There is however a strong correspondence between AA and the development of open field systems in the mediaeval period, with 53% of AA units in the UK formed within the last 1000 years (Fig. 2). In Fig. 3 AA units are plotted by UK regions, with the first appearance of AA in southeast, central, southwest and northeast England, and in central and south Wales at c. 4400–4300 cal.

BP. AA in southeast, southwest, central England Autophagy inhibitor as well as in Wales is associated with prehistoric farming. In southwest England and Wales there was significant AA formation during the mediaeval and post-mediaeval periods. AA in southern Scotland and northwest and northern England appears to be associated with mediaeval land-use change. In Fig. 4 AA units

are sub-divided according to catchment size where study sites are located. Most dated AA units fall either in catchments of <1 km2 find more or are found in ones with drainage areas that are >100–1000 km2. The smallest catchments (<1 km2) have no dated AA units before c. 2500 cal. BP and most occur after c.1000 cal. BP. It is also perhaps surprising how few 14C-dated anthropogenic colluvial deposits there are in the UK, making it difficult to reconstruct whole-catchment sediment budgets. AA units from the larger catchments (>100 km2) show a greater range of dates with the earliest units dating to c. 4400 cal. BP. Fig. 5 plots AA units according to sedimentary environment. Channel beds (Fig. 5A) record earlier-dated AA, whereas AA units in palaeochannels (Fig. 5B), on floodplains (Fig. 5C) and in floodbasins

(Fig. 5D) increase in frequency from c.4000 cal. BP, and especially in the mediaeval period. One possible explanation for the early channel bed AA units is that channel erosion MRIP or gullying was contributing more sediment than erosion of soil, and that this was a reflection of a hydrological rather than a sediment-supply response to human activities (cf. Robinson and Lambrick, 1984). The earliest coarse AA unit in the UK uplands is dated to c. 2600 cal. BP (Fig. 6) with 73% of gravel-rich AA formed in the last 1000 years, and a prominent peak at c. 800–900 cal. BP. Fine-grained AA units in upland catchments have a similar age distribution to their coarser counterparts, and 80% date to the last 1300 years. By contrast, AA units in lowland UK catchments, outside of the last glacial limits, are entirely fine-grained and were predominantly (69%) formed before 2000 cal. BP, especially in the Early Bronze Age and during the Late Bronze Age/Early Iron Age transition c. 2700–2900 cal. BP. Fig. 7 plots relative probability of UK AA classified according to their association with deforestation, cultivation and mining. The age distributions of AA units attributed to deforestation and cultivation are similar with peaks in the later Iron Age (c.2200 cal. BP).

Abgesehen vom kontrovers diskutierten DMT-1, beobachteten Wang et al. eine Hochregulation von MTP1 (Metalltransportprotein 1) und des Transports mittels TfR im isolierten Plexus chorioideus der Ratte (der die Blut-Liquor-Schranke umfasst) als eine frühe Gewebeantwort auf eine Exposition gegenüber Mn oder Fe [61]. Des Weiteren kann Mn von den divalenten Metall-Bicarbonationen-Symportern ZIP8 und ZIP14, von verschiedenen Calciumkanälen, von der Familie SLC39 (Solute Carrier 39) von Zinktransportern, von park9/ATP13A2, vom Magnesiumtransporter hip14 und von den TRPM7-Kanälen/-Transportern Selleck Dabrafenib (Transient Receptor Potential Melastatin 7) transportiert werden [56]. Gitler et al. [62] haben vor kurzem berichtet,

dass das PARK9-Gen, das für das frühe Ausbrechen des Parkinsonismus verantwortlich ist, ebenfalls Mn transportiert. Es codiert für ein mutmaßliches Transmembran-ATPase-Protein vom P-Typ. Darüber hinaus haben die Mitglieder der SLC39-Familie

von Metallionentransportern eine hohe Affinität für Mn. Ihr Km von 2,2 μM für Mn2+ lag nahe bei der physiologischen Konzentration [7]. Schließlich scheint auch der Citrat-Transporter am Mn-Transport über die BBB beteiligt zu sein [56]. Es ist vorgeschlagen worden, dass ein dreizähniger Mn-Citrat-Komplex mit einer nicht-koordinierten find more zentralen Carboxylat-Erkennungsstelle ein Substrat des Transporters für organische Anionen oder eines Monocarboxylat-Transporters (MCT) sein könnte. Da die Aufnahme von Mn-Citrat aus einem Medium mit pH-Wert 6,9 effektiver war als aus einem Medium mit pH-Wert 7,4, wurde ein H+-abhängiger Mechanismus angenommen [3], der damit vereinbar wäre, dass MCT-1 die Aufnahme von Mn-Citrat vermittelt. Darüber hinaus könnten u. U. noch weitere zelluläre Prozesse an der Regulation

