Many cactus species have been introduced around the world and have subsequently become major invaders, inducing social and ecological costs. We recorded the distribution of Opuntia stricta in eastern Africa, and conducted 200 household interviews using semi-structured questionnaires to assess local perceptions of O. stricta in Laikipia County, Kenya. Opuntia stricta was widespread and abundant in parts of Kenya, Tanzania and Ethiopia and present at low densities in Uganda. In Laikipia County, pastoralists identified that O. stricta had been present for more than 10 years, and were of the opinion that it was still spreading and increasing in density. Two-thirds of respondents estimated that 50–75% of valuable grazing land had been invaded, and all felt that it contributed to the ill-health and death of livestock. Other negative impacts included reductions in native plant populations, rangeland condition, human health, and mobility of humans and animals. These negative impacts resulted in economic losses of US$ 500–1000 per household per year for 48% of households. Only 20% of respondents reported actively managing O. stricta, yet all respondents believed a reduction in the abundance of this weed would improve well-being. Management interventions are needed to reduce negative impacts.
Thousands of plant species have been introduced to countries around the world, both accidentally and intentionally for a host of reasons, including agriculture, forestry, and ornamental purposes (Mack 2003). Subsequently, many of these alien species have naturalised and some have become invasive (Blackburn et al. 2011). For example, it is estimated that there are over 751 invasive trees and shrub species globally (Rejmánek and Richardson 2013). These biological invasions are a major component of global change, and they cause numerous negative impacts on biodiversity, ecosystem services, and human well-being (Pimentel 2002; Simberloff et al. 2013). This makes their management important, especially when they also impact on livelihoods. However, it is often difficult to justify the expenditure of scarce resources to support the control of invasive alien species because of a lack of evidence of impacts, or in many cases differences of opinion regarding the magnitude of impacts (Shackleton et al. 2014). When impacts are studied, it is most often from ecological or economic perspectives and studies based on social perspectives are rare, although they are receiving increasing attention (Shackleton et al. 2007; Garcia et al. 2008; García-Llorente et al. 2011; Kull et al. 2011; Kannan et al. 2014; Shackleton et al. 2015). An understanding of social perspectives is important, as it is often people that influence plant distribution and need management of invasions to reduce impacts and enhance benefits. The impact of invasive alien species can often be reliably gauged through an assessment of local knowledge (Chalmers and Fabricius 2007; Sundaram et al. 2012). Such assessments can be particularly valuable in areas where information on impacts is virtually absent, for example in Africa and Southeast Asia (Nuñez and Pauchard 2009). This information can be used to help justify further research in data-scarce areas as well as aid in receiving much-needed management funding.
The Cactaceae is a large family with 130 genera and 1922 species with the majority native to North, Central and South America (Novoa et al. 2015). Numerous cactus species have been introduced around the world for different reasons, including as ornamental plants and to provide fodder and edible products. Of these species, 57 have become naturalised and problematic globally, particularly in arid rangelands (Novoa et al. 2015). Invasive cactus species impact negatively on biodiversity and a range of economic sectors (Novoa et al. 2015), but many species also provide benefits such as revenue through horticulture and provide food, medicinal products and fodder (Einkamerer et al. 2009; Shackleton et al. 2011; Novoa et al. 2016). The situation is often not static, as the costs of invasive species increase and eventually outweigh the benefits as they spread and increase in density (Shackleton et al. 2007; van Wilgen and Richardson 2014). Various invasive cactus species have negative impacts on people, wildlife and livestock movement, reduce the value of grazing land, and negatively impact livestock health and ecological processes (Ueckert et al. 1990; Taylor and Whitson 1999; Novoa et al. 2015), creating a need for active management in order to reduce the negative impacts.
