Recent urban landscape vegetation surveys conducted in many cities in China identified numerous plant nutrient deficiencies, especially in newly developed cities. Soil nutrients and soil nutrient management in the cities of Hubei province have not received adequate attention to date. The aims of this study were to characterize the available nutrients of urban soils from nine cities in Hubei province, China, and to assess how soil nutrient status is related to land use type and topography. Soil nutrients were measured in 405 sites from 1,215 soil samples collected from four land use types (park, institutional [including government building grounds, municipal party grounds, university grounds, and garden city institutes], residential, and roadside verges) and three topographies (mountainous [142–425 m a.s.l], hilly [66–112 m a.s.l], and plain [26–30 m a.s.l]). Chemical analyses showed that urban soils in Hubei had high pH and lower soil organic matter, available nitrogen (N), available phosphorus (P), and available boron (B) concentrations than natural soils. Nutrient concentrations were significantly different among land use types, with the roadside and residential areas having greater concentrations of calcium (Ca), sulfur (S), copper (Cu), manganese (Mn), and zinc (Zn) that were not deficient against the recommended ranges. Topographic comparisons showed statistically significant effects for 8 of the 11 chemical variables (p < 0.05). Concentrations of N, Ca, Mg, S, Cu, and Mn in plain cities were greater than those in mountainous cities and show a negative correlation with city elevation. These results provide data on urban soils characteristics in land use types and topography, and deliver significant information for city planners and policy makers.
Citation: Li Z-g, Zhang G-s, Liu Y, Wan K-y, Zhang R-h, Chen F (2013) Soil Nutrient Assessment for Urban Ecosystems in Hubei, China. PLoS ONE 8(9): e75856. https://doi.org/10.1371/journal.pone.0075856
Editor: Peter Shaw, Roehampton university, United Kingdom
Received: March 12, 2013; Accepted: August 23, 2013; Published: September 27, 2013
Copyright: © 2013 Li et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Funding: The study was supported by the National Key Technology R&D Program (2012BAD15B01), the National Natural Science Foundation of China (31100386), and the Cooperated Program with the International Plant Nutrition Institute (IPNI-HB-33). The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
Urbanization has been an especially rapid process in developing countries such as China. By 2050, more than half of the world’s population will probably reside in cities, and almost all population growth will be in cities in developing countries . Consequently, the expansion of urban construction will intensify as will the potential for emission of greenhouse gases .
Urban greenland is an important and essential component of urban construction that not only filters harmful substances, improves micro-climates, and reduces noise, but also improves the aesthetic value of the city, propagates progressive city culture, and reduces greenhouse gas emissions . Many cities extend greenland areas within their limited urban space and improve the quality of urban greenland areas to build ‘green’ or ‘low-carbon’ cities. However, after extensive ‘green city’ construction, it has been found that garden plants fail to form the expected ‘garden’ landscape, and some plants die from wilt disease a few years later after transplanting . These problems have become the main limiting factor for urban landscape construction in many cities in China.
Poor soil condition may be one of the main reasons for unhealthy urban garden plants . Urban soils are often dramatically altered by human activities such as construction, compaction, degradation, land filling, and mixing. Topsoil is usually filled with stones, construction rubble, bricks, and other building materials, which likely contribute to poor soil fertility  and are not within the recommended nutrient requirements range [7-9]. However, to date there is little consensus among researchers on this issue. In Hong Kong, Jim  found that two-thirds of sampled soils had an elevated pH up to 8.68 and low organic carbon at 0.88%. Zhang et al.  reported that available nitrogen (N) (26.5 mg kg-1) and available phosphorus (P) (19.7 mg kg-1) in urban soils were significantly lower than the recommended range (50–100 mg kg-1 for N and 30–60 mg kg-1 for P) of non-urban soils [7-9]. White and McDonnell  also found that the net N mineralization rate in urban forest soils in New York City was significantly lower than that in rural forest soils. In contrast, Pouyat et al.  found, although a subset of soil chemical and physical properties varied considerably among different land use and cover types in Baltimore, MD, USA, most sites had sufficient available soil nutrients to support plant growth.
Land use and topography are important factors affecting soil nutrients , but knowledge on these factors in urban areas is limited. The aim of our study was to characterize the available nutrients of urban soils from nine cities in Hubei province, China, and to assess how soil nutrient status was related to land use type and topography. It was hypothesized that the status of available nutrients in urban soil would vary significantly with land use and topography. These baseline findings could provide practical information for making better urban soil management strategies in Chinese cities.
Materials and Methods
This study has been approved by the City Planning Office Construction Department of Hubei province, which takes care of the planning of urban construction in Hubei province. All the data in this study can be published and shared.