der Aktivität obenerwähnter Transporter in Antwort auf Mn-Mangel oder -Überladung beteiligt sein. Schließlich spekulierten Jursa und Smith [63], dass Ceruloplasmin im Gehirn eine Rolle beim Efflux von Mn spielen könnte. Es wird angenommen, dass neben der Akkumulation von Mn im Gehirn auch die Induktion von oxidativem Stress in den betroffenen Gehirnregionen eine Rolle bei der Neurotoxizität von Mn spielt. Mn ist ein Kofaktor einiger wichtiger Enzyme, die an der Erhaltung des oxidativen Gleichgewichts beteiligt sind, wie z. B. der Superoxiddismutase (SOD) [64] oder der Acetylcholinesterase (AchE). Bei einer Studie an Neuroblastomzellen, die mit MnCl2 behandelt GABA Receptor wurden (200 und 800 μM), zeigte sich eine signifikante Abnahme der spezifischen Aktivität der Mn-SOD, Cu/Zn-SOD, der Katalase (CAT) und der Glutathionperoxidase (GPx). Interessanterweise erhöhte die Kultivierung dieser Zellen in Anwesenheit von Silymarin die Aktivität signifikant, was nahe legt, dass Silymarin Schutz gegen Mn-Toxizität bieten könnte [65]. Dies eröffnet ein mögliches neues Anwendungsfeld für Silymarin bei der Prävention des Manganismus und sollte daher weiter untersucht werden. Bei einer neueren Studie von Santos et al. erhielten Ratten 4 bzw.

However, it contradicts qualitative findings suggesting that cancer patients do distinguish Ganetespib in vitro between

dimensions of trust [11] and [26]. This apparent discrepancy deserves further research attention. As yet, it appears difficult to quantitatively expose patients’ possible distinction between trust dimensions. Further validation among specific groups of cancer patients with likely more varying levels of trust should be conducted, e.g., among second opinion patients, immigrants, or patients in palliative care, to investigate if the TiOS is responsive to more pronounced dimensionality and varying trust levels. The current results contribute to research on cancer patients’ trust in their oncologist. Use of the TiOS allows further expansion of this field of study, resulting in better insight into the nature, predictors, and consequences of cancer patients’ trust. Confidence in the

cross-cultural validity of the TiOS enables its use in different countries, allowing direct comparisons between patients’ trust levels internationally. Ultimately, this could improve patient care. Our findings suggest that the English translation of the Trust in Oncologist Scale is suitable for use among English-speaking cancer patients in Australia and other countries with similarly organized health care systems. For the present we suggest that when applying the TiOS, a single score can be used. However, for a more refined understanding of patients’ trust, one might test whether patients in a specific sample distinguish AG-014699 in vivo different dimensions of trust. This study was financially supported by the Dutch Cancer Society (Grant number: UVA 2008-4015). In addition, Marij Hillen received a travel grant from the Dutch Cancer Society. We would like to acknowledge Karen Bird for her kind assistance in the Dimethyl sulfoxide recruitment of patients. “
“Cardiovascular disease (CVD) is the leading cause of death in the industrialized world [1] and [2]. Dyslipidemia is an important

risk factor for CVD, estimated to cause 18% of cerebrovascular disease and 56% of ischemic heart disease [3]. Cholesterol lowering has been the primary goal of therapies aimed at CVD risk reduction, and several randomized studies have demonstrated the benefits of statins (hydroxymethylglutaryl-CoA reductase inhibitors) in the reduction of cardiovascular-related events within high-risk patient groups [4]. Currently, statin drug treatment is one of the most important treatment strategies when managing patients with, or at high risk of, CVD. Adherence is defined as the extent to which a person’s behavior, such as taking medication, following a diet or executing lifestyle changes, corresponds with the recommendations from a health care provider [5].

