated by the gross amount of crops (
i.e., wheat = 45.1 × 10
6 US$; oil plant = 11.3 × 10
6 US$; tomato = 15.93 × 10
6 US$; cotton
t = 44.02 × 10
6 US$ and other crops = 47.33 × 10
6 US$) and the water demand (
i.e., wheat = 24.1 × 10
6 m
3; oil plant = 2.91 × 10
6 m
3; tomato = 3.41 × 10
6 m
3; cotton = 29.4 × 10
6 m
3 and other crops = 28.18 × 10
6 m
3). Meanwhile, the lowest net benefit was 1530 US$/10
3 m
3 in 2005. Therefore, the interval value of the net benefit is acquired as [1530, 1860] US$/10
3 m
3, which is on the basis of the highest and lowest value of the net benefit. The method calculated for the net benefit of the agricultural user in Hejing County can be applied to other users, districts and even other economic data.
is a basic form of trading cost, which is estimated by the actual price of water exceed water permit in Kaidu-kongque Basin.
is estimated according to the opportunity cost of water, which is affected by a number of factors, such as the scarcity of water resources, the relationship between supply and demand and the status of socio-economic development.
Table 2 shows policy data
, which are acquired from the water permits of the water authority of Uygur Autonomous Region from 2005 to 2010 directly. Additionally, water target
is estimated by the users’ actual water usage in recent years, which takes the situation of economic development into consideration. The value of
should be derived by conducting statistical analyses with the results of the annual streamflow of the Kaidu-kongque River (2005–2010). Due to the rainy seasons in the Kaidu-kongque River Basin, more than 80% of the total annual precipitation falls from May to September, and less than 20% of the total falls from November to the following April [
37]. Therefore, the total water availability can be converted to several levels.
Table 3 shows the total water availability of the Kaidu-kongque River Basin under several level probabilities.
Table 1 shows basic economic data and trading costs, which are estimated indirectly based on the statistical yearbook of the Xinjiang Uygur Autonomous Region in the Uygur Autonomous Region, 2005–2010, and the water price for the Xinjiang Autonomous Region. Values of
and
are estimated according to different users’ gross national product in different counties indirectly, the upper bound values of which are estimated as the highest from the yearbook (2005–2010) and the lower bound values of which are the opposite. For example, the net benefit (
) for the agricultural user in Hejing County is estimated by the gross amount of crops (
i.e., wheat, corn, tomato, cotton and fruit) and the total water demand (net benefit = gross amount of crops/total water demand). From 2005 to 2010, the highest net benefit was 1860 US$/10
3 m
3 in 2008, which was estimated by the gross amount of crops (
i.e., wheat = 45.1 × 10
6 US$; oil plant = 11.3 × 10
6 US$; tomato = 15.93 × 10
6 US$; cotton
t = 44.02 × 10
6 US$ and other crops = 47.33 × 10
6 US$) and the water demand (
i.e., wheat = 24.1 × 10
6 m
3; oil plant = 2.91 × 10
6 m
3; tomato = 3.41 × 10
6 m
3; cotton = 29.4 × 10
6 m
3 and other crops = 28.18 × 10
6 m
3). Meanwhile, the lowest net benefit was 1530 US$/10
3 m
3 in 2005. Therefore, the interval value of the net benefit is acquired as [1530, 1860] US$/10
3 m
3, which is on the basis of the highest and lowest value of the net benefit. The method calculated for the net benefit of the agricultural user in Hejing County can be applied to other users, districts and even other economic data.
is a basic form of trading cost, which is estimated by the actual price of water exceed water permit in Kaidu-kongque Basin.
is estimated according to the opportunity cost of water, which is affected by a number of factors, such as the scarcity of water resources, the relationship between supply and demand and the status of socio-economic development.
Table 2 shows policy data
, which are acquired from the water permits of the water authority of Uygur Autonomous Region from 2005 to 2010 directly. Additionally, water target
is estimated by the users’ actual water usage in recent years, which takes the situation of economic development into consideration. The value of
should be derived by conducting statistical analyses with the results of the annual streamflow of the Kaidu-kongque River (2005–2010). Due to the rainy seasons in the Kaidu-kongque River Basin, more than 80% of the total annual precipitation falls from May to September, and less than 20% of the total falls from November to the following April [
37]. Therefore, the total water availability can be converted to several levels.
Table 3 shows the total water availability of the Kaidu-kongque River Basin under several level probabilities.