Hubei Province (Latitude 29° 05’–33°20′, Longitude 108° 21′–116°07′) is located in central China, with an area of 185,900 km2 and a population of 61.7 million in 2010 . Hubei has always been the waterway and overland transportation hub of central China . Landforms in this region are a diverse arrangement of mountains, hills, and plains. Mountainous area occupies ~55.5% of the total provincial area, with 24.5% classed as hilly, and 20% classed as plains . Average annual rainfall is 800–1600 mm and average annual temperature is 15–17°C. Because of these different landforms, there are large differences in temperature and rainfall between the mountainous and plain areas with plains usually having more rain and higher temperatures in summer .
Nine cities in Hubei, including three mountainous cities (Yichang, Shiyan and Enshi, with an average elevation of 276 m); three hilly cities (Jingmen, Suizhou and Xiangfan, with an average elevation of 83 m); and three plain cities (Jingzhou, Wuhan and Xiaogan, with an average elevation of 28 m) were selected (Table 1). Most of the sampled soils at each site were yellow-brown, derived from water-transported (alluvium) or wind-blown (loess) material, yet some have been formed by in-situ weathering of rocks (carbonate rocks and clastic rocks including shale, silt limestone, and pelitic siltstone). The urban greenland of each city was classified into four land use categories (Table 2) based on satellite remote-sensing imagery (10 August, 2010). The park areas were the least disturbed with a natural soil material but a small amount of building rubble incorporated. The soil at the institutional areas was moderately disturbed with remnants of building rubble and natural substrates and typical managed vegetation. By contrast, the residential areas were more heavily disturbed with additions of building rubble and domestic sewage. The soil in the roadside was also the most heavily disturbed and often compacted by humans and vehicles. The mixed substrates, with transferred natural substrates, remnants of building rubble, pitch, and domestic waste, were the parent material for soil development at roadside sites.
|Site||Landforms||Elevation (m)||Average annual precipitation (mm)||Average annual temperature (°C)||Soil types||Population size (thousand)||City area (km2)||Soil sampling numbers|
|Shiyan||Mountain||263||800||13.1-16||Yellow brown soil||310||62||42|
|Enshi||Mountain||425||1000-1200||13.4-16.3||Yellow brown soil||800||80||39|
|Yichang||Mountain||142||992||13.1-18||Yellow brown soil||557||92||45|
|Suizhou||Hill||66||865-1070||15.5||Yellow brown soil||650||43||39|
|Xiangfan||Hill||71||878||15.1-16.9||Yellow brown soil||2230||107||42|
|Jingzhou||Plain||30||1100-1300||15.9-16.6||Yellow brown soil||1140||66||42|
|Wuhan||Plain||27||1100||15.8-17.5||Yellow brown soil||5170||500||78|
|Land use type||Number of samples||Parent material||Vegetation||Management||Disturbance degree |
|Park||87||Natural substrates, small building rubble||Unmanaged and managed trees, shrubs, herbaceous||Irrigation, no fertilizer||Little disturbance|
|Institution||131||Transferred natural mixed substrates, building rubble, bricks, cement||Managed trees, shrubs, herbaceous||Irrigation, no fertilization, human trampling||Moderate disturbance|
|Residential||98||Transferred natural mixed substrates, building rubble, bricks, cement, domestic garbage||Managed trees, shrubs, herbaceous||Irrigation, no fertilizer, human trampling, pet feces, sewage||Heavy disturbance|
|Roadside||95||Transferred natural mixed substrates, building rubble, bricks, cement, domestic waste, plastics pitch||Managed trees, shrubs, herbaceous||Irrigation, no fertilizer, human trampling, mechanical compression||Heaviest disturbance|
Soil sampling and chemical analysis
Soil sampling was conducted from August 10–29th in 2010. Nine to 20 sites in each greenland land use type of each city were selected depending on city size. Within each site, three 3 × 5 m replicate subplots were randomly established. Soil samples from the surface layer (0–20 cm), with a composite of 10 subsamples, were taken with a 2-cm diameter stainless steel sample auger at each subplots. A total of 1215 soil samples were taken from 405 sites. In the laboratory the samples were air dried and sieved to 1 and 2 mm. Soil pH was measured in a soil-to-water suspension ratio of 1:1. Soil organic matter (SOM) was determined using the K2CrO7-H2SO4 oxidation method, available N was determined by the Alkali N-proliferation method. Available calcium (Ca), magnesium (Mg), potassium (K), P, sulfur (S), iron (Fe), copper (Cu), manganese (Mn), zinc (Zn), and boron (B) were determined using ASI methods [7,16] modified by Agro Services International, Inc. (ASI). Three soil extraction solutions were used to extract soil available nutrients: (1) ASI soil extracting solution (0.25 mol L-1 NaHCO3, 0,01 mol L-1 EDTA, 0.01 mol L-1 NH4F, and 0.05 g L-1 Superfloc), used to measure available P with a UV-8500 spectrophotometer (Tianmei Co., Shanghai, China) and K, Fe, Cu, Mn and Zn with an AA-6300 atomic absorption spectrometer (Shimadzu, Kyoto, Japan); (2) ASI-KCl extraction, used to measure available Ca and Mg with an AA-6300 atomic absorption spectrometer (Shimadzu, Kyoto, Japan); and (3) ASI-Ca(H2PO4)2 extraction, used to measure available S and B with UV-8500 spectrophotometer (Tianmei Co., Shanghai, China).
