1. Introduction
The growth of urban areas accompanied by increased parking lots,
roadways and rooftops has increased spatially and has resulted in
expanded impervious surfaces. This has clear implication on the
hydrological characteristics of a watershed by preventing surface flow
infiltration (Sahoo and Sreeja, 2012). This increase in impervious
surfaces becomes a major cause for flash flooding. Subsequently, it is
responsible for damage to urban infrastructures and utilities (Gholami
et al., 2010). A more sustainable land cover type regulating the
watershed hydrology and the riparian environment is vegetation cover.
The watershed ecosystem services endowment is determined by the
structure and distribution of the vegetation cover (Engelhardt et al.,
2011). Moreover, Rosenmeier et al. (2002) showed the positive influence
of vegetation cover on surface runoff reduction and groundwater
recharge. Bosch and Hewlett (1982) have studied the water yield change
due to the conversion of different vegetation cover types in watersheds.
The traditional way of identification and classification of land cover
types is less explanatory and time-consuming. The current remote sensing
technology has made land use and cover classification much easier
(Piyoosh and Ghosh, 2017a). The remotely sensed data can give a general
picture of a relatively large area within a short period of time through
spectral indices. Though most indices represent a single land cover
type, they can mix one land cover type with the others (Deng and Wu,
2012). There are different types of indices that can represent the
features that are of interest. For instance, Bhatti and Tripathi (2014)
listed the Normalized Difference Vegetation Index (NDVI) for vegetation,
the normalized difference snow index (NDSI) for snow, the normalized
difference water index (NDWI) for water, and the normalized difference
built-up index (NDBI) for built-up areas. Similarly, for impervious
surface evaluation, Xu (2010) used the normalized difference impervious
surface index (NDISI), whereas Piyoosh and Ghosh (2017b) applied the
normalized difference soil index (NDSI) for bare soil. To quantify these
indices different remote sensing imagery types are available, but
require their own adjustment because of the spectral variability. There
are a number of previous studies on evaluation of Landsat-8 Operational
Land Imager (OLI) data for these different indices (Bhatti and Tripathi,
2017; Piyoosh and Ghosh, 2017a).
Morphometric analysis helps to evaluate the watershed geospatial,
hydrological and hydraulic characteristics (Srivastava et al., 2014).
Strahler (1964) used morphometric analysis to show the geologic
characteristics, landform pattern, soil physical properties, soil
erodibility, and the hydrologic response of the watershed. By applying
geographic information systems (GIS) and remote sensing technology,
automated and semi-automated morphometric analysis becomes fast and
easy. As a result, the extent of morphometric analysis application has
broadened. Javed (2009) and Patel et al. (2012) used morphometric
analysis to detect spaces and their physical barriers for different
development and economic benefits. Others have used it to prioritize
sub-watersheds for soil erosion control measures (Ahmed et al., 2017;
Farhan et al., 2017; Meshram and Sharma, 2015). Morphometric analysis
can also be used to identify areas that are affected by flash flood
hazards (Farhan et al., 2016, Youssef et al., 2010).
According to Engelhardt et al. (2011), the watershed geomorphology
controls the extent and abundance of riparian vegetation, which
influence runoff regimes. This shows the need of considering the
relationship between geomorphology and the riparian vegetation cover, as
this helps to analyze the watershed development and restoration.
Besides, Groffman et al. (2003) revealed that riparian zones are hot
spots of interactions between plants, soil, water, microorganisms and
people, and may be seriously affected by urbanization.
Addis Ababa’s unprecedented growth has also a clear impact on the land
cover dynamics and the urban and sub-urban watershed characteristics.
Furthermore, Addis Ababa’s roadways are experiencing frequent flooding,
which makes traffic difficult. The 2017 Addis Ababa City Fire, Emergency
Prevention and Rescue Agency report shows that more than 70 flood
incidences were recorded following the 2017 rainy season and caused more
than 740,000 USD worth damage to infrastructure and private property.
Belete (2011) related the enhanced flash flood hazard to the increase of
uncontrolled impervious surface growth. For the riparian buffering, the
urban planning guidelines of the Ministry of Urban Development and
Construction (MUDC, 2012) recommends fifteen meter buffering distance on
either side of the stream. However, these recommendations have not been
implemented in most of Addis Ababa. Thus, the riparian zones are in a
degraded condition and hardly provide the expected ecosystem services.
As Alemayehu (2001) revealed, they are used for household and industrial
sewer and waste disposal sites instead.
Overall, while research has been done on the issues, it is hardly
possible to find a kind of assessment for this specific watershed, and
other research has also failed to integrate the methods of urban land
cover and hydro-morphological characteristics for area prioritization
and mapping the flash flooding and functioning of riparian landscape.
Moreover, not much attention has been put on this area and the current
preservation and river side development efforts have focused largely on
physical and structural solutions to the problems. The city projects
development also have given little concern on the landscape based
watershed monitoring and conservation planning. Studies have weakly
shown the relationship of the hydro-morphological and land cover
dimension to measure the vulnerability of flash floods and the role of
the riparian landscape. Thus the main objectives of this study were:
- Map and evaluate the flash flood vulnerability levels of the area
using the quantitative measures of urban land cover and the
hydro-morphological characteristics of the watershed
- Assess the level of the riparian landscape functioning to identify
sustainable solutions to urban watershed and riparian ecosystem
management and conservation.
2. Methods and
Data
2.1. The Study
Area
Kebena watershed is one of the oldest settlement quarters of Addis
Ababa, which covers Yeka, Gulele, Arada, Kirkos and Bole sub-cities. It
also extends to Sululta District of Oromiya special zone surrounding
Addis Ababa. The Kebena watershed is located in the northern part of the
city, and covers about 5000 hectares of land. It is a predominantly
rugged highland terrain with the elevation ranging from 2317 to 3182
m.a.s.l (fig 1).
