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Marine Species Introduced on the French Channel-Atlantic Coasts: A Review of Main Biological Invasions and Impacts

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The impacts of anthropogenisation modify permanently the distribution patterns of brackish and marine species. Globalization leads to a rapid increase of the numbers of introduced species anywhere in the world. Biological invasions often result in significant losses in the economic value, biological diversity and function of invaded ecosystems. This review presents the main pathways of introduction of non-indigenous species and the main benthic taxonomic groups being established and/or invasive along the French Channel-Atlantic coasts. A focus is put on main invasive marine species in the intertidal and subtidal zones of Brittany (France), among macroalgae (Sargassum muticum, Grateloupia turuturu, Undaria pinnatifida, Codium fragile and Gracilaria vermiculophylla), halophytes (Spartina alterniflora) and benthic invertebrates (Mollusks: Crepidula fornicata, Crassostrea gigas and Venerupis philippinarum). The species biology, introduction vectors, reproductive and dispersal capacities are considered, together with proliferation patterns along the Channel-Atlantic coasts. The ecological impacts of these species on the environment are also described, as well as the European regulations existing to limit alien species introduction and some examples of struggle against the invaders including eradication trials and biomass valorization. Last, the on-going impacts of global changes on alien species invasiveness along the Channel- Atlantic coasts are discussed.
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Open Journal of Ecology, 2015, 5, 227-257
Published Online May 2015 in SciRes. http://www.scirp.org/journal/oje
http://dx.doi.org/10.4236/oje.2015.55019
How to cite this paper: Stiger-Pouvreau, V. and Thouzeau, G. (2015) Marine Species Introduced on the French Chan-
nel-Atlantic Coasts: A Review of Main Biological Invasions and Impacts. Open Journal of Ecology, 5, 227-257.
http://dx.doi.org/10.4236/oje.2015.55019
Marine Species Introduced on the French
Channel-Atlantic Coasts: A Review of Main
Biological Invasions and Impacts
Valérie Stiger-Pouvreau, Gérard Thouzeau
*
UBO-CNRS, Institut Universitaire Européen de la Mer, UMR 6539 (LEMAR), Plouzané, France
Email:
*
gerard.thouzeau@univ-brest.fr
Received 15 March 2015; accepted 24 May 2015; published 29 May 2015
Copyright © 2015 by authors and Scientific Research Publishing Inc.
This work is licensed under the Creative Commons Attribution International License (CC BY).
http://creativecommons.org/licenses/by/4.0/
Abstract
The impacts of anthropogenisation modify permanently the distribution patterns of brackish and
marine species. Globalization leads to a rapid increase of the numbers of introduced species any-
where in the world. Biological invasions often result in significant losses in the economic value,
biological diversity and function of invaded ecosystems. This review presents the main pathways
of introduction of non-indigenous species and the main benthic taxonomic groups being estab-
lished and/or invasive along the French Channel-Atlantic coasts. A focus is put on main invasive
marine species in the intertidal and subtidal zones of Brittany (France), among macroalgae (Sar-
gassum muticum, Grateloupia turuturu, Undaria pinnatifida, Codium fragile and Gracilaria ver-
miculophylla), halophytes (Spartina alterniflora) and benthic invertebrates (Mollusks: Crepidula
fornicata, Crassostrea gigas and Venerupis philippinarum). The species biology, introduction vec-
tors, reproductive and dispersal capacities are considered, together with proliferation patterns
along the Channel-Atlantic coasts. The ecological impacts of these species on the environment are
also described, as well as the European regulations existing to limit alien species introduction and
some examples of struggle against the invaders including eradication trials and biomass valoriza-
tion. Last, the on-going impacts of global changes on alien species invasiveness along the Channel-
Atlantic coasts are discussed.
Keywords
Invasive Species, French Channel-Atlantic Coasts, Halophyte, Macroalgae, Mollusks, Impacts,
Remediation
*
Corresponding author.
V. Stiger-Pouvreau, G. Thouzeau
228
1. Introduction
The geographic distribution of species on the Planet is in constant evolution through increases, decreases or
shifting (horizontal/vertical niche movements for “northern” and “southern” taxa) of species distribution areas.
The latter are regulated by natural or anthropogenic mechanisms including ecological processes (natural disper-
sal of species), evolutionary mechanisms, and changes of environmental conditions (climate, hydrodynamics,
habitats, food availability, contaminants, etc.). These dynamics contribute creating local and regional biotopes
along time and defining biogeographical realms and ecoregions at global scale. WWF defines an ecoregion as a
large unit of land or water containing a geographically distinct assemblage of species, natural communities, and
environmental conditions. The boundaries of an ecoregion are not fixed and sharp, but rather encompass an
area within which important ecological and evolutionary processes most strongly interact. Several international
organizations have defined ecoregions: the Commission for Environmental Cooperation of North America, The
European Environment Agency (EEA-DMEER), the National Oceanic and Atmospheric Administration, the
World Wildlife Fund, etc. Thus, Brittany (west of France) belongs to the North-Atlantic Temperate realm and
comprises two marine ecoregions: the South European Atlantic Shelf and the Celtic seas (http://www.world
wildlife.org/science/ecoregions/marine/ecoregion_area3.html
). These two ecoregions are separated by the Ushant
thermal front off northwestern France, which acts for ages as a genuine geographical barrier.
The impacts of anthropogenisation modify permanently the distribution patterns of brackish and marine spe-
cies. Increasing shipping, aquaculture of mollusks, fish and macroalgae species (including species introduced
from Asia and North America), rise of aquarium trade and Lessepsian (Erythrean) migrations have led to in-
creasing introductions of non-indigenous species in the different ecoregions. In the Mediterranean Sea, the ma-
jority of alien species entered through the Suez Canal (53%) and an additional 11% were introduced primarily
through the Canal and then dispersed by vessels [1]. At global scale, at least one alien species would be invasive
in 84% of the 232 marine ecoregions [2]. The first introductions are ancient; thus, the steamer clam, Mya arena-
ria (Mollusca Bivalvia), would have been introduced in Europe by the Viking ships coming back from America
[3]. Globalization leads to a rapid increase of the numbers of introduced species and, subsequently, of the num-
bers of invasive species. Along the European Atlantic coasts, 50% of introductions of marine plants and algae
occurred after 1960 [3].
Once introduced, these non-indigenous species can settle and be invasive in some cases. It is now possible to
get a comprehensive overview of which alien species are present in Europe, their impacts and consequences for
the environment and society. More than 11,000 alien species have been documented by DAISIE (Delivering
Alien Invasive Species Inventory for Europe), a unique three year research project with more than 100 European
scientists, funded by the European Union that provides new knowledge on biological invasions in Europe. Bio-
logical invasions by alien species often result in significant losses in the economic value, biological diversity
and function of invaded ecosystems [4]. The majority of these 11,000 alien species are however, not harmful.
About 15% of these alien species would cause economic damages and 15% would cause harm to biological di-
versity that is the environment, habitats and native plants, animals and micro-organisms, according to the
DAISIE “Handbook on alien species in Europe” [5] (see also www.europe-aliens.org
). Species-specific review
of the impacts of invasive alien marine species on ecosystem services and biodiversity in the European Seas has
been published recently [4].
2. Definitions
2.1. Introduced Species
A given species is considered being introduced if it matches four criteria [6]: 1) the species is non-native to the
ecosystem under consideration; 2) its occurrence and development are directly or indirectly linked to anthropo-
genic activities; 3) its dispersal has created a geographic discontinuity between its original distribution area and
the colonized area; and 4) there is no need of man intervention to give birth to new generations of this species.
Thus, the latter is going to reproduce naturally and constitute self-sufficient populations allowing sustainable
settlement. Ultimately, this species will become a naturalized species.
Introductions of alien species are said “primarywhen the species are identified for the first time in a given
area that would be the French Atlantic-Channel coasts in this study. Introductions are “secondary” when they
come from introduction centers located elsewhere on the European coasts with a secondary transfer on the
V. Stiger-Pouvreau, G. Thouzeau
229
French coasts.
2.2. Invasive Species
According to the IUCN (http://www.iucn.org) definition, “invasive alien species are animals, plants or other or-
ganisms introduced by man into places out of their natural range of distribution, where they become established
and disperse, generating a negative impact on the local ecosystem and species”. Negative impacts encompass
economic (on fisheries, aquaculture, tourism, etc.) or environmental (on native species biodiversity, habitats,
biogeochemical cycles, etc.) harm or harm to human health (e.g. toxic harmful algae blooms).
The understanding of invasiveness (i.e. the ability of species to establish in, spread to or become abundant in
novel communities) and invasibility (i.e. the susceptibility of habitats to the establishment or proliferation of in-
vaders; [7]) requires solving two evolutionary paradoxes: 1) why does a non-native species succeed in estab-
lishing in and spreading to an ecosystem for which it is not adapted in theory, sometimes outcompeting native
species; and 2), why do invasive populations succeed so rapidly in adapting to their new environment.
2.3. The Keys to Introduction Success
The factors leading to the success or failure of the establishment of non-native populations are multiple and of-
ten difficult to determine or rank. Success likelihood is often defined from the propagule pressure that is a com-
posite measure of the number of individuals released into a region to which they are not native [8]. It incorpo-
rates estimates of the absolute number of individuals involved in any one release event (propagule size) and the
number of discrete release events (propagule number). As the number of releases and/or the number of individu-
als released increases, propagule pressure also increases [9]. This pressure, which also takes the potential exis-
tence of introduction hot spots into account, is generally high in coastal marine environment, partly due to the
vectors of introduction being involved. Introduction success will depend on the ability of the alien species to
overcome various “barriers” to and within its new environment, with several demographic, ecological and evo-
lutionary mechanisms being involved at each step.
1) Geographical barrier: to cross it, the population collected in its native environment must survive transport.