Variables were tested for normality (Kolmogorov–Smirnov) and for homogeneity of variances (Levene’s test). A two-way ANOVA using SPSS version 16.0 (SPSS Inc., Chicago, IL, USA) was performed for the effects of land use and topography types on each soil variable . Differences between means were tested using Duncan’s multiple range at p < 0.05.
Urban soil pH ranged from 4.90 to 8.76, with a mean of 7.88 (Table 3). Only 8% samples fell below neutrality, all the rest were alkaline. The concentrations of SOM were very low, with a mean of 6.7 g kg-1. For most soils, SOM < 10 g kg-1 is considered low. As to available N and P, urban soils had relatively lower levels (31.5 and 28.3 mg kg-1, respectively) when compared with the normal range (50–100 mg kg-1 and 30–60 mg kg-1, respectively) of non-urban soils (Table 3). However, for available K, it is apparent that in many of the plots, Hubei urban soils have sufficient nutrient levels (125 mg kg-1). Compared with macronutrients, secondary nutrients (Ca, Mg, and S) did not show deficiency, and in the case of available Ca (2694 mg kg-1) were excessive. The micronutrients (Mn, Fe, and Zn) had sufficient or excessive nutrient levels to support plant growth. Mean urban soil B concentration was 0.86 mg kg-1 (within the common range of 0.6–1 mg kg-1); however, from the frequency distribution of B in the samples, 60% of samples fell below the critical value. Thus, most urban soils, especially in the plain cities, have inadequate soil B supply.
|Soil properties||Minimum||Maximum||SE||CV (%)||Mean||Recommended rangea|
|Organic matter, g kg-1||0.94||19.42||2.97||43.55||6.73||>10|
|N, mg kg-1||1.96||314.01||35.55||112.52||31.56||50-100|
|P, mg kg-1||1.2||385.85||43.72||111.43||28.33||30-60|
|K, mg kg-1||33.45||507.42||69.13||55.39||125.31||78-156|
|Ca, mg kg-1||892||6048||916||34||2694||300-1000|
|Mg, mg kg-1||26.25||830.1||139.16||57.26||244.35||100-500|
|S, mg kg-1||1.93||146.31||23.87||74.74||31.92||24-40|
|Fe, mg kg-1||5.03||149.74||21.21||64.37||32.94||20-30|
|Cu, mg kg-1||0.43||23.65||2.82||73.34||3.87||3.0-4.0|
|Mn, mg kg-1||1.71||146.44||20.38||84.82||23.9||6.0-15.0|
|Zn, mg kg-1||0.91||43.06||5.63||88.49||6.38||3.0-6.0|
|B, mg kg-1||0.01||5.33||0.88||101.8||0.86||0.6-1.00|
Table 4 shows the results of a two-way ANOVA for the effects of land-use and topography types on each soil variable. Significant differences in soil nutrients between four land use types were found (p < 0.05, Table 4). Concentrations of available Ca, S, and Cu in the roadside sites were significantly higher than those in the institutional sites, while available Mn in the park sites was much higher than that in residential sites (Table 5). Interestingly, for available soil N and K, no significant differences were found between the four land use types, but for available P, it was as much as 1.6 times greater in parks than in the residential sites (27.1 mg kg-1). Compared with the recommended range, soil P concentration in the residential sites was slightly lower than the critical level, while for N, the concentrations in all land types were significantly lower than the critical level. No significant differences in SOM were found among the four land use types, but the mean values in all types were significantly lower than the critical level.
|Land use (A)||3||3.86||0.01||0.68||NS||0.33||NS||3.84||0.01||1.08||NS||3.24||0.03||1.82||NS|
|Topography (B)||2||8.41||< 0.01||10.25||0.01||18.34||< 0.01||1.59||NS||4.11||0.01||4.44||0.01||5.19||< 0.01|
|Land use (A)||3||4.13||< 0.01||1.9||NS||4.07||< 0.01||3.11||0.04||3.98||0.01||0.32||NS|
|Topography (B)||2||3.72||0.03||3.88||0.02||10.25||< 0.01||6.19||< 0.01||1.73||NS||23.35||< 0.01|
|A* B||6||3.41||< 0.01||1.72||NS||1.07||NS||1.65||NS||0.97||NS||0.46||NS|
|Soil properties||Land use||ANOVA p|
|Organic matter, g kg-1||0.65±0.03||0.64±0.03||0.67±0.06||0.69±0.04||NS a|
|N, mg kg-1||23.57±3.62||25.73±3.14||29.15±6.87||33.13±4.42||NS|
|P, mg kg-1||43.01±4.58a||33.52±8.35ab||27.17±3.82b||35.33±5.37ab||0.013|
|K, mg kg-1||117±6.85||112±5.82||117±12.69||131±8.13||NS|
|Ca, mg kg-1||2407±80b||2394±68b||2634±148ab||2663±96a||0.028|
|Mg, mg kg-1||255±14||234±11||240±26||224±16||NS|
|S, mg kg-1||30.87±2.53b||25.03±2.10b||26.04±4.77b||37.23±3.02a||0.001|
|Fe, mg kg-1||35.11±2.26||32.73±1.86||28.36±4.13||35.12±2.66||NS|
|Cu, mg kg-1||4.64±0.63ab||3.56±0.57b||4.82±1.27ab||6.21±0.73a||0.003|
|Mn, mg kg-1||27.04±1.85a||23.93±1.55ab||20.11±3.46b||27.08±2.13ab||0.035|
|Zn, mg kg-1||5.54±0.66b||6.21±0.55ab||6.47±1.12ab||7.91±0.73a||0.010|
|B, mg kg-1||0.70±0.07||0.73±0.06||0.68±0.12||0.69±0.86||NS|
Different topographies also exhibited a statistically significant effect for 8 of the 11 chemical variables (p < 0.05, Table 4). Most of the concentrations of macro and micronutrients in plain cities were always higher than those in mountainous cities (Table 6), showing a clear negative correlation with elevation. For N, Ca, Mg, S, Cu, and Mn, differences were nearly 1.5 times as high for the plain cities as for the mountainous cities. Interactions between land use and topography were not significant except for pH and available S concentration (Table 4).