2.2. Methods
The watershed was defined based on the 30m shuttle radar topographic
mission (SRTM) data of the United State Geological Survey (USGS). To
support this the 30m grid elevation data were collected from the Addis
Ababa city administration. The topographic data were reprocessed and
converted to a digital elevation model (DEM). The Arc- hydro and
Arc-swat modeling tools were used to extract the Kebena watershed by
taking an outlet at a point before meeting the stream locally known as
Banteyiketu. The watershed includes the streams locally known as the
main Kebena and Ginfile rivers. The Arc-hydro modeling tools were again
used to subdivide the micro-watersheds. For image indices evaluation the
ArcGIS raster calculator was used and a Principal Component Analysis
(PCA) of the morphometric variables was made using the R-studio
programing language.
2.2.1. Land Cover Analysis
The study identified urban and suburban land cover based on a
distinction between vegetation cover and impervious surface cover. This
study calculated NDVI and BCI to identify the vegetation and impervious
surface covers, respectively. The main data used was Landsat-8
Operational Land Imager (OLI) data collected on 23rd of December, 2015
along row 168 and path 54, and then extracted by the target area shape
file. Before performing the calculation the atmospheric correction and
band rationing was made first by eq. 1 and eq. 2, based on the metadata
(USGS, 2015):
\(L\lambda=\ M\rho Qcal+\ A\rho\) (1)
\(P_{\lambda}=\frac{L_{\lambda}^{{}^{\prime}}}{\sin\left(\theta_{\text{SE}}\right)}\)(2)
Where: Lλ is top of atmosphere spectral radiance (Watts/ (m2 * srad *
μm));
Mρ is Band-specific multiplicative rescaling factor from the metadata
(REFLECTANCE_MULT_BAND_x, where x is the band number);
Qcal is the Digital Number of the band being processed;
Aρ is Band-specific additive rescaling factor from the metadata
(REFLECTANCE_ADD_BAND_x, where x is the band number) and
Pλ is top of atmosphere planetary reflectance (\(L_{\lambda}^{{}^{\prime}}\)),
with correction for solar angle (θSE)
The NDVI was calculated using eq. 3 to determine the amount of
vegetation cover in the watershed:
\(\text{NDVI}=\ \frac{\text{OLIBand}\ 5-\text{OLIBand}\ 4}{\text{OLIBand}\ 5+\text{OLIBand}\ 4}\)(3)
Recently different studies used various indices in impervious surface
extraction. For instance, Sun et al. (2017) used a modified NDISI and
Bhatti and Tripathi (2014) applied NDBI to maximize their specific
advantages. However, BCI appears a more effective index type to
represent the urban land cover type. It has a high positive value for
impervious surfaces (Deng and Wu, 2012), which differentiates the
feature easily. To calculate the BCI (eq. 4; Baig et al., 2014), it is
necessary to assess the tasseled cap (TC) transformation of greenness,
brightness and wetness (eq. 5 – 7; Deng and Wu, 2012).
\(\text{BCI}=\ \frac{\frac{H+L}{2}-V}{\frac{H+L}{2}+V}\) (4)
\(H=\ \frac{TC1-TC1min}{TC1max-TC1min}\) (5)
\(V=\ \frac{TC2-TC2min}{TC2max-TC2min}\) (6)
\(L=\ \frac{TC3-TC3min}{TC3max-TC3min}\) (7)
Where: H is “high albedo”, the normalized TC1;
L is “low albedo”, the normalized TC3;
V is “vegetation”, the normalized TC2;
TCi (i=1, 2, and 3) are the first three TC components and
TCimin and TCimax are the minimum and maximum values of the
ith TC components, respectively.
Although the land cover type of the study area can be classified
essentially into impervious, bare and green areas, there is an inherent
mixture of land cover types, particularly between impervious versus bare
land and bare land versus green spaces. As a result, histogram
evaluation was applied to show the threshold value separating the land
cover types. The intersection point in the histograms of the two classes
was taken as the threshold value (Sun et al., 2017). Then, spectral
discrimination index (SDI) was used to measure the degree of
dissociation. The use of SDI degree of separability between the two
selected land cover classes depends on the two variables between and
within group variance. The SDI value greater than one implies that the
two land cover classes are distinguished well, while values less than
one represents poor separability because of large overlaps (Deng and Wu,
2014). SDI is calculated as follows:
SDI =\(\frac{\left|\mu_{i}-\mu_{s}\right|}{\sigma_{i}+\sigma_{s}}\) (8)
Where SDI is separability index value of the selected land covers,μi and μs are average
index values of two land cover classes and σi andσs are standard deviations of a certain index for
the two classes.
2.2.2 Morphometric analysis
A morphometric analysis of the
watershed provides a mathematical measure of the earth’s surface
structure. It also measures the spatial characteristics of the drainage
basin runoff potential, and helps to manage the ground and surface water
reserves. There are several features used to evaluate the watershed
landform arrangement. Farhan et al. (2016) and Pareta and Pareta (2011)
grouped the parameters into network, geometry, area and relief. This
study also used these categories and 20 morphometric measures were
calculated under these categories. Similar to Farhan et al. (2017) and
Meshram and Sharma (2015) the study used PCA to identify the most
important morphometric factors, which are described below. These six
variables were identified based on the PCA component matrices
relationship. In the first factor loading matrix the degree of
association shows that some factors are correlated highly, some
moderately, and others do not correlate at all. Hence, to optimize
correlation the study applied the Varimax rotation to transform the
factor loadings (Fabrigar et al., 1999). The six main morphometric
factors are described below.
