Nature on my doorstep

I know I’ve been away for a long time (has it really been four months?) but I have a good reason. I have just moved from Durham in the north of England all the way to Wales where I am working on a PhD project looking the effects of urban noise. It’s all very interesting and a lot of fun. Wales is also a beautiful place with lots of amazing countryside to explore and unique animals to see. I will talk more about my research soon but today I wanted to share a few pictures that I took while walking home from the beach this afternoon.

If you live in the UK you will know just how wet it has been recently, I don’t think I’ve seen the sun for two weeks and there is water everywhere. That’s why when I woke up this morning and saw the sun I planned to get out and make the most of it. There is a footpath that runs from just by my house and along the cliff tops by the beach. The views are fantastic and it is a great place to see seabirds wheeling and diving out in the bay, red kites flying overhead and I’m told that come summer it will also be possible to see dolphins swimming just offshore which I am inordinately excited about.

Thinking today would be a good opportunity for some wildlife photography I took my camera with me for a walk along the coast and managed to get what I think are some great shots of the town and a house sparrow (Passer domesticus*) perching in some bushes. I’ll be back with some proper posts soon but for now here are some pictures for you to enjoy. Ten points to whoever can guess the name of the town (without looking at my about page).

House sparrow (Passer domesticus) (7)

House sparrow (Passer domesticus) (3)

House sparrow (Passer domesticus) (4)

House sparrow (Passer domesticus) (5)

House sparrow (Passer domesticus) (6) _MG_0006

* Incidentally the house sparrow is the type species after which all song birds (Passerines) are named.


Two new species profiles on ARKive

Just over a year ago I was asked if I’d like to write some species profiles for the website ARKive as part of their ARKive and universities scheme. Well, it’s been a long time coming but my two profiles have finally been published! You can now go read all about Allen’s rainbowfish of northern Papua, a species that was only discovered in 1997. What ARKive doesn’t tell you is that this species has not been seen since its initial discovery and no one knows exactly where it was originally found. Thankfully several type specimens have been preserved as a record, although without a known location its conservation status is not clear.

Allen's rainbowfish
Allen’s rainbowfish (Chilatherina alleni)

You can also read about the Southern blue-ringed octopus of Australia, a beautiful animal but also one of the most deadly. At less than 15cm across its bite, containing the venom tetrodotoxin, has been known to kill humans, luckily for us they are not aggressive and generally shy away from people.

The southern blue ringed octopus
The southern blue ringed octopus (Hapalochlaena maculosa)

So, what is a species anyway?

A recent paper published in PLoS Biology estimated that the total number of eukaryotic species on the planet was 8.7 million (+/- 1.3 million). The sheer diversity of life on Earth is certainly breathtaking, if this figure is accurate it means that 86% of all land species and 91% of all marine species remain to be discovered. However, although we can now estimate how many species there are, there is still no definition of “species” that works in all situations. In fact there may be as many as 22 (or more) species concepts in use today (Mayden 1997).

The question of how best to define “species” is something that biologists have struggled with for well over a century, this has become known as “the species problem”. Charles Darwin himself mentioned it in On the origin of species saying:

No one definition has satisfied all naturalists; yet every naturalist knows vaguely what he means when he speaks of a species. Generally the term includes the unknown element of a distinct act of creation.

He later revised his view, writing in The descent of man:

But it is a hopeless endeavour to decide this point on sound grounds, until some definition of the term “species” is generally accepted; and the definition must not include an element that cannot possibly be ascertained, such as an act of creation.

In an ideal situation all of life could be neatly organised into discrete groups, completely isolated and distinct from one another. But the world is not ideal and nature is a lot messier than that. The boundaries that determine where one species ends and another begins are often blurred and overlapping.

One of the most widely used species definitions was proposed by the renowned evolutionary biologist Ernst Mayr and is known as the biological species concept or BSC. Mayr defined a species as:

groups of actually or potentially interbreeding natural populations, which are reproductively isolated from other such groups

Mayr’s definition works well in most cases, particularly for multicellular sexually reproducing organisms. However, for the small number of multicellular organisms that reproduce by parthenogenesis and for single-celled organisms such as bacteria and archaea this definition is useless. There are other situations in which the BSC is less than helpful. For example, some species may occasionally hybridise and produce fertile offspring. It is not clear whether reproductive isolation between species has to be absolute or if some small degree of hybridization is permissable under this definition.

The BSC is also difficult to apply to populations that change gradually over a continuous gradient such that neighboring populations can interbreed but populations at the far ends of the gradient cannot. This situation in known as a cline or, when the cline is circular, a ring species.