The cactus genus Opuntia contains a high number of problematic species that invade the arid and semi-arid lands of the world—including Opuntia stricta (Haw.) Haw. (known variously as erect or sour prickly pear, or Australian pest pear) (Novoa et al. 2015). Opuntia stricta is a spiny perennial succulent shrub with elongated blue-green cladodes and red–purple fruits which is native to south-east USA, eastern Mexico and some Caribbean Islands. This species has been recorded as naturalised and/or invasive in several African countries, India and Sri Lanka in Asia, Yemen and Saudi Arabia in the Middle East, France, Italy and Spain in Europe, and on the Galápagos islands, Cuba, Madagascar and Australia (CABI 2016). Opuntia stricta was initially introduced to many regions for ornamental and hedging (live fencing) purposes (Foxcroft et al. 2008), but has escaped cultivation and has spread, including into conservation areas (Vilá et al. 2003; Foxcroft et al. 2004), rangelands (Strum et al. 2015) and agricultural areas (Vilá and Gimeno 2003), where it is responsible for a range of negative impacts that have not been systematically quantified (CABI 2016). In Madagascar, invasive O. stricta was rated as having no benefits in comparison to other Opuntia species as the fruit were seen as inferior and cladodes were not used as fodder (Larsson 2004). Furthermore, O. stricta was seen as the most problematic invasive Opuntia species on the island, causing problems such as reduced fodder production, impeding mobility and impacting livestock and human health (Larsson 2004).
In the study reported here, we surveyed the broad-scale distribution and extent of invasions of O. stricta in eastern Africa, and gauged local perceptions of the value, impact and management of this species in the context of rural pastoralists in Africa. We then used our findings to make recommendations for management of this species in the region.
The study took place at two spatial scales. One was at a broad regional scale and included a survey of the distribution and abundance of O. stricta in parts of Kenya, Rwanda, Tanzania, Uganda and Ethiopia (Fig. 1). The second was an assessment of the distribution of O. stricta at a local level, in Laikipia County, Kenya (Fig. 2).
The livelihood impact survey was conducted in the small town of Dol Dol and neigbouring villages (0.393884°S:37.164296°E) in the northeast of Laikipia County, central Kenya, where O. stricta is common on communal land (Fig. 2). Surveys were conducted in this area because it is considered to be the source of current O. stricta invasions. Dol Dol also has relatively high human population levels compared to the rest of the invaded area, making it easier to undertake socio-economic surveys. This area has a temperate climate with mean annual rainfall of between 200 and 600 mm and mean annual temperatures of 16–26 °C. Laikipia County lies at the meeting point of the Somalia-Maasai Bushland and the Afromontane-Afroalpine biotic zones represented by grasslands, bushland, woodland and dry forests (Butyanski and de Jong 2015). The vegetation of the survey area is a mixture of grasslands and savannas, where the most common native trees are those in the genera Vachellia (formerly Acacia) and Commiphora.
Communities residing in the communal rangelands of Laikipia County are mainly Mukogodo Maasai pastoralists who have recently adopted a semi-sedentary lifestyle. Areas of settlement are relatively under-developed, with most households relying on livestock (for meat and milk, or sale), and natural resources for sustenance. The human development index, which is a combined statistic of life expectancy, education, and per capita income indicators, for the region is low (0.412) and is less than the national average (0.561) (Government of Kenya 2013). This suggests that the communities in the study site would be vulnerable to any further degradation of the environment on which they depend. Dol Dol and the surrounding areas have a population density of 12 people/km2, which is lower than the 42 people/km2 found in other areas within Laikipia County (Kenya National Bureau of Statistics 2010). The economy of the County is largely driven by tourism (private wildlife ranches/conservancies) and rangeland grazing on communal lands (Government of Kenya 2013). Both of these land tenure systems rely heavily on large and intact rangelands.
Mapping of O. stricta
Information on the presence and status of O. stricta was recorded during roadside surveys in Kenya, Tanzania, Uganda, Rwanda and Ethiopia. These surveys took place between 2008 and 2015, and covered tens of thousands of kilometres. Similar roadside surveys have been undertaken in Angola and South Africa and are a cost-effective way of getting a broad scale understanding of the extent of invasions and have been a key data source for aiding research and management in the country as well as guiding further detailed mapping (Henderson 2007; Rejmánek et al. 2016). We recorded the GPS co-ordinates of sites where O. stricta occurred, and noted it’s status in terms of the categories proposed by Blackburn et al. (2011) (present/casual, naturalized or invasive). As there are two varieties or sub-species of O. stricta in eastern Africa, we also noted the variety present (either O. stricta var. stricta or O. stricta var. dillenii). Opuntia stricta var. dillenii has 4–7, and sometimes up to 11 spines per areole, while var. stricta has 0–1 spines per areole (Parfitt and Gibson 2003). Isolated individual plants, across a wider landscape, were considered to be present or casual while naturalized plants were considered to be those that had established self-perpetuating populations, but which were not yet widespread and abundant or localized and abundant (invasive) in the areas where they were found. The distribution and abundance of O. stricta within eastern Africa was mapped at 1/2-degree grid cells (~55 × 55 km), by recording in which grid cells the species was present and/or naturalized or invasive (see Fig. 1). Distributions within Laikipia County, Kenya, were mapped at a higher resolution (~7 × 7 km), showing where O. stricta was present but not naturalized or invasive (yellow), naturalized (orange) or invasive (red) (see Fig. 2). It should be noted that in most cases only a part of each grid cell could be surveyed, and as such the distribution maps are merely an approximation of the presence and density of O. stricta.