The intentional or accidental introductions of species via transoceanic transfers, even from one ocean to the oth-
er, bypass the natural dispersal processes. The species is said introduced.
2) Ecological barrier: various biotic and abiotic factors can weaken the introduced population. On another
hand, exotic species in their new environment are free from their native enemies, like predators and parasites:
this is the enemy release hypothesis [10] [11], which seems not to be always fully convincing [12]. The relations
developed by the nonindigenous species with its new environment are then crucial for its survival. The species
becomes acclimatized.
3) Reproduction barrier: the latter is limited, amongst others, by the depression of consanguinity, high in
small-sized populations. Population adaptation to its new environment, which improves the capacities of surviv-
al and reproduction, would play a key role in numerous cases. The species is naturalized.
4) Dispersal barrier: a species able to cross this barrier and to establish new populations in varied biotopes
will have chances to proliferate. The dispersal competence of a species will partly determine its invasion poten-
tial. The species phenotypic plasticity (local adaptations for reproduction, growth, etc.) promotes also the geo-
graphical expansion of introduced populations.
When a species is in the process of naturalization, the population size in its new environment will fluctuate
with time, both during the expansion and persistence phases [13].
2.4. Introduction Mechanisms
The relative importance (%) of the main pathways of introduction of non-indigenous species (NIS) across re-
gional seas of Europe in 2014 is shown on Figure 1 (http://www.eea.europa.eu/data-and-maps/figures/mode-of-
introduction-of-nis
). Marked geographic patterns depending on the pathway of introduction have been shown,
with specific countries acting as gateways to alien invasions [14]. France and Italy would be the countries most-
ly responsible for introductions by aquaculture, while Lessepsian species were first reported in the countries of
the Levantine Sea, especially Israel. Shipping is the most important pathway of introduction in European Seas
V. Stiger-Pouvreau, G. Thouzeau
230
Figure 1. Relative importance (%) of the main pathways of introduction of non-indigenous species (NIS) across regional
seas of Europe in 2014. Main pathways of introduction on the French Atlantic coasts are shipping and aquaculture. In many
cases, it is impossible to identify the introduction pathway. Where more than one pathway of introduction can be attributed,
the analysis has considered both modes of introduction. Thus the resulting percentage of introductions per pathway amounts
to more than 100%. Data from the European Environment Agency (http://www.eea.europa.eu).
[14]. In particular, numerous species take invasion corridors superimposed to the maritime shipping ways, in-
cluding the one extending between the North-West Atlantic and British waters [15]. Along the Channel-Atlantic
coasts, at least 104 non-indigenous marine or brackish species have been introduced [16]. The voluntary intro-
ductions resulting from aquaculture (macroalgae, fishes, mollusks: 13 species listed in 2002) have to be distin-
guished from the accidental introductions, via oyster spat transfers (25 species would have hitch-hike on oyster
shells), the ballast water of ships and boat hull fouling (38 introduced species by maritime ways). One counts
also 4 species of parasites introduced with other cultivated species (mussels or eels) and 11 species (at the time
of the census of 2002) for which the modes of introduction are unknown.
Today, it is advisable to add to these mechanisms of introduction those related to climate warming and chan-
ges, not always perceptible, of the main oceanic currents. Thus, fish species living in waters normally warmer
than Breton waters (triggerfish, seabreams, salema, bogue) are more and more regularly observed at the tip of
Brittany. Some of them undoubtedly constitute self-recruiting populations today, in particular among the de-
mersal species (the seabream hot spots of the spearfishing divers on the Finistère north coast are an edifying
example), whereas it is more difficult to find clear trends for pelagic fishes with great migration capacity [17].
The first seabreams (Diplodus sargus and D. annularis) were fished at the tip of Morgat in the Eighties. Some
specimens of salemas (Sarpa salpa) and bogues (Boops boops) were first captured in the trawls of the UBO
(Université de Bretagne Occidentale) scientists about 25 years ago in Douarnenez Bay, but it seems that the fish
shoals are increasingly dense over the years. It does not seem however that one or more of these alien species
became invasive along the Breton coasts. On another hand, Sardina pilchardus tends to disappear in the English
Channel; the reasons why remain to be determined. Major impacts of climate change on fish species distribution
have been also observed in Aquitaine and Gulf of Biscay waters [18].
V. Stiger-Pouvreau, G. Thouzeau
231
3. Inventory along the Channel-Atlantic Coasts
In the year 2002, 104 species were listed as introduced in the wild on the French Channel-Atlantic coasts since
the beginning of the 20th century [16], including 2 protists, 8 phytoplankton species, 21 macroalgae, 4 top plants,
68 invertebrates (including 22 mollusks) and 1 vertebrate (fish). Thus, invertebrates constitute the majority of
introduced species, followed by macroalgae.
Most of these introduced species are native of the Pacific (59%), followed by the East coast of the USA
(16%), the Mediterranean sea (7%), the North-East Atlantic (5%), the Indian-Pacific zone (5%), the South-West
Atlantic (2%), the Indian ocean (2%), etc. Invasion rate strongly increased from the 60s on (Figure 2), mainly
because of increasing shipping and aquaculture. It is thus not surprising that the main zones of introduction are
localized between the Normandy coasts and the Arcachon Basin that is the main seashell production sites of the
Channel-Atlantic coasts.
These introductions were most abundant in the 70s and still significant in the 90s, in spite of the setting up of
French and European legislations limiting the introductions of exotic species. The situation did not improve in
the years 2000 since a new census carried out in 2006 led to the enumeration of 153 introduced species (of
which ten were invasive), that is to say 12 new species per year on average on the Channel-Atlantic coasts [3].
4. Main Invasive Species in Brittany
On the 104 marine species introduced on the Channel-Atlantic coasts in 2002, 70 were established, i.e. settled,
reproducing, and thus constituting perennial populations, whereas 20 species had an unpredictable status. Only
14 species seemed not to have succeeded in establishing, thus highlighting the fact that non-native species tend
overall to colonize their areas of introduction. Today, about thirty introduced species can be considered as inva-
sive along the Breton coasts (http://www.bretagne-environnement.org/especes-invasives/
).
4.1. Macroalgae
France constitutes the European country most colonized by introduced species of macroalgae, with 22 species
first found on the French coasts (against 9 for England and 6 for Italy) [16].
The top 5 invasive species of macroalgae in Europe comprise, in order of importance, Codium fragile, Caul-
erpa taxifolia, Undaria pinnatifida, Asparagopsis armata and Grateloupia turuturu [19]: all these species are
present in Brittany and are considered for the moment as potentially invasive. Among the species of macroalgae
Figure 2. Numbers of records per decades of new non-indigenous species on the French and Span-
ish Channel-Atlantic coasts (in [16]).
V. Stiger-Pouvreau, G. Thouzeau
232
introduced in Brittany, Grateloupia turuturu, Codium fragile and Undaria pinnatifida are particularly interesting
to be studied like models of biological invasion. Even if it does not belong to the top 5 of the invasive species of
macroalgae in Europe, Sargassum muticum is the invasive species most studied in Europe, with Caulerpa taxi-
folia, in order to understand its proliferation, how to eradicate it (especially in the Mediterranean Sea) and how
to exploit it. Still nowadays, this species concentrates a lot of attention because of its large distribution in Europe,
its settlement in Northern countries (Ireland, Norway) and recently in the north of Morocco, together with nui-
sances caused by its growth in rock pools in summertime.
Sargassum muticum is a brown macroalga belonging to the order of Fucales. It is native of Japan and was in-
troduced in France via the transfers of the Pacific oyster (Crassostrea gigas), with two centres of introduction
(Figure 3(A)): a first one in the Eastern part of the Channel (end of the 60s) and a second one in the Thau la-
goon (1980). In less than 30 years, it colonized rocky shores all along the Atlantic coasts: its distribution extends
now from Norway to Portugal and to the Adriatic Sea. At the beginning of the introduction process, there were
tests of eradication in England and France, mechanical tests primarily, which all failed. This alga, strongly es-
tablished on the Channel-Atlantic coasts, is regarded henceforth as belonging now to the marine local flora. It is
a pseudo-perennial alga, which is very discrete from November to February but which presents strong biomasses
during the summertime. The individuals can reach important sizes and, as a consequence, a massive filling by
laterals of the surface of the rock pools in summer (Figure 3(B)). Only one generation is present during the de-
velopment cycle of this alga: it is the diploid meiosporophyte which produces gametes. Sargassum muticum is
Figure 3. (A) Main sites (hot spots) of introduction and proliferation of Sargassum muticum in Europe (beige: 1973-1980;
orange: 1981-1990; brown: 1991-2000; black: 2001 to today) modified according to the DAISIE (Delivering Alien Invasive
Species Inventories for Europe) project (http://www.europe-aliens.org). (B) Colonization of intertidal rock pools in summer.
(C) Colonization of subtidal areas.
B
C
A
V. Stiger-Pouvreau, G. Thouzeau
233
able to proliferate by marginal dispersal (release of the zygotes) and dispersal by jump (floating fragments of
thalli, aquaculture, fouling, etc.). S. muticum occupies all the rock pools in the intertidal zone and also forms
populations in subtidal zones (Figure 3(C)) along the French littoral. Most recent works on this species were
addressing ecological and ecophysiological processes [20]-[23]. On-going research is turned towards the com-
prehension of the mechanisms of species dispersal and recruitment, together with a potential valorisation of the
biomass by the search for bioactive molecules (see paragraph 7.2.).
Grateloupia turuturu is a red macroalga belonging to the order of Halymeniales. It is also originating from the
Pacific and was also introduced in France via transfers of the Pacific oyster, with two ways of introduction like
Sargassum muticum. G. turuturu has an important polymorphism; according to the colonized environment, the
thallus is represented by a foliaceous blade, which can be either single or divided (Figure 4(A)). This alga, also
originating from Japan, was present in Thau lagoon by 1982. It is a large-sized macroalga, described for the
moment like the tallest red alga since an individual of 3 m long was measured on the Callot Island, close to Ca-
rantec, in 1999 [24]. On the coasts of Brittany, the species was first described at Fort Bloq, on the commune
of Ploemeur close to Lorient in 1989, and in the second time in the area of Carantec, in the Callot Island, in 1992.