Mean Stream Length Ratio (Lurm): One of the important factors for
measuring the watershed surface flow and discharge is the Stream Length
Ratio (Lur). It is the ratio of the mean stream length of a given order
to the mean stream length of the next lower order, and is computed for
each pair of the orders (Horton, 1945). The mean Lur (Lurm) is the
average of all orders of the watershed. Lurm is an important variable
that can be used to examine the hydrological characteristics of the
drainage basin, for example, surface runoff and the hydrological
properties of the underlying bedrock permeability (Farhan and Ayed,
2017).
Mean Bifurcation Ratio (Rbm): bifurcation ratio (Rb) is the ratio
of the number of stream segments of a given order to the number of
segments of the next higher order (Schumn, 1956). The average of the Rb
of each level of stream order in the given watershed is called Rbm. Rbm
is related to the branching pattern of a drainage network and is defined
as the ratio between the total numbers of stream segments of one order
to that of the next higher order in a drainage basin, and an index
indicating the relief and dissections of the landscape. According to
Strahler (1957), the high value of Rb confirms geological and structural
disturbances of the area that restrict runoff. Therefore, high value of
Rb limit the surface runoff responses of the area.
Circularity Ratio (Rƈ) is the ratio of a watershed area to the
equivalent circle area having the same perimeter of the watershed
(Pareta and Pareta, 2011). The value of Rc is ranging between 0,
showing a line, and 1 displays a perfect circle. The higher the circular
character of the basin is, the greater the rapid response of the
watershed after a heavy rainstorm event (Altaf et al., 2013).
Length of overland flow (Lf): is defined as the length of the
runoff of rainwater on the surface of the land before it reaches a
channel of the main river (Prasad et al., 2008). The variation ofLf is related to variation in slope, lithology, land cover,
rainfall intensity and infiltration capacity (Al-Saady et al., 2016). A
high Lf value of a watershed denotes a high vulnerability to
flash floods.
Gradient ratio (Rg) is the ratio of basin relief and basin
length, and measures the overall slope of the basin. Hence it is defined
as the elevation difference between the source and the mouth of the
course of the river channel in a drainage basin divided by the length of
the longest channel. It computes the channel slope and helps to evaluate
the runoff volume (Sreedevi et al., 2004). The higher the value reflects
the greater exposure to flash flooding.
Dissection index (Dis): the ratio of relative relief and absolute
relief of the basin (Farhan et al., 2016). The value always ranges
between zero for complete absence of dissection and the prevalence of
plane topography, and one for uncommon instances, such as vertical cliff
topography at the seashore, or a vertical escarpment (Pareta and Pareta,
2010). Dis of different blocks (upper, middle and lower course)
within the basin correlate with flood height and flood stagnation period
of the basin. Accordingly, flash flood occurrence should be expected at
areas with high dissection index values, that is to say, high potential
energy (Vara, 2018).
2.2.3. Multi-criteria fuzzy overlay
analysis
To prioritize areas by flash flood vulnerability level, the research
employed a multi-criteria decision-making process. The model considers
both the land cover and morphometric factors. As it is shown in fig 2,
eight different factor maps of the watershed area were used to map the
flash flood vulnerability. Two of these maps are the land cover maps
that highlight the impervious and vegetation cover areas. The other six
factor maps were produced using the micro watershed morphometric
characteristics computed by Lurm, Rbm, Rg, Dis, Lf and Rc. Although
different methods were applied to standardize the multi-criteria
evaluation, this study used fuzzy logic, which provides a broader range
of membership functions than other methods of standardization (Myint and
Wang, 2006). Ahmed et al. (2017) applied fuzzy logics to prioritize
sub-watersheds by their morphometric characteristics. In a traditional
overlay analysis, the results are transformed into 0 and 1 binomial
functions, but the fuzzy membership function transforms the input raster
into a 0 to 1 scale. This transformation indicates the strength of a
membership in a set, based on a specified fuzzification algorithm. Thus
1 represents full membership and 0 infers the complete exclusion from
the membership of the fuzzy set (Esri, 2015). However, the varying set
of membership ranges between 0 and 1 (Jiang and Eastman, 2000). The
Arc-GIS fuzzy environment specifies the algorithm used in fuzzification
of the input to set the membership the environment has about seven types
of membership function (Gaussian, Small, Large, Near calculates,
Ms-large, Ms-small, Leaner).
This study also applied fuzzy overlay analysis for flash flood
vulnerability mapping using the land cover and morphometric values of
the area. Figure 2 illustrates the method and organization of the model.
Based on related literature, experts consultation and researchers
personal knowledge of the area, the membership functions of the land
cover and morphometric factors were determined. After the factors were
selected and the fuzzy membership functions were assigned, the model
indicated how these factors interact by choosing fuzzy-logic operators.
These operators are mainly known as AND / OR operators that show the
minimum and maximum possible suitability of the factors, respectively
(Jiang and Eastman, 2000; Mohammed et al., 2017)
First, the BCI and NDVI based land cover maps were classified. Then, for
impervious surfaces the MS-large membership function was used in the
model, which helps to incorporate large values in high membership. For
the vegetation cover the MS-small membership function was used in the
model that allows to consider reversal membership. This means that flash
flood is getting higher in areas of higher impervious surfaces and lower
vegetation cover. Besides, the fuzzy overlay of the morphometric factors
was executed step by step, and the broader categories of these factors
(network, relief, area and geometry) were overlaid independently, before
the model executed the overlay of the whole categories of the
morphometric parameters together. Consequently, the final flash flood
vulnerability map was produced by making an overlay analysis using the
morphometric and the land cover based vulnerability map (see figure 2).