Information on local knowledge and perceptions of O. stricta was collected using semi-structured questionnaires in which 200 respondents were interviewed at their households in late 2014. This technique (eliciting local ecological knowledge) is growing in the field of invasion biology, as it is a cost-effective way of providing a useful understanding of how invasive species impact on humans (García-Llorente et al. 2011; Shackleton et al. 2015). The questionnaire surveys were conducted in Dol Dol and 20 villages in Laikipia County where the extent of invasion by O. stricta on communal land varied from moderate to high (Fig. 2). Households were randomly selected, and the head of the household (or a suitable alternative if the head was not present) was interviewed in their local language (Maasai or Swahili) by a local field assistant. The questionnaires consisted of mainly close-ended, listing and ranking questions, but also some open-ended questions with four key sections. These sections included: (1) demographics of the household; (2) understanding and perceptions of the introduction and spread of O. stricta; (3) understanding and perceptions about the benefits and costs of O. stricta and; (4) questions relating to management practices. Values are reported in US$ based on a current (2016) exchange rate of approximately 100 KSH (Kenyan Shillings) to one US$ (US Dollars).
Data mining techniques (Principle Component and Cluster analysis) were used to assess broad scale relationships between the demographic variables of the participants and their responses. However, these revealed no significant relationships or clustering. We then ran Chi square analysis for categorical variables, independent T tests (Mann–Whitney U tests if assumptions not upheld), one-way ANOVA and Games Howell post hoc tests, and linear regressions for continuous and ordinal data. We ran these analyses using the demographic data (gender, employment, age, education level and number of livestock) as independent variables, and the questionnaire responses as dependent variables. We only report on those relationships that were found to be significant.
Distribution of O. stricta in eastern Africa
Opuntia stricta was found to be present in Ethiopia, Kenya, Tanzania, and Uganda but was not found in Rwanda (Fig. 1; Table 1). Opuntia stricta var. stricta was found to be widespread and abundant in eastern Ethiopia, especially between and around Alemaya and Jijiga, where it was often found to be growing in semi-arid rangelands and on rocky outcrops in association with O. ficus-indica (L.) Mill (sweet prickly pear). In Kenya, O. stricta var. stricta was found to be abundant in Laikipia County and Tsavo East National Park. It is assumed that O. stricta var. stricta infestations originated in the town of Dol Dol in Laikipia County, where it is now present, naturalized or invasive on 34 (31%) of the 110 (48%) 1/16 degree grid cells surveyed in the County itself. It is abundant on overgrazed communal rangelands and some of the adjoining conservancies, which are well managed and not overgrazed. We estimate that this variety has also invaded about 500 km2 of Tsavo East National Park and assume that it is also present on adjoining rangelands. Insecurity and poor road access, in both East Africa and Ethiopia, prevented detailed surveys from being undertaken in some areas, so cactus distributions are possibly an underestimate, but are an important baseline to guide future surveys and management strategies.
Opuntia stricta var. dillenii was also present along the Kenyan coastline where it has escaped from hedge plantings. More recently a small infestation was found near Lake Baringo, growing amongst metamorphic and volcanic rocks, in association with O. elatior Mill. (red-flower prickly pear) and Prosopis juliflora (Sw.) DC. (Fabaceae; mesquite). This variety is widespread and abundant in parts of the Serengeti District, Tanzania, especially near Ikoma and Robanda, on the edge of Grumeti Game Reserve and Serengeti National Park with some isolated stands further to the west. There are smaller infestations in dry savanna to the south of Mount Kilimanjaro and along the Tanzanian coast. It is present, but at low densities, in parts of Uganda where it has escaped from planted hedges.