Due to its toxicity, most of the fly ash is landfilled

after detoxification, or recycled as a secondary material [26]. Since some of the elements (e.g. Cu and Zn) are present in high concentration and may permit an economic recovery, fly ash may be considered as an artificial ore [5]. The leached and recovered metals may be recycled for re-use as raw materials [17]. Conventional pyro- or hydro-metallurgical techniques in fly ash detoxification and heavy metal recovery include thermal treatment, chloride evaporation process and chemical leaching. Although these techniques provide a rapid treatment and complete destruction of toxic compounds in fly ash, they are very energy intensive and result in the release of hazardous emissions during treatment. The high cost and the negative environmental impact of conventional methods have led to the investigation Ipilimumab of bioleaching (considered a clean technology) as an alternative in the extraction of heavy metals from fly ash [24] and [26].

The main focus in bioleaching was initially the recovery of metals from insoluble metal sulfide minerals in mining ores, based on the ability of microorganisms VE-822 ic50 to oxidize reduced iron and sulfur compounds, via the production of organic or inorganic acids. There are patents on pilot- or commercial-scale bioleaching plants, with most focused on low-grade ore [8]. Recently, however, there have been interests in the application of bioleaching in industrial wastes as increasingly vast quantities of hazardous industrial wastes (such as spent catalyst, electronic waste, MSW incineration fly ash etc.), are generated [4] and [30]. Although much has been reported on bioleaching by the chemolithoautotrophic acidophilic microorganisms of the genus Acidithiobacillus, fly ash is not a suitable substrate for bioleaching due to its high pH [26]. Acidithiobacillus sp. grow well under pH 2–3, while fungi are generally able to grow over a wide pH range, from 1.5 to 9.8 [7] and [26]. Fungal bioleaching of Cell Penetrating Peptide heavy metals have been reported for solid wastes including

electronic scrap material [6], spent refinery processing catalyst [2] and [27] and incineration fly ash [5], [31] and [33]. In general, bioleaching may be conducted using either one-step or two-step. In the former, the microorganism is incubated together with the metal-bearing waste. In two-step bioleaching, the microorganism is first cultured in the growth media and incubated for a period of time before the metal-bearing waste is added to the culture and the incubation continued. In order to better exploit this intrinsic capability of selected microorganisms for metal leaching and recycling, more efforts are needed to understand the behavior of both the microorganisms and the metal substrate during bioleaching.

, 2009 and Price et al., 2012). By influencing the extent to selleck screening library which mating duration is extended following exposure to rivals males can therefore respond adaptively to the likely level of sperm competition ( Parker et al., 1996 and Parker et al., 1997). Such responses are therefore predicted to be strongly selected. However, it cannot be discounted that the extension of mating duration could be driven by female responses to the type

of male encountered. Our data suggest that the extension of mating duration in this context is indeed under male control, as responses by males to the potential threat of sperm competition were seen in matings with intact and with decapitated females in which female responses to males should be minimised. However, there may be other effects of female decapitation. For example, decapitated females can remain alive for up to 7 days and are reported to respond to physical contact ( Spieth, 1966) although

in our experiments the females did not exhibit rejection behaviours as previously observed ( Spieth, 1966). Females were also immobilised so they could not move away from males. What does seem clear though is that the decapitation treatment minimised the ability of females to exhibit rejection responses towards males and thereby influence the duration of mating through this mechanism. Selleckchem MAPK Inhibitor Library There was an effect, however, of female decapitation on the overall duration of mating. Males took significantly

longer to mate, and mated for a significantly shorter time overall, with decapitated females. This is consistent with previous work showing that male D. melanogaster will court decapitated females ( Cook and Cook, 1975, Grossfield, 1972 and Spieth, 1966), but at a reduced rate ( Cook and Cook, 1975). This is also in line with evidence that in Drosophilapalustris and D. subpalustris the proportion of inseminated decapitated females was half that of intact females ( Grossfield, 1972). However, the findings contrast with a study in D. montana, in which males were observed to mate for longer with decapitated females ( Mazzi et al., 2009). Females could influence courtship and mating duration in complex ways. For example, the manner in which the ovipositor is extruded can determine rejection or acceptance behaviour (Lasbleiz et Thalidomide al., 2006). Wild type patterns of courtship in males presumably therefore depend upon elements of female behaviour or other inputs that were not present in our immobilised, decapitated females. If females influenced mating duration through their rejection behaviours, then we might expect males to mate for longer with decapitated females in which such rejection is minimised. However, the opposite was found, as matings were shorter overall when with decapitated females. This suggests that there may be some positive feedback from females to prolong mating duration.