Both sites present an important oyster aquaculture activity. G. turuturu then dispersed in a marginal way (liberation
of spores), and by jumps, until currently occupying the rock points of north-Cotentin to the Vendée (Figure 4(B)).
This species, today very discrete in the colonized area, expects perhaps only one variation of one or several en-
vironmental parameters to become invasive. Ecological and biochemical studies were undertaken on Grate-
loupia turuturu recently [21] [24]. Populations are constituted of a mix of gametophytes and tetrasporophytes
and densities vary all year long. G. turuturu is a euryhaline species, producing osmolytes, like floridoside or
isethionic acid, for its osmoregulation [24]. On-going studies address the mechanisms of dispersal and osmo-
regulation of the species and potential valorisation of its biomass by the search of bioactive molecules.
Native of Asia, Undaria pinnatifida, also known under the name of “wakame”, is a brown macroalga, which
belongs to the order of the Laminariales and measures ca. 1 to 2 m long (Figure 5(A)). It is a species which
faced a world expansion since the years 1970 (Figure 5(B)). It was introduced via the aquaculture but several
ways of introduction would be at the origin of the populations observed in Brittany [25]-[27]. In Europe, it is a
species colonizing three types of biotopes: aquaculture zones, rockyshores (spontaneous populations) and artifi-
cial structures (wharfs, dykes, etc.). Undaria pinnatifida is an alga of cold moderate water which colonizes the
higher level of the subtidal zone, generally in areas characterized by strong tidal currents but not beaten [28]
[29]. According to the turbidity of the colonized zone, it can settle deeper in the subtidal zone, down to 15 m
depth. Undaria pinnatifida is an annual species presenting a sexual reproductive cycle characterized by an al-
ternation of haploid (gametophytes) and diploid (sporophytes) stages. The sporophytes are the macroscopic
phase of the cycle whereas the gametophytic stage is microscopic.
Figure 4. (A) Illustration of Grateloupia turuturu polymorphism according to the colonized environment: the foliaceous-
blade can be either single or divided [24]. (B) Main sites (hot spots) of introduction of G. turuturu in Europe modified ac-
cording to the DAISIE project (http://www.europe-aliens.org).
10cm
A
V. Stiger-Pouvreau, G. Thouzeau
234
Figure 5. (A) Thallus of Undaria pinnatifida on rocky shore. (B) Distribution according to the DAISIE project
(http://www.europe-aliens.org).
Codium fragile is a green macroalga of dark green color presenting a spongy morphology and axes which di-
vide by dichotomy (Figure 6). From a taxonomic point of view, it belongs to the order of Bryopsidales. It is a
species which dangerously proliferated at last century between various oceans but also between the two hemi-
spheres [30]. Regarded as native of Japan, it appeared for the first time on European coasts in the Netherlands in
the 1900s and then dispersed very quickly in Europe and colonized also the Mediterranean Sea [30]. Codium
fragile is a shade-loving species, which lives in the intertidal and subtidal zones on rocky shores all year long
(perennial species). The dispersal of C. fragile is made in a marginal way (emission of gametes, asexual repro-
duction by fragmentation) and by jumps (yachting, aquaculture, packaging of products for fish shop, floating of
fragments of thalli). A combination of both types of dispersal is at the origin of its fast proliferation in Europe.
Gracilaria vermiculophylla is a red macroalga (order of Gracilariales), which can form more or less dense
carpets in the intertidal zone of muddy shores and upper sublittoral zone, where it attaches to rocks or pebbles. It
was originally described in Japan in 1956 as Gracilariopsis vermiculophylla. It is thought to be native of and
widespread throughout the Northwest Pacific Ocean. It has been introduced to the East Pacific, the West Atlan-
tic and the East Atlantic, where it rapidly colonized new environments. Now, its distribution range in the
North-East Atlantic Ocean extends from Portugal to Norway. It can become very abundant in estuarine areas,
like in some streams from the Bay of Brest (Figure 7). G. vermiculophylla consists of a basal disc and a 4-
to-50-cm-long main axis with cylindrical alternate ramifications also ramified and flexible. It was identified in
1996 in the estuary of Belon and in 2002 in the Wadden Sea [31] [32].
At present, several invasive marine species of macroalgae in Europe, including S. muticum, C. fragile and
G. vermiculophylla, are investigated from an ecological point of view within the framework of an ERA-NET
Seasera and ANR project entitled “Invasive seaweeds in rising temperatures: impacts and risk assessments
(INVASIVES)”. This project aims to study the becoming of invasive species in relation with an increase of the
seawater temperature in the North Atlantic Ocean and to do predictions in regard of their potential development
on the Atlantic coasts.
4.2. Marine Plants (Halophytes)
The smooth cordgrass, Spartina alterniflora, is a perennial salt-tolerant herbaceous that grows in dense stands
along shorelines. It belongs to the order of Poales and to the family of Poaceae. It is native of the East coast of
North America and was introduced on the Western European coasts and North-West American coast. In Europe,
S. alterniflora was accidentally introduced during the 19th Century in Western France and Southern England
(Figure 7). In France, S. alterniflora was introduced in Brittany in the Bay of Brest (Elorn Estuary), and in the
Basque region near Hendaye (Bidassoa Estuary) [33]. S. alterniflora is a plant of the intertidal zone, where it
colonizes mud or sandflats in marine or brackish water. In Brittany, S. alterniflora colonizes the shores as well
© Yann Fontana
© S Gollasch 2008
A B
V. Stiger-Pouvreau, G. Thouzeau
235
Figure 6. (A) Distribution area of Codium fragile in 2008 (modified from B. Galil). (B) and (C) Codium morphology with
axes which divide by dichotomy.
as the top of the saltmarshes (Figure 8). The inflorescence is a flowering panicle made of many spikes and it is
10 - 40 cm long with dense colorless flowers, which are closely appressed and overlapping. Its alternate 2-D leaf
blades, which are grey-green in color, measure from 60 to 120 cm length. This plant spreads rapidly by frag-
mentation of its rhizome. It forms monospecific dense meadows, characterized by clonal populations. This spe-
cies exhibits high tolerance to many ecological factors, in particular tidal submersion. S. alterniflora is in com-
petition with annual native species like Salicornia [34]. In regions where S. alterniflora was introduced, it has
hybridized with indigenous species. A sterile hybrid between S. alterniflora and S. maritima was discovered in
1892 in the South-West of France in the Bidassoa estuary [35]. S. alterniflora is at the origin of another invasive
species, S. anglica. Indeed, in England, its hybridization with the native S. maritima gave rise to S. × townsendii,
V. Stiger-Pouvreau, G. Thouzeau
236
Figure 7. (A) Distribution areas of Gracilaria vermiculophylla and Spartina alterniflora. (B) and (C) Views of Gracilaria
vermiculophylla mats at low tide on intertidal mudflats (Photographies from G. Surget).
Figure 8. (A) Spartina alterniflora colonizing the upper zone of an intertidal mudflat. (B) Close-up view of the 2-D leaf
blades.
a perennial sterile hybrid. After 1890, S. × townsendii fertile plants were recorded in England; they resulted from
chromosome doubling in S. × townsendii, thus leading to the creation of S. anglica [35].
4.3. Mollusks
The main invasive species of benthic invertebrates in Brittany encompass Mollusk Bivalves (Crassostrea gigas,
Venerupis philippinarum known before as Ruditapes philippinarum) and Gastropods (Crepidula fornicata,
Gibbula albida), one Polychete species (Ficopomatus enigmaticus), 2 barnacle species (Cirriped Crustaceans:
Elminius modestus and Balanus improvisus), one crab (Decapod Crustacean: Hemigrapsus takanoi, which com-
petes with the native green crab), and one Tunicate (Styela clava). Only the case of the Mollusks is detailed be-
low.
A
B
C
Gracilaria vermiculophylla
Spartina alterniflora
© J. Versterren, 2014
V. Stiger-Pouvreau, G. Thouzeau
237
The American slipper limpet, Crepidula fornicata L., is native of the East coast of North America (from
Canada to the Gulf of Mexico); its introduction in Europe is ancient since it was first observed in the Bay of Li-
verpool in 1872. Introduction would be accidental, via repeated transfers of American oysters, Crassostrea vir-
ginica. The first observations on the European continent were made in 1911 in Belgium (Ostende). Along the
French coasts, it was first observed in Calvados (Hermanville) and in the Bay of Brest in 1949, with a secondary
dispersal in the English Channel and the Bay of Biscay. Nowadays, this species is found all along the Chan-
nel-Atlantic coasts (Figure 9); C. fornicata proliferates in bays and estuaries, reaching several thousands of in-
dividuals per m² [36]-[40].
The mechanisms of its introduction in France (Figure 10) include: 1) introductions starting in the 30s due to
seashell imports from England and the Netherlands; 2) a main introduction event in 1944 (during the second
World War) on the Calvados beaches and in the ports of Cherbourg and Brest (the slipper limpets were attached
to the hull of the landing ships), with a secondary dispersal along the Atlantic coast due to oyster transfers be-
tween culture areas; and 3) new introductions from British Columbia and Japan in the 70s. At that time, the Pa-
cific oyster started to stand for the Portuguese oyster in European oyster farming, the latter being wiped out by
diseases. Following the colonization of Atlantic oyster farms, all the French oyster farming areas, from Nor-
mandy to the Mediterranean Sea, have been progressively colonized by direct introductions. This third coloniza-
tion phase corresponds to the proliferation phase along the French coasts.