Table 1.
Economic data and trading costs.
Table 1.
Economic data and trading costs.
District | User |
---|
i = 1 | i = 2 | i = 3 | i = 4 |
---|
Municipality | Agriculture | Industry | Ecology |
---|
Net benefits (unit: US$/103 m3) |
j = 1 Kuerle county | [6030, 6670] | [2320, 2520] | [4530, 4670] | [1960, 2120] |
j = 2 Yanqi county | [5500, 6040] | [1420, 1560] | [2600, 2930] | [1680, 1930] |
j = 3 Hejing county | [4670, 4800] | [1530, 1860] | [3730, 3810] | [1540, 1780] |
j = 4 Heshuo county | [5300, 5530] | [2010, 2340] | [3440, 3620] | [1660, 1940] |
j = 5 Bohu county | [4910, 5100] | [1780, 2010] | [3620, 3740] | [1530, 1840] |
j = 6 Yuli county | [4600, 5260] | [2230, 2460] | [3220, 3440] | [1690, 1990] |
Penalties (unit: US$/103 m3) |
j = 1 Kuerle county | [9045, 10005] | [3480, 3765] | [6795, 7005] | [2940, 3180] |
j = 2 Yanqi county | [8250, 9060] | [2130, 2340] | [3900, 4395] | [2520, 2895] |
j = 3 Hejing county | [7005, 7200] | [2295, 2790] | [5595, 5725] | [2310, 2670] |
j = 4 Heshuo county | [7950, 8295] | [3015, 3510] | [5160, 5430] | [2190, 2490] |
j = 5 Bohu county | [7365, 7650] | [2670, 3015] | [5430, 5610] | [2295, 2760] |
j = 6 Yuli county | [6900, 7890] | [3345, 3690] | [4830, 5160] | [2535, 2985] |
Trading fix cost (unit: US$/103 m3) |
j = 1 to 6 | [3050, 3150] | [550, 650] | [2400, 2600] | [280, 350] |
Trading variable cost (unit: US$/103 m3) |
j = 1 to 6 | [1200, 1350] | [700, 800] | [150, 200] | [100, 150] |
Since linguistic terms are encountered in the practical process of data acquisition associated with human subjective judgment, scales of linguistic terms have been established [
41]. Semantic scales are used to present the credibility levels of decision makers (
i.e., quite, very, almost and practical degree of satisfaction corresponding to λ
= 0.6 to 0.9) and violated constraints (
i.e., quite, very, almost and practical violation risk level corresponding to λ
= 0.4 to 0.1). There is a strong negative correlation between credibility levels and violated levels (
i.e., credibility levels + violated levels = 1), in which is manifest the relationship between the degree of satisfaction and the violation risk level. For example, the quite satisfied constraint (λ
= 0.6) corresponds to the quite violated constraint (
r = 0.4), which indicates a high satisfaction degree corresponding to a low violation risk. By setting the acceptable semantic terms of decision makers, acceptable interval credibility levels can then be generated. In order to ensure that the constraints would be practically satisfied and not violated in the study system, the credibility level, λ, in this model is set as [0.6, 0.9] [
32]. In this study, two cases were examined based on different water resource management policies. Case 1 was based on a policy for a 5% decrease in the water permit and a 100% trading ratio. Case 2 was based on a policy for a 10% decrease in the water permit and a 90% trading ratio. Since the credibility level, λ, in this model is set as [0.6, 0.9], different violation risk levels of water availability and water resource constraints are considered in two cases, which can help in analyzing different water resource management policies under the credibility levels.
Table 2.
Water targets and water permits.
Table 2.
Water targets and water permits.