2.2.4. Riparian buffer zone
evaluation
The effect of land cover and the flash flood vulnerability was evaluated
in each strip of buffering distance. This study considered the MUDC’s
(2012) 15m buffer distance on either side of the river, and other
countries’ experiences which have more detailed riparian buffering
tools. In this regard, the Montgomery County Planning Commission (2012)
considered 7.5m as a shorter distance, 23m as a medium and 91m as a
longer buffering distance. Therefore in this study the buffer strip
widths of 15m, 30 m and 90m were evaluated. Thus, the degree of
imperviousness, vegetation cover and flash flood vulnerability was
quantified for each buffer strip width. This helps to measure the
watershed and riparian landscape status, and to propose different
intervention mechanisms.
3.
Results
3.1. Land cover extraction
Flash flood vulnerability mapping of the Kebena watershed used the land
cover and the micro-watershed morphometric feature evaluation. The land
cover assessment classified the impervious surface from the calculated
BCI values (fig 3a and c), and the vegetation cover using the NDVI
values (fig 3b and d). It is, however, difficult to separate impervious
surface, bare land and vegetated land due to spectral mixing. But, the
histograms (fig 4) show a reasonably good separability between bare and
impervious cover, based on the value of BCI, while the NDVI histogram
shows a high separation capability between bare and vegetated surfaces.
As shown in figure 4a, in the BCI histogram, impervious surface has its
highest point around 0.35 whereas the bare land has a peak around the
index value of 0.0, with a crossing point at 0.12. On the other hand, in
the NDVI histogram, vegetation has the highest point at about 0.4 and
bare land has a peak around 0.09 with the crossing point at 0.17 (fig
4b). Based on these separation points, the impervious and vegetation
cover of the watershed was extracted with a good precision as shown in
figures 3c and 3d. The separability of the land cover classes was at a
best level in both cases as it is confirmed by the SDI value. The BCI
separability of impervious versus bare land estimated about 1.6.
Similarly, the NDVI based vegetation cover versus bare land dissociation
level appears as high as 2.1.
3.2. Morphometric analysis
The morphometric analysis of the Kebena watershed was conducted by
subdividing the watershed into 29 micro-watersheds. Each micro-watershed
was identified by continuous ID number. There are several morphometric
parameters that may broadly be categorized into four classes: ‘network’,
‘areal’, ‘geometry’ and ‘relief’. As it is shown in table 1, of these,
micro-watershed numbered 9 has the largest area and the highest number
of stream segments. The longest perimeter was recorded for
micro-watershed 18 followed by 9. Micro-watershed 15 has a relatively
longest stream length next to the micro-watershed 9 and 16. On the other
hand, the micro-watershed 17 has the shortest perimeter, smallest area
and number of stream segment. fig 5 illustrates the micro-watershed area
and the streams with their orders.
Initially 20 morphometric factors were calculated, but only six were
used for the morphometric analysis. Fourteen factors were discarded
after conducting the PCA analysis. The remaining six factors are Lurm,
Rbm, Lg, Rc, Diss and Rg.
3.3. Flash flood vulnerability
mapping of Kebena
Watershed
The final flash flood vulnerability map (fig 6) was developed by the
fuzzy overlay modeling technique. In fact, the extracted morphometric
factors represented the broader classes of ‘network’, ‘geometry’, ‘area’
and ‘relief’. When the value of the extracted morphometric factors
(Lurm, Rbm, Lg, Rc, Diss and Rg) is high, the model sets a high priority
to flash flood vulnerability. This means that the flash flood is getting
higher as the value of the selected morphometric factor is greater. The
land cover factor considered both the NDVI and BCI indices to identify
the land cover classes. The model again sets high vulnerability with
increasing impervious and decreasing vegetation covers. Figure 6 reveals
that 969.8 ha (about 19%) of the watershed area is highly vulnerable to
flash flood, 2092.1 ha (about 41.5%) of the area is moderately
vulnerable to flash flood, and 1980.5 ha (about 39.3%) has a low
vulnerability.
Historical records of the flood incidences in micro
watersheds during the last ten years were collected by the Addis Ababa
fire and emergency preparedness office till 2017. The GPS locations of
the locations with recurrent flash floods indicate that four of them are
located in our study area (indicated by yellow triangles in fig 6).
Comparison of the modeled flash flood risk and the observed flood
incidences shows a good relation. Out of the four spots three of them
are lying on the very high vulnerable area, while the fourth location
was classified as having a high flash flood risk.
The Addis Ababa fire and emergency preparedness office have
collected the flood data across the city when incidents damage human
life or property. Although the extent of the flash flood varies from
time to time, it creates a problem in any rainy seasons of the country.
According to the office expert the flash flooding in this study area,
which is caused by the seasonal heavy rain, disrupts pedestrians and
vehicle movement. Since the area constitutes high built-up and rugged
sloped terrain the city administration has not paid much attention to
this problem.
3.4. Riparian buffering and the
status of its landscape functioning
The riparian buffer assessment considered 15m, 30m and 90m buffering
distances. The study measured the extent of imperviousness, vegetation
abundance and the flash flood vulnerability, in the stripes of buffer
distances. The pattern of impervious and vegetation cover in each
buffering distance shows the extent of the riparian landscape
functioning.
Having this in mind the extents of the given land covers were measured.
With a 15m buffering width, 21.0 ha (about 32%) of the area was covered
by vegetation, and 29.0 ha (44%) of the area was impervious. With the
30m buffering distance vegetation cover and impervious surface occupy
about 20.7 hectare (32%) and 28.3 hectare (44%), respectively.