Demographic data of respondents in Laikipia County
The majority (65%) of the 200 interview respondents were male. The mean (±SD) age of the respondents was 39 ± 13 (min. −19; max. −72) years, living in households with a mean of 7 ± 5 (min. −1; max. −17) people. The majority of respondents had no formal schooling (59%) with 21% having only primary schooling. Most respondents were pastoralists (36%), followed by housewives or those having no formal employment (33%), with 18% working as unskilled labour and the remainder (13%) working skilled jobs or owning small businesses. The skilled jobs included rangers, teachers and social workers. Almost all households had livestock (99%) with a mean (±SD) of 32 ± 44 (min. −0; max. −300) goats, 33 ± 48 (min. −0; max. −300) sheep and 10 ± 14 (min. −0; max. −78) cattle with 77% of respondents grazing their livestock between 1 and 5 km away from their homesteads. Male-headed households had significantly more cattle (Mann–Whitney U: F = 15.85; p < 0.01) than female-headed households. Education level, having a job, and a large number of cattle were highly correlated (indicator of poverty/wealth). For example, households with tertiary and secondary education had significantly more cattle (mean of 152 and 118 cattle respectively) than households with primary and no education (mean of 76 and 73 cattle respectively) (F = 4.52; p = 0.01).
Introduction and spread of Opuntia stricta in Laikipia County
Invasions of O. stricta are perceived to be widespread and increasing in many different environments in the Dol Dol area. All respondents (100%) mentioned that O. stricta was present on the land where they grazed their livestock (Fig. 3). The majority of respondents indicated that O. stricta had been in the area for more than 10 years (Fig. 4). Significantly more men than women did not know in which time period O. stricta first appeared in the area (χ2 = 8.53 (df = 1); p < 0.03); furthermore less educated respondents were better at giving an approximate period of arrival than better educated respondents (χ2 = 8.64 (df = 3); p = 0.034). Two-thirds of respondents (67%) estimated that O. stricta covered 50–75% of their grazing land, while 20% thought it was less widespread, and 10% thought it was more widespread (Fig. 5). All respondents (100%) thought that O. stricta invasions were increasing in their area. More than 25% of people identified that the three primary areas that O. stricta invades are near rivers, homes and on hills/mountains (which are the most valuable grazing areas), while 14% mentioned it as being common on rocky outcrops (Figs. 3, 6).
Perceptions of the reasons for the introduction of O. stricta differed between respondents. The majority of respondents (74%) did not know why O. stricta was originally introduced. Others believed it was introduced either as a hedge (11%) or as a garden plant (8%), to combat erosion (5%), with very few (3%) believing that it was introduced for food and fodder. Older respondents knew the reason for introduction, unlike many of the younger respondents (Mann–Whitney U: F = 4.457; p = 0.05). One respondent (mistakenly) believed it was introduced by researchers to feed baboons as part of a scientific experiment. People did, however, have a better knowledge on the vectors of spread in the local area. Most respondents (>25%) believed it to be spread by wildlife (primarily baboons) or livestock, or that it spread naturally on its own, with fewer (14%) mentioning that it was spread by people (Figs. 3, 7).
Benefits of Opuntia stricta
According to residents, O. stricta did not provide much in the way of benefits (Table 2). A fifth (20%) of respondents reported eating O. stricta fruit, with the remaining 80% saying they ate it only rarely or never. Significantly, more men reported eating O. stricta than women (χ2 = 4.02 (df = 1); p = 0.044) as they are likely to spend more time in the rangelands herding their livestock (Tangka et al. 2000). Respondents mentioned that a lot of time and effort is needed to remove the small barbs (glochids) from the fruit and that it could only be eaten in moderation otherwise it would result in stomach ‘irritation’ (see below). In addition, 50% of respondents mentioned that O. stricta increased the presence of other trees and shrubs, because invaded areas protect native seedlings and saplings from livestock browsing. This is not uncommon, and is known as “associational resistance”, whereby spiny or unpalatable plant species effectively protect other plant species from browsing animals (Smit et al. 2005, 2006). According to Smit et al. (2007) an “extremely toxic and well-defended nurse plant” would provide significant protection to associated recruits.