Take for example a hypothetical situation in which there are three neighboring populations which we’ll call A, B and C. Population A can successfully interbreed with population B and population B can successfully interbreed with population C. However, when A and C come together they are completely incompatible with each other and cannot interbreed. In this case it is not at all clear how many species should be recognised. We could classify A, B and C as three separate species but that doesn’t seem right since populations A and B or B and C do fulfill Mayr’s criteria by interbreeding. We could classify them all as one species but that doesn’t seem right either since A and C cannot interbreed and so do not fill Mayr’s criteria.

Schematic representation of a cline (A) and ring species (B and C).

Although unusual, situations just like the example above have been found in nature. One such case is that of the Greenish warbler (Phylloscopus trochiloides). This small and unremarkable bird from northern and central Asia occurs in Siberia in two distinct forms which have different colouration, different songs and which do not interbreed. In most cases this would be enough to classify these two groups as completely separate species. However, the two forms are linked by a continuous chain of gradually changing and interbreeding populations which encircle the Tibetan plateau to form a ring. Thus there is gene flow through the ring connecting the two Siberian populations yet there are no clear points at which the ring can be divided in separate species. At present Phylloscopus trochiloides is divided into five subspecies.

The Greenish warbler (Phylloscopus trochiloides)
Greenish warbler populations encircle the Tibetan plateau. Currently six populations are recognised each of which blends seamlessly into its neighboring population. Populations are represented in this image by different colours. Also shown are the song spectrograms showing variation between the populations. Image from Irwin et al. (2001). Click to enlarge.

An alternative to Mayr’s BSC that is growing in popularity is the phylogenetic species concept (PSC) this has been defined as:

a monophyletic group composed of the smallest diagnosable cluster of individual organisms within which there is a parental pattern of ancestry and descent

Put simply a species, as defined under the PSC, is a group containing all the descendents of one common ancestor that are united by traits that evolved uniquely in that population. These are known as derived characters and may be morphological, behavioural or chemical so long as they have a genetic basis and are heritable.

The PSC differs from the BSC in that it focuses on the phylogenetic history of organisms rather than their ability to interbreed. It therefore solves many of the problems with the BSC for example, hybridizing, parthenogenetic and clinal populations can be easily divided into species using the PSC.

However, although the PSC has many benefits it has also been criticised for not defining clearly how much variation is permissible within a species or how many derived characters are required to elevate a population to a species status. For example it has been suggested that derived character traits as small as one extra hooklet on the barbule of the primary feathers in a population of swans could, theoretically, distinguish that population as a distinct evolutionary unit and therefore as a separate species (McKitrick and Zink 1988). In this way the PSC has the potential to spilt populations up into very small groups which would be of no practical use to science.

The BSC and PSC are the two most widely used species concepts however there are many more.

  • As used by Linaeus and many other naturalists of his time the typological species concept was one of the first to be proposed. Under this concept species are groups of individuals united by shared morphology such that they can be distinguished from other groups. In other words they were groups of similar looking individuals. Typological species were defined by reference to a type specimen, usually kept in a museum, to which individuals could be compared. We now know that phenotypes can vary substantially within a species (e.g. amongst eusocial insects such as ants) and so the concept is no longer used.
  • Ecological species are defined as populations occupying the same ecological niche.
  • Genetic species are defined based on the similarity of DNA sequences. This may be determined by DNA fingerprinting or genome sequencing.
  • The mate recognition species concept defines a species as a group of organisms that recognize each other as potential mates. Like the BSC this only applies to sexually reproducing species.

“The species problem” is unlikely ever to be resolved. While species concepts have been developed that work well in a wide range of cases none is applicable to every situation. In the words of Theodosius Dobzhansky:

…the futility of attempts to find a universally valid criterion for distinguishing species has come to be fairly generally, if reluctantly, recognized.


Grant, P. R. & Grant, B. R. (1992) Hybridisation of bird species. Science 256, 193-197.

Irwin, D.E., Bensch, S. and Price, T.D. (2001) Speciation in a ring. Nature. 409, 333-337.

Mayden, R. L. (1997) A hierarchy of species concepts: the denouement in the saga of the species problem. Methodology. 54, 381-424.

Mayr, E. (1942) Systematics and the origin of species from the viewpoint of a zoologist. New York: Columbia University Press. p 334.

McKitrick, M. C. & Zink, R. M. (1988). Species concepts in ornithology. Condor. 90, 1-14.

Mora, C., Tittensor, D. P., Adl, S., Simpson, A. G. B. and Worm, B. (2011) PLoS Biology. 9, e1001127.

How does urbanization affect biodiversity?