Finally, when the 90 m buffer widths are considered, 82.0 hectare (32%)
of the land is covered by vegetation and 106.1 hectare (42%) of it was
covered by impervious surface. In all levels of buffering, the
percentage share of impervious surface cover is higher than the
vegetation cover (see table 2). This shows that the riparian buffering
area is dominated by built-up zones, which potentially increases the
flash flood risk.
Concerning flash flood vulnerability, within a 15m buffered distance 7
hectares (about 10.7%) of an area was highly vulnerable. 7.6 hectares
(about 11.9%) of land of the 30m buffering was under highly vulnerable
and 40 hectares (16%) of land of the 90m buffering distance is also
under highly vulnerable zone (see table. 3).
4.
Discussion
4.1. Flash flood vulnerability
mapping
Researches have been made Flash flood hazard assessment using the
different aspects of the morphometric parameters (Elkhrachy, 2015; and
Angilieri, 2010). This research integrated the land cover assessment,
morphometric analysis and the final flash flood vulnerability map which
depicted 969.8ha of land as highly vulnerable area. It is significant on
the southeastern and southwestern part where the land cover is dominated
by impervious and northeast part where high, rugged terrain and depleted
vegetation cover area of the watershed.
The fuzzy overlay method proves to be an effective technique in the area
where sufficient flash flood records were not available. This method is
helpful to identify flash flood prone zones of the watershed. Historical
flash flood records partly match with our analysis results, which
indicates that the applied methods are effective and can be used to
prioritize areas for intervention measures.
4.2. The status of the riparian
environment
The integrated aspect of the watershed land cover and morphometry
controls the watershed and riparian landscape status. The stream
ecosystem of the study area was highly degraded and hardly provides the
expected services. In all buffering distances the area covered by
impervious surface is greater than the cover of vegetated surface. The
urban planning guideline of 15m buffering distance is also seriously
violated and continuously occupied by built-up, covering about 31.7
hectares of land, which may represent about 1585 housing plots. Riparian
vegetated zones have different advantages like controlling surface
hydraulic retention and the stream nutrient up-taking time (Weigelhofer
et al., 2012), to monitor urban nonpoint source pollution (Allison et
al., 2006) and to keep up species richness (Spackman and Hughes, 1994).
It also helps in maximizing cultural services for local low income
urbanites (Vollmer et al., 2015). So different levels of riparian
buffering should be one of the important conservation planning and
management strategies (Marczak et al., 2010). However, further studies
have to be made in the riparian buffering zones less than 15m to support
specific stream level analysis and design recommendation.
Measures to control flash flooding
and maintain the watershed and riparian
landscape
The analyses results presented in the previous sections, show the flood
prone areas of the watershed and the status of the riparian environment.
Other studies also indicated that the present and future conditions of
the flood hazard are more exacerbated in Addis Ababa and Ethiopia as a
whole. For instance, the Intergovernmental Panel on Climate Change
(IPCC, 2013) scenario and the current climate variability report of the
National Adaptation Program of Action (NAPA, 2007) predict an increasing
trend of rainfall and more flooding in the country. It is, therefore
necessary to alleviate vulnerability to flash flooding by implementing
measures that enhance infiltration of rain and reduce surface runoff.
Maintaining the watershed green spaces and controlling the impervious
surface growth is an important flash flood mitigation mechanism. In
fact, it is part of the natural flood management approach that works
with natural hydrological and morphological processes, features and
characteristics as compared to traditional engineering and structural
approach (Saiff, 2011). This would be a more effective and
cost-efficient mechanism in most developing countries for urban and
suburban watersheds conservation management. Cruijsen (2015), for
instance, suggested public spaces, parks, water squares and green
squares for water retention, open water and urban farming as a best fit
design to confront the flash flood problem. However, it is hardly
possible in most African cities since these the competition for space is
huge, especially from commercial business and residential land
construction, and because of several other reasons (Burak et al., 2017;
Kimengsi and Fogwe, 2017). This is also true in Ethiopia urban centers,
particularly in Addis Ababa. If it would be somehow possible to maintain
the green spaces at least along the riverine landscape it could help to
reduce the flash flood problem. Nevertheless, as urbanization gets
strong, some marginalized areas and this riparian vegetation cover also
becomes occupied by impervious surface. According to our analysis, the
share of vegetation cover is already lower than the proportion of
impervious surface in the Kebena watershed. Therefore, maintaining the
remaining riparian vegetation is an important way to control the flash
flood damage, which is more sustainable and cost effective methods to
conserve the watershed.
The riparian buffering is also helpful to take multistep intervention to
confront the existing and upcoming challenges. Accordingly, stripes of
buffering distances help to take a choice of intervention measures at
different part of the stream block. For example, removal or relocation
of people who were inhabited on flash flood vulnerable area (969.8ha) is
difficult. It is also hardly possible to remove impervious surface even
in a15m buffering distance, which is taken as the national standard
since it is challenging to relocate this large number of inhabitants.
However, the impervious surfaces that lie in a flash flood vulnerable
areas requires the city administration’s special consideration because
of the following two reasons. Firstly, peoples who are living in this
area highly exposed to heavy rainfall and flash flooding event that
damage their house itself and take human life too. Secondly, it occupies
2.8 hectares of land, which may represent nearly 141 housing units,
which may somehow be modest to relocate from this hazardous area. In
fact, the present and upcoming intensity of urbanization and built-up
growth continued to occupy the remaining green spaces and bare land,
thus, it is necessary to control and maintain the existing green spaces
up to the maximum buffering distance (90m). This helps to gain the
benefits of green spaces like flood slowing function and other stream
ecosystem services, and it enables to compensate the existing impervious
area impact. Inspire of the fact that afforestation approach has some
argumentative issues (Calder and Aylward, 2009), it is possible
to rehabilitate the remaining bare lands up to the maximum buffering
distances to minimize flooding and control the consequent damage.