Recent studies in population genetics have focused on C. fornicata colonization patterns. In particular, the
study of genetic polymorphism of native populations (East-Atlantic coast) and alien European populations
looked for potential successive colonization steps. Colonization history turned out to be difficult to track how-
ever, since the various populations are genetically much diversified [41]. Thus, genetic diversity within the Bay
of Brest population is as high as diversity observed between several European populations [41].
Figure 9. Distribution of the slipper limpet, Crepidula fornicata, in Europe in the
1990s (from Blanchard, 1997; [36]).
V. Stiger-Pouvreau, G. Thouzeau
238
Figure 10. Main phases of introduction of the slipper limpet, Crepidula fornicata, in Europe (modified from [16]).
In the Bay of Brest, the slipper limpet proliferation was progressive, likely due to long-time changes in phy-
sico-chemical characteristics and trophic webs within the ecosystem. The first census in 1979 showed that the
species was mainly located in the southern basin of the Bay and the oyster farms of the northern basin. A fast
increase of the colonization process was recorded between 1995 and 2000 [39]: the slipper limpet biomass in-
creased from less than 20,000 tons dry weight in 1995 to ca. 85,000 tons DW in 2000 (Figure 11). The Center
of the Bay of Brest and the northern Basin were colonized at that time. However, carrying capacity of the Bay
(i.e. the maximum biomass per surface unit that a given site can support) was reached locally in the southern
Basin in 2000. Recent study by Ifremer in 2013 and 2014 showed strong decreases in total abundance and bio-
mass of C. fornicata in the Center and southern Basin of the Bay of Brest (A. Carlier, Ifremer, pers. comm.).
The reasons of this decline remain to be determined. Elsewhere in northern Brittany, the dynamics of Crepidula
proliferation would have been faster, possibly due to earlier colonization. Total slipper limpet biomass in the
Normand-Breton Gulf was estimated at 250,000 tons as early as 1974 [42], but speeding up of the colonization
was also observed between 1996 and 2004 in the Bay of Mont Saint-Michel. Repeated slipper limpet stock as-
sessments by Ifremer in this Bay showed that total biomass increased from 100,000 tons wet weight to 150,000
tons WW in the 8-yr period [40].
Crepidula fornicata, which is a protandrous hermaphroditic species [43], is ideal for investigating reproduc-
tive patterns in relation to sequential hermaphroditism. The patterns of gender allocation of this gastropod have
been investigated for almost an entire century [see [41]], an interest largely due to its grouping behavior. This
long-lived species (lifetime of ca. 10 years; [42] [43]) is typically found in stacks (i.e. groups of individuals at-
tached to each other), with larger (older) individuals, usually females, at the base and smaller (younger) indi-
viduals, usually males, at the top. Because fertilization is internal and these groups are perennial, they generally
constitute independent mating groups in which sex change occurs according to various factors including sex ra-
tio, number and size of individuals within the stack [41]. The location of the individuals within a stack remains
unchanged over time except for small individuals (male or immature), potentially imparting an advantage to
males directly attached above a female. The female at the base of a stack is usually fixed on a dead shell of slip-
per limpet, valves of the King scallop, Pecten maximus (Figure 12), or any other hard substrate. The invasive
potential of C. fornicata partly lies in the main features of its reproductive cycle: long reproductive period, an-
nual reproduction with multi-trials”, high female fecundity, internal fertilization between the males on top of
the stack and the females at the base, survival of brooded embryos and young larvae close to 100% with em-
bryos packed in thin-walled capsules attached to the substratum by a peduncle. The females incubate the cap-
sules between the propodium and neck [44]. Larvae are spawned after a three-week larval stage in the capsules
C. virginica
1872
1911
1944
C. gigas
C. gigas
1967
1967
C. virginica
1872
1911
1944
C. gigas
C. gigas
1967
1967
V. Stiger-Pouvreau, G. Thouzeau
239
Figure 11. Dry biomass (g dry weight m
2
) of Crepidula fornicata in 1995 and 2000 in the Bay of Brest (modified from
[39]). Total biomass in the Bay increased from less than 20,000 tons dry weight in 1995 to ca. 85,000 tons DW in 2000.
V. Stiger-Pouvreau, G. Thouzeau
240
Figure 12. (A) View typical of the Crepidula fornicata community in the southern basin of the Bay of Brest in the early
2000s. (B) Free stacks of slipper limpets. (C) Crepidula Stacks settled on Pecten maximus valves.
only if environmental conditions are good for survival (e.g. no harmful algae bloom at that time). In the Bay of
Brest, paternity assignment of larvae, sampled from a set of brooding females and carried out using five micro-
satellite loci, revealed that 92% of the crosses occurred between individuals located in the same stack [41].
These stacks thus function as independent mating groups in which individuals may reproduce consecutively as
male and female over a short time period, a pattern explained by sperm storage capacity. Gregariousness and sex
reversal are promoting reproductive insurance in this species. In addition, females are usually fertilized by sev-
eral males of the stack (78% of the broods were multiply sired), highlighting sperm competition [41]. Mating
behaviors and patterns of gender allocation vary in concert across sites suggesting that multiple paternities might
enhance sex reversal depending on sperm competition intensity.
The Pacific oyster, Crassostrea gigas, is a second example of introduced Mollusk species, whose proliferation
V. Stiger-Pouvreau, G. Thouzeau
241
along the French coasts is particularly dramatic. This oyster, native of South-East Asia, has been progressively
introduced on all the continents since the mid-20
th
century (1960-70) for aquaculture purpose. This species ac-
counted for 97% of the world oyster production in 2010 (http://www.fao.org/fishery/culturedspecies/Crasso
strea_gigas/fr
; 4.6 million tons in 2006). The Pacific oyster is now introduced in at least 48 countries, with wild
populations being established in 17 countries. Acclimatization is not fulfilled in 19 countries while the species
status still remains unknown in the last 12 countries [45]. The failure of species establishment in new natural
environments would result from introduction in environments too warm and oligotrophic for survival (e.g. Fiji,
French Polynesia, New Caledonia) or too cold for reproduction (e.g. Alaska). C. gigas has been introduced in
France in the Marennes-Oléron and Arcachon oyster farms from the late 60s on, to replace the Portuguese oyster,
Crassostrea angulata, which had been wiped out by two viral diseases. From 1971 to 1977, more than 10,000
tons of Pacific oyster spat were imported from Japan and ca. 560 tons of adult oysters from British Colombia
[45]. Nowadays, the French oyster production is ranked 4th in the world, with 116,000 tons produced in 2006,
but only 95,000 tons in 2010 due to summer mortalities (herpes virus).
The first oyster recruitments in the wild were observed in 1975 at Marennes-Oléron and Arcachon. In the 80s,
a few wild recruitments have been observed to the north of the Loire River, but the colonization remained spo-
radic at that time. From the mid-90s on, reproduction events increased further North, in Brittany: colonization
now extends, on the Channel-Atlantic coasts, from the Normand-Breton Gulf to the Spanish frontier (Figure 13).
The Bay of Brest and the Morbihan Gulf are heavily colonized, with oyster wild stocks reaching 10,000 and
6420 tons wet weight on ca. 3 and 5 km
2
, respectively [45]. The wild oysters colonize preferentially the intertid-
al sheltered rocky substrates (Figure 14), but also the discarded oyster farming devices, the slipways or the piers.
Oyster biomass can exceed 50 kgm
2
. Wild populations are also observed on mud and mussel beds. In the latter
case, oysters settle on mussel shells.
C. gigas is a particular protandrous hermaphroditic oviparous species: the individuals are usually male during
Figure 13. Colonization of the Brittany coasts by Crassostrea gigasin the late 2000s (from [45]). Signification of the density
indices: 1: <0.01 ind. m
2
, 2: 0.01 - 1 ind. m
2
, 3: 1 - 10 ind. m
2
, 4: 10 - 100 ind. m
2
, and 5: 100 - 1000 ind. m
2
.
V. Stiger-Pouvreau, G. Thouzeau
242
Figure 14. Proliferation of the Pacific oyster, Crassostrea gigas, on the intertidal rocky shore of the
southern basin of the Bay of Brest (Moulin Mer) in January 2005. Close-up view at high tide (crédit: Er-
wan Amice).
the first year of reproduction and then they change sex from one reproductive season to the other (erratic
changes). The oyster gonad is not a permanent organ. It develops around the digestive gland at each reproduc-
tive cycle during spring gametogenesis and declines after summer spawnings. C. gigas fecundity is very high: a
single female can spawn up to 60 million oocytes in one spawning [45]. Spawning occurs in one or several trials
in summer when water temperature is higher than 18˚C - 20˚C. Fertilization is external and the pelagic larval
phase is going to last ca. 3 weeks before metamorphosis and post-larval settlement occurs. Coastal water warm-
ing since the early 90s would have increased C. gigas proliferation along the Breton coasts, except for the Abers
region in the North Finistère where summer temperatures generally lower than 17.5˚C preclude oyster reproduc-
tion. The Pacific oyster is also absent in the Bays of Douarnenez and Audierne because of no oyster farming in
the area and tidal currents against larval drift for larvae originating from the Bay of Brest.
Third and last example of introduced Mollusk, the Manila clam, Venerupis philippinarum, is native of the
North-West Pacific (from the Kuril Islands to Java) and the Indian Ocean (up to Pakistan at the West). The Ma-
nila clam was subsequently introduced to Hawaii in 1929 and to the North-West coast of the USA ten years later
(accidental introduction). Naturally established populations are now present from Oregon to British Columbia.
The species was introduced for aquaculture purpose on the French (Brittany, Marennes-Oléron and Arcachon;
hatcheries and enclosure farming) and English Atlantic coasts between 1972 and 1980 [46]. Clam spat and ma-
ture individuals originated from the Seattle region and Puget Sound (USA). Manila clam farming quickly grew
in the 80s, thanks to hatchery and growing techniques which were developed to fit the species requirements.