1A). These 31 sites represented our best judgment of conditions before the Selleck Venetoclax oil entered the estuaries. We were prevented from accessing most marshes until the fall 2010. Various agency and satellite image analyses at that time indicated that the most prominent oiling was in east and west Barataria Bay and eastern Terrebonne Bay. We focused on these three areas and chose the target areas before the field trip began, and then made our final selection while in the field and before landing the boat. Subsequent sampling included these three general areas, but the same exact sites were not always re-sampled because of landowner

permission, erosion, or logistical issues (principally the shallow water depth that hindered check details boat access). A core set of 12–13 site locations were sampled on each trip. Thirty sites were established on the northern edge of Bay Batiste in February 2011 (Fig. 1C). These were clusters of 3 stations 10 m apart and are the same sites used by McClenachan et al. (2013) for a marsh erosion study. Sites were marked

with a plastic 0.25 m2 quadrat to facilitate repeated sampling at the same location. We had no access to data on oil concentration to assist in site selection for any site until late summer 2011. We collected 405 surface-sediment samples from Louisiana coastal wetlands during May 2010 (n = 31), September 2010 (n = 64), February 2011 (n = 30), May 2011 (n = 87), September 2011 (n = 66), June 2012 (n = 22), August 2012 (n = 30), September 2012 (n = 30), October 2012 (n = 15), and June 2013 (n = 30) ( Fig. 1). The majority of the samples were collected within 10 m of the shoreline. Others were collected every 20 m along eight 90 m transects in June 2011, and five 100 m transects Carnitine palmitoyltransferase II in September 2011. These transects were perpendicular to the wetland/water interface. Sampling in February 2011, August 2012, September 2012, and June 2013 were within 1 m of each other. The primary emergent vegetation was Spartina alterniflora

and Juncus sp. with minor amounts of Schneoplectus americanus. The wetland type is commonly known as a ‘salt marsh’. All sediment samples were collected as a composite sample of the upper 5 cm, stored on ice until delivery to the laboratory, and either immediately extracted or refrigerated at 4 °C for no more than 14 days until extraction, as recommended by the US EPA (2007). The samples were analyzed using GC/MS-SIM that targeted 28 alkanes, 18 parent PAHs, and 25 alkyl homolog groups (Table 2). The target petrogenic compounds were extracted from the sediment samples using EPA SW-846 method 3540C (US EPA, 2000). Reagent grade or pesticide grade solvents were used in all the extractions and analyses. Samples were homogenized and a 15–20 g subsample was weighed, spiked with surrogate recovery standards (5-alpha androstane and phenanthrene-d10, AccuStandard, Inc.

5A). These vesicles were not seen in fresh or frozen morulaes of same quality. Cytoplasm discontinuities, as well as organelle-free

areas were common after vitrification (Fig. 5B), as in frozen embryos. Vitrified grade III and also frozen embryos had heterogeneous cytoplasm in addition to mitochondrial Selleck GSK3235025 and SER swelling (Fig. 5C). Large vesicles occupying great areas of the cytoplasm (Fig. 5D) and degenerated cells among viable embryonic cells (not shown) were characteristics found only in the vitrified group. In this study, fresh embryos revealed intense mitochondrial activity. Active mitochondria were distributed throughout the cytoplasm, regardless of the embryonic developmental stage. However, no mitochondrial activity could be observed in cryopreserved embryos, either frozen or vitrified. The evaluation of mitochondrial activity after cryopreservation are unpublished in this species and it is known that mitochondrial dysfunctions 5-FU chemical structure or abnormalities may compromise developmental processes by inducing chromosomal segregation disorders, maturation and fertilization failures or even embryo fragmentation [4]. Sohn et al. [35] studied the effect of two frequencies of liquid N2 infusion on the cryopreservation of mice two-cell embryos on the mitochondrial activity and actin filaments distribution using

fluorescent markers similar to those used on the present work. Very similar to what this study revealed, those authors [35] showed that the number of mitochondria with high membrane potential decreased on cryopreserved embryos, and described gaps or discontinuities in the peripheral actin fibers (those in close association with the cell membrane), especially on the low frequency N2 infusion treatment. Disturbances in function and distribution of mitochondria, as well as changes in the organization of cytoskeleton related to insufficient culture conditions or cryopreservation are expected to occur and may reduce developmental capacity [12] and [15]. Previous studies have demonstrated succesfull cryopreservation

of mitochondria isolated from rat liver [17], muscles [25] and brain [29]. In brain tissue, mitochondria showed a reduction in respiratory activity after cryopreservation. However, this effect was not due to mitochondrial membranes rupture [29]. Penetration of the fluorochrome used in this experiment is proportional to the inner mitochondrial Cyclin-dependent kinase 3 membrane activity and equilibrium [28], which was surely altered. However, in the present work no rupture of mitochondrial membranes was seen on the ultrastructural analysis. Nukala et al. [29] also found that freezing mitochondria without any cryoprotective agent destroyed their structural integrity and functional viability, and that the use of a cryopretective agent prevents most but not all damages. Moreover, the ability to restore a satisfactory metabolic activity or regenerate damaged structures after exposure to low temperatures requires time. For example, Leoni et al.