Therefore, stripes of buffering distances are useful planning
instruments to take multistep intervention measures to conserve urban
and suburban watershed. Though there is strong competition and land use
tradeoff over space in the urban landscape, it is possible to maintain
riparian green spaces as it is helpful not only to upgrade the riverine
landscape but also alleviate flash flood vulnerability over the
watershed. Furthermore, as it is an urban landscape it is impossible to
prohibit the impervious growth. However, all the urban planning and
design works and the grey infrastructure development have to enhance
pervious structures and encompasses green infrastructures.
Conclusion
This research evaluates the urban and suburban watershed land cover and
morphometry as the main factors of the watershed hydrology, and its
riparian environment functioning. The study identified 29
micro-watershed and analyzed 20 morphometric parameters, then the PCA
measure reduced the variables in to six. These are Lurm, Rbm, Lg, Rc,
Diss and Rg. The fuzzy multi-criteria overlay analysis depicted 969
hectares of flash flood vulnerable area. The 15, 30 and 90m riparian
buffering distances were delineated and the cover of the impervious was
greater than the vegetation cover and large proportion of the riparian
buffering area are also vulnerable to flash flood. Within the national
urban planning minimum buffering standard about three hectares of
impervious was found on flash flood vulnerable areas.
Generally, Kebena watershed environment is significantly degraded and
highly exposed to a flash flood that is mainly caused by the rapid
expansion of urban built-up, degraded vegetation cover and the upland
rugged terrain of the area. Besides, this rapid growth of the impervious
surface and the continuous degradation of the vegetation cover
distressed the status of the watershed and the riparian environment
making the intended landscape function weak. The study, therefore
concludes that geospatial modeling technique has a vital role to
generate integrated, well developed urban flash flood data and hazard
controlling approach in areas where continues data recording of events
were not accustomed, like in Ethiopia. Such a research result, thus, is
important to prioritize areas for immediate intervention like drawing
early warning and controlling system. At the same time stripes of
buffering distances are taken as an important planning tool, to monitor
riparian green spaces, control flash flood vulnerability and maintain
the riverine ecosystem services. As a recommendations, the grey
infrastructure including roadways and city drainage system planning and
design should integrate the green infrastructure and other perviousness
enhancing structures. By using stripes of the riparian buffering
distances, it is possible to devise measures to maintain the stream
ecosystem based on the watershed geomorphic, hydraulic and environmental
characteristics. It is also helpful to take an important decisions on
relocating vulnerable built-up, preserving the existing green space and
rehabilitating some degraded spaces.
Replicating these methods of quantifying and mapping other watersheds of
the city of Addis Ababa and the surrounding urban region is one of the
major areas of concern for future research. The Work can strengthen
again by using a very high-resolution grid information to integrate
hydro-metrological analysis.. Moreover, the research shall quantify and
measure the level of ecosystem services that can produced in the
riparian landscape.
Author Contributions: A.M. was primarily responsible for the
original idea, experimental design, and did the experiments; H.W.
provided helpful suggestions; A.M. wrote the manuscript; H.W. and G.S.
provided ideas to improve the quality of the manuscript in the writing
procedure; A.M., H.W. and G.S. revised the manuscript.
Conflict of interest : No potential conflict of interest was
reported by the authors
Data Availability Statement: The data that supports the
findings of this study are available in the supplementary material of
this article
Acknowledgement: We gratefully acknowledge the financial
support from Addis Ababa University Office of the Director of Research
under the thematic research title “Resource efficiency, environmental
quality and sustainability of urban areas in Ethiopia”, Grant no.
TR/11/2013.
Reference
Ahmed, R., Sajjad, H., & Husain, I. (2017). Morphometric
Parameters-Based Prioritization of Sub- watersheds Using Fuzzy
Analytical Hierarchy Process : A Case Study of Lower Barpani Watershed
, India. Natural Resources Research .
https://doi.org/10.1007/s11053-017-9337-4
Allison, B., & S. M. Fatula and D.p. Wolanski. (2006) Evaluating
Riparian Buffers For Nonpoint Source Pollution Control In An Urban
Setting Using The Riparian Ecosystem Management Model, Remm. Hydrology
and Management of Forested Wetlands, Proceedings of the International
Conference, April 8-12, 2006, New Bern, North Carolina.
doi:10.13031/2013.20307
Altaf, F., Meraj, G., & Romshoo, S. A. (2013). Morphometric Analysis to
Infer Hydrological Behaviour of Lidder Watershed , Western Himalaya ,
India. Hindawi Publishing Corporation Geography Journal ,2013 , 1–14. https://doi.org/org/10.1155/2013/178021
Baig, H. M. A., Zhang, L., Shuai, T., & Tong, Q. (2017). Derivation of
a tasselled cap transformation based on Landsat 8 at-satellite
reflectance. Remote Sensing Letters , 5 (5), 423–431.
https://doi.org/10.1080/2150704X.2014.915434
Bhatti, S. S., & Tripathi, N. K. (2014). GIScience & Remote Sensing
Built-up area extraction using Landsat 8 OLI imagery. GIScience &
Remote Sensing , 51 (4), 37–41.
https://doi.org/10.1080/15481603.2014.939539
Bosch, J. M., & Hewlett, J. D. (1982). A review of catchment
experiments to determine the effect of vegetation changes on water yield
and evapotranspiration. Journal of Hydrology , 55 , 3–23.