However, Manila clam aquaculture is marginal in Brittany now, due to the brown ring disease (Vibrio pathogen)
and above all competition with fisheries which developed on natural clam beds. Acclimation of the Manila clam
to the wild has indeed generated large wild populations from 1987 on, from the northern part of Brittany to Ar-
cachon, particularly in the Arcachon Bay and Morbihan Gulf. Whether the Manila clam competes for space and
food with the native clam (Venerupis philippinarum) in these areas remains to be determined. At the European
scale, natural populations are found on the South coast of Great Britain and all along the French and Spanish
Atlantic and Mediterranean coasts (mainly in the Adriatic Sea). Venerupis philippinarum has also been reported
V. Stiger-Pouvreau, G. Thouzeau
243
from different other places in the world: Norway, California, Morocco, Tunisia, Israel and Tahiti (see [47]).
The Manila clam is an infaunal filter feeder that mainly lives in shallow embayments and estuaries. It is able
to tolerate temporarily freshwater inputs at low tide and its bathymetric distribution ranges from high spring tide
levels to a few meters deep into the subtidal zone. This species can be found in various soft sediments: coarse
sand, sand, muddy gravel, mud and in Zostera noltii meadows. As attested by its wide geographic distribution,
the thermal tolerance range of the Manila clam is wide; optimal growth temperature ranges from 20˚C to 24˚C
[47].
Venerupis philippinarum is a gonochoric species. As in most venerids, its gonad is a diffuse organ within the
visceral mass. Although exceptions can be found in cold waters, gametogenesis is initiated when water temper-
ature rises over 12˚C and lasts for 2 to 5 months before the first spawning events occur (see [47]). Spawning pe-
riods vary geographically. Along the French Atlantic coast, a major spawning event occurs in late Au-
gust-beginning of September (see [47]), with all the individuals of the population spawning synchronously. De-
pending on the environmental conditions, several asynchronous partial spawnings can occur between May and
the end of August. If environmental conditions are favorable, a late spawning event can still occur at the end of
fall. Planktonic life lasts for 10 to 15 days and post-larvae exhibit an active substrate selection process at settle-
ment in which they prefer sandy over muddy substrates [47].
5. Impacts on the Environment
The multiple ecological effects of invaders and their impacts on native species populations and related ecosys-
tems have been widely documented [48] [49]. At the ecosystem level, invasive species influence the processes
determining the carbon and nutrient cycling [50]-[55]. In aquatic environment, mollusks such as Dreissena po-
lymorpha, Venerupis philippinarum, Potamocorbula amurensis, and Crepidula fornicata are among the most
common invaders [36] [56]-[58]. These species are very active suspension feeders and their dense assemblages
may exert strong influence on suspended particulate matter [59]. The feeding activity of filter feeders results in
the packaging of suspended material into faeces and pseudofeces that settle to the bottom, diverting primary
production and energy flow from planktonic to benthic food webs and increasing the release of dissolved end
products of organic matter mineralization from the bottom [50]. In addition to stimulate benthic bacterial respi-
ration through biodeposition, suspension feeders also release carbon through their own metabolism [53] [54]
[56]. In shallow coastal waters, benthic communities dominated by dense populations of suspension feeders are
important zones for carbon cycling and may dominate ecosystem processes and metabolism [60].
More generally, the consequences of biological invasions include at the same time impacts on the environ-
ment, the various compartments of the food webs (biotic interactions: competition, predation, parasitism, dis-
eases, etc.), ecosystem functioning overall, and socio-economy (e.g. interactions with the biological cycles of
exploited species like the King and Queen scallops). Whatever their origin, invasive species can lead to major
changes in the structure, functioning and dynamics of coastal ecosystems. The main impacts of biological inva-
sions relate to: 1) the marine habitats: substrate type, near-bottom hydrodynamics and shear stress, increased
light penetration due to filter feeding, number of microhabitats (spatial and/or trophic niches); 2) the native bio-
diversity (strong decrease in general); 3) the ecosystem structure and functioning (sediment chemistry, biogeo-
chemical fluxes, food web complexity, biotic interactions within the same trophic niche, etc.); and 4) the human
uses of marine resources: yachting, fishing, aquaculture, tourism, etc. A review of the ecosystem engineering at-
tributes of non-indigenous invasive bivalves can be found in [61]. Sargassum muticum, Crepidula fornicata and
Crassostrea gigas are the three main biological models used in this section to illustrate the effects of the prolif-
eration of alien marine benthic species on coastal ecosystems. Indeed, the former are among the species having
the most detrimental impacts on French Channel-Atlantic coasts.
5.1. Impacts of Sargassum muticum Proliferation
S. muticum seems to be in regression now, while many ecological and economic impacts were noticed in the
past. Nevertheless, this introduced species can still cause momentary awkwardness in summertime, but without
comparison with the environmental disturbances of the 1980s.
Ecological impacts. When the populations become dense, Sargassum muticum competes for space, light and
nutrients with the other benthic macroalgae. The important canopy formed by S. muticum during summertime
creates a genuine screen, which prevents light diffusion (Figure 3(B)). It can thus reduce and even prevent the
V. Stiger-Pouvreau, G. Thouzeau
244
development of the other macroalgae. Part of the native Laminaria digitata forest was decimated by the arrival
and proliferation of Sargassum muticum in the Channel in the 90s [13]. In fall, this phenomenon fades since the
algae laterals often separate from the main axis and float or sink, which reduce the screen effect. The competi-
tion for space between S. muticum and the other macroalgae is stabilized today, in particular because of the ad-
aptation of native species, like other macroalgae, epiphytes, or grazers like the sea urchin. As an example, S. muticum
is now sharing space with the native Sargassaceae, i.e. Cystoseira baccata. or Bifurcaria bifurcata, in rock pools
from Brittany [22] [62]. In some sites, the Laminariales species are rare or even totally absent because strong
water turbidity precludes photosynthetic activity. In such habitat, S. muticum, which is much more tolerant, be-
comes a structuring species by providing shelter and protection to many associated fauna and flora (Figure
3(C)). Fish larvae, adult fishes and crustaceans take refuge under the canopy while the cuttlefish drops off its
eggs on the algae axis, etc. Once grounded as foreshore, S. muticum becomes a food source for amphipods.
Economic impacts. Several human activities are constrained in sites exhibiting strong density of S. muticum.
Shellfish farming is the most impacted: 1) S. muticum settle on oyster shells in culture creating extra work at
harvest; 2) The algae make harder the access to the oyster farms and maintenance of the culture devices: laterals
of S. muticum roll up around the feet of mussel beds and oyster tables or settle on longlines and weigh down
them; 3) The fishing activities are also impacted with navigation problems (propellers or turbines clogged by the
algae) and fishing gears becoming inefficient (pots and nets overloading, hanging and loss of the hooks in the
algal canopy, etc.). The floating vesicles of the macroalgae can also clog the engine cooling system.
5.2. Impacts of Spartina alterniflora Proliferation
Only ecological impacts are mentioned. Spartina alterniflora produces viable seeds and multiplies vegetatively
by propagated rhizomes at the same time [34]. Generally, colonization starts from individualized circular spots
which, by coalescence, end up constituting monospecific meadows with rounded contours. This pattern, which
characterizes a clonal organization, clearly differentiates this species from the other vegetable formations of the
intertidal zone. Few saltmarshes in Europe are colonized by S. alterniflora. In the Bay of Brest, a long-time
study allowed understanding its expansion and characterizing its ecological consequences on the intertidal eco-
system. Observations carried out from 1952 to 2004 in three sites of the Bay [63] showed that S. alterniflora
first settled on upstream sites, on mud de-salted by freshwater, and also on the upper parts of the bare slikke.
Then, it gradually progressed towards the main channels together with the substrate raise. In the same time, new
spots of colonization appeared downstream in the middle of the mud flats on both sides. Expansion continued in
all the directions including within the schorres already present; the latter were progressively colonized starting
from the upper slikke and the secondary channels. Today, many areas of the Bay are largely covered by S. alter-
niflora, with considerable impacts on the environment as shown by the conceptual model of changes that Spar-
tina can generate on physical, chemical, and biological processes (Figure 15). Spartina reduces light and tidal
water flow and increases deposition of fine sediments and sediment organic matter. The increased belowground
biomass together with changes in the sediments results in increased levels of sulfide and decreased ammonium
levels, which can negatively affect other plants and animals [64]. These changes result in increasing detrital
loads and decreasing productivity of benthic microalgae, which favor subsurface deposit feeders and detritivores
at the expense of grazers, suspension feeders, and surface deposit feeders. The shift toward smaller, subsurface
species may reduce invertebrate food resources for larger consumers such as crabs, birds, and fishes [64].
S. alterniflora first impacts the sedimentology of the colonized areas, because the species is an ecosystem en-
gineer, i.e. a species able to create, maintain, modify, or destroy their habitat, and is capable to collect the sedi-
ments [65]. Indeed, its rigid stems decrease tidal flow rate, causing suspended sediment to precipitate, while the
dense rhizomes system traps the sediment [65]. In New Zealand, sediment accumulation rates of 4 cmyr
1
have
been reported in S. alterniflora meadows, while adjacent bare mud showed no change. Still in New Zealand, the
introduction and the expansion of S. alterniflora and S. anglica are responsible of an accumulation of sediment
likely draining the marshes and the mangrove swamps [66]. Another interesting aspect is the capacity of S. al-
terniflora to provide a substratum for a diverse assemblage of epiphytic microalgae that contribute significantly
to saltmarsh primary production and estuarine nitrogen fixation [64]. Moreover, S. alterniflora is a siliceous
plant which can potentially act like a silicon pump and modify biogenic silica recycling and silicate inputs to the
coastal environment. By comparing invaded and not invaded salt marshes, Queret al. [67] estimated that Si
retention is 2-fold higher in the invaded marsh (8%) than in the free marsh (4%). Moreover, biogenic silica bu-
V. Stiger-Pouvreau, G. Thouzeau
245
Figure 15. Modifications in ecosystem structure and functioning due to the invasion of Spartina alterniflora on salt marshes,
showing positive (+) and negative (−) effects on a range of physical, chemical and biological processes (from [64]).
rying increases by 50% in the colonized salt marshes.