|Soil properties||Physiographic||ANOVA p|
|Organic matter, g kg-1||0.74±0.03a||0.52±0.04c||0.66±0.03b||0.010|
|N, mg kg-1||25.42±3.51b||21.65±4.82b||34.84±3.16a||0.001|
|P, mg kg-1||37.76±4.32||35.05±5.93||29.17±3.82||NS a|
|K, mg kg-1||121.31±6.65a||98.74±9.02b||128.39±5.98a||0.014|
|Ca, mg kg-1||2327±78b||2160±106b||2839±69a||0.011|
|Mg, mg kg-1||218±14b||178±19c||295±12a||0.005|
|S, mg kg-1||25.06±2.53b||26.93±3.49b||35.44±2.25a||0.027|
|Fe, mg kg-1||28.46±2.11b||31.45±2.92 b||39.74±1.91a||0.019|
|Cu, mg kg-1||5.52±0.61a||2.89±0.84b||4.70±0.55a||<0.001|
|Mn, mg kg-1||18.03±1.80b||12.31±2.48c||40.11±1.68a||0.003|
|Zn, mg kg-1||6.00±0.59||6.82±0.80||6.65±0.52||NS|
|B, mg kg-1||0.95±0.08a||0.69±0.08b||0.48±0.05c||<0.001|
Urban soils are often subjected to compacting, crushing, sealing, dust, sewage, or alkalizing products; therefore, soil physical biological properties will be affected [18,19]. In this study, urban soil pH, with a mean of 7.88 (Table 3), has clearly deviated from the range found in local plain, hill, or mountain soils (5.0–6.8) . A similar result was observed by Jim  in Hong Kong, where only 8% of samples fell below neutrality, and the remainders were alkaline. Chon et al.  also found that pH was much higher in roadside soils of Seoul; however, without a noticeable seasonal variation. High pH values are mainly a result of alkalizing products such as calcium carbonate or calcium-magnesium carbonate in gravel, flagstones, cement, concrete, mortar, and atmospheric particulate deposition [4,10,22]. Messenger , Short et al. , and Pouyat et al.  also found that urban soils with construction wastes were alkaline. These alkaline substances become an enduring chemical legacy within the soil profile [11,25]. Leaching, especially by rain or sewage water, can lead to the movement of CaCO3 contained in these materials to adjacent intact soils . Elevated soil pH can influence the form and availability of nutrients and can result in plant nutrition imbalances and deficiencies and chlorosis symptoms . Although elevated pH may increase vigor for some alkaline-favoring plant species, it is detrimental to many predominantly humid-subtropical plant species that are adapted to acidic soil.
Soil organic matter is an important part of soil that maintains and protects soil nutrients from environmental loss . In this study, most SOM concentrations were ≤10 g kg-1. This is significantly lower than other systems in this region, such as 14.5 g kg-1 in agro-ecosystems , and 29.8 g kg-1 in forest ecosystems . Land preparation generally removes surface plants and topsoil and results in further reductions of SOM [4,22]. Besides these reasons, lower SOM concentration may be related to urban greenland management . In an effort to increase the aesthetic value of cities, workers repeatedly remove fallen leaves, grass clippings and other organic residues, which further reduce organic matter input to soil. City management sectors should improve the management of soil improvement, transportation, and stacking in urban construction to ensure the sustainable use of greenland and soil resources. The stalks and dry leaves, grass clippings, and other organic wastes in cities can be used as a good organic fertilizer when returned to soil [28,29].