Costs of Opuntia stricta
The majority of local people were of the opinion that O. stricta invasions resulted in net negative impacts by degrading rangelands, reducing the benefits gained from livestock production, and impacting on their own health (Table 2). All respondents (100%) mentioned that O. stricta infestations had a negative impact on livestock health. The major negative impacts on livestock included blindness caused by O. stricta spines piercing their eyes, especially during dry periods when little other forage is available, and livestock try to access grass and small shrubs growing near or in cactus stands (Fig. 3; Table 3). Consumption of fruit resulted in the lodging of glochids in the lips, mouths and gastro-intestinal tracts of animals, leading to weight loss and a reduction in milk production, often followed by death (Fig. 3; Table 3). In addition, many respondents mentioned that if livestock eat O. stricta fruit there is a reduction in tripe quality and value (Tables 2, 3). People mentioned that the intestinal lining of slaughtered livestock were full of glochids, which often resulted in the formation of yellow pustules. The majority of people (90%) said they could no longer sell tripe (a delicacy, especially for Maasai women).
Opuntia stricta was also seen by many respondents as reducing the value of livestock by causing illness leading to poor condition. Another key negative impact of O. stricta invasion, mentioned by 96% of respondents, was the fact that invasions hinder human and livestock movement to water sources, homesteads and grazing lands. Numerous negative impacts caused by O. stricta were highlighted by 91% of respondents who mentioned that invasions reduced access to grasses (important for livestock) and impacted negatively on wildlife populations (Table 2). Loss of useful plants, primarily medicinal plants, was mentioned by 43% of respondents, while 84% highlighted that invasions impacted negatively on human health by causing eye and skin irritations, probably as a result of coming into contact with the glochids on the fruit. The only significant differences that arose between the demographic variables and responses on costs of O. stricta were that women mentioned negative impacts on water availability significantly more than men (χ2 = 5.84; p = 0.015). This could be ascribed to the fact that in most rural communities women are tasked with collecting water for household use.
Respondents estimated that in the past year they had lost (on average, ± SD) 9 ± 11 (min. −0; max. −180) goats, 7 ± 8 (min. −0; max. −250) sheep, and 15 ± 20 (min. −0; max. −120) cattle due to the presence of O. stricta. This amounts to mean annual losses of between US$ 500–1000 and US$100–500 per household for 48 and 30% of the respondents, respectively (Fig. 8).
Costs of Opuntia stricta relative to other social-ecological drivers
When asked to select the most important threat to livestock production, the largest proportion of respondents (35%) identified weeds and poisonous plants as the most important, followed by insufficient grazing (31%), which may also be as a result of plant invasions, followed by disease (20%), livestock-wildlife conflict (11%), with lack of water and stock theft being ranked as very low (Fig. 9a). When asked to identify the most problematic plant species, O. stricta was cited as the worst weed in the area (55%) followed by Austrocylindropuntia subulata (Muehlenpf.) Backeb. (Cactaceae; Colville cactus) (35%), native Sansevieria spp. (Asparagaceae) and O. ficus-indica (L.) Mill., both 5% (Fig. 9b). This illustrates that people were well aware of the multiple factors that could affect their wellbeing, including how these issues were affected by invasive alien plants.
Management of Opuntia stricta
Despite the fact that residents recognised that O. stricta caused many negative impacts, only 20% of respondents mentioned that they had attempted to remove or control the spread of O. stricta. Significantly more women respondents reported managing O. stricta than men (χ2 = 4.54 (df = 1); p = 0.03). Of those that did attempt management, 29% reporting trying to burn the plants, and 98% reporting using both physical methods (slashing, cutting, digging) and burning. Only 7% of respondents reported paying people to help to clear infestations and payments were all less than US$ 100 per ha. The majority of respondents (89%) had heard of biological control with 88% of respondents having seen the cochineal (Dactylopius spp.; Dactylopiidae), a sap sucking insect, on Opuntia spp. in the area (Fig. 3). Based on these observations, about a third of respondents (36%) believed that biological control was safe, with the remainder being unsure of the potential risks or benefits it posed. However, all respondents were happy to endorse and support any cost-effective and safe way of managing O. stricta. All respondents (100%) also believed that a reduction in O. stricta invasion density would improve grazing land, livestock health and livelihoods, while 99% were of the opinion that it would increase the value of land.