Retrieved from http://coweeta.uga.edu/publications/2117.pdf
Burak G¨uneralp, Shuaib Lwasa, Hillary Masundire, S. P. and K. C. S.
(2017). Urbanization in Africa : challenges and opportunities for
conservation OPEN ACCESS Urbanization in Africa : challenges and
opportunities for conservation. Environmental Research Letters .
Retrieved from
https://iopscience.iop.org/article/10.1088/1748-9326/aa94fe/pdf
Cruijsen, A. (2015). Design opportunities for flash flood
reduction by improving the quality of the living environment: A Hoboken
City case study of environmental driven urban water management . Delft
University of Technology.
Dagnachew, A. B. (2011). Road and urban storm water drainage network
integration in Addis Ababa : Addis Ketema Sub-city. Journal of
Engineering and Technology Research , 3 (7), 217–225. Retrieved
from
http://www.academicjournals.org/app/webroot/article/article1380190860_Belete.pdf
Deng, C., & Wu, C. (2012). BCI : A biophysical composition index for
remote sensing of urban environments. Remote Sensing of
Environment , 127 , 247–259.
https://doi.org/10.1016/j.rse.2012.09.009
Elkhrachy, I. (2015). Flash Flood Hazard Mapping Using Satellite Images
and GIS Tools : A case study of Najran City , Kingdom of Saudi Arabia (
KSA ). The Egyptian Journal of Remote Sensing and Space Sciences ,18 (2), 261–278. https://doi.org/10.1016/j.ejrs.2015.06.007
Engelhardt, B. M., Weisberg, P. J., & Chambers, J. C. (2011).
Influences of watershed geomorphology on extent and composition of
riparian vegetation, 1–13.
https://doi.org/10.1111/j.1654-1103.2011.01328.x
Fabrigar, L. R., Wegener, D. T., MacCallum, R. C., & Erin J. Strahan.
(1999). Evaluating the Use of Exploratory Factor Analysis in
Psychological Research. Psychological Methods , 4 (3),
272–299.
Farhan, Y., Anaba, O., & Salim, A. (2016). Morphometric Analysis and
Flash Floods Assessment for Drainage Basins of the Ras En Naqb Area ,
South Jordan Using GIS. Journal of Geoscience and Environment
Protection , 4 , 9–33. Retrieved from
http://www.scirp.org/journal/gep
http://dx.doi.org/10.4236/gep.2016.46002%0AMorphometric
Farhan, Y., Anbar, A., Al-Shaikh, N., & Mousa, R. (2017).
Prioritization of Semi-Arid Agricultural Watershed Using Morphometric
and Principal Component Analysis , Remote Sensing , and GIS Techniques ,
the Zerqa River Watershed ,. Agricultural Sciences , 8 ,
113–148. https://doi.org/10.4236/as.2017.81009
Farhan, Y., & Ayed, A. (2017). Assessment of Flash-Flood Hazard in Arid
Watersheds of Jordan. Journal of Geographic Information System ,9 , 717–751. https://doi.org/10.4236/jgis.2017.96045
Gholami, V., Saravi, M. M., & Ahmadi, H. (2010). Effects of impervious
surfaces and urban development on runoff generation and flood hazard in
the Hajighoshan watershed. Caspian J. Env. Sci. , 8 (1),
1–12. Retrieved from
https://cjes.guilan.ac.ir/article_1031_877fcf2fe2bf92d3689e6be79b500ebb.pdf
Groffman, P. M., Bain, D. J., Band, L. E., Belt, K. T., Brush, G. S., &
Grove, J. M. (2003). Down by the riverside : urban riparian ecology.Frontiers in Ecology and the Environment , 1 (16), 315–321.
https://doi.org/https://doi.org/170.144.166.92
Harinath, V., & Raghu, V. (2013). Morphometric Analysis using Arc GIS
Techniques A Case Study of Dharurvagu , South Eastern Part of Kurnool
District , Andhra Pradesh , India. International Journal of
Science and Research (IJSR) , 2 (1), 182–187. Retrieved from
https://www.ijsr.net/archive/v2i1/IJSR13010155.pdf
Horton, R. E. (1945) Erosion development of streams and the drainage
basins; Hydrophysical approach to quantitative morphology. Geol Soc
America Bull, 56(3), 275. doi:10.1130/0016
7606(1945)56[275:edosat]2.0.co;2
Javed, A., Yousuf, M., & Rizwan, K. (2009). Prioritization of
Sub-watersheds based on Morphometric and Land Use Analysis using Remote
Sensing and GIS Techniques. J. Indian Soc. Remote Sens ,37 (2), 261–274. https://doi.org/DOI: 10.1007/s12524-009-0016-8
Kimengsi, J. N., & Fogwe, Z. N. (2017). Urban Green Development
Planning Opportunities and Challenges in Sub-Saharan Africa : Lessons
from Bamenda City, Cameroon. International Journal of Global
Sustainability , 1 (1), 1–17.
https://doi.org/10.5296/ijgs.v1i1.11440
MARCZAK, L. B., SAKAMAKI, T., TURVEY, S. L., DEGUISE, I., WOOD, S. L.
R., & RICHARDSON, J. S. (2010). Are forested buffers an effective
conservation strategy for riparian fauna ? An assessment using
meta-analysis. Ecological Applications , 20 (1), 126–134.
https://doi.org/https://doi.org/10.1890/08-2064.1
Meshram, S. G., & Sharma, S. K. (2015). Prioritization of watershed
through morphometric parameters : a PCA-based approach. Applied
Water Science . https://doi.org/10.1007/s13201-015-0332-9
Pareta, K., Pareta, U., & Decisions, S. (2011). Quantitative
Morphometric Analysis of a Watershed of Yamuna Basin , India using ASTER
( DEM ) Data and GIS, 2 (1), 248–269.