The changes of the urban soil environment also affect the effectiveness of soil nutrients, in particular, available N and P. In this study, the available N concentration of 98% samples was below the critical level (50 mg kg-1) , suggesting that most urban soils in Hubei do not have sufficient N to support garden vegetation growth. Similar results were observed by Baxter et al.  in New York City, Jim  in Hong Kong, and Zhang et al.  in Hefei, which suggests that N deficiency in urban soil is likely to be possibly a common phenomenon. Baxter et al.  found that lower soil N concentration may be regulated by the low rates of N mineralization and nitrification in urban soil. Mineralization of N from organic matter in urban soil could be suppressed by the input of poor quality litter or increased amounts of organic matter transferred to recalcitrant pools, or both . White and McDonnell  found trampling and high levels of heavy metals in urban areas also indirectly reduced the numbers and diversity of soil microbes and invertebrates, likely leading to low rates of N mineralization and nitrification. Like available soil N, the available soil P was low (mean of 28.3 mg kg-1) when compared with the common range (i.e. 30–60 mg kg-1) of non-urban soils. Lower available P in urban soil is likely a result of the reduced organic inputs [11,30]. The abundance of carbonates in this region  may bind soil P and further limit its availability. The deficiency of both N and P could be rectified by suitable soil improvement measures able to positively affect soil organic matter concentration.
Generally, available K concentration decreases from the north to the south in China primarily due to the higher rainfall and consequent leaching of K in southern China . In the land south of the Yangtze River, farmers need to add K fertilizer for high yields . However, the concentration of available K (125 mg kg-1) in urban soil of this region was found to be moderate, slightly higher than the rural average of 79.3 mg kg-1 . Similarly, an increase of available K in urban soils has been reported by Hamberg et al. . It is speculated that these results may be related to the high Ca concentration in urban soil, since divalent Ca has higher surface charge densities, and cation exchange interaction, than monovalent K . Consequently, fixed or absorbed K ions from soil colloids could be exchanged with abundant soil Ca, resulting in the higher available soil K.
Compared with macronutrients, the available Ca concentrations of 99% of samples in this study were beyond the recommended range for Ca (Table 3) as were other cities, such as Baltimore (1620 mg kg-1)  and O’ahu (1280 mg kg-1) . Carbonate rock in Hubei is abundant, which has released large amounts of Ca into the soil by weathering . Also, Ca is an important component of atmospheric particulates in urban areas and comes from construction sites where lime, mainly composed of CaO or Ca(OH)2, is used . There is much evidence that higher soil Ca concentrations are related to urban construction and road building . Zhang and Iwasaka  found that soil Ca concentrations increased along the urban/rural gradient and with increased road density. Suitable increases of Ca in urban soil can be favorable to the cation exchange complex, especially in acid soil, and could remove aluminum toxicity, manganese toxicity, or salt damage . However, excessive Ca would reduce the availability of other nutrients such as B, P, Mo, Fe, and Zn [38,39].
Urban soil had sufficient or excessive micronutrient levels (Mn, Fe, Cu, and Zn), to support plant growth. However, 60% of samples have inadequate soil B supply. The other 40% of samples with high available B may be due to the higher total soil B concentration [40,41]. In addition to the parent material, soil pH was another important factor influencing available soil B concentration . Generally, in peracidic (pH < 3) and peralkaline (pH > 10) soil, available B concentration is low . The reason is that water-soluble B is easily formed and lost in acid soil and that strong absorption to B exists in alkaline soil especially rich in calcium carbonate. However, under subalkaline (pH 7–9) condition, soil available B concentration increases as pH increases . This study verified the above view that, in subalkaline soils, available B concentrations in mountainous and hilly cities with high pH was higher than that in plain cities with low pH.
Effect of Urban Land Use
Different environments and degrees of human disturbance in different land use areas induced great changes in some soil physical and chemical properties [22,42]. Pouyat et al.  reported that K, P, pH, and bulk density in urban forest (undisturbed and unmanaged) were significantly lower than in institutional and residential areas (disturbed and managed), suggesting that human disturbance and management increased soil nutrients (particularly P and K from fertilizers). In this study, soil pH and available P concentration significantly differed between land use types, with the highest values for pH and lowest concentrations for available P in the residential types and the lowest values for pH and highest concentrations for available P in the park sites. As the initial disturbances of land development often incorporate many alkaline substances such as liming and cement and elevated soil pH can influence the form and availability of nutrients, the difference between land use types may be due to the extent of surface site disturbance. Park soils are generally minimally disturbed and have no fertilizer management while road, institution, and residential soils are impacted by human trampling, mechanical compression, incorporation of human sewage, and building materials. Urban soil nutrients were also likely to be influenced by dust precipitation, because dust could provide a rich source of Ca, Mg, and S  and their concentrations are significantly different in each landscape, with the road site having the highest concentration of dust [21,37]. In this study, the roadside site had significantly higher concentrations of available soil Ca and S than the institutional and park sites, but available Mg was not significantly different (p > 0.05) among the four land use types. Most soils in this region are derived from dolomite, which is rich in Mg. In contrast, dust contains small amounts of Mg, and hence likely did not lead to the differences among land use types. In this study, available Cu, Mn, and Zn significantly differed among the four land use types, with the road sites having the highest of concentrations of Cu, Mn, and Zn. It is speculated that the higher soil temperature at the road sites resulted in higher soil mineralization and higher nutrient availability . Oke  reported that the introduction of asphalt of urban soil surfaces could increase the absorption and storage of solar energy that later is released as sensible heat, which increases adjacent soil temperatures by as much as 3–5°C. An increase in the content of available nutrients such as Cu, Mn, and Zn of road sites caused by high temperature was greatly beyond the maximum threshold values of these elements. This may explain why plants along the roads in some areas are more prone to leaf yellowing phenomenon or fails of plant establishment than in other land use sites. So, it should be choose some plants that are not sensitive to Cu, Mn, and Zn at the road sides.