Distribution and impacts of Opuntia stricta
This study found that O. stricta var. stricta was widespread and abundant in Kenya and in areas in eastern Ethiopia that we were able to survey, with O. stricta var. dillenii dominating in Tanzania. Invasions only started becoming prolific in the recent past, based on opinions of landowners and community members, and it is believed that they could potentially spread and increase in density in many areas in eastern Africa. Local people had a good understanding of the reason for introduction (ornamental purposes and hedging), and that wildlife and livestock were the main dispersal agents, as has been demonstrated in the Kruger National Park, South Africa, where baboons (Papio ursinus Kerr; Cercopithecidae) and elephants (Loxodonta africana Blumenbach; Elephantidae) were found to be key dispersers of O. stricta (Foxcroft et al. 2004). Baboons were also identified as one of the main dispersal agents in pastoral rangelands in Kenya (Strum et al. 2015) together with elephants, tortoises and possibly also vulturine guineafowl (Acryllium vulturinum Hardwicke; Numididae) (A.B.R. Witt pers. obs.). Baboons are largely responsible for dispersing cactus seeds to rocky hilltops because that is where they tend to reside at night, a habitat identified by pastoralists as having large and dense infestations. In addition, high cactus densities are likely to occur around water sources and near homesteads, since livestock spend considerably more time in these areas, where they deposit cactus seeds in manure. Crows are a major dispersal agent of invasive Opuntia species across large parts of the arid interior of South Africa (Dean and Milton 2000), and other bird species in Laikipia, such as lark’s, sparrows and pipits, were observed eating O. stricta seeds, especially in elephant dung (D. Scott pers. obs.), and as such are also likely dispersal agents.
In Madagascar, Larsson (2004) highlighted that unlike other Opuntia species, O. stricta has less benefits and higher impacts which reduce human well-being. This is in accordance with our findings which show substantial negative impacts of O. stricta for local livelihoods with very few benefits. All villagers were of the opinion that O. stricta invasions had a negative impact on ecosystem goods and services, biodiversity and human well-being. In particular loss of livestock production and a reduction in animal health were seen to increase vulnerability of pastoralists in Laikipia County, with significant economic losses.
Veterinary studies documenting the livestock health impacts of Opuntia species (Ueckert et al. 1990; Hanselka and Paschal 1991) support the claims made by local pastoralists in this study. The spines and glochids are known to cause irritation, swelling and ulceration of lips, tongues and mouths, an affliction referred to as pear mouth and cactus tongue. The glochids on the fruit, once consumed, also lodge in the gastro-intestinal tract causing irritation, ulcers and pustules, often leading to secondary infections, and death. Excessive consumption of fruit may result in constipation, affecting rumen function, which has also been linked to the loss of livestock (Ueckert et al. 1990; Hanselka and Paschal 1991) and to reduced lactation and often loss of young (Merrill et al. 1980). In a national beef quality audit it was found that 22.5% of US cattle had cactus tongue, making them unsuitable for market and human consumption (Garcia et al. 2008). Other semi-arid rangeland invasive species such as Prosopis spp. are also known to impact negatively on livestock health, through loss of teeth (due to consumption of the pods which have a high sugar content), and thorn injuries (Shackleton et al. 2015).
Furthermore, O. stricta invasions were perceived by many villagers to reduce native plant occurrence, which negatively impacts livestock production, natural resource collection and biodiversity in the area. In contrast, some pastoralists mentioned that O. stricta presence increased the abundance of grasses, shrubs and trees. Opuntia stricta may act as a nurse plant, supporting and protecting native plant species growing within stands from browsing by livestock and wildlife, considerably reducing the carrying capacities of invaded landscapes (Taylor and Whitson 1999). In other words cactus spines, which can cause serious injury to many animal species, prevent them from gaining access to, and feeding on palatable species growing within individual plants and/or cactus stands. The loss of grazing potential due to Opuntia species invasions is supported by other studies (Price et al. 1985). Research in the USA found that around each cactus plant there was a 15–20 cm wide buffer that was not grazed, which is comparable to twice the area of the cactus plant itself (Taylor and Whitson 1999). If 20% of a pasture, which produces 450 kg of forage, is invaded by cactus, 160 kg of potentially utilisable forage is lost or inaccessible to livestock (Taylor and Whitson 1999). This amounts to a considerable reduction in carrying capacities based on the premise that one sheep consumes 2.5–3% of its body weight per day which amounts to approximately 3 kg of hay or grass daily (Taylor and Whitson 1999). One hundred and sixty kilograms of grass could potentially feed 53 sheep for 1 day. If 50% of the same pasture, one that produces 450 kg of forage, was invaded by cactus, forage availability could be reduced by 225 kg, enough to feed 75 sheep for 1 day.