Generation of the Histocompatibility Map report. Preparation of CSV files is related to transferring CSV files to the input directory of the EpHLA program’s directory tree. The CSV files copied to the input directory are shown in the form Available CSV files in directory ( Fig. 1, [B]). Using this form, one or more files can be selected and processed (workflow’s second step). The EpHLA software uses information available in the HLAMatchmaker program’s spreadsheets ( [5]http://www.hlamatchmaker.net), including class of HLA and lot number of SPA kits (obtained from the Selleckchem Alisertib manufacturer — Fig. 1, [C]). The result of the processing is available in the EpHLA

— Local repository form. This form contains information on the recipient and his/her SPA results. Thus, one must access the Local repository form of the EpHLA software and type in the class I and class II HLA alleles of the recipient and donor. The next step is to determine the cutoff value. The standard value of the EpHLA

program is 500 of Median-Fluorescence Intensity (MFI). However, the laboratory personnel can define the value or alter to the suggested value in section Calculated Cutoff, according to Rene Duquesnoy [16] ( Fig. 2). In the last step, the EpHLA program executes the HLAMatchmaker algorithm to generate the Histocompatibility Map report. During this step, the recipient’s eplets of the self HLA molecules are removed from the histocompatibility analysis; click here the remaining eplets (non-self) are shown in the Histocompatibility Map report and classified by the EpHLA program as potentially or weakly immunogenic based on the adopted MFI cutoff value. All alleles of the panel whose MFI is lower than the cutoff established by the laboratory personnel will have its eplets classified as weakly immunogenic in all HLA molecules studied.

These eplets are shown in blue. Otherwise, the eplet is considered potentially immunogenic and is typed black or red. A black eplet means that it is not the only eplet responsible for immunogenicity Tacrolimus (FK506) of the HLA molecule. On the other hand, a red eplet stands for a unique eplet responsible for immunogenicity in at least one HLA molecule for the tested serum whose MFI value is larger than the cutoff. The Histocompatibility Map report from the EpHLA program contains two tabsheets: (i) Eplets Map and (ii) Eplet’s Report. Eplets Map contains five predictable tabs groupings: Acceptable Mismatches, No Mismatches, Recipient × Donor, Unacceptable Mismatches and All Mismatches (Fig. 3). These tabs allow the laboratory personnel to visualize, to order and to group HLA alleles so as to improve the histocompatibility study of the recipient/donor pair. The Recipient × Donor tab shows the donor’s HLA antigens and his/her eplets easing the immunological risk definition associated to the recipient/donor pair in the study.

1). The structural differences among HLö-7, HI-6, and obidoxime this website are in the number and position(s) of aldoximes on the pyridine rings (Kuca et al., 2006 and Ekström et al., 2009). Also, one of the ring groups

in HLö-7 and HI-6 is an isonicotinamide, which was included in their original synthesis to reduce toxicity (Oldiges and Schoene, 1970) but which, as molecular dynamic studies suggest, may also enhance ChE reactivation (Maxwell et al., 2008). HLö-7 and obidoxime are the most potent reactivators of phosphonylated and phosphorylated AChE, respectively (Worek et al., 2004). MMB4 and TMB-4 are the same 4-position bis-pyridinium aldoxime, except that MMB4 has a -CH2- linker while TMB-4 (a dibromide salt) has a -C3H6- linker. TMB-4 originated in 1958 and was the first bis-pyridinium oxime to be effective against GA (Schoene and Oldiges, 1973 and Inns and Leadbeater, 1983). The difference between these two similar compounds click here in terms of toxicity to the Hartley guinea pig by IM injection is remarkable: the 24-hour LD50 (median lethal dose) is 679 mg/kg (1514 μmol/kg) for MMB4 DMS (unpublished data), and 80 mg/kg (179 μmol/kg) for TMB-4 (Shih et al., 2009). The overall objective of this study was to compare rigorously the efficacy of currently fielded and select promising novel AChE oxime reactivators under strict standardized experimental conditions to enable an accurate and unbiased assessment