Imagine that you’re standing in the very centre of a large city complete with roads, skyscrapers, traffic, noise and pollution. How much wildlife is there around you? How many species are there? How much of what you see is native?

Now imagine you walk in a straight line out of the city, for every mile you walk you stop and observe the wildlife, You count how many species there are (species richness) and how many individuals of each species there are (abundance). What you are measuring is biodiversity, the straight line you are walking along is a transect. By studying biodiversity at regular points along the transect you are able to observe changes as the habitat becomes increasingly rural, in turn this allows you to determine what effect (if any) the city has on biodiversity.

Approaching the city centre. Species rich or Species poor?

So, what might you expect to find? Does biodiversity increase or decrease in response to urbanization? Are different species found in cities than in rural areas? Is there no change at all?

Sadly, it is often the case that urbanization causes biodiversity to decline. As cities grow vital habitat is destroyed or fragmented into patches not big enough to support complex ecological communities. In the city, species may become endangered, or even locally extinct as previously natural areas are swallowed up by the urban jungle. In the United Kingdom for example, an increasing human population density, and the resulting increase in urban development were found to be the cause of 35% of scarce plant species extinctions in the counties surrounding urbanized areas (2). Similarly, in the United States urbanization has been found to be directly responsible for the endangerment of 275 species, only invasion by non-native species had a greater impact causing 305 species to become endangered (1). Ironically it is urban growth that is often responsible for the introduction of non-native species, either accidentally (e.g. the brown rat, Rattus norvegicus), or deliberately, for food, pets or for aesthetic reasons. Non-native plants for example, are often planted in urban and suburban gardens and subsequently “escape” into the wild (3).

Why does biodiversity decline in urban areas?

The growth of cities may cause biodiversity to decline by fragmenting or destroying large areas of natural habitat on which many species depend. The rising human population is driving the expansion of urban areas and increasing the demand for natural resources such as timber and fossil fuels. This inevitably leads to habitat destruction which has been called “the largest factor contributing to the current global extinction event”(4). The rate of urbanization is alarming, for example, in the city of Concepción, Chile, 1734ha of wetlands and 1417ha of agricultural land, forest and scrub was lost to urban development between 1975 and 2000 (5). Similarly, in the United States the amount of urbanized land has increased year on year since 1970. Over 5% of the US land surface is now urbanized, substantially exceeding the combined total of both conservancy and national park land cover (3).  Although there are many causes of habitat loss, urbanization has been shown to be one of the most damaging in terms of numbers of species lost or threatened (2).  Numerous studies have found that both the richness and abundance of native species including plants (1), mammals (6), insects (7) and amphibians (8) decrease in response to urbanization.

Closely related to habitat loss is habitat fragmentation which can be defined as the transformation of a large and continuous habitat into many smaller, isolated habitats. The expansion of cities causes the fragmentation of large areas of natural habitat through the construction of roads, houses and industry. In many cases all that remains are small remnant patches of the original habitat contained within the confines of the city. Biodiversity is greatly reduced when large areas of natural habitat are fragmented. Small habitat patches are unable to support the same level of genetic or taxanomic diversity as they formerly could (9), while some of the more sensitive species may become locally extinct (4).

How severely fragmentation affects biodiversity depends to a large extent on the size of habitat patch that remains. Many species require large contiguous habitat patches in order to maintain stable populations. Smaller patches therefore typically contain fewer species than do large patches. As an example, a study in the US looking at forest birds in fragmented and contiguous forests found that in fragmented forests brood parasitism and predation on the birds significantly increased whilst reproductive success declined (10). Similar effects have also been shown for reptiles. Predation pressure on the lizard Psammodromus algirus was found to increase as patch size decreased leading to the lizard’s  extinction in small patches while populations in large patches remained viable (11). Small patch size can also have genetic effects for example, it was found that populations of the plant Trillium camschatcense had much lower genetic diversity in fragmented habitat compared to those growing in contiguous habitat (12).

Understanding the impact of small patch size is critical for scientists and conservationists alike if biodiversity is to be preserved. However, it is not the only factor in need of consideration. The distance between habitat patches and the quality of the intervening land also have significant effects. For example, two closely spaced patches of woodland habitat separated by farmland are likely to be much more biodiverse than the same habitat isolated on either side of a city. Populations occupying habitat fragments are rarely self-sustaining, rather they act as sinks relying on immigration from larger stable populations to remain viable. As a result poor quality intervening habitat or a high degree of isolation may substantially reduce the long-term survival potential of fragment populations (12). Different species have different requirements, some may be able to tolerate high levels of fragmentation and isolation while other more sensitive species may not. However, if we are to preserve biodiversirty for the future reducing habitat loss and fragmentation should be priorities.