Other than the loss of access to forage and negative impacts on livestock health, local pastoralists mentioned that these invasive cacti also inhibited the movement of people, decreased the availability of natural resources (native plants primarily for medicinal purposes), and had negative impacts on human health. Spines and glochids have been reported in medical journals to cause physical injuries, and can induce allergenic reactions resulting in sarcoma, foreign-body granulomas and ulceration (Barney 1925; Boyd 1955; Schreiber et al. 1971), which supports local claims.
Although this study focused on human livelihoods, O. stricta also has negative effects on wildlife, which could impact on ecotourism, a major source of employment for many community members. It is unknown if fruit consumption by wildlife has similar negative impacts as those reported for livestock. Elephants readily consume cactus fruit and are key dispersal agents (Foxcroft et al. 2004). During a drought in Laikipia County in 2009, a large number of young elephants died. Abscesses, similar to those found in livestock, were also observed in the mouths of dead elephants, and the assumption was made that these were caused by glochids from the cactus fruit lodging in their mucosal membranes, an observation supported by many respondents employed as game guards. Whether or not the consumption of cactus fruit contributed to the demise of these animals remains unknown, and further research would be needed to establish whether this observation is valid. The attraction of elephants to the fruit of cacti has also contributed to increased human-wildlife conflict, with elephants encroaching on grazing especially in communal lands, which have extensive cactus infestations.
Shackleton et al. (2007) proposed a framework that classified invasive alien species in terms of their potential effects on livelihoods. Under this framework, species are placed into one of four possible categories: (1), undesirable but weakly competitive species that have little effect on human well-being (2), undesirable species that are strongly competitive, resulting in large negative impacts on local livelihoods (3), desirable species that are weakly competitive, therefore being primarily beneficial and (4), species that are useful and strongly competitive, and so have both substantial benefits and costs for humans and therefore often have conflicts of interest surrounding them. According to the framework, O. stricta can be categorised as an undesirable strongly competitive weed. This is a species that has few benefits and major costs for community livelihoods. According to the framework, as O. stricta spreads and increases in density, there will be an increase in the vulnerability of local communities. This is different from other invasive species such as Australian acacias that can be both beneficial and harmful at the same time (de Wit et al. 2001; Richardson and Rejmánek 2011) and can be categorised as useful strongly competitive invasive species (Shackleton et al. 2007). This suggests that management will be needed to prevent a decline in human well-being, especially for communities that are already vulnerable, since negative impacts are likely to increase. The research here has provided a basis for further study (detailed mapping and field experiments to measure impacts on biodiversity and human and livestock health), and can be used as leverage to encourage governments and other agencies to provide additional funds for research and management.
The negative effects of O. stricta on human well-being, ecosystem services and biodiversity highlights the need to manage these invasions. Various control options exist for O. stricta which need to be integrated and coordinated for maximum effect, especially in conservation areas as has been done in the Kruger National Park (KNP), South Africa (Lotter and Hoffmann 1998; Foxcroft and Richardson 2003). This includes the integration of various control options such as physical, chemical and biological control which should be implemented in conjunction with other activities, including awareness creation and capacity development. In the Dol Dol area (and we suspect for the rest of eastern Africa) there is currently little control, and that which is being undertaken focusses mainly on physical removal and burning which is time-consuming, expensive and largely ineffective, especially if all the roots and/or cladodes are not removed (Lotter and Hoffmann 1998). Opuntia stricta can reproduce vegetatively, making physical control difficult, as any piece of the plant left on the soil surface will regenerate. Herbicide application is more effective and monosodiummethylarsenate (MSMA) can be injected onto large plants or sprayed onto small plants and loose cladodes (Lotter and Hoffmann 1998). However, this herbicide can be costly and can be damaging to other plants so care needs to be taken in its use. More recently, glyphosate has been suggested as a safer alternative however, the waxy layer on the cladodes means that high concentrations need to be applied which increases costs. Triclopyr based herbicides are also widely used. Larsson (2004) reports that no community in Madagascar was able to effectively control O. stricta invasions using manual methods, making the provision of herbicides to aid control important in the future.