Effect of Topography
Large differences in urban soil nutrients existed among cities on the three topographies (p < 0.01; Table 6). The concentrations of N, K, Ca, Mg, S, Fe, Cu, and Mn in plain cities were higher than those in mountainous cities, showing a negative correlation with city elevation. Pouyat et al.  found soil chemical and physical properties differed between geological provinces; however, lower values corresponded to the Atlantic Coastal Plain and higher values to the Piedmont Plateau. These differences are possibly caused by differences in the elemental composition of parent material between cities with different elevations. In this study, urban soils were yellow-brown, mainly derived from water-transported alluvium or formed by in-situ weathering of rocks (carbonate and sandshale), and easily suffered nutrient leaching during the rainy season. Soil in higher terrain was more vulnerable to leaching of available soil nutrients than in relative lower terrain because of the loss of soil organic matter [14,46].
Differences in temperature along the topographies may be the second reason for differences in available nutrients between cities of different elevations. Temperature in most plain cities was higher than in mountainous cities . Curtin et al.  found higher soil temperatures to significantly increase soil C and N mineralization and solubility of available soil nutrients. Li et al.  also reported the concentrations of available soil N and P increased by ~50% and 10%, respectively when the temperature increased from 12 to 18°C. Higher temperatures in plain cities likely increased soil nutrient mineralization and its availability.
Dust is likely to be another reason for the difference in soil nutrients as it is a major source of nutrient input . Based on a dust study in Hubei, mountainous urban environments usually had lower concentrations and depositional fluxes of atmospheric dust than plain urban environments . Urbanization is often more rapid in plain areas because road alignment is relatively easy and construction costs are also lower. Increased air pollution (providing soil input of N, Ca, Mg, and S) in plain areas likely further increased soil nutrients compared with those in mountainous areas.
In general, urban soils in Hubei Province had a higher pH than natural soils, were deficient in organic matter, and low in available N, P, and B concentrations. Concentrations of Ca, Mg, and S, however, were sufficient in many areas, particularly along roadside and residential land use types. This study indicates that these nutrient properties are highly variable across urban land uses and topographies, suggesting that urban soils are diverse, complex, and affected by numerous management practices, disturbances, and environmental factors. Future research should examine urban soil properties in various spatial and temporal scales. This would provide more specific information about the spatial and temporal variability in urban soils, to develop appropriate techniques and strategies for future urban design and planning.
Conceived and designed the experiments: ZGL FC. Performed the experiments: YL. Analyzed the data: GSZ. Contributed reagents/materials/analysis tools: KYW. Wrote the manuscript: ZGL RHZ.
- 1. Cohen JE (2003) Human population: The next half century science, 302: 1172-1175.
- 2. Pouyat RV, Russell-Anelli J, Yesilonis ID, Groffman PM (2003) Soil carbon in urban forest ecosystems. In: JM KimbleLS HeathRA BirdseyR. Lal. The potential of U.S. forest soils to sequester carbon and mitigate the greenhouse effect. Boca Raton, FL: CRC Press. pp. 347-362.
- 3. De Kimpe CR, Morel JL (2000) Urban soil management: A growing concern. Soil Sci 165: 31-40. doi:https://doi.org/10.1097/00010694-200001000-00005.
- 4. Jim CY (1999) Trees and greening of Hong Kong’s urban landscape: Subaerial and soil constraints. Remediation Manage Degraded Lands: 209-224.
- 5. Trammell TLE, Schneid BP, Carreiro MM (2011) Forest soils adjacent to urban interstates: Soil physical and chemical properties, heavy metals, disturbance legacies, and relationships with woody vegetation. Urban Ecosyst 14: 525-552. doi:https://doi.org/10.1007/s11252-011-0194-3.
- 6. Jin JW, Ye HC, Xu YF, Shen CY, Huang YF (2011) Spatial and temporal patterns of soil fertility quality and analysis of related factors in urban-rural transition zone of Beijing. Afr J Biotechnol 10: 10948-10956.
- 7. Portch S, Hunter A, editors (2002) A systematic approach to soil fertility evaluation and improvement, Modern Agriculture and Fertilizers, China Program, Special Publication NO. 5:10-42.