As to native communities, introduced Spartina species are often inferred to outcompete native saltmarsh
plants in the intertidal zone. The ecological impacts of Spartina invasions have been documented primarily
through observational studies. The invader develops in spots which progressively join and constitute monospe-
cific meadows being responsible for native species extinctions in some cases. Moreover, S. alterniflora often has
a canopy higher than that of the native species, which reduces significantly light penetration to the sediment in-
terface [68]. Consequently, the production of benthic microalgae is much weaker in salt marshes invaded by
Spartina and dominant primary producers switch from benthic microalgae to Spartina [68]. The expansion of
S. alterniflora in the Bay of Brest resulted in the replacement of annual halophyte communities such as glass-
worts Salicornia procumbens, Suaeda maritima, and Halimoine portulacoides, but also Limonium humile, a
protected perennial species whose only populations in France occur in the Bay of Brest (UICN red list since
1995) [69]. Post-invasion changes in the physical and chemical characteristics of the environment have also
major impacts on the benthic macrofauna. The development of the canopy allows an increase of the epifauna
[68], while the important biomass of Spartina rhizomes and changes of organic matter quality resulting from the
dead biomass lead to a significant reduction of the infauna diversity [70]. The benthic macrofauna switches from
a community dominated by filter feeders to a detritivore-dominated assemblage [64] [71]. Finally, shore birds
face habitat loss for food due to the reduction of the bare mud zones in the colonized areas [64] [72] [73].
5.3. Impacts of Slipper Limpet Proliferation
Ecological impacts. Many experimental and in situ studies performed in the Bay of Brest showed that C. forni-
cata would play a key role in ecosystem functioning as an ecosystem engineer [74] and biological filter [37] [38]
[51]-[55] [75]. The latter does not help sustainable management actions such as dredging-regulated biomass de-
creases for environmental restoration in the Bay. C. fornicata colonized more than half of the benthic surface
area in the early 2000s [39] and induced both economic and ecological consequences through disturbance of
mollusk cultures and fisheries, and shifts in benthic community species composition and trophic structure [37]
[38]. The ecological risk associated with the proliferation of the slipper limpet was due to increased competition
for space and food between benthic species (the colonized surface area increased from 45 km
2
in 1978 to 90 km
2
V. Stiger-Pouvreau, G. Thouzeau
246
in 1995) and biodeposition rates extremely high. If the reasons of increased colonization rate in the late 1990s-
early 2000s remain unknown, the ecological impacts of Crepidula proliferation on the sediments, other benthic
species and ecosystem functioning have been well established:
- Sediment silting due to biodeposit production (faeces and pseudofaeces) by the slipper limpet [37] [76];
- Decrease of macrofauna species richness at Bay scale (70 species were considered endangered in 1998; [76])
due to bottom homogenization and constitution of a faunal assemblage typical of the Crepidula community
(whatever the original assemblage before colonization);
- Decreases of the King scallop (Pecten maximus) and Queen Scallop (Aequipecten opercularis) stocks and
distribution areas in the Bay, the latter presenting an exclusion relationship with C. fornicata [37] [76]. This
negative interaction between scallop species and the slipper limpet is due to the fact that scallop post-larvae
cannot settle and survive on muddy Crepidula bottoms. Stock decrease, increased production costs (more
time required to sort the dredge contents and clean the scallop shells) and recurrent toxic events due to
harmful Pseudo-nitzschia blooms and domoic acid bioaccumulation in the King scallop digestive gland have
led to the fishery closure in recent years;
- Control of the phytoplankton primary production (annual microalgal total biomass and species succession).
Several studies [38] [51]-[55] [75] showed that 1) the decrease of chlorophyll biomass during the first spring
bloom would result from silicic acid limitation and increased suspension feeder activity; 2) benthic filtration
and biodeposition activities would enhance biogenic silica retention at the sediment-water interface; and 3)
recycling of trapped biogenic silica would maintain diatom populations by providing silicic acid in summer
and would reduce primary production seasonality. These results suggest that benthic organisms control the
export rate of biogenic silica towards the open-water ocean and thus the specific composition of secondary
phytoplankton blooms in the Bay;
- Impact on the hydrodynamics and transport properties of the benthic boundary layer. These results were ob-
tained combining three different approaches: 1) in-situ measurements of near-bottom current and suspended
sediment concentration on two sites in the Bay of Brest (high vs. low Crepidula density); 2) velocity mea-
surements in controlled laboratory experiments of flows over a bed of artificial Crepidula shells and 3) nu-
merical simulations of the flow over two-dimensional shell-like bed forms [74]. Numerical and laboratory
experiments showed that both the bed erosion and the exchange velocity between the canopy and the outer
flow decrease as the roughness density increases. These results suggest a sheltering effect by the Crepidula
shells increasing with the surface density of shells. This trend was also found in field measurements: during
spring tides, higher particle resuspension was observed on the muddy sand bottom with few chains of slipper
limpets compared with the high-density area. C. fornicata is a main ecosystem engineer whose shell stacks
would modify food availability for suspension feeders and surface deposit feeders;
- Changes in biogeochemical fluxes at the water-sediment interface (O
2
, CO
2
, nutrients). In the early 2000s,
the estimated annual Crepidula community respiration in the whole Bay of Brest was found higher than the
overlying phytoplankton and microphytobenthos carbon production in the bay [54]. C. fornicata is thus con-
sidered as a source of carbon influencing pCO
2
in seawater and favoring CO
2
effluxes to the atmosphere.
The proliferation of C. fornicata since the pre-invasion, 50 years before, to the 2001 situation would have
increased carbon release by a factor 1.5, corresponding to 10,000 tons C yr
1
[54]. Both the slipper limpet
respiration and shell calcification contribute to carbon release, since carbon release by C. fornicata shell cal-
cification represents 20% of carbon release by C. fornicata respiration [53]. The respiration of the other
components of the community, micro-, meio- and macro-organisms, also contributes to the increase of pCO
2
in seawater. Community respiration in sites with high C. fornicata densities in 2000-2001 (530 g C m
2
yr
1
)
falls within the highest range of values reported for communities displaying high mollusk densities (230 -
600 g C m
2
yr
1
; see review in [56]). At global scale, calcified benthic organisms living in estuaries would
produce as much CO
2
as the Great lakes or the whole Earth volcanoes [56]. This biogenic source of CO
2
is
increasing constantly due to continuous mollusk introductions and high capabilities of the latter to colonize
new habitats.
The researches performed in the Bays of Saint-Brieuc and Bourgneuf, and in the Marennes-Oléron and Arca-
chon basins led to results partly similar on the impacts of C. fornicata proliferation in these ecosystems, though
colonization dynamics exhibited local characteristics [77]-[80].
Economic impacts. In the Bays of Brest and Saint-Brieuc, the slipper limpet proliferation threatens the sus-
tainability of scallop (Pecten maximus) fisheries. In the Bay of Brest, the local fisheries committee has initiated
V. Stiger-Pouvreau, G. Thouzeau
247
in the mid-2000s a containment project intending to make the scallop restocking program consistent with the
alien species presence in the fishery. The issue is complicated by the occurrence of harmful microalgae blooms
affecting the scallop fishery. A model dealing with the economic impact of the invasive process and a metho-
dology for cost-benefit analysis of invasion management have been realized [81]. The invasion has a marginal
direct cost, because fishermen have to scrape C. fornicata fixed on scallop shells on board, and a major indirect
cost due to the reduction of habitat suitable for scallops. According to numerical simulation, the invasion is a se-
rious threat to the economic viability of the restocking program and invasion management would help maintain-
ing the long term sustainability of the fishery. Recurrent algal blooms cut the initial net present value of the tra-
ditional scallop restocking program by approximately 25%, and the invasive process reduces it by approximately
two thirds. Combining restocking and local control of the invasive process could reduce the cost of invasion by
55% in present value terms. Sensitivity tests highlighted the importance of long term equilibrium scallop catches
on the program results, depending on scallop farming technical performance and ecosystem disturbance. In par-
ticular, sensitivity tests suggested that uncontrolled consequences of harmful microalgae blooms occurring more
than every two years would definitely ruin the economic sustainability of the restocking program, whether or not
associated to local invasion control.
In the Bay of Saint-Brieuc, where the biological invasion by C. fornicata is addressed by a control program, a
bioeconomic model of the commercial scallop fishery has also been established [82]. The model combines the
dynamics of the two competing stocks and analyzes the equilibrium of the fishery under various assumptions
concerning invasive species control. According to the simulations, the control program generates a cumulated
global present value which is greater by approximately 25 percent than the laissez-faire scenario, whatever the
variant considered for the invasive species harvest function. Moreover, invasive species control allows sustaina-
ble fishing, while the laissez-faire scenario implies long term non-sustainability. The results emphasize also the
importance of the starting date of the control program. Postponing this date is not neutral, because the level of
invasion which is to be addressed by the program is time-dependent, and the discounted present value of a set of
cash flows depends on their time-pattern.
5.4. Impacts of Crassostrea gigas Proliferation
Ecological impacts. The impact of Crassostrea gigas proliferation on native intertidal communities is variable.