Biological control is often considered as the most cost-effective and successful method of control for many invasive species (Moran et al. 2005; Page and Lacey 2006; van Wilgen et al. 2012) and the same has been suggested for O. stricta (Lotter and Hoffmann 1998). Cactoblastis cactorum Berg, a phycitid moth, was introduced into Australia and successfully controlled O. stricta (Dodd 1940), but was less successful in the KNP (Lotter and Hoffmann 1998; Hoffmann et al. 1998). It was also released in Kenya in 1971, but did not establish (Greathead 1971). As a result, the sap-sucking cochineal, Dactylopius opuntiae (Cockerell), originally introduced from Australia (ex Mexico) for the biological control of O. ficus-indica in South Africa, was also introduced on O. stricta in the KNP, but did not provide significant control either (Lotter and Hoffmann 1998). Opuntia stricta was deemed to be a sub-optimal host for this cochineal genotype. Another genotype of D. opuntiae, originally from Texas in the USA, was introduced to South Africa from Australia in 1997, where it had successfully controlled O. stricta and O. inermis (Dodd 1940; Hosking et al. 1994). This genotype showed a strong preference for O. stricta (Hoffmann et al. 1999; Volchansky et al. 1999). Its release in the KNP has resulted in a drop in the biomass of around 35 O. stricta cladodes/m2 to under 5 cladodes/m2 (Paterson et al. 2011) and negated the need for physical and/or chemical control.
According to Winston et al. (2015), a genotype of the cochineal D. opuntiae which attacks O. ficus-indica, was accidentally introduced into Kenya in the 1990s. It readily established in Laikipia County and significantly reduced the abundance of sweet prickly pear. Occasionally this cochineal will establish at very low densities on O. stricta where it has no impact whatsoever, as this cactus species is a sub-optimal host. In February 2014, after the initial release had been approved by the regulatory authorities, the genotype of D. opuntiae, which has effectively controlled O. stricta in South Africa, was released onto Ol Jogi Conservancy through a CABI initiative, in partnership with Ol Jogi, the local community and other agencies. The control agent has established well at OI Jogi and has started to spread from the initial release sites, reducing flowering, fruiting and in many cases has resulted in the death of plants. Permission to actively release this agent at other sites has been granted by the National Environment Authority and further introductions will be undertaken on communal lands.
A concerted effort is needed to mass-rear and release the genotype of D. opuntiae, introduced to Laikipia County for the control of O. stricta, in other invaded areas across eastern Africa. This will hopefully reduce the negative impacts on local livelihoods and the environment. Additional resources are required for research, to validate some of the findings of this study, and to monitor the effectiveness of the introduced biocontrol agent. It is also critical that management interventions, especially biocontrol, be developed and implemented for a large number of other invasive alien plant species in eastern Africa. Failure to address plant invasions will drive rural communities further into poverty with serious social and political ramifications.
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We thank Winnie Nunda for assisting with surveys and data entry; Corin Pratt for data entry and analysis; Tim Beale for developing the distribution maps; landowners for access to their land to undertake the surveys, for providing accommodation (especially John Weller and other Ol Jogi staff); and Laikipia community members who participated in the survey. Funding was also made available by the CABI Development Fund, which is supported by contributions from the Australian Centre for International Agricultural Research, Australia, the UK’s Department for International Development, and others. Support for surveys and the production of distribution maps was provided by the GEF Small Grants Programme and JRS Biodiversity Foundation. We acknowledge support from the DST-NRF Centre of Excellence for Invasion Biology (C.I.B). During the writing of the paper ABRW was supported as a C.I.B Fellow. RTS acknowledges additional support from Stellenbosch University through “Consolidoc” funding through the office of the Vice Rector: Research, Innovation and Postgraduate Studies.
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Shackleton, R.T., Witt, A.B.R., Piroris, F.M. et al. Distribution and socio-ecological impacts of the invasive alien cactus Opuntia stricta in eastern Africa. Biol Invasions 19, 2427–2441 (2017). https://doi.org/10.1007/s10530-017-1453-x
- Biological invasions
- Distribution mapping
- Human well-being
- Local ecological knowledge