- 8. Pouyat RV, Yesilonis ID, Russell-Anelli J, Neerchal NK (2007) Soil chemical and physical properties that differentiate urban land-use and cover types. Soil. Sci Soc Am: J71: 1010-1019.
- 9. Whitcomb CE (1987) Establishment and maintenance of landscape trees. Stillwater, OK: Lacebark Publishing.
- 10. Zhang K, Xu XN, Wang Q (2010) Characteristics of N mineralization in urban soils of Hefei, East China. Pedosphere 20: 236-244. doi:https://doi.org/10.1016/S1002-0160(10)60011-2.
- 11. Jim CY (1998) Urban soil characteristics and limitations for landscape planting in Hong Kong. Landscape Urban Plan 41: 19-26. doi:https://doi.org/10.1016/S0169-2046(98)00052-8.
- 12. White CS, Mcdonnell MJ (1988) Nitrogen cycling processes and soil characteristics in an urban versus rural forest. Biogeochemistry 5: 243-262. doi:https://doi.org/10.1007/BF02180230.
- 13. Province Hubei Bureau of Statistics (2010). Hubei statistical yearbook 2010. Beijing, China: Statistics Press.
- 14. Wang QY, Xu NH, editors (1997) Brief on soil series of Hubei province. Hubei: Hubei Science and Technology Press.
- 15. Kang LF, Li FR, Hua W, Tan JA, Yang FW et al. (2006) The effects of different land-use types on quality of urban soils. Ecol Sci 25: 59-63.
- 16. Wu W, Fan Y, Wang ZY, Liu HB (2008) Assessing effects of digital elevation model resolutions on soil-landscape correlations in a hilly area. Agric Ecosyst Environ 126: 209-216. doi:https://doi.org/10.1016/j.agee.2008.01.026.
- 17. Wang SB, Zheng HT, Shao QQ, editors (2003) SPSS statistical analysis. Beijing: Machinery Industry Press.
- 18. Kissling M, Hegetschweiler KT, Rusterholz HP, Baur B (2009) Short-term and long-term effects of human trampling on above-ground vegetation, soil density, soil organic matter and soil microbial processes in suburban beech forests. Appl Soil Ecol 42: 303-314. doi:https://doi.org/10.1016/j.apsoil.2009.05.008.
- 19. Scalenghe R, Marsan FA (2009) The anthropogenic sealing of soils in urban areas. Landscape Urban Plan 90: 1-10. doi:https://doi.org/10.1016/j.landurbplan.2008.10.011.
- 20. Hong S, Zehou Z, Junsheng C (2001) Environmental geochemical characteristics of some microelements in the yellow brown soil of Hubei province. Acta Pedolo Sinica 38: 89-96.
- 21. Chon HT, Ahn JS, Jung MC (1998) Seasonal variations and chemical forms of heavy metals in soils and dusts from the satellite cities of Seoul, Korea. Environ Geochem Heal 20: 77-86. doi:https://doi.org/10.1023/A:1006593708464.
- 22. Scharenbroch BC, Lloyd JE, Johnson-Maynard JL (2005) Distinguishing urban soils with physical, chemical, and biological properties. Pedobiologia 49: 283-296. doi:https://doi.org/10.1016/j.pedobi.2004.12.002.
- 23. Messenger S (1986) Alkaline runoff, soil pH and white oak manganese deficiency. Tree Physiol 2: 317-325. doi:https://doi.org/10.1093/treephys/2.1-2-3.317. PubMed: 14975865.
- 24. Short JR, Fanning DS, Mcintosh MS, Foss JE, Patterson JC (1986) Soils of the Mall in Washington, Dc. 1. Statistical Summary of Properties. Soil. Sci Soc Am: J50: 699-705.
- 25. Wong F, Kurt-Karakus P, Bidleman TF (2012) Fate of brominated flame retardants and organochlorine pesticides in urban soil: volatility and degradation. Environ Sci Technol 46: 2668-2674. doi:https://doi.org/10.1021/es203287x. PubMed: 22243402.
- 26. Liu JS, Hu XM, Hu CX, Qiu WH, Lu JW et al. (2011) Differences in soil fertility parameters between 1981 and 2006 in Jingzhou County, China associated with changes of agricultural practices. Commun. Soil Sci Plan 42: 2504-2514. doi:https://doi.org/10.1080/00103624.2011.609258.
- 27. Yang YS, Guo JF, Chen GS, Yin YF, Gao R et al. (2009) Effects of forest conversion on soil labile organic carbon fractions and aggregate stability in subtropical China. Plant Soil 323: 153-162. doi:https://doi.org/10.1007/s11104-009-9921-4.
- 28. Kavitha P, Rao KJ (2010) Comparative studies of sewage sludge, urban compost and FYM on yield parameters, major nutrients uptake and economics of tomato (Lycopersicon esculentum Mill). J Soils Crops 20: 183-188.