of their efficacies against OP CWNAs and pesticides. To accomplish this, the human equivalent FDA-approved dose of 2-PAM Cl was used as the experimental standard

and the equimolar oxime therapy was administered to atropinized guinea pigs after an LD85 challenge of each OP CWNA or pesticides (data not shown). The LD85 was selected as the challenge level across OPs because it maximized the power of the test to discriminate among the oximes in terms of lethality. Additionally, those Fludarabine chemical structure oximes with a safety index greater than 2-PAM Cl, i.e., MMB4 DMS, HI-6 DMS, MINA, and RS194B were also evaluated at an additional ‘therapeutic dose’ level equal to the median lethal dose (LD50) for the oxime divided by the TI for 2-PAM Cl. Overall efficacy was determined specifically in terms of QOL, blood cholinesterase levels in 24-hour survivors, and lethality. The five CWNAs evaluated were tabun (GA; O-ethyl N,N-dimethyl phosphoramidocyanidate), sarin (GB; O-isopropyl methylphosphonofluoridate), soman (GD; O-pinacolyl methylphosphonofluoridate), cyclosarin (GF, cyclohexyl methylphosphonofluoridate), and VX (O-ethyl S-(2-diisopropylaminoethyl) methylphosphonothiolate). They were obtained from the U.S. Army Edgewood Chemical Biological Center (Aberdeen Proving Ground, MD). The purity values of the CWNAs were > 98.5% as determined by gas chromatography. Chlorpyrifos oxon (purity ≥ 98%) and paraoxon (purity ≥ 98%) were purchased from Chem Service, Inc, West Chester, PA. Phorate oxon (purity ≥ 97.

The third spawning bed, which is dominated by F. lumbricalis, was visited twice within a period of three days at the end of April 2009. The sample taken on 21 April 2009 contained eggs Selleckchem PLX3397 in the embryonic developmental stages (m–n), and 3 days later the eggs had embryos already in developmental stages (o–p). According to Rajasilta et al. (1989, 1993, 2006) red algae (including F. lumbricalis) have a negative effect on Baltic herring eggs, causing higher egg mortality. However, in this study, the embryos in the eggs collected from F. lumbricalis thalli developed normally to the very last developmental stages, resulting in successful mass hatching. One of the advantages of F. lumbricalis as a spawning

substrate could CX-4945 cost be the extensive 3D structure of the firm F. lumbricalis thalli. This can accommodate a larger number of eggs while ensuring their proper aeration compared with other spawning surfaces, on which eggs may be laid in multilayers. It is known that embryonic oxygen uptake increases in the later development stages ( Silva & Tytlerb 1973); in multilayer mats only the eggs in the upper layers develop successfully to the last stages, whereas the eggs in the deeper layers abort (the abortion stage is layer-dependent: the deeper the egg, the earlier the abortion stage) and/or show severe embryonic abnormalities ( Messieh & Rosenthal 1989), most likely due to the lack of

oxygen. This is less likely to happen when F. lumbricalis is used as a spawning substrate. The locations of Baltic herring spawning beds are

usually very specific (Geffen 2009), and there are reports that Baltic herrings return to the same spawning beds year after year (Oulasvirta & Lehtonen 1988, Bergstrm et al., 2007). This occurs even if there is a strong anthropogenic impact in the area (Rajasilta et al. 2006). During this study the hydrological conditions between two spawning seasons were very different: in 2009 there was strong upwelling resulting in colder water and higher salinity. In 2010 the upwelling was not significant and the water in the coastal area was mixed with hyper-eutrophic Curonian Lagoon waters, resulting in greater turbidity and lower salinity. Moreover, the winter in 2010 was much colder and longer compared with 2009, resulting in later spawning (Figure 4). Despite these differences, ID-8 the spatial pattern of the spawning persisted, indicating that there are more stable factors determining the distribution of the spawning beds than just the hydrological conditions. One such factor could be the bottom geomorphology, which was tested in this study in terms of the bottom slope. Table 3 shows the average 100 m profile slopes to the east and west of the sampling points, the average profile depth gradients as well as the average maximum westward and eastward slopes values for 10 m segments with corresponding standard deviations. Graphical representations of the bottom profiles are shown in Figure 5.