The Pacific oysters large filtration capacity and eco-engineering characteristics induced many changes in re-
ceiving ecosystems. All estuaries are not affected in the same way; in the Dutch Oosterschelde estuary, expand-
ing stocks saturate the carrying capacity whereas in the Wadden Sea no such problems exist [83]. According to
the latter, the Pacific oyster seems to fit well within continental NW European estuarine ecosystems and there is
no evidence that the invader outcompetes native bivalves. In the Netherlands and neighboring countries, C. gi-
gas induces major changes in plankton composition, habitat heterogeneity and biodiversity, carrying capacity,
food webs and parasite life cycles [84]. In particular, C. gigas may change entire ecosystems through cascading
effects on other trophic levels. Thus, the increased filtration pressure in the Oosterschelde estuary due to an in-
creased oyster stock already appears to have affected the phytoplankton community [83]. The oysters exert a
top-down control on phytoplankton abundance and composition that may in turn affect higher trophic levels in
the food web (e.g. zooplankton fish fish-eating birds and seals). Similarly, the oysters might induce cas-
cading effects by exerting a top-down control on zooplankton abundance and composition.
In Brittany, the impact of the Pacific oyster on native communities is low as long as the oyster distribution
stays 2-dimensional (low to moderate oyster densities). By contrast, when colonization amplifies and 3-D oyster
reefs start to develop on the rocky shore or the mudflat, the impacts on benthic communities become obvious
[45] [84]. Total abundance and species richness of the macrofauna are higher on oyster reefs and the relative
abundances of taxonomic and trophic groups are modified. By contrast, the analysis of sediment grain size, se-
diment organic matter content and ecological groupings did not reveal any perturbation of the infauna due to
organic matter enrichment. Opposite trend was found on rocky substrates of Bahía Anegada (Argentina) where
C. gigas reefs trap sediments at higher rates than bare rocky platforms, increasing the habitat available for in-
faunal polychaetes (see [61]). Last, the comparison of benthic species associated with oyster reefs on Breton
rocky shore and soft bottom did not highlight homogenization of intertidal communities, contrary to what is ob-
served for the slipper limpet community.
The studies undertaken in Brittany did not allow showing an impact of oyster reefs on mobile predator abun-
V. Stiger-Pouvreau, G. Thouzeau
248
dances (fishes, crustaceans and birds). These impacts have been demonstrated elsewhere (see [45] [83] for re-
view). In the Wadden Sea for example, the proliferation of oyster reefs on the intertidal mudflats would be re-
sponsible for the disappearance of the oystercatchers (Haematopus ostralegus). In the Bay of Brest, changes in
diet behavior have been observed for the herring gull (Larus argentatus): the birds have learnt to feed on adult
oyster specimens who drop off the reef and stay lonely on the sediment. Thus, the herring gulls have developed
complex behaviors, the oysters being dropped off from several meters high, even several times in a row, until
the oyster shells smash [45].
Oyster proliferation does impact biogeochemical cycles at the water-sediment interface. The study of oyster
reef respiration and calcification in the Bay of Brest [85] has shown that C. gigas does not breathe during the
emersion time, contrary to other intertidal species [86]. Only the biofilm living on the oyster shells contributes
(for 3.5%) to the oyster CO
2
total production during low tide. Oyster CO
2
production (respiration) only occurs
during the flood. Carbon annual production by oysters, 36 g C m
2
yr
1
[45] [85], is similar to carbon production
of another intertidal species, the barnacle Chthamalus montagui [86]. Carbon total annual production of the
rocky shore intertidal community would be multiplied by 20 (762 g C m
2
yr
1
) when C. gigas occurs in high
density (700 ind. m
2
), compared with a substrate without oyster [86]. If the 3 km
2
colonized by C. gigas in the
Bay of Brest were covered by this oyster high density, the annual carbon production of oysters would corres-
pond to the mean annual production of more than 1100 cars of medium engine size (mean production of 175 g C
Km
1
and mean distance travelled per year of 12,230 Km; SOFRES 2005 data). C. gigas does not impact the in-
tertidal community respiration at low tide, but oyster reefs would favor benthic primary production: the reefs
would protect the microalgae from desiccation and high lighting, thus limiting photoinhibition in summer.
Socio-economic impacts. The Pacific oyster proliferation along the NW European coasts generates also vari-
ous nuisances for the users of the maritime domain. The colonization of harbor facilities (piers, wharfs, etc.) and
aquaculture devices increases maintenance activities (the damages of nautical equipment can be important). The
multiplication of sharp-edged oyster reefs in the intertidal zone disturbs people moving and increases the risk of
being cut for foot-walking fishermen and swimmers. Finally, and unlike subtidal invasive species, oyster proli-
feration leads to clearly visible landscape transformation not always well accepted by the users. For oyster far-
mers, the proliferation of wild oysters within the farms is two-edged: it allows collection of wild oyster spat
which is resistant to Vibrio-regulated summer mortalities, but the extra costs due to the cleaning of aquaculture
devices may be prohibitive. Some oyster farmers of the Bay of Brest are currently transferring their production
in the Aber Benoît or in the Paimpol sector (Côtes d’Armor), i.e. sites where wild recruitment does not occur.
Cleaning the seabed from dead oyster shells is also a main concern in the Arcachon basin where the biomass of
dead shells has been estimated to 50,000 tons Wet Weight in 2011 [87]. By contrast, the development of oyster
reefs may compensate for habitat loss and biodiversity loss in estuarine environments that were caused by hu-
man activities in the previous decades. In the Wadden Sea, oyster reefs may in the future play an important role
in the capturing of sediment and the protection of tidal flats from erosion, thereby buffering the effects of sea
level rise due to global warming [83]. In the Arcachon Basin, the biomass of wild oysters (65,000 tons vs.
16,600 tons WW in culture) could sustain oyster farming which is facing massive summer mortalities. Spat col-
lection and harvest of wild oysters on the mudflat are two management options proposed by the French Marine
Protected Areas Agency, together with the creation of protected zones to maintain spat production potential [87].
6. European Regulations Existing to Limit Introduction of Alien Species
The environmental awareness of the risks related to the biological invasions is relatively recent. Many interna-
tional conventions emphasize the need for containing them; the 1982 Montego Bay Convention on the Law of
the Sea (http://www.un.org/depts/los/convention_agreements/texts/unclos/unclos_e.pdf
) stipulates in particular
that “the States must take all the necessary measures to prevent, reduce, and control the intentional or accidental
introduction in the marine environment of foreign or new species which can cause considerable or harmful
changes”. The BWM (Ballast Water Management) Convention of the IMO (International Maritime Organiza-
tion), adopted in February 2004, imposes the exchange from at least 95% of the volume of ship ballast water at
least at 200 nautical miles from a coast and in water depth higher than or equal to 200 m. This convention in-
cludes also a standard (BWPS, for Ballast Water Performance Standard), which sets limits at the number of
lived organisms released with ballast water. This standard will be applicable only when the new ships will be
equipped with systems of water treatment (by 2016 normally). As for the BWM convention, it requires 30 sig-
V. Stiger-Pouvreau, G. Thouzeau
249
natory countries to come into effect, which is not yet the case: at the end of 2009, only 18 countries had signed
this convention including four European countries (Spain, France, Albania and Norway). Yet, there is no inter-
national legislation enforced with regard to ballast water exchange in the open sea [3]. In France, the Strategic
Action Plan for marine environments set by the Ministry for Ecology and Sustainable development (MEDD)
recommended in 2005 to support a well-argued management of marine areas and to preserve the marine natural
heritage and biodiversity (short note No. 3). The setting of a “plan of intervention against the invading exotic
species” was one of the identified actions, without knowing how, nor with which means, this plan could be im-
plemented.
7. Struggle against the Invaders: Eradication or Sustainable Management?
Invasive alien species represent the second most significant cause of species extinction worldwide after habitat
destruction (https://www.iucn.org
). They are often accompanied by serious healthcare consequences and can be
a threat for animal and human health, or result in considerable economic and financial damages. They can com-
pete with native species, act as pests or pathogens for cultivated or domesticated species, or even disseminate
allergic or infectious agents. Three strategies are possible to struggle against the invaders: 1) eradication, always
difficult, even impossible; 2) control, i.e. maintaining the abundance of the introduced species at a level such as
its ecological or economic consequences become bearable: this control must be repeated regularly and is an ex-
pensive process; and 3) prevention: the most effective and least expensive strategy, it requires nevertheless the
setting up of an effective legislation on a worldwide scale.
7.1. Eradication Trials and Biomass Control
To date, there are few examples of successful eradication or effective struggle against marine invasive species
[88]. The reasons may vary, but it is clear that the multiplication of the vectors of introduction makes the intro-
ductions of species difficult to control. Eradication is not, a fortiori, possible when it relates to an edible species
like Crassostrea gigas, whose exploitation generates important incomes.
There is a well-accepted set of conditions which must be met for the eradication of any population. These
standard conditions for success include proper planning, putting the entire population of the invader in jeopardy,
removing the individuals faster than they reproduce, and preventing re-invasion. Additional conditions are sup-
port from local people and the ability to demonstrate the benefits of the eradication project. The case of Caul-
erpa taxifolia in California is meaningful: field containment and treatments began 17 days after the notification
of infestation in Agua Hedionda lagoon on June 12, 2000. Three well-integrated components of this rapid re-
sponse would have resulted in an effective eradication program: 1) expertise and knowledge on the biology of
C. taxifolia; 2) knowledge on the uses, ownershipand characteristics of the infested site; and 3) knowledge
and experience in the implementation of aquatic plant eradication [88]. Together, with the requisite resources
(approximately $US1.2 million per year), this approach has resulted in containment, treatment and excellent
progress toward eradication of C. taxifolia. Elsewhere, few marine invasions have resulted in response actions
and, among them, a limited number have succeeded. Two examples of eradication trials on the French Chan-
nel-Atlantic coasts, which gave opposite results, are given below.