District | User |
---|
i = 1 | i = 2 | i = 3 | i = 4 |
---|
Municipality | Agriculture | Industry | Ecology |
---|
Water target (unit: 106 m3) |
j = 1 Kuerle County | [8.80, 14.00] | [258.00, 275.00] | [53.30, 620.00] | [56.00, 76.00] |
j = 2 Yanqi County | [6.00, 8.20] | [158.00, 165.00] | [28.00, 39.00] | [31.00, 47.00] |
j = 3 Hejing County | [2.40, 4.30] | [81.00, 88.00] | [16.00, 20.10] | [14.70, 23.00] |
j = 4 Heshuo County | [0.24, 0.50] | [9.70, 10.10] | [1.78, 2.25] | [1.28, 2.60] |
j = 5 Bohu County | [2.20, 4.30] | [75.00, 85.00] | [15.60, 19.00] | [13.70, 23.00] |
j = 6 Yuli County | [4.60, 6.00] | [110.00, 120.00] | [21.60, 27.00] | [24.00, 33.00] |
Allocated allowable water permit (unit: 106 m3) |
j = 1 Kuerle County | [9.72, 13.75] | [261.60, 275.08] | [55.44, 61.89] | [59.56, 75.65] |
j = 2 Yanqi County | [[6.64, 8.14] | [158.33, 162.87] | [30.31, 36.65] | [32.26, 44.79] |
j = 3 Hejing County | [2.89, 4.23] | [82.22, 84.50] | [15.70, 19.01] | [17.08, 23.24] |
j = 4 Heshuo County | [0.36, 0.53] | [9.11, 9.38] | [1.89, 2.11] | [1.69, 2.70] |
j = 5 Bohu County | [2.56, 4.09] | [78.89, 81.84] | [15.78, 18.41] | [15.58, 22.58] |
j = 6 Yuli County | [4.94, 5.87] | [110.56, 117.41] | [22.33, 26.42] | [25.56, 32.29] |
Table 3.
Probability levels and total water availabilities.
Table 3.
Probability levels and total water availabilities.
District | Level | Probability | User |
---|
i = 1 | i = 2 | i = 3 | i = 4 |
---|
Municipality | Agriculture | Industry | Ecology |
---|
Total water availability (unit: 106 m3) |
j = 1 Kuerle County | h = 1 (low) | 0.6 | [6.57, 10.67] | [202.32, 216.00] | [43.47, 49.96] | [42.30, 58.50] |
| h = 2 (medium) | 0.3 | [7.30, 11.85] | [224.80, 240.00] | [48.30, 55.51] | [47.00, 65.00] |
| h = 3 (high) | 0.1 | [8.03, 13.04] | [247.28, 264.00] | [53.13, 61.06] | [51.70, 71.50] |
j = 2 Yanqi County | h = 1 (low) | 0.6 | [4.77, 6.38] | [124.02, 128.70] | [22.86, 29.41] | [22.95, 35.55] |
| h = 2 (medium) | 0.3 | [5.30, 7.09] | [137.80, 143.00] | [25.40, 32.68] | [25.50, 39.50] |
| h = 3 (high) | 0.1 | [5.83, 7.80] | [151.58, 157.30] | [27.94, 35.95] | [28.05, 43.45] |
j = 3 Hejing County | h = 1 (low) | 0.6 | [1.89, 3.24] | [66.11, 68.40] | [12.96, 16.29] | [11.43, 17.82] |
| h = 2 (medium) | 0.3 | [2.10, 3.60] | [73.45, 76.00] | [14.40, 18.10] | [12.70, 19.80] |
| h = 3 (high) | 0.1 | [2.31, 3.96] | [80.80, 83.60] | [15.84, 19.91] | [13.97, 21.78] |
j = 4 Heshuo County | h = 1 (low) | 0.6 | [0.19, 0.38] | [7.90, 8.19] | [1.40, 1.62] | [0.88, 1.90] |
| h = 2 (medium) | 0.3 | [0.21, 0.42] | [8.78, 9.10] | [1.55, 1.80] | [0.98, 2.11] |
| h = 3 (high) | 0.1 | [0.23, 0.46] | [9.66, 10.01] | [1.71, 1.98] | [1.08, 2.32] |
j = 5 Bohu County | h = 1 (low) | 0.6 | [1.79, 3.33] | [58.50, 65.70] | [12.69, 15.38] | [11.16, 18.20] |
| h = 2 (medium) | 0.3 | [1.99, 3.70] | [65.00, 73.00] | [14.10, 17.09] | [12.40, 20.23] |
| h = 3 (high) | 0.1 | [2.19, 4.07] | [71.50, 80.30] | [15.51, 18.80] | [13.64, 22.25] |
j = 6 Yuli County | h = 1 (low) | 0.6 | [3.69, 4.75] | [86.85, 93.82] | [17.64, 21.79] | [19.35, 26.10] |
| h = 2 (medium) | 0.3 | [4.10, 5.28] | [96.50, 104.25] | [19.60, 24.21] | [21.50, 29.00] |
| h = 3 (high) | 0.1 | [4.51, 5.81] | [106.15, 114.67] | [21.56, 26.63] | [23.65, 31.90] |