Patel, D. P., Gajjar, C. A., & Srivastava, P. K. (2012). Prioritization
of Malesari mini-watersheds through morphometric analysis : a remote
sensing and GIS perspective. Environ Earth Sci , 69 (8).
https://doi.org/10.1007/s12665-012-2086-0
Perucca, L. P., & Angilieri, Y. E. (2011). Morphometric
characterization of del Molle Basin applied to the evaluation of fl ash
fl oods hazard , Iglesia Department , San Juan , Argentina.Quaternary International , 233 (1), 81–86.
https://doi.org/10.1016/j.quaint.2010.08.007
Piyoosh, A. K., & Ghosh, S. K. (2017a). Development of a modified
bare-soil and urban index for Landsat 8 satellite data. Geocarto
International , 33 (4), 1–20.
https://doi.org/10.1080/10106049.2016.1273401
Piyoosh, A. K., & Ghosh, S. K. (2017b). Semi-automatic mapping of
anthropogenic impervious surfaces in an urban / suburban area using
Landsat 8 satellite data. GIScience & Remote Sensing ,54 (4), 1–24. https://doi.org/10.1080/15481603.2017.1282414
Rosenmeier, M. F., Hodell, D. A., Brenner, M., Curtis, J. H., Martin, J.
B., Flavio, S., … Guilderson, T. P. (2002). Influence of
vegetation change on watershed hydrology : implications for
paleoclimatic interpretation of lacustrine δ 18 O records. Journal
of Paleolimnology , 27 (1), 117–131. Retrieved from
https://link.springer.com/article/10.1023/A:1013535930777
Sahoo, S. N., & Sreeja, P. (2012). Application of Geospatial
Technologies to Determine Imperviousness in Peri-Urban Areas,2 (4), 47–51. Retrieved from
https://ia800306.us.archive.org/8/items/IJRSA10068/IJRSA10068.pdf
Spackman, S. C., & Hughes, J. W. (1995). FOR BIOLOGICAL CONSERVATION :
SPECIES RICHNESS A N D DISTRIBUTION ALONG MID-ORDER STREAMS IN.Biological Conservation , 71 , 325–332.
https://doi.org/doi:10.1016/0006-3207(94)00055-u
Sreedevi, P. D., K. Subrahmanyam, & Ahmed, S. (2005). The significance
of morphometric analysis for obtaining groundwater potential zones in a
structurally controlled terrain. Environmental Geology ,47 (3), 412–420. https://doi.org/10.1007/s00254-004-1166-1
Srivastava, O. S., Denis, D. M., Srivastava, S. K., & Kumar, N. (2014).
Morphometric analysis of a Semi Urban Watershed , trans Yamuna ,
draining at Allahabad using Cartosat ( DEM ) data and GIS. The
International Journal Of Engineering And Science (IJES) , 3 (11),
71–79. Retrieved from
http://www.theijes.com/papers/v3-i11/Version-2/I031102071079.pdf
STRAHLER, A. N. . (1957). Quantitative Analysis of Watershed
Geomorphology. American Geophysical Union , 38 (6),
913–920. https://doi.org/doi:10.1029/tr038i006p00913
Strahler, A. N. (1964) Quantitative geomorphology of drainage basin and
channel networks. Handbook of applied hydrology.
Sun, Z., Wang, C., Guo, H., & Shang, R. (2017). A Modified Normalized
Difference Impervious Surface Index ( MNDISI ) for Automatic Urban
Mapping from Landsat Imagery. Remote Sensing , 9 (942),
1–18. https://doi.org/10.3390/rs9090942
Tamiru, A. (2001). The impact of uncontrolled waste disposal on surface
water quality in Addis Ababa, Ethiopia. SINET: Ethiopian. Ethiop.
J. Sci., 24 (1), 93–104. Retrieved from
https://www.ajol.info/index.php/sinet/article/view/18177/17157
Vara, B. T. (2018). GIS-based evaluation of topography with regard
to flash floods . Technical University Munich. Retrieved from
https://www.hydrologie.bgu.tum.de/fileadmin/w00bpg/www/Christiane1/Lehre/Studentische_arbeiten/fertige_Arbeiten/S87_Kaiser_Torres_GIS-based_evaluation_of_topography_with_regard_to_flash.pdf
Vollmer, D., Prescott, M. F., Padawangi, R., Girot, C., & Grêt-regamey,
A. (2015). Understanding the value of urban riparian corridors:
Considerations in planning for cultural services along an Indonesian
river. Landscape and Urban Planning , 138 , 1–10.
https://doi.org/10.1016/j.landurbplan.2015.02.011
Weigelhofer, G., Fuchsberger, J., Teufl, B., Welti, N., & Hein, T.
(2012). Eff ects of Riparian Forest Buff ers on In-Stream Nutrient
Retention in Agricultural Catchments. Journal of Environmental
Quality , 41 (2), 373–379. https://doi.org/10.2134/jeq2010.0436
Xu, H. (2010). Analysis of Impervious Surface and its Impact on Urban
Heat Environment using the Normalized Difference Impervious Surface
Index ( NDISI ), 76 (5), 557–565.
https://doi.org/doi:10.14358/pers.76.5.557
Youssef, A. M., Pradhan, B., & Hassan, A. M. (2010). Flash flood risk
estimation along the St . Katherine road , southern Sinai , Egypt using
GIS based morphometry and … Environmental Earth Sciences ,62 (3), 611–623. https://doi.org/10.1007/s12665-010-0551-1