In addition to the twin effects of fragmentation and habitat loss there is another factor working to reduce biodiversity in urban areas. Biotic homogenization refers to the replacement of regional native (and often endemic) species with non-native, invasive and cosmopolitan species. Often it is the same non-native invasive species that are found in many cities worldwide (for example the rock dove Columba livia could be considered a global species), the result is a high species overlap between areas of formerly distinct biota, the homogenization of biological communities and a decrease in regional and global biodiversity (13, 14).

Many studies have shown that the expansion of the urban environment causes declines and local losses of native species including plants (1) and insects (15). As native species decline the number of non-native species rises. For example, as of 2006 New York city has lost 578 native species and gained 411 non-natives meanwhile, Massachusetts has lost over 330 native species and gained over 200 non-native species (16). It has been suggested that the increase of non-native species in urban areas may be due to one of two factors, (i) the importation into cities of non-native species and (ii) the city providing a favourable habitat for non-native species (16). Human settlements have been shown to provide ideal conditions for invasive and exotic species due to high levels of disturbance which tends to favour non-native species at the expense of native species (17).

The removal of native species from urban areas and their replacement with non-native species drastically alters the composition of urban biological communities, the ecology of cities is therefore very different to the surrounding undeveloped areas. For example urban bird communities are often composed of granivorous (seed eating) rather than insectivorous species (18), while insect communities have been shown to become more generalist towards the urban centre and more specialist in less urbanized environments (7).

Replacing native species with non-native species does not necessarily cause biotic homogenization. If different communities of non-native species replace native species at cities around the world then biotic differentiation rather than homogenization will have occurred. However, there is no evidence that this is happening. Many studies have shown that the extirpation of native species in urban environments and the influx and non-native invasive species is leading to global biotic homogenization. For example a study of urban bird populations from two distant locations (Ohio and California) found urban populations to be much more similar to each other than rural populations the same distance apart (19). Similarly, a study in Canada found that the ecology of cities across the country was becoming increasingly alike with many of the same species found in cities nationwide (14).

The trend towards global biotic homogenization of urban areas poses a serious threat to local, native species in countries around the world. The importation and introduction of exotic species is changing biological communities by forcing out local indigenous species, which may not be so well adapted to the urban environment, and replacing them with globally common and widespread species. If we are to preserve distinct regional species the importation of non-natives species should be discouraged and the diversity of native and indigenous species promoted and protected.

Does biodiversity always decline?

Perhaps surprisingly, no. Although many studies have found that declines in biodiversity and increasing urbanization are strongly correlated (5, 15), research has also shown that in some situations biodiversity actually peaks in suburban areas for certain groups such as insects (7), and plants (6). For example, it was found that in the Finnish city of Vantaa the number of vascular plant species was much higher on urban wasteland than in the surrounding forest. The reason being that wasteland contained large numbers of non-native introduced plant species while the forest did not (20).

Three explanations have been proposed that may explain the suburban peak in biodiversity, (i) The import of exotic species into urban areas increases species richness at a faster rate than native species are lost. (ii) Urban areas contain a large number of widely different habitats at small scales such as gardens, parks and wasteland. Each of these may provide very different habitats and so support a wide variety of species, urban gardens in particular are highly variable with no two containing quite the same combination of plants. (iii) The importation of large amounts of water, fertilizers and food into urban areas provides the nutrients required to significantly increase primary productivity. This in turn supports larger numbers of individuals than would be able to survive otherwise. These three proposals are not mutually exclusive, it is likely that all three (and possibly other factors) play a role in increasing urban biodiversity (6).

My research

I have been studying the effects of urbanization on biodiversity in the city of Leicester in the UK. By collecting arthropods along an urban-rural gradient I have been able to observe changes in species composition, richness and abundance. The diversity of arthropod communities then served as an indicator of the overall biodiversity of the sampling area.

Using sets of pitfall traps set at one mile intervals along the gradient, I collected just over 2000 arthropods belonging to more than 250 species over a period of one month. By identifying how many species and  individuals of each species were found at different locations along the gradient I was able to identify changes correlated with urbanization.

The aim of the study was to answer two questions. (i) Does urbanization affect biodiversity? And (ii) If so how?. Although these questions have been answered many times before the results have varied widely depending on location and experimental design of the studies. Previous studies have also often focused on a limited range of taxa such as bees (15) or plants (1), whereas this study aimed to examine biodiversity as a whole. Finally, with a few notable exceptions (1, 21) there has been little research of this type in Britain, the hope therefore, is that this study will provide an interesting insight into the response of Britain’s wild flora and fauna to urban development.