The brown macroalga Macrocystis pyrifera, also called the giant kelp, represents one example of eradication
success in Brittany. This species was introduced in Brittany in 1970s for aquaculture to develop the industry of
alginates. M. pyrifera produces a high-quality alginate allowing good yields for harvesters [89] [90]. It was first
recorded in 1972 in Roscoff [16]. Its cultivation in Brittany was permitted on the basis that low water tempera-
tures would preclude reproduction by spores. Nevertheless, its cultivation was banned later on in Normandy
when it was clear that the alga could complete its reproductive cycle with the temperatures occurring in the Eng-
lish Channel and the North Sea [91]. In Brittany, it was decided to eradicate M. pyrifera when considering its
competition with native laminarian species on rocky shores. Eradication was successful because the giant kelp
was found only in its introduction sites on rocky substrates, thus limiting the likelihood of dispersal, and because
only small populations with low reproductive rates were introduced.
The winkle Japanese oyster drill Pteropurpura inornatus is a good illustration of the difficulty of fighting
against the proliferation of an alien species. This exotic predator, a little bit larger than the indigenous winkle
driller, Ocenebra erinacea, is native of the North-West Pacific. It initially invaded the East coast of the Pacific
between 1920 and 1940 and was first observed in the Marenne-Oléron basin in 1995. P. inornatus would have
V. Stiger-Pouvreau, G. Thouzeau
250
been introduced with Pacific oyster imports. This winkle driller is a bivalve predator generating increased preda-
tion on cultivated oyster stocks. It is likely to compete with O. erinacea, the two species occupying the same
ecological niche. The localized initial distribution (Marenne-Oléron) of P. inornatus - one did not find it in the
Ré Island for example - aroused eradication tests as soon as its first records. Three types of actions were under-
taken, primarily by the Regional Section of Conchyliculture: 1) destruction of the ovigerous capsules using pro-
pane burners; 2) incentive harvest operations in the intertidal zone; and 3) pot fishing using oyster meat like bait.
Today, the species is present from Brittany, except perhaps for Finistère, to Arcachon Bay; it is considered inva-
sive on the Breton coasts (http://www.bretagne-environnement.org/especes-invasives/
).
The relevance of the measures of struggle against the invader, often wished by the various categories of users
impacted by the biological invasion, is not always obvious; the case of Crepidula is a good illustration in two
ways. 1) In the Bay of Brest, during the early 2000s, bottom cleaning (dredging of Crepidula) on a large scale
was once planned in order to grow hatchery-produced scallop juveniles in areas which had become unfavourable
for scallop survival and growth. However, several studies emphasized the potential role of biological filter
played by C. fornicata in the Bay. In particular, filtration and biodeposition activities of Crepidula and benthic
remineralisation were found to sustain summer diatom production whereas the dystrophic conditions in summer
should lead to the recrudescence of non-siliceous microalgae species (of which the toxic dinoflagellates) [38].
Thus, large-scaled bottom cleaning at that time could have had disastrous consequences on ecosystem function-
ing and survival of commercially exploited species. In 1995, summer blooms of Gymnodinium cf nagasakiense
led to mortality of all the scallop post-larvae produced at the Tinduff hatchery, no recruitment of scallop juve-
niles in the wild and strong decreases in daily shell growth of 1-year-old and older individuals (juveniles and
adults). The risk to see increasing summer blooms of toxic phytoplankton species could not be neglected, be-
cause of the excess of nitrate and the associated silicate shortage in river inputs. 2) In the Bays of Saint-Brieuc
and Cancale, massive extractions of Crepidula were carried out between 2002 and 2007. Two ships extracted
110,000 tons WW (instead of the 175,000 tons initially scheduled) before the dredging was stopped. In addition
to the lack of profitability of the project, one could note that the bottom-cleaned zones were recolonized very
quickly. This pattern may be related with data from Arcachon Bay showing that the Crepidula P:B ratio was
higher in sites where this species was facing anthropogenic perturbations [92]. On the whole, more than 1.5 mil-
lion euros would have been spent to remove Crepidula from northern Brittany, without convincing result
(Ouest-France, edition of June 15th, 2007).
Crassostrea gigas is an example for which both eradication trials and control of the wild biomass have been
performed (see [93] for review). In Australia, C. gigas is considered a noxious species in areas where it can
outcompete native oysters. A comprehensive methodological approach to best practices for the management of
introduced marine species has been developed by the Australian Global Invasive Species Program. Notably, in-
cluding lessons from terrestrial bioinvasions and clues to evaluate the side effects of eradication methods, this
approach also stresses the importance of risk assessment, surveillance, and the development of adequate infor-
mation, coordination, and legislative tools. Information tools have been developed by the National Introduced
Marine Pest Information System (NIMPIS; http://www.marine.csiro.au/crimp/nimpis/
; http://adl.brs.gov.au/ma
rinepests/
), which also aims to provide potential control options. However, none of the methods described have
proven to be totally effective for the eradication of C. gigas [93]. A similar approach has been enforced by
northern European countries, where the Nordic-Baltic Network on Invasive Species database (NOBANIS;
http://www.nobanis.org
), based on the Australian information system, was implemented. However, despite these
efforts, the Netherlands is the only European country where significant mass reduction trials have been con-
ducted. In France, several studies have been carried out in the Marennes-Oléron Basin, the Gulf of Morbihan,
Bourgneuf Bay, and at a national level. The collection of such data is an essential preliminary step towards the
determination of the most appropriate actions, taking into account the particular characteristics of individual
sites [93]. The Marennes-Oléron Basin is an example of successful reduction measures. Indeed, the restructuring
of leases in the Basin, enforced over the last 15 years, allowed a significant reduction of wild stocks in farmed
areas. The thorough removal of wild C. gigas and, at the same time, its trophic competitor Crepidula fornicata
and predator Ocinebrellus inornatus, involved the use of powerful caterpillar tractors and snow ploughs espe-
cially equipped for marine activities.
7.2. Valorization of Invasive Species
When eradication cannot be set up, a possible way of regulating the proliferation of invasive species is the ex-
V. Stiger-Pouvreau, G. Thouzeau
251
ploitation of their important biomasses. Thus, the invaders become potential marine resources for diverse indus-
trial sectors. According to the species, various types of valorization are looked for. In Brittany, the marine ma-
croalgae being exploited are Sargassum muticum, Grateloupia turuturu, Codium fragile and Undaria pinnatifida.
S. muticum proves to be a species producing active biomolecules acting like anti-microfouling [21] [94]-[97]
(interest for shipyards). Antioxidant molecules and anti-inflammatory drugs were also isolated from S. muticum
[22] [23] [98]-[102], with potential outlets in the cosmetics and Para pharmacy sectors. G. turuturu also produc-
es anti-microfouling molecules [95] [103] and molecules which act against the European abalone pathogen Vi-
brio harveyi [104], as well as great quantities of R-phycoerythrin red pigment interesting various industrial sec-
tors [105] [106]. This species was also studied for its biochemical composition to be proposed as an edible spe-
cies [107]. C. fragile is exploited for cosmetics in Brittany [30] and Undaria pinnatifida for agri-food (4 tons of
algae collected from algoculture in Brittany in 2008). The natural populations of the latter are not exploited, due
to biomasses being not sufficient.
With regard to Crepidula fornicata, several attempts have been made until now (fresh product or transforma-
tion into fertilizers, limestone soil enrichment product and feed meal) with poor success, due to low economic
profitability. The current studies, in the field of human health, are directed towards the search for active mole-
cules with high added value. Antimicrobial properties, the chelation of heavy metals or the trapping of phos-
phate are targeted. The food trail was also revived by 3 Breton SMBs, with the opening of a treatment plant of
Crepidula in Cancale in January 2009. Three shipyards from Cancale supply the factory which is expected to
treat 10 to 20 tons per day. The sector of exploitation is double: the meat is used to design new dishes in agribu-
siness industries, whereas the shell is exploited to replace the maërl as marine soil enrichment product or to
produce pet food (calcium supply), once crushed. Today, a SMB (www.Britexa.com
) also markets this shellfish
exclusively and offers the product raw and in the form of recipes developed in partnership with Breton indu-
strialists and a well-known Michelin-starred chef.
8. Conclusion
The ecological impact of aquatic invasive species is a growing concern for coastal zone management and con-
servation. The French Channel-Atlantic coasts make no exception, mainly due to international shipping and aq-
uaculture practices. France even constitutes the European country most colonized by introduced species of ma-
croalgae. Cost-benefit analysis of invasion management is not simple when several living resources economics
are based upon the species invasiveness patterns (e.g. in shellfish and macrophyte aquaculture). Crassostrea gi-
gas may be considered a pest in the Wadden Sea or in Australia where it outcompetes native oysters, but it sup-
ports a large fishery in France at the same time. Furthermore, there are numerous historical cases showing that
initial “under control” does not mean permanent under control, even after several decades. Understanding inte-
ractions between human activities, ecosystem functioning and global changes is critical for further management
options. New approaches should be developed to prevent any unintentional introduction as well as to limit side-
effects of on-going invasions. One cannot be optimistic when considering the on-going impacts of global change.
Thus, the French Atlantic coast is facing at least three major environmental changes (P. Goulletquer, Ifremer,
pers. com.): 1) mean annual seawater temperature is increasing regularly (ca. 1.5˚C over the last 25 years); 2)
there is a clear positive trend in the North Atlantic Oscillation; and 3) there is a drastic decline of freshwater in-
puts due to weather change and concomitant modifications in watershed activities (e.g. irrigation practices for
agriculture). The marinization of estuaries leads to increased potential risks for new marine species invasions
due to harbor proximity, while global warming favors the establishment of alien subtropical species (e.g. the
harmful dinoflagellates of the genera Ostreopsis and Gambierdiscus in the Bay of Biscay). By definition, inva-
sive species are capable to adapt to their new environment and they are best suited to face global changes. What
about the native species which are not used to such environmental changes? Though global change is progres-
sive, are all the species (native and invasive) going to adapt or are we going to observe homogenization of the
flora and fauna at global scale?
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