- 29. Sterrett SB, Chaney RL, Gifford CH, Mielke HW (1996) Influence of fertilizer and sewage sludge compost on yield and heavy metal accumulation by lettuce grown in urban soils. Environ Geochem Heal 18: 135-142. doi:https://doi.org/10.1007/BF01771236.
- 30. Baxter JW, Pickett STA, Dighton J, Carreiro MM (2002) Nitrogen and phosphorus availability in oak forest stands exposed to contrasting anthropogenic impacts. Soil Biol Biochem 34: 623-633. doi:https://doi.org/10.1016/S0038-0717(01)00224-3.
- 31. Chen F, Lu JW, Zhang MC, Wan KY, Liu DB (2009) Mulberry nutrient management for silk production in Hubei Province of China. J Plant Nutr Soil Sci 172: 245-253. doi:https://doi.org/10.1002/jpln.200800093.
- 32. Hamberg L, Malmivaara-Lamsa M, Lehvavirta S, Kotze DJ (2009) The effects of soil fertility on the abundance of rowan (Sorbus aucuparia L.) in urban forests. Plant Ecol 204: 21-32.
- 33. Moussa AS, van Rensburg L, Kellner K, Bationo A (2009) Exploring differences of soil quality as related to management in semiarid rangelands in the western Bophirima District, North West province, South Africa. Afr J Range For Sci 26: 27-36.
- 34. Sutherland RA, Tolosa CA (2001) Variation in total and extractable elements with distance from roads in an urban watershed, Honolulu, Hawaii. Water Air Soil Pollut 127: 315-338. doi:https://doi.org/10.1023/A:1005283932003.
- 35. Chetelat B, Liu CQ, Zhao ZQ, Wang QL, Li SL et al. (2008) Geochemistry of the dissolved load of the Changjiang Basin rivers: Anthropogenic impacts and chemical weathering. Geochim Cosmochim Acta 72: 4254-4277. doi:https://doi.org/10.1016/j.gca.2008.06.013.
- 36. Zhang DZ, Iwasaka Y (1999) Nitrate and sulfate in individual Asian dust-storm particles in Beijing, China in spring of 1995 and 1996. Atmos Environ 33: 3213-3223. doi:https://doi.org/10.1016/S1352-2310(99)00116-8.
- 37. Farmer AM (1993) The effects of dust on vegetation - a review. Environ Pollut 79: 63-75. doi:https://doi.org/10.1016/0269-7491(93)90179-R. PubMed: 15091915.
- 38. Jakobsen ST (1993) Interaction between plant nutrients: Ⅲ. Antagonism between potassium, magnesium and calcium. Acta Agr Scand Bs: 43: 1-5.
- 39. Nazrulislam AKM (1982) Effect of calcium and manganese concentrations on root shoot ratio and uptake of nutrients in 3 ecologically distinct plant-species. Bangl J Bot 11: 132-147.
- 40. Communar G, Keren R (2006) Rate-limited boron transport in soils: The effect of soil texture and solution pH. Soil. Sci Soc Am: J70: 882-892.
- 41. Xu JM, Wang K, Bell RW, Yang YA, Huang LB (2001) Soil boron fractions and their relationship to soil properties. Soil. Sci Soc Am: J65: 133-138.
- 42. Lorenz K, Kandeler E (2005) Biochemical characterization of urban soil profiles from Stuttgart, Germany. Soil Biol Biochem 37: 1373-1385. doi:https://doi.org/10.1016/j.soilbio.2004.12.009.
- 43. Goodrich BA, Koski RD, Jacobi WR (2009) Condition of soils and vegetation along roads treated with magnesium chloride for dust suppression. Water Air Soil Pollut 198: 165-188. doi:https://doi.org/10.1007/s11270-008-9835-4.
- 44. Curtin D, Beare MH, Chantigny MH, Greenfield LG (2011) Controls on the extractability of soil organic matter in water over the 20 to 80 degrees C temperature range. Soil. Sci Soc Am: J75: 1423-1430.
- 45. Oke TR (1989) The micrometeorology of the urban forest. Philos TR Soc B 324: 335-349. doi:https://doi.org/10.1098/rstb.1989.0051.
- 46. Clark DB, Clark DA, Brown S, Oberbauer SF, Veldkamp E (2002) Stocks and flows of coarse woody debris across a tropical rain forest nutrient and topography gradient. Forest Ecol Manag 164: 237-248. doi:https://doi.org/10.1016/S0378-1127(01)00597-7.
- 47. Chen ZH, Wang HJ, Ren GY, Xiang H, Xie L (2005) Change of urban heat island intensity and its effect on regional temperature series: a case study in Hubei Province. Clim. Environ Res 10: 771-779.
- 48. Li FS, Kang SZ, Zhang FC, Li ZJ (2002) Effects of atmospheric temperature on soil nutrient movement and dry matter accumulation of spring wheat. Acta Agr Boreali Sin 11: 132-137.
- 49. Ma WJ (2003) Analysis of dust precipitaiton in urban area of Jingmen. Environ Sci Technol 26: 21-22,