1. Thompson, K. and Jones, A. 1999. Human Population Density and Prediction of Local Plant Extinction in Britain. Conservation Biology. 13, 185-189.

2. Czech B, Krausman P.R, Devers P.K. 2000. Economic Associations Among Causes of Species Endangerment in the United States. BioScience 50, 593–601.

3. McKinney, M. 2002. Urbanization, Biodiversity and conservation. BioScience. 52, 883-890.

4. Fahrig, L. 2001. How Much Habitat is Enough?. Biological Conservation. 100, 65-74.

5. Paucharda, A., Aguayob, M., Peñaa, E., Urrutia, R. 2006. Multiple Effects of Urbanization on the Biodiversity of Developing Countries: The Case of a Fast-Growing Metropolitan Area (Concepción, Chile). Biological Conservation. 127, 272-281.

6. McKinney, M.L.. 2008. Effects of Urbanization on Species Richness – A Review of Plants and Animals. Urban Ecosystems. 11, 161-176.

7. McIntyre, N.E., Rangob, J., Faganb, W.F., Faeth, S.H. 2000. Ground Arthropod Community Structure in a Heterogeneous Urban Environment. Landscape and Urban Planning. 52, 257-274.

8. Riley, S.P.D., Busteed, G.T., Kats, L.B., Vandergon, T.L., Lee, L.F.S., Dagit, R.G., Kerby, J.L., Fisher, R.N., Sauvajot, R.M. 2005. Effects of Urbanization on the Distribution and Abundance of Amphibians and Invasive Species in Southern California Streams. Conservation Biology. 19 (6), 1894–1907.

9. Cane, J.H., Minckley, R.L., Kervin, L.J., Roulston, T.H., and Williams, N.M.. (2006). Complex Responses Within a Desert Bee Guild (Hymenoptera: Apiformes) to Urban Habitat Fragmentation. Ecological applications. 16 (2), 632–644.

10. Diaz, J.A., Carbonell R.,Virgos E., Santos T., Telleria J.L., 2000. Effects of forest fragmentation on the distribution of the lizard Psammodromus algirus. Animal Conservation. 3, 235–40.

11. Robinson, S.K., Thompson III, F.R., Donovan, T.M., Whitehead, D.R. and Faaborg, J.. (1995). Regional forest fragmentation and the nesting success of migratory birds. Science. 267 (5206), 1987-1990.

12. Tomimatsu, H., and M. Ohara. 2003. Genetic diversity and local population structure of fragmented populations of Trillium camschatcense (Trilliaceae). Biological Conservation 109, 249–258.

12. Donovan, T.M., Thompson, F.R., Faaborg, J., Probst, J. 1995. Reproductive success of migratory birds in habitat sources and sinks. Conservation Biology. 9 (6),1380–95.

13. McKinney, M.L. and Lockwood, J. L.. 2001. Biotic Homogenization: A Sequential and Selective Process. In: Biotic Homogenization. New York: Kluwer Academic/Plenum Publishers. 1.

14. Olden, J.D., Poff, N.L., Mckinney, M.L.. 2006. Forecasting Faunal and Floral Homogenization Associated with Human Population Geography in North America. Biological Conservation. 127 (9), 261-271.

15. Ahrné K, Bengtsson J, Elmqvist T. 2009. Bumble Bees (Bombus spp.) along a Gradient of Increasing Urbanization. PLoS ONE 4(5): e5574.

16. McKinney, M. 2006. Urbanization as a Major Cause of Biotic Homogenization. Biological Conservation. 127, 247-260.

17. D’Antonio, C., Meyerson, L.A., 2002. Exotic plant species as problems and solutions in ecological restoration: a synthesis. Restoration Ecology 10, 703–713.

18. Grimm, N.B., Faeth, S.H., Golubiewski, N.E., Redman, C.L., Wu, J., Bai, X., Briggs, J.M. 2008. Global Change and the Ecology of Cities. Science. 319, 756-760.

19. Blair, R.B., 2001. Birds and Butterflies Along Urban Gradients in two Ecoregions of the United States: is Urbanization Creating a Homogeneous Fauna. In: Lockwood, J.L., McKinney, M.L. (Eds.), Biotic Homogenization. Kluwer Academic/Plenum Publishers, New York, pp. 33–56.

20. Niemelä, J. 1999. Is there a need for a theory of urban ecology?. Urban Ecosystems. 3, 57–65.

21. Thompson K, Austin KC, Smith RM, Warren PH, Angold PG, Gaston KJ (2003) Urban domestic gardens (I): putting small-scale plant diversity in context. Journal of Vegetation Science 14, 71–78.